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HomeMy WebLinkAbout06-24-2020 Board Item 9 - 2018-19 Marine Monitoring Report ral Gay i i ddW 'b. ORANGE COUNTY SANITATION DISTRICT Marine Monitoring Annual ort Year 2018-2019 Orange County, California ORANGE COUNTY SANITATION DISTRICT LABORATORY, MONITORING, AND COMPLIANCE DIVISION 10844 Ellis Avenue Fountain Valley, California 92708-7018 714.962.2411 www.ocsewers.com n 1 Serving: Orange County Sanitation District Anaheirn March 13, 2020 10844 Ellis Avenue,Fountain Valley,CA 92708 714.962.2411 • www.ocsd.com Brea Buena Park Hope Smythe Executive Officer Cypress California Regional Water Quality Control Board Santa Ana Region 8 Fountain Valley 3737 Main Street, Suite 500 Fullerton Riverside, CA 92501-3348 Garden Grove SUBJECT: Board Order No. R8-2012-0035, NPDES No. CA0110604, 2018-19 Marine Monitoring Annual Report Huntington Beach Irvine Dear Ms. Smythe, La Habra Enclosed is the Orange County Sanitation District's (OCSD) 2018-19 Marine La Palma Monitoring Annual Report. This report focuses on the findings and conclusions for Los Alamitos the monitoring period July 1, 2018 to June 30, 2019. The results of the monitoring program document that the discharge of our combined Newport Beach secondary-treated wastewater and water reclamation flows (collectively, the final effluent) into the coastal waters off Huntington Beach and Newport Beach, Orange California, neither affected the receiving environment nor posed a risk to human health. i; Placentia Santa Ana The results of the 2018-19 monitoring effort showed only minor changes in the coastal receiving water. Plume-related changes in dissolved oxygen, pH, and light Seal Beach transmissivity beyond the zone of initial dilution (ZID) were well within the range of natural variability, and compliance with numeric receiving water criteria was Stanton achieved at least 95% of the time. This demonstrated that the receiving water Tustin outside the ZID was not degraded by OCSD's final effluent discharge. Furthermore, the low concentrations of fecal indicator bacteria in water contact zones, together Villa Park with the low concentrations of ammonium at depth, also suggest that the final effluent discharge posed no human health risk and did not compromise recreational County of Orange use. i 8 Costa Mesa There were no impacts to the benthic animal communities within and adjacent to the y sanitary District ZID. Infauna and fish communities in the monitoring area were healthy based on, Midway City respectively, the low Benthic Response Index (<25) and Fish Response Index (<45) I Sanitary District values. In addition, contaminants in all sediment samples were comparable to background levels and no measurable toxicity was observed in whole sediment Irvine Ranch toxicity tests. The low levels of contaminants in fish tissue samples and the absence Water District Y p of disease symptoms in fish samples demonstrated that the outfall was not an Yorba Linda epicenter of disease. Water District h -I m �a T �r e N Our Mission: To protect public health and the environment by providing effective wastewater collection, treatment, and recycling. o�J�jV SANI r47,10 0 m � = 9 Should you have questions regarding the information provided in this report, or wish to meet with OCSD's staff to discuss any aspect of our ocean monitoring program, please feel free to contact me at (714) 593-7450 or at Iwiborgca--)ocsd.com. However, you may also contact Dr. Jeff Armstrong, the Environmental Supervisor of our Ocean Monitoring section, who may be reached at (714) 593-7455 or at larmstronq(cD-ocsd.com. Lan C. Wiborg, MPH Director of Environmental Services LCW:DT:bg \\filer-1\Lab\890\Groups\OMP\Common\Annual Reports\2018-19 Annual Report\01 -Cover and Front Matter\Cover Letters Enclosure cc: Tomas Torres, U.S. EPA, Region IX I a Serving. Orange County Sanitation District i Anaheim 10844 Ellis Avenue,Fountain Valley,CA 92708 j 714.962.2411 • www.ocsd.com Brea i Buena Park Cypress March 13, 2020 Fountain Valley Fullerton Certification Statement Garden Grove Huntington Beach The following certification satisfies Attachment E of the Orange County Irvine Sanitation District's Monitoring and Reporting Program, Order No. l._a Habra R8-2012-0035, NPDES No. CA0110604, for the submittal of the attached OCSD Annual Report 2020 — Marine Monitoring. La Palma Los Alamitos I certify under penalty of law that this document and all attachments were Newport Beach prepared under my direction or supervision in accordance with a system designed to assure that qualified personnel properly gathered and Orange evaluated the information submitted. Based on my inquiry of the person or persons who manage the system, or those persons directly responsible for Placentia gathering the information, the information submitted is, to the best of my knowledge and belief, true, accurate, and complete. I am aware that there Santa Ana are significant penalties for submitting false information, including the Seal Beach possibility of fines and imprisonment for known violations. Stanton Tustin � Villa Park r County of Orange Costa Mesa Lan C. Wiborg, MPH Sanitary District Director of Environmental Services Midway City Sanitary District Irvine Ranch Water District Yorba Linda Water District k INi 1^ i 9oj�cli�G N�a°��� "E` Our Mission: To protect public health and the environment by providing effective wastewater collection, treatment, and recycling. This page intentionally left blank. Contents Contents i List of Tables v List of Figures viii Acknowledgments x Executive Summary ES-1 WATER QUALITY ES-1 SEDIMENT QUALITY ES-1 BIOLOGICAL COMMUNITIES ES-1 Infaunal Communities ES-1 Demersal Fishes and Epibenthic Macro invertebrates ES-2 Contaminants in Fish Tissue ES-2 Fish Health ES-2 CONCLUSION ES-2 CHAPTER 1 The Ocean Monitoring Program 1-1 INTRODUCTION 1-1 ENVIRONMENTAL SETTING 1-1 DESCRIPTION OF OCSD'S OPERATIONS 1-5 REGULATORY SETTING FOR THE OCEAN MONITORING PROGRAM 1-7 REFERENCES 1-9 CHAPTER 2 Compliance Determinations 2-1 INTRODUCTION 2-1 WATER QUALITY 2-1 Offshore bacteria 2-1 Floating Particulates and Oil and Grease 2-1 Ocean Discoloration and Transparency 2-2 Dissolved Oxygen (DO) 2-3 Acidity (pH) 2-3 Nutrients (Ammonium) 2-3 COP Water Quality Objectives 2-4 Radioactivity 2-4 Overall Results 2-4 i Contents SEDIMENT GEOCHEMISTRY 2-5 BIOLOGICAL COMMUNITIES 2-10 Infaunal Communities 2-10 Epibenthic Macroinvertebrate Communities 2-11 Fish Communities 2-11 FISH BIOACCUMULATION AND HEALTH 2-11 Demersal and Sport Fish Tissue Chemistry 2-11 Fish Health 2-12 Liver Histopathology 2-12 CONCLUSIONS 2-12 REFERENCES 2-20 CHAPTER 3 Strategic Process Studies and Regional Monitoring 3-1 INTRODUCTION 3-1 STRATEGIC PROCESS STUDIES 3-1 ROMS-BEC Ocean Outfall Modeling (2019-2022) 3-1 Microplastics Characterization (2019-2020) 3-2 Contaminants of Emerging Concern Monitoring (2019-2020) 3-2 Sediment Linear Alkylbenzenes (2020-2021) 3-2 Meiofauna Baseline (2020-2021) 3-2 REGIONAL MONITORING 3-2 Regional Nearshore (Surfzone) Bacterial Sampling 3-2 Southern California Bight Regional Water Quality Program 3-3 Bight Regional Monitoring 3-4 Regional Kelp Survey Consortium — Central Region 3-5 Ocean Acidification and Hypoxia Mooring 3-6 SPECIAL STUDIES 3-6 California Ocean Plan Compliance Determination Method Comparison 3-6 Fish Tracking Study 3-8 REFERENCES 3-9 APPENDIX A Methods A-1 INTRODUCTION A-1 WATER QUALITY MONITORING A-1 Field Methods A-1 Laboratory Methods A-3 ii Contents Data Analyses A-3 Compliance Determinations A-3 SEDIMENT GEOCHEMISTRY MONITORING A-7 Field Methods A-7 Laboratory Methods A-7 Data Analyses A-8 BENTHIC INFAUNA MONITORING A-9 Field Methods A-9 Laboratory Methods A-9 Data Analyses A-9 TRAWL COMMUNITIES MONITORING A-10 Field Methods A-10 Laboratory Methods A-11 Data Analyses A-11 FISH TISSUE CONTAMINANTS MONITORING A-12 Field Methods A-12 Laboratory Methods A-12 Data Analyses A-12 FISH HEALTH MONITORING A-13 Field Methods A-13 Data Analyses A-13 REFERENCES A-14 APPENDIX B Supporting Data B-1 APPENDIX C Quality Assurance/Quality Control C-1 INTRODUCTION C-1 WATER QUALITY NARRATIVE C-1 Ammonium C-2 Bacteria C-4 SEDIMENT CHEMISTRY NARRATIVE C-5 PAHs, PCBs, and Organochlorine Pesticides C-5 Trace Metals C-5 Mercury C-10 DS C-10 TOC C-10 iii Contents Grain Size C-10 TN C-10 TP C-11 FISH TISSUE CHEMISTRY NARRATIVE C-11 Organochlorine Pesticides and PCB Congeners C-11 Lipid Content C-11 Mercury C-11 Arsenic and Selenium C-12 BENTHIC INFAUNA NARRATIVE C-13 Sorting C-13 Taxonomy C-13 REFERENCES C-15 iv List of Tables Table 2-1 List of compliance criteria from OCSD's NPDES permit (Order No. R8-2012-0035, Permit No. CA0110604) and compliance status for each criterion in 2018-19. N/A= Not Applicable. 2-2 Table 2-2 Summary of offshore water quality compliance testing results for dissolved oxygen, pH, and light transmissivity for 2018-19. 2-6 Table 2-3 Physical properties, as well as biogeochemical and contaminant concentrations, of sediment samples collected at each semi-annual station in Summer 2018 compared to Effects Range-Median (ERM) and regional values. ND = Not Detected, N/A= Not Applicable. 2-7 Table 2-4 Metal concentrations (mg/kg) in sediment samples collected at each semi- annual station in Summer 2018 compared to Effects Range-Median (ERM) and regional values. N/A= Not Applicable. 2-8 Table 2-5 Physical properties, as well as biogeochemical and contaminant concentrations, of sediment samples collected at each semi-annual station in Winter 2019 compared to Effects Range-Median (ERM) and regional values. ND = Not Detected, N/A= Not Applicable. 2-9 Table 2-6 Metal concentrations (mg/kg) in sediment samples collected at each semi- annual station in Winter 2019 compared to Effects Range-Median (ERM) and regional values. ND =Not Detected, N/A= Not Applicable. 2-10 Table 2-7 Whole-sediment Eohaustorius estuarius (amphipod) toxicity test results for 2018-19. The home sediment represents the control; N/A= Not Applicable. 2-10 Table 2-8 Community measure values for each semi-annual station sampled during the Summer 2018 infauna survey, including regional and historical values. NC = Not Calculated. 2-12 Table 2-9 Community measure values for each semi-annual station sampled during the Winter 2019 infauna survey, including regional and historical values. NC = Not Calculated. 2-13 Table 2-10 Summary of epibenthic macroinvertebrate community measures for each semi-annual station sampled during the Summer 2018 and Winter 2019 trawl surveys, including regional and historical values. NC = Not Calculated. 2-16 Table 2-11 Summary of demersal fish community measures for each semi-annual station sampled during the Summer 2018 and Winter 2019 trawl surveys, including regional and District historical values. NC = Not Calculated. 2-16 Table 2-12 Means and ranges of tissue contaminant concentrations in selected flatfishes collected by trawling in July 2018 at Stations T1 (Outfall) and T11 (Non-outfall), as well as historical values. ND = Not Detected. 2-18 v List of Tables Table 2-13 Means and ranges of muscle tissue contaminant concentrations in selected scorpaenid and sand bass fishes collected by rig-fishing in April/May 2019 at Zones 1 (Outfall) and 3 (Non-outfall), including historical values and state and federal thresholds. ND = Not Detected; NC = Not Collected; N/A = Not Applicable. 2-19 Table 3-1 Comparison of monthly California Ocean Plan compliance determinations using OCSD and SCCWRP methodologies for dissolved oxygen, pH, and light transmissivity for 2018-19. 3-7 Table A-1 Water quality sample collection and analysis methods by parameter during 2018-19. A-2 Table A-2 Sediment collection and analysis summary during 2018-19. A-7 Table A-3 Parameters measured in sediment samples during 2018-19. A-8 Table A-4 Benthic infauna taxonomic aliquot distribution for 2018-19. A-9 Table A-5 Fish tissue handling and analysis summary during 2018-19. A-13 Table A-6 Parameters measured in fish tissue samples during 2018-19. A-13 Table B-1 Percent of fecal indicator bacteria by quarter and depth strata for the 2018-19 REC-1 water quality surveys (5 surveys/quarter; 8 stations/survey). B-1 Table B-2 Depth-averaged total coliform bacteria (MPN/100 mL) collected in offshore waters and used for comparison with California Ocean Plan Water-Contact (REC-1) Standards, July 2018 through June 2019. B-2 Table B-3 Depth-averaged fecal coliform bacteria (MPN/100 mL) collected in offshore waters and used for comparison with California Ocean Plan Water-Contact (REC-1) Standards, July 2018 through June 2019. B-3 Table B-4 Depth-averaged enterococci bacteria (MPN/100 mL) collected in offshore waters and used for comparison with California Ocean Plan Water-Contact (REC-1) Standards and EPA Primary Recreation Criteria in Federal Waters, July 2018 through June 2019. B-4 Table B-5 Summary of floatable material by station group observed during the 28-station grid water quality surveys, July 2018 through June 2019. Total number of station visits = 336. B-5 Table B-6 Summary of floatable material by station group observed during the REC-1 water quality surveys, July 2018 through June 2019. Total number of station visits = 108. B-5 Table B-7 Summary of Core water quality compliance parameters by quarter and depth strata for 2018-19 (3 surveys/quarter; 28 stations/survey). B-6 Table B-8 Summary of Core water quality ammonium (mg/L) receiving water criteria by quarter and depth strata for 2018-19 (3 surveys/quarter; 22 stations/survey). B-7 A List of Tables Table B-9 Species richness and abundance values of the major taxonomic groups collected in the Middle Shelf Zone 2 stratum (51-90 m) for the 2018-19 infauna surveys. Values represent the mean and range (in parentheses). B-7 Table B-10 Abundance and species richness of epibenthic macroinvertebrates by station and species for the Summer 2018 and Winter 2019 trawl surveys. B-8 Table B-11 Biomass (kg) of epibenthic macro invertebrates by station and species for the Summer 2018 and Winter 2019 trawl surveys. B-9 Table B-12 Abundance and species richness of demersal fishes by station and species for the Summer 2018 and Winter 2019 trawl surveys. B-10 Table B-13 Biomass (kg) of demersal fishes by station and species for the Summer 2018 and Winter 2019 trawl surveys. B-11 Table B-14 Summary statistics of OCSD's legacy nearshore stations for total coliform, fecal coliform, and enterococci bacteria (CFU/100 mL) by station and quarter during 2018-19. B-12 Table C-1 Method detection limits (MDLs) and reporting limits (RLs), July 2018—June 2019. C-2 Table C-2 Water quality QA/QC summary, July 2018-June 2019. C-4 Table C-3 Acceptance criteria for standard reference materials, July 2018-June 2019. C-6 Table C-4 Sediment QA/QC summary, July 2018-June 2019. C-8 Table C-5 Fish tissue QA/QC summary, July 2018-June 2019. C-12 Table C-6 Percent error rates calculated for the July 2018 infauna QA samples. C-14 vii List of Figures Figure 1-1 Regional setting and sampling area for OCSD's Ocean Monitoring Program. 1-2 Figure 1-2 United States 2010 urbanized areas. (https://www.census.gov/library/ visualizations/2010/geo/ua2010—uas—and_ucs—map.html). 1-3 Figure 1-3 Annual Newport Harbor rainfall (A) and Santa Ana River flows (B). 1-4 Figure 1-4 Monthly 2018-19 beach attendance and air temperature (A) and annual beach attendance (B) for the City of Newport Beach, California. 1-6 Figure 1-5 OCSD's average annual influent and ocean discharge, OCWD's reclamation, and annual population for Orange County, California, 1974-2019. 1-7 Figure 2-1 Offshore water quality monitoring stations for 2018-19. 2-3 Figure 2-2 Benthic (sediment geochemistry and infauna) monitoring stations for 2018-19. 2-4 Figure 2-3 Trawl monitoring stations, as well as rig-fishing locations, for 2018-19. 2-5 Figure 2-4 Summary of mean percent compliance for dissolved oxygen (DO), pH, and light transmissivity for all compliance stations compared to reference stations, 1999-2019. 2-6 Figure 2-5 Dendrogram (top panel) and non-metric multidimensional scaling (nMDS) plot (bottom panel) of the infauna collected at within- and non-ZID stations along the Middle Shelf Zone 2 stratum for the Summer 2018 (S) and Winter 2019 (W) benthic surveys. Stations connected by red dashed lines in the dendrogram are not significantly differentiated based on the SIMPROF test. The 5 main clusters formed at a 45% similarity on the dendrogram are superimposed on the nMDS plot. 2-14 Figure 2-6 Dendrogram (top panel) and non-metric multidimensional scaling (nMDS) plot (bottom panel) of the epibenthic macroinvertebrates collected at outfall and non-outfall stations along the Middle Shelf Zone 2 stratum for the Summer 2018 (S) and Winter 2019 (W) trawl surveys. Stations connected by red dashed lines in the dendrogram are not significantly differentiated based on the SIMPROF test. The three main clusters formed at a 50% similarity on the dendrogram are superimposed on the nMDS plot. 2-15 Figure 2-7 Dendrogram (top panel) and non-metric multidimensional scaling (nMDS) plot (bottom panel) of the demersal fishes collected at outfall and non-outfall stations along the Middle Shelf Zone 2 stratum for the Summer 2018 (S) and Winter 2019 (W) trawl surveys. Stations connected by red dashed lines in the dendrogram are not significantly differentiated based on the SIMPROF test. The single cluster formed at a 61% similarity on the dendrogram is superimposed on the nMDS plot. 2-17 viii List of Figures Figure 3-1 Offshore and nearshore (surfzone) water quality monitoring stations for 2018-19. 3-3 Figure 3-2 Southern California Bight Regional Water Quality Program monitoring stations for 2018-19. 3-4 Figure 3-3 OCSD's Bight'18 sampling stations. 3-5 Figure 3-4 Comparison of monthly OCSD (blue) and SCCWRP (red) California Ocean Plan Compliance results for Program Years 2016-17 to 2018-19 (n=36). N/A = Not Applicable. 3-8 Figure A-1 Offshore water quality monitoring stations and zones used for California Ocean Plan compliance determinations. A-4 ix Acknowledgments The following individuals are acknowledged for their contributions to the 2018-19 Marine Monitoring Annual Report: Orange County Sanitation District Management: Lan C. Wiborg...............................................Director, Environmental Services Department Ron Coss................................. Manager, Laboratory, Monitoring, and Compliance Division Dr. Jeffrey L. Armstrong.................... Environmental Supervisor, Ocean Monitoring Section Ocean Monitoring Team: George Robertson........................................................................................Senior Scientist Dr. Danny Tang........................................................................................................Scientist Kelvin Barwick................................................................ Principal Environmental Specialist Ken Sakamoto....................................................................Senior Environmental Specialist Hai Nguyen.........................................................................Senior Environmental Specialist Robert Gamber...................................................................Senior Environmental Specialist Laura Terriquez..................................................................Senior Environmental Specialist Ernest Ruckman.................................................................Senior Environmental Specialist Benjamin Ferraro................................................................Senior Environmental Specialist Geoffrey Daly......................................................................... Environmental Specialist MarkKibby.....................................................................................................Boat Captain MeganNguyen............................................................................................................ Intern Laboratory Team: Miriam Angold, Jim Campbell, Dr. Sam Choi, Absalon Diaz, Arturo Diaz, Joel Finch, Elaine Galvez, Thang Mai, Joe Manzella, Ryan McMullin, Dawn Myers, Canh Nguyen, Thomas Nguyen, Paulo Pavia, Vanh Phonsiri, Anthony Pimentel, Larry Polk, Paul Raya, Joseph Robledo, Jesus Rodriguez, Luis Ruiz, Dr. Yu-Li Tsai, and Brandon Yokoyama. IT and LIMS Data Support: Emmeline McCaw and Matthew Garchow. Contributing Authors: Kelvin Barwick, Dr. Sam Choi, Benjamin Ferraro, Robert Gamber, Thang Mai, Joe Manzella, Dawn Myers, Hai Nguyen, Vanh Phonsiri, Anthony Pimentel, George Robertson, Ernest Ruckman, Ken Sakamoto, Dr. Danny Tang, Laura Terriquez, and Dr. Yu-Li Tsai. x EXECUTIVE SUMMARY To evaluate potential environmental and human health impacts from its discharge of final effluent into the Pacific Ocean, the Orange County Sanitation District (OCSD) conducts extensive water quality, sediment quality, fish and invertebrate community, and fish health monitoring off the coastal cities of Newport Beach and Huntington Beach, California. The discharge, consisting of secondary- treated wastewater mixed with water reclamation flows, is released through a 120-in (305-cm) outfall extending 4.4 miles (7.1 km) offshore in 197 ft (60 m) of water. The data collected are used to determine compliance with receiving water conditions as specified in OCSD's National Pollution Discharge Elimination System permit (Order No. R8-2012-0035, Permit No. CA0110604), jointly issued in 2012 by the U.S. Environmental Protection Agency, Region IX and the Regional Water Quality Control Board, Region 8. This report focuses on monitoring results and conclusions from July 2018 through June 2019. WATER QUALITY The public health risks and measured environmental effects to the receiving water continue to be negligible. All state and federal offshore bacterial standards were met during the monitoring period. Minimal plume-related changes in dissolved oxygen, pH, and light transmissivity were detected less than 1.2 miles (2.0 km) beyond the initial mixing zone during some surveys. However, the limited, observable plume effects occurred primarily at depth, even during the winter when stratification was weakest. In addition, the changes were within the ranges of natural variability for the monitoring area and reflected seasonal and yearly changes of large-scale regional influences. In summary, the 2018-19 discharge of final effluent did not greatly affect the receiving water environment; therefore, beneficial uses were protected and maintained. SEDIMENT QUALITY Sediment parameters were comparable between benthic stations located within and beyond the zone of initial dilution' (ZID), and all measured values were below applicable Effects-Range-Median guidelines of biological concern. In addition, whole sediment toxicity tests showed no measurable toxicity. These results, together with the presence of diverse fish and invertebrate communities adjacent to and farther afield from the outfall (see below), indicate good sediment quality in the monitoring area. BIOLOGICAL COMMUNITIES Infaunal Communities Infaunal communities were generally similar among within-ZID and non-ZID benthic stations based on comparable community measure values and the results of multivariate analyses. Moreover, the infaunal communities within the monitoring area can be classified as reference condition based on their low Benthic Response Index values (<25) and high Infaunal Trophic Index values (>60). These results indicate that the outfall discharge had an overall negligible effect on the benthic community structure within the monitoring area. ' The zone of initial dilution represents a 60 m area around the OCSD outfall diffuser. ES-1 Executive Summary Demersal Fishes and Epibenthic Macroinvertebrates Community measure values of the epibenthic macroinvertebrates (EMIs) and demersal fishes collected at outfall and non-outfall trawl stations were comparable and were within regional and OCSD historical ranges. In addition, fish communities at all stations were classified as reference condition based on their low Fish Response Index values (<45). These results indicate that the monitoring area supports normal fish and EMI populations. Contaminants in Fish Tissue Concentrations of chlorinated pesticides and trace metals in muscle and/or liver tissues of flatfish and rockfish samples were similar between outfall and non-outfall locations. Moreover, mean concentrations of contaminants in muscle tissue of rockfish samples were below federal and state human consumption guidelines. These results suggest that demersal fishes residing near the outfall are not more prone to bioaccumulation of contaminants and demonstrate there is negligible human health risk from consuming demersal fishes captured in the monitoring area. Fish Health The color and odor of demersal fish samples appeared normal during the monitoring period. In addition, the low incidence (<1%) of external parasites and morphological abnormalities, combined with the absence of tumors, fin erosion, and skin lesions, in demersal fish samples showed that fishes in the monitoring area were healthy. These results indicate that the outfall is not an epicenter of disease. CONCLUSION Consistent with previous program years, California Ocean Plan water quality criteria, as well as state and federal bacterial standards, were met within the monitoring area in 2018-19. Sediment quality was not degraded by chemical contaminants or by physical changes from the discharge of final effluent. This was supported by the absence of sediment toxicity in controlled laboratory tests, the presence of normal invertebrate and fish communities throughout the monitoring area, the absence of symptoms of fish disease, and no exceedances in federal and state fish consumption guidelines in rockfish samples. In summary, OCSD's discharge of final effluent neither affected the receiving environment nor posed a risk to human health during the 2018-19 monitoring period. ES-2 _- -=- CHAPTER 1 The Ocean Monitoring Program INTRODUCTION The Orange County Sanitation District (OCSD) operates 2 wastewater treatment facilities located in Fountain Valley (Plant 1) and Huntington Beach (Plant 2), California. OCSD discharges treated wastewater to the Pacific Ocean through a 120-in (305-cm) submarine outfall located offshore of the Santa Ana River (Figure 1-1). This discharge is regulated by the US Environmental Protection Agency (EPA), Region IX and the Regional Water Quality Control Board (RWQCB), Region 8 under the Federal Clean Water Act, the California Ocean Plan, and the RWQCB Basin Plan. Specific discharge and monitoring requirements are contained in a National Pollutant Discharge Elimination System (NPDES) permit issued jointly by the EPA and the RWQCB ( _)ruer ivo. reel-zu I L-uu.5e, NPDES Permit No. CA0110604) on June 15, 2012. ENVIRONMENTAL SETTING OCSD's ocean monitoring area is adjacent to one of the most highly urbanized areas in the United States (Figure 1-2). The monitoring area covers most of the San Pedro Shelf and extends southeast off the shelf (Figure 1-1). These nearshore coastal waters receive wastes from a variety of anthropogenic sources, such as wastewater discharges, dredged material disposal, oil and gas activities, boat/vessel discharges, urban and agricultural runoff, and atmospheric fallout. The majority of municipal and industrial sources are located between Point Dume and San Mateo Point (Figure 1-1) while discharges from the Los Angeles, San Gabriel, and Santa Ana Rivers are responsible for substantial surface water contaminant inputs to the Southern California Bight (SCB) (Schafer and Gossett 1988, SCCWRP 1992, Schiff et al. 2000, Schiff and Tiefenthaler 2001, Tiefenthaler et al. 2005). The San Pedro Shelf is primarily composed of soft sediments (sands with silts and clays) and is inhabited by biological communities typical of these environments (OCSD 2004). Seafloor depths increase gradually from the shoreline to approximately 262 ft (80 m), after which it increases rapidly down to the open basin. The outfall diffuser lies at about 197 ft (60 m) depth on the shelf between the Newport and San Gabriel submarine canyons, located southeast and northwest, respectively. The area southeast of the San Pedro Shelf is characterized by a much narrower shelf and deeper water offshore (Figure 1-1). The 120-in outfall represents one of the largest artificial reefs in this coastal region and supports communities typical of hard substrates that would not otherwise be found in the monitoring area (Lewis and McKee 1989, OCSD 2000). Together with OCSD's 78-in (198-cm) outfall, approximately 1.1 x 106 ft2 (102,193 m2) of seafloor was converted from a flat, sandy habitat into a raised, hard-bottom substrate. 1-1 The Ocean Monitoring Program Pain, Dume 3-mile Line _ ——— ——\ 11 2 City OflI yyLOS AngCI05 2 c I Outfells� \ Um \, y J Rmer � Santa Ana Palos Verdes \ Peninsula coumySanitanunoilt', ofLusnngoles OCSD's Service Area (J,1WI,pcp \ Olfalls /San Pedro\` o shelf a oli t of osnn�eles �� 'r�iilandl � � �r� O ` an` S Gabriel ` CSO` canyon I cap on S OCSD "'Outfalls San e. so—A s," Oars I e t 0 13 26 Miles 0 10.5 21 42 Kllomelers Esri,Garmin,6EBC0,NOAA N6DC,and other contributors OCSD March 2020 1 Figure 1-1 Regional setting and sampling area for OCSD's Ocean Monitoring Program. Conditions within OCSD's monitoring area are affected by both regional- and local-scale oceanographic influences. Large regional climatic and current conditions, such as El Nino and the California Current, influence the water characteristics and the direction of water flow along the Orange County coastline (Hood 1993). Locally, the predominant low-frequency current flows in the monitoring area are alongshore (i.e., either upcoast or downcoast) with minor across-shelf (i.e., toward the beach) transport (OCSD 1997, 1998, 2004, 2011; SAIC 2001, 2009, 2011). The specific direction of the flows varies with depth and is subject to reversals over time periods of days to weeks (SAIC 2011). Other natural oceanographic processes, such as upwelling, coastal eddies and algal blooms, also influence the characteristics of receiving waters on the San Pedro Shelf. Tidal flows, currents, and internal waves mix and transport OCSD's wastewater discharge with coastal waters and resuspended sediments. Tidal currents in the monitoring area are relatively weak compared to lower frequency currents, which are responsible for transporting material over long distances (OCSD 2001, 2004). Combined, these processes contribute to the variability of seawater movement observed within the monitoring area. Harmful algal blooms, while variable, have both regional and local distributions that can impact human and marine organism health (UCSC 2018, CeNCOOS 2019). Episodic storms, drought, and climatic cycles influence environmental conditions and biological communities within the monitoring area. For example, stormwater runoff has a large influence on 1-2 The Ocean Monitoring Program •t.,M� Py. 0 500MIles • k:i �Tii F' #'• .Urbanized Area * Urban Cluster •} . VV tetl States di o too Mlle: Sus •o_soMues Source:U.S.Census Bureau,2010 Census Urban Area Delineation Program Figure 1-2 United States 2010 urbanized areas. (https://www.census.gov/library/ visual izations/2010/geo/ua2010_uas_and_ucs_map.html). sediment movement in the region (Brownlie and Taylor 1981, Warrick and Millikan 2003). Major storms contribute large amounts of contaminants to the ocean and can generate waves capable of extensive shoreline erosion, sediment resuspension, and movement of sediments along the coast as well as offshore. Some of the greatest effects are produced by wet weather cycles, periods of drought, and periodic oceanographic events, such as El Nino and La Nina conditions. An understanding of the effects of the inputs from rivers and watersheds, particularly non-point source runoff, is important for evaluating spatial and temporal trends in the environmental quality of coastal areas. River flows, together with urban stormwater runoff, represent significant, episodic sources of fresh water, sediments, suspended particles, nutrients, bacteria and other contaminants to the coastal area (Hood 1993, Grant et al. 2001, Warwick et al. 2007), although some studies indicate that the spatial impact of these effects may be limited (Ahn et al. 2005, Reifel et al. 2009). While many of the materials supplied to coastal waters by rivers are essential to natural biogeochemical cycles, an excess or a deficit may have important environmental and human health consequences. For 2018-19, both annual rainfall (NCEI 2019) and Santa Ana River flows (USGS 2019) were at or above historical averages (Figure 1-3). A previous year of well below average rainfall led to high quality beaches, with 95% of southern California beaches receiving "grades" of A or B by Heal the Bay (2019). Beaches are a primary reason for people to visit coastal California (Kildow and Colgan 2005, NOAA 2015). Although highest visitations occur during the warmer, summer months, southern 1-3 The Ocean Monitoring Program 30 A 25 20 N N L V C 15 16 C M Mean(1923-2019) 10 5 0 1,000,000 100,000 B Mean 1923.2019 10,000 rn 0 01 C O R - 1,000 O 3 0 LL 100 10 1 9 9 W 9 V N N W O N V (D T O N V (D W rn m rn rn rn rn rn o 0 0 0 0 0 0 0 0 0 rn m rn rn m w rn o 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 N N N N N N N N N N N N N N N N N N N Program Year(July to June) Figure 1-3 Annual Newport Harbor rainfall (A) and Santa Ana River flows (B). 1-4 The Ocean Monitoring Program California's Mediterranean climate and convenient beach access results in significant year-round use by the public (Figure 1-4). For 2018-19, beach attendance for the City of Newport Beach was just below 7.5 million. A large percentage of the local economies rely on beach use and its associated recreational activities, which are highly dependent upon local water quality conditions (Turbow and Jiang 2004, Leeworthy and Wiley 2007, Leggett et al. 2014). In 2012, Orange County's coastal economy accounted for $3.8 billion (2%) of the County's Gross Domestic Product (NOAA 2015). It has been estimated that a single day of beach closure at Bolsa Chica State Beach would result in an economic loss of$7.3 million (WHOI 2003). DESCRIPTION OF OCSD'S OPERATIONS OCSD's mission is to safely collect, process, recycle, and dispose of treated wastewater while protecting human health and the environment in accordance with federal, state, and local laws and regulations. These objectives are achieved through extensive industrial pre-treatment (source control), secondary treatment processes, biosolids management, and water reuse programs. OCSD's 2 wastewater treatment plants receive domestic sewage from approximately 80% of the County's 3.2 million residents and industrial wastewater from 688 permitted businesses within its service area. Under normal operations, the treated wastewater (effluent) is discharged through a 120-in diameter ocean outfall, which extends 4.4 miles (7.1 km) from the Huntington Beach shoreline (Figure 1-1). The last 1.1 miles (1.8 km) of the outfall consists of a diffuser with 503 ports that discharge the treated effluent at an approximate depth of 60 m. OCSD will accept up to 10 million gallons per day (MGD; 3.8 x 10' L/day) of dry-weather urban runoff that would otherwise have entered the ocean without treatment (OCSD 2019). The collection and treatment of dry-weather runoff, which began as a regional effort to reduce beach bacterial pollution associated with chronic dry-weather flows, has grown to include accepting diversions of high selenium flows to protect Orange County's waterways. Currently there are 21 active diversions including stormwater pump stations, the Santa Ana River, several creeks, and 3 flood control channels. For 2018-19, OCSD treated 337 million gallons (MG; 1.3 x 109 L) of flow, nearly identical to the 2013-2018 average yearly flow of 378 MG (1.4 x 109 L). Monthly average daily diversion flows ranged from 0.3-1.6 MGD (1.1-6.1 x 106 L/day) with an average daily amount of 1 MGD (3.8 x 106 L/day). OCSD has a long history of providing treated effluent to the Orange County Water District (OCWD) for water reclamation starting with Water Factory 21 in the late 1970s. Since July 1986, 3-10 MGD (1.1-3.8 x 107 L/day) of the final effluent have been provided to OCWD where it received further (tertiary) treatment to remove residual solids in support of the Green Acres Project (GAP). OCWD provides this water for a variety of uses including public landscape irrigation (e.g., freeways, golf courses) and for use as a saltwater intrusion barrier in the local aquifer OCWD manages. In 2007-08, OCSD began diverting additional flows to OCWD for the Groundwater Replenishment System (GWRS) totaling 35 MGD (1.3 x 108 L/day). Over time, the average net GAP and GWRS diversions (diversions minus return flows to OCSD) increased to 44 MGD (1.7 x 101 L/day) in 2008-09, 61 MGD (2.3 x 10$ L/day) in 2013-14, and 97 MGD (3.7 x 101 L/day) in 2018-19 (Figure 1-5). During 2018-19, OCSD's 2 wastewater treatment plants received and processed influent volumes averaging 191 MGD (7.2 x 101 L/day). After diversions to the GAP and GWRS and the return of OCWD's reject flows (e.g., brines), OCSD discharged an average of 104 MGD (3.9 x 101 L/day) of treated wastewater to the ocean (Figure 1-5). 1-5 The Ocean Monitoring Program 2.5 .` 80 A 75 2.0 ; _70 a 65 -2018-19 Mean / 0 ---1921-2019 Mean / 1.5 60, // / i� Q %% 55 Ju1-18 Aug-18 Sep-18 Oct-18 Nov-18 Dec-18 Jan-19 Feb-19 Mar-19 Apr-19 May-19 Jun-19 I csi 1.0 % cc ` / d ` m ; / % ———Range Mean % 0.5 0.0 Jul-18 Aug-18 Sep-18 Oct-18 Nov-18 Dec-18 Jan-19 Feb-19 Mar-19 Apr-19 May-19 Jun-19 Month 11 B 10 Mean(1993-2019) 9 8 c O 7 d 6 0 c m 5 r Q cLi 4 m d m 3 2 1 0 V Ln O r� OJ O O N M V m O n of m O N (2 V L2 m m T lT O m O O O O O O O O O O M 'IT (n (D r-- W � O N M V V) (D r.- M M O N M O) tT tT O 6) tT O O O O O O O O O O 6) O O O O O O O O O O O O O O O O O O O O O O N N N N N N N N N N N N N N N N N N N Program Year(July to June) Figure 1-4 Monthly 2018-19 beach attendance and air temperature (A) and annual beach attendance (B) for the City of Newport Beach, California. 1-6 The Ocean Monitoring Program 300 3.5 i 3.0 250 / 2.5 ' \ _ 200 II ✓ ✓ ` _ � o ✓ 2.0 = d p 150 LL 3 C v 1.5 p �2 H 100 Ocean Discharge / 1.0 Influent OCWD Reclamation 50 � OC Population / .� / 0.5 0 — 0.0 (D (O r W O O N M V lD (D r W D) O N M V 0 W r W m O N M V In W t` W d) O W N M_ 7 lD W t\ W O W W W W W W W W W W (n ,, ,) QJ , 0 0 M 4) 0 0 0 0 0 0 0 0 0 0 V In Co r W M O N M v (n M t_ W M O N M I In (O r- 00 M O — N M V U) (O I- M M O N M 4 6 (O I-� Oj 00 W W W W W Co Co W W M M W m M O M 0) M W 0 0 0 0 0 0 0 0 0 0 d1 O) W D7 O) O) d2 Q) O Q2 W m Ql D) m O Q) O D) T D) d) O D) Q) 0 NO ON ON 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 0 � � � � � � � � � � � � � � � � N N N N N N N N N N N N N N N N N N N Program Year(July to June) Figure 1-5 OCSD's average annual influent and ocean discharge, OCWD's reclamation, and annual population for Orange County, California, 1974-2019. Prior to 1990, the annual wastewater discharge volumes increased faster than Orange County population growth (CDF 2019) (Figure 1-5). Wastewater flows decreased in 1991-92 due to drought conditions and water conservation measures and then rose at the same rate as the population until the end of the late 1990s. Since then, influent flows have decreased. Reductions in influent flows have been attributed to improved water efficiency and decreases in water use. The combined effect of reduced influent and increased water reclamation flows have dramatically reduced ocean discharge flows. REGULATORY SETTING FOR THE OCEAN MONITORING PROGRAM OCSD's NPDES permit includes requirements to monitor influent, effluent, and the receiving water. Effluent flows, constituent concentrations, and toxicity are monitored to determine compliance with permit limits and to provide data for interpreting changes to receiving water conditions. Wastewater impacts to coastal receiving waters are evaluated by OCSD's Ocean Monitoring Program (OMP) based on 3 inter-related components: (1) Core monitoring, (2) Strategic Process Studies (SPS), and (3) Regional monitoring. In addition, OCSD conducts special studies not required under the existing NPDES permit. Information obtained from each of these program components is used to further the understanding of the coastal ocean environment and improve interpretations of the monitoring data. These program elements are summarized below. 1-7 The Ocean Monitoring Program The Core monitoring program was designed to measure compliance with permit conditions and for temporal trend analysis. Four major components comprise the program: (1) coastal oceanography and water quality, (2) sediment quality, (3) benthic infaunal community health, and (4) demersal fish and epibenthic macroinvertebrate community health, which include fish tissue contaminant analyses. OCSD conducts SPS, as well as other smaller special studies, to provide information about relevant coastal and ecotoxicological processes that are not addressed by Core monitoring. Recent studies have included contributions to the development of ocean circulation and biogeochemical models and fish tracking. Since 1994, OCSD has participated in 6 regional monitoring studies of environmental conditions within the SCB: 1994 Southern California Bight Pilot Project, Bight'98, Bight'03, Bight'08, Bight'13, and Bight'18. OCSD plays an integral role in these regional projects by leading many of the program design decisions and conducting field sampling, sample analysis, data analysis, and reporting. Results from these efforts provide information that is used by individual dischargers, local, state, and federal resource managers, researchers, and the public to improve understanding of regional environmental conditions. This provides a larger-scale perspective for comparisons with data collected from local, individual point sources. Program documents and reports can be found at the Southern California Coastal Water Research Project's website Other collaborative regional monitoring efforts include: • Participation in the Southern California Bight Regional Water Quality Program (previously known as the Central Bight Water Quality Program), a water quality sampling effort with other Publicly Owned Treatment Works (POTWs) such as the City of Oxnard, the City of Los Angeles, the County Sanitation Districts of Los Angeles, and the City of San Diego. • Supporting and working with the Southern California Coastal Ocean Observing System to upgrade sensors on the Newport Pier Automated Shore Station (http://www.sccoos.org/data/ autos). • Partnering with the Orange County Health Care Agency and other local POTWs to conduct regional nearshore (aka surfzone) bacterial monitoring used to determine the need for beach postings and/or closure. • Collaborating on a regional aerial kelp monitoring program. The complexities of the environmental setting and related difficulties in assigning a cause or source to a pollution event are the rationale for OCSD's extensive OMP. The program has contributed substantially to the understanding of water quality and environmental conditions along Orange County beaches and coastal ocean reach. The large amount of information collected provides a broad understanding of both natural and anthropogenic processes that affect coastal oceanography and marine biology, the near-coastal ocean ecosystem, and its related beneficial uses. This report presents OMP compliance determinations for data collected from July 2018 through June 2019. Compliance determinations were made by comparing OMP findings to the criteria specified in OCSD's NPDES permit. Any related special studies or regional monitoring efforts are also documented. 1-8 The Ocean Monitoring Program REFERENCES Ahn, J.H., S.B. Grant, C.Q. Surbeck, P.M. Digiacomo, N.P. Nezlin, and S. Jiang. 2005. Coastal water quality impact of stormwater runoff from an urban watershed in Southern California. Environ. Sci. Technol. 39:5940-5953. Brownlie, W.D. and B.D. Taylor. 1981. Sediment management for Southern California mountains, coastal plains, and shorelines. Part C. Coastal Sediment Delivery by Major Rivers in Southern California. Environmental Quality Laboratory Report 17C. California Institute of Technology, Pasadena, CA. CDF (California State Department of Finance). 2019. Demographic Reports. California County Population Estimates and Components of Change by Year - July 1, 2010-2016. Internet address: dot.ca.gov/Forecasting/Demographics/Estimates/E-2/2010-16/. (December 2019). CeNCOOS (Central and Northern California Ocean Observation System. 2019. Harmful Algal Bloom Impacts. Internet address: https://www.cencoos.org/learn/blooms/habs/impacts. (January 2019). City of Newport Beach. 2019. Fire Department/Marine Operations Division Beach Monthly Statistics. Unpublished data. (November 2019). Grant, S.B., B.F. Sanders, A.B. Boehm, J.A. Redman, J.H. Kim, R.D. Mrse, A.K. Chu, M. Gouldin, C.D. McGee, N.A. Gardiner, B.H. Jones, J. Svejkovsky, G.V. Leipzig, and A. Brown. 2001. Generation of enterococci bacteria in a coastal saltwater marsh and its impacts on surf zone water quality. Environ. Sci. Technol. 35:2407-2416. Heal the Bay. 2019. 2018-19 Beach Report Card. Internet address: https://healthebay.org/wp-content/ uploads/2019/06/BRC_2019_FINAL2.pdf. (December 2019). Hood, D. 1993. Ecosystem relationships. In: Ecology of the Southern California Bight: A Synthesis and Interpretation (M.D. Dailey, D.J. Reish, and J.W. Anderson - Eds.). University of California Press, Berkeley, CA. p. 782-835. Kildow, J.T. and C.S. Colgan. 2005. California's Ocean Economy. Publications. 8. Internet address: https:// cbe.miis.edu/noep_put)ijcations/t5. (December 19, 2018). Leeworthy, V.R. and P.C. Wiley. 2007. Economic Value and Impact of Water Quality Change for Long Beach in Southern California. National Oceanic and Atmospheric Administration Report, Silver Spring, MD. Leggett, C., N. Scherer, M. Curry, R. Bailey, and T. Haab. 2014. Assessing the Economic Benefits of Reductions in Marine Debris: A Pilot Study of Beach Recreation in Orange County, California. Final, Marine Debris Division, National Oceanic and Atmospheric Administration, Cambridge: Industrial Economics Incorporated. Internet address: https://marinedebris.noaa.gov/report/economic-study- shows-marine-debris-costs-california-residents-millions-dollars. (December 17, 2018). Lewis, R.D. and K.K. McKee. 1989. A Guide to the Artificial Reefs of Southern California. California Department of Fish and Game, Sacramento, CA. NCEI (NOAA National Centers for Environmental Information). 2019. Daily Global Historical Climatology Network, Newport Harbor, California (Station USC00046175). Internet address: https://www.ncd(, noaa.yuviuuu-web/datasets/GHCND/stations/GHCND:USC00046175/detail. (October 2019). NOAA (National Oceanic and Atmospheric Administration). 2015. The National Significance of California's Ocean Economy. Final Report Prepared for the NOAA Office for Coastal Management. Internet address: https://coast.noaa.gov/data/digitalcoast/pdf/california-ocean-economy.pdf (November 30, 2016). OCSD (Orange County Sanitation District). 1997. Annual Report, July 1995-June 1996. Marine Monitoring. Fountain Valley, CA. OCSD. 1998.Annual Report, July 1996-June 1997. Marine Monitoring. Fountain Valley, CA. OCSD. 2000.Annual Report, July 1998-June 1999. Marine Monitoring. Fountain Valley, CA. OCSD. 2001.Annual Report, July 1999-June 2000. Marine Monitoring. Fountain Valley, CA. 1-9 The Ocean Monitoring Program OCSD. 2004. OCSD Annual Report 2003: Ocean Monitoring Program Science Report (July 1985-June 2003). Marine Monitoring. Fountain Valley, CA. OCSD. 2011.Annual Report, July 2009-June 2010. Marine Monitoring. Fountain Valley, CA. OCSD. 2019. 2018-19 Annual Report. Resource Protection Division, Pretreatment Program. Fountain Valley, CA. Reifel, K.M., S.C. Johnson, P.M. DiGiacomo, M.J. Mengel, N.P. Nezlin, J.A. Warrick, and B.H. Jones. 2009. Impacts of stormwater runoff in the Southern California Bight - Relationships among plume constituents. Cont. Shelf Res. 29:1821-1835. SAIC (Science Applications International Corporation). 2001. Strategic Processes Study#1: Plume Tracking- Ocean Currents. Final Report Prepared for the Orange County Sanitation District. Fountain Valley, CA. SAIC. 2009. Orange County Sanitation District Ocean Current Studies: Analyses of Inter- and Intra-Annual Variability in Coastal Currents. Final Report Prepared for the Orange County Sanitation District. Fountain Valley, CA. SAIC. 2011. Statistical Analysis of Multi-Year Currents at Inshore Locations in San Pedro Bay. Final Report Prepared for the Orange County Sanitation District. Fountain Valley, CA. SCCWRP (Southern California Coastal Water Research Project). 1992. Southern California Coastal Water Research Project Biennial Report 1990-91 and 1991-92 (J.N. Cross and C. Francisco - Eds.). Long Beach, CA. Schafer, H.A. and R.W. Gossett. 1988. Characteristics of Stormwater Runoff from the Los Angeles and Ventura Basins. Technical Report Number 221. Southern California Coastal Water Research Project, Long Beach, CA. Schiff, K.C., M.J.Allen, E.Y. Zeng, and S.M. Bay. 2000. Southern California. Mar. Pollut. Bull. 41:76-93. Schiff, K. and L. Tiefenthaler. 2001. Anthropogenic versus natural mass emissions from an urban watershed. In: Southern California Coastal Water Research Project Annual Report, 1999-2000 (S.B. Weisberg and D. Elmore - Eds.). Southern California Coastal Water Research Project, Westminster, CA. p. 63-70. Tiefenthaler, L.L., K.S. Schiff, and M.K. Leecaster. 2005. Temporal variability in patterns of stormwater concentrations in urban runoff. Proceedings of the Water Environment Federation. 2005. 10.2175/193864705783966837. Turbow, D.T. and L.S. Jiang. 2004. Impacts of beach closure events on perception of swimming related health risks in Orange County, California. Mar. Pollut. Bull. 48:312-316. UCSC (University of California, Santa Cruz): Biological and Satellite Oceanography Laboratory. 2018. A Primer on California Marine Harmful Algal Blooms. Internet address: ittp://oceandatacenter.ucsc.edu/ home/outreach/HABwestcoast20l8.pcI . (January 2019). USGS (United States Geological Survey). 2019. Santa Ana River: USGS, 5th Street Station, Santa Ana. Internet address: nttp://waterdata.usgs.gov/usa/nwis/uv?site_no=l10780C . (October 2019). Warrick, J.A. and J.D. Millikan. 2003. Hyperpycnal sediment discharge from semiarid southern California rivers: Implications for coastal sediment budgets. Geology 31:781-784. Warrick, J.A., P.M. DiGiacomo, S.B. Weisberg, N.P. Nezlin, M. Mengel, B.H. Jones, J.C. Ohlmann, L. Washburn, E.J. Terrill, and K.L. Farnsworth. 2007. River plume patterns and dynamics within the Southern California Bight. Cont. Shelf Res. 27:2427-2448. WHOI (Woods Hole Oceanographic Institute). 2003. An Inventory of California Coastal Economic Sectors. Internet address: http://www.whoi.edu/mpcweb/research/NOPP/California%20region%20 progress%20report%20Jan03.pdf. (November 30, 2016). 1-10 CHAPTER 2 Compliance Determinations INTRODUCTION This chapter provides compliance results for the 2018-19 monitoring year for the Orange County Sanitation District's (OCSD) Ocean Monitoring Program (OMP). The program includes sample collection, analysis, and data interpretation to evaluate potential impacts of wastewater discharge on the following receiving water characteristics: • Bacterial • Physical • Chemical • Biological • Radioactivity Each of these characteristics have specific criteria (Table 2-1) for which permit compliance must be determined each monitoring year based on the Federal Clean Water Act, the California Ocean Plan (COP), and the Regional Water Quality Control Board Basin Plan. The 2018-19 Core OMP sampling locations included 28 offshore water quality stations, 29 benthic stations to assess sediment chemistry and bottom-dwelling communities, 6 trawl stations to evaluate demersal fish and macroinvertebrate communities, and 2 rig-fishing zones for assessing human health risk from the consumption of sport fishes (Figures 2-1, 2-2, and 2-3). Monitoring frequencies varied by component and ranged from 2-5 days per week for nearshore (also called surfzone) water quality to annual assessments of fish health and tissue analyses (see Appendix A). WATER QUALITY Offshore bacteria For all 3 fecal indicator bacteria (FIB), over 98% of the samples were below their 30-day geomean values (Table B-1). Overall, less than 1% of the samples exceeded single sample criteria with the highest density observed for any single sample at any single depth for total coliforms, fecal coliforms, and enterococci was 4,611, 583, and 1,467 MPN/100 mL, respectively. With most (61-89%) samples being below detection, the majority of the depth-averaged values used for water contact compliance were below detection (Tables B-2, B-3, and B-4). Compliance for all 3 FIB was achieved 100% for both state and federal criteria, indicating no impact of bacteria to offshore receiving waters. Floating Particulates and Oil and Grease There were no observations of oils and grease or floating particles of sewage origin at any inshore (Zone A) or offshore (Zone B) station groups in 2018-19 (Tables B-5 and B-6). Therefore, compliance was achieved. 2-1 Compliance Determinations Table 2-1 List of compliance criteria from OCSD's NPDES permit (Order No. R8-2012-0035, Permit No. CA0110604) and compliance status for each criterion in 2018-19. N/A= Not Applicable. Criteria Criteria Met Bacterial Characteristics V.A.1.a.For the CA Ocean Plan Water-Contact Standards,total coliform density shall not exceed a 30-day Geometric Mean of 1,000 Yes per 100 mL nor a single sample maximum of 10,000 per 100 mL.The total coliform density shall not exceed 1,000 per 100 mL when the single sample maximum fecal coliform/total coliform ratio exceeds 0.1. V.A.1.a.For the CA Ocean Plan Water-Contact Standards,fecal coliform density shall not exceed a 30-day Geometric Mean of 200 Yes per 100 mL nor a single sample maximum of 400 per 100 mL. V.A.1.a.For the CA Ocean Plan Water-Contact Standards,enterococci density shall not exceed a 30-day Geometric Mean of 35 per Yes 100 mL nor a single sample maximum of 104 per 100 mL. V.A.1.b. For the USEPA Primary Recreation Criteria in Federal Waters, enterococci density shall not exceed a 30 day Geometric Yes Mean(per 100 mL)of 35 nor a single sample maximum(per 100 mL)of 104 for designated bathing beach,158 for moderate use,276 for light use,and 501 for infrequent use. V.A.1.c. For the CA Ocean Plan Shellfish Harvesting Standards,the median total coliform density shall not exceed 70 per 100 mL, N/A and not more than 10 percent of the samples shall exceed 230 per 100 mL. Physical Characteristics V.A.2.a.Floating particulates and grease and oil shall not be visible. Yes V.A.2.b.The discharge of waste shall not cause aesthetically undesirable discoloration of the ocean surface. Yes V.A.2.c. Natural light shall not be significantly reduced at any point outside the initial dilution zone as a result of the discharge of Yes waste. V.A.2.d.The rate of deposition of inert solids and the characteristics of inert solids in ocean sediments shall not be changed such that Yes benthic communities are degraded. Chemical Characteristics V.A.3.a. The dissolved oxygen concentration shall not at any time be depressed more than 10 percent from that which occurs Yes naturally,as the result of the discharge of oxygen demanding waste materials. V.A.3.b.The pH shall not be changed at any time more than 0.2 units from that which occurs naturally. Yes V.A.3.c.The dissolved sulfide concentration of waters in and near sediments shall not be significantly increased above that present Yes under natural conditions. V.A.3.d.The concentration of substances,set forth in Chapter ll,Table 1 (formerly Table B)of the Ocean Plan,in marine sediments Yes shall not be increased to levels which would degrade indigenous biota. V.A.3.e.The concentration of organic materials in marine sediments shall not be increased to levels which would degrade marine life. Yes V.A.3.f.Nutrient materials shall not cause objectionable aquatic growths or degrade indigenous biota. Yes V.A.3.g.The concentrations of substances,set forth in Chapter ll,Table 1 (formerly Table B)of the Ocean Plan,shall not be exceeded Yes in the area within the waste field where initial dilution is completed. Biological Characteristics V.AA.a.Marine communities,including vertebrate,invertebrate,and plant species,shall not be degraded. Yes V.A.4.b. The natural taste, odor, and color of fish, shellfish, or other marine resources used for human consumption shall not be Yes altered. V.AA.c.The concentration of organic materials in fish, shellfish, or other marine resources used for human consumption shall not Yes bioaccumulate to levels that are harmful to human health. V.A.5. Discharge of radioactive waste shall not degrade marine life. Yes Ocean Discoloration and Transparency The water clarity standards were met 99.2% and 97.8% of the time for Zone A and B station groups, respectively, with an overall compliance rate of 98.5% (Table 2-2). This is above the 20-year average of 95% (Figure 2-4). All light transmissivity values (Table B-7) were within natural ranges of variability to which marine organisms are exposed (OCSD 1996a). Hence, there were no impacts from the wastewater discharge relative to ocean discoloration at any offshore station. 2-2 Compliance Determinations 10m 2ft. J Reclamation �P Plant 1 Huntington Beach 30m Treatment 24030 Plant 2 23510 Newport 2404U Beach 40m 2303* 23520 24050 22230 2304* 23530 2203* 24060 22240, 50m 23050 2183S 23540 22040 60m 22250 21030 2306* 2184S SOm 22 100m 22260 2104�•_ 2185* 22060 21050 200m � 2186* 2106* 300m N CTD profiling only 0 0.75 1.5 3 Miles • CTD profiling+ammonium samples • CTD profiling+ammonium and bacteria samples 0 1.25 2.5 5 Kilometers —Ocean Outfalls OCSD February 2020 Esri,Garmin.GEBCO,NOAA NGDC,and other contributors Figure 2-1 Offshore water quality monitoring stations for 2018-19. Dissolved Oxygen (DO) In 2018-19, compliance was met 97.3% for Zone A and 92.4% for Zone B with a combined compliance of 94.9% (Table 2-2), slightly below the 20-year average of 96% (Figure 2-4). The DO values (Table B-7) were well within the range of long-term monitoring results (OCSD 1996b, 2004). Thus, it was determined that there were no environmentally significant effects to DO from the wastewater discharge. Acidity (pH) Compliance was nearly 100% for Zone A and 97% for Zone B; the combined overall compliance was 98.3% which was above the 20-year average of 95% (Table 2-2; Figure 2-4). There were no environmentally significant effects to pH from the wastewater discharge as the measured values (Table B-7) were within the range to which marine organisms are naturally exposed. Nutrients (Ammonium) For the 2018-19 program year, nearly 80% of the samples were below the method detection limit (Table B-8). Detectable ammonium concentrations, including estimated values, ranged from 0.014 to 0.379 mg/L. Plume-related changes in ammonium were not considered environmentally significant as maximum values were 10 times less than the chronic (4 mg/L) and 15 times less than the acute (6 mg/L) toxicity standards of the COP (SWRCB 2012). In addition, there were no detectable plankton-associated impacts (i.e., excessive plankton blooms caused by the discharge). 2-3 Compliance Determinations 68 0 69 60m ° 0 70 72 84 0 71 ° 0 73 0 74 0 70m 0 ° 75 860 0 850 0 °ZB o 4 Treatment 0 076 Plant 2 3 79° 87° p2 800 078 77 810 82' Esri,Garmin,GEBCO,NOAA NGDC,and other contributors 78"OUtfall CON ° 60m C /120"Outfall 0 loom I I o ° 0 I ° o 0 0 0 I °0° 0 o I 0 ° o ° ° ° °0 0 0 0 I I I 300m - _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ _ 0 0.42 0.83 1.67 2.5 Miles 0 1 2 3 4 Kilamelers o Semi-annual Benthic Station(n=29) OCSD March 2020 Esri,Garmin,GEBCO,NOAA NGDC,and other contributors Figure 2-2 Benthic (sediment geochemistry and infauna) monitoring stations for 2018-19. COP Water Quality Objectives OCSD's NPDES permit contains 8 constituents from Table 1 (formerly Table B) of the COP that have effluent limitations (see Table 9 of the permit). During the period from July 2018 through June 2019, none of these constituents exceeded their respective effluent limitations, so receiving water compliance was met. Radioactivity Pursuant to OCSD's NPDES Permit, OCSD measures the influent and the effluent for radioactivity but not the receiving waters. The results of the influent and the effluent analyses during 2018-19 indicated that both state and federal standards were consistently met and are published in OCSD's Discharge Monitoring Reports. As fish and invertebrate communities are diverse and healthy, compliance was met. Overall Results Overall, results from OCSD's 2018-19 water quality monitoring program detected minor changes in measured water quality parameters related to the discharge of wastewater to the coastal ocean. This is consistent with previously reported results (e.g., OCSD 2017). Plume-related changes in DO, pH, and light transmissivity were measurable beyond the initial mixing zone during some surveys. This usually extended only into the nearfield stations, typically <2 km away from the 2-4 Compliance Determinations Reclamation Plant 1 Treatment Photo78"Outfall ♦ T11 ."♦ O ♦� i n3 T17 som 4♦ �� • T12 ♦ . O •♦ \(♦♦ 0 1 loom ♦ T23 • `�`♦ T22 ,. ' 120"Outfall 300m 0 1 z a woes • Semi-annual Trawl Station m=6) Rig-fishing Boundary m=2) 0 1.57 3.15 6.3 Klbmeters OCSD March 2020 Esri,Garmin,GEBCO,NOAA NGDC,and other contributors Figure 2-3 Trawl monitoring stations, as well as rig-fishing locations, for 2018-19. outfall, consistent with past findings. None of these changes were determined to be environmentally significant since they fell within natural ranges to which marine organisms are exposed (OCSD 1996a, 2004; Wilber and Clarke 2001, Chavez et al. 2002, Jarvis et al. 2004, Allen et al. 2005, Hsieh et al. 2005). Overall, the public health risks and measured environmental effects to the receiving water continue to be small. All values were within the ranges of natural variability for the monitoring area and reflected seasonal and yearly changes of large-scale regional influences. The limited observable plume effects occurred primarily at depth, even during the winter when stratification was weakest. In summary, OMP staff concluded that the discharge in 2018-19 did not demonstrably affect the receiving water environment and that beneficial uses were protected and maintained. SEDIMENT GEOCHEMISTRY The physical properties and chemical concentrations of sediment samples collected in the summer and winter surveys were similar between the within-ZID and non-ZID station groups (Tables 2-3, 2-4, 2-5, and 2-6). Chemical contaminant concentrations of the sediment samples were also well below applicable Effects Range-Median (ERM) guidelines of biological concern (Long et al. 1995) and were comparable to regional values. Furthermore, there was no measurable sediment toxicity at any of the 9 stations monitored in the winter survey (Table 2-7). These results indicate that compliance was met. 2-5 Compliance Determinations Table 2-2 Summary of offshore water quality compliance testing results for dissolved oxygen, pH, and light transmissivity for 2018-19. Number of Out-of-Range Occurrences Out-of-Compliance Parameter Observations Number Percent Number Percent Zone A Stations(Inshore Station Group) Dissolved Oxygen 523 56 10.7% 14 2.7% pH 523 39 7.5% 1 0.2% Light Transmissivity 523 258 49.3% 4 0.8% Zone 8 Stations(Offshore Station Group) Dissolved Oxygen 503 52 10.3% 38 7.6% pH 503 16 3.2% 16 3.2% Light Transmissivity 503 94 18.7% 11 2 2% Zone A and Zone 8 Stations Combined Dissolved Oxygen 1026 108 10.5% 52 5.1% pH 1026 55 5.4% 17 1.7% Light Transmissivity 1026 352 34.3% 15 1.5% ■Dissolved Oxygen ■pH ■Light Transmissivity 100 90 y 80 U C to .Q E O U 0 70 60 50 O N M LO W r.- W O) O N M VLOco n W O O O O O O O O O O O O O N M V 0 W r- W O _O _ N_ m O O O O O O O O O O O O O O O O O O O O O O O O O O O O O O � N N N N N N N N N N N N N N N N N N N Program Year(July to June) Figure 2-4 Summary of mean percent compliance for dissolved oxygen (DO), pH, and light transmissivity for all compliance stations compared to reference stations, 1999-2019. 2-6 Compliance Determinations Table 2-3 Physical properties, as well as biogeochemical and contaminant concentrations, of sediment samples collected at each semi-annual station in Summer 2018 compared to Effects Range-Median (ERM) and regional values. ND = Not Detected, N/A = Not Applicable. Nominal Median Fines TOC Sulfides Total P Total N EPAH EDDT EPest EPCB Station Depth Phi (%) N (mg/kg) (mg/kg) (mg/kg) (mg/kg) (mg/kg) (mg/kg) (mg/kg) (m) (41) Middle Shelf Zone 2,Non-ZID(51-90 m) 1 56 3.15 7.1 0.38 ND 1000 70 59.9 1.42 ND 0.51 3 60 3.06 9.8 0.42 1.91 1000 130 43.9 1.53 ND 1.56 5 59 3.34 10.0 0.42 1.61 1000 100 40.5 1.55 ND ND 9 59 2.90 7.2 0.36 2.54 860 390 89.2 1.24 ND ND 12 58 2.75 6.4 0.37 2.33 750 420 45.2 1.18 ND ND 68 52 3.31 11.0 0.42 ND 950 420 82.1 2.94 ND ND 69 52 3.20 9.1 0.38 1.71 1000 410 69.0 1.41 ND 4.31 70 52 3.22 15.4 0.41 ND 940 460 47.3 1.54 ND ND 71 52 3.06 9.1 0.34 1.28 860 430 47.2 1.23 ND ND 72 55 3.21 8.6 0.39 1.61 980 420 87.1 1.52 ND 29.89 73 55 3.13 10.1 0.50 2.43 1100 390 89.6 1.87 ND 12.49 74 57 3.06 10.4 0.39 2.72 980 480 49.7 1.18 ND 15.50 75 60 3.00 6.4 0.34 1.75 950 410 72.9 1.23 ND 11.99 77 60 3.01 7.5 0.38 2.38 1000 440 110.5 1.29 ND ND 78 63 3.03 8.0 0.37 2.41 950 380 61.3 1.23 ND ND 79 65 3.16 10.8 0.38 3.53 960 370 62.8 1.13 1.00 0.24 80 65 3.29 14.1 0.39 2.02 940 350 22.6 1.19 ND ND 81 65 3.14 11.3 0.37 4.77 910 340 ND ND ND ND 82 65 2.76 6.3 0.34 1.45 820 70 29.6 ND ND ND 84 54 3.14 10.8 0.51 2.18 1100 430 137.1 0.86 ND 7.29 85 57 2.98 7.3 0.49 3.23 1300 130 200.5 1.69 ND 28.60 86 57 3.00 7.1 0.45 2.79 1400 69 527.2 0.88 ND 15.21 87 60 3.09 8.2 0.37 1.47 1100 380 63.8 ND ND ND C 56 3.04 8.3 0.37 2.56 990 330 37.3 ND ND ND CON 59 3.20 9.7 0.39 1.78 1000 370 28.2 1.10 ND ND Mean 3.09 9.2 0.40 2.29 994 328 87.7 1.17 0.04 5.10 Middle Shelf Zone 2, Within-ZID(51-90 m) 0 56 2.99 7.0 0.49 2.01 1400 110 249.5 1.59 ND 5.59 4 56 3.03 6.4 0.34 ND 950 90 21.5 1.13 ND ND 76 58 2.99 8.1 0.37 2.24 1100 360 38.4 1.13 ND 0.68 ZB 56 3.01 7.4 0.41 2.03 970 360 116.7 ND ND 2.08 Mean 3.00 7.2 0.40 2.09 1105 230 106.5 0.96 ND 2.09 Sediment quality guidelines ERM N/A N/A N/A N/A N/A N/A 44792.0 46.10 N/A 180.00 Regional summer values(area weighted mean) Bight'l3 Middle Shelf N/A 48.0 0.70 N/A N/A 690 55.0 18.00 N/A 2.70 2-7 Compliance Determinations Table 2-4 Metal concentrations (mg/kg) in sediment samples collected at each semi-annual station in Summer 2018 compared to Effects Range-Median (ERM) and regional values. N/A= Not Applicable. Nominal Station Depth Sb As Ba Be Cd Cr Cu Pb Hg Ni Se Ag Zn (m) Middle Shelf Zone 2,Non-ZID(51-90 m) 1 56 0.1 3.91 36.8 0.26 0.14 18.20 8.54 6.31 0.02 8.1 1.38 0.12 38.9 3 60 0.1 3.50 32.2 0.27 0.15 18.60 8.65 5.93 0.04 8.4 1.21 0.11 43.4 5 59 0.1 4.15 42.9 0.31 0.21 18.80 8.86 6.69 0.02 8.8 1.50 0.15 39.5 9 59 0.1 3.55 47.4 0.26 0.11 17.10 6.43 5.34 0.01 7.5 1.30 0.08 36.8 12 58 0.0 3.21 34.7 0.24 0.11 15.90 5.60 5.30 0.02 7.3 1.26 0.07 35.0 68 52 0.1 4.19 45.7 0.27 0.15 18.10 7.88 6.64 0.02 8.4 1.34 0.13 40.5 69 52 0.1 3.19 40.5 0.25 0.20 18.10 8.20 6.00 0.07 8.5 1.31 0.20 40.6 70 52 0.1 3.06 39.8 0.26 0.20 17.80 7.84 6.25 0.02 8.1 1.32 0.13 41.6 71 52 0.1 3.32 37.2 0.25 0.22 16.50 6.55 5.33 0.02 7.8 1.39 0.11 38.7 72 55 0.1 3.05 38.2 0.26 0.16 17.90 8.39 6.24 0.02 8.4 1.52 0.14 38.6 73 55 0.1 3.88 37.8 0.25 0.31 19.90 10.60 7.44 0.04 8.2 1.38 0.17 42.6 74 57 0.1 3.57 39.8 0.26 0.19 17.60 7.36 5.71 0.01 8.0 1.41 0.10 40.1 75 60 0.0 3.97 42.0 0.26 0.21 16.90 6.80 5.26 0.01 7.9 1.39 0.10 39.5 77 60 0.0 3.72 35.3 0.27 0.11 17.50 7.11 5.44 0.01 8.2 1.30 0.09 38.4 78 63 0.0 2.74 34.1 0.28 0.10 17.10 6.81 5.25 0.01 7.8 1.49 0.09 36.8 79 65 0.0 3.13 37.1 0.26 0.12 17.40 7.81 5.66 0.02 8.9 1.69 0.13 39.9 80 65 0.0 3.95 40.5 0.30 0.08 16.90 7.69 5.82 0.01 8.2 1.38 0.08 39.9 81 65 0.0 3.02 35.2 0.28 0.09 16.70 6.47 5.30 0.01 8.0 1.32 0.08 38.5 82 65 0.1 3.22 37.9 0.30 0.09 17.70 6.84 5.23 0.01 8.6 1.21 0.08 41.9 84 54 0.1 3.54 39.8 0.26 0.38 19.20 10.10 6.23 0.03 8.4 1.46 0.19 44.2 85 57 0.1 3.24 32.4 0.27 0.59 20.60 11.80 6.39 0.03 8.3 1.37 0.20 42.6 86 57 0.1 3.94 36.0 0.27 0.28 19.10 11.40 7.13 0.03 7.8 1.45 0.19 42.1 87 60 0.1 4.31 39.1 0.29 0.10 17.80 7.12 5.66 0.02 8.1 1.35 0.09 39.7 C 56 0.1 2.86 45.1 0.25 0.11 17.20 6.58 5.83 0.01 8.3 1.27 0.08 39.7 CON 59 0.1 3.07 49.3 0.25 0.10 17.90 6.61 6.20 0.02 8.5 1.39 0.08 39.0 Mean 0.1 3.49 39.1 0.27 0.18 17.86 7.92 5.94 0.02 8.2 1.38 0.12 39.9 Middle Shelf Zone 2,Within-ZID(51-90 m) 0 56 0.1 4.44 35.2 0.26 0.30 19.30 10.50 7.07 0.31 8.2 1.52 0.20 40.8 4 56 0.1 3.21 35.7 0.27 0.18 17.80 6.84 5.42 0.02 7.6 1.40 0.10 39.0 76 58 0.1 3.15 35.0 0.26 0.14 16.60 7.20 5.05 0.05 7.7 1.24 0.11 39.0 ZB 56 0.1 3.39 38.7 0.27 0.26 17.40 7.92 5.46 0.02 8.1 1.51 0.11 42.6 Mean 0.1 3.55 36.2 0.26 0.22 17.78 8.12 5.75 0.10 7.9 1.42 0.13 40.4 Sediment quality guidelines ERM N/A 70.00 N/A N/A 9.60 370.00 270.00 218.00 0.70 51.6 N/A 3.70 410.0 Regional summer values(area weighted mean) Bight'13 Middle Shelf 0.9 2.70 130.0 0.21 0.68 30.00 7.90 7.00 0.05 15.0 0.10 0.29 48.0 2-8 Compliance Determinations Table 2-5 Physical properties, as well as biogeochemical and contaminant concentrations, of sediment samples collected at each semi-annual station in Winter 2019 compared to Effects Range-Median (ERM) and regional values. ND = Not Detected, N/A = Not Applicable. Nominal Median Fines TOC Sulfides Total P Total N EPAH EDDT EPest EPCB Station Depth Phi (%) N (mg/kg) (mg/kg) (mg/kg) (mg/kg) (mg/kg) (mg/kg) (mg/kg) (m) (4)) Middle Shelf Zone 2,Non-ZID(51-90 m) 1 56 3.36 15.5 0.41 1.16 1000 480 27.0 1.44 ND 0.73 3 60 3.15 10.9 0.44 2.68 1000 430 26.3 1.56 ND 0.67 5 59 3.50 12.9 0.41 2.36 840 450 2.7 1.81 ND ND 9 59 3.12 11.8 0.42 2.80 820 370 21.8 1.10 ND ND 12 58 2.98 10.2 0.35 2.36 790 420 55.0 1.25 ND ND 68 52 3.38 14.0 0.48 2.41 920 470 40.5 1.90 ND ND 69 52 3.34 13.0 0.39 ND 920 510 40.3 1.64 ND ND 70 52 3.32 16.6 0.48 1.60 940 500 29.5 1.87 ND ND 71 52 3.18 12.3 0.48 2.66 860 480 26.5 1.59 ND ND 72 55 3.33 13.6 0.44 1.59 890 440 100.7 1.79 ND ND 73 55 3.30 16.9 0.46 5.45 1400 450 260.2 1.81 ND 7.33 74 57 3.28 16.1 0.45 2.21 820 460 12.1 1.42 ND 0.64 75 60 3.03 7.9 0.37 2.41 850 410 60.0 0.98 ND ND 77 60 3.11 9.9 0.46 3.42 850 410 18.6 1.06 ND ND 78 63 3.02 5.6 0.39 3.49 830 340 16.0 0.98 ND ND 79 65 3.25 8.5 0.42 1.83 900 440 174.4 1.21 ND ND 80 65 3.41 15.0 0.43 2.73 880 440 17.9 1.16 ND ND 81 65 3.14 10.4 0.37 1.56 850 440 14.6 1.03 ND ND 82 65 3.04 9.6 0.39 2.80 870 360 13.1 0.91 ND ND 84 54 3.26 15.0 0.46 2.85 1000 660 51.3 1.41 ND 0.59 85 57 3.06 9.0 0.48 3.45 1100 460 74.7 1.55 ND 0.64 86 57 3.20 12.7 0.42 4.20 980 470 36.5 1.26 ND ND 87 60 3.15 12.4 0.49 2.96 890 390 407.1 1.31 ND ND C 56 3.34 13.9 0.43 3.89 900 510 40.0 1.62 ND ND CON 59 3.22 11.4 0.39 2.53 980 460 20.5 1.55 ND ND Mean 3.22 12.2 0.43 2.72 923 450 63.5 1.41 ND 0.42 Middle Shelf Zone 2, Within-ZID(51-90 m) 0 56 3.17 13.4 0.48 3.11 1200 510 62.2 1.79 1.42 7.05 4 56 3.19 11.8 0.37 2.76 830 470 6.5 1.14 ND ND 76 58 3.17 10.4 0.35 3.21 960 400 65.6 1.14 ND ND ZB 56 3.12 11.0 0.45 3.58 910 580 58.1 0.77 ND ND Mean 3.16 11.6 0.41 3.16 975 490 48.1 1.21 0.36 1.76 Sediment quality guidelines ERM N/A N/A N/A N/A N/A N/A 44792.0 46.10 N/A 180.00 Regional summer values(area weighted mean) Bight'l3 Middle Shelf N/A 48.0 0.70 N/A N/A 690 55.0 18.00 N/A 2.70 2-9 Compliance Determinations Table 2-6 Metal concentrations (mg/kg) in sediment samples collected at each semi-annual station in Winter 2019 compared to Effects Range-Median (ERM) and regional values. ND =Not Detected, N/A= Not Applicable. Nominal Station Depth Sb As Ba Be Cd Cr Cu Pb Hg Ni Se Ag Zn (m) Middle Shelf Zone 2,Non-ZID(51-90 m) 1 56 0.1 3.23 36.2 0.26 0.15 18.10 8.71 6.68 0.02 8.3 2.34 0.14 40.3 3 60 0.1 4.16 39.3 0.28 0.15 18.90 9.40 6.12 0.01 8.6 2.35 0.16 43.2 5 59 0.1 3.40 46.2 0.28 0.16 19.80 9.06 6.78 0.02 9.5 2.40 0.15 44.5 9 59 0.1 2.89 32.5 0.27 0.09 17.60 6.51 5.35 0.01 8.1 2.51 0.07 37.4 12 58 0.1 3.94 34.2 0.24 0.09 16.80 6.14 7.41 0.01 7.9 2.35 0.06 35.5 68 52 0.1 4.09 42.7 0.27 0.14 19.00 8.76 7.02 0.03 9.1 2.82 0.12 42.1 69 52 0.1 3.90 41.0 0.26 0.15 19.00 8.55 6.67 0.01 9.3 2.83 0.12 40.3 70 52 0.1 3.40 38.4 0.26 0.15 18.30 8.06 6.32 0.02 8.7 2.81 0.10 40.1 71 52 0.1 4.47 38.0 0.27 0.15 18.70 8.34 6.89 0.01 8.7 2.21 0.13 41.2 72 55 0.1 3.11 39.7 0.26 0.14 19.10 8.75 6.46 0.02 8.8 2.74 0.13 41.1 73 55 0.1 3.46 36.6 0.26 0.40 20.40 13.20 7.87 0.03 8.1 2.68 0.40 43.5 74 57 0.1 3.90 38.3 0.27 0.16 18.30 8.27 5.94 0.01 8.9 2.78 0.10 41.8 75 60 0.1 3.48 35.1 0.25 0.19 16.50 6.83 4.98 0.01 8.0 2.65 0.08 39.8 77 60 0.1 3.36 36.6 0.28 0.11 18.20 7.59 6.59 0.02 8.5 2.36 0.07 41.4 78 63 0.1 3.27 33.5 0.26 0.09 17.50 7.64 5.37 0.01 8.3 2.59 0.08 37.4 79 65 0.1 2.79 36.4 0.26 0.11 18.10 8.10 5.72 0.01 8.4 2.35 0.12 42.0 80 65 0.1 3.58 42.1 0.33 0.08 19.20 8.41 5.78 0.01 10.0 2.82 0.07 46.1 81 65 0.1 3.38 35.2 0.28 0.08 17.20 6.83 5.48 0.01 8.5 2.96 0.06 39.1 82 65 0.1 3.21 35.9 0.29 0.08 17.70 7.55 5.19 0.01 8.6 2.58 0.07 39.6 84 54 0.1 3.37 37.2 0.25 0.32 18.80 12.90 6.70 0.02 8.6 2.99 0.13 42.1 85 57 0.1 3.07 34.6 0.25 0.38 19.80 11.00 6.50 0.02 8.2 2.43 0.26 42.5 86 57 0.1 3.11 36.4 0.26 0.28 19.00 12.00 6.25 0.02 8.5 2.57 0.22 40.6 87 60 0.1 4.42 35.2 0.28 0.12 18.90 8.62 6.01 0.01 8.8 2.60 0.09 42.4 C 56 ND ND ND ND ND ND ND ND ND ND ND ND ND CON 59 0.1 2.97 52.6 0.25 0.09 19.10 7.02 6.22 0.01 9.3 2.72 0.06 39.5 Mean 0.1 3.50 38.1 0.27 0.16 18.50 8.68 6.26 0.02 8.7 2.60 0.12 41.0 Middle Shelf Zone 2,Within-ZID(51-90 m) 0 56 0.1 4.90 35.9 0.26 0.29 20.60 12.20 7.90 0.03 9.2 2.16 0.16 44.8 4 56 0.1 3.90 33.4 0.27 0.10 18.50 6.92 5.89 0.01 8.4 2.36 0.08 39.2 76 58 0.1 2.88 35.1 0.26 0.10 17.30 7.17 5.10 0.01 8.1 2.12 0.08 40.1 ZB 56 0.1 3.80 35.7 0.25 0.19 17.60 7.71 5.65 0.02 8.4 2.45 0.10 40.2 Mean 0.1 3.87 35.0 0.26 0.17 18.50 8.50 6.14 0.02 8.5 2.27 0.10 41.1 Sediment quality guidelines ERM N/A 70.00 N/A N/A 9.60 370.00 270.00 218.00 0.70 51.6 N/A 3.70 410.0 Regional summer values(area weighted mean) Bight'l3 Middle Shelf 0.9 2.70 130.0 0.21 0.68 30.00 7.90 7.00 0.05 15.0 0.10 0.29 48.0 Table 2-7 Whole-sediment Eohaustorius estuarius (amphipod) toxicity test results for 2018-19. The home sediment represents the control; N/A= Not Applicable. Station %Survival %of home p-value Assessment home 96 N/A N/A N/A 0 99 103 1.00 Nontoxic 1 95 99 0.89 Nontoxic 4 89 93 0.17 Nontoxic 72 98 102 0.99 Nontoxic 73 97 101 0.97 Nontoxic 76 96 100 0.91 Nontoxic 77 97 101 0.96 Nontoxic CON 98 102 0.99 Nontoxic ZB 92 96 0.96 Nontoxic ZB Dup 91 95 0.32 Nontoxic BIOLOGICAL COMMUNITIES Infaunal Communities A total of 566 invertebrate taxa comprising 22,056 individuals were collected in the 2018-19 monitoring year. The Annelida (segmented worms) was the dominant taxonomic group (Table B-9). Mean community measure values were comparable between within- and non-ZID stations, and all station values were within regional and OCSD historical ranges in both surveys (Tables 2-8 and 2-9). The infaunal community at all within-ZID and non-ZID stations in both surveys 2-10 Compliance Determinations can be classified as reference condition based on their low (<25) Benthic Response Index (BRI) values and/or high (>60) Infaunal Trophic Index (ITI) values. The community composition at most within-ZID stations was similar to that of non-ZID stations based on multivariate analyses of the infaunal species and abundances (Figure 2-5). These multiple lines of evidence suggest that the outfall discharge had an overall negligible effect on the benthic community structure within the monitoring area. We conclude, therefore, that the biota was not degraded by the outfall discharge, and as such, compliance was met. Epibenthic Macroinvertebrate Communities A total of 35 epibenthic macroinvertebrate (EMI) species, comprising 13,614 individuals and a total weight of 35.5 kg, was collected from 12 trawls conducted along the Middle Shelf Zone 2 stratum during the 2018-19 monitoring period (Tables B-10 and B-11). As with the previous monitoring period, Ophiura luetkenii (brittle star) was the most dominant species in terms of abundance (n=8,045; 59% of total), while Sicyonia penicillata (shrimp) was the dominant species in respect to biomass (12.0 kg; 34% of total). The EMI community composition was similar at the outfall and non-outfall stations in both Summer and Winter surveys based on the results of the multivariate analyses (cluster and non-metric multidimensional scaling (nMDS) analyses) (Figure 2-6). Furthermore, the community measure values at the outfall stations are within regional and OCSD historical ranges (Table 2-10). These results suggest that the outfall discharge had an overall negligible effect on the EMI community structure within the monitoring area. We conclude that the EMI communities within the monitoring area were not degraded by the outfall discharge, and consequently, compliance was met. Fish Communities A total of 37 fish taxa, comprising 8,050 individuals and a total weight of 185.2 kg, were collected from the monitoring area during the 2018-19 trawling effort (Tables B-12 and B-13). The mean species richness, abundance, biomass, Shannon-Wiener Diversity (W), and Swartz's 75% Dominance Index (SDI) values of demersal fishes were comparable between outfall and non- outfall stations in both surveys, with values falling within regional and/or OCSD historical ranges (Table 2-11). More importantly, the fish communities at outfall and non-outfall stations were classified as reference condition based on their low (<45) mean Fish Response Index (FRI) values in both surveys. Multivariate analyses (cluster and nMDS) of the demersal fish species and abundance data further demonstrated that the fish communities were similar between the outfall and non-outfall stations (Figure 2-7). These results indicate that the outfall discharge had no adverse effect on the demersal fish community structure within the monitoring area. We conclude that the demersal fish communities within the monitoring area were not degraded by the outfall discharge, and thus, compliance was met. FISH BIOACCUMULATION AND HEALTH Demersal and Sport Fish Tissue Chemistry Concentrations of trace metals and chlorinated pesticides in muscle and/or liver tissues of flatfishes and rockfishes were similar between outfall and non-outfall locations (Tables 2-12 and 2-13). Furthermore, mean concentrations of these contaminants in muscle tissue of rockfishes were below federal and state human consumption guidelines. These results suggest that demersal fishes residing near the outfall are not more prone to bioaccumulation of contaminants and demonstrate there is negligible human health risk from consuming demersal fishes captured in the monitoring areas. 2-11 Compliance Determinations Table 2-8 Community measure values for each semi-annual station sampled during the Summer 2018 infauna survey, including regional and historical values. NC = Not Calculated. Nominal Total Total Station Depth No.of Abundance H' SDI ITI BRI (m) Species Middle Shelf Zone 2,Non-ZID(51-90 m) 1 56 80 295 3.90 30 75 16 3 60 103 450 4.00 35 75 12 5 59 77 276 3.70 27 76 16 9 59 87 387 3.87 27 77 14 12 58 98 377 3.86 30 75 14 68 52 103 514 3.89 28 72 15 69 52 104 433 3.92 28 76 15 70 52 101 511 3.70 24 74 12 71 52 97 506 3.77 24 74 17 72 55 90 307 3.98 31 80 13 73 55 98 411 3.98 31 74 15 74 57 80 330 3.79 25 74 15 75 60 70 281 3.71 23 74 22 77 60 93 411 3.80 26 73 14 78 63 91 378 3.91 30 81 14 79 65 85 349 3.80 25 71 16 80 65 83 264 4.00 33 78 9 81 65 92 375 3.95 30 80 13 82 65 62 264 3.56 21 75 8 84 54 104 464 4.01 30 77 12 85 57 85 272 3.91 29 82 12 86 57 106 377 4.10 37 71 15 87 60 76 256 3.84 31 77 12 C 56 78 248 3.79 27 70 16 CON 59 102 391 3.80 30 71 13 Mean 90 365 3.86 28 75 14 Middle Shelf Zone 2, Within-ZID(51-90 m) 0 56 106 446 4.02 33 74 19 4 56 77 271 3.82 27 75 13 76 58 101 326 4.02 35 71 15 ZB 56 66 212 3.81 26 81 16 Mean 88 314 3.92 30 75 16 Regional summer values[mean(range)] Bight'13 Middle Shelf 90(45-171) 491 (142-2718) 3.60(2.10-4.10) NC NC 18(7-30) OCSD historical summer values(2008-2018 Fiscal Years)[mean(range)] Middle Shelf Zone 2,Non-ZID 94(20-142) 408(90-785) 3.68(2.27-4.43) 27(5-52) 77(40-94) 18(10-49) Middle Shelf Zone 2,Within-ZID 88(33-138) 482(212-1491) 3.39(0.36-4.10) 23(1-38) 60(1-91) 25(13-52) Fish Health The color and odor of demersal fishes appeared normal during the monitoring period. The absence of tumors, fin erosion, and skin lesions in demersal fishes showed that fishes in the monitoring area were healthy. External parasites and morphological abnormalities occurred in less than 1% of the fishes collected, which is comparable to southern California Bight background levels. These results indicate that the outfall is not an epicenter of disease. Liver Histopathology No histopathology analysis was conducted for the 2018-19 monitoring period (see Appendix A). CONCLUSIONS COP criteria for water quality were met, and state and federal bacterial standards were also met at offshore stations. Sediment quality was not affected based on the low concentration of chemical contaminants in the monitoring area and the absence of sediment toxicity in controlled laboratory tests. In addition, the animal communities were comparable between outfall and non-outfall areas, there was negligible disease symptoms in fish samples, and contaminant concentrations in fish tissue samples did not exceed federal and state fish consumption guidelines. These results suggest that the receiving environment was not degraded by OCSD's discharge of treated wastewater, and as such, all permit compliance criteria were met in 2018-19 and environmental and human health were protected. 2-12 Compliance Determinations Table 2-9 Community measure values for each semi-annual station sampled during the Winter 2019 infauna survey, including regional and historical values. NC = Not Calculated. Nominal Total Total Station Depth No.of Abundance H' SDI ITI BRI (m) Species Middle Shelf Zone 2,Non-ZID(51-90 m) 1 56 82 501 3.40 20 69 21 3 60 102 454 3.91 31 74 16 5 59 67 271 3.30 19 72 16 9 59 97 527 3.49 23 74 14 12 58 89 361 3.65 25 74 16 68 52 82 495 3.53 20 65 19 69 52 88 430 3.67 24 70 15 70 52 105 574 3.67 24 76 13 71 52 98 507 3.55 20 73 14 72 55 81 486 3.29 18 71 20 73 55 118 750 3.81 26 72 15 74 57 122 498 4.09 34 74 15 75 60 107 610 3.82 28 74 15 77 60 88 508 3.47 20 74 13 78 63 100 597 3.67 24 74 14 79 65 80 404 3.39 20 71 18 80 65 84 500 3.48 19 75 15 81 65 84 324 3.70 25 79 16 82 65 85 403 3.68 23 76 15 84 54 112 734 3.61 24 69 16 85 57 80 283 3.77 26 82 13 86 57 114 539 3.85 29 75 15 87 60 79 330 3.74 25 74 13 C 56 82 279 3.71 29 74 17 CON 59 47 208 3.26 16 75 17 Mean 91 463 3.62 24 73 16 Middle Shelf Zone 2, Within-ZID(51-90 m) 0 56 82 255 3.90 31 73 21 4 56 95 495 3.69 24 72 16 76 58 86 387 3.60 21 75 18 ZB 56 98 406 3.89 29 74 16 Mean 90 386 3.77 26 74 18 Regional summer values[mean(range)] Bight'13 Middle Shelf 90(45-171) 491 (142-2718) 3.60(2.10-4.10) NC NC 18(7-30) OCSD historical winter values(2008-2018 Fiscal Years)[mean(range)] Middle Shelf Zone 2,Non-ZID 85(45-142) 327(96-634) 3.74(2.87-4.32) 28(9-48) 78(47-95) 17(9-46) Middle Shelf Zone 2,Within-ZID 79(35-135) 364(88-1230) 3.46(0.89-4.68) 24(1-76) 62(3-89) 23(9-45) 2-13 Compliance Determinations 40 Zones Within-ZID --- — — ------------------ ------------------------------------------------------------------------------------ ----- ■Non-ZID I I r------- -� I ' I I r I I 60 I _ ___•f__•__ (n 80 100 0 Z r r d`W ,Z r 6 U OU Stations 2D Stress:0.23 Similarity 45 ■ sy Zones �' j ♦ `I ♦Within-ZID �� -. -- �`` ��—,i ■Non-ZID 74-S ZB-S `. 74-W \� f �� ♦ 84-S 70_S �`�` 7—21-W ( ■ 8'S ``�1Z9-W ♦ j 69-8 S ' w- 68 -5 79 W1-W �t Ck3N<�S I I 1 54 S■ 3- tt ■ I I i 81-92-� ♦/8- ■87 80-W ■ ■ ■ ■ \ ■ 1-W 12-W \ ■ \\ 80-S 8S82-S 12-S ■ t ■ 85-l1 ■ 09-S ■ ■ ■t `. ■ 5-W i i � C-S i CgWw ; ------------------------ Figure 2-5 Dendrogram (top panel) and non-metric multidimensional scaling (nMDS) plot (bottom panel) of the infauna collected at within- and non-ZID stations along the Middle Shelf Zone 2 stratum for the Summer 2018 (S) and Winter 2019 (W) benthic surveys. Stations connected by red dashed lines in the dendrogram are not significantly differentiated based on the SIMPROF test. The 5 main clusters formed at a 45% similarity on the dendrogram are superimposed on the nMDS plot. 2-14 Compliance Determinations 40- Sites Outfall ------------------------------------ --------------- CIJ Stations 2D Stress:0.09 Similarity Sites Outfall ---------------- Figure 2-6 Oendrognarn (top panel) and non-metric multidimensional scaling (nM[>G) plot (bottom panel) of the epibenthic rnocnninwartebna&an collected at outfo|| and non-outfo|| stations along the Middle Shelf Zone 2 ntnotunn for the Gurnnner 2018 /8\ and VVinter2O1S (VV) trovv| surveys. Stations connected by red dashed lines in the dendrogrom are not significantly differentiated boned on the 8|yNPRC)F test. The three main clusters formed at 50% similarity on the dendrogrom are superimposed on the nK8O8plot. 2-15 Compliance Determinations Table 2-10 Summary of epibenthic macroinvertebrate community measures for each semi- annual station sampled during the Summer 2018 and Winter 2019 trawl surveys, including regional and historical values. NC = Not Calculated. Nominal Total Total Biomass Quarter Station Depth No.of Abundance (kg) H' SDI (m) Species Middle Shelf Zone 2,Non-outfall(51-90 m) T23 58 9 708 1.37 0.45 1 T12 57 10 1155 1.98 0.66 1 T 1 7 60 6 188 0.60 0.90 2 Tit 60 17 1620 3.15 0.44 1 Summer Mean 11 918 1.77 0.61 1 Middle Shelf Zone 2,Outfall(51-90 m) T22 60 13 456 0.94 0.58 1 T1 55 12 208 0.99 1.56 3 Mean 13 332 0.97 1.07 2 Middle Shelf Zone 2,Non-outfall(51-90 m) T23 58 14 1392 1.20 0.67 1 T12 57 9 4284 2.83 0.36 1 T17 60 7 898 5.34 0.43 1 T11 60 17 1163 1.77 0.72 1 Winter Mean 12 1934 2.79 0.55 1 Middle Shelf Zone 2,Outfall(51-90 m) T22 60 13 372 0.47 1.62 3 T1 55 12 1170 2.49 1.58 3 Mean 13 771 1.48 1.60 3 Regional summer values[area-weighted mean(range)] Bight'13 Middle Shelf 12(3-23) 1093(19-17973) 5.00(0.31-36) 1.11 (0.09-2.49) NC OCSD historical values(2008-2018 FY)[mean(range)] Middle Shelf Zone 2,Non-outfall 11 (5-19) 365(12-2498) 1.57(0.04-11.16) 1.33(0.06-2.43) 3(1-9) Middle Shelf Zone 2,Outfall 12(7-18) 287(49-1436) 1.42(0.08-5.67) 1.44(0.22-2.15) 3(1-5) Table 2-11 Summary of demersal fish community measures for each semi-annual station sampled during the Summer 2018 and Winter 2019 trawl surveys, including regional and District historical values. NC = Not Calculated. Nominal Total No. Total Biomass Quarter Station Depth of Abundance (kg) H' SDI FRI (m) Species Middle Shelf Zone 2,Non-outfall(51-90 m) T23 58 15 395 23.89 1.55 2 20 T12 57 17 428 5.21 1.83 3 21 T17 60 14 262 4.09 2.20 5 22 T11 60 13 341 5.45 1.58 2 23 Summer Mean 15 357 9.66 1.79 3 22 Middle Shelf Zone 2,Outfall(51-90 m) T22 60 17 411 11.58 1.57 3 23 T1 55 13 506 6.10 1.58 3 16 Mean 15 459 8.84 1.58 3 19 Middle Shelf Zone 2,Non-outfall(51-90 m) T23 58 17 540 19.51 2.00 5 23 T12 57 19 485 20.92 2.06 4 27 T17 60 17 835 10.00 1.66 3 25 T11 60 20 2736 55.85 0.89 1 32 Winter Mean 18 1149 26.57 1.65 3 27 Middle Shelf Zone 2,Outfall(51-90 m) T22 60 16 561 7.99 1.81 4 22 T1 55 18 550 14.59 2.18 5 25 Mean 17 556 11.29 2.00 5 23 Regional summer values[area-weighted mean(range)] Bight'13 Middle Shelf 15(5-24) 506(12-2446) 12(0.70-64.20) 1.65(0.67-2.35) NC 28(17-61) OCSD historical values(2008-2018 Fiscal Years)[mean(range)] Middle Shelf Zone 2,Non-outfall 14(3-25) 580(45-12274) 12.90(1.25-135.64) 1.72(0.14-2.18) 3(1-6) 23(12-34) Middle Shelf Zone 2,Outfall 13(2-18) 415(110-3227) 16.97(2.47-78.72) 1.69(0.67-2.14) 3(1-6) 22(13-32) 2-16 Compliance Determinations 60 Sites Outfall ■ Non-outfall 70 . 80 - I U I I 90 100 N M M N N �_ N I� H H N H H N (— Stations 2D Stress:0.09 SiMilarit ------------------- -------- y --- T Sites 6l ■ ♦ Outfall `. ■ Non-outfall T22-W ` fi TW ♦ `� ■ T17-S T23-W ■ ` J� T23-S 1 i ■ i 1 T22-S 1 j T12-W ♦ ;I ■ I T1-W T11-S T1-S \� T11-W ♦ ■ ■ Figure 2-7 Dendrogram (top panel) and non-metric multidimensional scaling (nMDS) plot (bottom panel) of the demersal fishes collected at outfall and non-outfall stations along the Middle Shelf Zone 2 stratum for the Summer 2018 (S) and Winter 2019 (W) trawl surveys. Stations connected by red dashed lines in the dendrogram are not significantly differentiated based on the SIMPROF test. The single cluster formed at a 61% similarity on the dendrogram is superimposed on the nMDS plot. 2-17 Table 2-12 Means and ranges of tissue contaminant concentrations in selected flatfishes collected by trawling in July 2018 at Stations o T1 (Outfall) and T11 (Non-outfall), as well as historical values. ND = Not Detected. Standard Percen (mm) t Mercury EDDT EPCB EChlordane Dieldrin Species Tissue Station n Length Lipid (mg/kg) (jig/kg) (Ng/kg) (Ng/kg) (pgikg) n fD 2018-2019 values Non-outfall 10 121 0.31 0.02 9.21 0.14 ND ND Muscle (102-154) (0-1.07) (0.01-0.03) (0-19.07) (0-1.30) (All ND) (All ND) 1C 130 ND 0.03 1.72 1.62 ND ND Pleuronichthys verticalis Outfall 5 (111-163) (All ND) (0.01-0.06) (0-4.49) (1.30-2.20) (All ND) (All ND) (Hornyhead Turbot) Non-outfall 10 121 1.46 0.08 392.20 26.92 ND ND Liver (102-154) (0-8.74) (0.05-0.12) (8.39-1754.90) (0-72.80) (All ND) (Ail ND) ty Outfall 5 130 5.72 0.09 99.66 ND ND ND '= (111-163) (1.08-14.70) (0.01-0.16) (61.90-148) (All ND) (All ND) (All ND) 0 183 1.26 0.04 18.84 1.62 ND ND Non-outfall 10 to Muscle (156-218) (0.65-2.93) (0.02-0.07) (6.18-84.16) (0-10.50) (All ND) (All ND) 190 1.24 0.05 15.21 3.38 ND ND Parophrys vetulus Outfall 10 (152-268) (0-2.76) (0.02-0.10) (3.75-34.60) (1.10-8.11) (All ND) (All ND) (English Sole) Non-outfall 10 183 8.45 0.06 144.24 29.29 ND ND Liver (156-218) (3.17-13.40) (0.03-0.12) (42.60-292) (0-78.96) (All ND) (All ND) Outfall 10 190 12.57 0.06 159.49 16.34 ND ND (152-268) (4.03-25.30) (0.02-0.14) (70.70-449.60) (0-48.60) (All ND) (All ND) OCSD historical values(2008-2018 Fiscal Years) Non-outfall 64 152 0.17 0.06 10.49 2.43 0.06 ND Muscle (98-217) (0-0.68) (0.01-0.30) (0-38.75) (0-18.36) (0-1.45) (All ND) 159 0.14 0.08 6.91 1.47 0.01 0.20 N Pleuronichthysverticalis Outfall 91 (110-204) (0-0.77) (0.01-0.42) (0-54.50) (0-12.57) (0-0.71) (0-12.70) (Hornyhead Turbot) Non-outfall 64 157 6.05 0.21 540.82 44.79 ND ND 00 Liver (98-217) (0.42-30.40) (0.05-0.79) (0-2100) (0-432.59) (All ND) (All ND) Outfall 91 158 8.13 0.18 484.28 98.89 3.46 ND (110-204) (0-24.60) (0.02-0.59) (0-1822.70) (0-457.80) (0-81.70) (All ND) Non-outfall 91 183 0.83 0.06 73.80 8.21 ND 0.05 Muscle (124-268) (0-6.22) (0.02-0.12) (0-524.30) (0-61.20) (All ND) (0-4.45) 185 1.16 0.06 106.25 14.33 ND ND Parophrys vetulus Outfall 78 (136-290) (0-8.23) (0.01-0.11) (3.97-633.46) (0-130.90) (All ND) (All ND) (English Sole) Non-outfall 91 183 10.29 0.06 1316.70 175.41 0.08 ND Liver (124-268) (1.93-26.80) (0.02-0.19) (71.10-14300) (0-1694.70) (0-5.27) (All ND) Outfall 78 184 11.66 0.06 1532.90 203.93 1.25 ND (136-290) (0-27.10) (0.02-0.16) (95.70-20967) (0-1627.29) (0-30.80) (All ND) Table 2-13 Means and ranges of muscle tissue contaminant concentrations in selected scorpaenid and sand bass fishes collected by rig-fishing in April/May 2019 at Zones 1 (Outfall) and 3 (Non-outfall), including historical values and state and federal thresholds. ND = Not Detected; NC = Not Collected; N/A= Not Applicable. Standard Percent Mercury Arsenic Selenium EDDT EPCB EChlordane Dieldrin Zone Species n Length Lipid (mg/kg) (mg/kg) (mg/kg) (pg/kg) (pg/kg) (pg/kg) (pg/kg) (mm) 2018-2019 values Scorpaena guttata 3 190 1.76 0.08 8.17 0.65 28.29 3.21 ND ND (California Scorpionfish) (175-215) (0.69-2.66) (0.06-0.10) (2.30-13.30) (0.55-0.78) (5.08-63.40) (0-7.01) (All ND) (All ND) Non-outfall Sebastes caurinus 1 265 0.56 0.08 4.58 0.29 ND ND ND ND (Copper Rockfish) Sebastes miniatus 241 1.10 0.04 2.74 0.42 11.71 1.92 ND ND (Vermilion Rockfish) 6 (210-281) (0-2.45) (0.04-0.05) (1.47-5.18) (0.29-0.56) (2.57-31.63) (0-8.02) (All ND) (All ND) Paralabrax nebulifer 8 304 1.80 0.07 1.42 0.47 101.51 69.99 0.96 ND (Barred Sand Bass) (240-360) (0.434.60) (0.05-0.09) (0.58-2.72) (0.28-0.62) (18.30-243.68) (16.59-152.27) (0-8) (All ND) Outfall Sebastes miniatus 2 260 1.08 0.03 2.48 0.46 9.84 1.62 ND ND (Vermilion Rockfish) (both 260) (0.33-1.84) (0.02-0.04) (2.13-2.82) (0.39-0.53) (3.10-16.58) (0-3.25) (All ND) (All ND) OCSD historical values(2012-2018 Fiscal Years) Scorpaena guttata NC - - - - - - - - - (California Scorpionfish) N Sebastes caurinus 310 0.66 0.12 1.64 0.69 16.88 1.60 ND ND Non-outfall (Copper Rockfish) 10 (225-780) (0-1.08) (0.06-0.19) (0.52-2.21) (0.16-1.64) (5.61-43) (0-7.60) (All ND) (All ND) Cfl Sebastes miniatus 18 245 0.69 0.08 2.90 0.71 19.22 0.39 ND ND (Vermilion Rockfish) (215-295) (0.34-1.28) (0.05-0.20) (1.07-10.30) (0.07-1.54) (4.00-99.20) (0-2.46) (All ND) (All ND) Paralabrax nebulifer INC - - - - - - - - - (Barred Sand Bass) Outfall Sebastes miniatus 43 266 1.20 0.05 2.68 0.54 13.15 1.97 0.24 ND (Vermilion Rockfish) (149-317) (0-3.82) (0.02-0.08) (0.68-5.89) (0.17-0.88) (0-58.30) (0-17.24) (0-8.80) (All ND) Tissue Thresholds CA Advisory Tissue Level N/A N/A 0.44 N/A 15 2100 120 560 46 Federal Action Level for edible tissue N/A N/A 1 N/A N/A 5000 2000 300 300 0 O 0 fD v CID (D 3 01 O 7 to Compliance Determinations REFERENCES Allen, M.J., R.W. Smith, E.T. Jarvis, V. Raco-Rands, B.B. Bernstein, and K.T. Herbinson. 2005. Temporal trends in southern California coastal fish populations relative to 30-year trends in oceanic conditions. In: Southern California Coastal Water Research Project Annual Report 2003-2004 (S.B. Weisberg — Ed.). Southern California Coastal Water Research Project, Westminster, CA. p. 264-285. Chavez, F.P., J.T. Pennington, C.G. Castro, J.P. Ryan, R.P. Michisaki, B. Schlining, P. Walz, K.R. Buck, A. McFadyen, and C.A. Collins. 2002. Biological and chemical consequences of the 1997-1998 El Nino in central California waters. Prog. Oceanogr. 54:205-232. Hsieh, C., C. Reiss, W. Watson, M.J. Allen, J.R. Hunter, R.N. Lea, R.H. Rosenblatt, P.E. Smith, and G. Sigihara. 2005. A comparison of long-term trends and variability in populations of larvae of exploited and unexploited fishes in the southern California region: A community approach. Prog. Oceanogr. 67:160-185. Jarvis, E.T., M.J. Allen, and R.W. Smith. 2004. Comparison of recreational fish catch trends to environment- species relationships and fishery-independent data in the Southern California Bight, 1980-2000. CaICOFI Rep. Vol. 45. Long, E.R., D.D. McDonald, S.L. Smith, and F.C. Calder. 1995. Incidence of adverse biological effects within ranges of chemical concentrations in marine and estuarine sediments. Environ. Manage. 19:81-97. OCSD (Orange County Sanitation District). 1996a. Science Report and Compliance Report, Ten Year Synthesis, 1985-1995. Marine Monitoring. Fountain Valley, CA. OCSD. 1996b. Water Quality Atlas. Ten-Year Synthesis, 1985-1995. Marine Monitoring. Fountain Valley, CA. OCSD. 2004.Annual Report, Science Report, July 2002—June 2003. Marine Monitoring. Fountain Valley, CA. OCSD. 2017.Annual Report, July 2015—June 2016. Marine Monitoring. Fountain Valley, CA. SWRCB (State Water Resources Control Board). 2012. Water Quality Control Plan - Ocean Waters of California. Sacramento, CA. Wilber, D.H. and D.G. Clarke. 2001. Biological effects of suspended sediments: A review of suspended sediment impacts on fish and shellfish with relation to dredging activities in estuaries. No.Am. J. Fish. Manage. 21:855-875. 2-20 Compliance Determinations 2-21 This page intentionally left blank. r CHAPTER 3 Strategic Process Studies and Regional Monitoring ME INTRODUCTION The Orange County Sanitation District (OCSD) operates under the requirements of a National Pollutant Discharge Elimination System (NPDES) permit issued jointly by the United States Environmental Protection Agency and the State of California Regional Water Quality Control Board (RWQCB) (nrv-IAr Nin RR_,)ni?_on1rti NIPnFQ PArmif Nln rAn11nr-n!) in June 2012. To document the effectiveness of its source control and wastewater treatment operations in protecting the coastal ocean, OCSD conducts an Ocean Monitoring Program (OMP) that includes Strategic Process Studies (SPS) and regional monitoring programs. In addition, OCSD performs special studies, which are generally less involved than SPS and have no regulatory requirement for prior approval or level of effort. SPS are designed to address unanswered questions raised by the Core monitoring program results and/or focus on issues of interest to OCSD and/or its regulators, such as the effect of contaminants of emerging concern on local fish populations. SPS are proposed and must be approved by the RWQCB to ensure appropriate focus and level of effort. For the 2018-19 program year, 5 SPS were started. Regional monitoring studies focus on the larger areas of the Southern California Bight. These may include the "Bight" studies coordinated by the Southern California Coastal Water Research Project (SCCWRP) or studies conducted in coordination with other public agencies and/or non-governmental organizations in the region. Examples include the Central Region Kelp Survey Consortium and the Southern California Bight Regional Water Quality Program. This chapter provides overviews of recently completed and ongoing studies and regional monitoring efforts. Unlike other chapters in this report, these summaries are not restricted to the most recent program year (i.e., July 2018-June 2019) and include the most recent information available to date. When appropriate, this information is also incorporated into other report chapters to supplement Core monitoring results. Links to final study reports, if available, are listed under each section below. STRATEGIC PROCESS STUDIES For the 2018-19 program year, OCSD had 5 SPS that were designed to address potential changes in the quantity and quality of its discharged effluent when the Groundwater Replenishment System (GWRS) Final Expansion project is completed in 2023. ROMS-BEC Ocean Outfall Modeling (2019-2022) OCSD last modeled and characterized its discharge plume in the early 2000s. Since then, significant changes have occurred in both the quantity and quality of the effluent discharged due to 3-1 Strategic Process Studies and Regional Monitoring water conservation and reclamation efforts. To evaluate the spatial extent and temporal variability of the discharged plume, OCSD will work with SCCWRP and their collaborators to model and assess the spatial and temporal extent of its discharged effluent before and after (compare and contrast) the implementation of the GWRS Final Expansion. Microplastics Characterization (2019-2020) Wastewater treatment plants are a known microplastics (1-5 mm) conduit to aquatic, marine, and terrestrial environments; however, data regarding microplastics from OCSD treatment processes are non-existent. This SPS will characterize the quantity and types of microplastics throughout OCSD's treatment system. Another goal of this study is to develop methods and analyses to help inform the transport, fate, and impacts of microplastics through OCSD's wastewater treatment process to the receiving environment. Contaminants of Emerging Concern Monitoring (2019-2020) Contaminants of Emerging Concern (CEC) are generally not lethal but can be detrimental to living organisms (including humans) over time. This study will provide a preliminary assessment of non-targeted CECs in OCSD's receiving environment using in-vitro cell bioassay techniques. Used as a screening tool, cell bioassays should help researchers evaluate potential impacts resulting from changes in the effluent and receiving environment water quality associated with the GWRS Final Expansion. Sediment Linear Alkylbenzenes (2020-2021) Linear Alkylbenzenes (LABs) are organic contaminants that can be used to track the presence and settling of wastewater particles in the offshore environment. From 1998-2014, OCSD used LABs to measure its discharge footprint and investigate whether other contaminants present in the sediment were associated with the effluent discharge. This study will provide updated data within OCSD's monitoring area for evaluating future changes due to GWRS Final Expansion. Included will be a literature review of potential alternative effluent tracers that may be used to complement or enhance the current LAB tracers for future applications. Meiofauna Baseline (2020-2021) The increase of reverse osmosis concentrate (brine) return flows from the GWRS Final Expansion may negatively affect marine biota in the receiving water. While meiofauna (animals ranging from 63-500 pm in size) are known to be more sensitive to anthropogenic impacts than macrofauna, information on meiofauna diversity and abundance in OCSD's monitoring area is non-existent. This study will characterize the meiofauna communities in the receiving environment and evaluate the suitability of using meiofauna for a Before-After Control-Impact study of the GWRS Final Expansion. REGIONAL MONITORING Regional Nearshore (Surfzone) Bacterial Sampling OCSD partners with the Orange County Health Care Agency (OCHCA), the South Orange County Wastewater Authority, and the Orange County Public Works in the Ocean Water Protection Program, a regional bacterial sampling program that samples 126 stations along 42 miles (68 km) of coastline (from Seal Beach to San Clemente State Beach) and 70 miles (113 km) of harbor and bay frontage. OCSD samples 38 stations 1-2 days/week along 19 miles (31 km) of beach from Seal Beach to Crystal Cove State Beach (Figure 3-1). OCHCA reviews bacteriological data to determine whether a station meets Ocean Water-Contact Sports Standards (i.e., Assembly Bill 411; AB411), and uses these results as the basis for health advisories, postings, or beach closures. Results are provided in OCHCA(2019). 3-2 Strategic Process Studies and Regional Monitoring 5Q'p5 10m Op 60605p •Corewateroualitystation �0 p0^ O Regional water Quality Slatlon O� •Regional Surtz Station O JQj •Legacy surtzone station ocean omran: O 20m • 2451 •�C�O Reclamation zgsz 1� Huntington Plant 1 Beach 2453'•, 2401 �p y� 30m 2402 2349y O ^tit Treatment 2454� 24030 _ • c5� + Plant 2 2350 2301 • zass 2351• 2221 • o¢ PQ- Newport 24040 302 1 ,�Nl p Beach 40m 2456 23520 2303 .2222 220 • 15 24050 22230 • 23040 220 2181r yp 24060 2224• 2182 210111 • A9 p 50m 2305• 21830 20210 •�•0�pop 2354• 2204• 2102' O O p O 60m 22250 2103• 2022 2001 QQy� g 0 2306• 21840, 2023'• 0 80m •� �pn' O O • 22 2003 O p O loom 2226 2104••, �O OQP 21850 2206• ��— 1901 O(J 200m 2105• 2004 21880 1902C 2025 U 300m � 2106• 2005 1903O 2026 1904 N 2006' 0 1 2 4 Miles 1905` 0 1.5 3 6 Kilometers J 1906 OCSD January 2020 Esri,Garmin,GEBCO.NOAA NGDC,and other contributors Figure 3-1 Offshore and nearshore (surfzone)water quality monitoring stations for 2018-19. Of the 38 OCSD-sampled regional surfzone stations, 18 are legacy (Core) stations sampled since the 1970s (Figure 3-1). Results for these stations were similar to those of previous years (OCSD 2017, 2018) with fecal indicator counts varying by quarter, location, and bacteria type (Table B-14). A general spatial pattern was associated with the mouth of the Santa Ana River. Quarterly geomeans peaked near the river mouth (Station 0) and tapered off upcoast and downcoast. Southern California Bight Regional Water Quality Program OCSD continued as a member of a regional cooperative sampling effort known as the Southern California Bight Regional Water Quality Program (SCBRWQP; previously known as the Central Bight Regional Water Quality Monitoring Program) with the City of Oxnard, City of Los Angeles, the County Sanitation Districts of Los Angeles, and the City of San Diego. Each quarter, the participating agencies sample 301 stations that cover the coastal waters from Ventura County to Crystal Cove State Beach and from Point Loma to the United States—Mexico Border (Figure 3-2). The participants use comparable conductivity-temperature-depth (aka CTD) profiling systems and field sampling methods. OCSD samples 66 stations, which includes the 28 Core water quality program stations, as part of this program (Figure 3-1). The SCBRWQP monitoring provides regional data that enhances the evaluation of water quality changes due to natural (e.g., upwelling) or anthropogenic discharges (e.g., outfalls and stormwater flows) and provides a regional context for comparisons with OCSD's monitoring results. The SCBRWQP serves as the basis for SCCWRP's Bight water quality sampling (see section below). Additionally, the group has been evaluating the 3-3 Strategic Process Studies and Regional Monitoring Ventura San Los Angeles Bernardino p pow oo� o o 8® �o0d9 �� f • i Orange 8 0°•v,� Riverside 0 0 San Diego 119e0.0 00 • City of Oxnard 0 p 000 O City of Los Angeles • LACSD • OCSD 0 25 O City of San Diego-Point Loma a 20 ao so K Kibmaters 0 City of San Diego-IWTP OCSD March 2020 Esri,Garmin,GEBCO,NOAA NGDC,and other contributors Figure 3-2 Southern California Bight Regional Water Quality Program monitoring stations for 2018-19. establishment of data quality assurance guidelines and data quality flags for submitting data to the Southern California Coastal Ocean Observing System in order to comply with national Integrated Ocean Observing System (IOOS) guidelines. Bight Regional Monitoring Since 1994, OCSD has participated in 6 regional monitoring studies of environmental conditions within the Southern California Bight (SCB): 1994 Southern California Bight Pilot Project, Bight'98, Bight'03, Bight'08, Bight'13, and Bight'18. OCSD has played a considerable role in all aspects of these regional projects, including program design, sampling, quality assurance, data analysis, and reporting. Results from these efforts provide information that is used by individual dischargers, resource managers, and the public to improve region-wide understanding of environmental conditions and to provide a regional perspective for comparisons with data collected from individual point sources. During the summer of 2018, OCSD staff conducted field operations, ranging from Dana Point in southern Orange County to the Long Beach breakwater in southern Los Angeles County and southwest to the southern end of Santa Catalina Island, as part of the Bight'18 sampling effort (Figure 3-3). Summer 2018 benthic sampling included sediment geochemistry and infauna and trawling for epibenthic fish and macroinvertebrates. Ocean acidification sampling, including bongo net towing to collect pteropods, has taken place quarterly since January 2019. 3-4 Strategic Process Studies and Regional Monitoring O O Benthic Station Only(n=20) C 0 Trawl Station Only(n=7) • ® Benthic and Trawl Stations(n=14) Reclamation Plant 1 r • Ocean Acidification Hypoxia Station(n=5) Bongo Net Tow Station(n=4) • O O O O 0 Treatment O O O O </ Plant 2 O O •• CID O O • O O O 0 O O O O 8 OCSD Outfalls 0 O O O • O = aa O O O 0 75 15 Miles 0 12 24 Kilometers OCSD March 2020 Esn,Garmin,GEBCO,NOAA NGDC,and other contributors Figure 3-3 OCSD's Bight'18 sampling stations. Detailed information is available on SCCWRP's website ( p://www.sccwrp.org/about/research- areas/regional-monitoring/). Regional Kelp Survey Consortium — Central Region OCSD is a member of the Central Region Kelp Survey Consortium (CRKSC), which was formed in 2003 to map giant kelp (Macrocystis pyrifera) beds off Ventura, Los Angeles, and Orange Counties via aerial photography. The program is modeled after the San Diego Regional Water Quality Control Board, Region Nine Kelp Survey Consortium, which began in 1983. Both consortiums sample quarterly to count the number of observable kelp beds and calculate maximum kelp canopy coverage. Combined, the CRKSC and San Diego aerial surveys provide synoptic coverage of kelp beds along approximately 81% of the 270 miles (435 km) of the southern California mainland coast from northern Ventura County to the United States—Mexico Border. Survey results are published and presented annually by MBC Applied Environmental Sciences (MBC 2019) to both consortium groups, regulators, and the public. Reports are available at ttps://www.mbcaquatic.com/reports/ southern-california-bight-regional-aerial-kelp-surveys. 2018 CRKSC Results Total combined kelp surface canopy in the Central Region increased by 61% in 2018 compared to 2017 (7.9 km2 versus 4.8 km2), the highest in 50 years. Of the 26 recognized beds, 24 showed a surface canopy, with 23 increasing in size and 1 decreasing in size. Eighteen beds exceeded 3-5 Strategic Process Studies and Regional Monitoring 40% of their historical maximum size, with 12 at or above 80%, including 3 that reached maximum levels recorded. Six beds declined to less than 10% of their maximum size. Since 2007 total kelp coverage for the Central Region has been at or above the long-term average every year. For the 4 survey areas nearest to OCSD's outfall, 3 (Horseshoe Kelp, Huntington Flats and Huntington Flats to Newport Harbor) continued to show no surface canopy. The Newport/Irvine Coast beds showed a 1-year increase of 261% (0.033 km2 to 0.119 km2). However, this large increase represents only 28% of the maximum canopy area recorded in 2011. There was no evidence of any adverse effects on giant kelp resources from any of the region's dischargers. Rather, the regional kelp surveys continue to demonstrate that most kelp bed dynamics in the Central region are influenced by the large-scale oceanographic environment and micro-variations in local topography and currents that can cause anomalies in kelp bed performances. Ocean Acidification and Hypoxia Mooring OCSD's Ocean Acidification and Hypoxia Mooring was deployed for just over 7 months during the program year. Routine service and maintenance, vessel scheduling, and technical issues with a telemetry modem prevented continuous deployment. During the course of the year, a second mooring was procured to address the primary issues of non-deployment status. Rotating the 2 moorings—swapping one with the other—should improve deployment and recovery schedules while allowing for routine maintenance and repairs of sensors on the off-cycle mooring. Additionally, work was begun on establishing an automated data quality control system for telemetered data based on IOOS protocols (ittps://ioos.noaa.gov/project/gartoc ). SPECIAL STUDIES California Ocean Plan Compliance Determination Method Comparison Southern California ocean dischargers maintain extensive monitoring programs to assess their effects on ambient receiving water quality and to determine compliance with California Ocean Plan (COP) standards. However, historically each agency used a different approach for analyzing these data and determining COP compliance. In 2009, in collaboration with southern California ocean dischargers, the State Water Resources Control Board and SCCWRP began developing a new method to establish an out-of-range occurrence (ORO) for dissolved oxygen, pH, and light transmissivity. Appendix A contains the steps on how the comparison was compiled. Results for 2018-19 were the same as previous comparisons. The SCCWRP methodology identified greater numbers of reference stations and fewer stations that did not meet COP criteria (Table 3-1, Figure 3-4). The probable source of these differences is the different approaches used in identifying reference stations, out-of-range values and statistical significance testing, and subsequently out-of-compliance (OOC). OCSD uses multiple parameters and contextual information (e.g., Is the station up-current of the outfall? Was there a large phytoplankton bloom? Was it adjacent to other plume impacted station(s)?) and divides up the stations into 2 zones with one reference station per zone. SCCWRP's approach identifies plume-impacted stations using CDOM only and compares those stations to a larger set of reference stations. As a result, SCCWRP can identify stations "impacted" due to other sources. For example, in June 2019, the 3 stations identified with oxygen OROs and OOCs were located in the northwest portion of the OCSD station grid. Local currents showed a strong downcoast flow inshore at these stations with upcoast and offshore flows in the offshore portion of the grid where the outfall diffuser is located. The source of these impacts was more likely to be from the Long Beach area and not the outfall. 3-6 Strategic Process Studies and Regional Monitoring Table 3-1 Comparison of monthly California Ocean Plan compliance determinations using OCSD and SCCWRP methodologies for dissolved oxygen, pH, and light transmissivity for 2018-19. Current Plume Impacted Reference Out-of-Range Out-of-Compliance Survey Direction OCSD SCCWRP OCSD SCCWRP OCSD SCCWRP OCSD SCCWRP Dissolved Oxygen Jul-18 UC N/A 8 2 9 12 2 0 2 Aug-18 UC N/A 3 2 14 1 0 0 0 Sep-18 DC N/A 4 2 12 2 0 0 0 Oct-18 UC N/A 3 2 15 0 0 0 0 Nov-18 UC N/A 4 2 15 0 0 0 0 Dec-18 UC N/A 2 2 7 0 0 0 0 Jan-19 DC N/A 4 2 10 2 0 2 0 Feb-19 DC N/A 4 2 13 8 0 3 0 Mar-19 UC N/A 4 2 14 0 0 0 0 Apr-19 DC N/A 5 2 14 12 0 12 0 Apr-19 UC N/A 5 2 14 14 0 9 0 May-19 DC N/A 4 2 12 13 0 5 0 Jun-19 UC N/A 5 2 10 10 3 2 3 pH Jul-18 UC N/A 8 2 9 1 0 0 0 Aug-18 UC N/A 3 2 16 0 0 0 0 Sep-18 DC N/A 4 2 14 0 0 0 0 Oct-18 UC N/A 3 2 17 0 0 0 0 Nov-18 UC N/A 4 2 16 0 0 0 0 Dec-18 UC N/A 2 2 7 0 0 0 0 Jan-19 DC N/A 4 2 11 0 0 0 0 Feb-19 DC N/A 4 2 4 1 0 1 0 Mar-19 UC N/A 4 2 15 10 0 0 0 Apr-19 DC N/A 5 2 16 15 0 7 0 Apr-19 UC N/A 5 2 16 9 0 7 0 May-19 DC N/A 4 2 12 2 0 2 0 Jun-19 UC N/A 5 2 10 0 0 0 0 Light Transmissivity Jul-18 UC N/A 8 2 10 2 6 0 5 Aug-18 UC N/A 3 2 16 11 3 0 3 Sep-18 DC N/A 4 2 14 6 2 0 2 Oct-18 UC N/A 3 2 17 15 2 0 2 Nov-18 UC N/A 4 2 16 7 4 1 4 Dec-18 UC N/A 2 2 7 23 1 2 1 Jan-19 DC N/A 4 2 11 9 3 0 3 Feb-19 DC N/A 4 2 14 8 3 1 3 Mar-19 UC N/A 4 2 15 20 4 4 4 Apr-19 DC N/A 5 2 16 13 4 1 2 Apr-19 UC N/A 5 2 16 10 4 2 2 May-19 DC N/A 4 2 12 5 3 0 3 Jun-19 UC N/A 5 2 10 12 2 0 1 N/A=Not Applicable;DC=Downcoast;UC=Upcoast. 3-7 Strategic Process Studies and Regional Monitoring 28 Oxygen pH Transmissivity Oxygen pH Transmissivity 2s 24 22 20 18 C O 16 • Cf)14 C O 12 • (0 W 10 r • 8 O 6 O O a O o N/A O _ 1� Reference CDOM Impacted Out of Range Out of Compliance Figure 3-4 Comparison of monthly OCSD (blue) and SCCWRP (red) California Ocean Plan Compliance results for Program Years 2016-17 to 2018-19 (n=36). N/A = Not Applicable. Fish Tracking Study OCSD's OMP assesses discharge effects on marine communities, including bioaccumulation analyses of contamination levels in tissue samples of flatfishes (predominantly Hornyhead Turbot and English Sole; occasionally Pacific Sanddab) and rockfishes relative to background levels and human health consumption guidelines. In making these comparisons it is assumed that the location of capture is also the location of exposure. However, little is known about the movement patterns of sentinel fish species within OCSD's monitoring area. To assess this issue, OCSD contracted Professor Chris Lowe from California State University, Long Beach to conduct a fish tracking study using passive acoustic telemetry from 2017-18 to understand the site fidelity and potential risk exposure of sentinel fishes at the outfall and a reference area. The results indicated that residencies to both areas were low for Hornyhead Turbot, English Sole and Pacific Sanddab (<10% of the study duration was spent in either site), whereas Vermilion Rockfish showed higher degrees of residency to the outfall site (nearly 40% of the study duration) (Burns et al. 2019). These results suggest that tissue samples of sentinel flatfishes likely reflect the accumulation of contaminants across individuals' ranges, not just the outfall site. In addition, Vermilion Rockfish may be the most susceptible sentinel species to wastewater effluent effects. 3-8 Strategic Process Studies and Regional Monitoring REFERENCES Burns, E.S., J. Armstrong, D. Tang, K. Sakamoto, and C.G. Lowe. 2019. The residency, movement patterns and habitat association of several demersal fish species to the Orange County Sanitation District wastewater outfall. Mar. Pollut. Bull. 149:110638. MBC (MBC Applied Environmental Sciences). 2019. Status of the Kelp Beds In 2018: Ventura, Los Angeles, Orange, and San Diego Counties. Prepared for the Central Region Kelp Survey Consortium and Region Nine Kelp Survey Consortium. OCHCA(Orange County Health Care Agency). 2019. OCHCA 2017 and 2018 Ocean, Harbor and Bay Water Quality Report. OCSD (Orange County Sanitation District). 2017. Annual Report, July 2015—June 2016. Marine Monitoring. Fountain Valley, CA. OCSD. 2018.Annual Report, July 2016—June 2018. Marine Monitoring. Fountain Valley, CA. 3-9 This page intentionally left blank. APPENDIX A Methods INTRODUCTION This appendix contains a summary of the field sampling, laboratory testing, and data analysis methods used for the Ocean Monitoring Program (OMP) at the Orange County Sanitation District (OCSD). The methods also include calculations of water quality compliance with California Ocean Plan (COP) criteria. WATER QUALITY MONITORING Field Methods Offshore Zone Permit-specified water quality monitoring was conducted 6 times per quarter. Three surveys sampled the full 28 station grid for COP compliance determinations and 3 surveys sampled a subset of 8 stations located within 3 miles of the coast for water-contact (REC-1) compliance (Table A-1; Figure 2-1). Each survey included measurements of pressure (from which depth is calculated), temperature, conductivity (from which salinity is calculated), dissolved oxygen (DO), acidity/alkalinity (pH), water clarity (light transmissivity, beam attenuation coefficient [beam-c], and photosynthetically active radiation [PAR]), chlorophyll-a fluorescence, and colored dissolved organic matter (CDOM). Measurements were conducted using a Sea-Bird Electronics SBE911 plus conductivity-temperature- depth (CTD) profiling system deployed from the M/V Nerissa. Profiling was conducted at each station from 1 m below the surface to 2 m above the bottom or to a maximum depth of 75 m, when water depths exceeded 75 m. SEASOFT V2 (2017a) software was used for data acquisition, data display, and sensor calibration. PAR was measured in conjunction with chlorophyll-a because of the positive linkage between light intensity and photosynthesis per unit chlorophyll (Hardy 1993). Wind condition, sea state, and visual observations of floatable materials or grease that might be of sewage origin were also noted. Discrete ammonium (NH3-N) and fecal indicator bacteria (FIB) samples were collected at specified stations and depths using a Sea-Bird Electronics Carousel Water Sampler (SBE32) equipped with Niskin bottles. Six liters of surface seawater (control sample) were collected at Station 2106 during each survey for ammonium QA/QC analysis. All bottled samples were kept on ice in coolers and transported to OCSD's laboratory within 6 hours. A summary of the sampling and analysis methods is presented in Table A-1. Southern California Bight Regional Water Quality An expanded grid of water quality stations was sampled quarterly as part of the Southern California Bight Regional Water Quality monitoring program. These 38 stations were sampled by OCSD in conjunction with the 28 Core water quality stations (Figure 3-1) and those of the County Sanitation A-1 Table A-1 Water quality sample collection and analysis methods by parameter during 2018-19. rt #Sampling Sampling Method Field Holding Sampling Field 3 Parameter Events Method Reference Preservation Container Time Depth Replicates C Q Nearshore(Surfzone) to Total Coliforms 1-2/week Standard Methods 9222 B** 125 mL HDPE at least 10%of Fecal Coliforms 1-2/week grab Standard Methods 9222 D** Ice(<6°C) 8 hrs.(field+lab) Ankle-deep water Enterococci 1-2/week EPA Method 1600*** (Sterile container) samples Offshore Temperature 6/quarter in-situ probe LMC SOP 1500.1-CTD Operations not applicable not applicable not applicable every 1 m* at least 10%of stations Salinity(conductivity)2 6/quarter in-situ probe LMC SOP 1500.1-CTD Operations not applicable not applicable not applicable every 1 m* at least 10%of stations H 3 6/ uarter in-situ robe LMC SOP 1500.1-CTD Operations not applicable not applicable not applicable eve 1 * at least 10%of p q p p pp pp pp every m stations Dissolved Oxygen" 6/ uarter in-situ robe LMC SOP 1500.1-CTD Operations not applicable not applicable not applicable eve 1 * at least 10%of yg q p p pp PP pp every m stations Light Transmissivity s 6/quarter in-situ probe LMC SOP 1500.1-CTD Operations not applicable not applicable not applicable every 1 m* at least 10%of stations Photosynthetically Active at least 10%of Radiation(PAR)a 6/quarter in-situ probe LMC SOP 1500.1-CTD Operations not applicable not applicable not applicable every 1 m* stations Chloro h II-a fluorescence s 6/ uarter in-situ robe LMC SOP 1500.1-CTD Operations not applicable not applicable not applicable eve 1 * at least 10%of p y q p p pp pp pp every m stations Color Dissolved Organic Matter 6/quarter in-situ probe LMC SOP 1500.1-CTD Operations not applicable not applicable not applicable every 1 m* at least 10%of (CDOM)s stations Surface,10m,20m, at least 10%of Ammonium(NH3-N) 6/quarter Niskin bottle LMC SOP 4500-NH3.G,Rev.J** Ice(<6°C) 125 mL HDPE 28 days 30m,40m,50m, samples 60m,Bottom 20m 10m, , � Total Coliforms and 125 mL HDPE Surface, at least 10%of N Escherichia coli' 5/quarter a Niskin bottle Standard Methods 9223 C** Ice(<6°C) (Sterile container) 8 hrs.(field+lab) 30m,40m,50m, samples 60m,Bottom Surface,10m,20m, Enterococci 5/quarter 9 Niskin bottle Standard Methods 9230 D Ice(<6°C) 125 mL HDPE 8 hrs.(field+lab) 30m,40m,50m, at least 1 s of (Sterile container) 60m,Bottom samples Surface Observations 6/quarter visual Permit specs. not applicable not applicable not applicable surface not applicable observations 1 Calibrated to reference cells(0.0005°C accuracy)annually. 2 Calibrated to IAPSO Standard and Guildline 8400B Autosal annually. 3 Referenced and calibrated to NIST buffers of pH 7,8,and 9 prior to every survey. 4 Referenced and calibrated each survey by comparison with the lab DO probe,which is calibrated daily. 5 Referenced and calibrated to known transmittance in air. 6 Factory calibrated annually. 7 Fecal coliform count calculation:(Escherichia coli MPN/100mL x 1.1). 8 REC-1 surveys completed within 30 days for geomean calculations. Sampled continuously at 24 scans/second but data processed to 1 m intervals. **APHA(2012). ***Available online at:www.epa.gov. Methods Districts of Los Angeles, the City of Los Angeles, the City of Oxnard, and the City of San Diego. The total sampling area extends from the Ventura River in the north to the U.S./Mexico Border in the south, with a significant spatial gap between Crystal Cove State Beach and Mission Bay (Figure 3-2). Data were collected using CTDs within a fixed-grid pattern comprising 304 stations during a targeted period of 3-4 days. Parameters measured included pressure, water temperature, conductivity, DO, pH, chlorophyll-a, CDOM, and water clarity. Profiling was conducted from the surface to 2 m from the bottom or to a maximum depth of 100 m. OCSD's sampling and analytical methods were the same as those presented in Table A-1. Nearshore Zone Regional nearshore (also referred to as "surfzone") FIB samples were collected 1-2 days per week at a total of 38 stations (Figure 3-1). When creek/storm drain stations flowed to the ocean, 3 bacteriological samples were collected at the source, 25 yards downcoast, and 25 yards upcoast. When flow was absent, a single sample was collected 25 yards downcoast. Samples were collected in ankle-deep water, with the mouth of the sterile bottle facing an incoming wave but away from both the sampler and ocean bottom. After the sample was taken, the bottle was tightly capped and promptly stored on ice in the dark. The occurrence and size of any grease particles at the high tide line were also recorded. Laboratory analysis of FIB samples began within 6 hours of collection. Laboratory Methods Laboratory analyses of NH3-N and bacteriology samples followed methods listed in Table A-1. Quality assurance/quality control (QA/QC) procedures included analysis of laboratory blanks and duplicates. All data underwent at least 3 separate reviews prior to being included in the final database used for statistical analysis, comparison to standards, and data summaries. Data Analyses Raw CTD data were processed using both SEASOFT (2017b) and third party (IGODS 2012) software. The steps included retaining down-cast data and removing potential outliers (i.e., data that exceeded specific sensor response criteria limits). Flagged data were removed if they were considered to be due to instrument failures, electrical noise (e.g., large data spikes), or physical interruptions of sensors (e.g., by bubbles) rather than by actual oceanographic events. After outlier removal, averaged 1 m depth values were prepared from the down-cast data; if there were any missing 1 m depth values, then the up-cast data were used as a replacement. CTD and discrete data were then combined to create a single data file that contained all sampled stations for each survey day. Compliance Determinations COP compliance was assessed based on: (1) specific numeric criteria for DO, pH, and FIB (REC-1 zone only); and (2) narrative (non-numeric) criteria for light transmissivity, floating particulates, oil and grease, water discoloration, beach grease, and excess nutrients. DO, pH, and Light Transmissivity Station locations were defined as either Zone A (inshore) or Zone B (offshore) as shown in Figure A-1. Compliance evaluations for DO, pH, and light transmissivity were based on statistical comparisons to the corresponding Zone A or Zone B reference station located up-current of the outfall (OCSD 1999). For each survey, the depth of the pycnocline layer, if present, was calculated for each station using density data. The pycnocline is defined as the depth layer where stability is greater than 0.05 kg/m3 (Officer 1976). Data for each station and numeric compliance parameter (light transmissivity, DO, and pH) were binned by water column stratum: above, within, or below A-3 Methods 10m 20m 3�JQ Huntington Reclamation Beach Plant 1 30m 2403• Treatment • 23510 Plant 2 Newport Beach h 40m `23030 2352• ` 2405• 22230 2304• 2353• 22039 24060 22240 50m 23050 21830 23540 2204• ' 60m 2 2225• 21039 0�2306• e 21840 80 m 22 loom 2226• 21 pq0, 2185• 2206• 200m 21050 2186• O no sfnron 300m N 21060 •upw,,t Reference sfeto 0 1 2 4 Miles •Dewnceeef Rference Stzten •wager ouaiiry comPtance scafion —0ee1 0mr1111 0 1.5 3 6 Kilometers OCSD January 2020 Esrl,carmin,OEBCO,NOAA NODO,and other contributors Figure A-1 Offshore water quality monitoring stations and zones used for California Ocean Plan compliance determinations. the pycnocline. When a pycnocline was absent, data were binned into the top, middle, or bottom third of the water column for each station. Mean values for each parameter were calculated by stratum and station. The number of observations usually differed from station to station and survey to survey due to different water and pycnocline depths. The selection of appropriate reference stations (i.e., upcoast or downcoast) for each survey day were determined based on available current measurements and the presence or absence of typical plume "signals" (e.g., NH3-N, FIB, and/or CDOM). If the choice of a reference station was indeterminate, then the data were analyzed twice using both upcoast and downcoast reference stations. Once reference stations were determined, the data were analyzed using in-house MATLAB (2007) routines to calculate Out-of-Range occurrences (OROs) for each sampling date and parameter. These OROs were based on comparing the mean data by stratum and station with the corresponding reference station data to determine whether the following criteria were exceeded: • DO: cannot be depressed >10% below the reference mean; • pH: cannot exceed ±0.2 pH units of the reference mean; and • Natural light (defined as light transmissivity): shall not be significantly reduced, where statistically different from the reference mean is defined as the lower 95% confidence limit. In accordance with permit specifications, the outfall station (2205) was not included in the comparisons because it is within the zone of initial dilution (ZID). A-4 Methods To determine whether an ORO was Out-of-Compliance (OOC), distributional maps were created that identified the reference stations for each sampling date and location of each ORO, including which stratum was out of range. Each ORO was then evaluated to determine if it represented a logical OOC event. These evaluations were based on: (A) evaluation of the wastewater plume location relative to depth using a combination of temperature, density, salinity, CDOM, and when available, FIB and NH3-N; (B) evaluation of features in the water column relative to naturally occurring events (i.e., high chlorophyll-a due to phytoplankton); and (C) unique characteristics of some stations that may not be comparable with permit-specified reference stations (2104/2105 or 2404/2406) due to differences in water depth and/or variable oceanographic conditions. For example, some Zone A stations (e.g., 2403) are located at shallower depths than reference Station 2104. Waves and currents can cause greater mixing and resuspension of bottom sediments at shallower stations under certain conditions (e.g., winter storm surges). This can result in naturally decreased water clarity (light transmissivity) that is unrelated to the wastewater discharge. An ORO can be in-compliance if, for example, a down-current station is different from the reference, but no intermediate (e.g., nearfield) stations exhibited OROs. Once the total number of OOC events was summed by parameter, the percentage of OROs and OOCs were calculated according to the total number of observations. In a typical year, Zone A has a total of 468 possible comparisons if 13 stations (not including the reference station) and 3 strata over 12 survey dates per year are used. For Zone B, 432 comparisons are possible from 12 stations (not including the reference and outfall stations), 3 strata, and 12 sampling dates. The total combined number of ORO and OOC events was then determined by summing the Zone A and Zone B results. When all of the strata are not present (e.g., below thermocline at shallow stations) or additional surveys are conducted, the total number of comparisons in the analysis may be more or less than the target number of comparisons possible (900). Compliance was also calculated using a method developed by the Southern California Coastal Water Research Project (SCCWRP) in conjunction with its member agencies and the State Water Resources Control Board. The methodology involves 4 steps: (A) identification of the stations affected by effluent wastewater using CDOM, (B) selection of reference sampling sites representing "natural" conditions, (C) a per meter comparison between water quality profiles in the reference and plume-affected zones, and (D) calculation of maximum delta and comparison to COP standards to determine ORO SCCWRP. Reference sites were selected from the areas around the outfalls, excluding the sites affected by the effluent. Reference density profiles are calculated and the profiles in the plume zone are compared to the reference profiles and a maximum difference value is used to establish the number of ORO SCCWRP' Detailed methodology, as applied to DO, can be found in Nezlin et al. (2016). The 2 methods differ in their approach to establishing OROs and the SCCWRP methodology does not calculate OOCs, therefore the following steps were taken to make the output of both approaches more comparable. (1) The SCCWRP approach identifies a varying number of "plume impacted" and reference stations per survey while the OCSD method does not explicitly identify stations impacted by the plume and uses only 2 predetermined reference stations. For this analysis, only the number of reference stations can be directly compared. (2) SCCWRP methodology compares only those values located below the mixed layer while the OCSD method includes surface values. For this comparison, all ORO OCSDfound in the upper part of the water column (i.e., Stratum 1) were not considered. (3) Under the OCSD approach, a station may have multiple ORO and/or OOC values on a given survey, while the SCCWRP approach identifies a single maximum difference value per A-5 Methods station. Therefore, monthly station OROocso were recalculated as presence/absence when multiple OROocso occurred at a station. (4) Unlike the OCSD method, the SCCWRP method does not provide a path to evaluate whether an ORO did or did not constitute an OOC. For this comparison, it was assumed that an ORO SCCWRPwas equivalent to the OOCocso if it was located downcurrent from the outfall. (5) SCCWRP methodology does not exclude the outfall station (2205) which is located within the ZID. For this analysis, any ORO SCCWRPassociated with Station 2205 was not included. (6) SCCWRP methodology currently does not distinguish between positive and negative significant differences. For those instances when an ORO SCCWRPwas positive when the applicable COP criteria is relative to a negative impact, these OROs were not included. Fecal Indicator Bacteria FIB compliance used corresponding bacterial standards at each REC-1 station and for stations outside the 3-mile state limit. FIB counts at individual REC-1 stations were averaged per survey and compliance for each FIB was determined using the following COP criteria (SWRCB 2010): 30-day Geometric Mean • Total coliform density shall not exceed 1,000 per 100 mL. • Fecal coliform density shall not exceed 200 per 100 mL. • Enterococci density shall not exceed 35 per 100 mL. Single Sample Maximum • Total coliform density shall not exceed 10,000 per 100 mL. • Fecal coliform density shall not exceed 400 per 100 mL. • Enterococci density shall not exceed 104 per 100 mL. • Total coliform density shall not exceed 1,000 per 100 mL when the fecal coliform/total coliform ratio exceeds 0.1. Determinations of fecal coliform compliance were accomplished by multiplying E. coli data by 1.1 to obtain a calculated fecal coliform value. There are no compliance criteria for FIB at the nearshore stations. Nevertheless, FIB data were given to the Orange County Health Care Agency (which follows State Department of Health Service AB411 standards) for the Ocean Water Protection Program (http://ocbeachinfo.com ) and are briefly discussed in Chapter 3. Nutrients and Aesthetics These compliance determinations were done based on presence/absence and level of potential effect at each station. Station groupings are shown in Table B-5 and are based on relative distance and direction from the outfall. Compliance for the floating particulates, oil and grease, and water discoloration were determined based on presence/absence at the ocean surface for each station. Compliance with the excess nutrient criterion was based on evaluation of NH3-N compared to COP objectives for chronic (4 mg/L) and acute (6 mg/L) toxicity to marine organisms. Compliance was also evaluated by looking at potential spatial relationships between NH3-N distribution and phytoplankton (using chlorophyll-a fluorescence). A-6 Methods SEDIMENT GEOCHEMISTRY MONITORING Field Methods Sediment samples were collected for geochemistry analyses from 29 semi-annual stations in July 2018 (summer) and in January 2019 (winter) (Figure 2-2). In addition, 2-3 L of sediment was collected from Stations 0, 1, 4, 72, 73, 76, 77, CON, and ZB in January 2019 for sediment toxicity testing. Each station was assigned to 1 of 2 station groups: (1) Middle Shelf Zone 2, within-ZID (51-90 m) or (2) Middle Shelf Zone 2, non-ZID (51-90 m). In Chapter 2, the Middle Shelf Zone 2, within- and non-ZID station groups are simply referred to as within-ZID and non-ZID stations, respectively. The 39 NPDES permit-specified annual stations were not sampled during the 2018-19 monitoring period, as OCSD was given regulatory relief for participating in the Bight'18 regional monitoring program. A single grab was collected at each station using a paired 0.1 mz Van Veen grab sampler deployed from the M/V Nerissa. All sediment samples were qualitatively and quantitatively assessed for acceptability prior to processing. Samples were deemed acceptable if they had a minimum depth of 5 cm. However, if 3 consecutive sediment grabs each yielded a depth of <5 cm at a station, then the depth threshold was lowered to :54 cm. The top 2 cm of the sample was transferred into containers using a stainless steel scoop (Table A-2). The sampler and scoop were rinsed thoroughly with filtered seawater prior to sample collection. All sediment samples were transported on wet ice to the laboratory. Sample storage and holding times followed specifications in OCSD's Laboratory, Monitoring, and Compliance Standard Operating Procedures (LMC SOP) (OCSD 2016; Table A-2). Table A-2 Sediment collection and analysis summary during 2018-19. Parameter Container Preservation Holding Time Method Dissolved Sulfides HDPE container Freeze 6 months LMC SOP 4500-S G Rev.B Grain Size Plastic bag 4°C 6 months Plumb(1981) Mercury Amber glass jar Freeze 6 months LMC SOP 245.1 B Rev.G Metals Amber glass jar Freeze 6 months LMC SOP 200.8B_SED Rev.F Sediment Toxicity HDPE container 4°C 2 months LMC SOP 8810 Total Chlorinated Pesticides(FPest) Glass jar Freeze 6 months LMC SOP 8000-SPP Total DDT(EDDT) Glass jar Freeze 6 months LMC SOP 8000-SPP Total Nitrogen(TN) Glass jar Freeze 6 months EPA 351.2M and 353.2M Total Organic Carbon(TOC) Glass jar Freeze 6 months ASTM D4129-05 Total Phosphorus(TP) Glass jar Freeze 6 months EPA 6010E* Total Polychlorinated Biphenyls(FPCB) Glass jar Freeze 6 months LMC SOP 8000-SPP Total Polycyclic Aromatic Hydrocarbons(EPAH) Glass jar Freeze 6 months LMC SOP 8000-PAH *Available online at:www.epa.gov. Laboratory Methods Sediment grain size, total organic carbon, total nitrogen, and total phosphorus samples were subsequently transferred to local and interstate laboratories for analysis (see Appendix C). Sample transfers were conducted and documented using required chain of custody protocols through the Laboratory Information Management Systems software. All other analyses were conducted by OCSD lab staff. Sediment chemistry and grain size samples were processed and analyzed using the methods listed in Table A-2. The measured sediment chemistry parameters are listed in Table A-3. Method blanks, analytical quality control samples (duplicates, matrix spikes, and blank spikes), and standard reference materials were prepared and analyzed with each sample batch. Total polychlorinated biphenyls (7-PCB) and total polycyclic aromatic hydrocarbons (F-PAH) were calculated by summing the measured value of each respective constituent listed in Table A-3. Total dichlorodiphenyltrichloroethane (Y-DDT) represents the summed values of 4,4'-DDMU and the 2,4- and 4,4'-isomers of DDD, DDE, and DDT. Total chlorinated pesticides (ZPest) represents the summed values of 13 chlordane derivative compounds plus dieldrin. A-7 Methods Table A-3 Parameters measured in sediment samples during 2018-19. Metals Antimony Cadmium Lead Selenium Arsenic Chromium Mercury Silver Barium Copper Nickel Zinc Beryllium Organochlorine Pesticides Chlordane Derivatives and Dieldrin Aldrin Endosulfan-alpha gamma-BHC Hexachlorobenzene cis-Chlordane Endosulfan-beta Heptachlor Mirex trans-Chlordane Endosulfan-sulfate Heptachlor epoxide trans-Nonachlor Dieldrin Endrin DDT Derivatives 2,4'-DDD 2,4'-DDE 2,4'-DDT 4,4'-DDMU 4,4'-DDD 4,4'-DDE 4,4'-DDT Polychlorinated Biphenyl(PCB)Congeners PCB 18 PCB 81 PCB 126 PCB 170 PCB 28 PCB 87 PCB 128 PCB 177 PCB 37 PCB 99 PCB 138 PCB 180 PCB 44 PCB 101 PCB 149 PCB 183 PCB 49 PCB 105 PCB 151 PCB 187 PCB 52 PCB 110 PCB 153/168 PCB 189 PCB 66 PCB 114 PCB 156 PCB 194 PCB 70 PCB 118 PCB 157 PCB 201 PCB 74 PCB 119 PCB 167 PCB 206 PCB 77 PCB 123 PCB 169 Polycyclic Aromatic Hydrocarbon(PAH)Compounds Acenaphthene Benzo[g,h,i]perylene Fluoranthene 1-M ethyl naphthalene Acenaphthylene Benzo[k]fluoranthene Fluorene 2-M ethyl naphthalene Anthracene Biphenyl Indeno[1,2,3-c,d]pyrene 2,6-Di methyl naphthalene Benz[a]anth race ne Chrysene Naphthalene 1,6,7-Tri methyl naphthalene Benzo[a]pyrene Dibenz[a,h]anthracene Perylene 2,3,6-Tri methyl naphthalene Benzo[b]fluoranthene Dibenzothiophene Phenanthrene 1-Methylphenanthrene Benzo[e]pyrene Pyrene Other Parameters Dissolved Sulfides Total Nitrogen Total Organic Carbon Total Phosphorus Grain Size Sediment toxicity was conducted using the Eohaustorius estuarius amphipod survival test (EPA 1994). Amphipods were exposed to test and home (control) sediments for 10 days, and the percent survival of amphipods in each treatment was determined. Data Analyses All analytes that were undetected (i.e., value below the method detection limit) are reported as ND (not detected). Further, an ND value was treated as zero for calculating a mean analyte concentration; however, if a station group contained all ND for a particular analyte, then the mean analyte concentration is reported as ND. Sediment contaminant concentrations were evaluated against sediment quality guidelines known as Effects Range-Median (ERM) (Long et al. 1998). The ERM guidelines were developed for the National Oceanic and Atmospheric Administration National Status and Trends Program (NOAA 1993) as non-regulatory benchmarks to aid in the interpretation of sediment chemistry data and to complement toxicity, bioaccumulation, and benthic community assessments (Long and MacDonald 1998). The ERM is the 50th percentile sediment concentration above which a toxic effect frequently occurs (Long et al. 1995), and as such, an ERM exceedance is considered a significant potential for adverse biological effects. Bight'13 sediment geochemistry data (Dodder et al. 2016) were also used as benchmarks. Data analysis consisted of summary statistics and qualitative comparisons only. Toxicity threshold criteria applied in this report were consistent with those of the Water Quality Control Plan for Enclosed Bays and Estuaries — Part 1 Sediment Quality (Bay et al. 2009, SWRCB 2009). Stations with statistically different (p<0.05) amphipod survival rates when compared to the control, determined by a two-sample t-test, were categorized as nontoxic when survival was 90-100% of the control, lowly toxic when survival was 82-89% of the control, and moderately toxic A-8 Methods when survival was 59-81% of the control. Stations with no statistically different (p>0.05) amphipod survival rates when compared to the control were categorized as nontoxic when survival was 82-100% of the control and lowly toxic when survival was 59-81% of the control. Any station exhibiting amphipod survival less than 59% of the control was categorized as highly toxic. BENTHIC INFAUNA MONITORING Field Methods A paired, 0.1 m2 Van Veen grab sampler deployed from the M/V Nerissa was used to collect a sediment sample from the same stations (Figure 2-2) and frequencies as described above in the sediment geochemistry field methods section. The purpose of the semi-annual surveys was to determine long-term trends and potential effects along the 60-m depth contour. All sediment samples were qualitatively and quantitatively assessed for acceptability prior to processing as described above in the sediment geochemistry field methods section. At each station, acceptable sediment in the sampler was emptied into a 63.5 cm x 45.7 cm x 20.3 cm plastic tray and then decanted onto a sieving table whereupon a hose with a fan spray nozzle was used to gently wash the sediment with filtered seawater through a 40.6 cm x 40.6 cm, 1.0 mm sieve. Organisms retained on the sieve were rinsed with 7% magnesium sulfate anesthetic into one or more 1 L plastic containers and then placed in a cooler containing ice packs. After approximately 30 minutes in the anesthetic, animals were fixed by adding full strength buffered formaldehyde to the container to achieve a 10%, by volume, solution. Samples were transported to OCSD's laboratory for further processing. Laboratory Methods After 3-10 days in formalin, samples were rinsed with tap water and then transferred to 70% ethanol for long-term preservation. Samples were sent to Aquatic Bioassay and Consulting, Inc. (Ventura, CA), where they were sorted to 5 major taxonomic groups (aliquots): Annelida (worms), Mollusca (snails, clams, etc.), Arthropoda (shrimps, crabs, etc.), Echinodermata (sea stars, sea urchins, etc.), and miscellaneous phyla (Cnidaria, Nemertea, etc.). Removal of organisms was monitored to ensure that at least 95% of all organisms were successfully separated from the sediment matrix (see Appendix C). Upon completion of sample sorting, the major taxonomic groups were distributed for identification and enumeration (Table A-4). Taxonomic differences were resolved and the database was edited accordingly (see Appendix C). Species names used in this report follow those given in Cadien and Lovell (2018). Data Analyses Infaunal community data were analyzed to determine if populations outside the ZID were affected by the outfall discharge. Six community measures were used to assess infaunal community health Table A-4 Benthic infauna taxonomic aliquot distribution for 2018-19. Quarter Survey Taxonomic Aliquots Contractor OCSD (No.of samples) Annelida 16 13 Semi-annual Arthropoda 7 22 Summer 2018 (29) Echinodermata 29 0 Mollusca 14 15 Miscellaneous Phyla 7 22 Annelida 29 0 Semi-annual Arthropoda 29 0 Winter 2019 Echinodermata 29 0(29) Mollusca 0 29 Miscellaneous Phyla 29 0 Totals 189 101 A-9 Methods and function: (1) total number of species (richness), (2) total number of individuals (abundance), (3) Shannon-Wiener Diversity (H'), (4) Swartz's 75% Dominance Index (SDI), (5) Infaunal Trophic Index (ITI), and (6) Benthic Response Index (BRI). H' was calculated using loge (Zar 1999). SDI was calculated as the minimum number of species with combined abundance equal to 75% of the individuals in the sample (Swartz 1978). SDI is inversely proportional to numerical dominance, thus a low index value indicates high dominance (i.e., a community dominated by a few species). The ITI was developed by Word (1978, 1990) to provide a measure of infaunal community "health" based on a species' mode of feeding (e.g., primarily suspension vs. deposit feeder). ITI values greater than 60 are considered indicative of a "normal" community, while 30-60 represent a "changed" community, and values lower than 30 indicate a "degraded" community. The BRI measures the pollution tolerance of species on an abundance-weighted average basis (Smith et al. 2001). This measure is scaled inversely to ITI with low values (<25) representing reference conditions and high values (>72) representing defaunation or the exclusion of most species. The intermediate value range of 25-34 indicates a marginal deviation from reference conditions, 35-44 indicates a loss of biodiversity, and 45-72 indicates a loss of community function. The BRI was used to determine compliance with NPDES permit conditions, as it is a commonly used Southern California benchmark for infaunal community structure and was developed with the input of regulators (Ranasinghe et al. 2007, 2012). OCSD's historical infauna data from the past 10 monitoring periods, as well as Bight'13 infauna data (Gillett et al. 2017), were also used as benchmarks. The presence or absence of certain indicator species (pollution sensitive and pollution tolerant) was also determined for each station. The presence of pollution sensitive species, i.e., Amphiodia urtica (brittle star) and amphipod crustaceans in the genera Ampelisca and Rhepoxynius, typically indicates the existence of a healthy environment, while the occurrence of large numbers of pollution tolerant species, i.e., Capitella capitata Cmplx (polychaete), may indicate stressed or organically enriched environments. Patterns of these species were used to assess the spatial and temporal influence of the wastewater discharge in the receiving environment. PRIMER v7 (2015) multivariate statistical software was also used to examine the spatial patterns of infaunal invertebrate communities at the 29 stations. Analyses included (1) hierarchical clustering with group-average linking based on Bray-Curtis similarity indices and similarity profile (SIMPROF) permutation tests of the clusters and (2) ordination of the same data using non-metric multidimensional scaling (nMDS) to confirm hierarchical clustering. Prior to the calculation of the Bray-Curtis indices, the data were fourth root transformed in order to down-weight the highly abundant species and to incorporate the less common species (Clarke and Warwick 2014). TRAWL COMMUNITIES MONITORING Field Methods Demersal fishes and epibenthic macroinvertebrates (EMIs) were collected by trawling in July 2018 (summer) and in February 2019 (winter) at Stations T23, T22, T1, T12, T17, and T11 in the Middle Shelf Zone 2 (60 m) stratum (Figure 2-3). The 8 NPDES permit-specified annual stations were not sampled during the 2018-19 monitoring period, as OCSD was given regulatory relief for participating in the Bight'18 regional monitoring program. OCSD's trawl sampling protocols are based upon regionally developed sampling methods (Kelly et al. 2013). These methods require that a portion of the trawl track must pass within a 100 m radius of the nominal station position and be within 10% of the station's nominal depth. In addition, the speed and bottom-time duration of the trawl should range from 0.77-1.0 m/s and 8-15 minutes, respectively. A minimum of 1 trawl was conducted from the M/V Nerissa at each station using a 7.6 m wide, Marinovich, semi-balloon otter trawl (2.54 cm mesh) with a 0.64 cm mesh cod-end liner, an 8.9 m chain-rigged foot rope, and 23 m long trawl bridles following regionally adopted A-10 Methods methodology (Mearns and Allen 1978). The trawl wire scope varied from a ratio of approximately 5:1 at the shallowest stations to approximately 3:1 at the deepest station. To minimize catch variability due to weather and current conditions, which may affect the bottom-time duration of the trawl, trawls generally were taken along a constant depth at each station, and usually in the same direction. Station locations and trawling speeds and paths were determined using Global Positioning System navigation. Trawl depths were determined using a Sea-Bird Electronics SBE 39 pressure sensor attached to one of the trawl boards. Upon retrieval of the trawl net, the contents (fishes and EMIs) were emptied into a large flow-through water tank. Fishes were sorted by species into separate containers; EMIs were placed together in one or more containers. The identity of individual fish in each container was checked for sorting accuracy. Fish samples collected at Stations T1 and T11 were processed as follows: (1) up to 15 arbitrarily selected specimens of each species were weighed to the nearest gram and measured individually to the nearest millimeter (standard length for most species; total length for some species); and (2) if a trawl catch contained more than 15 individuals of a species, then the excess specimens were enumerated in 1 cm size classes and a bulk weight was recorded. Fish samples collected at the other stations were enumerated in 1 cm size classes and a bulk weight was recorded for each species. EMIs were sorted to species, counted, and batch weighed. For each invertebrate species with large abundances (n>100),100 individuals were counted and then batch weighed; the remaining individuals were batch weighed and enumerated later by back calculating using the weight of the first 100 individuals. EMI specimens that could not be identified in the field were preserved in 10% buffered formalin for subsequent taxonomic analysis in the laboratory. Laboratory Methods After 3-10 days in formalin, the EMI specimens retained for further taxonomic scrutiny were rinsed with tap water and then transferred to 70% ethanol for long-term preservation. These EMIs were identified using relevant taxonomic keys and, in some cases, were compared to voucher specimens housed in OCSD's Taxonomy Lab. Species and common names used in this report follow those given in Page et al. (2013) and Cadien and Lovell (2018). Data Analyses Total number of species, total abundance, biomass, H', and SDI were calculated for both fishes and EMIs at each station. Fish biointegrity in OCSD's monitoring area was assessed using the Fish Response Index (FRI). The FRI is a multivariate weighted-average index produced from an ordination analysis of calibrated species abundance data (Allen et al. 2001, 2006). FRI scores lower than 45 are classified as reference (normal) and those greater than 45 are non-reference (abnormal or disturbed). OCSD's historical trawl EMI and fish data from the past 10 monitoring periods, as well as Bight'13 trawl data (Walther et al. 2017), were also used as benchmarks. PRIMER v.7 (2015) multivariate statistical software was used to examine the spatial patterns of the fish and EMI assemblages at the 6 stations. Analyses included (1) hierarchical clustering with group-average linking based on Bray-Curtis similarity indices and SIMPROF permutation tests of the clusters and (2) ordination of the same data using nMDS to confirm hierarchical clustering. Prior to the calculation of the Bray-Curtis indices, the data were fourth root transformed in order to down-weight the highly abundant species and incorporate the importance of the less common species (Clarke and Warwick 2014). Middle Shelf Zone 2 stations were grouped into the following categories to assess spatial, outfall-related patterns: "outfall" (Stations T22 and T1) and "non-outfall" (Stations T23, T12, T17, and T11). A-11 Methods FISH TISSUE CONTAMINANTS MONITORING Two demersal fish species, English Sole (Parophrys vetulus) and Hornyhead Turbot (Pleuronichthys verticalis), were targeted for analysis of muscle and liver tissue chemistry. Muscle tissue was analyzed because contaminants may bioaccumulate in this tissue and can be transferred to higher trophic levels. Liver tissue was analyzed because it typically has higher lipid content than muscle tissue and thus bioaccumulates relatively higher concentrations of lipid-soluble contaminants that have been linked to pathological conditions as well as immunological or reproductive impairment (Arkoosh et al. 1998). Demersal fishes in the families Scorpaenidae (e.g., California Scorpionfish and Vermilion Rockfish) and Serranidae (e.g., Kelp Bass and Sand Bass) were also targeted, as they are frequently caught and consumed by recreational anglers. As such, contaminants in the muscle tissue of these fishes were analyzed to gauge human health risk. Field Methods The sampling objective for bioaccumulation analysis was to collect 10 individuals each of English Sole and Hornyhead Turbot at outfall (T1) and non-outfall (T11) stations during the 2018-19 monitoring period. Five hauls were conducted at each station in July 2018. Ten individuals in total of scorpaenid and serranid fishes were targeted at the outfall (Zone 1) and non-outfall (Zone 3) areas using hook-and-line fishing gear ("rig-fishing") in April and May 2019 (Figure 2-3). Each fish collected for bioaccumulation analysis was weighed to the nearest gram and its standard length measured to the nearest millimeter; placed in pre-labelled, plastic, re-sealable bags; and stored on wet ice in an insulated cooler. Bioaccumulation samples were subsequently transported under chain of custody protocols to OCSD's laboratory. Sample storage and holding times for bioaccumulation analyses followed specifications in OCSD's LMC SOP (OCSD 2016; Table A-5). Laboratory Methods Individual fish were dissected in the laboratory under clean conditions. Muscle and liver tissues were analyzed for various parameters listed in Table A-6 using methods shown in Table A-5. Method blanks, analytical quality control samples (duplicates, matrix spikes, and blank spikes), and standard reference materials were prepared and analyzed with each sample batch. All reported concentrations are on a wet weight basis. 7_DDT and ZPCB were calculated as described in the sediment geochemistry section. Total chlordane (7-Chlordane) represents the sum of 7 derivative compounds (cis- and trans-chlordane, cis- and trans-nonachlor, heptachlor, heptachlor epoxide, and oxychlordane). Organic contaminant data were not lipid normalized. Data Analyses All analytes that were undetected (i.e., value below the method detection limit) are reported as ND. Further, an ND value was treated as zero for calculating a mean analyte concentration; however, if fish tissue samples had all ND for a particular analyte, then the mean analyte concentration is reported as ND. Data analysis consisted of summary statistics (i.e., means and ranges) and qualitative comparisons only. The U.S. Food and Drug Administration action levels and the State of California Office of Environmental Health Hazard Assessment advisory tissue levels for 7-DDT, 7-PCB, methylmercury, dieldrin and 7-Chlordane were used to assess human health risk in rig-caught fish (Klasing and Brodberg 2008, FDA 2011). A-12 Methods Table A-5 Fish tissue handling and analysis summary during 2018-19. Parameter Container Preservation Holding Time Method Arsenic and Selenium Ziplock bag Freeze 6 months LMC SOP 200.86 SED Rev.F Organochlorine Pesticides Ziplock bag Freeze 6 months NS&T(NOAA 1993);EPA 8270 DDTs Ziplock bag Freeze 6 months NS&T(NOAA 1993);EPA 8270 Lipids Ziplock bag Freeze N/A EPA 9071* Mercury Ziplock bag Freeze 6 months LMC SOP 245.1 B Rev.G Polychlorinated Biphenyls Ziplock bag Freeze 6 months NS&T(NOAA 1993);EPA 8270 Available online at www.epa.gov;N/A=Not Applicable. Table A-6 Parameters measured in fish tissue samples during 2018-19. Metals Arsenic* Mercury Selenium Organochlorine Pesticides Chlordane Derivatives and Dieldrin cis-Chlordane Dieldrin cis-Nonachlor trans-Chlordane Heptachlor trans-Nonachlor Oxychlordane Heptachlor epoxide DDT Derivatives 2,4'-DDD 2,4'-DDE 2,4'-DDT 4,4'-DDD 4,4'-DDE 4,4'-DDT 4,4'-DDMU Polychlorinated Biphenyl(PCB)Congeners PCB 18 PCB 101 PCB 156 PCB 28 PCB 105 PCB 157 PCB 37 PCB 110 PCB 167 PCB 44 PCB 114 PCB 169 PCB 49 PCB 118 PCB 170 PCB 52 PCB 119 PCB 177 PCB 66 PCB 123 PCB 180 PCB 70 PCB 126 PCB 183 PCB 74 PCB 128 PCB 187 PCB 77 PCB 138 PCB 189 PCB 81 PCB 149 PCB 194 PCB 87 PCB 151 PCB 201 PCB 99 PCB 153/168 PCB 206 Other Parameter Lipids *Analyzed only in rig-fish specimens. FISH HEALTH MONITORING Assessment of the overall health of fish populations is also required by the NPDES permit. This entails documenting physical symptoms of disease in fish samples collected during each monitoring period, as well as conducting liver histopathology analysis once every 5 years (starting from June 15, 2012, the issue date of the current NPDES permit). Field Methods All trawl fish samples collected during the 2018-19 monitoring period were visually inspected for lesions, tumors, large, non-mobile external parasites, and other signs (e.g., skeletal deformities) of disease. Any atypical odor and coloration of fish samples were also noted. No fish samples were collected for liver histopathology analysis, as this analysis was conducted during the 2015-16 monitoring period (OCSD 2017). Data Analyses Analysis of fish disease data consisted of qualitative comparisons only. A-13 Methods REFERENCES Allen, L.G., D.J. Pondella II, and M.H. Horn, Eds. 2006. The Ecology of Marine Fishes: California and Adjacent Waters. University of California Press, Berkeley, CA. 660 p. Allen, M.J., R.W. Smith, and V. Raco-Rands. 2001. Development of Biointegrity Indices for Marine Demersal Fish and Megabenthic Invertebrate Assemblages of Southern California. Prepared for United States Environmental Protection Agency, Office of Science and Technology, Washington, DC. Southern California Coastal Water Research Project, Westminster, CA. APHA (American Public Health Association, American Water Works Association, and Water Environment Federation). 2012. Standard Methods for the Examination of Water and Wastewater, 22nd edition. American Public Health Association, Washington, D.C. Arkoosh, M.R., E. Casillas, P.A. Huffman, E.R. Clemons, J. Evered, J.E. Stein, and U. Varanasi. 1998. Increased susceptibility of juvenile Chinook salmon from a contaminated estuary to Vibrio anguillarum. Trans.Am. Fish. Soc. 127:360-374. Bay, S.M., D.J. Greenstein, J.A. Ranasinghe, D.W. Diehl, and A.E. Fetscher. 2009. Sediment Quality Assessment Draft Technical Support Manual. Technical Report Number 582. Southern California Coastal Water Research Project, Costa Mesa, CA. Cadien, D.B. and L.L. Lovell, Eds. 2018. A Taxonomic Listing of Benthic Macro- and Megainvertebrates from Infaunal and Epifaunal Monitoring and Research Programs in the Southern California Bight. Edition 12. The Southern California Association of Marine Invertebrate Taxonomists, Los Angeles, CA. 167 p. Clarke K.R. and R.M. Warwick. 2014. Change in Marine Communities:An Approach to Statistical Analysis and Interpretation: 31 edition. Plymouth Marine Laboratory, Plymouth, United Kingdom. 262 p. Dodder, N., K. Schiff, A. Latker, and C.L. Tang. 2016. Southern California Bight 2013 Regional Monitoring Program: IV. Sediment Chemistry. Southern California Coastal Water Research Project, Costa Mesa, CA. EPA (Environmental Protection Agency). 1994. Methods for Measuring the Toxicity and Bioaccumulation of Sediment-associated Contaminants with Estuarine and Marine Amphipods. EPA 600/R-94/025. FDA (Food and Drug Administration). 2011. Fish and Fishery Products Hazards and Controls Guidance: Fourth edition. Department of Health and Human Services, Silver Spring, MD. 468 p. Gillett, D.J., L.L. Lovell, and K.C. Schiff. 2017. Southern California Bight 2013 Regional Monitoring Program: Volume VI. Benthic Infauna. Southern California Coastal Water Research Project, Costa Mesa, CA. Hardy, J. 1993. Phytoplankton. In: Ecology of the Southern California Bight: A Synthesis and Interpretation (M.D. Dailey, D.J. Reish, and J.W. Anderson — Eds.). University of California Press, Berkeley, CA. p. 233-265. IGODS. 2012. IGODS (Interactive Graphical Ocean Database System)Version 3 Beta 4.41 [software]. Ocean Software and Environmental Consulting, Los Angeles, CA. Kelly, M., D. Diehl, B. Power, F. Stern, S. Walther, T. Petry, M. Mengel, K. Sakamoto, L. Terriquez, C. Cash, K. Patrick, E. Miller, B. Isham, B. Owens, M. Lyons, K. Schiff, S. Bay, L. Cooper, N. Dodder, D. Greenstein, S. Moore, and R. Wetzer. 2013. Southern California Bight 2013 Regional Monitoring Survey (Bight'13): Contaminant Impact Assessment Field Operations Manual. Southern California Coastal Water Research Project, Costa Mesa, CA. Klasing, S. and R. Brodberg. 2008. Development of Fish Contaminant Goals and Advisory Tissue Levels for Common Contaminants in California Sport Fish: Chlordane, DDTs, Dieldrin, Methylmercury, PCBs, Selenium, and Toxaphene. California Environmental Protection Agency, Oakland, CA. 115 p. Long, E.R. and D.D. MacDonald. 1998. Recommended uses of empirically derived, sediment quality guidelines for marine and estuarine ecosystems. Human and Ecol. Risk Assess. 4:1019-1039. Long, E.R., D.D. McDonald, S.L. Smith, and F.C. Calder. 1995. Incidence of adverse biological effects within ranges of chemical concentrations in marine and estuarine sediments. Environ. Manage. 19:81-97. A-14 Methods Long, E.R., L.J. Field, and D.D. MacDonald. 1998. Predicting toxicity in marine sediments with numerical sediment quality guidelines. Environ. Toxicol. Chem. 17:714-727. MATLAB. 2007. MATLAB Version 7.4 [software]. The Mathworks Inc., Natick, MA. Mearns, A.J. and M.J. Allen. 1978. Use of small otter trawls in coastal biological surveys. U.S. Environ. Prot. Agcy., Environ. Res. Lab. Corvallis, OR. EPA-600/3-78-083. Nezlin, N.P., J.A.T. Booth, C. Beegan, C.L. Cash, J.R. Gully, A. Latker, M.J. Mengel, G.L. Robertson, A. Steele, and S.B. Weisberg. 2016. Assessment of wastewater impact on dissolved oxygen around southern California's submerged ocean outfalls. Reg. Stud. Mar. Sci. 7:177-184. NOAA (National Oceanic and Atmospheric Administration). 1993. Sampling and Analytical Methods of the National Status and Trends Program National Benthic Surveillance and Mussel Watch Projects 1984- 1992: Overview and Summary of Methods, Volume I. NOAA Technical Memorandum NOS ORCA 71. Silver Spring, MD. OCSD (Orange County Sanitation District). 1999. Annual Report, July 1997-June 1998. Marine Monitoring. Fountain Valley, CA. OCSD. 2016. Laboratory, Monitoring, and Compliance Standard Operating Procedures. Fountain Valley, CA. OCSD. 2017.Annual Report, July 2015-June 2016. Marine Monitoring. Fountain Valley, CA. Officer, C.B. 1976. Physical Oceanography of Estuaries and Associated Coastal Waters. John Wiley, New York. 465 p. Page, L.M., H. Espinosa-Perez, L.T. Findley, C.R. Gilbert, R.N. Lea, N.E. Mandrak, R.L. Mayden, and J.S. Nelson. 2013. Common and Scientific Names of Fishes from the United States, Canada, and Mexico, 7th Edition.American Fisheries Society, Bethesda, MD. 243 p. Plumb, R.H. 1981. Procedures for handling and chemical analysis of sediment and water samples. Tech. Rep. EPA/CE-81-1. Prepared by U.S. army Corps of Engineers, Waterways Experiment Station, Vicksburg, MS. 478 p. PRIMER. 2015. PRIMER Statistical Software Package Version 7 [software]. Plymouth Marine Laboratory, Plymouth, UK. Ranasinghe, J.A., A.M. Barnett, K. Schiff, D.E. Montagne, C.A. Brantley, C. Beegan, D.B. Cadien, C. Cash, G.B. Deets, D.R. Diener, T.K. Mikel, R.W. Smith, R.G. Velarde, S.D. Watts, and S.B. Weisberg. 2007. Southern California Bight 2003 Regional Monitoring Program: III. Benthic Macrofauna. Southern California Coastal Water Research Project, Costa Mesa, CA. Ranasinghe, J.A., K.C. Schiff, C.A. Brantley, L.L. Lovell, D.B. Cadien, T.K. Mikel, R.G. Velarde, S. Holt, and S.C. Johnson. 2012. Southern California Bight 2008 Regional Monitoring Program: VI. Benthic Macrofauna. Southern California Coastal Water Research Project, Costa Mesa, CA. SEASOFT. 2017a. Seasoft CTD Data Acquisition Software, Version 7.26.6.26 [software]. Seabird Electronics, Inc., Bellevue, WA. SEASOFT. 2017b. Seasoft CTD Data Processing Software, Version 7.26.7.1 [software]. Seabird Electronics, Inc., Bellevue, WA. Smith, R.W., M. Bergen, S.B. Weisberg, D. Cadien, A. Dalkey, D. Montagne, J.K. Stull, and R.G. Velarde. 2001. Benthic response index for assessing infaunal communities on the southern California mainland shelf. Ecol.Appl. 11:1073-1087. Swartz, R.C. 1978. Techniques for sampling and analyzing the marine macrobenthos. U.S. Environmental Protection Agency (EPA), Doc. EPA-600/3-78-030, EPA, Corvallis, OR. SWRCB (State Water Resources Control Board, California Environmental Protection Agency). 2009. Water Quality Control Plan for Enclosed Bays and Estuaries— Part 1 Sediment Quality. Sacramento, CA. SWRCB. 2010. California Ocean Plan. Sacramento, CA. A-15 Methods Walther, S.M., J.P. Williams, A.K. Latker, D.B. Cadien, D.W. Diehl, K. Wisenbaker, E. Miller, R. Gartman, C. Stransky, and K.C. Schiff. 2017. Southern California Bight 2013 Regional Monitoring Program: Volume VII. Demersal Fishes and Megabenthic Invertebrates. Southern California Coastal Water Research Project, Costa Mesa, CA. Word, J. 1978. The infaunal trophic index. Southern California Coastal Water Research Project Annual Report, 1979. Southern California Coastal Water Research Project, Long Beach, CA. Word, J.Q. 1990. The Infaunal Trophic Index. A functional approach to benthic community analyses [dissertation]. University of Washington, Seattle, WA. 297 p. Zar, J.H. 1999. Biostatistical Analysis. Prentice-Hall Publishers, Upper Saddle River, NJ. 663 p. +Appendices. A-16 Table B-1 Percent of fecal indicator bacteria by quarter and depth strata for the 2018-19 REC-1 water quality surveys (5 surveys/quarter; 8 stations/survey). Total Coliforms Fecal Coliforms Enterococci Quarter Depth Strata n <10 10- 1,001- >10,000** <10 10-200 201 >400** <10 1035 36 >104** (m) 1,000 10,000* 400* 104 1-15 80 67.5% 28.8% 3.8% 0.0% 96.3% 2.5% 1.3% 0.0% 93.8% 3.8% 0.0% 2.5% 16-30 65 63.1% 32.3% 4.6% 0.0% 96.9% 3.1% 0.0% 0.0% 89.2% 9.2% 1.5% 0.0% Summer 31-45 20 60.0% 40.0% 0.0% 0.0% 90.0% 10.0% 0.0% 0.0% 90.0% 10.0% 0.0% 0.0% 46-60 30 66.7% 33.3% 0.0% 0.0% 93.3% 6.7% 0.0% 0.0% 90.0% 10.0% 0.0% 0.0% Water Column 195 65.1% 31.8% 3.1% 0.0% 95.4% 4.1% 0.5% 0.0% 91.3% 7.2% 0.5% 1.0% 1-15 79 58.8% 41.3% 0.0% 0.0% 90.0% 10.0% 0.0% 0.0% 90.0% 6.3% 1.3% 2.5% 16-30 65 56.9% 43.1% 0.0% 0.0% 90.8% 9.2% 0.0% 0.0% 92.3% 3.1% 4.6% 0.0% Fall 31-45 20 70.0% 30.0% 0.0% 0.0% 90.0% 10.0% 0.0% 0.0% 95.0% 5.0% 0.0% 0.0% 46-60 30 76.7% 23.3% 0.0% 0.0% 86.7% 13.3% 0.0% 0.0% 100.0% 0.0% 0.0% 0.0% Water Column 194 62.1% 37.9% 0.0% 0.0% 89.7% 10.3% 0.0% 0.0% 92.8% 4.1% 2.1% 1.0% 1-15 80 46.3% 53.8% 0.0% 0.0% 87.5% 12.5% 0.0% 0.0% 86.3% 11.3% 1.3% 1.3% 16-30 65 49.2% 50.8% 0.0% 0.0% 81.5% 18.5% 0.0% 0.0% 92.3% 7.7% 0.0% 0.0% Winter 31-45 20 30.0% 70.0% 0.0% 0.0% 55.0% 45.0% 0.0% 0.0% 70.0% 25.0% 5.0% 0.0% 46-60 30 40.0% 53.3% 6.7% 0.0% 63.3% 30.0% 0.0% 6.7% 73.3% 16.7% 3.3% 6.7% Water Column 195 44.6% 54.4% 1.0% 0.0% 78.5% 20.5% 0.0% 1.0% 84.6% 12.3% 1.5% 1.5% 1-15 80 93.7% 6.3% 0.0% 0.0% 100.0% 0.0% 0.0% 0.0% 87.3% 12.7% 0.0% 0.0% 16-30 65 61.5% 36.9% 1.5% 0.0% 83.1% 15.4% 0.0% 1.5% 877% 7.7% 4.6% 0.0% Spring 31-45 20 45.0% 50.0% 5.0% 0.0% 60.0% 35.0% 0.0% 5.0% 85.0% 5.0% 10.0% 0.0% 46-60 30 53.3% 46.7% 0.0% 0.0% 73.3% 26.7% 0.0% 0.0% 83.3% 10.0% 6.7% 0.0% Water Column 195 71.6% 27.3% 1.0% 0.0% 86.1% 12.9% 0.0% 1.0% 86.6% 9.8% 3.6% 0.0% 1-15 80 66.5% 32.6% 0.9% 0.0% 93.4% 6.3% 0.3% 0.0% 89.3% 8.5% 0.6% 1.6% 16-30 65 57.7% 40.8% 1.5% 0.0% 88.1% 11.5% 0.0% 0.4% 90.4% 6.9% 2.7% 0.0% Annual 31-45 20 51.3% 47.5% 1.3% 0.0% 73.8% 25.0% 0.0% 1.3% 85.0% 11.3% 3.8% 0.0% 46-60 30 59.2% 39.2% 1.7% 0.0% 79.2% 19.2% 0.0% 1.7% 86.7% 9.2% 2.5% 1.7% Water Column 195 60.8% 37.9% 1.3% 0.0% 87.4% 11.9% 0.1% 0.5% 88.8% 8.3% 1.9% 0.9% 'Geomean; "Single sample. Cn D T o rn Z c� vX � vo Supporting Data Table B-2 Depth-averaged total coliform bacteria (MPN/100 mL) collected in offshore waters and used for comparison with California Ocean Plan Water-Contact (REC-1) Standards, July 2018 through June 2019. Meets 30-day Meets Single Meets Single Station Date Geometric Mean Sample Standard Sample Standard of<-1,000/100 mL of<_10,000/100 mL of 51,000/100 mL 711012018 711112018 711212018 81612018 81712018 2103 <10 <10 <10 33 52 YES YES YES 2104 <10 <10 10 17 66 YES YES YES 2183 10 <10 <10 <10 138 YES YES YES 2203 <10 <10 <10 81 156 YES YES YES 2223 <10 <10 <10 <10 <10 YES YES YES 2303 <10 <10 <10 130 251 YES YES YES 2351 <10 <10 <10 1216 512 YES YES YES 2403 <10 <10 <10 778 159 YES YES YES 1011612018 1011712018 1011812018 111512018 111612018 2103 <10 15 12 <10 <10 YES YES YES 2104 <10 <10 <10 <10 <10 YES YES YES 2183 14 22 13 <10 <10 YES YES YES 2203 19 11 14 <10 <10 YES YES YES 2223 94 13 18 <10 <10 YES YES YES 2303 69 11 31 <10 15 YES YES YES 2351 113 38 72 <10 <10 YES YES YES 2403 316 178 29 <10 <10 YES YES YES 112312019 112412019 2/6/2019 21712019 2/19/2019 2103 16 18 17 21 16 YES YES YES 2104 93 61 31 17 62** YES YES YES** 2183 36 17 40 29 27 YES YES YES 2203 <10 <10 60 74 <10 YES YES YES 2223 <10 <10 134 40 <10 YES YES YES 2303 <10 <10 54 45 <10 YES YES YES 2351 <10 <10 127 58 <10 YES YES YES 2403 <10 <10 235 38 <10 YES YES YES 412312019 412412019 4/25/2019 51612019 51812019 2103 10 <10 <10 56 54** YES YES YES** 2104 13 <10 12 21 118** YES YES YES** 2183 <10 <10 <10 14 39 YES YES YES 2203 <10 <10 <10 11 16 YES YES YES 2223 <10 <10 <10 <10 10 YES YES YES 2303 <10 <10 <10 <10 <10 YES YES YES 2351 <10 <10 <10 <10 <10 YES YES YES 2403 <10 <10 <10 <10 <10 YES YES YES Standard is based on when the single sample maximum fecal coliform/total coliform ratio>0.1. Depths combined,meet single sample standard(2/19/19,5/8/19). B-2 Supporting Data Table B-3 Depth-averaged fecal coliform bacteria (MPN/100 mL) collected in offshore waters and used for comparison with California Ocean Plan Water-Contact (REC-1) Standards, July 2018 through June 2019. Meets 30-day Meets single sample Station Date Geometric Mean standard 5200/100 mL of 5400/100 mL 711012018 711112018 711212018 8/6/2018 81712018 2103 <10 <10 <10 <10 <10 YES YES 2104 <10 <10 <10 <10 <10 YES YES 2183 <10 <10 <10 <10 <10 YES YES 2203 <10 <10 <10 <10 <10 YES YES 2223 <10 <10 <10 <10 <10 YES YES 2303 <10 <10 <10 <10 11 YES YES 2351 <10 <10 <10 <10 <10 YES YES 2403 <10 <10 <10 <10 24 YES YES 1011612018 1011712018 1011812018 111512018 111612018 2103 <10 <10 <10 <10 <10 YES YES 2104 <10 <10 <10 <10 <10 YES YES 2183 <10 <10 10 <10 <10 YES YES 2203 <10 <10 <10 <10 <10 YES YES 2223 <10 <10 <10 <10 <10 YES YES 2303 18 <10 <10 <10 <10 YES YES 2351 14 11 <10 <10 <10 YES YES 2403 28 <10 <10 <10 <10 YES YES 112312019 112412019 21612019 21712019 2/19/2019 2103 10 10 <10 <10 <10 YES YES 2104 35 17 <10 <10 26* YES YES* 2183 17 10 <10 <10 <10 YES YES 2203 <10 <10 14 <10 <10 YES YES 2223 <10 <10 10 <10 <10 YES YES 2303 <10 <10 <10 <10 <10 YES YES 2351 <10 <10 <10 <10 <10 YES YES 2403 <10 <10 11 <10 <10 YES YES 4/23/2019 412412019 412512019 5/6/2019 5/8/2019 2103 <10 <10 <10 15 16* YES YES* 2104 10 <10 <10 <10 42* YES YES* 2183 <10 <10 <10 <10 21 YES YES 2203 <10 <10 <10 <10 <10 YES YES 2223 <10 <10 <10 <10 <10 YES YES 2303 <10 <10 <10 <10 <10 YES YES 2351 <10 <10 <10 <10 <10 YES YES 2403 <10 <10 <10 <10 <10 YES YES Depths combined,meet single sample standard(2/19/19,5/8/19). B-3 Supporting Data Table B-4 Depth-averaged enterococci bacteria (MPN/100 mL) collected in offshore waters and used for comparison with California Ocean Plan Water-Contact (REC-1) Standards and EPA Primary Recreation Criteria in Federal Waters, July 2018 through June 2019. Meets COP Meets COP Meets EPA 30-day single sample single sample Station Date Geometric standard of standard of Mean of :5104/100 mL :5501/100 mL :535/100 mL 711012018 711112018 711212018 81612018 8/7/2018 2103 <10 <10 <10 <10 <10 YES YES YES 2104 <10 11 <10 17** <10 YES YES** YES** 2183 <10 <10 <10 <10 <10 YES YES YES 2203 <10 <10 <10 <10 <10 YES YES YES 2223 <10 <10 <10 <10 <10 YES YES YES 2303 <10 <10 <10 <10 <10 YES YES YES 2351 21** <10 <10 <10 <10 YES YES** YES 2403 <10 <10 <10 <10 <10 YES YES YES 1011612018 1011712018 1011812018 111512018 111612018 2103 <10 <10 <10 <10 10 YES YES YES 2104 <10 <10 <10 <10 <10 YES YES YES 2183 <10 <10 <10 <10 <10 YES YES YES 2203 <10 <10 15 <10 <10 YES YES YES 2223 <10 <10 12 <10 <10 YES YES YES 2303 20** <10 16 14 <10 YES YES** YES 2351 <10 <10 <10 10 <10 YES YES YES 2403 <10 <10 25** <10 <10 YES YES** YES 1/23/2019 112412019 Z16/2019 21712019 211912019 2103 <10 <10 <10 <10 <10 YES YES YES 2104 12 <10 <10 <10 17** YES YES** YES 2183 <10 <10 10 <10 10 YES YES YES 2203 <10 13 10 <10 <10 YES YES YES 2223 <10 <10 <10 <10 <10 YES YES YES 2303 <10 <10 <10 <10 <10 YES YES YES 2351 <10 <10 <10 <10 <10 YES YES YES 2403 <10 32** 10 <10 <10 YES YES** YES** 4/23/2019 412412019 4/25/2019 5/6/2019 5/8/2019 2103 <10 10 <10 <10 11 YES YES YES 2104 <10 <10 <10 <10 21 YES YES YES 2183 <10 10 <10 <10 <10 YES YES YES 2203 <10 <10 <10 <10 10 YES YES YES 2223 10 <10 <10 <10 <10 YES YES YES 2303 <10 <10 <10 <10 <10 YES YES YES 2351 <10 <10 <10 <10 <10 YES YES YES 2403 <10 <10 <10 <10 <10 YES YES YES Standard is based on area of infrequent use. **Depths combined,meet single sample standard(7/10/18,8/6/18,10/16/18,10/18/18,1/24/19,2/19/19). B-4 Supporting Data Table B-5 Summary of floatable material by station group observed during the 28-station grid water quality surveys, July 2018 through June 2019. Total number of station visits = 336. Station Group Upcoast Upcoast Infield Within-ZID Infield Downcoast Downcoast Offshore Inshore Offshore Inshore Offshore Inshore Surface Observation Totals 2225,2226 2223,2224 2305,2306 2303,2304 2206 2205 2203,2204 2105,2106 2103,2104 2353,2354 2351,2352 2185,2186 2183,2184 2405,2406 2403,2404 Oil and Grease 0 0 0 0 0 0 0 0 Trash/Debris 0 2 0 0 0 0 1 3 Biological Material(kelp) 1 1 0 0 0 0 0 2 Material of Sewage Origin 0 0 0 0 0 0 0 0 Totals 1 3 0 0 0 0 1 5 Table B-6 Summary of floatable material by station group observed during the REC-1 water quality surveys, July 2018 through June 2019. Total number of station visits = 108. Station Group Surface Observation Upcoast Inshore Within-ZID Infield Downcoast Inshore Inshore Totals 2223,2303 2103,2104, 2351,2403 2205 2203 2183 Oil and Grease 0 0 0 0 0 Trash/Debris 1 0 0 0 1 Biological Material(kelp) 4 1 0 1 6 Material of Sewage Origin 0 0 0 0 0 Totals 5 1 0 1 7 B-5 Table B-7 Summary of Core water quality compliance parameters by quarter and depth strata for 2018-19 (3 surveys/quarter; N c 28 stations/survey). 0 Quarter Depth Strata Dissolved Oxygen(mg/L) pH Light Transmissivity (m) Minimum Mean Maximum Std.Dev. Minimum Mean Maximum Std.Dev. Minimum Mean Maximum Std.Dev. 1-15 5.64 7.86 11.23 0.70 7.96 8.05 8.16 0.05 55.18 84.73 87.73 3.06 16-30 5.20 8.04 11.40 0.69 7.65 7.98 8.18 0.07 50.51 82.40 87.85 5.86 31-45 4.24 6.74 8.37 1.14 7.54 7.83 7.98 0.12 74.10 85.35 87.78 1.68 Summer 46-60 3.79 5.79 7.62 1.00 7.47 7.72 7.91 0.12 81.25 86.41 88.63 1.72 61-75 3.87 5.22 6.99 0.73 7.47 7.65 7.85 0.10 82.13 86.85 88.86 1.85 Water Column 3.79 7.09 11.40 1.34 7.47 7.90 8.18 0.17 50.51 84.73 88.86 3.93 1-15 7.05 7.50 8.29 0.31 7.89 7.95 8.01 0.03 71.26 85.53 88.21 3.32 16-30 7.07 7.58 8.32 0.27 7.82 7.92 7.98 0.03 75.45 85.56 88.22 2.93 Fall 31-45 6.42 7.33 8.12 0.32 7.76 7.87 7.95 0.04 81.58 86.33 88.19 1.19 46-60 6.19 6.95 7.86 0.42 7.74 7.81 7.91 0.04 81.29 86.70 88.56 1.02 61-75 5.73 6.55 7.45 0.44 7.69 7.76 7.85 0.03 83.06 87.17 88.68 1.28 Water Column 5.73 7.30 8.32 0.48 7.69 7.89 8.01 0.07 71.26 86.04 88.68 2.55 1-15 6.56 7.82 8.50 0.27 7.83 7.95 8.02 0.03 25.44 80.06 86.19 6.54 16-30 5.30 7.31 8.16 0.51 7.73 7.90 7.98 0.05 66.69 83.66 88.04 2.36 Winter 31-45 4.67 6.49 7.82 0.89 7.62 7.83 7.97 0.10 81.13 85.68 88.89 1.50 46-60 4.15 5.56 7.52 0.81 7.56 7.72 7.94 0.09 82.09 87.17 89.33 1.86 61-75 3.76 4.93 6.35 0.71 7.52 7.65 7.80 0.08 79.21 87.23 89.40 2.52 Water Column 3.76 6.78 8.50 1.19 7.52 7.85 8.02 0.13 25.44 83.89 89.40 4.86 1-15 4.05 8.15 9.89 1.00 7.59 7.99 8.26 0.13 57.92 76.56 85.71 4.95 16-30 3.89 5.63 8.71 1.05 7.49 7.72 8.03 0.13 69.51 81.18 87.50 3.63 Spring 31-45 3.72 4.48 6.40 0.45 7.45 7.60 7.82 0.08 70.99 84.77 88.38 2.40 46-60 3.37 4.13 5.08 0.33 7.41 7.56 7.69 0.07 80.97 86.14 88.48 1.51 i 61-75 3.32 3.88 4.72 0.27 7.39 7.52 7.66 0.06 74.97 86.57 89.05 1.72 Water Column 3.32 5.75 9.89 1.85 7.39 7.73 8.26 0.21 57.92 81.80 89.05 5.26 1-15 4.05 7.83 11.23 0.68 7.59 7.98 8.26 0.08 25.44 81.72 88.21 5.93 16-30 3.89 7.14 11.40 1.14 7.49 7.88 8.18 0.12 50.51 83.20 88.22 4.25 Annual 3145 3.72 6.26 8.37 1.32 7.45 7.78 7.98 0.14 70.99 85.53 88.89 1.84 46-60 3.37 5.61 7.86 1.22 7.41 7.70 7.94 0.13 80.97 86.61 89.33 1.61 61-75 3.32 5.13 7.45 1.10 7.39 7.65 7.85 0.11 74.97 86.96 89.40 1.92 Water Column 3.32 6.73 11.40 1.44 7.39 7.84 8.26 0.17 25.44 84.11 89.40 4.55 Supporting Data Table B-8 Summary of Core water quality ammonium (mg/L) receiving water criteria by quarter and depth strata for 2018-19 (3 surveys/quarter; 22 stations/survey). Quarter Depth Stratan <MDL* MDL-3.9 4-5.9** >6*** 1-15 180 83.3% 16.7% 0.0% 0.0% 16-30 169 77.5% 22.5% 0.0% 0.0% Summer 31-45 55 76.4% 23.6% 0.0% 0.0% 46-60 96 71.9% 28.1% 0.0% 0.0% Water Column 500 78.4% 21.6% 0.0% 0.0% 1-15 183 76.0% 24.0% 0.0% 0.0% 16-30 153 80.4% 19.6% 0.0% 0.0% Fall 31-45 60 65.0% 35.0% 0.0% 0.0% 46-60 106 54.7% 45.3% 0.0% 0.0% Water Column 502 71.5% 28.5% 0.0% 0.0% 1-15 138 86.2% 13.8% 0.0% 0.0% 16-30 142 77.5% 22.5% 0.0% 0.0% Winter 31-45 52 80.8% 19.2% 0.0% 0.0% 46-60 91 73.6% 26.4% 0.0% 0.0% Water Column 423 79.9% 20.1% 0.0% 0.0% 1-15 150 100.0% 0.0% 0.0% 0.0% 16-30 134 92.5% 7.5% 0.0% 0.0% Spring 31-45 52 69.2% 30.8% 0.0% 0.0% 46-60 78 85.9% 14.1% 0.0% 0.0% Water Column 414 91.1% 8.9% 0.0% 0.0% 1-15 651 85.7% 14.3% 0.0% 0.0% 16-30 598 81.6% 18.4% 0.0% 0.0% Annual 31-45 219 72.6% 27.4% 0.0% 0.0% 46-60 371 70.4% 29.6% 0.0% 0.0% Water Column 1839 79.7% 20.3% 0.0% 0.0% MDL range 0.014-0.04;**COP chronic crteria;***COP acute criteria. Table B-9 Species richness and abundance values of the major taxonomic groups collected in the Middle Shelf Zone 2 stratum (51-90 m) for the 2018-19 infauna surveys. Values represent the mean and range (in parentheses). Quarter Parameter Area Annelida Arthropoda Echinodermata Misc.Phyla Mollusca Number of Within-ZID 52(43-62) 19(13-23) 5(2-9) 6(3-13) 7(4-12) Summer Species Non-ZID 52(39-63) 18(9-26) 5(2-8) 6(3-12) 9(5-15) Within-ZID 223(148-313) 52(41-66) 12(5-25) 8(3-22) 19(6-37) Abundance Non-ZID 258(158-394) 58(30-133) 14(6-28) 14(3-26) 21 (10-32) Number of Within-ZID 53(52-55) 16(10-20) 4(3-6) 11(9-14) 6(1-10) Winter Species Non-ZID 57(31-73) 16(8-27) 3(0-6) 9(3-13) 7(2-13) Abundance Within-ZID 309(187-407) 42(31-55) 6(3-10) 17(11-24) 12(1-18) Non-ZID 377(171-638) 51 (15-107) 7(0-19) 15(7-32) 13(3-22) B-7 Table B-10 Abundance and species richness of epibenthic macroinvertebrates by station and species for the Summer 2018 and c Winter 2019 trawl surveys. 0 Station T23 T22 T1 T12 T17 T11 rt Nominal Depth 58 60 55 57 60 60 to Quarter S W S W S W S W S W S W Total % Ophiura luetkenii 18 64 12 46 482 980 3982 8 1484 969 8045 59.1 M. Lytechinus pictus 645 1194 405 196 86 64 67 14 129 8 1 2809 20.6 Sicyonia penicillata 12 18 1 10 10 816 36 903 6.6 Thesea sp B 21 60 16 42 67 176 27 94 5 34 31 78 651 4.8 Hamatoscalpellum californicum 10 12 2 4 11 30 5 126 24 49 53 326 2.4 Pleuroncodes planipes 4 322 326 2.4 Sicyonia ingentis 4 20 17 16 48 12 42 12 30 201 1.5 Astropecten californicus 7 24 3 28 12 50 19 36 10 1 4 194 1.4 Luidia foliolata 2 2 2 4 3 4 6 4 2 2 1 32 0.2 Ophiothrix spiculata 4 7 10 1 1 9 32 0.2 Luidia asthenosoma 3 10 2 2 1 1 2 21 0.2 Heterogorgia tortuosa 1 1 1 6 1 10 0.1 Pleurobranchaea californica 1 4 1 4 10 0.1 Octopus rubescens 2 2 2 1 1 8 0.1 Strongylocentrotus fragilis 5 3 8 0.1 Acanthoptilum sp 4 1 5 <0.1 Pyromaia tuberculata 2 1 3 <0.1 Rossia pacifica 2 1 3 <0.1 Apostichopus californicus 1 1 2 <0.1 Coryrhynchus lobifrons 2 2 <0.1 W Doryteuthis opalescens 2 2 <0.1 Flabellinopsis iodinea 1 1 2 <0.1 Lamellaria diegoensis 2 2 <0.1 Megasurcula carpenteriana 2 2 <0.1 Neverita draconis 2 2 <0.1 Paguristes baked 2 2 <0.1 Philine auriformis 1 1 2 <0.1 Simnia sp 2 2 <0.1 Baptodoris mimetica 1 1 <0.1 Calliostoma turbinum 1 1 <0.1 Ericerodes hemphillii 1 1 <0.1 Muricidae 1 1 <0.1 Orthopagurus minimus 1 1 <0.1 Stylasterias forreri 1 1 <0.1 Tritonia festiva 1 1 <0.1 Total Abundance 708 1392 456 372 208 1170 1155 4284 188 898 1620 1163 13614 100 Total No.of Species 9 14 13 13 12 12 10 9 6 7 17 17 35 Table B-11 Biomass (kg) of epibenthic macroinvertebrates by station and species for the Summer 2018 and Winter 2019 trawl surveys. Station T23 T22 T1 T12 T17 T11 Nominal Depth 58 60 55 57 60 60 Quarter S W S W S W S W S W S W Total % Sicyonia penicillata 0.154 0.270 0.019 0.112 0.116 10.620 0.693 11.984 33.8 Ophiura luetkenii 0.010 0.040 0.004 0.028 0.650 1.500 5.296 0.002 1.900 0.998 10.428 29.4 Lytechinus pictus 1.310 2.006 0.830 0.360 0.205 0.098 0.153 0.022 0.273 0.020 0.001 5.278 14.9 Pleuroncodes planipes 0.050 3.696 3.746 10.6 Apostichopus californicus 0.545 0.903 1.448 4.1 Thesea sp B 0.015 0.070 0.011 0.032 0.095 0.210 0.025 0.114 0.003 0.030 0.029 0.060 0.694 2.0 Sicyonia ingentis 0.002 0.018 0.053 0.028 0.163 0.002 0.263 0.008 0.103 0.640 1.8 Astropecten californicus 0.010 0.030 0.010 0.066 0.026 0.162 0.105 0.096 0.039 0.002 0.004 0.550 1.6 Octopus rubescens 0.080 0.020 0.110 0.006 0.009 0.225 0.6 Pleurobranchaea californica 0.011 0.028 0.020 0.140 0.199 0.6 Luidia foliolata 0.002 0.002 0.001 0.002 0.025 0.002 0.012 0.002 0.002 0.017 0.001 0.068 0.2 Luidia asthenosoma 0.011 0.014 0.012 0.002 0.011 0.002 0.001 0.053 0.1 Hamatoscalpellum californicum 0.003 0.002 0.001 0.002 0.006 0.002 0.001 0.008 0.002 0.009 0.002 0.038 0.1 Strongylocentrotus fragilis 0.011 0.014 0.025 0.1 Ophiothrix spiculata 0.002 0.007 0.006 0.001 0.001 0.001 0.018 0.1 Rossia pacifica 0.002 0.014 0.016 <0.1 Megasurcula carpenteriana 0.008 0.008 <0.1 Heterogorgia tortuosa 0.001 0.001 0.001 0.002 0.001 0.006 <0.1 Muricidae 0.005 0.005 <0.1 Paguristes baked 0.004 0.004 <0.1 W Acanthoptilum sp 0.002 0.001 0.003 <0.1 C4 Pyromaia tuberculata 0.002 0.001 0.003 <0.1 Doryteuthis opalescens 0.002 0.002 <0.1 Flabellinopsis iodinea 0.001 0.001 0.002 <0.1 Neverita draconis 0.002 0.002 <0.1 Philine auriformis 0.001 0.001 0.002 <0.1 Simnia sp 0.002 0.002 <0.1 Stylasterias forred 0.002 0.002 <0.1 Baptodoris mimetica 0.001 0.001 <0.1 Calliostoma turbinum 0.001 0.001 <0.1 Coryrhynchus lobifrons 0.001 0.001 <0.1 Ericerodes hemphillii 0.001 0.001 <0.1 Lamellaria diegoensis 0.001 0.001 <0.1 Orthopagurus minimus 0.001 0.001 <0.1 Tritonia festiva 0.001 0.001 <0.1 Total 1.373 2.408 0.944 0.944 0.989 4.972 1.980 5.658 0.599 10.672 3.145 1.774 35.458 100 Cn O to v sv rt !y Table B-12 Abundance and species richness of demersal fishes by station and species for the Summer 2018 and Winter 2019 trawl c surveys. 0 Station T23 T22 T1 T12 T17 T11 rt Nominal Depth 58 60 55 57 60 60 tQ Quarter S W S W S W S W S W S W Total % p Sebastes semicinctus 2 4 1 7 2 9 3 6 15 2189 2238 27.8 rt Citharichthys sordidus 202 232 248 210 208 132 94 141 59 134 105 129 1894 23.5 Zaniolepis latipinnis 101 57 13 33 18 94 81 127 35 410 19 131 1119 13.9 Icelinus quadriseriatus 8 26 47 80 159 87 149 4 55 9 151 8 783 9.7 Symphurus atricaudus 18 67 18 42 26 61 10 53 7 124 6 129 561 7.0 Zalembius rosaceus 18 30 15 130 34 4 18 4 62 4 56 375 4.7 Parophrys vetulus 5 15 5 3 1 20 2 51 3 14 10 31 160 2.0 Chitonotus pugetensis 9 22 26 9 41 7 24 11 1 150 1.9 Synodus lucioceps 15 15 9 2 18 40 17 6 3 18 4 147 1.8 Citharichthys xanthostigma 5 10 1 1 42 36 20 1 18 10 144 1.8 Microstomus pacificus 4 19 14 18 1 1 6 19 15 16 4 11 128 1.6 Hippoglossina stomata 2 39 5 22 3 23 1 16 1 9 121 1.5 Pleuronichthys verticalis 4 12 4 7 4 3 12 3 13 19 81 1.0 Porichthys notatus 7 2 1 1 9 2 20 1 43 0.5 Sebastes saxicola 25 25 0.3 Scorpaena guttata 1 2 3 2 1 8 17 0.2 Odontopyxis trispinosa 1 1 1 2 1 1 3 10 0.1 Genyonemus lineatus 5 3 1 9 0.1 Lycodes pacificus 1 7 8 0.1 Zaniolepis frenata 3 2 2 1 8 0.1 W Sebastes sp 1 3 4 <0.1 Argentina sialis 3 3 <0.1 O Sebastes hopkinsi 3 3 <0.1 Citharichthys stigmaeus 1 1 2 <0.1 Lyopsetta exilis 2 2 <0.1 Paralichthys californicus 1 1 2 <0.1 Sebastes miniatus 1 1 2 <0.1 Xystreurys liolepis 1 1 2 <0.1 Ophiodon elongatus 1 1 <0.1 Paralabrax clathratus 1 1 <0.1 Podothecus accipenserinus 1 1 <0.1 Porichthys mynaster 1 1 <0.1 Raja inornata 1 1 <0.1 Scomber japonicus 1 1 <0.1 Sebastes dallii 1 1 <0.1 Sebastes jordani 1 1 <0.1 Squatina californica 1 1 <0.1 Total Abundance 395 540 411 561 506 550 428 485 262 835 341 2736 8050 100 Total No.of Species 15 17 17 16 13 18 17 19 14 17 13 20 37 Table B-13 Biomass (kg) of demersal fishes by station and species for the Summer 2018 and Winter 2019 trawl surveys. Station T23 T22 T1 T12 T17 T71 Nominal Depth 58 60 55 57 60 60 Quarter S W S W S W S W S W S W Total % Citharichthys sordidus 17.720 10.910 5.596 3.210 1.057 3.378 0.418 2.810 0.778 1.333 1.583 6.840 55.633 30.0 Sebastes semicinctus 0.003 0.118 0.002 0.053 0.005 0.016 0.014 0.007 0.150 38.597 38.965 21.0 Zaniolepis latipinnis 2.073 1.048 0.075 0.598 0.138 1.977 1.348 0.900 0.288 3.095 0.316 2.384 14.240 7.7 Parophrys vetulus 0.548 1.500 0.898 0.358 0.062 1.850 0.228 3.300 0.098 0.688 1.020 1.698 12.248 6.6 Squatina californica 9.500 9.500 5.1 Citharichthys xanthostigma 0.598 0.694 0.065 0.029 2.350 0.989 1.328 0.160 1.648 0.903 8.764 4.7 Symphurus atricaudus 0.298 0.948 0.298 0.613 0.441 0.970 0.188 0.868 0.143 1.748 0.098 1.924 8.537 4.6 Synodus lucioceps 1.098 0.673 0.673 0.098 1.110 0.783 0.455 0.048 0.096 0.370 0.204 5.608 3.0 Pleuronichthys verticalis 0.648 0.574 0.393 0.318 0.240 0.428 0.850 0.128 0.530 0.853 4.962 2.7 Hippoglossina stomata 0.088 1.348 0.318 0.948 0.027 0.591 0.008 0.460 0.063 0.669 4.520 2.4 Zalembius rosaceus 0.428 0.268 0.648 0.673 0.822 0.173 0.033 0.188 0.228 0.160 0.302 3.923 2.1 Microstomus pacificus 0.238 0.518 0.948 0.594 0.083 0.052 0.048 0.498 0.173 0.290 0.020 0.262 3.724 2.0 Icelinus quadriseriatus 0.048 0.096 0.203 0.298 0.582 0.284 0.568 0.010 0.218 0.007 0.540 0.016 2.870 1.5 Scorpaena guttata 0.088 0.120 0.750 0.180 0.280 1.234 2.652 1.4 Paralichthys californicus 1.810 0.798 2.608 1.4 Chitonotus pugetensis 0.056 0.253 0.236 0.043 0.418 0.060 0.248 0.089 0.007 1.410 0.8 Porichthys notatus 0.248 0.103 0.110 0.013 0.085 0.038 0.598 0.027 1.222 0.7 Genyonemus lineatus 0.608 0.276 0.120 1.004 0.5 Raja inornata 0.750 0.750 0.4 Xystreurys liolepis 0.500 0.014 0.514 0.3 Sebastes miniatus 0.290 0.016 0.306 0.2 Porichthys mynaster 0.290 0.290 0.2 Lycodes pacificus 0.045 0.223 0.268 0.1 Zaniolepis frenata 0.088 0.098 0.012 0.007 0.205 0.1 Lyopsetta exilis 0.103 0.103 0.1 Sebastes saxicola 0.088 0.088 <0.1 Scomber japonicus 0.073 0.073 <0.1 Sebastes hopkinsi 0.048 0.048 <0.1 Ophiodon elongatus 0.040 0.040 <0.1 Argentina sialis 0.024 0.024 <0.1 Odontopyxis trispinosa 0.003 0.002 0.001 0.004 0.002 0.001 0.005 0.018 <0.1 Sebastesjordani 0.011 0.011 <0.1 Sebastes sp 0.004 0.007 0.011 <0.1 Citharichthys stigmaeus 0.003 0.008 0.011 <0.1 Podothecus accipenserinus 0.009 0.009 <0.1 Sebastes dallii 0.008 0.008 <0.1 Paralabrax clathratus 0.002 0.002 <0.1 Total Biomass 23.887 19.512 11.578 7.986 6.098 14.586 5.211 20.920 4.091 9.996 5.450 55.854 185.169 100 C/) t= O to v sv rt !y Table B-14 Summary statistics of OCSD's legacy nearshore stations for total coliform, fecal coliform, and enterococci bacteria c (CFU/100 ml-) by station and quarter during 2018-19. 0 Summer Fall Winter Spring Annual rt Std Std Std Std Std Station Min. Mean Max. Dev Min. Mean Max. Dev Min. Mean Max. Dev Min. Mean Max. Dev Min. Mean Max. Dev Total Coliforms 39N <17 19 170 2.04 <17 18 67 1.7 <17 29 >5000 6.41 <17 16 120 1.85 <17 20 >5000 2.91 ' 33N <17 15 33 1.43 <17 15 33 1.31 <17 35 >5500 6.52 <17 18 400 2.57 <17 19 >5500 3.01 w 27N <17 15 33 1.34 <17 16 33 1.41 <17 34 >4300 6.33 <17 16 50 1.45 <17 19 >4300 2.72 21 N <17 17 67 1.7 <17 16 67 1.65 <17 31 3400 5.62 <17 14 17 1.13 <17 18 3400 2.62 15N <17 20 100 1.84 <17 18 350 2.48 <17 46 3400 5.61 <17 14 33 1.31 <17 22 3400 2.99 12N <17 16 83 1.67 <17 19 50 1.75 <17 48 1800 4.8 <17 18 33 1.46 <17 22 1800 2.65 9N <17 21 180 1.92 <17 18 83 1.69 <17 67 >20000 7.75 <17 15 33 1.39 <17 25 >20000 3.41 6N <17 32 580 2.88 <17 28 470 2.61 <17 104 >20000 6.93 <17 22 1100 2.71 <17 38 >20000 4.12 3N <17 39 1000 3.81 <17 42 5900 4.76 <17 92 >20000 8.31 <17 26 500 2.65 <17 44 >20000 4.95 0 <17 20 330 2.46 <17 28 1600 3.4 <17 229 >20000 9.08 <17 22 1200 2.7 <17 40 >20000 5.52 3S <17 15 33 1.31 <17 19 33 1.6 <17 88 >2400 5.44 <17 21 67 1.84 <17 27 >2400 3.18 6S <17 15 33 1.31 <17 17 83 1.84 <17 85 1900 3.9 <17 14 17 1.13 <17 23 1900 2.89 9S <17 13 <17 1 <17 19 83 1.85 <17 49 800 3.67 <17 15 67 1.58 <17 20 800 2.46 15S <17 13 17 1.11 <17 20 330 2.5 <17 43 600 3.02 <17 15 33 1.31 <17 20 600 2.34 21S <17 13 17 1.11 <17 14 17 1.13 <17 30 200 2.83 <17 26 67 1.87 <17 19 200 2.02 27S <17 13 <17 1 <17 14 17 1.13 <17 32 500 2.79 <17 14 50 1.46 <17 17 500 1.93 29S <17 22 >100 2.14 <17 30 11000 5.91 <17 61 >1400 5.42 <17 16 33 1.42 <17 28 11000 3.91 39S <17 14 >17 1.25 <17 16 100 1.76 <17 50 >20000 9.22 <17 15 33 1.43 <17 20 >20000 3.48 All <17 18 1000 0.73 <17 20 11000 1.27 <17 64 >20000 2.03 <17 18 1200 0.55 <17 25 >20000 0.95 Fecal Coliforms ,W 39N <17 17 100 1.91 <17 16 83 1.67 <17 16 200 2.14 <17 17 170 2.11 <17 16 200 1.93 33N <17 14 17 1.13 <17 13 17 1.08 <17 19 130 2.22 <17 17 400 2.59 <17 16 400 1.87 N 27N <17 14 17 1.13 <17 13 17 1.08 <17 19 300 2.49 <17 14 67 1.58 <17 15 300 1.69 21N <17 14 17 1.16 <17 16 67 1.65 <17 17 150 2.02 <17 14 33 1.31 <17 15 150 1.57 15N <17 18 67 1.82 <17 17 200 2.13 <17 17 150 2.02 <17 13 17 1.08 <17 16 200 1.81 12N <17 17 130 1.95 <17 17 50 1.72 <17 22 83 2.09 <17 15 33 1.31 <17 18 130 1.79 9N <17 19 330 2.1 <17 15 50 1.56 <17 37 >20000 5.64 <17 15 33 1.29 <17 20 >20000 2.75 6N <17 29 520 2.93 <17 21 100 1.92 6 60 >20000 6.3 <17 19 860 2.4 6 29 >20000 3.55 3N <17 33 1200 3.5 <17 32 3200 4.15 <17 40 >20000 5.52 <17 23 600 2.45 <17 32 >20000 3.85 0 <17 18 300 2.3 <17 21 230 2.44 <17 67 5600 5.47 <17 20 1000 2.43 <17 26 5600 3.42 3S <17 15 33 1.31 <17 18 50 1.77 <17 31 200 3.11 <17 15 67 1.58 <17 19 200 2.09 6S <17 13 17 1.11 <17 16 67 1.65 <17 29 150 2.52 <17 14 33 1.31 <17 17 150 1.85 9S <17 13 <17 1 <17 15 33 1.42 <17 22 100 2.13 <17 13 <17 1 <17 15 100 1.59 15S <17 14 33 1.31 <17 17 150 1.96 <17 27 120 2.3 <17 13 17 1.08 <17 17 150 1.84 21S <17 15 83 1.68 <17 13 <17 1 <17 21 83 1.79 <17 18 50 1.66 <17 16 83 1.64 27S <17 13 <17 1 <17 13 17 1.11 <17 17 50 1.65 <17 14 17 1.13 <17 14 50 1.32 29S <17 14 17 1.13 <17 26 9500 5.87 <17 28 1000 3.92 <17 14 17 1.13 <17 19 9500 3.18 39S <17 13 <17 1 <17 13 17 1.08 <17 32 >20000 7.94 <17 13 <17 1 <17 16 >20000 2.95 All <17 17 1200 0.72 <17 17 9500 1.22 6 29 >20000 1.91 <17 16 1000 0.56 6 19 >20000 0.79 Table B-14 continues. Table B-14 continued. Summer Fall Winter Spring Annual Station Min. Mean Max. Std Min. Mean Max. Std Min. Mean Max. Std Min. Mean Max. Std Min. Mean Max. Std Dev Dev Dev Dev Dev Enterococci 39N 2 5 16 2.24 <2 5 130 3.99 <2 4 280 4.28 <2 2 8 1.87 <2 4 280 3.16 33N <2 4 14 2.33 <2 5 70 3.26 <2 9 350 4.89 <2 5 24 2.8 <2 5 350 3.29 27N <2 4 10 2.29 <2 3 20 2.26 <2 10 >400 6.82 <2 3 10 2.03 <2 4 >400 3.57 21 N <2 3 14 1.93 <2 5 96 2.98 <2 8 256 5.35 <2 3 12 2.04 <2 4 256 3.12 15N <2 5 14 1.86 <2 5 42 3.03 <2 7 294 5.26 <2 2 6 1.67 <2 4 294 3.09 12N <2 4 136 3.51 <2 5 36 3.21 <2 8 144 4.44 <2 4 16 2.33 <2 5 144 3.35 9N <2 7 74 2.7 <2 5 58 3.15 <2 10 >400 6.1 <2 6 40 2.73 <2 6 >400 3.61 6N <2 11 176 3.77 <2 6 78 3.7 <2 14 >400 5.48 <2 5 256 3.6 <2 8 >400 4.28 3N <2 10 230 4.33 <2 14 >400 4.56 <2 16 >400 6.03 <2 8 128 4.02 <2 12 >400 4.7 0 <2 4 22 2.41 <2 7 136 4.53 2 24 >400 5.53 <2 4 >400 3.77 <2 7 >400 4.74 3S <2 2 6 1.65 <2 5 42 3.29 <2 20 >400 6.68 <2 3 34 2.89 <2 5 >400 4.62 6S <2 3 10 1.98 <2 4 38 3.52 <2 18 >400 4.51 <2 2 24 2.44 <2 5 >400 3.94 9S <2 2 8 1.69 <2 5 42 3.14 <2 10 164 4.57 <2 2 16 1.9 <2 4 164 3.34 15S <2 2 2 1.16 <2 3 138 3.58 <2 7 72 4.7 <2 2 8 1.71 <2 3 138 3.1 21S <2 2 4 1.55 <2 2 12 2.18 <2 9 184 6 <2 3 8 1.83 <2 3 184 3.32 27S <2 2 8 1.67 <2 2 24 2.18 <2 5 118 4.7 <2 2 8 1.81 <2 3 118 2.66 29S 2 5 34 2.71 <2 6 66 3.63 2 13 >400 7.81 <2 8 28 2.23 <2 8 >400 4.02 39S <2 2 12 1.93 <2 3 40 3.27 <2 7 >400 5.89 <2 2 6 1.47 <2 3 >400 3.32 All <2 4 230 0.83 <2 5 >400 0.68 <2 11 >400 0.96 <2 4 >400 0.76 <2 5 >400 0.62 W W t= O to v :v rt This page intentionally left blank. APPENDIX C Quality Assurance/Quality Control INTRODUCTION The Orange County Sanitation District's (OCSD) Core Ocean Monitoring Program (OMP) is designed to measure compliance with permit conditions and for temporal and spatial trend analysis. The program includes measurements of: • Water quality; • Sediment quality; • Benthic infaunal community health; • Fish and epibenthic macroinvertebrate community health; • Fish tissue contaminant concentrations (chemical body burden); and • Fish health (including external parasites and diseases). The Core OMP complies with OCSD's Quality Assurance Project Plan (QAPP) (OCSD 2016a) requirements and applicable federal, state, local, and contract requirements. The objectives of the quality assurance program are as follows: • Scientific data generated will be of sufficient quality to stand up to scientific and legal scrutiny. • Data will be gathered or developed in accordance with procedures appropriate for the intended use of the data. • Data will be of known and acceptable precision, accuracy, representativeness, completeness, and comparability as required by the program. The various aspects of the program are conducted on a schedule that varies weekly, monthly, quarterly, semi-annually, and annually. Sampling and data analyses are designated by quarters 1 through 4, which are referred to as the Summer (July—September), Fall (October—December), Winter (January—March), and Spring (April—June) quarters, respectively. This appendix details quality assurance/quality control (QA/QC) information for the collection and analysis of water quality, sediment geochemistry, fish tissue chemistry, and benthic infauna for OCSD's 2018-19 Core OMP. WATER QUALITY NARRATIVE OCSD's Laboratory, Monitoring, and Compliance (LMC) staff collected 650, 654, 735, and 654 quarterly ammonium samples between July 1, 2018 and June 30, 2019. Twelve surface seawater samples were also collected at a control site (Station 2106) in each quarter. All samples were iced upon collection. Ammonium samples were preserved with 1:1 sulfuric acid upon receipt by the C-1 Quality Assurance/Quality Control LMC laboratory staff, and then stored at <6.0 °C until analysis according to the LMC's Standard Operating Procedures (SOPs) (OCSD 2016b). LMC staff also collected 175 bacteria samples in each of the Summer, Fall, and Winter quarters of the 2018-19 monitoring period. In the 2019 Spring quarter, 174 samples were collected. All samples were iced upon collection and stored at <10 °C until analysis in accordance with LMC SOPs. Ammonium The samples were analyzed for ammonium on a segmented flow analyzer using Standard Methods 4500-NH3 G-Ocean Water. Sodium salicylate and dichloroisocyanuric acid were added to the samples to react with ammonium to form indophenol blue in a concentration proportional to the ammonium concentration in the sample. The blue color was intensified with sodium nitroprusside and was measured at 660 nm. For each batch, a blank and a spike in a seawater control were analyzed every 20 or fewer samples. In addition, a matrix spike and matrix spike replicate were analyzed every 10 or fewer samples. An external reference sample was analyzed once each month. The method detection limit (MDL) for low-level ammonium samples using the segmented flow instrument is shown in Table C-1. All samples were analyzed within the required holding time. All analyses conducted met the QA/QC criteria for accuracy and precision, with one noted exception in the Spring quarter Table C-1 Method detection limits (MDLs) and reporting limits (RLs), July 2018-June 2019. Receiving waters Parameter MDL R Parameter (MPN/00mL) (MPN/100mL) (mg/L) (g/L) Total coliform 10 10 Ammonium(effective to 12/17/2018) 0.014* 0.040 E.coli 10 10 Ammonium(effective on 12/18/2018) 0.040* 0.040 Enterococci 10 10 Sediments Parameter (ng/g dry) (ng g dry) Parameter (ng/g dry) (ng g dry) Organochlorine Pesticides 2,4'-DDD 0.61 1.00 Endosulfan-alpha 0.78 1.00 2,4'-DDE 0.62 1.00 Endosulfan-beta 0.75 1.00 2,4'-DDT 0.71 1.00 Endosulfan-sulfate 1.01 2.00 4,4'-DDD 1.14 2.00 Endrin 0.61 1.00 4,4'-DDE 0.68 1.00 gamma-BHC 0.67 1.00 4,4'-DDT 0.56 1.00 Heptachlor 2.64 5.00 4,4'-DDMU 0.84 1.00 Heptachlor epoxide 0.80 1.00 Aldrin 1.97 2.00 Hexachlorobenzene 0.80 1.00 cis-Chlordane 0.70 1.00 Mirex 0.43 1.00 trans-Chlordane 0.76 1.00 trans-Nonachlor 0.82 1.00 Dieldrin 0.48 1.00 PCB Congeners PCB 18 0.19 0.50 PCB 126 0.53 1.00 PCB 28 0.43 0.50 PCB 128 0.61 1.00 PCB 37 0.47 0.50 PCB 138 0.71 1.00 PCB 44 0.47 0.50 PCB 149 0.60 1.00 PCB 49 0.61 1.00 PCB 151 0.35 0.50 PCB 52 0.51 1.00 PCB 153/168 0.75 1.00 PCB 66 0.62 1.00 PCB 156 0.67 1.00 PCB 70 0.74 1.00 PCB 157 0.70 1.00 PCB 74 0.61 1.00 PCB 167 0.55 1.00 PCB 77 0.52 1.00 PCB 169 0.28 0.50 PCB 81 0.39 0.50 PCB 170 0.36 0.50 PCB 87 0.43 0.50 PCB 177 0.61 1.00 PCB 99 0.41 0.50 PCB 180 0.38 0.50 PCB 101 0.47 0.50 PCB 183 0.57 1.00 PCB 105 0.58 1.00 PCB 187 0.55 1.00 PCB 110 0.58 1.00 PCB 189 0.34 0.50 PCB 114 0.49 0.50 PCB 194 0.29 0.50 PCB 118 0.76 1.00 PCB 201 0.58 1.00 PCB 119 0.32 0.50 PCB 206 0.36 0.50 PCB 123 0.43 0.50 Table C-1 continues. C-2 Quality Assurance/Quality Control Table C-1 continued. Parameter MDL RL MDL RL (ng/g dry) (ng g dry) Parameter (nglg dry) (ng g dry) PAH Compounds 1,6,7-Trimethylnaphthalene 0.87 1.00 Benzo[g,h,i]perylene 2.34 5.00 1-Methyl naphthalene 1.15 2.00 Benzo[k]fluoranthene 1.07 2.00 1-Methylphenanthrene 1.09 2.00 Biphenyl 1.22 2.00 2,3,6-Trimethylnaphthalene 1.03 2.00 Chrysene 1.09 2.00 2,6-Dimethylnaphthalene 1.01 2.00 Dibenz[a,h]anthracene 2.96 5.00 2-Methyl naphthalene 1.64 2.00 Dibenzothiophene 0.69 1.00 Acenaphthene 0.70 1.00 Fluoranthene 0.98 1.00 Acenaphthylene 0.79 1.00 Fluorene 1.26 2.00 Anthracene 0.83 1.00 Indeno[1,2,3-c,d]pyrene 2.19 5.00 Benz[a]anthracene 1.07 2.00 Naphthalene 2.80 5.00 Benzo[a]pyrene 0.98 1.00 Perylene 1.33 2.00 Benzo[b]fluoranthene 0.95 1.00 Phenanthrene 0.87 1.00 Benzo[e]pyrene 1.20 2.00 Pyrene 1.27 2.00 MDL RL Parameter (Ng/kg dry) (Ng/kg dry) Parameter (jig/kg dry) (pgk g dry) Metals Antimony 0.116 0.200 Lead 0.040 0.100 Arsenic 0.054 0.100 Mercury 0.038 0.040 Barium 0.151 0.200 Nickel 0.114 0.200 Beryllium 0.030 0.100 Selenium 0.481 0.500 Cadmium 0.089 0.100 Silver 0.139 0.200 Chromium 0.058 0.100 Zinc 0.862 1.500 Copper 0.138 0.200 Parameter MDL RL Parameter MDL RL (mg/kg dry) (mg/kg dry) N N Miscellaneous Parameters Dissolved Sulfides 1.03 1.03 Total Organic Carbon 0.02 0.10 Total Nitrogen(Summer) 0.52 65.00 Grain Size 0.01 0.01 Total Nitrogen(Winter) 0.49 120.00 Total Phosphorus(Summer) 0.36 7.90 Total Phosphorus(Winter) 0.18 3.80 Fish Tissue MDL RL MDL RL Parameter (ng/g wet) (ng g wet) Parameter (ng/g wet) (ng g wet) Organochlorine Pesticides 2,4'-DDD 1.22 2.00 cis-Chlordane 1.40 2.00 2,4'-DDE 1.41 2.00 trans-Chlordane 0.94 1.00 2,4'-DDT 1.58 2.00 Oxychlordane 2.64 5.00 4,4'-DDD 2.16 5.00 Heptachlor 2.25 5.00 4,4'-DDE 1.12 2.00 Heptachlor epoxide 1.26 2.00 4,4'-DDT 1.20 2.00 cis-Nonachlor 1.21 2.00 4,4'-DDMU 1.28 2.00 trans-Nonachlor 1.13 2.00 Dieldrin 2.41 5.00 PCB Congeners PCB 18 1.89 1.89 PCB 126 0.91 1.00 PCB 28 1.33 1.33 PCB 128 1.07 1.07 PCB 37 1.64 1.64 PCB 138 0.79 1.00 PCB 44 1.19 1.19 PCB 149 0.89 1.00 PCB 49 0.62 1.00 PCB 151 0.93 1.00 PCB 52 0.69 1.00 PCB 153/168 1.46 1.46 PCB 66 0.85 1.00 PCB 156 0.72 1.00 PCB 70 1.35 1.35 PCB 157 0.75 1.00 PCB 74 2.06 2.06 PCB 167 0.70 1.00 PCB 77 1.06 1.06 PCB 169 0.69 1.00 PCB 81 0.70 1.00 PCB 170 0.70 1.00 PCB 87 0.78 1.00 PCB 177 1.12 1.12 PCB 99 0.61 1.00 PCB 180 1.13 1.13 PCB 101 1.45 1.45 PCB 183 0.66 1.00 PCB 105 1.17 1.17 PCB 187 0.59 1.00 PCB 110 0.92 1.00 PCB 189 0.94 1.00 PCB 114 0.72 1.00 PCB 194 0.71 1.00 PCB 118 0.76 1.00 PCB 201 0.86 1.00 PCB 119 0.70 1.00 PCB 206 0.57 1.00 PCB 123 1.12 1.12 MDL Parameter (Ng kg wet) (pg/gL IYIDL L wet) Parameter (Ng kg wet) (pgl gwet) Metals Arsenic 0.054 0.100 Mercury 0.008 0.020 Selenium 0.481 0.500 Values reported between the MDL and the RL were estimated. C-3 Quality Assurance/Quality Control (Table C-2). This exception was found to be caused by analyst error; a repeat analysis met the QA/QC criteria. Bacteria Samples collected offshore (i.e., Recreational (aka REC-1)) were analyzed for bacteria using EnterolertT"^ for enterococci and Colilert-18TM for total coliforms and Escherichia coli. Fecal coliforms were estimated by multiplying the E. coli result by a factor of 1.1. These methods utilize enzyme substrates that produce, upon hydrolyzation, a fluorescent signal when viewed under long-wavelength (365 nm) ultraviolet light. For samples collected along the surfzone, samples were analyzed by culture-based methods for direct count of bacteria. EPA Method 1600 was applied to enumerate enterococci bacteria. For enumeration of total and fecal coliforms, Standard Methods 9222B and 9222D were used, respectively. MDLs for bacteria are presented in Table C-1. All samples were analyzed within the required holding time. REC-1 samples were processed and incubated within 8 hours of sample collection. At least one duplicate sample was analyzed in each sample batch; additional duplicates were analyzed based on the number of samples in the batch. At a minimum, duplicate analyses were performed on 10% of samples per sample batch. All equipment, reagents, and dilution waters were sterilized before use. Sterility of sample bottles was tested for each new lot/batch before use. Each lot of medium, whether prepared or purchased, was tested for sterility and performance with known positive and negative controls prior to use. For Table C-2 Water quality QA/QC summary, July 2018-June 2019. Number Number of Number of % Total samples of QA/QC Quarter Parameter (Total batches) QA/QC Sample Type Samples Compounds Compounds Compounds Tested Passed Passed' Tested Blank 38 1 38 100 Blank Spike 38 1 38 100 Summer Ammonium 650(8) Matrix Spike 69 1 69 100 Matrix Spike Dup 69 1 69 100 Matrix Spike Precision 69 1 69 100 Blank 39 1 39 100 Blank Spike 39 1 39 100 Fall Ammonium 654(10) Matrix Spike 71 1 71 100 Matrix Spike Dup 71 1 71 100 Matrix Spike Precision 71 1 71 100 Blank 44 1 44 100 Blank Spike 44 1 44 100 Winter Ammonium 735(10) Matrix Spike 79 1 79 100 Matrix Spike Dup 79 1 79 100 Matrix Spike Precision 79 1 79 100 Blank 38 1 38 100 Blank Spike 38 1 38 100 Spring Ammonium 654(8) Matrix Spike 69 1 69 100 Matrix Spike Dup 69 1 69 100 Matrix Spike Precision 69 1 68 99 An analysis passed if the following criteria were met: For blank-Target accuracy%recovery<2X MDL. For blank spike-Target accuracy%recovery 90-110. For matrix spike and matrix spike duplicate-Target accuracy%recovery 80-120. For matrix spike precision-Target precision%RPD<11%. Total Coliforms 35(5) Duplicate 35 1 33 94 Summer Fecal Coliforms 35(5) Duplicate 35 1 33 94 Enterococci 35(5) Duplicate 35 1 28 80 Total Coliforms 35(5) Duplicate 35 1 33 94 Fall Fecal Coliforms 35(5) Duplicate 35 1 31 89 Enterococci 35(5) Duplicate 35 1 32 91 Total Coliforms 35(5) Duplicate 35 1 33 94 Winter Fecal Coliforms 35(5) Duplicate 35 1 32 91 Enterococci 35(5) Duplicate 35 1 29 83 Total Coliforms 35(5) Duplicate 35 1 32 91 Spring Fecal Coliforms 35(5) Duplicate 35 1 32 91 Enterococci 35(5) Duplicate 35 1 31 89 Total Coliforms 140(20) Duplicate 140 1 131 94 Annual Fecal Coliforms 140(20) Duplicate 140 1 128 91 Enterococci 140(20) Duplicate 140 1 120 86 *Analysis passed if the average range of logarithms is less than the precision criterion. C-4 Quality Assurance/Quality Control surfzone samples, a positive and a negative control were run simultaneously with each batch of sample for each type of media used to ensure performance. New lots of Quanti-Tray and petri dish were checked for sterility before use. Each Quanti-Tray sealer was checked monthly by addition of Gram stain dye to 100 mL of water, and the tray was sealed and subsequently checked for leakage. Each lot of commercially purchased dilution blanks was checked for appropriate volume and sterility. New lots of <_10 mL volume pipettes were checked for accuracy by weighing volume delivery on a calibrated top loading scale. Duplicate analyses were performed on a minimum of 10% of routine samples. Although the precision criterion is used to measure the precision of duplicate analyses for plate-based methods (APHA 2017), this criterion was used for most probable number methods due to a lack of criterion. Over 90% of duplicate analyses passed in all 4 quarters for 2 of the 3 fecal indicator bacteria (Table C-2). The lowest analytical pass rate of 80% and 83% were observed in the Summer and Winter quarters, respectively, for enterococci. SEDIMENT CHEMISTRY NARRATIVE OCSD's LMC laboratory received 29 sediment samples from LMC's OMP staff in July 2018, and 29 samples in January 2019. All samples were stored according to LMC SOPs. All samples were analyzed for organochlorine pesticides, polychlorinated biphenyl congeners (PCBs), polycyclic aromatic hydrocarbons (PAHs), trace metals, mercury, dissolved sulfides (DS), total organic carbon (TOC), total nitrogen (TN), total phosphorus (TP), and grain size. All samples were analyzed within the required holding times. PAHs, PCBs, and Organochlorine Pesticides The analytical methods used to detect PAHs, organochlorine pesticides, and PCBs in the samples are described in the LMC SOPs. All sediment samples were extracted using an accelerated solvent extractor (ASE). Approximately 10 g (dry weight) of sample was used for each analysis. A separatory funnel extraction was performed using 100 mL of sample when field and rinse blanks were included in the batch. All sediment extracts were analyzed by gas chromatography—mass spectrometry (GC/MS). A typical sample batch included 20 field samples with required QC samples. Sample batches that were analyzed for PAHs, organochlorine pesticides, and PCBs included the following QC samples: 1 sand blank, 1 blank spike, 1 standard reference material (SRM), 1 matrix spike, and 1 matrix spike duplicate. MDLs and SRM acceptance criteria for each PAH, PCB, and pesticide constituent are presented in Tables C-1 and C-3, respectively. All analyses were performed with appropriate QC measures, as stated in OCSD's QAPP, with most of the compounds tested during the 2 quarters meeting QA/QC criteria (Table C-4). The only QC samples with a percentage of passing compounds lower than 80% occurred in the summer PCB and pesticides analyses, where the matrix spike and matrix spike duplicate passed for 58% and 57% of compounds, respectively. This lower percentage of passing compounds was most likely caused by matrix interference. When constituent concentrations exceeded the calibration range of the instrument, dilutions were made and the samples were reanalyzed. Any deviations from standard protocol that occurred during sample preparation or analysis are noted in the raw data packages. Trace Metals Dried sediment samples were analyzed for trace metals in accordance with methods in the LMC SOPs. A typical sample batch for antimony, arsenic, barium, beryllium, cadmium, chromium, copper, nickel, lead, silver, selenium, and zinc analyses included 3 blanks, a blank spike, and 1 SRM. Additionally, sample duplicates, matrix spikes, and matrix spike duplicates were analyzed at least once for every 10 sediment samples. The analysis of the blank spike and SRM provided a measure C-5 Quality Assurance/Quality Control Table C-3 Acceptance criteria for standard reference materials, July 2018-June 2019. Sediments True Value Acceptance Range(ngig) Parameter (ng/g) Minimum Maximum Organochlorine Pesticides,PCB Congeners,and Percent Dry Weight (SRM 1944;New YorWNew Jersey Waterway Sediment,National Institute of Standards and Technology) PCB 8 22.3 13.38 31.22 PCB 18 51.0 30.6 71.4 PCB 28 80.8 48.48 113.12 PCB 44 60.2 36.12 84.28 PCB 49 53.0 31.8 74.2 PCB 52 79.4 47.64 111.16 PCB 66 71.9 43.14 100.66 PCB 87 29.9 17.94 41.86 PCB 99 37.5 22.5 52.5 PCB 101 73.4 44.04 102.76 PCB 105 24.5 14.7 34.3 PCB 110 63.5 38.1 88.9 PCB 118 58.0 34.8 81.2 PCB 128 8.47 5.082 11.86 PCB 138 62.1 37.26 86.94 PCB 149 49.7 29.82 69.58 PCB 151 16.93 10.16 23.70 PCB 153/168 74.0 44.4 103.6 PCB 156 6.52 3.912 9.128 PCB 170 22.6 13.56 31.64 PCB 180 44.3 26.58 62.02 PCB 183 12.19 7.314 17.07 PCB 187 25.1 15.06 35.14 PCB 194 11.2 6.72 15.68 PCB 195 3.75 2.25 5.25 PCB 206 9.21 5.53 12.89 PCB 209 6.81 4.09 9.53 2,4'-DDD* 38.0 22.8 53.2 2,4'-DDE* 19.0 11.4 26.6 4,4'-DDD* 108.0 64.8 151.2 4,4'-DDE* 86.0 51.6 120.4 4,4'-DDT* 170.0 102 238 cis-Chlordane 16.51 9.91 23.11 trans-Chlordane* 19.0 11.4 26.6 gamma-BHC* 2.0 1.2 2.8 Hexachlorobenzene 6.03 3.62 8.44 trans-Nonachlor 8.20 4.92 11.48 Percent Dry Weight 1.3 - - PAH Compounds and Percent Dry Weight (SRM 1944;New YorWNew Jersey Waterway Sediment,National Institute of Standards and Technology) 1-Methylnaphthalene* 470 282 658 1-Methylphenanthrene* 1700 1020 2380 2-Methylnaphthalene* 740 444 1036 Acenaphthene* 390 234 546 Anthracene* 1130 678 1582 Benz[a]anthracene 4720 2832 6608 Benzo[a]pyrene 4300 2580 6020 Benzo[b]fluoranthene 3870 2322 5418 Benzo[e]pyrene 3280 1968 4592 Benzo[g,h,i]perylene 2840 1704 3976 Benzo[k]fuoranthene 2300 1380 3220 Biphenyl* 250 150 350 Chrysene 4860 2916 6804 Dibenz[a,h]anthracene 424 254 594 Dibenzothiophene* 500 300 700 Fluoranthene 8920 5352 12488 Fluorene* 480 288 672 Indeno[1,2,3-c,d]pyrene 2780 1668 3892 Naphthalene* 1280 768 1792 Perylene 1170 702 1638 Phenanthrene 5270 3162 7378 Pyrene 9700 5820 13580 Percent Dry Weight 98.7 Table C-3 continues. C-6 Quality Assurance/Quality Control Table C-3 continued. True Value Acceptance Range(mg/kg) Parameter (mg/kg) Minimum Maximum Metals (CRM-540 ERA Metals in Soil;Lot No.D099-540) Antimony 75.5 14.5 199 Arsenic 161 113 209 Barium 260 195 325 Beryllium 97.6 73.2 112 Cadmium 211 158 264 Chromium 136 95.2 177 Copper 166 124 207 Lead ill 78.8 143 Mercury 11.5 6.87 16 Nickel 91.9 64.3 119 Selenium 191 131 252 Silver 43.3 30.1 56.5 Zinc 199 139 259 Fish Tissue True Value Acceptance Range(ng/g) Parameter (ng/g) Minimum Maximum Organochlorine Pesticides and PCB Congeners (SRM1946,Lake Superior Fish Tissue;National Institute of Standards and Technology) PCB 18* 0.840 0.504 1.176 PCB 28* 2.0 1.2 2.8 PCB 44 4.66 2.796 6.524 PCB 49 3.80 2.28 5.32 PCB 52 8.10 4.86 11.34 PCB 66 10.8 6.48 15.12 PCB 70 14.9 8.94 20.86 PCB 74 4.83 2.898 6.762 PCB 77 0.327 0.196 0.458 PCB 87 9.40 5.64 13.16 PCB 99 25.6 15.36 35.84 PCB 101 34.6 20.76 48.44 PCB 105 19.9 11.94 27.86 PCB 110 22.8 13.68 31.92 PCB 118 52.1 31.26 72.94 PCB 126 0.380 0.228 0.532 PCB 128 22.8 13.68 31.92 PCB 138 115 69 161 PCB 149 26.3 15.78 36.82 PCB 153/168 170 102 238 PCB 156 9.52 5.712 13.328 PCB 170 25.2 15.12 35.28 PCB 180 74.4 44.64 104.16 PCB 183 21.9 13.14 30.66 PCB 187 55.2 33.12 77.28 PCB 194 13.0 7.8 18.2 PCB 201* 2.83 1.698 3.962 PCB 206 5.40 3.24 7.56 2,4'-DDD 2.20 1.32 3.08 2,4'-DDE* 1.04 0.624 1.456 2,4'-DDT* 22.3 13.38 31.22 4,4'-DDD 17.7 10.62 24.78 4,4'-DDE 373 223.8 522.2 4,4'-DDT 37.2 22.32 52.08 cis-Chlordane 32.5 19.5 45.5 trans-Chlordane 8.36 5.016 11.704 Oxychlordane 18.90 11.34 26.46 Dieldrin 32.5 19.5 45.5 Heptachlor epoxide 5.5 3.3 7.7 cis-Nonachlor 59.1 35.46 82.74 trans-Nonachlor 99.6 59.76 139.44 True Value Acceptance Range(%) Parameter N Minimum Maximum Lipid (SRM1946,Lake Superior Fish Tissue;National Institute of Standards and Technology) Lipid* 10.17 6.1 14.2 True Value Acceptance Range(mg/kg) Parameter (mg/kg) Minimum Maximum Metals (SRM DORM-4;National Research Council Canada) Arsenic 6.87 4.81 8.93 Selenium* 3.45 2.42 4.49 Mercury 0.412 0.288 0.536 *Parameter with non-certified value(s). G7 Quality Assurance/Quality Control Table C-4 Sediment QA/QC summary, July 2018-June 2019. Number Number of Number of Total samples of QA/QC Quarter Parameter (Total batches) QA`/QC Sample Type Samples Compounds Compounds Compounds Tested Passed Passed* Tested Blank 2 26 52 100 Blank Spike 2 26 52 100 Summer PAHs 29(2) Matrix Spike 2 26 52 100 Matrix Spike Duplicate 2 26 52 100 Matrix Spike Precision 2 26 52 100 SRM Analysis 2 21 36 86 Blank 2 25 50 100 Blank Spike 2 25 49 98 Winter PAHs 29(2) Matrix Spike 2 25 50 100 Matrix Spike Duplicate 2 25 50 100 Matrix Spike Precision 1 25 25 100 SRM Analysis 2 21 37 88 An analysis passed if the following criteria were met: For blank-Target accuracy%recovery<3X MDL. For blank spike-Target accuracy%recovery 60-120. For matrix spike and matrix spike duplicate-Target accuracy%recovery 40-120. For matrix spike precision-Target precision%RPD<25%. For SRM analysis-Target accuracy%recovery 60-140 or certified value,whichever is greater. Blank 2 60 120 100 Blank Spike 2 60 110 92 Summer PCBs and Pesticides 29(2) Matrix Spike 2 60 70 58 Matrix Spike Duplicate 2 60 68 57 Matrix Spike Precision 2 60 120 100 SRM Analysis 2 33 56 85 Blank 2 60 120 100 Blank Spike 2 60 100 83 Winter PCBs and Pesticides 29(2) Matrix Spike 2 60 119 99 Matrix Spike Duplicate 2 60 120 100 Matrix Spike Precision 2 60 120 100 SRM Analysis 2 33 55 83 An analysis passed if the following criteria were met: For blank-Target accuracy%recovery<3X MDL. For blank spike-Target accuracy%recovery 60-120. For matrix spike and matrix spike duplicate-Target accuracy%recovery 40-120. For matrix spike precision-Target precision%RPD<25%. For SRM analysis-Target accuracy%recovery 60-140 or certified value,whichever is greater. Blank 4 12 48 100 Antimony,Arsenic, Blank Spike 2 12 24 100 Barium,Beryllium, Matrix Spike 4 12 43 90 Summer Cadmium,Chromium, 29(1) Matrix Spike Dup 4 12 43 90 Copper,Lead,Nickel, Matrix Spike Precision 4 12 48 100 Selenium,Silver,Zinc Duplicate 4 12 43 90 SRM Analysis 1 12 12 100 Blank 2 1 2 100 Blank Spike 2 1 2 100 Matrix Spike 4 1 4 100 Summer Mercury 29(1) Matrix Spike Dup 4 1 4 100 Matrix Spike Precision 4 1 4 100 Duplicate 4 1 4 100 SRM Analysis 1 1 1 100 Blank 4 12 47 98 Antimony,Arsenic, Blank Spike 2 12 24 100 Barium,Beryllium, Matrix Spike 3 12 33 92 Winter Cadmium,Chromium, 29(1) Matrix Spike Dup 3 12 33 92 Copper,Lead,Nickel, Matrix Spike Precision 3 12 36 100 Selenium,Silver,Zinc Duplicate 3 12 36 100 SRM Analysis 1 12 12 100 Blank 2 1 2 100 Blank Spike 2 1 2 100 Matrix Spike 3 1 2 100 Winter Mercury 29(1) Matrix Spike Dup 3 1 2 100 Matrix Spike Precision 3 1 2 100 Duplicate 3 1 2 67 SRM Analysis 1 1 1 100 'An analysis passed if the following criteria were met. For blank-Target amount<3X MDL or<10%of sample result,whichever is greater. For blank spike-Target accuracy%recovery 90-110 for mercury and 85-115 for other metals. For matrix spike and matrix spike duplicate—Target accuracy%recovery 70-130. For matrix spike precision-Target precision%RPD<20. For duplicate-Target precision%RPD<20%at 3X MDL of sample mean. For SRM analysis-Target accuracy%recovery 80-120%or certified value,whichever is greater. Table C-4 continues. C-8 Quality Assurance/Quality Control Table C-4 continued. Number Number of Number of % Total samples of QA/QC Quarter Parameter (Total batches) QA`/QC Sample Type Samples Compounds Compounds Compounds Tested Passed Passed* Tested Blank 2 1 2 100 Blank Spike 2 1 0 0 Summer Dissolved Sulfides 29(2) Matrix Spike 3 1 3 100 Matrix Spike Dup 3 1 3 100 Matrix Spike Precision 3 1 3 100 Duplicate 3 1 0 N/A Blank 3 1 3 100 Blank Spike 3 1 2 67 Winter Dissolved Sulfides 29(3) Matrix Spike 3 1 3 100 Matrix Spike Dup 3 1 3 100 Matrix Spike Precision 3 1 3 100 Duplicate 3 1 3 100 An analysis passed if the following criteria were met: For blank-Target accuracy%recovery<2X MDL. For blank spike-Target accuracy%recovery 80-120. For matrix spike and matrix spike duplicate-Target accuracy%recovery 70-130. For matrix spike precision-Target precision%RPD<30%. For duplicate-Target precision%RPD<30%at 3X MDL of sample mean.N/A represents result<3X MDL. Blank 2 1 2 100 Blank Spike 2 1 2 100 Summer TOC 29(1) Matrix Spike 2 1 2 100 Matrix Spike Dup 2 1 2 100 Matrix Spike Precision 2 1 2 100 Duplicate 3 1 3 100 Blank 2 1 2 100 Blank Spike 2 1 2 100 Winter TOC 29(1) Matrix Spike 2 1 2 100 Matrix Spike Dup 2 1 2 100 Matrix Spike Precision 2 1 2 100 Duplicate 3 1 3 100 An analysis passed if the following criteria were met: For blank-Target accuracy%recovery<10X MDL. For blank spike,matrix spike,and matrix spike duplicate-Target accuracy%recovery 80-120. For matrix spike precision-Target precision%RPD<10%. For duplicate-Target precision%RPD<10%at 3X MDL of sample mean. Summer Grain Size 29(1) Duplicate 3 1 3 100 Winter Grain Size 29(1) Duplicate 3 1 3 100 'An analysis passed if the following criterion was met: For duplicate-Target precision mean%RPD<10%of mean phi. Blank 5 1 5 100 Blank Spike 5 1 5 100 Summer Total N 29(1) Matrix Spike 6 1 4 67 Matrix Spike Dup 6 1 4 67 Matrix Spike Precision 6 1 5 83 Duplicate 3 1 2 67 Blank 5 1 5 100 Blank Spike 5 1 5 100 Winter Total N 29(1) Matrix Spike 5 1 2 40 Matrix Spike Dup 5 1 2 40 Matrix Spike Precision 5 1 5 100 Duplicate 3 1 3 100 An analysis passed if the following criteria were met: For blank-Target accuracy%recovery<3X MDL. For blank spike-Target accuracy%recovery 90-110. For matrix spike and matrix spike duplicate-Target accuracy%recovery 80-120. For matrix spike precision-Target precision%RPD<20%. For duplicate-Target precision%RPD<20%at 3X MDL of sample mean. Blank 2 1 2 100 Blank Spike 2 1 2 100 Summer Total P 29(1) Matrix Spike 2 1 1 50 Matrix Spike Dup 2 1 1 50 Matrix Spike Precision 2 1 2 100 Duplicate 4 1 4 100 Blank 2 1 2 100 Blank Spike 2 1 2 100 Winter Total P 29(1) Matrix Spike 2 1 0 0 Matrix Spike Dup 2 1 1 50 Matrix Spike Precision 2 1 1 50 Duplicate 3 1 3 100 *An analysis passed if the following criteria were met: For blank-Target accuracy%recovery<3X MDL. For blank spike-Target accuracy%recovery 80-120. For matrix spike and matrix spike duplicate-Target accuracy%recovery 75-125. For matrix spike precision-Target precision%RPD<20%. For duplicate-Target precision%RPD<20%at 10X MDL of sample mean. C-9 Quality Assurance/Quality Control of the accuracy of the analysis. The analysis of the sample, its duplicate, and the 2 sample spikes were evaluated for precision. All samples were analyzed using inductively coupled mass spectroscopy. If any analyte exceeded both the appropriate calibration curve and linear dynamic range, the sample was diluted and reanalyzed. MDLs for metals are presented in Table C-1. Acceptance criteria for trace metal SRMs are presented in Table C-3. Duplicate sample precision failed in 5 of 48 compounds analyzed in the Summer quarter, possibly due to matrix interference (Table C-4). One of the 48 blanks analyzed in the Winter quarter produced a result for selenium which was slightly higher than the allowable range. Antimony displayed low recovery in the matrix spikes and matrix spike duplicates, due to sediment matrix interferences. All other samples met the QA/QC criteria for all compounds tested (Table C-4). Mercury Dried sediment samples were analyzed for mercury in accordance with methods described in the LMC SOPs. QC for a typical batch included a blank, blank spike, and SRM. A set of sediment sample duplicates, matrix spike, and matrix spike duplicates were run once for every 10 sediment samples. When sample mercury concentration exceeded the appropriate calibration curve, the sample was diluted with the reagent blank and reanalyzed. The samples were analyzed for mercury on a Perkin Elmer FIMS 400 system. The MDL for sediment mercury is presented in Table C-1. Acceptance criteria for the mercury SRM is presented in Table C-3. All samples met the QA/QC criteria guidelines for accuracy and precision, except for one duplicate analysis with a precision value slightly higher (20.8%) than the acceptance criterion (20%) (Table C-4). DS DS samples were analyzed in accordance with methods described in the LMC SOPs. The MDL for DS is presented in Table C-1. All QC samples in both quarters met the QC acceptance criteria, except for the blank spike (Table C-4). The blank spike failed in both summer batches, with recoveries of 79% and 74%, just below the acceptance limit of 80%. One winter batch blank spike failed, with a recovery of 75%. In all batches where the blank spike failed, the matrix spike and matrix spike duplicate not only passed the acceptance criterion of 70-130% recovery, but also the stricter blank spike criterion of 80-120%. A corrective action was implemented to prevent blank spike failures in the future. TOC TOC samples were analyzed by ALS Environmental Services, Kelso, WA. The MDL for TOC is presented in Table C-1. All analyzed TOC QC samples passed the QA/QC acceptance criteria (Table C-4). Grain Size Grain size samples were analyzed by Integral Consulting Inc., Santa Cruz, CA. The MDL for sediment grain size is presented in Table C-1. All analyzed grain size QC samples passed the QA/QC criteria of RPD <_10% (Table C-4). TN TN samples were analyzed by Weck Laboratories, Inc., City of Industry, CA. The MDL for TN is presented in Table C-1. Most matrix spike precisions and their duplicate analyses had an RPD of less than 20% in the Summer quarter, while the analyses in the Winter quarter resulted in 100% of matrix spike precisions and their duplicates passing (Table C-4). All blank and blank spikes met the C-10 Quality Assurance/Quality Control acceptance criteria; only 55% of matrix spikes and matrix spike duplicates met the recovery criteria of 80-120% for the year due to matrix interferences in the analyses (Table C-4). TP TP samples were analyzed by Weck Laboratories. The MDL for TP is presented in Table C-1. Most (75%) matrix spike precisions and all their duplicate analyses had an RPD of less than 20% for the year (Table C-4). All associated blank spikes met the acceptance criteria; only 25% and 50% of matrix spikes and matrix spike duplicates, respectively, met the recovery criteria of 75-125% for the year due to matrix interferences in the analyses (Table C-4). FISH TISSUE CHEMISTRY NARRATIVE For the 2018-19 monitoring year, the LMC laboratory received 35 trawl fish samples in July 2018, and 20 rig-fish samples in April 2019. All samples were stored, dissected, and homogenized according to methods described in the LMC SOPs. A 1:1 muscle to water ratio was used for muscle samples. No water was used for liver samples. After the individual samples were homogenized, equal aliquots of muscle from each rig-fish sample, and equal aliquots of muscle and liver from each trawl fish sample were frozen and distributed to the metals and organic chemistry sections of the analytical chemistry laboratory for analyses. Organochlorine Pesticides and PCB Congeners The analytical methods used for organochlorine pesticides and PCB congeners are described in the LMC SOPs. All fish tissue was extracted using an ASE 350 and analyzed by GC/MS. All analyses were performed within the required holding time and with appropriate QC measures. A typical organic tissue or liver sample batch included up to 20 field samples with required QC samples. The QC samples included a laboratory blank, blank spike (using tilapia), sample duplicates, matrix spike, matrix spike duplicate, and SRM. The MDLs for pesticides and PCBs in fish tissue are presented in Table C-1. Acceptance criteria for PCB and pesticides SRM in fish tissue are presented in Table C-3. Most compounds tested in each parameter group met the QA/QC criteria (Table C-5). One sample was lost due to insufficient sample for a second extraction during the Summer quarter. In cases where constituent concentrations exceeded the calibration range of the instrument, the samples were diluted and reanalyzed. Any variances that occurred during sample preparation or analyses are noted in the Comments/Notes section of each batch summary. Lipid Content Percent lipid content was determined for each sample of fish using methods described in the LMC SOPs. Lipids were extracted by dichloromethane from approximately 1 to 2 g of sample and concentrated to 2 mL. A 100 pL aliquot of the extract was placed in a tared aluminum weighing boat and allowed to air dry. The remaining residue was weighed, and the percent lipid content calculated. All analyses were performed within the required holding time and with appropriate QC measures. All analyzed samples passed (Table C-5). Mercury Fish tissue samples were analyzed for mercury in accordance with LMC SOPs. Typical QC analyses for a tissue sample batch included a blank, a blank spike, and SRMs (liver and muscle). In the same batch, additional QC samples included sample duplicates, matrix spikes, and matrix spike duplicates, which were run approximately once every 10 samples. C-11 Quality Assurance/Quality Control Table C-5 Fish tissue QA/QC summary, July 2018-June 2019. Number Number of Number of % Total samples of QAIQC Quarter Parameter (Total batches) QA/QC Sample Type Samples Compounds Compounds Compounds Tested Passed Passed* Tested Blank 8 54 432 100 Blank Spike 7 54 356 94 PCBs and Matrix Spike 4 54 201 93 Summer 70(4) Matrix Spike Dup 4 54 197 91 Pesticides Matrix Spike Precision 4 54 204 94 Duplicate 2 54 108 100 SRM 4 38 128 84 Blank 4 54 216 100 Blank Spike 4 54 191 88 PCBs and Matrix Spike 2 54 100 93 Spring 20(2) Matrix Spike Dup 2 54 92 85 Pesticides Matrix Spike Precision 2 54 102 94 Duplicate 2 54 107 99 SRM 2 41 69 84 An analysis passed if the following criteria were met: For blank-Target accuracy%recovery<3X MDL. For blank spike-Target accuracy%recovery 60-120. For matrix spike and matrix spike duplicate-Target accuracy%recovery 40-120. For matrix spike precision-Target precision%RPD<20%. For duplicate-Target precision%RPD<20%at 3X MDL of sample mean. For SRM analysis-Target accuracy%recovery 60-140 or certified value,whichever is greater. Percent Lipid- Duplicate 2 1 2 100 352 Summer Liver ( ) SRM 2 1 2 100 Percent Lipid- Duplicate 2 1 2 100 Muscle 35(2) SRM 2 1 2 100 Percent Lipid- Duplicate 2 1 2 100 Spring Muscle 20(2) SRM 2 1 2 100 *An analysis passed if the following criteria were met: For duplicate-Target precision%RPD<25%. For SRM-Target%recovery 60-140. Blank 4 1 4 100 Blank Spike 4 1 4 100 Matrix Spike 7 1 7 100 Summer Mercury 70(2) Matrix Spike Dup 7 1 7 100 Matrix Spike Precision 7 1 7 100 Duplicate 7 1 7 100 SRM Analysis 2 1 2 100 Blank 3 2 6 100 Blank Spike 1 2 2 100 Matrix Spike 2 2 4 100 Spring Arsenic&Selenium 20(1) Matrix Spike Dup 2 2 4 100 Matrix Spike Precision 2 2 4 100 Duplicate 2 2 4 100 SRM Analysis 1 2 2 100 Blank 1 1 1 100 Blank Spike 1 1 1 100 Matrix Spike 2 1 2 100 Spring Mercury 20(1) Matrix Spike Dup 2 1 2 100 Matrix Spike Precision 2 1 2 100 Duplicate 2 1 2 100 SRM Analysis 1 1 1 100 *An analysis passed if the following criteria were met: For blank-Target accuracy%recovery<2X MDL. For blank spike-Target accuracy%recovery 90-110. For matrix spike and matrix spike duplicate-Target accuracy%recovery 70-130. For matrix spike precision-Target precision%RPD<25%. For duplicate-Target precision%RPD<30%at 10X MDL of sample mean. For SRM analysis-Target accuracy%recovery 70-130 or certified value,whichever is greater. The MDL for fish mercury is presented in Table C-1. Acceptance criteria for the mercury SRMs are presented in Table C-3. All samples were analyzed within their 6-month holding time and met the QA criteria guidelines (Table C-5). Arsenic and Selenium Rig-fish tissue samples were analyzed for arsenic and selenium in accordance with LMC SOPs. Typical QC analyses for a tissue sample batch included 3 blanks, a blank spike, and an SRM (muscle). Additional QC samples included a sample duplicate, a matrix spike, and a matrix spike duplicate, which were run at least once every 10 samples. C-12 Quality Assurance/Quality Control The MDLs for fish arsenic and selenium are presented in Table C-1. Acceptance criteria for the arsenic and selenium SRMs are presented in Table C-3. All samples were analyzed within a 6-month holding time and all analyzed samples met the QA criteria guidelines (Table C-5). BENTHIC INFAUNA NARRATIVE The sorting and taxonomy QA/QC follow OCSD's QAPP. These QA/QC procedures were conducted on sediment samples collected for infauna) community analysis in July 2018 (summer) from 29 semi-annual stations (52-65 m) and in January 2019 (winter) from the same 29 semi-annual stations (Table A-4). Sorting The sorting procedure involved removal by Aquatic Bioassay and Consulting Laboratories, Inc. (ABC) of all organisms, including their fragments, from sediment samples into separate vials by major taxa (aliquots). The abundance of countable organisms (i.e., specimens with a head) per station was recorded. After ABC's in-house sorting efficiency criteria were met, the organisms and remaining particulates (grunge) were returned to OCSD. Ten percent of these samples (6 of 58) were randomly selected for re-sorting by OCSD staff. A tally was made of any countable organisms missed by ABC. A sample passed QC if the total number of countable animals found in the re-sort was :55% of the total number of individuals originally reported. Sorting results for all QA samples were well below the 5% QC limit. Taxonomy Selected benthic infauna samples underwent comparative taxonomic analysis by 2 independent taxonomists. Samples were randomly chosen for re-identification from each taxonomist's allotment of assigned samples. These were swapped between taxonomists with the same expertise in the major taxon. The resulting datasets were compared, and a discrepancy report generated. The participating taxonomists reconciled the discrepancies. Necessary corrections to taxon names or abundances were made to the database. The results were scored and errors tallied by station. Percent errors were calculated using the equations below: Equation 1: %Error#Individuals = (14 Individuals Resolved - # Individuals Onginai� _ # Individuals Resolved)x 100 Equation 2: %Error#IDTaxa = (#Taxa Misidentification _ #Taxa Resolved)x 100 Equation 3: %Error#ioIndividuals = (# Individuals Misidentification _ # Individuals Resolved) " 100 Please refer to OCSD's QAPP for detailed explanation of the variables. The first 2 equations are considered gauges of errors in accounting (e.g., recording on wrong line, miscounting, etc.), which, by their random nature, are difficult to predict. Equation 3 is the preferred measure of identification accuracy. It is weighted by abundance and has a more rigorous set of corrective actions (e.g., additional taxonomic training) when errors exceed 10%. In addition to the re-identifications, a Synoptic Data Review (SDR) was conducted upon completion of all data entry and QA. This consisted of a review of the infauna data for the survey year, aggregated by taxonomist (including both in-house and contractor). From this, any possible anomalous species reports, such as species reported outside its known depth range and possible data entry errors, were flagged for further investigation. QC objectives for identification accuracy (Equation 3) were met in 2018-19 (Table C-6). The SDR revealed some differences in application of names when compared with OCSD's internal data. While every attempt was made to standardize name application for non-specific names, i.e., specimens not identifiable to genus and species due to condition or developmental stage, the contractors differed in a few cases. We were able to identify these discrepancies and make the C-13 Quality Assurance/Quality Control changes to the final dataset. The use of provisional taxa familiar to the contractors but not OCSD's taxonomists was reconciled by sharing information by both parties to ensure there was no overlap with known taxa and to improve intercalibration between the taxonomists. No other changes to the 2018-19 infauna dataset was made as a result of the SDR. Table C-6 Percent error rates calculated for the July 2018 infauna QA samples. Station Error Type Mean 0 85 86 C 1.%Error#Individuals 1.1 1.8 1.6 2.4 1.7 2.%Error#ID Taxa 11.0 2.2 0.9 7.4 5.4 3.%Error#ID Individuals 3.4 1.1 0.3 3.2 2.0 C-14 Quality Assurance/Quality Control REFERENCES OCSD (Orange County Sanitation District). 2016a. Orange County Sanitation District — Ocean Monitoring Program. Quality Assurance Project Plan (QAPP), (2016-17). Fountain Valley, CA. OCSD. 2016b. Laboratory, Monitoring, and Compliance Standard Operating Procedures. Fountain Valley, CA. APHA (American Public Health Association, American Water Works Association, and Water Environment Federation). 2017. Standard methods for the examination of water and waste water, 23rd edition. American Public Health Association, Washington, DC. C-15 This page intentionally left blank. O�JNSV SANIiq J�ph � N = I 9 Q o W, 1J�P��g�2 ORANGE COUNTY SANITATION DISTRICT Laboratory, Monitoring, and Compliance Division 10844 Ellis Avenue Fountain Valley, California 92708-7018 714.962.2411 www.ocsewers.com 3/16