HomeMy WebLinkAboutAdministration Committee Item 2 - 2018-19 Marine Monitoring ReportORANGE COUNTY SANITATION DISTRICT
Marine Monitoring
Annual Report
Year 2018-2019 Orange County, California
ORANGE COUNTY SANITATION DISTRICTLABORATORY, MONITORING, AND COMPLIANCE DIVISION
10844 Ellis Avenue
Fountain Valley, California 92708-7018
714.962.2411
www.ocsewers.com
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i
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 Macroinvertebrates 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
ii
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
iii
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
iv
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
v
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
vi
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
vii
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 macroinvertebrates 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
viii
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
ix
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
x
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 SpecialistRobert Gamber...................................................................Senior Environmental Specialist
Laura Terriquez ..................................................................Senior Environmental Specialist
Ernest Ruckman .................................................................Senior Environmental Specialist
Benjamin Ferraro................................................................Senior Environmental Specialist
Geoffrey Daly .........................................................................Environmental SpecialistMark Kibby .....................................................................................................Boat Captain
Megan Nguyen ............................................................................................................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.
ES-1
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 dilution1 (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.
¹ The zone of initial dilution represents a 60 m area around the OCSD outfall diffuser.
ES-2
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.
1-1
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 (Order No. R8-2012-0035,
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 × 10⁶ ft² (102,193 m²) of seafloor was converted from a flat, sandy habitat into a raised,
hard-bottom substrate.
1-2
The 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 Niño 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
ReclamationPlant 1
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Figure 1–1 Regional setting and sampling area for OCSD’s Ocean Monitoring Program.
1-3
The Ocean Monitoring Program
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 Niño and La Niña 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
0 500Miles
0 100Miles
0 100Miles 0 50Miles
Urbanized Area
Urban Cluster
Source: U.S. Census Bureau, 2010 Census Urban Area Delineation Program
Figure 1–2 United States 2010 urbanized areas. (https://www.census.gov/library/visualizations/2010/geo/ua2010_uas_and_ucs_map.html).
1-4
The Ocean Monitoring Program
Figure 1–3 Annual Newport Harbor rainfall (A) and Santa Ana River flows (B).
1-5
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 × 10⁷ 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 × 10⁹ L) of flow, nearly identical
to the 2013-2018 average yearly flow of 378 MG (1.4 × 10⁹ L). Monthly average daily diversion
flows ranged from 0.3–1.6 MGD (1.1–6.1 × 10⁶ L/day) with an average daily amount of 1 MGD
(3.8 × 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 × 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 × 10⁸ L/day). Over time, the average net
GAP and GWRS diversions (diversions minus return flows to OCSD) increased to 44 MGD
(1.7 × 10⁸ L/day) in 2008-09, 61 MGD (2.3 × 10⁸ L/day) in 2013-14, and 97 MGD (3.7 × 10⁸ 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 × 10⁸ 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 × 10⁸ L/day) of
treated wastewater to the ocean (Figure 1-5).
1-6
The Ocean Monitoring Program
Figure 1–4 Monthly 2018-19 beach attendance and air temperature (A) and annual beach attendance (B) for the City of Newport Beach, California.
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Jul-18 Aug-18 Sep-18 Oct-18 Nov-18 Dec-18 Jan-19 Feb-19 Mar-19 Apr-19 May-19 Jun-19
Temperature (°F)
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1-7
The Ocean Monitoring Program
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.
Figure 1–5 OCSD’s average annual influent and ocean discharge, OCWD’s reclamation, and
annual population for Orange County, California, 1974-2019.
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Ocean Discharge
Influent
OCWD Reclama on
OC Popula on
1-8
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 (http://sccwrp.org).
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/
autoss).• 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.
1-9
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: http://www.
dof.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_publications/8. (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.ncdc.
noaa.gov/cdo-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.
1-10
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: http://oceandatacenter.ucsc.edu/home/outreach/HABwestcoast2018.pdf. (January 2019).
USGS (United States Geological Survey). 2019. Santa Ana River: USGS, 5th Street Station, Santa Ana. Internet address: http://waterdata.usgs.gov/usa/nwis/uv?site_no=11078000. (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%20progress%20report%20Jan03.pdf. (November 30, 2016).
2-1
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.
2-2
Compliance Determinations
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.
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 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.
Yes
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
per 100 mL nor a single sample maximum of 400 per 100 mL.
Yes
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 100 mL nor a single sample maximum of 104 per 100 mL.Yes
V.A.1.b. For the USEPA Primary Recreation Criteria in Federal Waters, enterococci density shall not exceed a 30 day Geometric
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.
Yes
V.A.1.c. For the CA Ocean Plan Shellfish Harvesting Standards, the median total coliform density shall not exceed 70 per 100 mL, and not more than 10 percent of the samples shall exceed 230 per 100 mL.N/A
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 waste.Yes
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 benthic communities are degraded.Yes
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 naturally, as the result of the discharge of oxygen demanding waste materials.Yes
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 under natural conditions.Yes
V.A.3.d. The concentration of substances, set forth in Chapter II, Table 1 (formerly Table B) of the Ocean Plan, in marine sediments shall not be increased to levels which would degrade indigenous biota.Yes
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 II, Table 1 (formerly Table B) of the Ocean Plan, shall not be exceeded in the area within the waste field where initial dilution is completed.Yes
Biological Characteristics
V.A.4.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 altered.Yes
V.A.4.c. The concentration of organic materials in fish, shellfish, or other marine resources used for human consumption shall not bioaccumulate to levels that are harmful to human health.Yes
V.A.5. Discharge of radioactive waste shall not degrade marine life.Yes
2-3
Compliance Determinations
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).
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Esri, Garmin, GEBCO, NOAA NGDC, and other contributorsOCSD February 2020
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Ocean Outfalls
´
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0 2.5 51.25 Kilometers
Figure 2–1 Offshore water quality monitoring stations for 2018-19.
2-4
Compliance Determinations
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
Figure 2–2 Benthic (sediment geochemistry and infauna) monitoring stations for 2018-19.
TreatmentPlant 2
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OCSD March 2020
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2-5
Compliance Determinations
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.
ReclamationPlant 1
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Figure 2–3 Trawl monitoring stations, as well as rig-fishing locations, for 2018-19.
2-6
Compliance Determinations
Table 2–2 Summary of offshore water quality compliance testing results for dissolved oxygen, pH, and light transmissivity for 2018-19.
Parameter Number of Observations
Out-of-Range Occurrences Out-of-Compliance
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 B 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 B Stations CombinedDissolved 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%
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.
2-7
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.
Station Nominal Depth (m)
Median Phi (ϕ)
Fines (%)TOC (%)Sulfides (mg/kg)Total P (mg/kg)Total N (mg/kg)ƩPAH (mg/kg)ƩDDT (mg/kg)ƩPest (mg/kg)ƩPCB (mg/kg)
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 0.513603.06 9.8 0.42 1.91 1000 130 43.9 1.53 ND 1.565593.34 10.0 0.42 1.61 1000 100 40.5 1.55 ND ND9592.90 7.2 0.36 2.54 860 390 89.2 1.24 ND ND12582.75 6.4 0.37 2.33 750 420 45.2 1.18 ND ND68523.31 11.0 0.42 ND 950 420 82.1 2.94 ND ND69523.20 9.1 0.38 1.71 1000 410 69.0 1.41 ND 4.3170523.22 15.4 0.41 ND 940 460 47.3 1.54 ND ND71523.06 9.1 0.34 1.28 860 430 47.2 1.23 ND ND72553.21 8.6 0.39 1.61 980 420 87.1 1.52 ND 29.8973553.13 10.1 0.50 2.43 1100 390 89.6 1.87 ND 12.4974573.06 10.4 0.39 2.72 980 480 49.7 1.18 ND 15.5075603.00 6.4 0.34 1.75 950 410 72.9 1.23 ND 11.9977603.01 7.5 0.38 2.38 1000 440 110.5 1.29 ND ND78633.03 8.0 0.37 2.41 950 380 61.3 1.23 ND ND79653.16 10.8 0.38 3.53 960 370 62.8 1.13 1.00 0.2480653.29 14.1 0.39 2.02 940 350 22.6 1.19 ND ND81653.14 11.3 0.37 4.77 910 340 ND ND ND ND82652.76 6.3 0.34 1.45 820 70 29.6 ND ND ND84543.14 10.8 0.51 2.18 1100 430 137.1 0.86 ND 7.2985572.98 7.3 0.49 3.23 1300 130 200.5 1.69 ND 28.6086573.00 7.1 0.45 2.79 1400 69 527.2 0.88 ND 15.2187603.09 8.2 0.37 1.47 1100 380 63.8 ND ND NDC563.04 8.3 0.37 2.56 990 330 37.3 ND ND NDCON593.20 9.7 0.39 1.78 1000 370 28.2 1.10 ND NDMean3.09 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 5.594563.03 6.4 0.34 ND 950 90 21.5 1.13 ND ND76582.99 8.1 0.37 2.24 1100 360 38.4 1.13 ND 0.68ZB563.01 7.4 0.41 2.03 970 360 116.7 ND ND 2.08Mean3.00 7.2 0.40 2.09 1105 230 106.5 0.96 ND 2.09
Sediment quality guidelinesERMN/A N/A N/A N/A N/A N/A 44792.0 46.10 N/A 180.00Regional summer values (area weighted mean)Bight’13 Middle Shelf N/A 48.0 0.70 N/A N/A 690 55.0 18.00 N/A 2.70
2-8
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.
Station Nominal Depth (m)Sb As Ba Be Cd Cr Cu Pb Hg Ni Se Ag Zn
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 38.93600.1 3.50 32.2 0.27 0.15 18.60 8.65 5.93 0.04 8.4 1.21 0.11 43.45590.1 4.15 42.9 0.31 0.21 18.80 8.86 6.69 0.02 8.8 1.50 0.15 39.59590.1 3.55 47.4 0.26 0.11 17.10 6.43 5.34 0.01 7.5 1.30 0.08 36.812580.0 3.21 34.7 0.24 0.11 15.90 5.60 5.30 0.02 7.3 1.26 0.07 35.068520.1 4.19 45.7 0.27 0.15 18.10 7.88 6.64 0.02 8.4 1.34 0.13 40.569520.1 3.19 40.5 0.25 0.20 18.10 8.20 6.00 0.07 8.5 1.31 0.20 40.670520.1 3.06 39.8 0.26 0.20 17.80 7.84 6.25 0.02 8.1 1.32 0.13 41.671520.1 3.32 37.2 0.25 0.22 16.50 6.55 5.33 0.02 7.8 1.39 0.11 38.772550.1 3.05 38.2 0.26 0.16 17.90 8.39 6.24 0.02 8.4 1.52 0.14 38.673550.1 3.88 37.8 0.25 0.31 19.90 10.60 7.44 0.04 8.2 1.38 0.17 42.674570.1 3.57 39.8 0.26 0.19 17.60 7.36 5.71 0.01 8.0 1.41 0.10 40.175600.0 3.97 42.0 0.26 0.21 16.90 6.80 5.26 0.01 7.9 1.39 0.10 39.577600.0 3.72 35.3 0.27 0.11 17.50 7.11 5.44 0.01 8.2 1.30 0.09 38.478630.0 2.74 34.1 0.28 0.10 17.10 6.81 5.25 0.01 7.8 1.49 0.09 36.879650.0 3.13 37.1 0.26 0.12 17.40 7.81 5.66 0.02 8.9 1.69 0.13 39.980650.0 3.95 40.5 0.30 0.08 16.90 7.69 5.82 0.01 8.2 1.38 0.08 39.981650.0 3.02 35.2 0.28 0.09 16.70 6.47 5.30 0.01 8.0 1.32 0.08 38.582650.1 3.22 37.9 0.30 0.09 17.70 6.84 5.23 0.01 8.6 1.21 0.08 41.984540.1 3.54 39.8 0.26 0.38 19.20 10.10 6.23 0.03 8.4 1.46 0.19 44.285570.1 3.24 32.4 0.27 0.59 20.60 11.80 6.39 0.03 8.3 1.37 0.20 42.686570.1 3.94 36.0 0.27 0.28 19.10 11.40 7.13 0.03 7.8 1.45 0.19 42.187600.1 4.31 39.1 0.29 0.10 17.80 7.12 5.66 0.02 8.1 1.35 0.09 39.7C560.1 2.86 45.1 0.25 0.11 17.20 6.58 5.83 0.01 8.3 1.27 0.08 39.7CON590.1 3.07 49.3 0.25 0.10 17.90 6.61 6.20 0.02 8.5 1.39 0.08 39.0Mean0.1 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 40.84560.1 3.21 35.7 0.27 0.18 17.80 6.84 5.42 0.02 7.6 1.40 0.10 39.076580.1 3.15 35.0 0.26 0.14 16.60 7.20 5.05 0.05 7.7 1.24 0.11 39.0ZB560.1 3.39 38.7 0.27 0.26 17.40 7.92 5.46 0.02 8.1 1.51 0.11 42.6Mean0.1 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 guidelinesERMN/A 70.00 N/A N/A 9.60 370.00 270.00 218.00 0.70 51.6 N/A 3.70 410.0Regional 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
2-9
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.
Station Nominal Depth (m)
Median Phi (ϕ)
Fines (%)TOC (%)Sulfides (mg/kg)Total P (mg/kg)Total N (mg/kg)ƩPAH (mg/kg)ƩDDT (mg/kg)ƩPest (mg/kg)ƩPCB (mg/kg)
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 0.733603.15 10.9 0.44 2.68 1000 430 26.3 1.56 ND 0.675593.50 12.9 0.41 2.36 840 450 2.7 1.81 ND ND9593.12 11.8 0.42 2.80 820 370 21.8 1.10 ND ND12582.98 10.2 0.35 2.36 790 420 55.0 1.25 ND ND68523.38 14.0 0.48 2.41 920 470 40.5 1.90 ND ND69523.34 13.0 0.39 ND 920 510 40.3 1.64 ND ND70523.32 16.6 0.48 1.60 940 500 29.5 1.87 ND ND71523.18 12.3 0.48 2.66 860 480 26.5 1.59 ND ND72553.33 13.6 0.44 1.59 890 440 100.7 1.79 ND ND73553.30 16.9 0.46 5.45 1400 450 260.2 1.81 ND 7.3374573.28 16.1 0.45 2.21 820 460 12.1 1.42 ND 0.6475603.03 7.9 0.37 2.41 850 410 60.0 0.98 ND ND77603.11 9.9 0.46 3.42 850 410 18.6 1.06 ND ND78633.02 5.6 0.39 3.49 830 340 16.0 0.98 ND ND79653.25 8.5 0.42 1.83 900 440 174.4 1.21 ND ND80653.41 15.0 0.43 2.73 880 440 17.9 1.16 ND ND81653.14 10.4 0.37 1.56 850 440 14.6 1.03 ND ND82653.04 9.6 0.39 2.80 870 360 13.1 0.91 ND ND84543.26 15.0 0.46 2.85 1000 660 51.3 1.41 ND 0.5985573.06 9.0 0.48 3.45 1100 460 74.7 1.55 ND 0.6486573.20 12.7 0.42 4.20 980 470 36.5 1.26 ND ND87603.15 12.4 0.49 2.96 890 390 407.1 1.31 ND NDC563.34 13.9 0.43 3.89 900 510 40.0 1.62 ND NDCON593.22 11.4 0.39 2.53 980 460 20.5 1.55 ND NDMean3.22 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 7.054563.19 11.8 0.37 2.76 830 470 6.5 1.14 ND ND76583.17 10.4 0.35 3.21 960 400 65.6 1.14 ND NDZB563.12 11.0 0.45 3.58 910 580 58.1 0.77 ND NDMean3.16 11.6 0.41 3.16 975 490 48.1 1.21 0.36 1.76
Sediment quality guidelinesERMN/A N/A N/A N/A N/A N/A 44792.0 46.10 N/A 180.00Regional summer values (area weighted mean)Bight’13 Middle Shelf N/A 48.0 0.70 N/A N/A 690 55.0 18.00 N/A 2.70
2-10
Compliance Determinations
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
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.
Station Nominal Depth (m)Sb As Ba Be Cd Cr Cu Pb Hg Ni Se Ag Zn
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 40.33600.1 4.16 39.3 0.28 0.15 18.90 9.40 6.12 0.01 8.6 2.35 0.16 43.25590.1 3.40 46.2 0.28 0.16 19.80 9.06 6.78 0.02 9.5 2.40 0.15 44.59590.1 2.89 32.5 0.27 0.09 17.60 6.51 5.35 0.01 8.1 2.51 0.07 37.412580.1 3.94 34.2 0.24 0.09 16.80 6.14 7.41 0.01 7.9 2.35 0.06 35.568520.1 4.09 42.7 0.27 0.14 19.00 8.76 7.02 0.03 9.1 2.82 0.12 42.169520.1 3.90 41.0 0.26 0.15 19.00 8.55 6.67 0.01 9.3 2.83 0.12 40.370520.1 3.40 38.4 0.26 0.15 18.30 8.06 6.32 0.02 8.7 2.81 0.10 40.171520.1 4.47 38.0 0.27 0.15 18.70 8.34 6.89 0.01 8.7 2.21 0.13 41.272550.1 3.11 39.7 0.26 0.14 19.10 8.75 6.46 0.02 8.8 2.74 0.13 41.173550.1 3.46 36.6 0.26 0.40 20.40 13.20 7.87 0.03 8.1 2.68 0.40 43.574570.1 3.90 38.3 0.27 0.16 18.30 8.27 5.94 0.01 8.9 2.78 0.10 41.875600.1 3.48 35.1 0.25 0.19 16.50 6.83 4.98 0.01 8.0 2.65 0.08 39.877600.1 3.36 36.6 0.28 0.11 18.20 7.59 6.59 0.02 8.5 2.36 0.07 41.478630.1 3.27 33.5 0.26 0.09 17.50 7.64 5.37 0.01 8.3 2.59 0.08 37.479650.1 2.79 36.4 0.26 0.11 18.10 8.10 5.72 0.01 8.4 2.35 0.12 42.080650.1 3.58 42.1 0.33 0.08 19.20 8.41 5.78 0.01 10.0 2.82 0.07 46.181650.1 3.38 35.2 0.28 0.08 17.20 6.83 5.48 0.01 8.5 2.96 0.06 39.182650.1 3.21 35.9 0.29 0.08 17.70 7.55 5.19 0.01 8.6 2.58 0.07 39.684540.1 3.37 37.2 0.25 0.32 18.80 12.90 6.70 0.02 8.6 2.99 0.13 42.185570.1 3.07 34.6 0.25 0.38 19.80 11.00 6.50 0.02 8.2 2.43 0.26 42.586570.1 3.11 36.4 0.26 0.28 19.00 12.00 6.25 0.02 8.5 2.57 0.22 40.687600.1 4.42 35.2 0.28 0.12 18.90 8.62 6.01 0.01 8.8 2.60 0.09 42.4C56NDNDNDNDNDNDNDNDNDNDNDNDNDCON590.1 2.97 52.6 0.25 0.09 19.10 7.02 6.22 0.01 9.3 2.72 0.06 39.5Mean0.1 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 44.84560.1 3.90 33.4 0.27 0.10 18.50 6.92 5.89 0.01 8.4 2.36 0.08 39.276580.1 2.88 35.1 0.26 0.10 17.30 7.17 5.10 0.01 8.1 2.12 0.08 40.1ZB560.1 3.80 35.7 0.25 0.19 17.60 7.71 5.65 0.02 8.4 2.45 0.10 40.2Mean0.1 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 guidelinesERMN/A 70.00 N/A N/A 9.60 370.00 270.00 218.00 0.70 51.6 N/A 3.70 410.0Regional 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
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/A0991031.00 Nontoxic195990.89 Nontoxic489930.17 Nontoxic72981020.99 Nontoxic73971010.97 Nontoxic76961000.91 Nontoxic77971010.96 NontoxicCON981020.99 NontoxicZB92960.96 NontoxicZB Dup 91 95 0.32 Nontoxic
2-11
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 (H′), 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.
2-12
Compliance Determinations
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.
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.
Station Nominal Depth (m)
Total No. of Species
Total Abundance H’SDI ITI BRI
Middle Shelf Zone 2, Non-ZID (51-90 m)1 56 80 295 3.90 30 75 163601034504.00 35 75 12559772763.70 27 76 16959873873.87 27 77 141258983773.86 30 75 1468521035143.89 28 72 1569521044333.92 28 76 1570521015113.70 24 74 127152975063.77 24 74 177255903073.98 31 80 137355984113.98 31 74 157457803303.79 25 74 157560702813.71 23 74 227760934113.80 26 73 147863913783.91 30 81 147965853493.80 25 71 168065832644.00 33 78 98165923753.95 30 80 138265622643.56 21 75 884541044644.01 30 77 128557852723.91 29 82 1286571063774.10 37 71 158760762563.84 31 77 12C56782483.79 27 70 16CON591023913.80 30 71 13Mean903653.86 28 75 14
Middle Shelf Zone 2, Within-ZID (51-90 m)0 56 106 446 4.02 33 74 19456772713.82 27 75 1376581013264.02 35 71 15ZB56662123.81 26 81 16Mean883143.92 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)
2-13
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.
Station Nominal Depth (m)
Total No. of Species
Total Abundance H’SDI ITI BRI
Middle Shelf Zone 2, Non-ZID (51-90 m)1 56 82 501 3.40 20 69 213601024543.91 31 74 16559672713.30 19 72 16959975273.49 23 74 141258893613.65 25 74 166852824953.53 20 65 196952884303.67 24 70 1570521055743.67 24 76 137152985073.55 20 73 147255814863.29 18 71 2073551187503.81 26 72 1574571224984.09 34 74 1575601076103.82 28 74 157760885083.47 20 74 1378631005973.67 24 74 147965804043.39 20 71 188065845003.48 19 75 158165843243.70 25 79 168265854033.68 23 76 1584541127343.61 24 69 168557802833.77 26 82 1386571145393.85 29 75 158760793303.74 25 74 13C56822793.71 29 74 17CON59472083.26 16 75 17Mean914633.62 24 73 16
Middle Shelf Zone 2, Within-ZID (51-90 m)0 56 82 255 3.90 31 73 21456954953.69 24 72 167658863873.60 21 75 18ZB56984063.89 29 74 16Mean903863.77 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)
2-14
Compliance Determinations
0-W
CON-S
CON-W
74-S
75-S
70-S
1-W
85-W
81-W
5-W
87-W
74-W
76-W
12-W
69-W
80-W
79-W
82-W
68-W
ZB-W
77-W
70-W
3-W
9-W
78-W
73-W
84-W
72-W
86-W
75-W
71-W
4-W
ZB-S
12-S
84-S
86-S
85-S
68-S
0-S
3-S
69-S
4-S
81-S
80-S
87-S
77-S
78-S
71-S
73-S
9-S
72-S
1-S
5-S
82-S
79-S
C-W C-S
76-S
Stations
100
80
60
40
Similarity
Zones
Within-ZID
Non-ZID
Similarity 45
ZonesWithin-ZID
Non-ZID
12-S
CON-S
C-S
5-S
72-S
1-S
68-S69-S
84-SZB-S
74-S
70-S
75-S
71-S
4-S 77-S9-S
82-S
81-S
80-S
3-S
79-S
86-S
73-S
85-S
0-S
87-S
76-S
78-S
CON-W
C-W
5-W
72-W
1-W
86-W
79-W 80-W3-W
85-W
73-W
0-W
84-W68-W
69-W70-W
74-W
ZB-W76-W
87-W
81-W
82-W
78-W
75-W 71-W
4-W77-W9-W
12-W
2D Stress: 0.23
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.
2-15
Compliance Determinations
T17-W
T17-S
T11-W
T23-W
T22-S
T23-S
T11-S
T12-W
T1-W
T1-S
T12-S
T22-W
Stations
100
80
60
40
Similarity
SitesOutfall
Non-Outfall
Similarity50
SitesOutfallNon-Outfall
T1-S
T11-S
T12-S
T17-S
T22-S
T23-S
T1-W
T11-W
T12-W
T17-W
T22-W T23-W
2D Stress: 0.09
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.
2-16
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.
Quarter Station Nominal Depth (m)
Total No. of Species
Total Abundance Biomass (kg)H’SDI
Summer
Middle Shelf Zone 2, Non-outfall (51-90 m)T23 58 9 708 1.37 0.45 1T12571011551.98 0.66 1T176061880.60 0.90 2T11601716203.15 0.44 1Mean119181.77 0.61 1Middle Shelf Zone 2, Outfall (51-90 m)T22 60 13 456 0.94 0.58 1T155122080.99 1.56 3Mean133320.97 1.07 2
Winter
Middle Shelf Zone 2, Non-outfall (51-90 m)T23 58 14 1392 1.20 0.67 1T1257942842.83 0.36 1T176078985.34 0.43 1T11601711631.77 0.72 1Mean1219342.79 0.55 1Middle Shelf Zone 2, Outfall (51-90 m)T22 60 13 372 0.47 1.62 3T1551211702.49 1.58 3Mean137711.48 1.60 3Regional 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)NCOCSD 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.
Quarter Station Nominal Depth (m)
Total No. of Species
Total Abundance Biomass (kg)H’SDI FRI
Summer
Middle Shelf Zone 2, Non-outfall (51-90 m)T23 58 15 395 23.89 1.55 2 20T1257174285.21 1.83 3 21T1760142624.09 2.20 5 22T1160133415.45 1.58 2 23Mean153579.66 1.79 3 22
Middle Shelf Zone 2, Outfall (51-90 m)T22 60 17 411 11.58 1.57 3 23T155135066.10 1.58 3 16Mean154598.84 1.58 3 19
Winter
Middle Shelf Zone 2, Non-outfall (51-90 m)T23 58 17 540 19.51 2.00 5 23T12571948520.92 2.06 4 27T17601783510.00 1.66 3 25T116020273655.85 0.89 1 32Mean18114926.57 1.65 3 27
Middle Shelf Zone 2, Outfall (51-90 m)T22 60 16 561 7.99 1.81 4 22T1551855014.59 2.18 5 25Mean1755611.29 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)
2-17
Compliance Determinations
T11-W
T17-W
T22-W
T23-W
T23-S
T22-S
T12-W
T1-W
T11-S
T1-S
T12-S
T17-S
Stations
100
90
80
70
60
Similarity
Sites
Outfall
Non-outfall
Similarity
61
Sites
Outfall
Non-outfall
T12-S
T11-S
T17-S
T23-S
T1-S
T22-S
T11-W
T17-W
T12-W
T1-W
T22-W
T23-W
2D Stress: 0.09
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.
2-18
Compliance Determinations
Ta
b
l
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2
–
1
2
Me
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(m
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(m
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(µ
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(µ
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(A
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26
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(A
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(A
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(A
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4
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29
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2
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(0
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7
8
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9
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(A
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ND
(A
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16
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3
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(0
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4
8
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(A
l
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)
ND
(A
l
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OC
S
D
h
i
s
t
o
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c
a
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v
a
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(
2
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0
8
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2
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F
i
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c
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)
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d
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)
Mu
s
c
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e
No
n
-
o
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f
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64
15
2
(
9
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2
1
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)
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1
7
(0
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0
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6
8
)
0.
0
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(0
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0
1
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.
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10
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4
9
(0
-
3
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7
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)
2.
4
3
(0
-
1
8
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3
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)
0.
0
6
(0
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1
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4
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ND
(A
l
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N
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)
Ou
t
f
a
l
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91
15
9
(
1
1
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2
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4
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7
7
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0
8
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.
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1
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4
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9
1
(0
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1.
4
7
(0
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2
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5
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)
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0
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7
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(0
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2
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7
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Li
v
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r
No
n
-
o
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f
a
l
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64
15
7
(
9
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1
7
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0
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4
2
-
3
0
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4
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0.
2
1
(0
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5
-
0
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7
9
)
54
0
.
8
2
(0
-
2
1
0
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)
44
.
7
9
(0
-
4
3
2
.
5
9
)
ND
(A
l
l
N
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)
ND
(A
l
l
N
D
)
Ou
t
f
a
l
l
91
15
8
(
1
1
0
-
2
0
4
)
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1
3
(0
-
2
4
.
6
0
)
0.
1
8
(0
.
0
2
-
0
.
5
9
)
48
4
.
2
8
(0
-
1
8
2
2
.
7
0
)
98
.
8
9
(0
-
4
5
7
.
8
0
)
3.
4
6
(0
-
8
1
.
7
0
)
ND
(A
l
l
N
D
)
Pa
r
o
p
h
r
y
s
v
e
t
u
l
u
s
(E
n
g
l
i
s
h
S
o
l
e
)
Mu
s
c
l
e
No
n
-
o
u
t
f
a
l
l
91
18
3
(
1
2
4
-
2
6
8
)
0.
8
3
(0
-
6
.
2
2
)
0.
0
6
(0
.
0
2
-
0
.
1
2
)
73
.
8
0
(0
-
5
2
4
.
3
0
)
8.
2
1
(0
-
6
1
.
2
0
)
ND
(A
l
l
N
D
)
0.
0
5
(0
-
4
.
4
5
)
Ou
t
f
a
l
l
78
18
5
(
1
3
6
-
2
9
0
)
1.
1
6
(0
-
8
.
2
3
)
0.
0
6
(0
.
0
1
-
0
.
1
1
)
10
6
.
2
5
(3
.
9
7
-
6
3
3
.
4
6
)
14
.
3
3
(0
-
1
3
0
.
9
0
)
ND
(A
l
l
N
D
)
ND
(A
l
l
N
D
)
Li
v
e
r
No
n
-
o
u
t
f
a
l
l
91
18
3
(
1
2
4
-
2
6
8
)
10
.
2
9
(1
.
9
3
-
2
6
.
8
0
)
0.
0
6
(0
.
0
2
-
0
.
1
9
)
13
1
6
.
7
0
(7
1
.
1
0
-
1
4
3
0
0
)
17
5
.
4
1
(0
-
1
6
9
4
.
7
0
)
0.
0
8
(0
-
5
.
2
7
)
ND
(A
l
l
N
D
)
Ou
t
f
a
l
l
78
18
4
(
1
3
6
-
2
9
0
)
11
.
6
6
(0
-
2
7
.
1
0
)
0.
0
6
(0
.
0
2
-
0
.
1
6
)
15
3
2
.
9
0
(9
5
.
7
0
-
2
0
9
6
7
)
20
3
.
9
3
(0
-
1
6
2
7
.
2
9
)
1.
2
5
(0
-
3
0
.
8
0
)
ND
(A
l
l
N
D
)
2-19
Compliance Determinations
Ta
b
l
e
2
–
1
3
Me
a
n
s
a
n
d
r
a
n
g
e
s
o
f
m
u
s
c
l
e
t
i
s
s
u
e
c
o
n
t
a
m
i
n
a
n
t
c
o
n
c
e
n
t
r
a
t
i
o
n
s
i
n
s
e
l
e
c
t
e
d
s
c
o
r
p
a
e
n
i
d
a
n
d
s
a
n
d
b
a
s
s
f
i
s
h
e
s
c
o
l
l
e
c
t
e
d
by
r
i
g
-
f
i
s
h
i
n
g
i
n
A
p
r
i
l
/
M
a
y
2
0
1
9
a
t
Z
o
n
e
s
1
(
O
u
t
f
a
l
l
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2-20
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 Niño
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.
CalCOFI 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.
2-21
Compliance Determinations
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3-1
CHAPTER 3
Strategic Process Studies and Regional Monitoring
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) (Order No. R8-2012-0035, NPDES Permit No. CA0110604) 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
3-2
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 µm 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).
3-3
Strategic Process Studies and Regional Monitoring
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
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!(Regional Surfzone Station
!(Legacy Surfzone Station
Ocean Outfalls
´
0 2 41 Miles
0 3 61.5 Kilometers
Figure 3–1 Offshore and nearshore (surfzone) water quality monitoring stations for 2018-19.
3-4
Strategic Process Studies and Regional Monitoring
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.
Figure 3–2 Southern California Bight Regional Water Quality Program monitoring stations for
2018-19.
Los Angeles
Orange Riverside
SanBernardino
San Diego
Ventura
Esri, Garmin, GEBCO, NOAA NGDC, and other contributors
0 5025 Miles
0 80204060 Kilometers
City of Oxnard
City of Los Angeles
LACSD
OCSD
City of San Diego - Point Loma
City of San Diego - IWTP
´
SANTACATALINAISLAND
OCSD March 2020
3-5
Strategic Process Studies and Regional Monitoring
Detailed information is available on SCCWRP’s website (http://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 https://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
Figure 3–3 OCSD’s Bight’18 sampling stations.
ReclamationPlant 1
TreatmentPlant 2
Esri, Garmin, GEBCO, NOAA NGDC, and other contributors
0 157.5 Miles
0 2412 Kilometers
Benthic Station Only (n=20)
Trawl Station Only (n=7)
Benthic and Trawl Stations (n=14)
Ocean Acidification Hypoxia Station (n=5)
Bongo Net Tow Station (n=4)
´
SantaCatalinaIsland
OCSD Outfalls
&
OCSD March 2020
3-6
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 (https://ioos.noaa.gov/project/qartod/).
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.
3-7
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.
Survey Current Direction
Plume Impacted Reference Out-of-Range Out-of-Compliance
OCSD SCCWRP OCSD SCCWRP OCSD SCCWRP OCSD SCCWRP
Dissolved OxygenJul-18 UC N/A 8 2 9 12 2 0 2Aug-18 UC N/A 3 2 14 1 0 0 0Sep-18 DC N/A 4 2 12 2 0 0 0Oct-18 UC N/A 3 2 15 0 0 0 0Nov-18 UC N/A 4 2 15 0 0 0 0Dec-18 UC N/A 2 2 7 0 0 0 0Jan-19 DC N/A 4 2 10 2 0 2 0Feb-19 DC N/A 4 2 13 8 0 3 0Mar-19 UC N/A 4 2 14 0 0 0 0Apr-19 DC N/A 5 2 14 12 0 12 0Apr-19 UC N/A 5 2 14 14 0 9 0May-19 DC N/A 4 2 12 13 0 5 0Jun-19 UC N/A 5 2 10 10 3 2 3pHJul-18 UC N/A 8 2 9 1 0 0 0Aug-18 UC N/A 3 2 16 0 0 0 0Sep-18 DC N/A 4 2 14 0 0 0 0Oct-18 UC N/A 3 2 17 0 0 0 0Nov-18 UC N/A 4 2 16 0 0 0 0Dec-18 UC N/A 2 2 7 0 0 0 0Jan-19 DC N/A 4 2 11 0 0 0 0Feb-19 DC N/A 4 2 4 1 0 1 0Mar-19 UC N/A 4 2 15 10 0 0 0Apr-19 DC N/A 5 2 16 15 0 7 0Apr-19 UC N/A 5 2 16 9 0 7 0May-19 DC N/A 4 2 12 2 0 2 0Jun-19 UC N/A 5 2 10 0 0 0 0Light TransmissivityJul-18 UC N/A 8 2 10 2 6 0 5Aug-18 UC N/A 3 2 16 11 3 0 3Sep-18 DC N/A 4 2 14 6 2 0 2Oct-18 UC N/A 3 2 17 15 2 0 2Nov-18 UC N/A 4 2 16 7 4 1 4Dec-18 UC N/A 2 2 7 23 1 2 1Jan-19 DC N/A 4 2 11 9 3 0 3Feb-19 DC N/A 4 2 14 8 3 1 3Mar-19 UC N/A 4 2 15 20 4 4 4Apr-19 DC N/A 5 2 16 13 4 1 2Apr-19 UC N/A 5 2 16 10 4 2 2May-19 DC N/A 4 2 12 5 3 0 3Jun-19 UC N/A 5 2 10 12 2 0 1
N/A = Not Applicable; DC = Downcoast; UC = Upcoast.
3-8
Strategic Process Studies and Regional Monitoring
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.
0
2
4
6
8
10
12
14
16
18
20
22
24
26
28
Stations/Month
N/A
Reference CDOM Impacted Out of Range Out of Compliance
Oxygen pH Transmissivity Oxygen pH Transmissivity
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.
3-9
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.
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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 SBE911plus 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
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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
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
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TreatmentPlant 2
ReclamationPlant 1
3-mile Line
2403
2351
2303
2223
2203
2183
2104
2103
2406
2405
2404
2354
2353
2352
2306
2305
2304
2226
2225
2224
2206
2205
2204
2186
2185
2184
2106
2105
Esri, Garmin, GEBCO, NOAA NGDC, and other contributorsOCSD January 2020
!(ZID Station
!(Upcoast Reference Station
!(Downcoast Reference Station
!(Water Quality Compliance Station
Ocean Outfalls
Zone A
Zone B
Huntington Beach
Newport Beach
´0 2 41 Miles
0 3 61.5 Kilometers
10m
20m
30m
40m
50m
60m
80m
100m
200m
300m
Figure A–1 Offshore water quality monitoring stations and zones used for California Ocean Plan
compliance determinations.
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 OROSCCWRP. 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 OROSCCWRP. 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 OROOCSD found 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 OROOCSD were recalculated as presence/absence when multiple OROOCSD 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 OROSCCWRP was equivalent to the OOCOCSD 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 OROSCCWRP associated with Station 2205 was not included.
(6) SCCWRP methodology currently does not distinguish between positive and negative
significant differences. For those instances when an OROSCCWRP was 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 m² 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 ≤4 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).
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 (ƩPCB) and total polycyclic aromatic hydrocarbons (ƩPAH) were
calculated by summing the measured value of each respective constituent listed in Table A-3. Total
dichlorodiphenyltrichloroethane (ƩDDT) represents the summed values of 4,4’-DDMU and the
2,4- and 4,4’-isomers of DDD, DDE, and DDT. Total chlorinated pesticides (ƩPest) represents the
summed values of 13 chlordane derivative compounds plus dieldrin.
A-7
Methods
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. BGrain Size Plastic bag 4° C 6 months Plumb (1981)Mercury Amber glass jar Freeze 6 months LMC SOP 245.1B Rev. GMetalsAmber glass jar Freeze 6 months LMC SOP 200.8B_SED Rev. FSediment Toxicity HDPE container 4° C 2 months LMC SOP 8810Total Chlorinated Pesticides (ƩPest)Glass jar Freeze 6 months LMC SOP 8000-SPPTotal DDT (ƩDDT)Glass jar Freeze 6 months LMC SOP 8000-SPPTotal 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 6010B *Total Polychlorinated Biphenyls (ƩPCB)Glass jar Freeze 6 months LMC SOP 8000-SPP
Total Polycyclic Aromatic Hydrocarbons (ƩPAH)Glass jar Freeze 6 months LMC SOP 8000-PAH
* Available online at: www.epa.gov.
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
Table A–3 Parameters measured in sediment samples during 2018-19.
Metals
Antimony Cadmium Lead SeleniumArsenicChromiumMercurySilverBariumCopperNickelZincBeryllium
Organochlorine Pesticides
Chlordane Derivatives and DieldrinAldrinEndosulfan-alpha gamma-BHC Hexachlorobenzenecis-Chlordane Endosulfan-beta Heptachlor Mirextrans-Chlordane Endosulfan-sulfate Heptachlor epoxide trans-NonachlorDieldrinEndrinDDT Derivatives2,4’-DDD 2,4’-DDE 2,4’-DDT 4,4’-DDMU4,4’-DDD 4,4’-DDE 4,4’-DDT
Polychlorinated Biphenyl (PCB) Congeners
PCB 18 PCB 81 PCB 126 PCB 170PCB 28 PCB 87 PCB 128 PCB 177PCB 37 PCB 99 PCB 138 PCB 180PCB 44 PCB 101 PCB 149 PCB 183PCB 49 PCB 105 PCB 151 PCB 187PCB 52 PCB 110 PCB 153/168 PCB 189PCB 66 PCB 114 PCB 156 PCB 194PCB 70 PCB 118 PCB 157 PCB 201PCB 74 PCB 119 PCB 167 PCB 206PCB 77 PCB 123 PCB 169
Polycyclic Aromatic Hydrocarbon (PAH) Compounds
Acenaphthene Benzo[g,h,i]perylene Fluoranthene 1-MethylnaphthaleneAcenaphthyleneBenzo[k]fluoranthene Fluorene 2-MethylnaphthaleneAnthraceneBiphenylIndeno[1,2,3-c,d]pyrene 2,6-DimethylnaphthaleneBenz[a]anthracene Chrysene Naphthalene 1,6,7-TrimethylnaphthaleneBenzo[a]pyrene Dibenz[a,h]anthracene Perylene 2,3,6-TrimethylnaphthaleneBenzo[b]fluoranthene Dibenzothiophene Phenanthrene 1-MethylphenanthreneBenzo[e]pyrene Pyrene
Other Parameters
Dissolved Sulfides Total Nitrogen Total Organic Carbon Total PhosphorusGrain Size
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 × 45.7 cm × 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 × 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
A-9
Methods
Table A–4 Benthic infauna taxonomic aliquot distribution for 2018-19.
Quarter Survey (No. of samples)Taxonomic Aliquots Contractor OCSD
Summer 2018 Semi-annual (29)
Annelida 16 13Arthropoda722Echinodermata290Mollusca1415Miscellaneous Phyla 7 22
Winter 2019 Semi-annual (29)
Annelida 29 0Arthropoda290Echinodermata290Mollusca029Miscellaneous Phyla 29 0
Totals 189 101
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.
ƩDDT and ƩPCB were calculated as described in the sediment geochemistry section. Total
chlordane (ƩChlordane) 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 ƩDDT, ƩPCB,
methylmercury, dieldrin and ƩChlordane were used to assess human health risk in rig-caught fish
(Klasing and Brodberg 2008, FDA 2011).
A-12
Methods
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
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 200.8B SED Rev. FOrganochlorine 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 245.1B Rev. GPolychlorinated 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 Dieldrincis-Chlordane Dieldrin cis-Nonachlortrans-Chlordane Heptachlor trans-NonachlorOxychlordaneHeptachlor epoxideDDT Derivatives2,4’-DDD 2,4’-DDE 2,4’-DDT4,4’-DDD 4,4’-DDE 4,4’-DDT4,4’-DDMUPolychlorinated Biphenyl (PCB) CongenersPCB 18 PCB 101 PCB 156PCB 28 PCB 105 PCB 157PCB 37 PCB 110 PCB 167PCB 44 PCB 114 PCB 169PCB 49 PCB 118 PCB 170PCB 52 PCB 119 PCB 177PCB 66 PCB 123 PCB 180PCB 70 PCB 126 PCB 183PCB 74 PCB 128 PCB 187PCB 77 PCB 138 PCB 189PCB 81 PCB 149 PCB 194PCB 87 PCB 151 PCB 201PCB 99 PCB 153/168 PCB 206
Other Parameter
Lipids
* Analyzed only in rig-fish specimens.
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Zar, J.H. 1999. Biostatistical Analysis. Prentice-Hall Publishers, Upper Saddle River, NJ. 663 p. + Appendices.
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B-1
APPENDIX B
Supporting Data
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60
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*G
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;
*
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.
B-2
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.
Station Date Meets 30-day Geometric Mean of ≤1,000/100 mL
Meets Single Sample Standard of ≤10,000/100 mL
Meets Single Sample Standard of ≤1,000/100 mL *
7/10/2018 7/11/2018 7/12/2018 8/6/2018 8/7/20182103<10 <10 <10 33 52 YES YES YES2104<10 <10 10 17 66 YES YES YES218310<10 <10 <10 138 YES YES YES2203<10 <10 <10 81 156 YES YES YES2223<10 <10 <10 <10 <10 YES YES YES2303<10 <10 <10 130 251 YES YES YES2351<10 <10 <10 1216 512 YES YES YES2403<10 <10 <10 778 159 YES YES YES10/16/2018 10/17/2018 10/18/2018 11/5/2018 11/6/20182103<10 15 12 <10 <10 YES YES YES2104<10 <10 <10 <10 <10 YES YES YES2183142213<10 <10 YES YES YES2203191114<10 <10 YES YES YES2223941318<10 <10 YES YES YES2303691131<10 15 YES YES YES23511133872<10 <10 YES YES YES240331617829<10 <10 YES YES YES1/23/2019 1/24/2019 2/6/2019 2/7/2019 2/19/201921031618172116 YES YES YES21049361311762 **YES YES YES **2183 36 17 40 29 27 YES YES YES2203<10 <10 60 74 <10 YES YES YES2223<10 <10 134 40 <10 YES YES YES2303<10 <10 54 45 <10 YES YES YES2351<10 <10 127 58 <10 YES YES YES2403<10 <10 235 38 <10 YES YES YES4/23/2019 4/24/2019 4/25/2019 5/6/2019 5/8/2019210310<10 <10 56 54 **YES YES YES **2104 13 <10 12 21 118 **YES YES YES **2183 <10 <10 <10 14 39 YES YES YES2203<10 <10 <10 11 16 YES YES YES2223<10 <10 <10 <10 10 YES YES YES2303<10 <10 <10 <10 <10 YES YES YES2351<10 <10 <10 <10 <10 YES YES YES2403<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-3
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.
Station Date Meets 30-day Geometric Mean ≤200/100 mL
Meets single sample standard of ≤400/100 mL
7/10/2018 7/11/2018 7/12/2018 8/6/2018 8/7/20182103<10 <10 <10 <10 <10 YES YES2104<10 <10 <10 <10 <10 YES YES2183<10 <10 <10 <10 <10 YES YES2203<10 <10 <10 <10 <10 YES YES2223<10 <10 <10 <10 <10 YES YES2303<10 <10 <10 <10 11 YES YES2351<10 <10 <10 <10 <10 YES YES2403<10 <10 <10 <10 24 YES YES10/16/2018 10/17/2018 10/18/2018 11/5/2018 11/6/20182103<10 <10 <10 <10 <10 YES YES2104<10 <10 <10 <10 <10 YES YES2183<10 <10 10 <10 <10 YES YES2203<10 <10 <10 <10 <10 YES YES2223<10 <10 <10 <10 <10 YES YES230318<10 <10 <10 <10 YES YES23511411<10 <10 <10 YES YES240328<10 <10 <10 <10 YES YES1/23/2019 1/24/2019 2/6/2019 2/7/2019 2/19/201921031010<10 <10 <10 YES YES21043517<10 <10 26 *YES YES *2183 17 10 <10 <10 <10 YES YES2203<10 <10 14 <10 <10 YES YES2223<10 <10 10 <10 <10 YES YES2303<10 <10 <10 <10 <10 YES YES2351<10 <10 <10 <10 <10 YES YES2403<10 <10 11 <10 <10 YES YES4/23/2019 4/24/2019 4/25/2019 5/6/2019 5/8/20192103<10 <10 <10 15 16 *YES YES *2104 10 <10 <10 <10 42 *YES YES *2183 <10 <10 <10 <10 21 YES YES2203<10 <10 <10 <10 <10 YES YES2223<10 <10 <10 <10 <10 YES YES2303<10 <10 <10 <10 <10 YES YES2351<10 <10 <10 <10 <10 YES YES2403<10 <10 <10 <10 <10 YES YES
* Depths combined, meet single sample standard (2/19/19, 5/8/19).
B-4
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.
Station Date
Meets COP 30-day Geometric Mean of ≤35/100 mL
Meets COP single sample standard of ≤104/100 mL
Meets EPA single sample standard of ≤501/100 mL *
7/10/2018 7/11/2018 7/12/2018 8/6/2018 8/7/20182103<10 <10 <10 <10 <10 YES YES YES2104<10 11 <10 17 **<10 YES YES **YES **2183 <10 <10 <10 <10 <10 YES YES YES2203<10 <10 <10 <10 <10 YES YES YES2223<10 <10 <10 <10 <10 YES YES YES2303<10 <10 <10 <10 <10 YES YES YES235121 **<10 <10 <10 <10 YES YES **YES2403<10 <10 <10 <10 <10 YES YES YES10/16/2018 10/17/2018 10/18/2018 11/5/2018 11/6/20182103<10 <10 <10 <10 10 YES YES YES2104<10 <10 <10 <10 <10 YES YES YES2183<10 <10 <10 <10 <10 YES YES YES2203<10 <10 15 <10 <10 YES YES YES2223<10 <10 12 <10 <10 YES YES YES230320 **<10 16 14 <10 YES YES **YES2351<10 <10 <10 10 <10 YES YES YES2403<10 <10 25 **<10 <10 YES YES **YES1/23/2019 1/24/2019 2/6/2019 2/7/2019 2/19/20192103<10 <10 <10 <10 <10 YES YES YES210412<10 <10 <10 17 **YES YES **YES2183<10 <10 10 <10 10 YES YES YES2203<10 13 10 <10 <10 YES YES YES2223<10 <10 <10 <10 <10 YES YES YES2303<10 <10 <10 <10 <10 YES YES YES2351<10 <10 <10 <10 <10 YES YES YES2403<10 32 **10 <10 <10 YES YES **YES **4/23/2019 4/24/2019 4/25/2019 5/6/2019 5/8/20192103<10 10 <10 <10 11 YES YES YES2104<10 <10 <10 <10 21 YES YES YES2183<10 10 <10 <10 <10 YES YES YES2203<10 <10 <10 <10 10 YES YES YES222310<10 <10 <10 <10 YES YES YES2303<10 <10 <10 <10 <10 YES YES YES2351<10 <10 <10 <10 <10 YES YES YES2403<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-5
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.
Surface Observation
Station Group
Totals
Upcoast Offshore Upcoast Inshore Infield Offshore Within-ZID Infield Inshore Downcoast Offshore Downcoast Inshore
2225, 2226 2305, 2306
2353, 2354 2405, 2406
2223, 2224 2303, 2304
2351, 2352 2403, 2404
2206 2205 2203, 2204 2105, 2106
2185, 2186
2103, 2104
2183, 2184
Oil and Grease 0 0 0 0 0 0 0 0Trash/Debris 0 2 0 0 0 0 1 3Biological Material (kelp)1 1 0 0 0 0 0 2Material of Sewage Origin 0 0 0 0 0 0 0 0Totals13000015
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.
Surface Observation
Station Group
TotalsUpcoast Inshore Within-ZID Infield Inshore Downcoast Inshore
2223, 2303 2351, 2403 2205 2203 2103, 2104, 2183Oil and Grease 0 0 0 0 0Trash/Debris 1 0 0 0 1Biological Material (kelp)4 1 0 1 6Material of Sewage Origin 0 0 0 0 0Totals51017
B-6
Supporting Data
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B-7
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 Strata (m)n <MDL *MDL-3.9 4-5.9 **≥6 ***
Summer
1-15 180 83.3%16.7%0.0%0.0%16-30 169 77.5%22.5%0.0%0.0%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%
Fall
1-15 183 76.0%24.0%0.0%0.0%16-30 153 80.4%19.6%0.0%0.0%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%
Winter
1-15 138 86.2%13.8%0.0%0.0%16-30 142 77.5%22.5%0.0%0.0%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%
Spring
1-15 150 100.0%0.0%0.0%0.0%16-30 134 92.5%7.5%0.0%0.0%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%
Annual
1-15 651 85.7%14.3%0.0%0.0%16-30 598 81.6%18.4%0.0%0.0%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
Summer
Number of Species
Within-ZID 52 (43-62)19 (13-23)5 (2-9)6 (3-13)7 (4-12)
Non-ZID 52 (39-63)18 (9-26)5 (2-8)6 (3-12)9 (5-15)
Abundance Within-ZID 223 (148-313)52 (41-66)12 (5-25)8 (3-22)19 (6-37)
Non-ZID 258 (158-394)58 (30-133)14 (6-28)14 (3-26)21 (10-32)
Winter
Number of
Species
Within-ZID 53 (52-55)16 (10-20)4 (3-6)11 (9-14)6 (1-10)
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-8
Supporting Data
Ta
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B-9
Supporting Data
Ta
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1
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(
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2
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7
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1
No
m
i
n
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l
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e
p
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h
58
60
55
57
60
60
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9
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0
B-10
Supporting Data
Ta
b
l
e
B
–
1
2
Ab
u
n
d
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n
c
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a
n
d
s
p
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a
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r
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8
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r
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.
St
a
t
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n
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3
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2
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2
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7
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1
No
m
i
n
a
l
D
e
p
t
h
58
60
55
57
60
60
Qu
a
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r
S
W
S
W
S
W
S
W
S
W
S
W
To
t
a
l
%
Se
b
a
s
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s
s
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m
i
c
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2
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1
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2
9
3
6
15
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8
9
22
3
8
27
.
8
Ci
t
h
a
r
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c
h
t
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s
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d
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s
20
2
23
2
24
8
21
0
20
8
13
2
94
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1
59
13
4
10
5
12
9
18
9
4
23
.
5
Za
n
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1
57
13
33
18
94
81
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7
35
41
0
19
13
1
11
1
9
13
.
9
Ic
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l
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s
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t
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s
8
26
47
80
15
9
87
14
9
4
55
9
15
1
8
78
3
9.7
Sy
m
p
h
u
r
u
s
a
t
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c
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d
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s
18
67
18
42
26
61
10
53
7
12
4
6
12
9
56
1
7.0
Za
l
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m
b
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s
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s
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18
30
15
13
0
34
4
18
4
62
4
56
37
5
4.7
Pa
r
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p
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y
s
v
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t
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l
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s
5
15
5
3
1
20
2
51
3
14
10
31
16
0
2.0
Ch
i
t
o
n
o
t
u
s
p
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t
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n
s
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s
9
22
26
9
41
7
24
11
1
15
0
1.9
Sy
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c
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s
15
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9
2
18
40
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6
3
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4
14
7
1.8
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5
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1
1
42
36
20
1
18
10
14
4
1.8
Mic
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s
4
19
14
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1
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6
19
15
16
4
11
12
8
1.6
Hi
p
p
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g
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s
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n
a
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a
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2
39
5
22
3
23
1
16
1
9
12
1
1.5
Ple
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c
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19
81
1.0
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b
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1
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t
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l
A
b
u
n
d
a
n
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39
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41
1
56
1
50
6
55
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42
8
48
5
26
2
83
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34
1
27
3
6
80
5
0
10
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To
t
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l
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o
.
o
f
S
p
e
c
i
e
s
15
17
17
16
13
18
17
19
14
17
13
20
37
B-11
Supporting Data
Ta
b
l
e
B
–
1
3
Bi
o
m
a
s
s
(
k
g
)
o
f
d
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m
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s
a
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a
n
d
s
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u
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e
r
2
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1
8
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n
d
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9
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.
St
a
t
i
o
n
T2
3
T2
2
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T1
2
T1
7
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1
No
m
i
n
a
l
D
e
p
t
h
58
60
55
57
60
60
Qu
a
r
t
e
r
S
W
S
W
S
W
S
W
S
W
S
W
To
t
a
l
%
Cit
h
a
r
i
c
h
t
h
y
s
s
o
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17
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7
2
0
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9
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0
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5
9
6
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2
1
0
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0
5
7
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3
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8
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4
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8
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8
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0
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8
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3
3
3
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5
8
3
6.
8
4
0
55
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6
3
3
30
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0
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3
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5
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1
6
0.
0
1
4
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7
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1
5
0
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9
7
38
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9
6
5
21
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0
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n
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0
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5
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5
9
8
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3
8
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9
7
7
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3
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8
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9
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8
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0
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5
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7
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5
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3
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2
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6
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u
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h
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9
8
9
1.
3
2
8
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1
6
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4
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9
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7
Sy
m
p
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0.
2
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8
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9
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2
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8
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6
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3
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4
4
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9
7
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1
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8
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8
6
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7
4
8
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0
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9
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4
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6
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s
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6
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6
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7
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4
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8
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0
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6
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0
Pl
e
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3
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8
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8
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0
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4
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6
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4
Za
l
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6
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8
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2
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1
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8
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6
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3
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3
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1
Mi
c
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2
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9
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5
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2
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4
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8
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2
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4
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r
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7
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8
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6
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1
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To
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B
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m
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s
23
.
8
8
7
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5
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7.
9
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0
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9
9
6
5.
4
5
0
55
.
8
5
4
18
5
.
1
6
9
10
0
B-12
Supporting Data
Ta
b
l
e
B
–
1
4
Su
m
m
a
r
y
s
t
a
t
i
s
t
i
c
s
o
f
O
C
S
D
’
s
l
e
g
a
c
y
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e
a
r
s
h
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s
t
a
t
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o
n
s
f
o
r
t
o
t
a
l
c
o
l
i
f
o
r
m
,
f
e
c
a
l
c
o
l
i
f
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r
m
,
a
n
d
e
n
t
e
r
o
c
o
c
c
i
b
a
c
t
e
r
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a
(C
F
U
/
1
0
0
m
L
)
b
y
s
t
a
t
i
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n
a
n
d
q
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g
2
0
1
8
-
1
9
.
Su
m
m
e
r
Fa
l
l
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n
t
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r
Sp
r
i
n
g
An
n
u
a
l
St
a
t
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o
n
Mi
n
.
Me
a
n
Ma
x
.
St
d
De
v
Mi
n
.
Me
a
n
Ma
x
.
St
d
De
v
Mi
n
.
Me
a
n
Ma
x
.
St
d
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v
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n
.
Me
a
n
Ma
x
.
St
d
De
v
Mi
n
.
Me
a
n
Ma
x
.
St
d
De
v
To
t
a
l
C
o
l
i
f
o
r
m
s
39
N
<1
7
19
17
0
2.
0
4
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7
18
67
1.
7
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7
29
>5
0
0
0
6.
4
1
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7
16
12
0
1.
8
5
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7
20
>5
0
0
0
2.
9
1
33
N
<1
7
15
33
1.
4
3
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7
15
33
1.
3
1
<1
7
35
>5
5
0
0
6.
5
2
<1
7
18
40
0
2.
5
7
<1
7
19
>5
5
0
0
3.
0
1
27
N
<1
7
15
33
1.
3
4
<1
7
16
33
1.
4
1
<1
7
34
>4
3
0
0
6.
3
3
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7
16
50
1.
4
5
<1
7
19
>4
3
0
0
2.
7
2
21
N
<1
7
17
67
1.
7
<1
7
16
67
1.
6
5
<1
7
31
34
0
0
5.
6
2
<1
7
14
17
1.
1
3
<1
7
18
34
0
0
2.
6
2
15
N
<1
7
20
10
0
1.
8
4
<1
7
18
35
0
2.
4
8
<1
7
46
34
0
0
5.
6
1
<1
7
14
33
1.
3
1
<1
7
22
34
0
0
2.
9
9
12
N
<1
7
16
83
1.
6
7
<1
7
19
50
1.
7
5
<1
7
48
18
0
0
4.
8
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7
18
33
1.
4
6
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7
22
18
0
0
2.
6
5
9N
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7
21
18
0
1.
9
2
<1
7
18
83
1.
6
9
<1
7
67
>2
0
0
0
0
7.
7
5
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7
15
33
1.
3
9
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7
25
>2
0
0
0
0
3.
4
1
6N
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7
32
58
0
2.
8
8
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7
28
47
0
2.
6
1
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7
10
4
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0
0
0
0
6.
9
3
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7
22
11
0
0
2.
7
1
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7
38
>2
0
0
0
0
4.
1
2
3N
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7
39
10
0
0
3.
8
1
<1
7
42
59
0
0
4.
7
6
<1
7
92
>2
0
0
0
0
8.
3
1
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7
26
50
0
2.
6
5
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7
44
>2
0
0
0
0
4.
9
5
0
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7
20
33
0
2.
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B-13
Supporting Data
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6
2
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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
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
C-2
Quality Assurance/Quality Control
Table C–1 Method detection limits (MDLs) and reporting limits (RLs), July 2018–June 2019.
Receiving waters
Parameter MDL (MPN/100mL)RL (MPN/100mL)Parameter MDL (mg/L)RL (mg/L)
Total coliform 10 10 Ammonium (effective to 12/17/2018)0.014 *0.040E. coli 10 10 Ammonium (effective on 12/18/2018)0.040 *0.040Enterococci1010
Sediments
Parameter MDL (ng/g dry)RL (ng/g dry)Parameter MDL (ng/g dry)RL (ng/g dry)
Organochlorine Pesticides2,4’-DDD 0.61 1.00 Endosulfan-alpha 0.78 1.002,4’-DDE 0.62 1.00 Endosulfan-beta 0.75 1.002,4’-DDT 0.71 1.00 Endosulfan-sulfate 1.01 2.004,4’-DDD 1.14 2.00 Endrin 0.61 1.004,4’-DDE 0.68 1.00 gamma-BHC 0.67 1.004,4’-DDT 0.56 1.00 Heptachlor 2.64 5.004,4’-DDMU 0.84 1.00 Heptachlor epoxide 0.80 1.00Aldrin1.97 2.00 Hexachlorobenzene 0.80 1.00cis-Chlordane 0.70 1.00 Mirex 0.43 1.00trans-Chlordane 0.76 1.00 trans-Nonachlor 0.82 1.00Dieldrin0.48 1.00 PCB CongenersPCB 18 0.19 0.50 PCB 126 0.53 1.00PCB 28 0.43 0.50 PCB 128 0.61 1.00PCB 37 0.47 0.50 PCB 138 0.71 1.00PCB 44 0.47 0.50 PCB 149 0.60 1.00PCB 49 0.61 1.00 PCB 151 0.35 0.50PCB 52 0.51 1.00 PCB 153/168 0.75 1.00PCB 66 0.62 1.00 PCB 156 0.67 1.00PCB 70 0.74 1.00 PCB 157 0.70 1.00PCB 74 0.61 1.00 PCB 167 0.55 1.00PCB 77 0.52 1.00 PCB 169 0.28 0.50PCB 81 0.39 0.50 PCB 170 0.36 0.50PCB 87 0.43 0.50 PCB 177 0.61 1.00PCB 99 0.41 0.50 PCB 180 0.38 0.50PCB 101 0.47 0.50 PCB 183 0.57 1.00PCB 105 0.58 1.00 PCB 187 0.55 1.00PCB 110 0.58 1.00 PCB 189 0.34 0.50PCB 114 0.49 0.50 PCB 194 0.29 0.50PCB 118 0.76 1.00 PCB 201 0.58 1.00PCB 119 0.32 0.50 PCB 206 0.36 0.50PCB 123 0.43 0.50
Table C–1 continues.
C-3
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Table C–1 continued.
Parameter MDL (ng/g dry)RL (ng/g dry)Parameter MDL (ng/g dry)RL (ng/g dry)
PAH Compounds1,6,7-Trimethylnaphthalene 0.87 1.00 Benzo[g,h,i]perylene 2.34 5.001-Methylnaphthalene 1.15 2.00 Benzo[k]fluoranthene 1.07 2.001-Methylphenanthrene 1.09 2.00 Biphenyl 1.22 2.002,3,6-Trimethylnaphthalene 1.03 2.00 Chrysene 1.09 2.002,6-Dimethylnaphthalene 1.01 2.00 Dibenz[a,h]anthracene 2.96 5.002-Methylnaphthalene 1.64 2.00 Dibenzothiophene 0.69 1.00Acenaphthene0.70 1.00 Fluoranthene 0.98 1.00Acenaphthylene0.79 1.00 Fluorene 1.26 2.00Anthracene0.83 1.00 Indeno[1,2,3-c,d]pyrene 2.19 5.00Benz[a]anthracene 1.07 2.00 Naphthalene 2.80 5.00Benzo[a]pyrene 0.98 1.00 Perylene 1.33 2.00Benzo[b]fluoranthene 0.95 1.00 Phenanthrene 0.87 1.00Benzo[e]pyrene 1.20 2.00 Pyrene 1.27 2.00
Parameter MDL (µg/kg dry)RL (µg/kg dry)Parameter MDL (µg/kg dry)RL (µg/kg dry)
MetalsAntimony0.116 0.200 Lead 0.040 0.100Arsenic0.054 0.100 Mercury 0.038 0.040Barium0.151 0.200 Nickel 0.114 0.200Beryllium0.030 0.100 Selenium 0.481 0.500Cadmium0.089 0.100 Silver 0.139 0.200Chromium0.058 0.100 Zinc 0.862 1.500Copper0.138 0.200
Parameter MDL (mg/kg dry)RL (mg/kg dry)Parameter MDL (%)RL (%)
Miscellaneous ParametersDissolved Sulfides 1.03 1.03 Total Organic Carbon 0.02 0.10Total Nitrogen (Summer)0.52 65.00 Grain Size 0.01 0.01Total Nitrogen (Winter)0.49 120.00Total Phosphorus (Summer)0.36 7.90Total Phosphorus (Winter)0.18 3.80
Fish Tissue
Parameter MDL (ng/g wet)RL (ng/g wet)Parameter MDL (ng/g wet)RL (ng/g wet)
Organochlorine Pesticides2,4’-DDD 1.22 2.00 cis-Chlordane 1.40 2.002,4’-DDE 1.41 2.00 trans-Chlordane 0.94 1.002,4’-DDT 1.58 2.00 Oxychlordane 2.64 5.004,4’-DDD 2.16 5.00 Heptachlor 2.25 5.004,4’-DDE 1.12 2.00 Heptachlor epoxide 1.26 2.004,4’-DDT 1.20 2.00 cis-Nonachlor 1.21 2.004,4’-DDMU 1.28 2.00 trans-Nonachlor 1.13 2.00Dieldrin2.41 5.00 PCB CongenersPCB 18 1.89 1.89 PCB 126 0.91 1.00PCB 28 1.33 1.33 PCB 128 1.07 1.07PCB 37 1.64 1.64 PCB 138 0.79 1.00PCB 44 1.19 1.19 PCB 149 0.89 1.00PCB 49 0.62 1.00 PCB 151 0.93 1.00PCB 52 0.69 1.00 PCB 153/168 1.46 1.46PCB 66 0.85 1.00 PCB 156 0.72 1.00PCB 70 1.35 1.35 PCB 157 0.75 1.00PCB 74 2.06 2.06 PCB 167 0.70 1.00PCB 77 1.06 1.06 PCB 169 0.69 1.00PCB 81 0.70 1.00 PCB 170 0.70 1.00PCB 87 0.78 1.00 PCB 177 1.12 1.12PCB 99 0.61 1.00 PCB 180 1.13 1.13PCB 101 1.45 1.45 PCB 183 0.66 1.00PCB 105 1.17 1.17 PCB 187 0.59 1.00PCB 110 0.92 1.00 PCB 189 0.94 1.00PCB 114 0.72 1.00 PCB 194 0.71 1.00PCB 118 0.76 1.00 PCB 201 0.86 1.00PCB 119 0.70 1.00 PCB 206 0.57 1.00PCB 123 1.12 1.12
Parameter MDL (µg/kg wet)RL (µg/kg wet)Parameter MDL (µg/kg wet)RL (µg/kg wet)
MetalsArsenic0.054 0.100 Mercury 0.008 0.020
Selenium 0.481 0.500
* Values reported between the MDL and the RL were estimated.
(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
Enterolert™ for enterococci and Colilert-18™ 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
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Table C–2 Water quality QA/QC summary, July 2018-June 2019.
Quarter Parameter Total samples (Total batches)QA/QC Sample Type
Number of QA/QC Samples Tested
Number of Compounds Tested
Number of Compounds Passed
% Compounds Passed *
Summer Ammonium 650 (8)
Blank 38 1 38 100Blank Spike 38 1 38 100Matrix Spike 69 1 69 100Matrix Spike Dup 69 1 69 100Matrix Spike Precision 69 1 69 100
Fall Ammonium 654 (10)
Blank 39 1 39 100Blank Spike 39 1 39 100Matrix Spike 71 1 71 100Matrix Spike Dup 71 1 71 100Matrix Spike Precision 71 1 71 100
Winter Ammonium 735 (10)
Blank 44 1 44 100Blank Spike 44 1 44 100Matrix Spike 79 1 79 100Matrix Spike Dup 79 1 79 100Matrix Spike Precision 79 1 79 100
Spring Ammonium 654 (8)
Blank 38 1 38 100Blank Spike 38 1 38 100Matrix Spike 69 1 69 100Matrix Spike Dup 69 1 69 100Matrix 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%.
Summer Total Coliforms 35 (5)Duplicate 35 1 33 94Fecal Coliforms 35 (5)Duplicate 35 1 33 94Enterococci35 (5)Duplicate 35 1 28 80
Fall Total Coliforms 35 (5)Duplicate 35 1 33 94Fecal Coliforms 35 (5)Duplicate 35 1 31 89Enterococci35 (5)Duplicate 35 1 32 91
Winter Total Coliforms 35 (5)Duplicate 35 1 33 94Fecal Coliforms 35 (5)Duplicate 35 1 32 91Enterococci35 (5)Duplicate 35 1 29 83
Spring Total Coliforms 35 (5)Duplicate 35 1 32 91Fecal Coliforms 35 (5)Duplicate 35 1 32 91Enterococci35 (5)Duplicate 35 1 31 89
Annual Total Coliforms 140 (20)Duplicate 140 1 131 94Fecal Coliforms 140 (20)Duplicate 140 1 128 91Enterococci 140 (20) Duplicate 140 1 120 86
* Analysis passed if the average range of logarithms is less than the precision criterion.
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
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Table C–3 Acceptance criteria for standard reference materials, July 2018-June 2019.
Sediments
Parameter True Value Acceptance Range (ng/g)
(ng/g)Minimum Maximum
Organochlorine Pesticides, PCB Congeners, and Percent Dry Weight
(SRM 1944; New York/New Jersey Waterway Sediment, National Institute of Standards and Technology)PCB 8 22.3 13.38 31.22PCB 18 51.0 30.6 71.4PCB 28 80.8 48.48 113.12PCB 44 60.2 36.12 84.28PCB 49 53.0 31.8 74.2PCB 52 79.4 47.64 111.16PCB 66 71.9 43.14 100.66PCB 87 29.9 17.94 41.86PCB 99 37.5 22.5 52.5PCB 101 73.4 44.04 102.76PCB 105 24.5 14.7 34.3PCB 110 63.5 38.1 88.9PCB 118 58.0 34.8 81.2PCB 128 8.47 5.082 11.86PCB 138 62.1 37.26 86.94PCB 149 49.7 29.82 69.58PCB 151 16.93 10.16 23.70PCB 153/168 74.0 44.4 103.6PCB 156 6.52 3.912 9.128PCB 170 22.6 13.56 31.64PCB 180 44.3 26.58 62.02PCB 183 12.19 7.314 17.07PCB 187 25.1 15.06 35.14PCB 194 11.2 6.72 15.68PCB 195 3.75 2.25 5.25PCB 206 9.21 5.53 12.89PCB 209 6.81 4.09 9.532,4’-DDD *38.0 22.8 53.22,4’-DDE *19.0 11.4 26.64,4’-DDD *108.0 64.8 151.24,4’-DDE *86.0 51.6 120.44,4’-DDT *170.0 102 238cis-Chlordane 16.51 9.91 23.11trans-Chlordane *19.0 11.4 26.6gamma-BHC *2.0 1.2 2.8Hexachlorobenzene6.03 3.62 8.44
trans-Nonachlor 8.20 4.92 11.48Percent Dry Weight 1.3 ––PAH Compounds and Percent Dry Weight (SRM 1944; New York/New Jersey Waterway Sediment, National Institute of Standards and Technology)1-Methylnaphthalene *470 282 6581-Methylphenanthrene *1700 1020 23802-Methylnaphthalene *740 444 1036Acenaphthene *390 234 546Anthracene *1130 678 1582Benz[a]anthracene 4720 2832 6608Benzo[a]pyrene 4300 2580 6020Benzo[b]fluoranthene 3870 2322 5418Benzo[e]pyrene 3280 1968 4592Benzo[g,h,i]perylene 2840 1704 3976Benzo[k]fluoranthene 2300 1380 3220Biphenyl *250 150 350Chrysene486029166804Dibenz[a,h]anthracene 424 254 594Dibenzothiophene *500 300 700Fluoranthene8920535212488Fluorene *480 288 672Indeno[1,2,3-c,d]pyrene 2780 1668 3892Naphthalene *1280 768 1792Perylene11707021638Phenanthrene527031627378Pyrene9700582013580Percent Dry Weight 98.7 ––
Table C–3 continues.
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Table C–3 continued.
Parameter True Value Acceptance Range (mg/kg)
(mg/kg)Minimum Maximum
Metals
(CRM-540 ERA Metals in Soil; Lot No. D099-540)Antimony 75.5 14.5 199Arsenic161113209Barium260195325Beryllium97.6 73.2 112Cadmium211158264Chromium13695.2 177Copper166124207Lead11178.8 143Mercury11.5 6.87 16Nickel91.9 64.3 119Selenium191131252Silver43.3 30.1 56.5Zinc199139259
Fish Tissue
Parameter True Value Acceptance Range (ng/g)
(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 1.176PCB 28 *2.0 1.2 2.8PCB 44 4.66 2.796 6.524PCB 49 3.80 2.28 5.32PCB 52 8.10 4.86 11.34PCB 66 10.8 6.48 15.12PCB 70 14.9 8.94 20.86PCB 74 4.83 2.898 6.762PCB 77 0.327 0.196 0.458PCB 87 9.40 5.64 13.16PCB 99 25.6 15.36 35.84PCB 101 34.6 20.76 48.44PCB 105 19.9 11.94 27.86PCB 110 22.8 13.68 31.92PCB 118 52.1 31.26 72.94PCB 126 0.380 0.228 0.532PCB 128 22.8 13.68 31.92PCB 138 115 69 161PCB 149 26.3 15.78 36.82PCB 153/168 170 102 238PCB 156 9.52 5.712 13.328PCB 170 25.2 15.12 35.28PCB 180 74.4 44.64 104.16PCB 183 21.9 13.14 30.66PCB 187 55.2 33.12 77.28PCB 194 13.0 7.8 18.2PCB 201 *2.83 1.698 3.962PCB 206 5.40 3.24 7.562,4’-DDD 2.20 1.32 3.082,4’-DDE *1.04 0.624 1.4562,4’-DDT *22.3 13.38 31.224,4’-DDD 17.7 10.62 24.784,4’-DDE 373 223.8 522.24,4’-DDT 37.2 22.32 52.08cis-Chlordane 32.5 19.5 45.5trans-Chlordane 8.36 5.016 11.704Oxychlordane18.90 11.34 26.46Dieldrin32.5 19.5 45.5Heptachlor epoxide 5.5 3.3 7.7cis-Nonachlor 59.1 35.46 82.74trans-Nonachlor 99.6 59.76 139.44
Parameter True Value Acceptance Range (%)
(%)Minimum Maximum
Lipid (SRM1946, Lake Superior Fish Tissue; National Institute of Standards and Technology)Lipid *10.17 6.1 14.2
Parameter True Value Acceptance Range (mg/kg)
(mg/kg)Minimum Maximum
Metals (SRM DORM-4; National Research Council Canada)Arsenic 6.87 4.81 8.93Selenium *3.45 2.42 4.49Mercury0.412 0.288 0.536
* Parameter with non-certified value(s).
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Table C–4 Sediment QA/QC summary, July 2018-June 2019.
Quarter Parameter Total samples (Total batches)QA/QC Sample Type
Number of QA/QC Samples Tested
Number of Compounds Tested
Number of Compounds Passed
% Compounds Passed *
Summer PAHs 29 (2)
Blank 2 26 52 100Blank Spike 2 26 52 100Matrix Spike 2 26 52 100Matrix Spike Duplicate 2 26 52 100Matrix Spike Precision 2 26 52 100SRM Analysis 2 21 36 86
Winter PAHs 29 (2)
Blank 2 25 50 100Blank Spike 2 25 49 98Matrix Spike 2 25 50 100Matrix Spike Duplicate 2 25 50 100Matrix Spike Precision 1 25 25 100SRM 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.
Summer PCBs and Pesticides 29 (2)
Blank 2 60 120 100Blank Spike 2 60 110 92Matrix Spike 2 60 70 58Matrix Spike Duplicate 2 60 68 57Matrix Spike Precision 2 60 120 100SRM Analysis 2 33 56 85
Winter PCBs and Pesticides 29 (2)
Blank 2 60 120 100Blank Spike 2 60 100 83Matrix Spike 2 60 119 99Matrix Spike Duplicate 2 60 120 100Matrix Spike Precision 2 60 120 100SRM 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.
Summer
Antimony, Arsenic, Barium, Beryllium, Cadmium, Chromium,
Copper, Lead, Nickel, Selenium, Silver, Zinc
29 (1)
Blank 4 12 48 100Blank Spike 2 12 24 100Matrix Spike 4 12 43 90Matrix Spike Dup 4 12 43 90Matrix Spike Precision 4 12 48 100Duplicate4124390SRM Analysis 1 12 12 100
Summer Mercury 29 (1)
Blank 2 1 2 100Blank Spike 2 1 2 100Matrix Spike 4 1 4 100Matrix Spike Dup 4 1 4 100Matrix Spike Precision 4 1 4 100Duplicate414100SRM Analysis 1 1 1 100
Winter
Antimony, Arsenic, Barium, Beryllium, Cadmium, Chromium, Copper, Lead, Nickel, Selenium, Silver, Zinc
29 (1)
Blank 4 12 47 98Blank Spike 2 12 24 100Matrix Spike 3 12 33 92Matrix Spike Dup 3 12 33 92Matrix Spike Precision 3 12 36 100Duplicate31236100SRM Analysis 1 12 12 100
Winter Mercury 29 (1)
Blank 2 1 2 100Blank Spike 2 1 2 100Matrix Spike 3 1 2 100Matrix Spike Dup 3 1 2 100Matrix Spike Precision 3 1 2 100Duplicate31267SRM 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.
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Quality Assurance/Quality Control
Table C–4 continued.
Quarter Parameter Total samples (Total batches)QA/QC Sample Type
Number of QA/QC Samples Tested
Number of Compounds Tested
Number of Compounds Passed
% Compounds Passed *
Summer Dissolved Sulfides 29 (2)
Blank 2 1 2 100Blank Spike 2 1 0 0Matrix Spike 3 1 3 100Matrix Spike Dup 3 1 3 100Matrix Spike Precision 3 1 3 100Duplicate310N/A
Winter Dissolved Sulfides 29 (3)
Blank 3 1 3 100Blank Spike 3 1 2 67Matrix Spike 3 1 3 100Matrix Spike Dup 3 1 3 100Matrix Spike Precision 3 1 3 100Duplicate313100
* 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.
Summer TOC 29 (1)
Blank 2 1 2 100Blank Spike 2 1 2 100Matrix Spike 2 1 2 100Matrix Spike Dup 2 1 2 100Matrix Spike Precision 2 1 2 100Duplicate313100
Winter TOC 29 (1)
Blank 2 1 2 100Blank Spike 2 1 2 100Matrix Spike 2 1 2 100Matrix Spike Dup 2 1 2 100Matrix Spike Precision 2 1 2 100Duplicate313100
* 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 100WinterGrain 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.
Summer Total N 29 (1)
Blank 5 1 5 100Blank Spike 5 1 5 100Matrix Spike 6 1 4 67Matrix Spike Dup 6 1 4 67Matrix Spike Precision 6 1 5 83Duplicate31267
Winter Total N 29 (1)
Blank 5 1 5 100Blank Spike 5 1 5 100Matrix Spike 5 1 2 40Matrix Spike Dup 5 1 2 40Matrix Spike Precision 5 1 5 100Duplicate313100
* 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.
Summer Total P 29 (1)
Blank 2 1 2 100Blank Spike 2 1 2 100Matrix Spike 2 1 1 50Matrix Spike Dup 2 1 1 50Matrix Spike Precision 2 1 2 100Duplicate414100
Winter Total P 29 (1)
Blank 2 1 2 100Blank Spike 2 1 2 100Matrix Spike 2 1 0 0Matrix Spike Dup 2 1 1 50Matrix Spike Precision 2 1 1 50Duplicate313100
* 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.
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
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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 µL 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.
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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.
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Table C–5 Fish tissue QA/QC summary, July 2018-June 2019.
Quarter Parameter Total samples (Total batches)QA/QC Sample Type
Number of QA/QC Samples Tested
Number of Compounds Tested
Number of Compounds Passed
% Compounds Passed *
Summer PCBs and Pesticides 70 (4)
Blank 8 54 432 100Blank Spike 7 54 356 94Matrix Spike 4 54 201 93Matrix Spike Dup 4 54 197 91Matrix Spike Precision 4 54 204 94Duplicate254108100SRM 4 38 128 84
Spring PCBs and Pesticides 20 (2)
Blank 4 54 216 100Blank Spike 4 54 191 88Matrix Spike 2 54 100 93Matrix Spike Dup 2 54 92 85Matrix Spike Precision 2 54 102 94Duplicate25410799SRM 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.
Summer
Percent Lipid - Liver 35 (2)Duplicate 2 1 2 100SRM 2 1 2 100Percent Lipid - Muscle 35 (2)Duplicate 2 1 2 100SRM 2 1 2 100
Spring Percent Lipid - Muscle 20 (2)Duplicate 2 1 2 100SRM 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.
Summer Mercury 70 (2)
Blank 4 1 4 100Blank Spike 4 1 4 100Matrix Spike 7 1 7 100Matrix Spike Dup 7 1 7 100Matrix Spike Precision 7 1 7 100Duplicate717100SRM Analysis 2 1 2 100
Spring Arsenic & Selenium 20 (1)
Blank 3 2 6 100Blank Spike 1 2 2 100Matrix Spike 2 2 4 100Matrix Spike Dup 2 2 4 100Matrix Spike Precision 2 2 4 100Duplicate224100SRM Analysis 1 2 2 100
Spring Mercury 20 (1)
Blank 1 1 1 100Blank Spike 1 1 1 100Matrix Spike 2 1 2 100Matrix Spike Dup 2 1 2 100Matrix Spike Precision 2 1 2 100Duplicate212100SRM 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 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 infaunal 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 ≤5% 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 = (|# Individuals Resolved − # Individuals Original| ÷ # Individuals Resolved) × 100
Equation 2: %Error # ID Taxa = (# Taxa Misidentification ÷ # Taxa Resolved) × 100
Equation 3: %Error # ID Individuals = (# 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
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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.
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Table C–6 Percent error rates calculated for the July 2018 infauna QA samples.
Error Type Station Mean08586C
1. %Error # Individuals 1.1 1.8 1.6 2.4 1.72. %Error # ID Taxa 11.0 2.2 0.9 7.4 5.43. %Error # ID Individuals 3.4 1.1 0.3 3.2 2.0
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.
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ORANGE COUNTY SANITATION DISTRICT
Laboratory, Monitoring, and Compliance Division
10844 Ellis Avenue
Fountain Valley, California 92708-7018
714.962.2411
www.ocsewers.com
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