________________________________________________________________________________

United States Office of Water EPA-822-P-16-001

Environmental Protection 4304T July 2016

Agency

DRAFT AQUATIC LIFE AMBIENT 

ESTUARINE/MARINE WATER 

QUALITY CRITERIA FOR

COPPER - 2016
ii

EPA-822-P-16-001

DRAFT AQUATIC LIFE

AMBIENT ESTUARINE/MARINE WATER QUALITY CRITERIA FOR

COPPER - 2016

(CAS Registry Number 7440-50-8)

July 2016

U.S. ENVIRONMENTAL PROTECTION AGENCY

OFFICE OF WATER

OFFICE OF SCIENCE AND TECHNOLOGY

HEALTH AND ECOLOGICAL CRITERIA DIVISION

WASHINGTON, D.C.
iii

NOTICES

This document provides information for states and tribes authorized to administer a water 

quality standards program, to consider in adopting water quality standards under the Clean Water 

Act (CWA), to protect aquatic life from toxic effects of copper in estuarine/marine 

environments. Under the CWA, states and tribes are to adopt water quality criteria to protect 

designated uses. State and tribal decision makers retain the discretion to adopt approaches on a 

case-by-case basis that differ from these criteria when appropriate. While this document contains 

EPA’s scientific recommendations regarding ambient concentrations of copper in 

estuarine/marine environments that protect aquatic life, it does not substitute for the CWA or 

EPA’s regulations; nor is it a regulation itself. Thus, it cannot impose legally binding 

requirements on EPA, states, tribes, or the regulated community, and might not apply to a 

particular situation based upon the circumstances. EPA may change this document in the future. 

This document has been approved for publication by the Office of Science and Technology, 

Office of Water, U.S. Environmental Protection Agency. 

Mention of trade names or commercial products does not constitute endorsement or 

recommendation for use. This document can be downloaded from: 

http://www.epa.gov/waterscience/criteria/aqlife.html.
iv

FOREWORD

Section 304(a) (l) of the Clean Water Act, 33 U.S.C. § 1314(a)(1), directs the 

Administrator of the Environmental Protection Agency to publish water quality criteria that 

accurately reflect the latest scientific knowledge on the kind and extent of all identifiable effects 

on health and welfare that might be expected from the presence of pollutants in any body of 

water, including ground water. This document is EPA’s new recommended ambient water 

quality criteria (AWQC) for the protection of aquatic life based upon consideration of available 

information relating to effects of copper on estuarine/marine organisms, and consideration of 

independent external peer review and EPA workgroup comments. 

The term "water quality criteria" is used in two sections of the Clean Water Act: section 

304(a)(l) and section 303(c)(2). The term has different meanings in each section. In section 304, 

the term represents a non-regulatory, scientific assessment of ecological and human health 

effects. The criteria presented in this document are such a scientific assessment of ecological 

effects. In section 303(c), the term water quality criteria refer to criteria adopted by a state or 

authorized tribe as part of their legally-binding water quality standards. Criteria in water quality 

standards establish the maximum acceptable pollutant concentrations in ambient waters 

protective of the state’s designated uses. States and authorized tribes may adopt water quality 

criteria in their water quality standards that have the same numerical values as EPA’s 

recommended section 304(a)(1) criteria. However, states and authorized tribes may decide to 

adopt water quality criteria different from EPA’s section 304 recommendations to reflect local 

environmental conditions and human exposure patterns. Alternatively, states and authorized 

tribes may use different data and assumptions than EPA in deriving numeric criteria that are 

scientifically defensible and protective of designated uses. It is not until their adoption as part of 

state or tribal water quality standards and approved by EPA (or in limited instances promulgated 

by EPA) under section 303(c) that criteria become applicable water quality standards for Clean 

Water Act purposes. Information to assist the states and authorized tribes in modifying the 

recommended criteria presented in this document is contained in the Water Quality Standards 

Handbook (U.S. EPA 2014). This handbook and additional information on the development of 

water quality standards and other water-related programs of this agency have been developed by 

the Office of Water. 

This document does not establish or affect legal rights or obligations. It does not establish 

a binding norm and cannot be finally determinative of the issues addressed. Agency decisions in 

any particular situation will be made by applying the Clean Water Act and EPA regulations on 

the basis of specific facts presented and scientific information then available. 

Elizabeth Southerland

Director 

Office of Science and Technology
v

AUTHORS / REVIEWERS / ACKNOWLEDGEMENTS

Technical Analysis Leads

Michael Elias, Office of Water, Office of Science and Technology, Health and Ecological 

Criteria Division, Washington, DC

elias.mike@epa.gov

Joseph Beaman, Office of Water, Office of Science and Technology, Health and Ecological 

Criteria Division, Washington, DC

Reviewers (2016)

Elizabeth Behl, Colleen Flaherty, Kathryn Gallagher, Office of Water, Office of Science and 

Technology, Health and Ecological Criteria Division, Washington, DC

EPA Peer Reviewers (2016)

Cindy Roberts, U.S. EPA, Office of Research and Development, Office of Science Policy, 

Washington, DC

Russ Erickson, U.S. EPA, Office of Research and Development, Mid-Continent Ecology 

Division, Duluth, MN

Glynis Hill, U.S. EPA, Office of Policy, Office of Regulatory Policy and Management, 

Washington, DC

Jeff Gallagher, U.S. EPA, Office of Chemical Safety and Pollution Prevention, Office of 

Pollution Prevention and Toxics, Washington, DC

Keith Sappington, U.S. EPA, Office of Chemical Safety and Pollution Prevention, Office of 

Pesticides Programs, Arlington, VA

Lars Wilcut and Heather Goss, U.S. EPA, Office of Water, Office of Science and Technology, 

Washington, DC

David Hair and William Cooper, U.S. EPA, Office of Water, Office of Wastewater Management, 

Washington, DC

Joel Hansel, U.S. EPA Region 4, Atlanta, GA

Candice Bauer, U.S. EPA Region 5, Chicago, IL

Lareina Guenzel, U.S. EPA Region 8, Denver, CO

Jane Hashimoto and Terrence Fleming, U.S. EPA Region 9, San Francisco, CA

Mark Jankowski, U.S. EPA Region 10, Seattle, WA
vi

EXECUTIVE SUMMARY

Guidance documents containing aquatic life criteria recommendations for copper (Cu) 

have been updated and published by EPA over the past 30 years as new science becomes 

available (e.g., U.S. EPA 1980, 1984, 1986a, 1995a, 1996, 2003, 2007). EPA’s most recent 2007 

updated recommended criteria for copper only provided an update for freshwater organisms, and 

differed from EPA’s previous metals criteria in that the biotic ligand model (BLM) (Di Toro et 

al. 2001) addressed the metal availability to organisms. The complexing ligands in water 

compete with the biotic ligand for metals and other cations in the water. Unlike the empirical 

toxicity to water hardness relationships, which EPA used to establish copper criteria prior to 

2007, the BLM explicitly accounts for individual water quality variables, is not linked to a 

particular correlation amongst the variables, and can address variables that are not a factor in the 

hardness relationship. EPA did not update estuarine/marine criteria in 2007 because a saltwater 

BLM had not been sufficiently developed and tested at that time. 

This document utilizes the recently developed saltwater BLM to provide updated BLMbased acute and chronic water quality criteria (WQC) for copper that are applicable to both 

estuarine and marine waters. This saltwater BLM includes a new characterization of copper 

binding to natural organic matter (NOM) in estuarine/marine systems and considers the binding 

of copper to the surface membranes of embryo-larval stages of several sensitive marine 

invertebrates. Development of the saltwater BLM for copper is detailed in Chadwick et al. 

(2008).

EPA is developing the recommended ambient WQC for copper in estuarine/marine 

waters pursuant to its authority under §304(a)(1) of the Clean Water Act (CWA). EPA developed 

the copper aquatic life criteria using peer reviewed methods and data that EPA determined to be 

acceptable for their derivation as described in U.S. EPA’s “Guidelines for Deriving Numerical 

National Water Quality Criteria for the Protection of Aquatic Organisms and Their Uses” 

(Guidelines) (Stephan et al. 1985). This update includes the evaluation of data submitted in

support of the registration of copper-containing pesticides that were reviewed by EPA’s Office 

of Pesticide Programs and studies reported in the open literature. 

The resulting recommended ambient WQC indicate that estuarine/marine aquatic 

organisms would have an appropriate level of protection if the 1-hour average and four-day 
vii

average dissolved copper concentrations do not respectively exceed the acute and chronic criteria 

concentrations calculated by the saltwater BLM more than once every three years on average. 

For the 2016 draft acute criteria, EPA has changed the duration to 1 hour from the 24 hours EPA 

recommended in the 2003 draft copper criteria for estuarine/marine organisms and the 2007 

recommended freshwater copper criteria. EPA made this change to the 2016 criteria to reflect the 

acute criteria duration recommended in EPA’s Guidelines (see Section 4.1.2). Because this 

updated WQC relies on the BLM, the numeric WQC change accordingly in response to changes

in water quality parameters (i.e., temperature, salinity, dissolved organic carbon and pH). At an 

example pH of 8.0, temperature of 22°C, DOC of 1.0 mg/L and salinity of 32 ppt, the 2016 acute 

criterion magnitude is 2.0 μg/L copper (lowered to protect the commercially important red 

abalone Haliotis rufescens), and the chronic criterion magnitude is 1.3 μg/L copper. Additional 

examples at different water chemistry conditions are provided in Appendix I.

This document provides guidance to states and authorized tribes to consider in adopting 

water quality standards under the CWA to protect estuarine/marine aquatic life from the acute 

and chronic effects of copper. Under the CWA, states and authorized tribes may adopt these 

WQC into water quality standards to protect designated uses. While this document constitutes 

EPA’s scientific recommendations regarding ambient concentrations of copper, this document 

does not substitute for the CWA or EPA’s regulations, nor is it a regulation itself. Thus, it cannot 

impose legally binding requirements on EPA, states, authorized tribes, or the regulated 

community, and it might not apply to a particular situation based upon the circumstances. State 

and tribal decision-makers retain the discretion to adopt approaches on a case-by-case basis that 

differ from this guidance when appropriate.
viii

TABLE OF CONTENTS

NOTICES.......................................................................................................................................iii

FOREWORD................................................................................................................................. iv

AUTHORS / REVIEWERS / ACKNOWLEDGEMENTS............................................................ v

EXECUTIVE SUMMARY ........................................................................................................... vi

TABLE OF CONTENTS............................................................................................................. viii

LIST OF FIGURES ....................................................................................................................... ix

LIST OF TABLES.......................................................................................................................... x

LIST OF APPENDICIES ............................................................................................................... x

ACRONYMS................................................................................................................................. xi

1 INTRODUCTION .................................................................................................................. 1

2 PROBLEM FORMULATION................................................................................................ 4

2.1 Overview of Copper Sources and Occurrence................................................................ 4

2.2 Environmental Fate and Transport of Copper in the Aquatic Environment................. 12

2.3 Overview of Copper Toxicity ....................................................................................... 14

2.4 Overview of Historic and BLM Criteria Development Methods ................................. 17

2.5 Conceptual Model......................................................................................................... 29

2.6 Assessment Endpoints .................................................................................................. 31

2.7 Measurement Endpoints................................................................................................ 31

2.7.1 Overview of Toxicity Data Requirements................................................................ 32

2.7.2 Measures of Effect .................................................................................................... 33

2.8 Analysis Plan ................................................................................................................ 36

2.8.1 Acute Criterion Derivation ....................................................................................... 37

2.8.2 Chronic Criterion Derivation .................................................................................... 38

2.8.3 BLM Evaluation........................................................................................................ 38

3 EFFECTS ANALYSES FOR AQUATIC ORGANISMS.................................................... 41

3.1 Summary of Acute Studies ........................................................................................... 41

3.2 Summary of Chronic Studies........................................................................................ 46

3.3 Summary of BLM Water Quality Input Parameters..................................................... 47

3.4 Bioaccumulation ........................................................................................................... 48

3.5 Toxicity to Aquatic Plants ............................................................................................ 48

3.6 The National Estuarine/Marine Criteria for Copper..................................................... 49

3.6.1 Acute Criterion Calculation ...................................................................................... 49

3.6.2 Chronic Criterion Calculation................................................................................... 53

3.7 Summary of National Criteria....................................................................................... 55

3.8 Identification of Data Gaps for Aquatic Organisms..................................................... 56

3.8.1 Chronic Toxicity Data for Estuarine/Marine Animals.............................................. 56

3.8.2 Chronic Toxicity Data for Aquatic Vascular Plants and Algae................................ 56

3.8.3 BLM Uncertainties and Performance ....................................................................... 57

4 EFFECTS CHARACTERIZATION .................................................................................... 58

4.1 Estuarine/Marine Acute Toxicity Data ......................................................................... 58

4.1.1 Uncertainty in the Estuarine/Marine FAV Calculation ............................................ 59

4.1.2 Acute Criteria Duration............................................................................................. 60

4.2 Estuarine/Marine Chronic Toxicity Data...................................................................... 61

4.2.1 Uncertainty in the Estuarine/Marine FCV Calculation............................................. 62
ix

4.3 Bioaccumulation ........................................................................................................... 63

4.3.1 Uncertainty with Copper Exposure Routes............................................................... 63

4.4 Effects on Aquatic Plants.............................................................................................. 67

4.5 Protection of Endangered Species ................................................................................ 68

4.5.1 Acute Toxicity Data for Listed Species.................................................................... 69

4.5.2 Chronic Toxicity Data for Listed Species................................................................. 69

4.6 Comparison of Draft 2003 and 2016 Criteria Values................................................... 69

5 REFERENCES ..................................................................................................................... 72

LIST OF FIGURES

Figure 1. Copper Usage Data for Agriculture................................................................................. 7

Figure 2. Environmental Bridging Chemical Species for Copper (Cu) Minerals and Complexes.

........................................................................................................................................ 14

Figure 3. Conceptual Diagram Showing Relationship between Chemical Speciation, Metal 

Binding at Biotic Ligand (BL) Sites, and Competition at These BL Sites for Other 

Cations. .......................................................................................................................... 20

Figure 4. Percent Abnormal Cells in Test Waters with Different Composition (primarily DOC) 

for M. galloprovincialis (Panel A) and S. purpuratus (Panel B)................................... 23

Figure 5. Predicted Copper Binding to Biotic Ligand Sites on Cell Membranes (solid lines) by 

the Saltwater BLM for Copper with a Single Set of Parameters Compared with 

Measured Copper Accumulation for Embryo-larval Stages of M. galloprovincialis

(Panel A) and S. purpuratus (Panel B). ......................................................................... 24

Figure 6. Predicted Copper Toxicity by the Saltwater BLM for Copper (solid lines) in Response 

to Changing DOC from a Variety of Estuarine and Marine Sites Compared with 

Measured Copper Toxicity for Embryo-larval Stages of M. galloprovincialis (Panel A) 

and S. purpuratus (Panel B)........................................................................................... 26

Figure 7. Predicted Copper Toxicity by the Saltwater BLM for Copper (solid lines) in Response 

to Changing DOC from a Variety of Estuarine and Marine Sites Compared with 

Measured Copper Toxicity for Embryo-larval Stages of Dendraster (Panel A) and 

Crassostrea (Panel B).................................................................................................... 27

Figure 8. Conceptual Model for Copper Effects on Aquatic Organisms...................................... 30

Figure 9. Ranked Estuarine/Marine GMAVs. .............................................................................. 51

Figure 10. Reported Dissolved Cu LC50s Ranked by the Geomean of the Normalized Cu Values 

(i.e., SMAVs)................................................................................................................. 52

Figure 11. Ranked Estuarine/Marine GMCVs.............................................................................. 55
x

LIST OF TABLES

Table 1. Ambient Dissolved and Total Copper Concentrations Reported for Coastal Harbors and 

Marinas. ......................................................................................................................... 12

Table 2. Summary of Assessment Endpoints and Measures of Effect Used in Criteria Derivation.

........................................................................................................................................ 32

Table 3. Summary Table of Acceptable Toxicity Data Used to Meet the Minimum Data 

Requirements in the “1985 Guidelines” and Count of Phyla, Families, Genera and 

Species. .......................................................................................................................... 35

Table 4. Water Quality Input Parameters for the Freshwater and Saltwater Versions of the BLM.

........................................................................................................................................ 39

Table 5. Ranked Estuarine/Marine Genus Mean Acute Values. .................................................. 42

Table 6. Ranked Estuarine/Marine Genus Mean Chronic Values with Species Mean AcuteChronic Ratios. .............................................................................................................. 47

Table 7. Water Quality Input Parameters Used for Saltwater BLM-Normalization. ................... 48

Table 8. Estuarine/Marine Water Final Acute Value (FAV) and Criteria Calculations............... 50

Table 9. Comparison of the Four Most Sensitive Taxa Used to Calculate the Estuarine/Marine 

FAV and CMC in the 2003 Draft Copper Document and 2016 Update........................ 71

LIST OF APPENDICIES

Appendix A Acceptable Estuarine/Marine Acute Toxicity Data ............................................ A-1

Appendix B Acceptable Chronic Toxicity Data...................................................................... B-1

Appendix C Estuarine/Marine Plant Toxicity Data ................................................................ C-1

Appendix D Acceptable Estuarine/Marine Bioaccumulation Data......................................... D-1

Appendix E Other Estuarine/Marine Toxicity Data.................................................................E-1

Appendix F Data Not Used in the Development of the Aquatic Life Ambient Estuarine/Marine 

Water Quality Criteria for Copper.......................................................................F-1

Appendix G Species Numbers Used in BLM Analysis........................................................... G-1

Appendix H Water Chemistry Used in BLM Analysis........................................................... H-1

Appendix I Discussion of BLM Water Quality Parameters in the Estuarine/Marine 

Environment and Example Numeric Criteria Values ...........................................I-1
xi

ACRONYMS

ACR Acute-Chronic Ratio

ALC Aquatic Life Criteria

BL Biotic Ligand

BLM Biotic Ligand Model

CCC Criterion Continuous Concentration

CF Conversion Factors

CHESS Chemical Equilibria in Soils and Solutions

CMC Criterion Maximum Concentration

CWA Clean Water Act

DIC Dissolved Inorganic Carbon

DOC Dissolved Organic Carbon

DOM Dissolved Organic Matter

EC50/EC20 Effect concentration to 50%/20% of the test population

ELS Early Life Stage

EPA Environmental Protection Agency

FACR Final Acute-Chronic Ratio

FAV Final Acute Value 

FCV Final Chronic Value

FFDCA Federal Food, Drug and Cosmetic Act 

FIAM Free Ion Activity Model

FQPA Food Quality Protection Act 

GDCI Generic Data Call-In

GMAV Genus Mean Acute Value

GMCV Genus Mean Chronic Value

GSIM Gill Surface Interaction Model

HA Humic Acid

IC50 Inhibition Concentration where effect is inhibited 50% compared to control organism

LA50 Lethal Level of Accumulation at 50% effect level

LC50 Lethal Concentration to 50% of the test population

LOAEC Lowest Observed Adverse Effect Concentration

LOEC Lowest Observed Effect Concentration

MATC Maximum Acceptable Toxicant Concentration (geometric mean of NOEC and LOEC)

MDR Minimum Data Requirements

Me:BL Metal-Biotic Ligand Complex

MSE Mean Square Error

NASQAN National Stream Quality Accounting Network

NOAEC No Observed Adverse Effect Concentration

NOEC No Observed Effect Concentration

NOM Natural Organic Matter

PLC Partial Life-Cycle

RED Reregistration Eligibility Decision 

SMAV Species Mean Acute Value

SMCV Species Mean Chronic Value

SSD Species Sensitivity Distribution

TSS Total Suspended Solids

WER Water-Effect Ratio

WET Whole Effluent Toxicity

WHAM Windermere Humic Aqueous Model

WQC Water Quality Criteria
1

1 INTRODUCTION

The U.S. Environmental Protection Agency (EPA) is developing ambient water quality 

criteria (WQC) for copper (Cu) for the protection of aquatic life in estuarine/marine waters 

through its authority under §304(a)(1) of the Clean Water Act (CWA). Over the past 30 years the 

EPA has published a number of guidance documents containing aquatic life criteria 

recommendations for copper (U.S. EPA 1980, 1984, 1986a, 1995a, 1996, 2003, and 2007). The 

most recent 2007 updated recommended WQC document only provided an update for freshwater 

criteria, and differed from EPA’s previous metals criteria primarily with regard to how metal 

availability to organisms is addressed. EPA based previous criteria recommendations on 

empirical relationships between toxicity and water hardness. In the 2007 freshwater acute and 

chronic recommended criteria, EPA instead used the biotic ligand model (BLM) (Di Toro et al. 

2001). The BLM is based on the premise that: (1) toxicity is related to the amount of metal 

bound to a biochemical site (the biotic ligand); and (2) binding is related to the total dissolved 

metal and complexing ligand concentrations in water. The biotic ligand is a binding site on

biological membranes which is associated with the mechanism of toxicity in the organism. Some 

ligands and cations complex with metals in water, while other elements compete for binding sites 

on the biotic ligand with the uncomplexed, bioavailable metals in water. Unlike the empirical 

hardness relationships, the BLM explicitly accounts for a broader range of water quality 

variables, including variables that are not a factor in the hardness relationship. The BLM is not 

linked to a particular correlation amongst these variables. 

EPA’s current recommended estuarine/marine criteria for copper are based on data for 33 

species representing 26 genera (U.S. EPA 1995a). EPA last updated the estuarine/marine criteria

as draft in 2003 and were derived without normalization of the available toxicity data. EPA 

based the draft 2003 acute criterion on Species Mean Acute Values (SMAVs) for 52 species in 

44 genera (34 invertebrates and 18 fish species), with mussels, oysters and the summer flounder

identified as the most sensitive species. Chronic saltwater tests were available only for the 

sheepshead minnow, Cyprinodon variegatus in the 2003 draft document. Sufficient toxicity data 

were available to fulfill requirements to calculate an acute estuarine/marine criterion using a 

species sensitivity distribution (SSD), as described in EPA’s Guidelines (Stephan et al. 1985). 

The Final Acute Value (FAV) and Criterion Maximum Concentration (CMC) were lowered to be 
2

protective of the commercially and recreationally important mussel, Mytilus. Data were not 

sufficient to calculate the chronic estuarine/marine criterion using a SSD, and therefore AcuteChronic Ratios (ACRs) were used to derive the 2003 draft criterion. 

EPA did not update the estuarine/marine criteria at the time of the 2007 release of the 

BLM-based freshwater criteria because the saltwater BLM had not been sufficiently developed 

or tested. This has now been addressed and details about the development of the saltwater 

version of the copper BLM were published in Chadwick et al. (2008). The saltwater BLM for 

copper includes a new description of copper binding to natural organic matter (NOM)

represented by dissolved organic carbon (DOC) in the model. DOC is an analytical measurement 

used to quantify NOM in marine systems, and considers copper binding to the biological

membranes of embryo-larval stages of several sensitive marine invertebrates. The chemical 

properties of NOM in saltwater and freshwater are similar as NOM from either medium can 

strongly affect the chemistry and bioavailability of copper to aquatic biota. However, the 

distribution of binding sites for NOM in marine waters differs enough from those in freshwater 

that a new BLM model was developed for saltwater. This document utilizes an updated version 

of the saltwater BLM, which was originally published in Chadwick et al. (2008), to provide

BLM-based water quality criteria for copper that are applicable to both estuarine and marine 

waters. Although the original development of the BLM (Chadwick et al. 2008) focused on 

several sensitive marine invertebrates, application of the model to the development of 

estuarine/marine WQC required changes to the model to account for additional species over a 

wider range of copper concentrations.

The present document contains EPA’s criteria recommendations for the protection of 

aquatic life in ambient estuarine/marine water from both acute and chronic toxic effects of

copper. EPA updated the estuarine/marine WQC provided in this document in accordance with 

methods outlined in the Agency’s “Guidelines for Deriving Numerical National Water Quality 

Criteria for the Protection of Aquatic Organisms and Their Uses” (EPA Guidelines) (Stephan et 

al. 1985). This document describes scientifically defensible water quality criteria values for 

copper in estuarine/marine waters pursuant to CWA §304(a)(1), derived utilizing best available 

data in a manner consistent with the EPA Guidelines and reflecting the latest available scientific 

information and best professional scientific judgments of toxicological effects. Once finalized, 
3

these criteria will supersede EPA’s previously published recommendations for copper in 

estuarine/marine water. 

This criteria document provides updated guidance to states and authorized tribes to adopt

water quality standards under the CWA to protect estuarine/marine aquatic life from copper. 

Under the CWA, states and authorized tribes adopt WQC to protect designated uses. Although 

this document constitutes EPA’s scientific recommendations regarding ambient concentrations 

of copper in estuarine/marine waters, it does not substitute for the CWA or EPA’s regulations, 

nor is it a regulation itself. Thus, it cannot impose legally binding requirements on EPA, states, 

authorized tribes, or the regulated community, and might not apply to a particular situation based 

on the circumstances. State and tribal decision makers retain the discretion in adopting 

approaches, on a case-by-case basis, that differ from this guidance when appropriate. 
4

2 PROBLEM FORMULATION

Problem formulation provides a strategic framework to develop water quality criteria by 

providing an overview of a chemical’s sources and occurrence, fate and transport in the 

environment, and toxicological characteristics and factors affecting toxicity. A problem 

formulation uses this information to develop a conceptual model and identify the most relevant 

chemical properties and endpoints for evaluation. The structure of the problem formulation 

developed for copper in estuarine/marine waters is consistent with U.S. EPA’s Guidelines for 

Ecological Risk Assessment (U.S. EPA 1998) and the approach used by EPA for pesticide 

effects assessment (U.S. EPA 2004).

Since copper is a registered pesticide in the United States, EPA issued Registration 

Standards in 1986 for copper sulfate (U.S. EPA 1986a) and in 1987 for Group II copper 

compounds (U.S. EPA 1987). As a result, Generic Data Call-In (GDCI) notices were issued to 

registrants in 1987 and 1993. The GDCI notices required registrants to submit ecological 

fate/effects studies and product chemistry/residue and avian toxicity studies for various copper 

compounds as part of the 40 CFR Part 158 data necessary to support reregistration (U.S. EPA 

2010a). In further support of reregistration, and as required by FIFRA and the Federal Food, 

Drug and Cosmetic Act (FFDCA) and amended by the Food Quality Protection Act (FQPA), 

EPA completed the copper Reregistration Eligibility Decision (RED). The RED was signed in 

July 2006 and was published, along with supporting documents, for public comment in August 

2006. The revised RED, which addressed the public comments, is available online (U.S. EPA 

2009).

2.1 Overview of Copper Sources and Occurrence

Copper is a naturally occurring element in the earth's crust, with concentrations typically 

ranging from 55 to 70 mg/kg (Nriagu 1979). U.S. soil levels commonly range from 1 to 40 

mg/kg and average around 9 mg/kg (Tisdale et al. 1985). Copper ranks 14th in relative abundance 

amongst all elements and is typically found combined with other minerals in the form of oxides, 

carbonates and sulfides (CDA 2003; Chemicool 2012). The highest copper concentrations are 

found in basaltic igneous rocks (averaging approximately 90 mg/kg), while much lower 

concentrations (averaging 4 mg/kg) are found in sedimentary limestones (CDA 2003).
5

Copper is commonly found in aquatic systems as a result of both natural and 

anthropogenic sources (Nriagu 1979). Natural sources of copper to aquatic systems include 

geological deposits, weathering and erosion of rocks and soils and volcanic activity (Kious and 

Tilling 1996). It is estimated that, on average, approximately 68% of the copper released to 

surface waters originates from these sources (ATSDR 1990). Naturally occurring copper

concentrations have been reported to range from 0.03 to 0.23 μg/L in surface seawaters (Bowen 

1985). In a review paper, Kennish (1998) reported copper concentrations ranging from 0.3 to 3.8 

μg/L in estuarine waters and from 0.1 to 2.5 μg/L in coastal waters of the United States. 

Copper concentrations in estuarine environments receiving anthropogenic inputs can 

range from background to more than 15 μg/L, and concentrations in impacted coastal waters 

have been reported to range from 0.5 to 2.6 μg/L (International Copper Association 2003). It

should be noted, however, that much of the quantitative metals data for samples collected from 

natural waters prior to the mid-1970s are considered inaccurate due to contamination from 

sampling methods or containers. 

Elevated concentrations of copper in the aquatic environment can result from both natural 

sources, such as from the erosion of soils, and from numerous anthropogenic point and nonpoint 

sources. The following discussion provides a description of some of the most notable 

anthropogenic sources.

A broad range of mining/resource extraction activities can represent a source of copper to 

the aquatic environment via both permitted discharges from active mines and uncontrolled 

releases from abandoned mines. Abandoned mines are a notable source of copper due to acid 

mine drainage, which solubilizes and transports a broad range of metals, including copper, to 

adjacent waterbodies. Copper mining activities can, in particular, represent a source of copper to 

the environment, with the majority of both historic and ongoing copper mining activity in the 

U.S. occurring in Arizona, Utah, New Mexico, Nevada and Montana (CDA 2012). EPA 

estimated that mining has impacted headwater streams in more than 40 percent of watersheds in 

the western United States (U.S. EPA 1994b, 2012a).

Copper is widely used in pesticides and elevated concentrations of copper in the 

environment can result from the application and use of registered pesticides. The first coppercontaining pesticide registration was issued in 1956. Currently, there are 19 copper compounds 
6

that have active food use registrations (12 for agricultural uses and 7 for antimicrobial uses) and 

that are subject to tolerance reassessment and registration review (U.S. EPA 2010a). 

Copper is widely used as a broad-spectrum bactericide, fungicide, antimicrobial, 

herbicide, algaecide, and molluscicide for a variety of agricultural, commercial and urban 

purposes. Marketed trade names include Kocide, CuproFix, Basicop, K-Tea, Cutrine Ultra and 

Triangle. In 2002, for example, it was estimated that approximately 106 million pounds of 

copper was applied nationwide as an agricultural fungicide (Figure 1). Primary applications 

were to rice (25%), citrus fruit (23%), walnuts (10%) and grapes (7%), with lesser amounts used 

on tomatoes, peaches, almonds, apples, cherries, and potatoes (U.S. EPA 2010a).

As pesticidal products, copper-containing compounds are also applied directly to aquatic 

systems to control algae, cyanobacteria, aquatic weeds, leeches, mollusks and tadpole shrimp 

(TDC Environmental 2004; U.S. EPA 2010a). Antimicrobial pesticide uses include wood 

preservatives including surface and pressure treatments, architectural and antifoulant paints, 

algae resistant roofing shingles, human drinking water treatment, and other material 

preservatives. Urban uses include application to control algae and moss in lawns, algae in 

outdoor swimming pools, and root growth in sewage and irrigation systems. 
7

Figure 1. Copper Usage Data for Agriculture.

(Source: http://water.usgs.gov/nawqa/pnsp/usage/maps/show_map.php?year=02&map=m5011, accessed 

on May 25, 2010).

Copper is an essential micronutrient for plant growth and agricultural fertilizers and 

biosolids containing copper are applied to bolster deficient soils and increase crop yields (CDA 

2003; University of Minnesota 2009). Copper is also used as a feed supplement for cattle and 

other livestock to prevent a deficiency that can make cattle less responsive to vaccines and more 

susceptible to disease (Oregon State University 2011), and to improve weight gain. Other 

agricultural uses include copper sulfate in dairy cattle foot baths to control hairy heel warts 

(Jokela et al. 2010), which can introduce copper to the environment. 

A number of other industries have been identified as sources of copper to the 

environment, including leather and leather product manufacturers, metal fabricators, and 

electrical equipment manufacturers, amongst others (Patterson et al. 1998; CDA 2003; TDC 

Environmental 2004). Copper is also released to the environment from the burning of fossil fuels 

(oil, diesel and coal) and wood (CDA 2003).

Urban runoff from the numerous and unrelated upland sources can cumulatively 

represent an important anthropogenic source of copper to surface water. In addition to the uses 
8

already discussed, sources of copper to runoff include copper roofs and gutters, chromate copper 

arsenate (CCA) treated wood1, automotive brake pads and tailpipe emissions, asphalt, coolant 

leaks and construction erosion. Storm water runoff is estimated to contribute approximately 2% 

of the total copper released to waterways (ASTDR 1990) compared to 68% contributed from 

soils through natural weathering and disturbance (Georgopoulis et al. 2001). However, in a study 

of copper sources to the San Francisco Bay, urban runoff was estimated to contribute 

approximately 53 percent of the copper loading to the Bay (45,000 to 47,000 pounds per year; 

TDC Environmental 2004). 

In estuarine and marine waters, and to lesser extent freshwater environments, antifouling 

paints and coatings (also known as Antifouling Systems or AFS’s) are pesticidal products used to 

protect boat/ship hulls, underwater surfaces, buoys and barges, while CCA-impregnated timbers

are used for the decking and pilings of boat docks and marine structures. Antifouling paints and 

coatings are intended to retard the growth of algae, weeds, and other encrusting organisms such 

as barnacles and mussels on the underwater portion of vessel hulls and underwater surfaces. 

These encrusting organisms can foul hulls and other underwater surfaces, increasing corrosion 

and drag, reducing safety and maneuverability, decreasing fuel efficiency and economy, and 

lengthening transit times (WHOI 1952). The development of antifouling paints and coatings has 

a long history, as mariners have tried for centuries to keep vessel hulls free from barnacles and 

other fouling growth (Thomas and Brooks 2010). In the late 1950s and early 1960s, antifouling 

paint formulations using tributyltin (TBT) were introduced and proved to be excellent at

preventing hull fouling. However, restrictions on the use of TBT-based compounds due to severe 

environmental impacts opened the market for manufacturers to develop new biocides for use on 

vessels (Kiaune and Singhasemanon 2011). Alternative metals, including copper and zinc, are 

currently used as substitutes for TBT.

The most common form of copper used in antifouling paints and coatings is cuprous 

oxide, which acts as a preventative biocide by leaching into the water. Most marine antifouling 

paints contain 40 to 70 percent cuprous oxide by weight. Since cuprous oxide is comprised of 89 

percent copper by weight, typical cuprous oxide marine antifouling paints are 36 to 62 percent 

copper by weight (TDC Environmental 2004). Although not as common, copper thiocyanate and 

 

1

In December 2003, chromated arsenicals manufacturers voluntarily discontinued manufacturing chromated 

arsenicals-treated wood products for homeowner uses (U.S. EPA 2010b)
9

copper hydroxide are also used as biocides in antifouling paints and coatings. Copper thiocyanate 

has the advantage of being compatible with aluminum. The contribution of copper to receiving 

waters from copper thiocyanate and copper hydroxide paints is small relative to biocides

containing cuprous oxide (TDC Environmental 2004).

Antifouling paints and coatings applied to vessel hulls represent one of the most 

commonly identified sources of copper in marinas. A number of studies have been done to 

estimate the loading of copper from these paints and coatings. EPA estimated that copper loading 

from the use of these biocides in California’s Lower Newport Bay, which harbors approximately 

10,000 boats, contributed more than 62,000 pounds of copper annually through passive leaching 

and underwater hull cleaning (U.S. EPA 2002). This release could account for as much as 80 

percent of the copper input into the Lower Newport Bay. Although this may represent an 

extreme case, based on the high number and density of boats that are docked and the minimal 

water circulation and flushing of the harbor, it illustrates the potential significance of antifouling 

paints and coatings as a source of copper to the aquatic environment. 

The U.S. Navy and private researchers conducted two copper source loading studies for 

the San Diego Bay in the late 1990s (Johnson et al. 1998; PRC Environmental Management, 

Inc.1997). Both studies concluded that antifouling paints and coatings accounted for the majority 

of dissolved copper loading to the bay. The San Diego Regional Water Quality Control Board 

estimated that passive leaching and the underwater hull cleaning of the 2,400 boats berthed in the 

Shelter Island Yacht Basin marina collectively contribute 98 percent of the copper discharged to 

the basin (Singhasemanon et al. 2009). Approximately 95 percent of the 1.8 pounds of copper

estimated to be released by each boat per year is believed to leach from antifouling paints and 

coatings while boats are moored at the dock, while the remaining five percent is believed to be 

released during underwater hull cleaning activities (TDC Environmental 2004). 

Copper leaching from vessel hulls represents a potential water quality concern in ports 

throughout the United States, including ports in the Chesapeake Bay, Port Canaveral and Indian 

River Lagoon in Florida, and various harbors in Washington State (Carson et al. 2009). In 

addition to AFS, antifouling paint particles are generated during boat maintenance and from 

abandoned structures and ships. These particles have the potential to leach metals more rapidly 

due to the increased surface area and also may be consumed by benthic invertebrates (Turner 

2010). 
10

As presented in EPA’s Study of Discharges Incidental to Normal Operation of 

Commercial Fishing Vessels and Other Non-Recreational Vessels Less than 79 Feet (U.S. EPA 

2010b), elevated levels of copper were found in the ambient water associated with a number of 

harbors and marinas (Table 1). A recent study of AFS biocides in California marinas found 

dissolved copper concentrations ranging from 0.1-18.4 μg/L in the water, which are similar to the 

range of concentrations reported in U.S. EPA (2010b). Concentrations were significantly higher 

in salt- and brackish water marinas than in freshwater marinas (Singhasemanon 2008).
11

Case Study: Mass Balance for Sources of Copper to the San Francisco Bay

There is a long history of investigation of copper sources to the San Francisco Bay and 

surrounding area, where copper has been a pollutant of concern since the late 1980s. The 1989 

designation of the lower South San Francisco Bay as impaired by copper (listing under §303(d) of 

the CWA) caused government agencies and businesses to make a significant investment in copper 

source identification andreduction measures. These activities created a wealth of information on 

copper releases to surface waters and greatly expanded the understanding of options to prevent or 

reduce copper releases to San Francisco Bay.

Copper Sources in Urban Runoff and Shoreline Activities (TDC Environmental 2004) was 

prepared for the Clean Estuary Partnership to summarize available information about the sources 

of copper in urban runoff that is released directly into the Bay from shoreline activities. Marine 

antifouling paint and copper algaecides applied to shoreline lagoons were included in the 

evaluation of direct release sources. The report did not address discharges from industrial or 

municipal wastewater treatment plants or non-urban copper sources, such as sediment erosion 

from open space, agricultural pesticide use, mine drainage, and reservoir releases. These were not 

considered to be significant sources of copper to urban runoff or from shoreline activities.

Nine categories of copper sources were found to have the potential to make a significant

contribution to copper levels in the San Francisco Bay Area via urban runoff and releases from 

shoreline activities. These sources are listed below, ordered from highest to lowest based on the 

estimated magnitude of loading:

 Marine antifouling coatings

 Vehicle brake pads

 Architectural copper

 Copper pesticides (including shoreline algaecides) and CCA-treated wood

 Industrial copper uses

 Copper air emissions

 Soil erosion

 Copper in domestic water discharged to storm drains

 Vehicle fluid leaks and dumping

In theory, there are thousands of potential sources for copper in urban runoff and shoreline 

activities. Additional information characterizing sources of copper is summarized in Diffuse

Sources of Environmental Copper in the United States (CDA 2003).
12

Table 1. Ambient Dissolved Copper Concentrations Reported for Coastal Harbors and 

Marinas.

Location Ambient Water

Copper Dissolved

(μg/L)

Baltimore (Fort McHenry), MD 18.7

Baltimore (Fells Point), MD 24.2

Gloucester, MA <5a

New Bedford, MA <5a

Philadelphia, PA <5a

Havre de Grace, MD <5a

Pensacola, FL 1.8

Gulf Breeze, FL 3.1

Lafitte, LA 3

Bayou La Batre, AL 4.3

Pass Christian, MS 4

Slidell, LA 2.4

Convent, LA 2.4

Sitka SB, AK <5a

Sitka, AK <5a

a Limit of detection

 (Source: U.S. EPA 2010b).

Monitoring in the Southern California Bight demonstrated that sediment from marinas 

throughout southern California had consistently elevated copper levels compared to surrounding 

waters (Bay et al. 2000). Surveys around the United States routinely find elevated copper 

concentrations in marina and harbor sediments relative to other areas with less vessel traffic or 

shoreline activities (NOAA 1994; U.S. EPA 1999).

2.2 Environmental Fate and Transport of Copper in the Aquatic Environment

Elemental copper, atomic number 29, is a reddish solid with a molecular weight of 

63.546 g/mol. Copper has a density of 8.94 g/mL at 20°C, a melting point of 1,083°C and is 

insoluble in water. Copper naturally occurs as two stable isotopes (63Cu and 65Cu) along with 

numerous unstable radioisotopes. Being a metallic element, copper will not break down and 

continues to cycle in the environment after it is released (Eisler 1998). 

Copper exists in four oxidation states: Cu0, Cu+, Cu2+, and Cu3+. The cupric ion (Cu2+) 

oxidation state is the form of copper generally encountered in water. Elemental copper (Cu0) is 

slightly soluble in dilute ammonia and is not oxidized in water, cuprous copper (Cu+) is only 
13

found in water when complexed (oxides, hydroxides and ligands), and trivalent copper (Cu3+) 

does not occur naturally. The pH of the medium and presence of other chemical species usually 

controls which forms of Cu+or Cu2+are found (ATSDR 1990; Eisler 1998). In oxic natural 

waters with neutral pH and above, the free cupric (Cu2+) ion is generally a minor species (Stumm 

and Morgan 1981). The cupric ion instead generally reacts with inorganic and organic chemicals 

in solution and in suspension, and forms moderate to strongly complexed solutes and precipitates 

with the numerous inorganic and organic constituents of natural waters (e.g., carbonate, 

phosphate, and organic materials). An overview of the chemistry of copper in aqueous systems is 

provided in Figure 2 (U.S. EPA 2010a).

Copper hydroxide, copper carbonate and cupric ion are the dominant copper species in 

seawater (U.S. EPA 1980). This is in contrast to freshwater, where cupric salts (chloride, nitrate 

and sulfate) are generally highly soluble and where solubility decreases under reducing 

conditions and is modified by water pH, temperature and hardness. Copper flux from 

estuarine/marine sediments is influenced by the presence of ligands in the sediment pore waters. 

In a study of two contrasting types of organic rich estuarine sediments from the Chesapeake Bay, 

it was determined that most of the total dissolved copper fluxing from these sediments would be 

complexed by ligands during the sediment-water exchange, and these sediments will influence 

the copper speciation in overlying waters when these ligands are released (Skrabal et al. 2000). 

Due to the complexation of the copper from the pore waters, only a small fraction of the copper

is exchanged as an organic species (the most bioavailable form) (Skrabal et al. 2000), indicating 

that the geochemistry of copper from estuarine/marine sediments is an important determinant of 

the fate and transport of copper to aquatic organisms.
14

Figure 2. Environmental Bridging Chemical Species for Copper (Cu) Minerals and 

Complexes.

2.3 Overview of Copper Toxicity

Copper is a micronutrient for organisms at low concentrations and is recognized as 

essential to virtually all plants and animals (Kapustka et al. 2004). It is also a key atom in the 

oxygen carrying protein (hemocyanin) of some invertebrates. However, it can become toxic to 

some forms of aquatic life at elevated concentrations. The specific mode of toxic action depends 

on the organism. In bacteria, fungi and algae, excess copper causes disruption of cell membrane 

integrity and the subsequent leakage of the cell contents (Borkow and Gabbay 2005). In 

mollusks, copper alters the normal function of peroxidase enzymes and surface epithelia, often 

producing peroxidation products that lethally disrupt vital functions of membranes and cells 

(Cheng 1979). In the mussel, Mytilus galloprovincialis, elevated copper concentrations have 

been found to interfere with Ca+2 homeostasis in the gill, and disrupt Na/K ATPase and Ca+2
15

ATPase activities (Viarengo et al. 1996). Copper also affects the gills of crabs, reducing 

hemocyanin-oxygen affinity in these organisms. Hansen et al. (1992) attributed copper exposed 

crab (Carcinus maenas) mortality to reduced oxygen transport and subsequent tissue hypoxia, 

with reductions in the activities of regulatory enzymes of ATP-synthesizing pathways. 

In marine fish, copper adversely affects osmoregulatory processes, ATP-synthesizing 

pathways and ion transport across the gills, and causes oxidative stress damage. The osmotic 

balance maintained by the gastrointestinal tract and gills in marine teleost fish is disrupted when 

elevated copper levels inhibit water absorption by the gut (active uptake of Na+and Cl-) and/or 

the secretion of Na+and Clby the gills (inhibition of branchial Na+/K+-ATPase) (Marshall and 

Grosell 2005; Stagg and Shuttleworth 1982). Excretion of nitrogenous waste by teleost fish can 

also be impacted by copper, with elevated plasma ammonia concentrations observed in seawateracclimated rainbow trout exposed to 400 μg/L copper (Wilson and Taylor 1993). In contrast, 

marine elasmobranchs retain nitrogenous compounds for osmoregulatory purposes, and exposure 

of spiny dogfish (Squalus acanthias) to 1,000 μg/L copper resulted in a loss of plasma urea (De

Boeck et al. 2007). Dodoo et al. (1992) observed inhibited calcium transport in juvenile flounder 

(Paralichthys sp.) exposed to copper, and speculated that it was caused by copper interference 

with gill chloride cells. 

Copper can also induce cellular oxidative stress, through the formation of reactive 

oxygen species (ROS), inhibition of antioxidant enzymes, alteration of the mitochondrial 

electron-transfer chain, or depletion of cellular glutathione (Shukla et al. 1987; Freedman et al. 

1989; Stohs and Bagchi 1995; Rau et al. 2004; Wang et al. 2004). Oxidative stress is normally 

mitigated with cellular antioxidant mechanisms, but prolonged exposure to elevated copper 

concentrations can exhaust these defenses, and may result in the oxidation of DNA (strand 

break), lipids (impaired cell membrane permeability) and proteins (Grosell 2012). ROS 

neutralization includes antioxidant enzymes such as catalase, glutathione peroxidase and 

reductase, and Cu/Zn superoxide dismutase. Detoxifying mechanisms include the induction of 

metallothioneins and heat shock protein 70 (Sato and Bremner 1993; McDuffee et al. 1997; 

Evans and Halliwell 2001). In summary, excessive copper concentrations compromise normal 

cell functions by disrupting osmoregulation and ion flow, inhibiting enzymes and ATP-driven 

pumps, and inducing oxidative stress, resulting in cell toxicity from oxidative damage and 
16

disruption of cell homeostasis, and leading to changes in internal pH balance, membrane 

potential, and osmosis (Okocha and Adedeji 2012).

Copper concentrations typically build up in tissues at the site of exposure, such as the gill 

surface and gut tract wall (Chevreuil et al. 1995). Copper is then transferred via circulation to 

other tissues and organs, with the liver and kidney typically accumulating high concentrations 

relative to muscle tissues (Grosell 2012). Although copper bioaccumulates in some aquatic 

species, there does not appear to be a consistent relationship between body burden and 

toxicological effect (Meyer et al. 2005; DeForest and Meyer 2015). This inconsistent relationship 

between whole body tissue concentration and toxic effect may be related to specific organs 

and/or tissues where the accumulation is occurring. Therefore, it may not be accurately 

quantified by whole body tissue residue analysis, and/or the metabolic bioavailability of copper 

in tissues. 

Since copper is an important trace nutrient, some organisms may have mechanisms for 

maintaining homeostasis, such as detoxification, making it more difficult to study the 

relationship between body burden and toxic effect. Detoxification mechanisms in aquatic 

organisms, including the formation and activation of antioxidants, metallothionein, glutathione, 

and heat shock proteins (McGeer et al. 2011) effectively sequester the metal in a detoxified form, 

thereby allowing the organism to accumulate elevated levels of copper before displaying a toxic 

response. While the amount of detoxified metal that an aquatic organism can accumulate is 

theoretically unlimited, an organism will only experience toxic effects once the concentration of 

metabolically required metal is exceeded (Rainbow 2002; Rainbow and Smith 2013). Under 

natural conditions, most accumulated copper in tissues is expected to exist in a detoxified state, 

which may explain the poor relationship between whole body tissue residue concentrations and 

toxic effect observed in tested aquatic invertebrates and fish (Rainbow 2002). 

An additional consideration is the potential for copper in aquatic prey items (e.g., 

invertebrates) to adversely affect higher trophic level organisms, such as fish and aquaticdependent wildlife via dietary exposure. This exposure pathway does not show a consistent doseresponse relationship because the bioavailability of copper to top predators differs substantially

among prey species that are consumed (U.S. EPA 1993). Further, there are numerous different 

prey types and amounts eaten by each predator, thus complicating the estimate of a safe dose to 

higher trophic level organisms (this and other uncertainties are discussed in Section 4.3.1). 
17

Overall, however, the risk to higher trophic level species is considered low because researchers 

have found that copper generally does not accumulate or biomagnify in aquatic food chains 

(Lewis and Cave 1982; Suedel et al. 1994). The evaluation of effects from the direct exposure of 

organism tissues (e.g., gills and other biological membranes) to copper in water is therefore 

considered more applicable to the development of criteria for aquatic life and was the focus of 

the development of criteria for estuarine/marine aquatic life.

The toxicity of copper to aquatic life is related primarily to the activity of the cupric ion, 

and possibly to some hydroxy complexes (Allen and Hansen 1996; Andrew 1976; Andrew et al. 

1977; Borgmann and Ralph 1983; Chakoumakos et al. 1979; Chapman and McCrady 1977; 

Dodge and Theis 1979; Howarth and Sprague 1978; Pagenkopf 1983; Petersen 1982; Rueter 

1983). Examples of the response of organisms to cupric ion activity, and limited exceptions, are 

reviewed by Campbell (1995). Any changes in water quality that would be expected to decrease 

free copper ion activity also would be expected to decrease copper bioavailability and resulting 

toxicity. For example, increases in pH, alkalinity, and NOM (as represented by DOC) would all 

tend to decrease copper bioavailability and be associated with increased copper LC50 values. The 

following section discusses in detail the characterization of water quality parameters and their 

effect on bioavailability.

2.4 Overview of Historic and BLM Criteria Development Methods

Early national recommended aquatic life criteria for copper (U.S. EPA 1980, 1984, 

1995a, 1996, 2003) considered bioavailability effects for freshwater organisms based on water 

hardness by incorporating linear regression equations into the criterion-calculation procedure to 

account for the decreasing acute and chronic toxicity of copper to freshwater biota with 

increasing water hardness. Temperature did not vary significantly for tests with most species, pH 

values were often not reported or were highly variable, and alkalinity and DOC were rarely 

reported. Accordingly, freshwater criteria for copper, and those for several other metals, were 

established as functions of water hardness alone. However, the regression coefficients for 

hardness did not only reflect how hardness affected copper toxicity. Hardness was instead a 

surrogate for other co-varying water quality parameters that were not included in the regression 

analyses and the criteria based on hardness alone did not explicitly account for the modifying 

effects of these other water parameters.
18

An alternate approach that has been proposed to predict metal toxicity is to (1) identify 

the bioavailable form(s) of the metal; (2) analyze or calculate the concentration(s) of the 

bioavailable form(s) in the exposure water; and (3) predict the toxicity based on an empirical 

relationship between the biological response and the concentration(s) of the bioavailable forms 

(Santore et al. 2001). This approach only requires the direct measure or calculation (using a 

geochemical-speciation model) of the free metal ion (Cu2+) concentration, which is the

bioavailable-fraction of copper in water. The concentration of Cu2+ has been demonstrated to be 

an accurate indicator of acute toxicity, as characterized by trends in the LC50 values, even in the 

presence of varying levels of inorganic or organic ligands, which can complex with copper and 

alter the Cu2+ concentration (e.g., Borgmann 1983; Santore et al. 2001). This approach, however,

loses accuracy when other cations are present in water that can interact with biota. For example, 

the LC50 of Cu2+ increases significantly as the concentration of Ca2+ (a major component of 

water hardness) increases (Campbell 1995; Meyer et al. 1999). This trend indicates that the 

concentration of cupric ion alone is not always sufficient to predict toxicity.

In general, there is no universally constant bioavailable fraction of a metal that can be 

identified by chemical analyses (Meyer et al. 2002). The interactions amongst the key abiotic 

components in exposure water must be considered in conjunction with the interactions of those 

key abiotic components directly with biota. Metal bioavailability may also be modified by 

competitive interactions at the biotic ligand (i.e. biological membranes of toxic interaction). 

Increased sodium and calcium concentrations, for example, can reduce the binding of copper to 

physiologically active binding sites and can thereby reduce copper bioavailability. Cation 

competition also has an effect on the complexation of copper by DOC, and this interaction will 

partially offset competitive interactions that occur at the biotic ligand. The complex interactions 

of Cu2+ with dissolved components, suspended particles, and biota therefore must be 

simultaneously considered in order to accurately predict copper toxicity.

The chemical speciation of copper in natural waters and explanatory power of the free 

copper ion in characterizing copper toxicity were first recognized more than 30 years ago 

(Anderson and Morel 1978; Sunda and Gillespie 1979; Sunda and Guillard 1976; Sunda and 

Lewis 1978; Zitko et al. 1973). These concepts were eventually formalized in models that linked 

metal chemistry and biological effects, such as the gill surface interaction model (GSIM) 

(Pagenkopf 1983) and the free ion activity model (FIAM) (Morel 1983). Playle and others 
19

demonstrated that copper binding to fish gills can be modeled using a chemical speciation 

approach (Playle et al. 1993a, 1993b). MacRae and others demonstrated that copper binding on 

the gill shows a dose-response relationship with mortality (MacRae et al. 1999). Although early 

models showed remarkable utility, several critical issues remained. Perhaps most notably, and 

until recently, few models could predict metal chemistry in the presence of NOM over a range of 

environmental conditions (Bergman and Dorward-King 1997). A considerable amount of 

information about metals speciation in the environment has since become available and 

computing techniques have been further developed to simulate metal speciation (e.g., Nordstrom 

et al. 1979). These early efforts, however, laid the foundation for the development and use of the 

BLM to predict adverse effect levels of metals as a function of site-specific water chemistry (Di 

Toro et al. 2001). A more comprehensive review of these historical developments is presented in 

Paquin et al. (2002).

The BLM is a metal bioavailability model that considers chemical and physiological 

effects information for metals in aquatic environments and was originally developed for 

freshwater settings (Di Toro et al. 2001; Paquin et al. 2002; Santore et al. 2001). The approach 

was first presented to EPA’s Science Advisory Board in 1999 where it received a generally 

favorable response (U.S. EPA 1999, 2000). Like the FIAM and GSIM, the BLM is based on a 

description of the chemical speciation of metals in aqueous systems (Figure 3). Chemical 

speciation is simulated as an equilibrium system that includes the complexation of inorganic ions 

and NOM. The chemical system for the original freshwater BLM was simulated by the chemical 

equilibria in soils and solutions (CHESS) model (Santore and Driscoll 1995), including a 

description of metal interactions with NOM based on the Windermere humic aqueous model 

(WHAM) (Tipping 1994). A significant advantage of the NOM chemistry developed for WHAM 

is that reactions and parameter values were developed by simultaneously considering numerous 

NOM samples and numerous metals. A chemical description was needed specifically 

characterizing chemical speciation for the saltwater BLM, but the basic principles of metal 

speciation are similar to those established by the development of the models used for the original 

freshwater BLM (Chadwick et al. 2008).
20

Figure 3. Conceptual Diagram Showing Relationship between Chemical Speciation, Metal 

Binding at Biotic Ligand (BL) Sites, and Competition at These BL Sites for Other Cations.

(Adapted from Santore et al. 2001).

In addition to considering chemical speciation, the BLM also includes reactions that 

describe the chemical interactions of copper and other cations with physiologically active sites, 

termed biotic ligands (BLs). BLs correspond to the proximate site of action of toxicity in aquatic 

organisms and can be present on any biological membrane. The model parameters define the 

degree of interaction based on binding affinity characteristics measured in gill-loading 

experiments. The BL is represented by a characteristic binding site density and conditional 

stability constant for each of the dissolved chemical species with which it reacts. Predictions of 

metal toxicity are made by assuming that the dissolved metal LC50, which varies with water 

chemistry, is always associated with a fixed critical level of metal binding with the BL. This 

fixed level of metal-biotic ligand (Me:BL) accumulation at 50 percent mortality has been 

referred to as the “lethal accumulation 50%” (LA50), but since the BLM can also apply to sublethal endpoints, this parameter has been more generically termed “critical accumulation.” 

Copper accumulation on the BL is characterized by a rapid and reversible chemical interaction 

with binding sites on biological membranes, and is not in any other way similar to accumulation 

that results from uptake within the organism. It is assumed to be constant, regardless of the 

chemical characteristics of the water (Meyer et al. 1999, 2002). This combination of reactions 
21

that describe aqueous metal speciation and organism interactions allows the BLM to predict 

copper toxicity to a variety of organisms over a variety of water quality conditions (Santore et al. 

2001).

The saltwater BLM for copper was developed from independent datasets that could be 

used to characterize copper speciation, surficial copper binding to membranes, and toxicity

(Chadwick et al. 2008). The chemistry model used to represent interactions between copper and 

dissolved organic matter (DOM, usually measured as DOC) included four discrete ligands and 

was calibrated to titration results with over 60 water samples. The calibrated model was then 

validated using an additional dataset that was similar in breadth (>60 titrations). The established 

relationship between free copper, dissolved copper, and DOC in marine waters was demonstrated 

to describe the range of copper concentrations that bracketed anticipated marine criteria values 

that would be protective of sensitive marine invertebrates (Chadwick et al. 2008). The 

development effort included calibration and validation steps. Extensive datasets from San Diego 

Bay and Pearl Harbor were used in the analysis. Subsets of the data from each site were assigned 

as calibration or validation data. Calibration data were used in the parameterization of the model, 

while the validation data were only used to test overall goodness of fit (Chadwick et al. 2008). 

Validation was performed by comparison with chemical speciation data (i.e., free copper ion), 

and measured copper toxicity to sensitive marine invertebrates.

Binding constants for copper and other cations to the BL for the saltwater BLM were 

developed from data reported by Rosen et al. (2008), which included copper accumulation data 

for both Mytilus galloprovincialis and Strongylocentrotus purpuratus. These accumulation data 

were measured in short-term exposures designed to quantify copper interactions with the 

surficial membranes of embryolarval forms of these marine organisms and should not be equated 

with whole-body accumulation in more well-developed life stages, which may represent uptake 

and incorporation of copper in the tissue of multiple organs. The dose-response (percent 

abnormal) curves for different water samples having different DOC levels differed from each 

other when the exposure was characterized only on the basis of dissolved copper. However, a 

single dose-response curve can characterize copper toxicity in these different samples when

exposure is expressed as embryo-larvae whole body copper concentrations (Figure 4). The 

ability of a single relationship between accumulation and toxicity in different samples indicates 

that the surficial copper binding to cell membranes (which can be measured as whole body 
22

accumulation in embryolarval forms of these organisms) on the larval life stages is directly 

related to the copper bound to the site of toxic action. The resulting saltwater BLM is thus 

demonstrated to consistently simulate accumulated copper using a single model representation 

for both M. galloprovincialis and S. purpuratus, as shown in Figure 5.

An advantage of the BLM is that most of the parameters are invariant for different 

organisms, despite the complexity of the modeling framework. All of the thermodynamic 

constants used to simulate inorganic and organic chemical equilibrium reactions are determined 

by characteristics of the metal and the available ligands. As such, the constants do not change for 

simulations involving different organisms. This is an important consideration in the development 

of the BLM. In a recent review, Erickson (2013) cautioned against the introduction of additional 

parameters that weaken the mechanistic framework of the model. In particular, Erickson 

cautioned about inferring accumulation-based effects from toxicity measurements. In the 

development of the marine copper BLM, the critical accumulation for several sensitive 

organisms were taken from direct measurements (Figure 4) rather than inferred from toxicity 

data. These measurements confirmed several assumptions made during the development of the 

freshwater model. First, that the same accumulation model (and hence the same BL parameters) 

could be used to describe accumulation to different organisms [for example Mytilus in Figure 4

(Panel A) and Strongylocentrotus in Figure 4 (Panel B)]. Second, that the difference in 

sensitivity between these organisms is due to different critical accumulation levels (vertical 

dashed lines in Figure 4). The critical accumulation, therefore, is the only model parameter that 

is needed to account for differences in organism sensitivity. 
23

A

B

Figure 4. Percent Abnormal Cells in Test Waters with Different Composition (primarily 

DOC) for M. galloprovincialis (Panel A) and S. purpuratus (Panel B).

(Samples collected from different areas are labeled with the sample identifier (N or S). Values collapse 

into a single dose response when compared with measured copper accumulation). (Chadwick et al. 

2008).
24

A

B

Figure 5. Predicted Copper Binding to BL Sites on Cell Membranes (solid lines) by the 

Saltwater BLM for Copper with a Single Set of Parameters Compared with Measured 

Copper Accumulation for Embryo-larval Stages of M. galloprovincialis (Panel A) and S. 

purpuratus (Panel B).

(Samples collected from different areas are labeled with the sample identifier (N or S). (Chadwick et al. 

2008).
25

Toxicity data were used to evaluate the critical accumulation values for M. 

galloprovincialis and S. purpuratus and to predict EC50 values for these two organisms. Coupled 

with the toxicity data, the BLM can predict how much dissolved copper is associated with 

critical accumulation in waters of varying composition, and how toxicity changes in response to 

changes in key environmental variables, such as DOC. The resulting model can predict toxicity 

to both M. galloprovincialis and S. purpuratus over a wide range of conditions for waters from 

different geographic regions (Figure 6). 

Accumulation values that were available for M. galloprovincialis and S. purpuratus were 

not available for other organisms having toxicity data. To incorporate other organisms into the 

BLM, water effect concentrations (ECs) were extrapolated for the biological species for which 

accumulation data are not available. This is the same approach as was used for the BLM-based 

copper criteria for fresh water (U.S. EPA 2007). The general procedure used for the freshwater 

criteria development was to normalize all available toxicity data to selected water chemistry 

values, calculate criteria values at these conditions, and then use the normalization procedure to 

compute criteria at other water chemistry conditions. With this approach, the BL parameter 

values developed from M. galloprovincialis and S. purpuratus accumulation measurements are 

assumed to be constant for other sensitive marine invertebrates. This approach has been shown to 

work well when used to predict copper effect levels for other freshwater organisms (U.S. EPA 

2007). The same accumulation model was first used to evaluate the critical accumulation for the 

additional organisms, and then used to predict effect levels. It was determined that 94% of all 

predictions were within a factor of two of the measured EC50 (Figure 7). 
26

A

B

Figure 6. Predicted Copper Toxicity by the Saltwater BLM for Copper (solid lines) in 

Response to Changing DOC from a Variety of Estuarine and Marine Sites Compared with 

Measured Copper Toxicity for Embryo-larval Stages of M. galloprovincialis (Panel A) and 

S. purpuratus (Panel B).

(Dashed lines indicate plus or minus a factor of two around the solid line. Variation within these 

boundaries represents the variability of replicate toxicity tests).
27

A

B

Figure 7. Predicted Copper Toxicity by the Saltwater BLM for Copper (solid lines) in 

Response to Changing DOC from a Variety of Estuarine and Marine Sites Compared with 

Measured Copper Toxicity for Embryo-larval Stages of Dendraster (Panel A) and 

Crassostrea (Panel B).

(Dashed lines indicate plus or minus a factor of two around the solid line. Variation within these 

boundaries represents the variability of replicate toxicity tests).
28

While many of the concepts and conditions applicable to the freshwater BLM for copper 

also apply to estuarine/marine waters, there are some differences. First, the concentrations of all 

ions in saltwater are much higher than in freshwater (Morel and Hering 1983). Second, in waters 

with constant salinity, the ionic composition is well defined and consistent so the likelihood that 

changes in ionic composition could result in observable bioavailability effects is lower than for 

freshwater (Stumm and Morgan 1981). Although water samples from estuaries may be collected 

across a range of salinities, toxicity tests with copper are typically conducted with embryo-larval 

stages of sensitive marine invertebrates such as Mytilus or Crassostrea (Arnold et al. 2010a; 

Rosen et al. 2005). Available toxicity data indicate that the early life stages of these bivalve 

molluscs are amongst the most sensitive marine organisms to copper (U.S. EPA 1995a; Table 3). 

However, the early life stages of these species have a narrow range of salinity tolerance. When 

used to test copper toxicity in estuarine samples, standard procedures therefore require that the 

salinity of test solutions be increased to full marine salinity (e.g., 30 to 32 ppt; U.S. EPA 1995a). 

Although it is expected that cation competition plays a role in determining metal bioavailability 

along salinity gradients, the effects of salinity on copper bioavailability are absent in the majority 

of toxicity data sets that are available, due to the standard practice of adjusting samples to full 

strength salinity. In tests where estuarine samples have been salted up to marine salinity, the 

potential effects of variable salinity on copper toxicity have been eliminated, leaving only DOC 

as the primary toxicity modifying factor (such as in Figure 6 and Figure 7).

Recent tests with sensitive invertebrates capable of tolerating a wide range of salinities 

have shown that the same bioavailability relationships involving pH, DOC, and salinity also 

apply in estuarine conditions when tested over a range of salinities (Arnold et al. 2010b, 2010c; 

Cooper et al. 2012; Hall et al. 1997, 2008). These studies have shown that copper bioavailability 

is reduced at high salinity, which is consistent with effects predicted by the saltwater BLM for 

copper. For example, Arnold et al. (2010c) found that EC50s for Brachionus plicatilis ranged 

from less than 40 μg/L at a salinity of 5 ppt, to approximately 70 μg/L at a salinity of 30 ppt. 

Similar results were reported by Cooper et al. (2012) for B. plicatilis. The overall results from 

Cooper et al. (2012) suggest that both salinity and DOC are important in estuarine samples and 

the combined effects are consistent with predictions by the saltwater BLM. Increasing salinity 

was also shown to have variable effects to the polychaete Hediste (Ozoh 1992a,b). In exposures 
29

with sediment, the effect of salinity on copper toxicity was small and variable depending on the 

temperature, while in water-only exposures there was a reduction in copper bioavailability with 

increasing salinity similar to that seen in rotifers (Ozoh 1992a,b). The saltwater BLM for copper 

is therefore considered predictive of copper effects to sensitive estuarine invertebrates. 

2.5 Conceptual Model

A conceptual model characterizes relationships between human activities, stressors and 

ecological effects on the assessment endpoints identified for evaluation (U.S. EPA 1998). The 

conceptual model links exposure characteristics with the ecological endpoints important for the 

development of management goals. Under the CWA, these management goals are established by 

states and tribes as designated uses of waters of the United States (for example, the protection of 

aquatic life). In deriving aquatic life criteria, U.S. EPA is developing acceptable thresholds for 

pollutants that, if not exceeded, are expected to be protective of aquatic life. A state and/or tribe 

may implement these criteria by adopting them into their respective water quality standards.

The conceptual model depicted in Figure 8 provides a broad overview of how aquatic 

organisms could be exposed to copper in the estuarine/marine environment. As depicted in 

Figure 8 and discussed in Section 2.1, copper enters the environment from both natural and 

anthropogenic sources. The environmental fate properties of copper indicate that weathering and 

erosion of natural sources and inputs from a variety of anthropogenic sources represent potential 

mechanisms that can transport copper from these sources to surface water (TDC Environmental 

2004; U.S. EPA 2010a). The model also depicts exposure pathways for potential biological 

receptors (e.g., non-target aquatic animals) and potential attribute changes (e.g., reduced 

survival, growth and reproduction) in those receptors due to copper exposure. The conceptual 

model diagram (Figure 8) depicts where the BLM predicts how water quality parameters 

(especially DOC) influence the uptake/gill or integument exposure pathway. Copper also has the

potential for adsorption to sediment and to bioaccumulate in aquatic organism tissues. There is 

accordingly the potential for the exposure of benthic organisms to copper in sediment (pore 

water) and the potential for the exposure of carnivorous mammals and birds via the consumption 

of aquatic invertebrates and fish that have accumulated copper (terrestrial effects were not 

assessed). Aquatic toxicity assessments assume anthropogenic exposure occurs primarily as a 

result of direct release/discharge to surface water and/or following partitioning from sediment to 
30

surface water. The transport and leaching of copper from groundwater to surface water is 

assumed to be negligible (U.S. EPA 2010a).

The conceptual model is intended to provide a broad overview of how aquatic organisms 

can potentially be exposed to copper. Transport mechanisms and exposure pathways are not 

considered in the derivation of aquatic life criteria. Derivation of criteria instead focuses on the 

effects of copper on survival, growth and reproduction of aquatic organisms based on its

presence in the aquatic environment. However, the pathways, receptors, and attribute changes 

depicted in Figure 8 may be helpful for states and authorized tribes as they adopt criteria into 

standards and need to evaluate potential exposure pathways affecting designated uses.

Figure 8. Conceptual Model for Copper Effects on Aquatic Organisms.

(Dotted arrows indicate exposure pathways that have a low likelihood of contributing to ecological risk).
31

2.6 Assessment Endpoints

Assessment endpoints are defined as the explicit expressions of the environmental values 

to be protected and are comprised of both the ecological entity (e.g., a species, community, or 

other entity) and the attributes or characteristics of the entity to be protected (U.S. EPA 1998). 

Assessment endpoints may be identified at any level of organization (e.g., individual organism, 

population, community). In context of the CWA, aquatic life criteria for toxic substances are 

typically determined based on the results of toxicity tests with aquatic organisms, for which 

adverse effects on growth, reproduction or survival are measured. This information is aggregated 

into a species sensitivity analysis that characterizes an impact to the aquatic community. Criteria 

are designed to be protective of the vast majority of aquatic organisms in an aquatic community 

(i.e., approximately the 95th percentile of tested aquatic organisms representing the aquatic 

community). Assessment endpoints consistent with the criteria developed in this document are 

summarized in Table 2.

2.7 Measurement Endpoints

Assessment endpoints require one or more measures of ecological effect, which are 

termed “measurement endpoints.” Measurement endpoints are the measures of ecological effect 

used to characterize or quantify changes in the attributes of an assessment endpoint or changes in 

a surrogate entity or attribute, in this case a response to chemical exposure. Toxicity data are 

used as measures of direct and indirect effects on representative biological receptors. The 

selected measures of effect for the development of aquatic life criteria encompass changes in the 

growth, reproduction, and survival of aquatic organisms. 

The toxicity data used for development of the aquatic life criteria depend on the 

availability of applicable toxicity test outcomes, the acceptability of test methodologies, and an 

in-depth evaluation of the acceptability of each specific test, as performed by the U.S. EPA per 

its Guidelines (1985). Measurement endpoints for the development of aquatic life criteria are 

derived using acute and chronic toxicity studies for representative test species, which are then 

quantitatively and qualitatively analyzed, as described in the Analysis Plan below. Measurement 

endpoints considered for each assessment endpoint in this criteria document are summarized in

Table 2. The following sections discuss toxicity data requirements for the fulfillment of these 

measurement endpoints.
32

Table 2. Summary of Assessment Endpoints and Measures of Effect Used in Criteria 

Derivation.

Assessment Endpoints for the Aquatic 

Community

Measures of Effect

Survival, growth, biomass, and reproduction of 

fish and invertebrates (estuarine/marine)

Acute: LC50, EC50

Chronic: EC20, MATC (only used when an EC20

could not be calculated for the genus)

Maintenance and growth of aquatic plants from 

standing crop or biomass (estuarine/marine)

LOEC, EC20, EC50, IC50, reduced growth rate, cell 

viability, calculated MATC

MATC=Maximum acceptable toxicant concentration (geometric mean of NOEC and LOEC)

NOEC=No observed effect concentration

LOEC=Lowest observed effect concentration

LC50=Lethal concentration to 50% of the test population

EC50/EC20=Effect concentration to 50%/20% of the test population

IC50=Concentration of copper at which some effect is inhibited 50% compared to control organism

2.7.1 Overview of Toxicity Data Requirements

U.S. EPA has specific data requirements to assess the potential effects of a stressor on an 

aquatic ecosystem and develop 304(a) aquatic life criteria under the CWA. To develop 304(a) 

criteria for estuarine/marine aquatic life under CWA, EPA typically requires the following:

 Acute toxicity test species data from a minimum of eight diverse taxonomic groups as 

follows:

o two families in the phylum Chordata

o a family in a phylum other than Arthropoda or Chordata 

o a family from either Mysidae or Peneidae

o three other families not in the phylum Chordata (may include Mysidae or 

Penaeidae, whichever was not used above)

o any other family

 Chronic toxicity test data (longer-term survival, growth, or reproduction) are generally 

required for a minimum of three taxa, with at least one chronic test being from an 

acutely-sensitive species. Acute-chronic ratios can be calculated with data for species of 

aquatic animals from at least three different families if the following data requirements 

are met:

o at least one is a fish 

o at least one is an invertebrate

o at least one is an acutely sensitive saltwater species (the other two may be 

freshwater species)
33

2.7.2 Measures of Effect

Acute measures of effect

The acute measures of effect used for organisms in this document are the LC50, EC50, and 

IC50. LC stands for “Lethal Concentration” and an LC50 is the concentration of a chemical that is 

estimated to kill 50 percent of the test organisms. EC stands for “Effective Concentration” and 

the EC50 is the concentration of a chemical that is estimated to produce a specific effect in 50

percent of the test organisms. IC stands for “Inhibitory Concentration” and the IC50 is the

concentration of a chemical that is estimated to inhibit some biological process (i.e. growth, etc.) 

by 50 percent compared to a control.

Chronic measures of effect

The endpoints for chronic measures of exposure are the NOEC, LOEC, MATC and EC20. 

The NOEC (i.e., “No-Observed-Effect-Concentration”) is the highest test concentration at which 

none of the observed effects were statistically different from the control. The LOEC (i.e., 

“Lowest-Observed-Effect-Concentration”) is the lowest test concentration at which observed 

effects is statistically different from the control. The Maximum Acceptable Toxicant 

Concentration (MATC) is the calculated geometric mean of the NOEC and LOEC. The EC20, 

which represents a 20 percent effect/inhibition concentration, is a low level of effect that is 

generally significantly different from the control treatment.

Data available for measuring effect

Effect data for copper were obtained from studies published in the open literature and

identified in a search of the ECOTOXicology database (Available online at: 

https://cfpub.epa.gov/ecotox/). ECOTOX is a source of high quality toxicity data for aquatic life, 

terrestrial plants, and wildlife. The database was created and is maintained by the EPA, Office of 

Research and Development, National Health and Environmental Effects Research Laboratory's 

Mid-Continent Ecology Division. The latest comprehensive literature search for this document 

was conducted in April 2016.

Following initial identification with the ECOTOX database search, a further evaluation of 

available data was performed by EPA to determine test acceptability. The amount of toxicity 

testing data available for any given pollutant varies significantly, depending primarily on 

whether it has raised any significant environmental issues and, in the case of a pesticide, how 
34

long it has been registered. Appendix A of Quality Criteria for Water 1986 (U.S. EPA 1986b) 

provides an in-depth discussion of the minimum data requirements and data quality requirements

for aquatic life criteria development.

As discussed above, the assessment endpoints for aquatic life criteria are based on the 

growth, reproduction, and survival of the assessed taxa, while the specific measures of effect are 

provided by the acute and chronic toxicity data (Table 2). The toxicity endpoints derived from 

these data are expressed as the geometric means of acute values for all species of the same genus

(GMAVs) or geometric means of the chronic values for all species of the same genus (GMCVs). 

GMAVs and GMCVs are used in the applicable species sensitivity distributions of the available 

aquatic community data to derive the acute and chronic aquatic life criteria. 

Table 3 provides a summary of the data used to fulfill the minimum data requirements 

(MDR) outlined in the EPA Guidelines (Stephan et al. 1985) for derivation of the 

estuarine/marine acute criterion for copper. It also provides a summary of the number of 

families, genera, and species with acceptable acute and chronic toxicity data. There are a total of 

seven phyla in the acute copper toxicity database representing 63 families, 78 genera, and 89 

species. The copper toxicity dataset far exceeds the MDRs for derivation of an estuarine/marine 

acute criterion. Acceptable estuarine/marine copper chronic values are available for only two 

species, the euryhaline rotifer, Brachionus plicatilis (Arnold et al. 2010b) and the sheepshead 

minnow, Cyprinodon variegatus (Hughes et al. 1989). Consistent with U.S. EPA’s Guidelines, 

freshwater toxicity data were therefore integrated into the derivation of the chronic criterion. 

Data that were determined to have acceptable quality and to be useable in the derivation of water 

quality criteria as described in U.S. EPA’s Guidelines for the derivation of acute and chronic 

criteria are presented in Appendix Table A-1 and Appendix Table B-1, respectively. 
35

Table 3. Summary Table of Acceptable Toxicity Data Used to Meet the Minimum Data Requirements in EPA’s Guidelines and 

Count of Phyla, Families, Genera and Species.

Family Minimum Data Requirement 

(Estuarine/Marine)

Acute

Phylum / Family / Genus

Chronic

Phylum / Family / Genus

Family in the phylum Chordata Chordata / Atherinopsidae / Menidia Chordata / Cyprinodontidae / Cyprinodon

Family in the phylum Chordata Chordata / Sciaenidae / Leiostomus -

Either the Mysidae or Penaeidae family Arthropoda / Mysidae / Americamysis -

Family in a phylum other than Arthropoda or Chordata Mollusca / Mytilidae / Mytilus Rotifera / Brachionidae / Brachionus 

Family in a phylum other than Chordata Rotifera / Brachionidae / Brachionus -

Family in a phylum other than Chordata Echinodermata / Diadematidae / Diadema -

Family in a phylum other than Chordata Cnidaria / Aiptasiidae / Aiptasia -

Any other family Arthropoda / Crangonida / Crangon -

Dash (-) indicates requirement not met (i.e., no acceptable data).

Estuarine/Marine Acute Estuarine/Marine Chronic

Phylum Families GMAVs SMAVs Families GMAVs SMAVs

Annelida 4 5 5 - - -

Arthropoda 23 31 34 - - -

Chordata 18 21 24 1 1 1

Cnidaria 1 1 1 - - -

Echinodermata 5 5 6 - - -

Mollusca 11 14 18 - - -

Rotifera 1 1 1 1 1 1

Total 63 78 89 2 2 2
36

2.8 Analysis Plan

Although the BLM-based approach for copper in estuarine/marine waters has now been 

developed for use in place of the former, non-BLM-based approach, the updated criteria 

derivations in this document are still based on the principles set forth in EPA’s Guidelines 

(Stephan et al. 1985). Therefore, it is useful to review how the Guidelines are applied.

During CWA §304(a) criteria development, U.S. EPA reviews and considers all relevant 

toxicity test data. Information available for all relevant species and genera are reviewed to 

identify: (1) data from acceptable tests that meet data quality standards; and (2) whether the 

acceptable data meet the MDRs as outlined in U.S. EPA’s Guidelines (Stephan et al. 1985; U.S. 

EPA 1986b). The taxa represented by the different groups comprising the MDRs are comprised 

of taxa with different ecological, trophic, taxonomic and functional characteristics in aquatic 

ecosystems, and are intended to be a representative subset of the diversity within a typical 

aquatic community. Although the aquatic life criteria process is based on selected toxicity 

endpoints from the most sensitive species tested, the criteria derived may not necessarily reflect 

the most sensitive species existing in a specific environment. If plants are more sensitive than 

vertebrates and invertebrates, plant criteria are developed if sufficient data are available to

support its derivation.

Application of the saltwater BLM to the derivation of the estuarine/marine Final Acute 

Value is analogous to procedures already described in EPA’s criteria for metals criteria using 

empirical hardness regressions. For these hardness-dependent metals criteria, LC50s at various 

hardness levels are normalized to a selected hardness using the regression slopes. Similarly, the 

acceptable acute and chronic data are normalized to the selected water chemistry conditions

using the BLM, and then the criteria are derived according to the Guidelines. The values 

presented below are relative only to the selected water chemistry for comparison purposes. The 

saltwater BLM-based criteria will in some cases be more stringent and in other cases less 

stringent than the previous criteria, depending on specific water conditions used with the BLM. 

As there is not a single criterion value to use for comparison purposes, it will only be possible to 

provide illustrative examples of each situation.
37

2.8.1 Acute Criterion Derivation

As recommended by the Guidelines, acute criteria are based on a species sensitivity 

distribution (SSD) comprised of genus mean acute values (GMAVs), which are calculated from 

species mean acute values (SMAVs) for available and acceptable data. SMAVs are calculated 

using the geometric mean for all acceptable toxicity tests for a given species (e.g. all tests for 

Mytilus edulis). If only one test is available, the SMAV is that test value by default. GMAVs are 

then calculated using the geometric means of all SMAVs within a given genus (e.g. all SMAVs 

for the genus Mytilus - Mytilus edulis, Mytilus galloprovincialis). 

The estuarine/marine acute criterion is based on the Final Acute Value (FAV). The FAV 

is determined by first ordering the GMAVs by rank from most sensitive (Rank 1) to least 

sensitive (Rank N) for linear regression analysis. The regression analysis is typically driven by

the four most sensitive genera reflecting the lowest GMAVs in the sensitivity distribution, based 

on the need to interpolate or extrapolate (as appropriate) to the 5th percentile of the distribution 

represented by the tested genera. The FAV represents a hypothetical genus more sensitive than 

95 percent of representative genera. Consistent with EPA’s Guidance, because more than 59 

GMAVs were available for copper, the FAV was derived from the four GMAVs that have 

cumulative probabilities closest to the 5th percentile toxicity value for all the tested genera. The 

acute criterion, defined as the Criterion Maximum Concentration (CMC), is then calculated by 

dividing the FAV by two, which is intended to provide an acute criterion protective of nearly all 

individuals in the distribution (Stephan et al. 1985). The FAV may be lowered to protect 

recreationally or commercially important species.

As discussed above, acute toxicity test data must be available for species from a 

minimum of eight genera with a specified minimum required taxonomic diversity as established 

by the MDRs. The diversity of tested species required by the MDRs is intended to ensure the 

protection of various components of an aquatic ecosystem. Although the aquatic life criteria 

derivation process relies on selected toxicity endpoints from the sensitive species tested, it does 

not necessarily mean that the selected toxicity endpoints reflect the sensitivity of the most 

sensitive species existing within a given habitat. The intent of the eight MDRs is instead to serve 

as a representative sample of the aquatic community, with the MDRs representative of the

different ecological, trophic, taxonomic and functional differences observed in the natural 

aquatic ecosystem. Use of the SSD method where the criteria values are based on the four most 
38

sensitive taxa is reflective of the whole distribution, representing a censored statistical approach 

that improves estimation of the lower tail when the shape of the whole distribution is uncertain.

2.8.2 Chronic Criterion Derivation

A chronic criterion is typically determined by one of two methods. If MDRs are met with 

acceptable chronic test data available for all eight families, then the chronic criteria can be 

derived using the same method as for the acute criteria, employing chronic values (e.g., EC20) 

estimated from acceptable toxicity tests. In cases where less chronic data are available, but where 

there are at least three chronic tests from taxa that also have appropriate acute toxicity data, the 

chronic criterion can be derived by determining an appropriate acute-chronic ratio (ACR). The 

ACR is a way of establishing a relationship between the acute and chronic toxicities of a 

chemical to aquatic organism. ACRs can be used to derive chronic criteria with data for species 

of aquatic animals provided that the MDR of at least three species is met and that:

 at least one species is a fish

 at least one species is an invertebrate

 at least one species is an acutely sensitive estuarine/marine species (the other two species 

data may be freshwater or estuarine/marine, as appropriate, for the derivation).

ACRs are calculated by dividing the acute toxicity test values by a “paired” chronic test value. 

Tests for a chemical are considered paired when they are conducted by the same laboratory, with 

the same test organism and with the same dilution water. A chronic criterion is not derived if 

there is more than a ten-fold difference amongst ACRs and if there is no clear trend related to 

species sensitivity (Stephan et al. 1985). If these criteria are met, the Final Acute-Chronic Ratio 

(FACR) may be the geometric mean of the available ACRs or an individual ACR (or 

combination therefore), based on the most sensitive taxa. The Final Chronic Value (FCV) is then 

estimated by dividing the FAV by the FACR. This serves as the basis for the chronic criterion. 

The FCV then may be lowered if necessary to protect recreationally or commercially important 

species.

2.8.3 BLM Evaluation

Use of the BLM to predict the bioavailability and toxicity of copper to estuarine/marine

organisms under site-specific conditions is a significant modification from the previous criteria 

derivation methodology, which used no relationships (e.g., salinity) to adjust the criteria. As 

detailed in Section 2.4, the BLM is based on the premise that toxicity is related to metal bound to 
39

a biochemical site (the biotic ligand) and that binding is related to total dissolved metal 

concentrations and complexing ligands in the water, with the BLM explicitly accounting for 

individual water quality variables that affect bioavailability and toxicity. This document utilizes 

the recently developed saltwater BLM to provide an updated BLM-based water quality criterion

that is applicable to marine and estuarine waters.

Table 4 summarizes the water quality input parameters required for the freshwater and 

marine copper BLMs. As shown in Table 4, the saltwater BLM for copper has relatively few 

input parameters, compared with the freshwater BLM.

Table 4. Water Quality Input Parameters for the Freshwater and Saltwater Versions of the 

BLM.

Freshwater BLM Input Parameters Saltwater BLM Input Parameters

Temperature Temperature

pH pH

DOC DOC

Calcium Salinity

Magnesium

Sodium

Potassium

Sulfate

Chloride

Alkalinity

Sulfide

Because the ionic composition of marine water is relatively constant (Turekian 1968), all 

of the cations, anions, and alkalinity are estimated from salinity. The major dissolved ions in 

seawater (Cl, Na, Mg, SO4, Ca, K, HCO3), and used in toxicity tests, are present in constant 

ratios. Individual ion concentrations can therefore be easily calculated from a known salinity or 

from the known concentration of a single ion (Pilson 1998). The defined and consistent ionic 

composition of saltwater is what reduces the needed input parameters for the copper saltwater 

BLM to just temperature, pH, DOC, and salinity. Approximating the ionic content of variable 

salinity samples in this way assumes that the freshwater component mixing with the marine 

water is devoid of ions. Actual freshwaters mixing into estuaries will, of course, have variable 
40

ionic content. The deviation from this simplified assumption and the actual chemistry of the 

estuary will depend on how ionically rich the freshwater is, and how far upstream the estuary 

(i.e., to how low a salinity level) the estimation is used. It is clear, however, that to the extent that 

the actual ionic content is different, it will always be higher than the estimate, and therefore the 

estimate will always be conservative. Despite the reduction in the number of parameters needed, 

much of the currently available aquatic toxicity literature for metals does not include the 

measurement or reporting of all key BLM input parameters. Additional data were therefore 

obtained from the authors, additional measurements were made in relevant water sources, or 

input parameters were estimated when necessary to fill in these data gaps. As with any modeling 

effort, however, the reliability of the BLM-derived accumulation and toxicity values for this 

project are subject to the limitations of the input measurements and estimation procedures 

described above.

The criteria presented herein are the agency’s best estimate of maximum concentrations 

of copper to protect most estuarine/marine aquatic organisms from any unacceptable short- or 

long-term effects. Results of such intermediate calculations such as SMAV and chronic values 

are specified to four significant figures to prevent rounding errors in subsequent calculations and 

the number of places beyond the decimal point does not reflect the precision of the value.
41

3 EFFECTS ANALYSES FOR AQUATIC ORGANISMS

3.1 Summary of Acute Studies

The acute criterion or CMC was calculated according to the procedure described in the 

following section. The reported acute toxicity values (LC50s or EC50s) determined to be 

acceptable for use in criteria development (summarized in Appendix Table A-1) and individual 

test water chemistry parameters were first used to calculate lethal accumulation values (LA50s). 

The LA50s represent the critical threshold concentrations at the biotic ligand that result in acute 

toxicity and were used to normalize toxicity values (e.g., LC50s) to a standard water condition 

(Appendix Table A-1, footnote e). As used here, “normalization” refers to the procedure by 

which all of the measured effect levels were adjusted, via use of the BLM, to predict effect 

concentrations that would have been expected in the selected water chemistry (see Section 3.3). 

LA50s were determined by running the saltwater BLM in speciation mode (see BLM User’s 

Guide)2. The resulting normalized effect concentrations were then used to calculate the Species 

Mean Acute Values (SMAVs), Genus Mean Acute Values (GMAVs), and the Final Acute Value 

(FAV) according to EPA’s Guidelines procedure. These values are relevant (for comparison 

purposes across species) only at the selected water chemistry values specified, but are used to 

allow the BLM model to predict the FAV and criteria in any water chemistry condition. Data that 

were identified during the review, but that were not considered to be acceptable and not included 

in the criteria calculations are listed in Appendix Table E-1.

Acceptable data on the acute effects of copper on estuarine/marine species were available

for 89 species representing 78 genera (Table 5). BLM-normalized (at the selected water 

chemistry) SMAVs ranged from 3.944 μg/L for the most sensitive species, the red abalone, 

Haliotis rufescens, to 81,550 μg/L for the least sensitive species, the amphipod Corophium 

volutator. Molluscs were among the most sensitive species, with H. rufescens, Mytilus edulis and

M. galloprovincialis, having three of the five lowest SMAVs. The other two of five lowest 

SMAVs were for the copepod, Tigriopus californicus, and the purple sea urchin, 

Strongylocentrotus purpuratus (Arnold et al. 2010a; City of San Jose 1998; Dinnel et al. 1989; 

 

2 The saltwater BLM has the same two prediction modes (speciation and toxicity) as the freshwater model. The 

speciation mode is only used in the context of a data processing step and is not a mode that is needed or publicly 

available in the software distributed for calculating estuarine/marine criteria.
42

O’Brien et al. 1988; Rosen et al. 2008). Invertebrates, including molluscs, were generally more 

sensitive than fish, representing 19 of the 20 lowest GMAVs (Table 5).

Table 5. Ranked Estuarine/Marine Genus Mean Acute Values.

(All values were normalized to select water chemistry conditions, see Section 3.3).

Rank

Genus Mean 

Acute Value 

(μg/L) Genus Species

Species Mean 

Acute Value 

(μg/L)

78 81,550 Corophium Amphipod,

Corophium volutator 81,550

77 43,694 Rangia Clam,

Rangia cuneata 43,694

76 >33,000 Opsanus Gulf toadfish,

Opsanus beta >33,000

75 31,716 Limulus Horseshoe crab,

Limulus polyphemus 31,716

74 >29,733 Gammarus Amphipod,

Gammarus duebeni >29,733

73 8,976 Callinectes Blue crab,

Callinectes sapidus 8,976

72 8,863 Micropogonias Atlantic croaker,

Micropogonias undulatus 8,863

71 8,423 Rivulus Mangrove killifish,

Rivulus marmoratus 8,423

70 4,898 Mugil Striped mullet,

Mugil cephalus 4,898

69 4,428 Centropomus Fat snook,

Centropomus parallelus 4,428

68 4,145 Lagodon Pinfish,

Lagodon rhomboides 4,145

67 3,715 Nitokra Copepod,

Nitokra spinipes 3,715

66 3,690 Boleophthalmus Mud-skipper,

Boleophthalmus sp. 3,690

65 3,014 Litopenaeus Whiteleg shrimp,

Litopenaeus vannamei 3,014

64 2,590 Palaemonetes Grass shrimp,

Palaemonetes pugio 2,590

63 2,512 Terapon Thornfish,

Terapon jarbua 2,512

62 2,492 Emerita Sand crab,

Emerita analoga 2,492

61 2,163 Palaemon Decapod,

Palaemon elegans 2,163

60 2,057 Amphiascoides Copepod,

Amphiascoides atopus 2,057
43

Rank

Genus Mean 

Acute Value 

(μg/L) Genus Species

Species Mean 

Acute Value 

(μg/L)

59 1,675 Eurythoe Polychaete,

Eurythoe complanata 1,675

58 1,672 Sphaeroma Isopod,

Sphaeroma serratum 1,672

57 1,538 Crepidula

Gastropod,

Crepidula convexa 1,105

Gastropod,

Crepidula fornicata 2,141

56 1,534 Archosargus Sheepshead,

Archosargus probatocephalus 1,534

55 1,416 Turbo Whelk,

Turbo coronatus 1,416

54 1,089 Planaxis Grooved snail,

Planaxis sulcatus 1,089

53 1,058 Penaeus Tiger shrimp,

Penaeus monodon 1,058

52 875.7 Trachinotus Pompano,

Trachinotus carolinus 875.7

51 730.8 Carcinus Shore crab,

Carcinus maenas 730.8

50 646.9 Perna Asian green mussel,

Perna viridis 646.9

49 623.4 Hediste Polychaete,

Hediste(Nereis) diversicolor 623.4

48 611.0 Cymatogaster Shiner perch,

Cymatogaster aggregata 611.0

47 589.5 Ophionereis Bristle star,

Ophionereis dubia 589.5

46 556.3 Fundulus Mummichog,

Fundulus heteroclitus 556.3

45 515.7 Allorchestes Amphipod,

Allorchestes compressa 515.7

44 512.2 Cyprinodon

Leon Springs pupfish, *

Cyprinodon bovinus 778.0

Sheepshead minnow,

Cyprinodon variegatus 337.2

43 445.6 Oncorhynchus Coho salmon,

*

Oncorhynchus kisutch 445.6

42 350.2 Mercenaria Hard clam,

Mercenaria mercenaria 350.2

41 341.6 Balanus

Barnacle,

Balanus amphitrite 139.7

Barnacle,

Balanus eburneus 835.4

40 260.8 Farfantepenaeus Pink shrimp,

Farfantepenaeus duorarum 260.8
44

Rank

Genus Mean 

Acute Value 

(μg/L) Genus Species

Species Mean 

Acute Value 

(μg/L)

39 255.4 Crangon Shrimp,

Crangon crangon 255.4

38 229.9 Morone Striped bass,

Morone saxatilis 229.9

37 222.9 Loligo Squid,

Loligo opalescens 222.9

36 190.6 Leiostomus Spot,

Leiostomus xanthurus 190.6

35 185.0 Atherinops Topsmelt,

Atherinops affinis 185.0

34 130.1 Echinogammarus Amphipod,

Echinogammarus olivii 130.1

33 112.8 Neanthes Polychaete,

Neanthes arenaceodentata 112.8

32 106.8 Metapenaeus Shrimp,

Metapenaeus sp. 106.8

31 106.4 Pseudopleuronectes Winter flounder,

Pseudopleuronectes americanus 106.4

30 101.2 Pseudodiaptomus Copepod,

Pseudodiaptomus coronatus 101.2

29 99.77 Tisbe Copepod,

Tisbe furcata 99.77

28 87.98 Hydroides Polychaete,

Hydroides elegans 87.98

27 85.48 Orchomenella Amphipod,

Orchomenella pinguis 85.48

26 82.57 Americamysis

Mysid,

Americamysis bahia 96.60

Mysid,

Americamysis bigelowi 70.57

25 75.27 Elasmopus Amphipod,

Elasmopus rapax 75.27

24 72.63 Aiptasia Sea anemone,

Aiptasia pallida 72.63

23 64.47 Menidia

Inland silverside,

Menidia beryllina 46.01

Atlantic silverside,

Menidia menidia 85.97

Tidewater silverside,

Menidia peninsulae 67.73

22 64.20 Scorpaenichthys Cabezon,

Scorpaenichthys marmoratus 64.20

21 53.80 Anaitides Polychaete,

Anaitides maculata 53.80

20 35.72 Cancer Dungeness crab,

Cancer magister 35.72
45

Rank

Genus Mean 

Acute Value 

(μg/L) Genus Species

Species Mean 

Acute Value 

(μg/L)

19 32.60 Neomysis Mysid,

Neomysis mercedis 32.60

18 28.37 Homarus Lobster,

Homarus americanus 28.37

17 28.35 Spisula Surf clam,

Spisula solidissima 28.35

16 23.03 Mya Softshell clam,

Mya arenaria 23.03

15 23.03 Brachionus Rotifer,

Brachionus plicatilis 23.03

14 22.44 Eurytemora Copepod,

Eurytemora affinis 22.44

13 16.49 Dendraster Sand dollar,

Dendraster excentricus 16.49

12 16.40 Acartia

Copepod,

Acartia clausi 21.86

Copepod,

Acartia tonsa 12.31

11 15.35 Argopecten Bay scallop,

Argopecten irradians 15.35

10 13.85 Arbacia Sea urchin,

Arbacia punctulata 13.85

9 12.58 Diadema Long-spined sea urchin,

Diadema antillarum 12.58

8 12.38 Mulinia Coot clam,

Mulinia lateralis 12.38

7 10.29 Strongylocentrotus

Green sea urchin,

Strongylocentrotus droebachiensis 13.29

Purple sea urchin, 

Strongylocentrotus purpuratus 7.971

6 10.10 Crassostrea

Pacific oyster,

Crassostrea gigas 11.94

Eastern oyster,

Crassostrea virginica 8.537

5 9.572 Holmesimysis Mysid,

Holmesimysis costata 9.572

4 9.153 Haliotis

Black abalone,*

Haliotis cracherodii 21.24

Red abalone,

Haliotis rufescens 3.944

3 8.848 Paralichthys Summer flounder,

Paralichthys dentatus 8.848

2 7.847 Tigriopus Copepod, 

Tigriopus californicus 7.847

1 5.577 Mytilus Blue mussel,

Mytilus edulis 4.238
46

Rank

Genus Mean 

Acute Value 

(μg/L) Genus Species

Species Mean 

Acute Value 

(μg/L)

Mediterranean mussel,

Mytilus galloprovincialis 7.338

a From Appendix Table A-1.

* Listed species.

3.2 Summary of Chronic Studies

Acceptable estuarine/marine copper chronic values are available for only two species, the 

euryhaline rotifer, Brachionus plicatilis (Arnold et al. 2010b) and the sheepshead minnow, 

Cyprinodon variegatus (Hughes et al. 1989) (Appendix Table B-1). These chronic toxicity 

values were obtained from a multigeneration life-cycle test with the rotifer, and a flow-through 

early life stage (ELS) test with the sheepshead minnow. Copper concentrations were measured in 

the test chambers of both tests. As for the acute values, the chronic values presented below are 

BLM-normalized and are relevant (for comparison purposes across species) only at the selected 

water chemistry values specified, but are used to allow the BLM model to predict the criteria in 

any water chemistry condition.

The static multigeneration life cycle test with the rotifer, conducted by Arnold et al. 

(2010b), was used to develop an acute-chronic ratio for the species (Table 6). Neonates were 

exposed to seven copper concentrations in artificial seawater for 96 hours (Note: due to the life 

history of this short-lived organism, this duration represents a chronic exposure). The intrinsic 

rate of rotifer population increase was negatively affected (37% decrease) at 10.3 μg/L dissolved 

copper, but not at 6.1 μg/L, with a MATC value of 7.927 μg/L. The authors reported an EC20 of 

10.9 μg/L dissolved copper, or 13.23 μg/L once BLM normalized. Dividing the 48-hr LC50s from 

this study by the EC20 resulted in an ACR of 1.229 (13.4 μg/L/10.9 μg/L) when the rotifers were 

not fed in the acute test, and an ACR of 1.908 (20.8 μg/L /10.9 μg/L) when the rotifers were fed

in the acute test (Appendix Table B-2).

The ELS test with sheepshead minnow did not provide concentration-response data and 

regression analysis could not be done. In the 28-day ELS test, growth was reported to be a more 

sensitive endpoint than mortality, and the chronic value for growth was 249 μg total Cu/L (or 

226.8 μg dissolved Cu/L). The BLM normalized MATC is 204.1 μg/L dissolved copper.
47

Dividing the 96-hr LC50 from this study by the 28-day chronic value (368/249 μg/L) resulted in 

an ACR of 1.475 (Appendix Table B-2).

Table 6. Ranked Estuarine/Marine Genus Mean Chronic Values with Species Mean AcuteChronic Ratios.

(All values were normalized to select water chemistry conditions, see Section 3.3).

Rank

Genus Mean 

Chronic Value

(μg/L) Genus Species

Species Mean 

Chronic Value

(μg/L)a ACR

2 204.1 Cyprinodon Sheepshead minnow,

Cyprinodon variegatus 204.1 1.475

1 13.23 Brachionus Rotifer,

Brachionus plicatilis 13.23 1.229 / 1.908 fed

a From Appendix Table B-1.

Other chronic toxicity data deemed unacceptable for quantitative use in the criteria 

derivation (Appendix Table E-1), but generally considered to be representative were evaluated 

to determine ACRs for additional species for purposes of comparison. A 28-day LC50 of 56 μg/L 

was reported for the polychaete, Neanthes arenaceodentata (Pesch and Hoffman 1982), which 

yields an ACR of 2.298 when divided into the SMAV of 128.7 μg/L. Pesch et al. (1979) reported 

an EC50 of 5.8 μg/L for reduced growth for the bay scallop, Argopecten irradians, based on 

exposure to copper for 42 days. Division of the SMAV (25.01 μg/L) by this value gives an ACR 

of 4.312. Data for these two additional invertebrate species, although not used quantitatively in 

the criteria derivation, are consistent with and generally support the lower (<2) ACRs given for 

the rotifer and sheepshead minnow.

3.3 Summary of BLM Water Quality Input Parameters

Table 7 summarizes the selected water quality input parameters used for the saltwater

BLM normalization. The designation of these parameters is not in and of itself important other 

than to define a consistent set of conditions to which to normalize all the data. The LC50 and 

EC50 values presented in Appendix Table A-1 were standardized to these specified water 

chemistry conditions (see footnote “e”). The reported chemistry for each individual study is 

presented in Appendix Table H-1 and summary statistics of all the test conditions are provided 

in Appendix Table H-2. Likewise, the estuarine/marine chronic values in Appendix Table B-1

are normalized to the same specified water chemistry conditions. These inputs were standardized 
48

in order to perform calculations with a consistent set of parameters and to ensure the selection of 

these parameters does not affect either the rank order of the species sensitivity distribution or the 

resulting criteria calculations (Di Toro et al. 2001). Following normalization of the data 

presented in Appendix Table A-1, the BLM can be used to calculate an FAV which accounts for 

changes to any variable included in the model (i.e., temperature, pH, salinity, and DOC). DOC is 

typically the most important variable because pH tends to have limited variation in marine water, 

while salinity and temperature have a lesser effect on copper bioavailability than does DOC.

Table 7. Water Quality Input Parameters Used for Saltwater BLM-Normalization.

Saltwater BLM Input Parameters Saltwater BLM Input Value

Temperature 22°C

pH 8

DOC 1.0 mg/L

Salinity 32 ppt

3.4 Bioaccumulation

Copper bioaccumulates in aquatic organisms, although increased accumulation through 

trophic levels in aquatic food chains (i.e., biomagnification) is not usually observed (Lewis and 

Cave 1982; Suedel et al. 1994). Total uptake generally depends on the environmental copper 

concentration, exposure route and the duration of exposure (McGeer et al. 2000). 

Bioconcentration Factors (BCFs) typically vary with the bioavailable concentration of copper in 

water, with higher BCFs occurring at lower copper concentrations (McGeer et al. 2003; U.S. 

EPA 2010a). Some of the highest reported BCFs for copper are for marine and freshwater 

bivalves (Hamelink et al. 1994). Copper bioavailability and toxicity is promoted by oxine and 

other lipid soluble synthetic organic chelators in marine ecosystems (Bryan and Langston 1992). 

In marine sediments, bioavailability is altered by increased acid volatile sulfide (AVS) content 

(Casas and Crecelius 1994), and ligand concentration (Skrabal et al. 2000). A more detailed 

discussion of bioaccumulative factors is provided in the Effects Characterization (Section 4.3).

3.5 Toxicity to Aquatic Plants

No acceptable estuarine/marine copper toxicity tests are available for algal or aquatic 

vascular plant species for which the concentrations of test material were measured. Therefore, a 
49

Final Plant Value (FPV) could not be determined. Effects on aquatic plants are discussed 

qualitatively in the Effects Characterization (Section 4.4).

3.6 The National Estuarine/Marine Criteria for Copper

3.6.1 Acute Criterion Calculation

Acceptable acute toxicity values are available for 89 species representing 63 taxonomic

families (Table 3). The ranked GMAVs are presented in Figure 9 and the ranked SMAVs and 

summaries of acute toxicity test data for individual species are shown in Figure 10 for 

comparison. Because more than 59 GMAVs were available for copper, the FAV was derived 

from the four GMAVs that have cumulative probabilities closest to the 5th percentile toxicity 

value for all the tested genera. The 5th percentile of the species sensitivity distribution, equivalent 

to the FAV, was estimated as 9.138 μg/L (Table 8) (Note: the FAV changes with respect to the 

conditions at the site, and the values represented below only apply to the selected conditions in 

Table 7). For previous estuarine/marine criteria, the FAV was lowered to protect commercially 

and recreationally important mussel species. For these data, a value that is protective of 

commercially and recreationally important species would involve lowering the FAV to the 

SMAV for Haliotis rufescens, which is the lowest SMAV amongst commercially and 

recreationally important species with a value of 3.944 μg/L. The calculated FAV was therefore 

lowered to the SMAV for H. rufescens and the CMC was set to this lowered FAV divided by 

two (3.944/2=2.0 μg/L) (Table 8).
50

Table 8. Estuarine/Marine Water Final Acute Value (FAV) and Criteria Calculations.

(All values were normalized to select water chemistry conditions see Section 3.3).

N Rankb Genus GMAV ln(GMAV) ln(GMAV)2 P=R/(N+1) sqrt(P)

78 5 Holmesimysis 9.572 2.26 5.10 0.063 0.252

4 Haliotis 9.153 2.21 4.90 0.051 0.225

3 Paralichthys 8.848 2.18 4.75 0.038 0.195

2 Tigriopus 7.847 2.06 4.24 0.025 0.159

Sum: 8.71 19.00 0.177 0.831

S

2 = 4.575

L = 1.734

A = 2.212

FAV (calculated) = 9.138

FAV (H. rufescens lowered) = 3.944

CMCa = 2.0

 Where, S=slope, L=intercept, A=ln(FAV); and FAV=final acute value

a

 When the temperature=22°C, pH=8, DOC=1.0 mg/L, and salinity=32 ppt.

b

 According to the Guidelines, ranks 2-5 are used in the calculation of the FAV (Stephan et al. 

1985).

The recommended CMC of 2.0 μg/L is specific for the seawater chemistry specified in 

Table 7, which consists of the following physical and chemical parameter assumptions: 

temperature=22°C, pH=8, DOC=1.0 mg/L and salinity=32 ppt. The BLM analysis can be 

adjusted to incorporate different physical and chemical parameters to be protective of aquatic life 

under varied conditions (see Appendix I).
51

Figure 9. Ranked Estuarine/Marine GMAVs.
52

Figure 10. Reported Dissolved Cu LC50s Ranked by the Geomean of the Normalized Cu Values (i.e., SMAVs).

(For each species, the box shows the range from the 25th to the 75th percentile of the available BLM normalized EC50s, and the geometric mean 

SMAV is shown by the horizontal line within the box. The whiskers show the maximum and minimum values, exclusive of outlier points. Outliers 

are shown as individual symbols. Test species are identified on the x-axis labels using species numbers listed in Appendix Table G-1).
53

3.6.2 Chronic Criterion Calculation

The Criterion Continuous Concentration (CCC) can be derived either from chronic values 

if the MDRs are met, or from the FAV divided by a FACR (Stephan et al. 1985). Since

estuarine/marine chronic values are available for only two species and the MDR is not met, the 

FAV divided by the FACR was used to determine the CCC.

Two valid estuarine/marine ACRs are available for copper (Table 6). The sheepshead 

minnow, Cyprinodon variegatus, is a relatively insensitive estuarine/marine water species on an 

acute basis, with a GMAV falling at approximately the midway point of sensitivity of all the 

tested estuarine/marine genera (Rank 44), while the rotifer Brachionus plicatilis is more 

sensitive, with a GMAV falling within the lower quarter of the all tested species (Rank 15)

(Table 5). The lowest estuarine/marine acute values are from tests with embryos and larvae of 

molluscs and embryos of summer flounder, which are also likely to be the most sensitive life 

stages of these species. Although estuarine/marine ACRs are not available for these sensitive 

species, ACRs are available for the most acutely sensitive freshwater species tested to date for 

copper (Appendix Table B-2). 

Individual ACRs varied amongst studies ranging from <1 (0.142) for Ceriodaphnia dubia 

(Harmon et al. 2003) to 191.6 for the snail, Campeloma decisum (Arthur and Leonard 1970). 

Species mean ACRs ranged from 1.229 for the rotifer, B. plicatilis to 171.2 for the freshwater 

snail, C. decisum. The Guidelines outline four primary ways to combine ACRs to calculate an 

appropriate FACR.

 If the species mean acute-chronic ratios seems to increase or decrease as the SMAV 

increases, the Final Acute-Chronic Ratio should be calculated as the geometric mean of 

the acute-chronic ratios for species whose SMAVs are close to the Final Acute Value.

 If no major trend is apparent and the acute-chronic ratios for a number of species are 

within a factor of ten, the Final Acute-Chronic Ratio should be calculated as the 

geometric mean of all the species mean acute-chronic ratios available for both freshwater 

and saltwater species.

 For acute tests conducted on metals and possibly other substances with embryos and 

larvae of barnacles, bivalve molluscs, sea urchins, lobsters, crabs, shrimp, and abalones, 

it is probably appropriate to assume that the acute-chronic ratio is 2. Thus, if the lowest 

available SMAVs were determined with embryos and larvae of such species, the Final 

Acute-Chronic Ratio should probably be assumed to be 2, so that the Final Chronic Value 

is equal to the Criterion Maximum Concentration.
54

 If the most appropriate species mean acute-chronic ratios are less than 2.0, and especially 

if they are less than 1.0, acclimation has probably occurred during the chronic test. 

Because continuous exposure and acclimation cannot be assured to provide adequate 

protection in field situations, the Final Acute-Chronic Ratio should be assumed to be 2, 

so that the Final Chronic Value is equal to the Criterion Maximum Concentration.

Since the available ACRs are not within a factor of 10, and because a relationship is 

evident between acute sensitivity and ACRs, the FACR was calculated as the geometric mean of 

the ACRs for species with SMAVs close to the FAV, and that have taxonomically related marine 

species. The FACR of 3.022 was calculated as the geometric mean of the genus mean ACRs for 

five sensitive freshwater genera, Ceriodaphnia (3.268), Daphnia (4.057), Oncorhynchus (3.630),

Acipenser (5.757) and Cottus (2.075), along with the two estuarine/marine genus mean ACRs for 

Cyprinodon (raised to 2.0) and Brachionus (raised to 2.0) (Appendix Table B-2). The final 

chronic value (FCV) for copper at the selected water chemistry (Table 7) is the FAV of 3.944

μg/L (lowered to protect H. rufescens) divided by the FACR and equals 1.3 μg/L Cu. The CCC, 

which is equivalent to the FCV, is lower than the two acceptable GMCVs available for copper 

(Figure 11) at the specified chemistry.
55

Figure 11. Ranked Estuarine/Marine GMCVs.

3.7 Summary of National Criteria

The resulting recommended ambient WQC indicate that estuarine/marine aquatic 

organisms would have an appropriate level of protection if the 1-hour average and four-day 

average dissolved copper concentrations do not respectively exceed the acute and chronic criteria 

concentrations calculated by the saltwater BLM more than once every three years on average. 

For the 2016 acute criteria, EPA has changed the duration to 1 hour from the 24 hours EPA 

applied in the 2003 draft copper criteria document and the 2007 freshwater copper criteria 

document. EPA made this change to the 2016 criteria to reflect the acute criteria duration 

recommended in the Guidelines (see Section 4.1.2). The WQC numeric values will change in 

response to changes in water quality parameters (i.e., temperature, salinity, dissolved organic 

carbon and pH).
56

For example, at the selected water chemistry conditions chosen for BLM-normalization 

(temperature=22°C, pH=8, DOC=1.0 mg/L and salinity=32 ppt), the resulting recommended 

ambient WQC indicate that estuarine/marine aquatic organisms would have an appropriate level 

of protection if the 1-hour average dissolved copper concentration does not exceed 2.0 μg/L 

more than once every three years on average, and if the four-day average dissolved copper 

concentration does not exceed 1.3 μg/L more than once every three years on average. There may 

be an exception, however, if a locally important species is more sensitive. 

The BLM can be used to adjust criteria values to be protective under different 

temperature, pH, DOC, and salinity conditions. For example, when the site conditions are 

changed to assume a temperature=20°C, pH=8, DOC=4.0 mg/L and salinity=15 ppt (which may 

be typical conditions for an estuary with moderate DOC concentrations), the resulting CMC and 

CCC are 7.1 and 4.7 μg/L, respectively. Appendix I provides a discussion of temperature, pH, 

DOC and salinity conditions expected to occur in estuarine and marine waters around the United 

States, a discussion of environmental variables affecting each of these conditions, and additional 

examples of numeric criteria values for copper depending on selected water quality inputs. 

3.8 Identification of Data Gaps for Aquatic Organisms

3.8.1 Chronic Toxicity Data for Estuarine/Marine Animals

Limited acceptable chronic copper toxicity data are available for estuarine/marine animal 

species. Studies are available for only two estuarine/marine animal species, as discussed in 

Section 3.2. The FCV is therefore based on the use of a FACR. The FACR assumes that the 

relationship between acute and chronic toxicity for each species is constant. Acceptable ACRs 

are averaged across taxa to calculate the final overall relationship between the acute and chronic 

toxicity values. Since freshwater ACRs are used to bolster the calculation of the FACR, due to 

only two estuarine/marine genus-level ACRs being available, this creates an additional 

uncertainty in the estuarine/marine FCV.

3.8.2 Chronic Toxicity Data for Aquatic Vascular Plants and Algae

Acceptable toxicity data are limited for aquatic vascular plants and algae for which the 

concentrations of test material were measured. Accordingly, the available plant data did not meet 

the MDRs established in the Guidelines to support the derivation of a plant-based value

(Appendix Table C-1). However, analysis of the toxicity data that are available for 
57

estuarine/marine plant species, which is discussed in Section 4.4, suggests that a chronic 

criterion value that is protective of estuarine/marine animals would also be protective of aquatic 

plants (see Section 4.4).

3.8.3 BLM Uncertainties and Performance

The BLM used to update the estuarine/marine copper criteria employs equilibrium 

reactions for copper and other anions/cations using a single and simple type of surface ligand to 

characterize the effects of all physical and chemical exposure conditions on toxicity. As such, the 

model is a simplified and approximate representation of a complex set of chemical reactions and 

transfers that are involved with environmental copper eliciting toxicity. As already noted, cation 

effects may involve mechanisms in addition to competition for a surface ligand. Further, the 

microenvironment at the gill surface and other biological membranes of toxic interaction for

juvenile and adult fish might change copper speciation, but the most sensitive organisms to 

which the criteria are applicable (and likely to determine the FAV) are embryo-larval life stages 

of invertebrates that do not have a gill microenvironment. Finally, because the biotic ligand 

refers to specific binding sites in the organism, accumulation measurements taken from digests 

of whole embryonic stages, or based on bulk gill tissue could include metal in addition to that 

bound to the biotic ligand, including metal that has been taken up and transported by the cell or 

organ. 

Despite the uncertainties described in this section, the BLM provides a reasonable 

mechanistic framework for the well-established effects of copper speciation, explicitly 

addressing the relative bioavailability of different copper species. It also includes a plausible 

mechanism that allows the effects of cations to be addressed and uses a comprehensive model for 

calculating the concentrations of various copper species. Even if the mechanistic descriptions are 

incomplete, this model allows the major empirical effects of complexing ligands and competing 

cations to be described in a more comprehensive and reasonable fashion than other approaches 

(U.S. EPA 2007).
58

4 EFFECTS CHARACTERIZATION

The Effects Characterization section evaluates the potential effects of copper on 

estuarine/marine aquatic life based on available test data and describes additional lines of 

evidence that were not used directly in the criteria calculations, but which support the 2016

aquatic life criteria values. This section also provides a summary of uncertainties and 

assumptions, and explanations for decisions about the acceptability and use of data in the effects 

assessment. Finally, this section describes substantive differences between the 2003 draft copper 

ALC and the 2016 update, based on incorporation of the latest scientific information. 

All acceptable acute and chronic values used to derive criteria are presented in Appendix 

Table A-1 and Appendix Table B-1, respectively. Studies that were determined to be 

scientifically sound, but not meeting with screening guidelines for inclusion in criteria

calculations are presented in Appendix Table E-1. Studies that were not used qualitatively or 

quantitatively in the criteria development and the reason they were not used are provided in 

Appendix Table F-1.

4.1 Estuarine/Marine Acute Toxicity Data

Acceptable acute toxicity data are available for 89 estuarine/marine species representing 

78 genera. These data were used to support the development of an estuarine/marine acute 

criterion.

Aquatic invertebrates are more acutely sensitive to copper than fish in the marine 

environment. Amongst the ten most sensitive genera to copper, nine are invertebrates and are

primarily represented by bivalves and echinoderms. BLM-normalized SMAVs for copper range 

from 3.944 to 81,550 μg/L. The most sensitive genus is the mussel Mytilus, followed by the 

copepod, Tigriopus, with BLM-normalized GMAVs of 5.577 and 7.847 μg/L, respectively. The 

two most tolerant genera were the amphipod, Corophium, and the clam, Rangia, with BLMnormalized GMAVs of 81,550 and 43,694 μg/L, respectively (Table 5). 

Several studies were identified as not meeting screening guidelines for inclusion in 

criteria calculations (Appendix Table E-1), but showed similar ranges of toxicity for a number 

of the most sensitive species (Note: the values below were BLM-normalized to the same water 

quality parameters in Table 7). Manley et al. (1984) reported a 72-hr LOEC of 4.258 μg/L 

copper to Mytilus edulis, which is similar to the GMAV for the genus (5.577 μg/L). Similarly, 
59

Fitzpatrick et al. (2008) observed increased abnormal larval development of Mytilus trossulus

embryos exposed to 4.623 μg/L copper for 48 hours. The Pacific oyster, Crassostrea gigas, was 

investigated by several authors and acute effect levels were observed at concentrations ranging 

from 1.890 to 65.90 μg/L copper for embryos exposed from one to three days, which is similar to 

the SMAV of 11.94 μg/L for the species (Brooks et al. 2007; Harrison et al. 1981; Worboys et al. 

2002). Eisler (1977) reported a 7-day LC50 of 16.22 μg/L copper for the soft-shell clam Mya 

arenaria, which is close to the GMAV of 23.03 μg/L reported for this species.

For fish, Anderson et al. (1994) reported 7-day LC50s for topsmelt, Atherinops affinis, 

larva that ranged from 25.46 to 78.71 μg/L copper. Pacific herring embryos, Clupea harengus 

pallasi, non BLM-normalized acute effect levels ranged from 33 to 900 μg/L copper (Rice and 

Harrison 1978). A 4-day LC50 of >164.4 μg/L copper was reported for larva of the sheepshead 

minnow, Cyprinodon variegates (Hutchinson et al. 1994). Cobia, Rachycentron canadum, 4-day 

LC50s ranged from 25.75 to 130.1 μg/L copper (Dung et al. 2005). The acute effect levels 

observed for all these species are similar to the BLM-normalized GMAV (64.20 μg/L copper) 

reported for the cabezon, Scorpaenichthys marmoratus, which was the second most sensitive fish 

species (Rank 22, Table 5) with acceptable acute data.

4.1.1 Uncertainty in the Estuarine/Marine FAV Calculation

A number of uncertainties are associated with calculation of the FAV as described in the

Guidelines (Stephan et al. 1985), and include use of limited data for a species or genus, 

application of safety factors, and extrapolation of laboratory data to the field. There are a number 

of cases in the acute database where only one acute test is used to determine the SMAV, and 

subsequently the GMAV is based on the one acute test. In this situation, species variability 

within a particular genus is unknown. The GMAV is still valid, in spite of absence of these 

additional data.

The final step in the acute criteria derivation process is to divide the FAV by a safety 

factor of 2 to yield the CMC. The CMC is set as equal to half of the FAV to represent a low level 

of effect for the fifth percentile genus, rather than a 50% effect. This adjustment factor was 

derived from an analysis of 219 acute toxicity tests with a variety of chemicals (see 43 FR 

21506-21518 for a complete description) where mortality data were used to determine the 

highest tested concentration that did not cause mortality greater than that observed in the control 
60

(or between 0 and 10%). Application of this safety factor is justified because that concentration 

represents minimal acute toxicity to the species.

Application of water-only laboratory toxicity tests to develop water quality criteria to 

protect aquatic species is a basic premise of the Guidelines, supported by the requirements of a 

diverse assemblage of eight families and the protection of 95 percent of all species. Confirmation 

has been reported by a number of researchers (Clements and Kiffney 1996; Clements et al. 2002; 

Mebene 2006; Norgberg-King and Mount 1986), thereby indicating that on the whole, 

extrapolation from the laboratory to the field is a scientifically valid and protective approach for 

aquatic life criteria development. 

4.1.2 Acute Criteria Duration

For the 2016 acute estuarine/marine copper criteria, EPA has changed the duration to 1-

hour from the 24 hours EPA applied in the 2003 draft copper criteria document and the 2007 

freshwater copper document. EPA made this change to the 2016 criteria to reflect the acute 

criteria duration recommended in the Guidelines. Both the 2003 and 2007 copper criteria 

documents used a 24-hour duration, but did not detail the rationale for this duration, and EPA has 

further examined this issue as part of the 2016 criteria update. 

EPA revised the acute duration in this document to be consistent with the more protective 

1-hour duration, which is generally supported by and consistent with the Guidelines. The 

Guidelines, for example, states the following:

“For the CMC the averaging period should again be substantially less than the lengths of 

the tests it is based on, i.e., substantially less than 48 to 96 hours. One hour is probably 

an appropriate averaging period because high concentrations of some materials can 

cause death in one to three hours. Even when organisms do not die within the first hour 

or so, it is not known how many might have died due to delayed effects of this short of an 

exposure. Thus it is not appropriate to allow concentrations above the CMC to exist for 

as long as one hour. The durations of the averaging periods in national criteria have 

been made short enough to restrict allowable fluctuations in the concentration of the 

pollutant in the receiving water and to restrict the length of time that the concentration in 

the receiving water can be continuously above a criterion concentration.” (Stephan et al. 

1985, page 5)
61

...“the one-hour average should never exceed the CMC.” (Stephan et al. 1985, page 6) 

Additional information supporting the 1-hour averaging period is presented in the 

Technical Support Document for Water Quality-based Toxics Control (U.S. EPA 1991) which 

states:

“For acute criteria, EPA recommends an averaging period of 1-hour. That is, to protect 

against acute effects, the 1-hour average exposure should not exceed the CMC. The 1-

hour acute averaging period was derived primarily from data on response time for 

toxicity to ammonia, a fast-acting toxicant. The l-hour averaging period is expected to be 

fully protective for the fastest-acting toxicants, and even more protective for sloweracting toxicants.” (U.S. EPA 1991, page 35)

The frequency of allowed exceedances is once in three years on average, as recommended 

in the Guidelines (Stephan et al. 1985). This is based on the ability of aquatic ecosystems to 

recover from criteria exceedances, which will depend in part on the magnitude and duration of 

the exceedance(s). 

4.2 Estuarine/Marine Chronic Toxicity Data

Data for only two estuarine/marine species are suitable for derivation of a chronic 

criterion. Suitable data are available for the rotifer, Brachionus plicatilis (BLM-normalized 

SMCV=13.23 μg/L dissolved Cu) and the sheepshead minnow, Cyprinodon variegatus (BLMnormalized SMCV=204.1 μg/L dissolved Cu).

Several studies that were identified as not meeting with screening guidelines for inclusion 

in criteria calculations reported chronic sublethal effects of copper on estuarine/marine 

invertebrates (Appendix Table E-1). The following data are BLM-normalized, unless noted. 

Three scleractinian coral species along with their algal symbionts were exposed to three 

measured copper concentrations for five weeks under flow-through conditions (Bielmyer et al. 

2010). The authors reported reduced growth chronic values of 14.69, >20.31 and <4.04 μg/L

copper (not BLM-normalized) for Acropora cervicornis, Montastraea faveolata and Pocillopora 

damicornis, respectively. Pesch et al. (1979) reported reduced growth for the bay scallop, 

Argopecten irradians, after exposure to 3.681 μg/L copper for 42-days. Gill alterations were 

observed by Frias-Espericueta et al. (2008a) in juvenile whiteleg shrimp, Litopenaeus vannamei,
62

after exposure to 80.61 μg/L copper for 28 days. The 26 to 28-day LC50s for the polychaete 

worms, Cirriformia spirabranchia and Neanthes arenaceodentata, ranged from 25.53 to 35.97

μg/L copper (Milanovich et al. 1976; Pesch and Hoffman 1982; Pesch and Morgan 1978). 

Channeled whelk, Busycon canaliculatum, Mediterranean mussel, Mytilus galloprovincialis, and 

quahog clam, Mercenaria, 28- to 77-day LC50 effect levels ranged from 25 to 470 μg/L copper 

(not BLM-normalized) (Bat et al. 2013; Betzer and Yevich 1975; Shuster and Pringle 1968). 

Limited chronic data are available for estuarine/marine fish species. Lacoue-Labarthe et 

al. (2010) exposed cuttlefish (Sepia officinalis) eggs to four unmeasured copper concentrations 

for 50 days and reported a hatchling weight NOEC and LOEC of 2.3 and 23 μg/L (not BLMnormalized), respectively. Several authors (Engel et al. 1976; Swedmark and Granmo 1981) 

conducted 14-day exposures for different species and reported copper not BLM-normalized LC50

effect levels of 10 μg/L for the Atlantic cod, Gadus morhua, 150 μg/L for the pinfish, Lagodon 

rhomboids, 160 μg/L for the spot, Leiostomus xanthurus, 210 μg/L for the Atlantic croaker,

Micropogonias undulates, and 610 μg/L for the Atlantic menhaden, Brevoortia tyrannus. 

Although the exposure periods were shorter than typically used for chronic studies, these data 

indicate response concentrations that are generally similar to the chronic effect level reported by 

Hughes et al. (1989) for sheepshead minnow, Cyprinodon variegatus (BLM-normalized 

SMCV=204.1 μg/L dissolved Cu), which was the only estuarine/marine fish for which 

acceptable chronic toxicity data were available.

4.2.1 Uncertainty in the Estuarine/Marine FCV Calculation

In addition to the uncertainties described above for the acute criteria derivation (Section 

4.1.1) and identification of data gaps (Section 3.8.1), the estuarine/marine FCV calculation is 

also influenced by the estimation of chronic values with MATC methods. The estimation of 

chronic values with an EC20 regression analysis is preferred over the use of MATCs because 

MATCs are highly dependent on the concentrations tested and can therefore potentially bias the 

chronic value either higher or lower than the EC20. Point estimates also provide additional 

information that is difficult to determine with an MATC, such as a measure of effect level across 

a range of tested concentrations. A MATC was used to determine the chronic value for the 

sheepshead minnow, whereas an EC20 was estimated for the rotifer.
63

4.3 Bioaccumulation

Bioconcentration factors (BCFs) for copper in estuarine/marine water are provided in 

Appendix Table D-1. In estuarine/marine water, the polychaete worms, Phyllodoc maculate, 

Neanthes arenaceodentata and Eudistylia vancouveri, had copper BCFs of 2,500, 2,950 and

1,006, respectively (McLusky and Phillips 1975; Pesch and Morgan 1978; Young et al. 1979). 

BCFs for six species of estuarine/marine bivalve molluscs range from 790 for the soft-shell clam,

Mya arenaria (Shuster and Pringle 1968), to 57,000 for the Pacific oyster, Crassostrea gigas

(Han and Hung 1990). Similarly, Shuster and Pringle (1968) found that the eastern oyster,

Crassostrea virginica, could concentrate copper to levels 27,800 times greater than ambient 

water concentrations during a 140-day continuous exposure to 25 μg/L copper. Even though the 

tissue of the oyster became bluish-green, mortalities were only slightly greater than in the 

controls. There are no BCF data for estuarine/marine fish or crustaceans meeting the data quality 

objectives required for inclusion in Appendix Table D-1 of this document. 

4.3.1 Uncertainty with Copper Exposure Routes

Aquatic organisms can accumulate copper from both aqueous and dietary exposure 

routes. The relative importance of each, however, is dependent upon the species. The filter 

feeding oyster Crassostrea gigas was found to accumulate more copper from ambient water than 

from phytoplankton food items (Ettajani et al. 1992), as did the suspension feeding cockle, 

Cerastoderma edule (Absil et al. 1996). Guo et al. (2013) exposed the abalone, Haliotis discus 

hannai, for eight weeks to either aqueous or dietary copper and observed that substantially more 

copper was accumulated in muscle tissue from the water exposure (10.8 fold increase) than the 

macroalgae diet (2.0 fold increase). Similar copper absorption efficiency or accumulation levels 

from water and diet were observed by Absil et al. (1994) for the sediment-dwelling bivalve, 

Macoma balthica (efficiencies ranged from 71-87% in aqueous exposures and from 78-90% in 

foodborne exposures), and by Long and Wang (2005) for the marine target fish, Terapon jarbua

(approximately two-fold increase for both). Pinho et al. (2007) also observed similar waterborne 

and waterborne plus dietborne copper accumulation for the copepod Acartia tonsa, irrespective 

of the salinity level (5, 15 and 30 ppt). Although accumulation decreased as salinity increased, no 

significant differences were observed between the exposure routes at each salinity exposure 

(from approximately 6.5 to 11.5 fold increases). Copper burdens in blackhead seabream 

Acanthopagrus schlegelii schlegelii intestine and liver after aqueous exposure (130 and 110 μg/g 
64

dw, respectively) were comparable to those after dietary exposure (140 and 95 μg/g dw, 

respectively) (Dang et al. 2012). In contrast, Bielmyer et al. (2005a) found significantly higher 

copper accumulation in the intestine and liver of saltwater-acclimated hybrid striped bass 

(Morone chrysops x Morone saxatilis) exposed to dietary copper (approximately 8-fold and 2-

fold increases, respectively) than those exposed to aqueous copper (no significant increases). In 

summary, the primary route of copper accumulation varies among species, with no consistent 

pattern.

The specific tissues/organs affected in an aquatic organism are also dependent on the 

exposure route. Several authors have postulated that copper speciation influences exposure route 

and the subsequent tissues and organs affected (Henry et al. 2012; Martins et al. 2011; Wang and 

Fisher 1996). Bivalve molluscs and crustaceans primarily accumulate dissolved metals across the 

gills, and particulate forms within the gut. In crustaceans, aqueous metals can be adsorbed to the 

body surface or taken up internally by ingestion, passive diffusion, or facilitated transport (Wang 

and Fisher 1998). For example, dissolved copper adsorbs onto the chitosan exoskeleton of 

pelagic and benthic crustaceans (Henry et al. 2012; Hook and Fisher 2001), or inert chitin 

surfaces of insects (Hare 1992), where it is rendered unavailable to interfere with internal 

metabolic processes. In contrast, ingested copper can accumulate into internal tissues potentially 

interfering with a variety of metabolic and reproductive processes (Hook and Fisher 2001). 

Copper assimilated from food is stored in the soft tissue of oysters (Amiard-Triquet et al. 1992). 

Lobsters accumulate aqueous copper primarily in their gills (Canli and Furness 1993), with most 

of the dietary copper deposited in the digestive gland (Chou et al. 1987). 

In marine fish, uptake of dissolved copper is either by the gills or the intestinal tract, and 

is sometimes influenced by ambient water and dietary levels (Grosell 2012). Accumulation of 

dissolved copper by the gills can be by either passive (diffusion) or active (pump) transport (Neff 

2002). Aqueous accumulation of copper via intestinal tissues is due to the ingestion of seawater 

for osmoregulatory purposes (Grosell et al. 2003, 2004). Fish exposed to metals in the presence 

of food initially absorb copper in the intestinal tract and to some degree the stomach, and 

subsequently transfer it to other tissues via the circulatory system (Wood et al. 2012). Waterborne copper primarily accumulated in the gill of the skate, Raja erinacea, and the sculpin, 

Myoxocephalus octodecemspinosus (Gosell et al. 2003). However, Blanchard and Grosell (2005) 

exposed the killifish, Fundulus heteroclitus, to aqueous copper at different salinities and 
65

observed the highest accumulations in the liver, gill and intestine. In comparison, dietary copper 

(as copper contaminated oysters) accumulated mainly in the intestine and to some extent the gill 

of the killifish, Fundulus heteroclitus (Blanchard et al. 2009). 

In an effort to determine the most toxic exposure route, three studies have compared the 

adverse effects of copper to marine organisms exposed separately to both aqueous and dietary 

copper. Bielmyer et al. (2005a) exposed saltwater-acclimated (15 ppt salinity) hybrid striped bass 

(Morone chrysops x Morone saxatilis) to dietary (571 to 1013 μg Cu/g), aqueous (22 to 44 μg 

Cu/L) and dietary plus aqueous copper concentrations for 42 days. None of the exposures 

scenarios had significant growth effects when compared to controls, although the authors noted 

that the dietary copper exposed fish had significant liver and intestinal copper accumulation. 

Conversely, Lauer and Bianchini (2010) observed exposure route differences when a copepod 

(Acartia tonsa) was exposed for six days to either dietary, aqueous or dietary plus aqueous 

copper concentrations at three different salinities (5, 15, 30 ppt). The copepods were exposed to 

three concentrations of aqueous copper, fed diatoms that were exposed to three aqueous 

concentrations of copper for 24 hours, or a combination of both. Pulsed exposures lasted 12 

hours each day over the six-day experiment, after which the copepods were transferred to clean 

media and allowed to reproduce for 24 hours. The water only exposure was the most toxic 

exposure route, with reduced egg production EC50s of 9.9, 36.8 and 48.8 μg/L dissolved copper,

followed by the dietary plus aqueous exposure with EC50s of 40.1, 63.7 and 109.9 μg/L dissolved 

copper at 5, 15 and 30 ppt, respectively. The diet only exposures exhibited the least effect, with a 

maximum of 43 percent reduction in reproduction regardless of exposure concentration or test 

salinity. A similar toxicological difference in exposure routes was observed in a 28-day study of 

juvenile blackhead seabream (Acanthopagrus schlegelii schlegelii) that was either fed a 

contaminated diet of copper or exposed to only copper in seawater. When based on similar 

estimated influx rates, the aqueous exposure was more toxic (31 percent mortality) than the diet 

only exposure (<10 percent mortality) (Dang et al. 2012).

Several other investigators examined the toxic effects of dietary copper exposures to 

marine organisms. Roberts et al. (2006) observed reduced survival of juvenile amphipods 

(Peramphithoe parmerong) fed a contaminated macroalgae that was cultured in a spiked solution 

containing 100 μg/L copper for 30 days. However, spiked solutions of up to 300 μg/L copper had 

no effect on the growth of survivors. Juvenile grey mullet (Chelon labrosus) fed a high-Cu diet 
66

of 2,400 μg/g dry weight for 67 days did not experience any mortality, but growth rate was 

reduced by 43 percent (Baker et al. 1998). Sea urchins (Lytechinus variegatus) fed two copper 

containing formulated diets (36 or 144 μg Cu/g) over twelve weeks had no significant difference 

in mortality, total diameter and total dry weight compared to the controls that were fed 12 μg 

Cu/g (Powell et al. 2010). Similarly, no death was observed when juvenile rock fish (Sebastes 

schlegeli) were fed one of four copper diets (50, 100, 250, 500 μg/g) for 60 days, but the specific 

growth rates for weight and length were reduced at 100 μg Cu/g and 250 μg Cu/g, respectively 

(Kang et al. 2005; Kim and Kang 2004). Lin et al. (2008) fed juvenile grouper (Epinephelus 

malabaricus) copper diets with eight different copper concentrations ranging from 0.11 to 20.05 

μg Cu/g for eight weeks. Weight gain and feed efficiency was significantly greater in diets 

containing 4.37 and 6.56 μg Cu/g, but was less in diets with ≤1.66 or ≥11.03 μg Cu/g. Survival 

in all exposures was ≥80 percent with no dose-response observed amongst treatments. No 

mortality was observed when adult male crabs (Neohelice granulata) were fed copper dosed 

algae (300 μg Cu/g) twice a week for five weeks. However, it should be noted that the exposure 

regime was equivalent to mean weekly doses of 6 μg Cu/g per crab (Sabatini et al. 2009).

Bielmyer et al. (2006b) exposed adult copepods (Acartia tonsa) to four copper-enriched 

diatom diets for seven days at a salinity of 30 ppt. The authors reported the 7-day reproductive 

EC20 as 22.3 μg Cu/g dry weight, or 1.2 μg Cu/L (the lowest diatom medium exposure 

concentration). In contrast, Lauer and Bianchini (2010) observed a diet-only 6-day reproductive 

EC20 of 23 μg Cu/g dry weight at a salinity of 30 ppt, or 40.1 μg Cu/L based on the diatom 

culture medium. In addition, they reported waterborne reproductive EC20s ranging from 8.3 to 

27.4 μg Cu/L. A review by Deforest and Meyer (2015) compared the results of these two studies 

and noted the following study design differences which may explain why the waterborne copper 

effect levels are different: 1) the dilution water in the Lauer and Bianchini (2010) study had a 

higher DOC level; 2) two different species of diatoms were used; 3) the diatoms were exposed 

for seven days in the Bielmyer et al. (2006b) study versus only 24 hours; and 4) the feeding 

regimes differed between the two studies. In addition, the Bielmyer et al. (2006b) study had 

unacceptable control survival (<80 percent) for a chronic test, which suggests that the test 

organisms may have been subjected to stresses other than copper during the exposure. So, while 

the 1.2 μg Cu/L effect concentration from the Bielmyer et al. (2006b) appears to be low, it may 

not be representative of the copper water effect concentration to this species. And as discussed 
67

earlier in Section 2.3, the apparent lack of aquatic food chain biomagnification (Lewis and Cave 

1982; Suedel et al. 1994) reduces the risk to higher trophic level predators including aquatic 

dependent wildlife.

Understanding the toxicological link between accumulated metal tissue levels and the 

observation of adverse effects remains difficult to characterize, and therefore has received 

considerable interest in recent years (Adams et al. 2011; Mebane 2006; Wood et al 2012). The 

poorly understood link between copper tissue levels and corresponding adverse effects is in part 

due to the various mechanisms utilized by different species to detoxify and/or sequester copper, 

thereby rendering it biologically unavailable. A well-known and widespread copper 

detoxification mechanism is the production of metal binding proteins (e.g., metallothioneins) by 

a number of invertebrates and fish in response to a metal exposure. Adams et al. (2011) noted 

that aquatic organisms contain a diverse array of homeostatic mechanisms that are both metaland species-specific, and therefore the risk to the aquatic organism could not be determined by 

whole-body tissue residue levels for metals, further suggesting tissue-based copper criteria may 

not accurately reflect ecotoxicological effects of copper under real-world exposure scenarios at 

the national-level. Thus, it is unclear if the copper accumulated in a specific fish organ is 

bioavailable or sequestered. Therefore, the link between total copper tissue levels and adverse 

effects is difficult to quantify since the majority of accumulated copper may be in a detoxified 

form.

4.4 Effects on Aquatic Plants

Data are available on the toxicity of copper to 26 species of estuarine/marine aquatic 

plants; however, these data were not used quantitatively in this effects assessment because they

did not meet the MDRs established in the Guidelines to support the derivation of a plant-based 

value (Appendix Table C-1). The species for which toxicity data are available encompass 

several classes of aquatic plants, inclusive of microalga, cyanobacterium, diatoms, 

dinoflagellates, green and red alga, and two species of kelp. The following data are not BLM 

normalized. A copper concentration of 60 μg/L copper caused a 50% decrease in photosynthesis 

in the giant kelp, Macrocystis pyrefera (Clendenning and North 1959), whereas a 21-day

exposure to 5 μg/L copper reduced gametophyte development rate in the kelp, Laminaria 

saccharina (Chung and Brinkhuis 1986). Zhu et al. (2011) reported a 7-day growth rate LOEC of 

50 μg/L copper for the brown alga, Hizikia fusiformis, and the less sensitive green seaweed, Ulva 
68

pertusa, had a chlorophyll fluorescence EC50 of 711 μg/L copper (Kumar et al. 2009). Growth

reduction in the red alga, Champia parvula, occurred in both the tetrasporophyte and female 

plants exposed to copper concentrations of 4.6 and 4.7 μg/L copper, respectively (Steele and 

Thursby 1983). Another red algal species, Ceramium tenuicorne, had a 7-day growth EC50 of 6.4 

μg/L copper. Dinoflagellates were equally sensitive to copper with growth rate reductions 

occurring at concentrations that ranged from 5 to 12,740 μg/L copper, with most reductions 

occurring at concentrations <50 μg/L copper. Diatoms were also sensitive to copper, with the 

most sensitive species, Thalassiosira aestevallis, having reduced growth at 19 μg/L copper with

a 3-4 day exposure period (Hollibaugh et al. 1980). 

The most sensitive plant effect concentrations were BLM-normalized to the same water 

chemistry to allow comparison to the FCV. All of the normalized values were greater than the 

FCV except a static, unmeasured 4-day IC50 for reduced growth of 0.8320 μg/L dissolved copper 

for the golden/brown flagellate (Isochrysis sp.) (Garr 2012). Saifullah (1978) reported a BLM 

normalized growth LOEC of 2.257 μg/L copper for two dinoflagellates (Prorocentrum micans 

and Scrippsiella faeronense) at 8 and 5 days, respectively. The red alga, Champia parvula, had 

BLM-normalized effect concentrations that ranged from 2.078 to 6.159 μg/L based on reduced 

growth and reproduction (Steele and Thursby 1983). Giant kelp, Macrocystis pyrifera, exposed 

to measured copper for 19-20 days using renewal procedures exhibited reduced sporophyte 

production at a BLM-normalized concentration of 4.552 μg/L copper (Anderson et al. 1990). The 

most sensitive effect concentration of 0.8320 μg/L copper reported by Garr (2012) was based on 

nominal concentrations and, as recommended by the Guidelines (Stephan et al. 1985), cannot be 

used to calculate a FPV. Since the majority of the other values show sensitivity to copper that is 

similar to animals, a chronic criterion that protects estuarine/marine animals should also protect 

plants.

4.5 Protection of Endangered Species

The estuarine/marine dataset for copper is extensive for the evaluation of acute toxicity,

but few data are available for the evaluation of chronic toxicity. Only limited data are available 

for species that are Federally-listed as threatened or endangered by the NOAA National Marine 

Fisheries Service. Summaries are provided here of data that are available for listed species and 

demonstrate that, based on the best and most current available data, the draft copper criteria in 

this 2016 update are protective of threatened or endangered species. 
69

4.5.1 Acute Toxicity Data for Listed Species

There are only three endangered and/or threatened estuarine/marine species that have 

acceptable acute toxicity data. The black abalone, Haliotis cracherodii, was tested as an adult in 

an acute static-renewal exposure with a BLM-normalized value of 21.24 μg/L copper (Martin et 

al. 1977). The genus Haliotis was the fourth most sensitive genus with the embryo nonendangered abalone species H. rufescens with a BLM-normalized value of 3.944 μg/L copper.

The endangered/threatened Coho salmon smolt (Oncorhynchus kisutch) was the 43rd most 

sensitive genera tested and had a BLM-normalized value of 445.6 μg/L copper. The Leon 

Springs pupfish, Cyprinodon bovinus, had a BLM-normalized SMAV of 778.0 μg/L copper, 

with the genus ranking 44th.

4.5.2 Chronic Toxicity Data for Listed Species

There is no threatened and/or endangered estuarine/marine species with acceptable or 

other chronic toxicity data for copper.

4.6 Comparison of Draft 2003 and 2016 Criteria Values

New acute data for estuarine/marine species have been added to the 2016 update. A total 

of 78 genera are used to derive the estuarine/marine CMC of 2.0 μg/L in the 2016 update (when 

selected water chemistry values were used for BLM normalization) in comparison to the 44 

genera used for the 2003 draft criteria, which resulted in a CMC of 3.1 μg/L (Table 9). The draft 

2003 acute criterion is more stringent than the current recommended 1995 criterion of 4.8 μg/L, 

because of additional data for sensitive organisms (U.S. EPA 1995a, 2003). The 2016 update 

uses the BLM to incorporate the interaction and effect of water physical and chemical parameters

(pH, temperature, salinity and DOC) that affect the bioavailability of copper to aquatic 

organisms. Thus, the numeric water quality criteria values derived from the BLM are dependent 

upon site-specific water quality parameters. The updated BLM-based WQC will in some cases 

be more stringent and in other cases less stringent than the previous criteria (which are not 

adjusted based on water chemistry condition). As there is not a single WQC value to use for 

comparison purposes, the values presented in Table 9 are illustrative only at the selected water 

chemistry values used for BLM-normalization (Table 7).

The four most sensitive genera with available data were used to calculate the CMC in the 

2003 draft document (because n<59 GMAVs), while the second to fifth more sensitive genera 
70

are used in the 2016 update (because n≥59 GMAVs). The CMC reported in U.S. EPA 1995a, 

2003 (draft), and this 2016 (draft) document were lowered to protect commercially important 

aquatic species, Mytilus edulis, Mytilus sp. and H. rufescens, respectively. The approximately 35

percent decrease in the 2016 CMC relative to the 2003 draft CMC is primarily due to the use of 

the BLM model and the default selected water quality parameters, and the additional genera used 

to calculate the new CMC including the following: amphipods (Allorchestes, Echinogammarus,

Gammarus and Orchomonella), barnacle Balanus, mussel Perna, crabs (Callinectes and 

Emerita), horseshoe crab Limulus, bristle star Ophionereis, copepods (Nitokra and Tisbe), 

decapod Palaemon, gastropods (Crepidula, Planaxis and Turbo), shrimps (Farfantepenaeus, 

Metapenaeus, Litopenaeus, Palaemonetes and Penaeus), hard clam Mercenaria, isopod 

Sphaeroma, sea urchins (Arbacia and Diadema), polychaetes (Eurythoe and Hydroides), rotifer 

Brachionus, sand dollar Dendraster, sea anemone Aiptasia, Gulf toadfish Opsanus, mud-skipper 

Boleophthalmus, fat snook Centropomus and thornfish Terapon.

One new estuarine/marine species with acceptable chronic data, the rotifer, Brachionus 

plicatilis, was included in the 2016 update. The addition of this species, along with sheepshead 

minnow data, which was included in the 2003 draft document, results in a total of two species 

with chronic values and ACRs. (Note: the chronic value used in the 1995 ALC from Lussier et 

al. 1985 for the mysid, Americamysis bahia, is no longer considered valid because of poor 

control survival). The 2016 CCC of 1.3 μg/L copper was derived from division of the FAV of 

3.944 μg/L by the FACR of 3.022, which is less than the 1995 CCC of 3.1 μg/L (FAV of 9.625

μg/L divided by an FACR of 3.127), and the 2003 draft CCC of 1.9 μg/L (FAV of 6.188 μg/L

divided by an FACR of 3.23) at the selected water chemistry conditions. As noted for the acute 

criterion, the lower CCC presented in the 2016 update relative to the previous criteria reflects use 

of the BLM that incorporates water physical and chemistry interactions that affect the 

bioavailability of copper to aquatic organisms.
71

Table 9. Comparison of the Four Most Sensitive Taxa Used to Calculate the 

Estuarine/Marine FAV and CMC in the 2003 Draft Copper Document and 2016 Update.

2003 Draft Copper Estuarine/Marine FAV and CMC

2016 Copper Update Estuarine/Marine FAV and 

CMC (at selected chemistry conditions)

Species

SMAV

(μg/L)

GMAV

[Rank]

(μg/L) Species

SMAV

(μg/L)

GMAV

[Rank]

(μg/L)

Mysid,

Holmesimysis costata 9.572 9.572[5]

Sea urchin,

Strongylocentrotus purpuratus 12.81 12.81[4]

Black abalone,

Haliotis cracherodii 21.24 9.153

Summer flounder, [4]

Paralichthys dentatus 12.66 12.66[3]

Red abalone,

Haliotis rufescens 3.944

Eastern oyster,

Crassostrea virginica 14.49 12.60

[2]

Summer flounder,

Paralichthys dentatus 8.848 8.848[3]

Pacific oyster,

Crassostrea gigas 10.96 Copepod,Tigriopus californicus 7.847 7.847[2]

Blue mussel,

Mytilus edulis 21.50 11.53

[1]

Blue mussel,

Mytilus edulis 4.238 5.577*

Mussel, [1]

Mytilus sp. 6.19 Mediterranean mussel,Mytilus galloprovincialis 7.338

Number of GMAVs 44 Number of GMAVs 78

FAV (calculated) 12.34 FAV (calculated) 9.138

CMC (calculated) 6.170 CMC (calculated) 4.6

Lowered FAVa 6.188 Lowered FAVb 3.944

Recommended CMC 3.1 Recommended CMC 2.0

c

* Not used to calculate CMC since number of GMAVs ≥59.

a Dissolved copper final acute value (FAV) was lowered from 12.34 to 6.188 to protect Mytilus sp.

b Dissolved copper final acute value (FAV) was lowered from 9.138 to 3.944 to protect Haliotis rufescens.

c When Temperature=22°C, pH=8, DOC=1.0 mg/L, and Salinity=32 ppt.
72

5 REFERENCES

Aanand, S., C.S. Purushothaman, A.K. Pal and K.V. Rajendran. 2010. Toxicological studies on 

the effect of copper, lead and zinc on selected enzymes in the adductor muscle and intestinal 

diverticula of the green mussel Perna viridis. Indian J. Mar. Sci. 39(2): 299-302.

Absil, M.P.C., J.J. Kroon and H.T. Wolterbeek. 1994. Availability of copper from phytoplankton 

and water for the bivalve Macoma baltica. II Uptake and elimination from 64Cu-labelled diatoms 

and water. Mar. Bio. 118: 129-135.

Abbasi, A.R. and S.E. Sheckley. 1995. Effects of copper on newly hatched larvae of herring, 

Clupea harengus L. Pakistan J. Zool. 27(4): 285-290.

Abbe, G.R. and J.G. Sanders. 1986. Condenser replacement in a coastal power plant: Copper 

uptake and incorporation in the American oyster, Crassostrea virginica. Mar. Environ. Res. 

19(2): 93-113.

Abbe, G.R., G.F. Riedel and J.G. Sanders. 2000. Factors that influence the accumulation of 

copper and cadmium by transplanted eastern oysters (Crassostrea virginica) in the Patuxent 

River, Maryland. Mar. Environ. Res. 49: 377-396.

Absil, M.C.P., L.J.A. Gerringa and B.T. Wolterbeek. 1993. The relation between salinity and 

copper complexing capacity of natural estuarine waters and the uptake of dissolved 64Cu by 

Macoma balthica. Chem. Spec. Bioavail. 5(4): 119-128.

Absil, M.C.P., M. Berntssen and L.J.A. Gerringa. 1996. The influence of sediment, food and 

organic ligands on the uptake of copper by sediment-dwelling bivalves. Aquat. Tox. 34(1): 13-

29.

Adema, D.M.M., S.I. Deswaaf-Mooy and P. Bais. 1972. Laboratory investigations concerning 

the influence of copper on mussels (Mytilus edulis) (Laboratoriumonderzoek over de invloed van 

koper op mosselen (Mytilus edulis). TNO Nieuws 27(9): 482-487.

Adema-Hannes, R. and J. Shenker. 2008. Acute lethal and teratogenic effects of tributyltin 

chloride and copper chloride on mahi mahi (Coryphaena hippurus) eggs and larvae. Environ. 

Toxicol. Chem. 27(10): 2131-2135.

Adeyemi, J.A. and P.L. Klerks. 2012. Salinity acclimation modulates copper toxicity in the 

sheepshead minnow, Cyprinodon variegatus. Environ. Toxicol. Chem. 31(7): 1573-1578.

Adeyemi, J.A., L.E. Deaton, T.C. Pesacreta and P.L. Klerks. 2012. Effects of copper on 

osmoregulation in sheepshead minnow, Cyprinodon variegatus acclimated to different salinities. 

Aquat. Toxicol. 109: 111-117.

Agell, G., M.J. Uriz, E. Cebrain and R. Marti. 2001. Does stress protein induction by copper 

modify natural toxicity in sponges? Environ. Toxicol. Chem. 20(11): 2588-2593.
73

Ahmad, I., M. Oliveira, M. Pacheco and M.A. Santos. 2005. Anguilla anguilla L. oxidative stress 

biomarkers responses to copper exposure with or without beta-naphthoflavone pre-exposure. 

Chemo. 61(2): 267-275.

Ahmad, I., V.L. Maria, M. Oliveira, M. Pacheco and M.A. Santos. 2008. Modulatory role of 

copper on beta-naphthoflavone-induced DNA damage in European eel (Anguilla anguilla L.). 

Ecotoxicol. Environ. Saf. 71(3): 806-812.

Ahmed, M.R., M. Elumalal, S.E. Balasubramanian and M.P. Balasubramanian. 1997. Individual 

and combined effect of copper and chromium on oxygen consumption and phosphatases of a 

marine edible crab, Scylla serrata. Biomed. Lett. 55(219-220): 147-152. 

Ahsanullah, M. and A.R. Williams. 1991. Sublethal effects and bioaccumulation of cadmium, 

chromium, copper, and zinc in the marine amphipod Allorchestes compressa. Mar. Biol. 108: 59-

65.

Ahsanullah, M., M.C. Mobley and P. Rankin. 1988. Individual and combined effects of zinc, 

cadmium and copper on the marine amphipod Allorchestes compressa. Aust. J. Mar. Freshwater 

Res. 39(1): 33-37.

Aitkenhead-Peterson, J.A., W.H. McDowell and J.C. Neff. 2003. Sources, production and 

regulation of allochthonous dissolved organic matter inputs to surface waters. In: Findlay, 

S.E.G., Sinsabaugh, R.L. (Eds.), Aquatic Ecosystems, Interactivity of Dissolved Organic Matter. 

Academic Press/Elsevier, San Diego, CA, pp. 25–70.

Albergoni, V., A. Cassini, O. Coppellotti, N. Favero, P. Irato, E. Piccinni and G. Santovito. 2000. 

Physiological responses to heavy metals and adaptation to increased oxygen partial pressure in 

Antarctic fish and protozoa. Ital. J. Zool. 1: 1-11.

Alekseev, V., A. Makrushin, J.S. Hwang and V. Alekseev. 2010. Does the survivorship of 

activated resting stages in toxic environments provide cues for ballast water treatment? Mar. 

Pollut. Bull. 61(4-6): 254-258.

Allen, H.E. and D.J. Hansen. 1996. The importance of trace metal speciation to water quality 

criteria. Water Environ. Res. 68(1): 42-54.

Alquezar, R. and A. Anastasi. 2013. The use of the cyanobacteria, Cyanobium sp., as a suitable 

organism for toxicity testing by flow cytometry. Bull. Environ. Contam. Toxicol. 90: 684-690.

Al-Subiai, S.N., A.J. Moody, S.A. Mustafa and A.N. Jha. 2011. A multiple biomarker approach 

to investigate the effects of copper on the marine bivalve mollusc, Mytilus edulis. Ecotoxicol. 

Environ. Saf. 74(7): 1913-1920.

Alvarado, N.E., A. Buxens, L.I. Mazon, I. Marigomez and M. Soto. 2005. Cellular biomarkers of 

exposure and biological effect in hepatocytes of turbot (Scophthalmus maximus) exposed to 

cadmium, copper, zinc and after depuration. Aquat. Toxicol. 74: 110-125.
74

Alvarado, N.E., I. Quesada, K. Hylland, I. Marigomez, M. Soto. 2006. Quantitative changes in 

metallothionein expression in target cell-types in the gills of turbot (Scophthalmus maximus) 

exposed to cadmium, copper, zinc and after a depuration treatment. Aquat. Toxicol. 77: 64-77.

Amaroli, A., S. Ferrando, M.C. Gagliani, L. Gallus and M.A. Masini. 2013. Identification of 

aquaporins in eggs and early embryogenesis of the sea urchin Paracentrotus lividus. Acta 

Histochem. 115(3): 257-263.

Amiard, J.C., C. Amiard-Triquet and C. Metayer. 1985. Experimental study of bioaccumulation, 

toxicity and regulation of some trace metals in various estuarine and coastal organisms. Symp. 

Biol. Hung. 29: 313-325.

Amiard-Triquet, C., B. Berthet, C. Metayer and J.C. Amiard. 1986. Contribution to the 

ecotoxicological study of cadmium, copper, and zinc in the mussel Mytilus edulis. Mar. Biol. 

92(1): 7-13.

Amiard-Triquet, C., R. Martoja and C. Marcaillou. 1992. Alternative methodologies for 

predicting metal transfer in marine food webs including filter-feeders. Water Sci. Tech. 25(11): 

197-204.

Amorim, M.J.B. and J.J. Scott-Fordsmand. 2012. Toxicity of copper nanoparticles and CuCl2 salt 

to Enchytraeus albidus worms: Survival, reproduction and avoidance responses. Environ. Pollut. 

164(0): 164-168.

Andersen, H.B., R.S. Caldwell, J. Toll, T. Do and L. Saban. 2010. Sensitivity of lamprey 

ammocoetes to six chemicals. Arch. Environ. Contam. Toxicol. 59(4): 622-631.

Anderson, B.S., J.W. Hunt, S.L. Turpen, A.R. Coulon and M. Martin. 1990. Copper toxicity to 

microscopic stages of giant kelp Macrocystis pyrifera: Interpopulation comparisons and temporal 

variability. Mar. Ecol. Prog. Ser. 68(1-2): 147-156.

Anderson, B.S., D.P. Middaugh, J.W. Hunt and S.L. Turpen. 1991. Copper toxicity to sperm, 

embryos and larvae of topsmelt Atherinops affinis, with notes on induced spawning. Mar. 

Environ. Res. 21: 17-35.

Anderson, B.S., J.W. Hunt, H.R. McNulty, S.L. Turpen and M. Martin. 1994. Off-season 

spawning and factors influencing toxicity test development with topsmelt Atherinops affinis. 

Environ. Toxicol. Chem. 13(3): 479-485.

Anderson, D.M. and F.M.M. Morel. 1978. Copper sensitivity of Gonyaulax tamarensis. Limnol. 

Oceanog. 23(2): 283-295.

Anderson, S.L. and T.J. Norberg-King. 1991. Precision of short-term chronic toxicity tests in the 

real world. Environ. Toxicol. Chem. 10: 143-145.
75

Andrew, R.W. 1976. Toxicity relationships to copper forms in natural waters. In: Toxicity to 

Biota of Metal Forms in Natural Water. R.W. Andrew, P.V. Hodosn and D.E. Konasewich (Eds.) 

International Joint Commission, Windsor, Ontario, Canada. p. 127.

Andrew, R.W., K.E. Biesinger and G.E. Glass. 1977. Effects of inorganic complexing on the 

toxicity of copper to Daphnia magna. Water Res. 11(3): 309-315.

Angel, B.M., S.L. Simpson and D.F. Jolley. 2010. Toxicity to Melita plumulosa from 

intermittent and continuous exposures to dissolved copper. Environ. Toxicol. Chem. 29(12): 

2823-2830.

Angel, B.M., S.L. Simpson, A.A. Chariton, J.L. Stauber and D.F. Jolley. 2015. Time-averaged 

copper concentrations from continuous exposures predicts pulsed exposure toxicity to the marine 

diatom, Phaeodactylum tricornutum: Importance of uptake and elimination. Aquat. Toxicol. 164: 

1-9.

Anjos, V.A., F.M.R. da Silva-Junior and M.M. Souza. 2014. Cell damage induced by copper: An 

explant model to study anemone cells. Toxicol. In Vitro 28: 365-372.

Araujo, C.V.M., F.R. Diz, I. Moreno-Garrido, L.M. Lubian and J. Blasco. 2008. Effects of cold 

storage on growth of Cylindrotheca closterium and its sensitivity to copper. Chemospere 72: 

1366-1372.

Arizza, V., G. Di Fazio, M. Celi, N. Parrinello and M. Vazzana. 2009. Cadmium, copper and 

tributyltin effects on fertilization of Paracentrotus lividus (Echinodermata). Ital. J. Anim. Sci. 

8(Suppl. 2): 839-841.

Arnold, W.R. 2005. Effects of dissolved organic carbon on copper toxicity: Implications for 

saltwater copper criteria. Integrat. Environ. Assess. Monit. 1(1): 34-39.

Arnold, W.R. and J.S. Cotsifas. 2008. An assessment of the application factor used to derive the 

saltwater acute ambient water copper criterion. Integ. Environ. Assess. Manag. 4(2): 252-254.

Arnold, W.R., R.C. Santore and J.S. Cotsifas. 2005. Predicting copper toxicity in estuarine and 

marine waters using the biotic ligand model. Mar. Pollut. Bull. 50(12): 1634-1640.

Arnold, W.R., J.S. Cotsifas and K.M. Corneillie. 2006. Validation and update of a model used to 

predict copper toxicity to the marine bivalve Mytilus sp. Environ. Toxicol. 21(1): 65-70.

Arnold, W.R., J.S. Cotsifas, A.R. Winter, J.S. Klinck, D.S. Smith and R.C. Playle. 2007. Effects 

of using synthetic sea salts when measuring and modeling copper toxicity in saltwater toxicity 

tests. Environ. Toxicol. Chem. 26(5): 935-943.
76

Arnold, W.R., J.S. Cotsifas, D.S. Smith, S. Le Page and K.M. Gruenthal. 2008. A comparison of 

the copper sensitivity of two economically important saltwater mussel species and a review of 

previously reported copper toxicity data for mussels: Important implications for determining 

future ambient copper saltwater criteria in the USA. Environ. Toxicol. 24(6): 618-628.

Arnold, W.R., J.S. Cotsifas, R.S. Ogle, S.G.S. DePalma and D.S. Smith. 2010a. A comparison of 

the copper sensitivity of six invertebrate species in ambient salt water of varying dissolved 

organic matter concentrations. Environ. Toxicol. Chem. 29(2): 311-319.

Arnold, W.R., R.L. Diamond and D.S. Smith. 2010b. Acute and chronic toxicity of copper to the 

euryhaline rotifer, Brachionus plicatilis (“L” strain). Arch. Environ. Contam. Toxicol. 60(2): 

250-260.

Arnold, W.R., R.L. Diamond and D.S. Smith. 2010c. The effects of salinity, pH, and dissolved 

organic matter on acute copper toxicity to the rotifer, Brachionus plicatilis “L” strain. Arch. 

Environ. Contam. Toxicol. 59: 225-234.

Arockia Vasanthi, L., P. Revathi, C. Arulvasu and N. Munuswamy. 2012. Biomarkers of metal 

toxicity and histology of Perna viridis from Ennore Estuary, Chennai, South East Coast of India. 

Ecotoxicol. Environ. Saf. 84: 92-98.

Arockia Vasanthi, L., P. Revathi, J. Mini and N. Munuswamy. 2013. Integrated use of 

histological and ultrastructural biomarkers in Mugil cephalus for assessing heavy metal pollution 

in Ennore Estuary, Chennai. Chemosphere 91(8): 1156-1164.

Arthur, J.W. and E.N. Leonard. 1970. Effects of copper on Gammarus pseudolimnaeus, Physa

integra, and Campeloma decisum in soft water. J. Fish. Res. Board Can. 27: 1277-1283.

Arumugam, M. and M.H. Ravindranath. 1987. Copper toxicity in the crab, Scylla serrata, copper 

levels in tissues and regulation after exposure to a copper-rich medium. Bull. Environ. Contam. 

Toxicol. 39: 708-715.

ATSDR (Agency for Toxic Substances and Disease Registry). 1990. Toxicological profile for 

copper. U.S. Public Health Service, Atlanta, Georgia, TP-90-08. 143 pp.

Ayling, G.M. 1974. Uptake of cadmium, zinc, copper, lead and chromium in the Pacific oyster, 

Crassostrea gigas, grown in the Tamar River, Tasmania. Water Res. 8(10): 729-738.

Bach, L., L. Ferguson, V. Feltelius and J. Sondergaard. 2014. Orchomenella pinguis

(Amphipoda) - a possible species for heavy metal biomonitoring of marine sediments. J. Coast. 

Life Med. 2(2): 116-123.

Bailey, H.C., J.L. Miller, M.J. Miller and B.S. Dhaliwal. 1995. Application of toxicity 

identification procedures to the echinoderm fertilization assay to identify toxicity in a municipal 

effluent. Environ. Toxicol. Chem. 14(12): 2181-2186.
77

Baker, J.T.P. 1969. Histological and electron microscopical observations on copper poisoning in 

the winter flounder (Pseudopleuronectes americanus). J. Fish. Res. Board Can. 26: 2785-2793.

Baker, R.T.M., R.D. Handy, S.J. Davies and J.C. Snook. 1998. Chronic dietary exposure to 

copper affects growth, tissue lipid peroxidation, and metal composition of the grey mullet, 

Chelon labrosus. Mar. Environ. Res. 45: 357-365.

Bakhmet, I.N., N.P. Kantserova, L.A. Lysenko and N.N. Nemova. 2012. Effect of copper and 

cadmium ions on heart function and calpain activity in blue mussel Mytilus edulis. J. Environ. 

Sci. Health Part A 47: 1528-1535.

Bao, V.W.W., K.M.Y. Leung, K.W.H. Kwok, A.Q. Zhang and G.C.S. Lui. 2008. Synergistic 

toxic effects of zinc pyrithione and copper to three marine species: Implications on setting 

appropriate water quality criteria. Mar. Pollut. Bull. 57(6-12): 616-623.

Bao, V.W., K.M. Leung, J.W. Qiu, M.H. Lam and V.W. Bao. 2011. Acute toxicities of five 

commonly used antifouling booster biocides to selected subtropical and cosmopolitan marine 

species. Mar. Pollut. Bull. 62(5): 1147-1151.

Bao, V.W.W., K.M.Y. Leung, G.C.S. Lui and M.H.W. Lam. 2013. Acute and chronic toxicities 

of Irgarol alone and in combination with copper to the marine copepod Tigriopus japonicas. 

Chemosphere 90: 1140-1148.

Bao, W.Y., O.O. Lee, H.C. Chung, M. Li and P.Y. Qian. 2010. Copper affects biofilm 

inductiveness to larval settlement of the serpulid polychaete Hydroides elegans (Haswell). 

Biofoul. 26(1): 119-128.

Baraj, B., F. Niencheski, G. Fillmann and C. De Martinez Gaspar Martins. 2011. Assessing the 

effects of Cu, Cd, and exposure period on metallothionein production in gills of the Brazilian 

brown mussel Perna perna by using factorial design. Environ. Monit. Assess. 179(1-4): 155-62.

Barka, S. 2007. Insoluble detoxification of trace metals in a marine copepod Tigriopus 

brevicornis (Muller) exposed to copper, zinc, nickel, cadmium, silver and mercury. Ecotoxicol. 

16(7): 491-502.

Barka, S., J.F. Pavillon and C. Amiard-Triquet. 2010. Metal distributions in Tigriopus 

brevicornis (Crustacea, Copepoda) exposed to copper, zinc, nickel, cadmium, silver, and 

mercury, and implication for subsequent transfer in the food web. Environ. Toxicol. 25(4): 350-

360.

Barrera-Garcia, A., T. O'hara, F. Galvan-Magana, L.C. Mendez-Rodriguez, J.M. Castellini and 

T. Zenteno-Savin. 2013. Trace elements and oxidative stress indicators in the liver and kidney of 

the blue shark (Prionace glauca). Comp. Biochem. Physiol. Part A 165(4): 483-490.

Bat, L., D. Raffaelli and I.L. Marr. 1998. The accumulation of copper, zinc and cadmium by the 

amphipod Corophium volutator (Pallas). J. Exper. Mar. Biol. Ecol. 223: 167-184.
78

Bat, L., A. Gundogdu, M. Sezgin, M. Culha, G. Gonlugur and M. Akbulut. 1999a. Acute toxicity 

of zinc, copper and lead to three species of marine organisms from the Sinop Peninsula, Black 

Sea. Turk. J. Biol. 23: 537-544.

Bat, L., M. Sezgin, A. Gundogdu and M. Culha. 1999b. Toxicity of zinc, copper and lead to 

Idotea baltica (Crustacea, Isopoda). Turk. J. Biol. (Turk. Biol. Derg.) 23(4): 465-472.

Bat, L., F. Ustun, O.G. Baki and F. Sahin. 2013. Effects of some heavy metals on the sizes of the 

Mediterranean mussel Mytilus galloprovincialis Lamarck, 1819. Fres. Environ. Bull. 22(7): 

1933-1938.

Bauer, J.E. and T.S. Bianchi. 2011. Dissolved organic carbon cycling and transformation. In: E. 

Wolanski and D.S. McLusky (Eds.), Treatise on Estuarine and Coastal Science, Waltham,

Academic Press. Vol 5, pp. 7–67.

Bautista-Covarrubias, J.C., M.G. Frias-Espericueta, G.J. Velarde-Montes, D. Voltolina, L.M. 

Garcia-de la Parra and M.F. Soto-Jimenez. 2015. Relationships between copper and stress 

indicators in the Pacific white shrimp, Litopenaeus vannamei. Mar. Fresh. Behav. Physiol. 48(3): 

193-203.

Bay, S.M., P.S. Oshida and K.D. Jenkins. 1983. A simple new bioassay based on echinochrome 

synthesis by larval sea urchins. Mar. Environ. Res. 8: 29-39.

Bay, S., R. Burgess and D. Nacci. 1993. Status and applications of echinoid (Phylum

Echniodermata) toxicity test methods. In: Environmental Toxicology and Risk Assessment, 

ASTM STP 1179. W.G. Landis, J.S. Hughes and M.A. Lewis (Eds.). Philadelphia: American 

Society for Testing and Materials, pp. 281-302. 

Bay, S.M., D. Lapota, J. Anderson, J. Armstrong, T. Mikel, A.W. Jirik and A. Asato. 2000. 

Southern California Bight 1998 regional monitoring program: IV. Sediment toxicity. Southern 

California Coastal Water Research Project. Westminster, CA.

Becerra-Huencho, R.M. 1984. The effect of organotin and copper sulfate on the late 

development and presettlement behavior of the hard clam Mercenaria mercenaria. M.S. Thesis, 

Univ. of Maryland, College Park, MD, 85 pp.

Bechmann, R.K. 1994. Use of life tables and LC50 tests to evaluate chronic and acute toxicity 

effects of copper on the marine copepod Tisbe furcata (Baird). Environ. Toxicol. Chem. 13(9): 

1509-1517.

Belanger, S.E., J.L. Farris and D.S. Cherry. 1989. Effects of diet, water hardness, and population 

source on acute and chronic copper toxicity to Ceriodaphnia dubia. Arch. Environ. Contam. 

Toxicol. 18(4): 601-611.
79

Bengtsson, B.E. 1978. Use of a harpacticoid copepod in toxicity tests. Mar. Pollut. Bull. 9: 238-

241.

Benoit, D.A. 1975. Chronic effects of copper on survival, growth, and reproduction of the 

bluegill (Lepomis macrochirus). Trans. Am. Fish. Soc. 104: 353-358.

Bergman, H.L. and E.J. Doward-King (Eds.) 1997. Reassessment of metals criteria for aquatic 

life protection: Priorities for research and implementation. SETAC Press, Pensacola, FL. 114 pp.

Berry, K.L., J. Seemann, O.S. Dellwig, W.C. Ulrich and R.R. Leinfelder. 2013. Sources and 

spatial distribution of heavy metals in Scleractinian coral tissues and sediments from the Bocas 

Del Toro Archipelago, Panama. Environ. Monit. Assess. 185(11): 9089-9099.

Bertilsson, S. and J.B. Jones. 2003. Supply of dissolved organic matter to aquatic systems:

Autochthonous sources. In: S.E.G. Findlay and R.L. Sinsabaugh (Eds.), Aquatic Ecosystems, 

Interactivity of Dissolved Organic Matter. Academic Press/Elsevier, San Diego, CA, pp. 3-24.

Besser, J.M., J.F. Dwyer, C.G. Ingersoll and N. Wang. 2001. Early life-stage toxicity of copper 

to endangered and surrogate fish species. EPA Project No. DW14937809-01-0. Office of 

Research and Development, Washington, DC.

Betzer, S.B. and P.P. Yevich. 1975. Copper toxicity in Busycon canaliculatun L. Biol. Bull. 148:

16-25.

Bhat, U.G. and K. Vamsee. 1993. Toxicity of heavy metals copper, cadmium and mercury to the 

gammarid amphipod Parhalella natalensis (Stebbing). Sci. Total Environ. 134: 887-897.

Bianchi, T.S., J.E. Bauer, E.R.M. Druffel and C. Lambert. 1998. Pyrophaeophorbide – as a tracer 

of suspended particulate organic matter from the Eastern North Pacific continental margin. Deep 

Sea Res. I 45: 715–773.

Bielmyer, G.K., D. Gatlin, J.J. Isely, J. Tomasso and S.J. Klaine. 2005a. Responses of hybrid 

striped bass to waterborne and dietary copper in freshwater and saltwater. Comp. Biochem. 

Physiol. Part C 140(1): 131-137.

Bielmyer, G.K., K.V. Brix, T.R. Capo and M. Grosell. 2005b. The effects of metals on embryolarval and adult life stages of the sea urchin, Diadema antillarum. Aquat. Toxicol. 74(3): 254-

263.

Bielmyer, G.K., J. Tomasso and S.J. Klaine. 2006a. Physiological responses of hybrid striped 

bass to aqueous copper in freshwater and saltwater. Arch. Environ. Contam. Toxicol. 50(3): 531-

538.

Bielmyer, G.K., M. Grosell and K.V. Brix. 2006b. Toxicity of silver, zinc, copper, and nickel to 

the copepod Acartia tonsa exposed via a phytoplankton diet. Environ. Sci. Technol. 40(6): 2063-

2068.
80

Bielmyer, G.K., M. Grosell, R. Bhagooli, A.C. Baker, C. Langdon, P. Gillette and T.R. Capo. 

2010. Differential effects of copper on three species of Scleractinian corals and their algal 

symbionts (Symbiodinium spp.). Aquat. Toxicol. 97(2): 125-133.

Bielmyer, G.K., T.A. Jarvis, B.T. Harper, B. Butler, L. Rice, S. Ryan and P. McLoughlin. 2012. 

Metal accumulation from dietary exposure in the sea urchin, Strongylocentrotus droebachiensis. 

Arch. Environ. Contam. Toxicol. 63(1): 86-94.

Birch, G.F. and T.D. Hogg. 2011. Sediment quality guidelines for copper and zinc for filterfeeding estuarine oysters? Environ. Pollut. 159(1): 108-115.

Birdsong, C.L. and J.W. Avault. 1971. Toxicity of certain chemicals to juvenile pompano. Prog. 

Fish Culturist. 33: 76-80.

Bisbal, G. 1987. Does copper affect the mating behavior of Gammarus annulatus Smith, 1873 

(Amphipoda: Gammaridae)? Biol. Bull. 173(2): 429 (ABS).

Biswas, T., P.K. Bandyopadhyay and S.N. Chatterjee. 2013. Accumulation of cadmium, copper, 

lead, zinc and iron in the edible oyster, Saccostrea cucullata in coastal areas of west Bengal. 

African J. Biotechnol. 12(24): 3872-3877.

Blanchard, J. and M. Grosell. 2005. Effects of salinity on copper accumulation in the common 

killifish (Fundulus heteroclitus). Environ. Toxicol. Chem. 24(6): 1403-1413.

Blanchard, J. and M. Grosell. 2006. Copper toxicity across salinities from freshwater to seawater 

in the euryhaline fish Fundulus heteroclitus: Is copper an ionoregulatory toxicant in high 

salinities? Aquat. Toxicol. 80(2): 131-139.

Blanchard, J., K. Brix and M. Grosell. 2009. Subcellular fractionation of Cu exposed oysters, 

Crassostrea virginica, and Cu accumulation from a biologically incorporated Cu rich oyster diet 

in Fundulus heteroclitus in fresh and sea water. Comp. Biochem. Physiol. C 149(4): 531-537.

Blaylock, B.G., M.L. Frank and J.F. McCarthy. 1985. Comparative toxicity of copper and 

acridine to fish, Daphnia and algae. Environ. Toxicol. Chem. 4(1): 63-71.

Blaxter, J.H.S. 1977. The effect of copper on the eggs and larvae of plaice and herring. J. Mar. 

Biol. Assoc. U.K. 57: 849-858.

Bodammer, J.E. 1985. Corneal damage in larvae of striped bass Morone saxatilis exposed to 

copper. Trans. Am. Fish. Soc. 114(4): 577-583.

Bodammer, J.E. 1987. A preliminary study on the corneas of American sand lance larvae 

exposed to copper. In: W.A. Vernberg, A. Calabrese, F.P. Thurberg and F.J. Vernberg (Eds.), 

Pollution of Estuarine Organisms, University of SC Press, Columbia, SC. pp. 439-448.
81

Bolognesi, C., E. Landini, P. Roggieri, R. Fabbri and A. Viarengo. 1999. Genotoxicity 

biomarkers in the assessment of heavy metal effects in mussels: Experimental studies. Environ. 

Mol. Mutagen. 33(4): 287-292.

Borgmann, U. 1983. Metal speciation and toxicity of free metal ions to aquatic biota. In: J.O. 

Nriagu (Ed.). Aquatic Toxicology, Vol 13. John Wiley and Sons, New York, NY. p. 47-72.

Borgmann, U. and K.M. Ralph. 1983. Complexation and toxicity of copper and the free metal 

bioassay technique. Water Res. 17(11): 1697-1703.

Borkow, G. and J. Gabbay. 2005. Copper as a biocidal tool. Curr. Med. Chem. 12: 2163-2175.

Botton, M.L. and T. Itow. 2009. The effects of water quality on horseshoe crab embryos and 

larvae. In: J.T. Tanacredi, M.L. Botton and D.R. Smith (Eds.), Intl. Symp. on the Science and 

Conservation of Horseshoe Crabs, Jun.11-17, 2007, Springer, NY. pp. 439-454. 

Botton, M.L., K. Johnson and L. Helleby. 1998. Effects of copper and zinc on embryos and 

larvae of the horseshoe crab, Limulus polyphemus. Arch. Environ. Contam. Toxicol. 35(1): 25-

32.

Boudjema, K., S. Kourdali, N. Bounakous, A. Meknachi and A. Badis. 2014. Catalase activity in 

brown mussels (Perna perna) under acute cadmium, lead, and copper exposure and depuration 

tests. J. Mar. Biol. 830657.

Bowen, H.J.M. 1985. Part D: The Natural environment and biogeochemical cycles. In: D. 

Hutzinger (Ed.), The Handbook of Environmental Chemistry, Vol. 1, Springer-Verlag, NY. p. 1-

26.

Bowmer, T., R.G.V. Boelens, B.F. Keegan and J. O'Neill. 1986. The use of marine benthic ‘key’

species in ecotoxicological testing: Amphiura filiformis (O.F. Muller) (Echinodermata: 

Ophiuroidea). Aquat. Toxicol. 8(2): 93-109.

Boyle, R.T., L.F. Oliveria, A. Bianchini and M.M. Souza. 2013. The effects of copper on 

Na+/K+-ATPase and aquaporin expression in two euryhaline invertebrates. Bull. Environ. 

Contam. Toxicol. 90: 387-390.

Brandt, O.M., R.W. Fujimura and B.J. Finlayson. 1993. Use of Neomysis mercedis (Crustacea: 

Mysidacea) for estuarine toxicity tests. Trans. Am. Fish. Soc. 122(2): 279-288.

Bright, G.R. 1995. Variability of the "water effect ratio" for copper toxicity - a case study. Proc. 

Toxic Subst. Water Environ. May 23-30, Water Environ. Fed., Alexandria, VA, 5.23-5.30.

Brooks, A., R.M. White and D.C. Paton. 1995. Effects of heavy metals on the survival of 

Diacypris compacta (Herbst) (Ostracoda) from the Coorong, South Australia. Int. J. Salt Lake 

Res. 4(2): 133-163.
82

Brooks, S.J., T. Bolam, L. Tolhurst, J. Bassett, J. La Roche, M. Waldock, J. Barry and K.V. 

Thomas. 2007. Effects of dissolved organic carbon on the toxicity of copper to the developing 

embryos of the Pacific oyster (Crassostrea gigas). Environ. Toxicol. Chem. 26(8): 1756-1763.

Brooks, S.J., E. Farmen, L.S. Heier, E. Blanco-Rayon and U. Izagirre. 2015. Differences in 

copper bioaccumulation and biological responses in three Mytilus species. Aquat. Toxicol. 160: 

1-12.

Brown, M.T., J.E. Newman and T. Han. 2012. Inter-population comparison of copper resistance 

and accumulation in the red seaweed, Gracilariopsis longissima. Ecotoxicol. 21: 591-600.

Bryan, G.W. 1983. Brown seaweed, Fucus vesiculosus, and the gastropod, Littorina littoralis, as 

indicators of trace-metal availability in estuaries. Sci. Total Environ. 28: 91-104.

Bryan, G.W. and W.J. Langston. 1992. Bioavailability, accumulation and effects of heavy metals 

in sediments with special reference to United Kingdom estuaries: A review. Environ. Pollut. 76: 

89-131.

Buffet, P.E., O.F. Tankoua, J.F. Pan, D. Berhanu, C. Herrenknecht, L. Poirier, C. AmiardTriquet, J.C. Amiard, J.B. Berard, C. Risso, M. Guibbolini, M. Romeo, P. Reip, E. ValsamiJones and C. Mouneyrac. 2011. Behavioural and biochemical responses of two marine 

invertebrates Scrobicularia plana and Hediste diversicolor to copper oxide nanoparticles. 

Chemosphere 84(1): 166-174.

Burlinson, F.C. and A.J Lawrence. 2007a. A comparison of acute and chronic toxicity tests used 

to examine the temporal stability of a gradient in copper tolerance of Hediste diversicolor from 

the Fal Estuary, Cornwall, UK. Mar. Pollut. Bull. 54(1): 66-71.

Burlinson, F.C. and A.J. Lawrence. 2007b. Development and validation of a behavioral assay to 

measure the tolerance of Hediste diversicolor to copper. Environ. Pollut. 145(1): 274-278.

Calabrese, A., J.R. MacInnes, D.A. Nelson and J.E. Miller. 1977. Survival and growth of bivalve 

larvae under heavy-metal stress. Mar. Biol. 41: 179-1984.

Calabrese, A., J.R. MacInnes, D.A. Nelson, R.A. Greig and P.P. Yevich. 1984. Effects of longterm exposure to silver or copper on growth, bioaccumulation and histopathology in the blue 

mussel Mytilus edulis. Mar. Environ. Res. 11(4): 253-274.

Caldeira, K. and M.E. Wickett. 2003. Oceanography: Anthropogenic carbon and ocean pH.

Nature 425: 365.

Caldwell, G.S., C. Lewis, G. Pickavance, R.L. Taylor and M.G. Bentley. 2011. Exposure to 

copper and a cytotoxic polyunsaturated aldehyde induces reproductive failure in the marine 

polychaete Nereis virens (Sars). Aquat. Toxicol. 104(1/2): 126-134.
83

Campana, O., S.L. Simpson, D.A. Spadaro and J. Blasco. 2012. Sub-lethal effects of copper to 

benthic invertebrates explained by sediment properties and dietary exposure. Environ. Sci. 

Technol. 46(12): 6835-6842.

Campbell, P.G.C. 1995. Interactions between trace metals and aquatic organisms: A critique of 

the free-ion activity model. In: Metal Speciation and Bioavailability in Aquatic Systems, A. 

Tessier and D.R. Turner (Eds.), John Wiley and Sons, NY. pp. 45-102.

Canli, M. and R.W. Furness. 1993. Toxicity of heavy metals dissolved in sea water and 

influences of sex and size on metal accumulation and tissue distribution in the Norway lobster 

Nephrops norvegicus. Mar. Environ. Res. 36: 217-236.

Cao, L., W. Huang, J. Liu, Z. Ye, S. Dou and L. Cao. 2010. Toxicity of short-term copper 

exposure to early life stages of Red Sea bream, Pagrus major. Environ. Toxicol. Chem. 29(9): 

2044-2052.

Caramujo, M.J., C.C.C.R. de Carvalho, S.J. Silva and K.R. Carman. 2012. Dietary carotenoids 

regulate astaxanthin content of copepods and modulate their susceptibility to UV light and 

copper toxicity. Mar. Drugs 10: 998-1018.

Cardeilhac, P.T., C.F. Simpson, R.L. Lovelock, S.F. Yosha, H.W. Calderwood and J.C. Gudat. 

1979. Failure of osmoregulation with apparent potassium intoxication in marine teleosts: A 

primary toxic effect of copper. Aquacult. 17(3): 231-239.

Cardin, J.A. 1982. EPA. (Memorandum to John H. Gentile). EPA, Narragansett, RI.

Cardin, J.A. 1985. Results of acute toxicity tests conducted with copper at ERL, Narragansett. 

(Memorandum to David Hansen). EPA, Narragansett, RI.

Carlson, A.R., H. Nelson and D. Hammermeister. 1986. Development and validation of sitespecific water quality criteria for copper. Environ. Toxicol. Chem. 5(11): 997-1012.

Carson, R.T., M. Damon, L.T. Johnson and J.A. Gonzalez. 2009. Conceptual issues in designing 

a policy to phase out metal-based antifouling paints on recreational boats in San Diego Bay. J. 

Environ. Manag. 90(8): 2460-2468. 

Casado-Martinez, C.M., B.D. Smith, S.N. Luoma, P.S. Rainbow and C.M. Casado-Martinez. 

2010. Metal toxicity in a sediment-dwelling polychaete: Threshold body concentrations or 

overwhelming accumulation rates? Environ. Pollut. 158(10): 3071-3076.

Casas, A.M. and E.A. Crecelius. 1994. Relationship between acid volatile sulfide and toxicity of 

zinc, lead and copper in marine sediments. Environ. Toxicol. Chem. 13: 529-536. 

Casas, S., J.L. Gonzalez, B. Andral and D. Cossa. 2008. Relation between metal concentration in 

water and metal content of marine mussels (Mytilus galloprovincialis): Impact of physiology. 

Environ. Toxicol. Chem. 27(7): 1543-1552.
84

Catarino, A.I., H.N. Cabral, K. Peeters, P. Pernet, U. Punjabi and P. Dubois. 2008. Metal 

concentrations, sperm motility, and RNA/DNA ratio in two echinoderm species from a highly 

contaminated fjord (the Sorfjord, Norway). Environ. Toxicol. Chem. 27(7): 1553-1560.

Cauwet, G. 2002. DOM in the coastal zone. In: D.A. Hansell and C.A. Carlson (Eds.),

Biogeochemistry of Marine Dissolved Organic Matter. Academic Press/Elsevier Science, New 

York, NY, pp. 579–602.

CDA (Copper Development Association). 1988. Copper in plant, animal and human nutrition. 

CDA Publication TN35. 106 pp., Available online at: 

http://www.copperinfo.co.uk/health/downloads/tn35-copper-plant-animal-human-nutrition.pdf.

CDA (Copper Development Association). 2003. Diffuse sources of environmental copper in the 

United States. Report submitted to the CDA by Parametrix, Inc. in association with Meridian 

Environmental, Co. and D-Squared A-Consulting. New York, NY. 151 pp.

CDA (Copper Development Association). 2012. Copper Facts (Fact Sheet A9007). Available

online at: http://www.copper.org/publications/pub_list/homepage.html.

Cebrian, E. and M.J. Uriz. 2007a. Contrasting effects of heavy metals and hydrocarbons on 

larval settlement and juvenile survival in sponges. Aquat. Toxicol. 81(2): 137-143.

Cebrian, E. and M.J. Uriz. 2007b. Do heavy metals play an active role in sponge cell behavior in 

the absence of calcium? Consequences in larval settlement. J. Exp. Mar. Biol. Ecol. 346(1/2): 60-

65.

Cebrian, E. and M.J. Uriz. 2007c. Contrasting effects of heavy metals on sponge cell behavior. 

Arch. Environ. Contam. Toxicol. 53(4): 552-558.

Cebrian, E., G. Agell, R. Marti and M.J. Uriz. 2006. Response of the Mediterranean sponge 

Chondrosia reniformis Nardo to copper pollution. Environ. Pollut. 141(3): 452-458.

CH2MHill. 1999a. Bioassay report acute toxicity of copper to summer flounder (Paralichthys 

dentatus). Final Report to U.S. Navy. Norfolk, VA.

CH2MHill. 1999b. Bioassay report acute toxicity of copper to blue mussel (Mytilus edulis). Final 

Report to U.S. Navy. Norfolk, VA.

Chadwick, D.B., I. Rivera-Duarte, P.F. Wang, G. Rosen, R. Santore, P. Paquin and A. Ryan.

2008. Demonstration of an integrated compliance model for predicting copper fate and effects in 

DoD Harbors, Environmental Security Technology Certification Program (ESTCP). Project ER0523, Final Report, November 1, 2008. Available online at: 

http://www.dtic.mil/dtic/tr/fulltext/u2/a499564.pdf.
85

Chaharlang, B.H., A.R. Bakhtiari and V. Yavari. 2012. Assessment of cadmium, copper, lead 

and zinc contamination using oysters (Saccostrea cucullata) as biomonitors on the coast of the 

Persian Gulf, Iran. Bull. Environ. Contam. Toxicol. 88(6): 956-961.

Chairi, H., C. Fernandez-Diaz, J.I. Navas, M. Manchado, L. Rebordinos and J. Blasco. 2010. In 

vivo genotoxicity and stress defenses in three flatfish species exposed to CuSO4. Ecotoxicol. 

Environ. Saf. 73(6): 1279-1285.

Chakoumakos, C., R.C. Russo and R.V. Thurston. 1979. Toxicity of copper to cutthroat trout 

(Salmo clarki) under different conditions of alkalinity, pH, and hardness. Environ. Sci. Technol.

13(2): 213-219.

Chang, E.Y., S.L. Coon, M. Walch and R. Weiner. 1996. Effects of hyphomonas PM-1 biofilms 

on the toxicity of copper and zinc to Crassostrea gigas and Crassostrea virginica larval set. J. 

Shellfish Res. 15(3): 589-595.

Chang, Y.Y.E. 1995. Impact of microbial biofilms on the toxicity of copper and zinc to oyster 

larval development. Ph.D. Thesis, Univ. of Maryland, College Park, MD. 218 pp.

Chapman, G.A. 1975. Toxicity of copper, cadmium, and zinc to Pacific Northwest salmonids. 

Interim Report, Task 002 ROAP 10CAR, U.S.EPA, Corvallis, OR, 27 p. (Letter to C.E. Stephan, 

U.S. EPA, Duluth, MN: 5 p.) (1982) (Publ in Part as 2123, 2060, 2027) (Author Communication 

Used).

Chapman, G.A. 1982. U.S. EPA, Corvallis, OR (Letter to Charles E. Stephan. U.S. EPA, Duluth, 

MN. December 6).

Chapman, G.A. and J.K. McCrady. 1977. Copper toxicity: A question of form. In: Recent 

Advances in Fish Toxicology. Tubb, R.A. (Ed.). EPA-600/3-77-085. National Technical 

Information Service, Springfield, VA. p. 132.

Chapman, G.A., S. Ota and F. Recht. Manuscript. Effects of water hardness on the toxicity of 

metals to Daphnia magna. U.S. EPA, Corvallis, OR.

Chelomin, V.P., N.N. Belcheva and M.V. Zakhartsev. 1998. Biochemical mechanisms of 

adaptation to cadmium and copper ions in the mussel Mytilus trossulus. Russ. J. Mar. Biol. (Biol. 

Morya) 24(5): 330-336.

Chemicool. 2012. Copper. Chemicool Periodic Table. Chemicool.com. 16 Oct. 2012. Accessed:

11/27/2012. Available at: http://www.chemicool.com/elements/copper.html.

Chen, J.C. and C.H. Lin. 2001. Toxicity of copper sulfate for survival, growth, molting and 

feeding of juveniles of the tiger shrimp, Penaeus monodon. Aquacult. 192(1): 55-65.
86

Chen, Q.L., Z. Luo, X. Liu, Y.F. Song, C.X. Liu, J.L. Zheng and Y.H. Zhao. 2013. Effects of 

waterborne chronic copper exposure on hepatic lipid metabolism and metal-element composition

in Synechogobius hasta. Arch. Environ. Contam. Toxicol. 64: 301-315.

Cheng, T.C. 1979. Use of copper as a molluscicide. In: J.O. Nriagu (Ed.). Copper in the 

environment. Part 2: Health effects. John Wiley, NY: 401-432.

Cheng, T.C. 1988a. In vivo effects of heavy metals on cellular defense mechanisms of 

Crassostrea virginica: Phagocytic and endocytotic indices. J. Invert. Pathol. 51(3): 215-220.

Cheng, T.C. 1988b. In vivo effects of heavy metals on cellular defense mechanisms of 

Crassostrea virginica: Total and differential cell counts. J. Invert. Pathol. 51(3): 207-214.

Cheung, S.G. and L.S. Wong. 1998. Physiological responses of the subtidal prosobranch, 

Babylonia lutosa (Gastropoda: Buccinidae), to copper. Sci. Total Environ. 214(1-3): 185-191.

Cheung, S.G., K.K. Tai, C.K. Leung and Y.M. Siu. 2002. Effects of heavy metals on the survival 

and feeding behaviour of the sandy shore scavenging gastropod Nassarius festivus (Powys). Mar. 

Pollut. Bull. 45(1-12): 107-113.

Chevreuil, M., A.M. Carru, A. Chesterikoff, P. Boet, E. Tales and J. Allardi. 1995. 

Contamination of fish from different areas of the river Seine (France) by organic (PCB and 

pesticides) and metallic (Cd, Cr, Cu, Fe, Mn, Pb and Zn) micropollutants. Sci. Total Environ. 

162: 31-42.

Chiu, K.H. and H.K. Mok. 2011. Study on the accumulation of heavy metals in shallow-water 

and deep-sea hagfishes. Arch. Environ. Contam. Toxicol. 60(4): 643-653.

Cho, Y.S., B.N. Choi, K.H. Kim, S.K. Kim, D.S. Kim, I.C. Bang and Y.K. Nam. 2006. 

Differential expression of Cu/Zn superoxide dismutase mRNA during exposures to heavy metals 

in rockbream (Oplegnathus fasciatus). Aquacult. 253(1-4): 667-679.

Choi, J.S., S.E. Kang, J.Y. Cho, H.W. Shin and Y.K. Hong. 2005. A simple screening method for 

anti-attachment compounds using monospores of Porphyra yezoensis Ueda. J. Fish. Sci. 

Technol. 8(2): 51-55.

Chou, C.L., J. F. Uthe, J. D. Castell and J. C. Keanz. 1987. Effect of dietary cadmium on growth, 

survival, and tissue concentrations of cadmium, zinc, copper, and silver in juvenile American 

lobster (Homarus americanus). Can. J. Fish. Aquat. Sci. 44(8): 1443-1450.

Christensen, E.R., J. Scherfig and P.S. Dixon. 1979. Effects of manganese, copper, and lead on 

Selenastrum capricornutum and Chlorella stigmatophora. Water Res. 13: 79-92.

Chu, K.Y. 1976. Effects of environmental factors on the molluscicidal activities of slow-release 

hexabutyldistannoxane and copper sulfate. Bull. W.H.O. 54(4): 417-420.
87

Chung, K.S. 1980. Effects of selected heavy metals on the survival of tropical grass shrimp 

(Palaemon northropi). Bol. Inst. Oceanogr. Univ. Oriente 19(1/2): 53-57.

Chung, I.K. and B.H. Brinkhuis. 1986. Copper effects in early life stages of the kelp, Laminaria 

saccharina. Mar. Pollut. Bull. 17(5): 213-218.

Cirik, Y., Z.M. Bekci, Y. Buyukates, I. Ak and M. Merdivan. 2012. Heavy metals uptake from 

aqueous solution using marine algae (Colpomenia sinuosa): kinetics and isotherms. Chem. Ecol. 

28(5): 469-480.

City of San Jose. 1998. Development of a site-specific water quality criterion for copper in South 

San Francisco Bay. San Jose/Santa Clara Water Pollution Control Plant. San Jose, CA.

Clearwater, S.J., K.J. Thompson and C.W. Hickey. 2014. Acute toxicity of copper, zinc, and 

ammonia to larvae (glochidia) of a native freshwater mussel Echyridella menziesii in New 

Zealand. Arch. Environ. Contam. Toxicol. 66: 213-226.

Clements, W.H. and P.M. Kiffney. 1996. Validation of whole effluent toxicity tests: Integrated 

studies using field assessments, microcosms, and mesocosms, In Grothe, D.L., Dickson, K.L., 

and Reed-Judkins, D.K., eds., Whole effluent toxicity testing: an evaluation of methods and 

prediction of receiving system impacts: Pensacola, Fla., Society of Environmental Toxicology 

and Chemistry (SETAC), p. 229–244.

Clements, W.H. D.M. Carlisle, L.A. Courtney and E.A. Harrahy. 2002, Integrating observational 

and experimental approaches to demonstrate causation in stream biomonitoring studies. Environ. 

Toxicol. Chem. 21(6): 1138–1146.

Clendenning, K.A. and W.J. North. 1959. Effects of wastes on the giant kelp, Macrocystis 

pyrifera. In: Proceedings of the First International Conference on Waste Disposal in the Marine 

Environment. E.A. Pearson (Ed.). Berkeley, CA. p. 82.

Cloern, J.E. 1996. Phytoplankton bloom dynamics in coastal ecosystems: a review with some 

general lessons from sustained investigation of San Francisco Bay, California. Rev. Geophys. 34:

127–168.

Coglianese, M.P. 1982. The effects of salinity on copper and silver toxicity to embryos of the 

Pacific oyster. Arch. Environ. Contam. Toxicol. 11(3): 297-303.

Coglianese, M.P. and M. Martin. 1981. Individual and interactive effects of environmental stress 

on the embryonic development of the Pacific oyster, Crassostrea gigas. I. The toxicity of copper 

and silver. Mar. Environ. Res. 5(1): 13-27.

Company, R., A. Serafim, R.P. Cosson, A. Fiala-Medioni, L. Camus, A. Colaco, R. SerraoSantos and M.J. Bebianno. 2008. Antioxidant biochemical responses to long-term copper 

exposure in Bathymodiolus azoricus from Menez-Gwen hydrothermal vent. Sci. Total Environ. 

389(2/3): 407-417.
88

Connan, S. and D.B. Stengel. 2011. Impacts of ambient salinity and copper on brown algae: 1. 

Interactive effects on photosynthesis, growth, and copper accumulation. Aquat. Toxicol. 

104(1/2): 94-107.

Connor, P.M. 1972. Acute toxicity of heavy metals to some marine larvae. Mar. Pollut. Bull. 

3(12): 190-192.

Conrad, G.W. 1988. Heavy metal effects on cellular shape changes, cleavage, and larval 

development of the marine gastropod mollusk, (Ilyanassa obsoleta Say). Bull. Environ. Contam. 

Toxicol. 41(1): 79-85.

Contreras, L., M.H. Medina, S. Andrade, V. Oppliger and J.A. Correa. 2007. Effects of copper 

on early developmental stages of Lessonia nigrescens Bory (Phaeophyceae). Environ. Pollut. 

145(1): 75-83.

Cooper, C.A., T. Tait, H. Gray, G. Webster, R.C. Santore, J.C. McGeer and D.S. Smith. 2012. 

Influence of salinity and dissolved organic carbon on acute Cu toxicity to the rotifer Brachionus 

plicatilis. Environ. Sci. Technol. Submitted.

Correia, A.D., G. Lima, M.H. Costa and D.R. Livingstone. 2002a. Studies on biomarkers of 

copper exposure and toxicity in the marine amphipod Gammarus locusta (Crustacea): I. 

Induction of metallothionein and lipid peroxidation. Biomarkers 7(5): 422-437.

Correia, A.D., M.H. Costa, K.P. Ryan and J.A. Nott. 2002b. Studies on biomarkers of copper 

exposure and toxicity in the marine amphipod Gammarus locusta (Crustacea): I. Coppercontaining granules within the midgut gland. J. Mar. Biol. Assoc. U.K. 82(5): 827-834.

Cotou, E., M. Henry, G. Rigos and M. Alexis. 2009. Cellular responses of the farmed sea bass 

Dicentrarchus labrax to copper oxide antifoulants. In: 9th Hellenic Symposium on 

Oceanography and Fisheries, Patra, Greece, 13-16 May 2009. Panellinio Symp. Okeanografias 

Alieias, Patra, Greece. pp. 1295-1302.

Cotou, E., M. Henry, C. Zeri, G. Rigos, A. Torreblanca and V.A. Catsiki. 2012. Short-term 

exposure of the European sea bass Dicentrarchus labrax to copper-based antifouling treated nets: 

Copper bioavailability and biomarkers responses. Chemosphere 89(9): 1091-1097.

Coulibaly, S., B.C. Atse, K.M. Koffi, S. Sylla, K.J. Konan and N.J. Kouassi. 2012. Seasonal 

accumulations of some heavy metal in water, sediment and tissues of black-chinned tilapia 

Sarotherodon melanotheron from Bietri Bay in Ebrie Lagoon, Ivory Coast. Bull. Environ. 

Contam. Toxicol. 88(4): 571-576.

Crecelius, E.A., J.T. Hardy, C.I. Gibson, R.L. Schmidt, C.W. Apts, J.M. Gurtisen and S.P. Joyce. 

1982. Copper bioavailability to marine bivalves and shrimp: Relationship to cupric ion activity. 

Mar. Environ. Res. 6: 13-26.
89

Crespo, E., P. Lozano, J. Blasco and I. Moreno-Garrido. 2014. Epiphyte toxicity bioassay for 

ecotoxicological and coastal monitoring. Environ. Monit. Assess.186: 4647-4654.

Cripe, G.M. 1994. Comparative acute toxicities of several pesticides and metals to Mysidopsis 

bahia and postlarval Penaeus duorarum. Environ. Toxicol. Chem. 13(11): 1867-1872.

Curtis, M.W. and C.H. Ward. 1981. Aquatic toxicity of forty industrial chemicals: Testing in 

support of hazardous substance spill prevention regulation. J. Hydrol. 51: 359-367.

Curtis, M.W., T.L. Copel and C.H. Ward. 1979. Acute toxicity of 12 industrial chemicals to 

freshwater and saltwater organisms. Water Res. 13: 137-141.

Curtis, T.M., R. Williamson and M.H. Depledge. 2000. Simultaneous, long-term monitoring of 

valve and cardiac activity in the blue mussel Mytilus edulis exposed to copper. Mar. Biol. 

(Berlin) 136(5): 837-846.

Daka, E.R. and S.J. Hawkins. 2004. Tolerance to heavy metals in Littorina saxatilis from a metal 

contaminated estuary in the Isle of Man. J. Mar. Biol. Assoc. U.K. 84(2): 393-400.

Damiens, G., C. Mouneyrac, F. Quiniou, E. His, M. Gnassia-Barelli and M. Romeo. 2006. Metal 

bioaccumulation and metallothionein concentrations in larvae of Crassostrea gigas. Environ. 

Pollut. 140(3): 492-499.

Dang, F., H. Zhong and W.X. Wang. 2009. Copper uptake kinetics and regulation in a marine 

fish after waterborne copper acclimation. Aquat. Toxicol. 94: 238-244.

Dang, F., W.X. Wang and P.S. Rainbow. 2012. Unifying prolonged copper exposure, 

accumulation, and toxicity from food and water in a marine fish. Environ. Sci. Technol. 46: 

3465-3471.

D'Asaro, C.N. 1985. Effects assessment of selected chemicals on estuarine and marine 

organisms. EPA-600/X-85/056, EPA, Gulf Breeze, FL. 77 pp.

Davies, I.M. and J.D. Paul. 1986. Accumulation of copper and nickel from anti-fouling 

compounds during cultivation of scallops (Pecten maximus L.) and Pacific oysters (Crassostrea 

gigas Thun.). Aquacult. 55(2): 93-102.

Davis, A. and D. Ashenberg. 1989. The aqueous geochemistry of the Berkeley Pit, Butte, 

Montana, U.S.A. Appl. Geochem. 4: 23-36.

De Boeck, G., J. Hattink, N.M. Franklin, C.P. Bucking, S. Wood, P.J. Walsh and C.M. Wood. 

2007. Copper toxicity in the spiny dogfish (Squalus acanthias): Urea loss contributes to the 

osmoregulatory disturbance. Aquat. Toxicol. 84(2): 133-141.
90

De Boeck, G., M. Eyckmans, I. Lardon, R. Bobbaers, A.K. Sinha and R. Blust. 2010. Metal 

accumulation and metallothionein induction in the spotted dogfish Scyliorhinus canicula. Comp. 

Biochem. Physiol. Part A Molec. Integr. Physiol. 155(4): 503-508.

DeForest, D.K and J.S. Meyer. 2015. Critical review: Toxicity of dietborne metals to aquatic 

organisms. Crit. Rev. Environ. Sci. Tech. 45: 1176-1241.

Del Giorgio, P.A., and J. Davis. 2003. Patterns in dissolved organic matter lability and

consumption across aquatic systems. In: S.E.G. Findlay and R.L. Sinsabaugh (Eds.), Aquatic 

Ecosystems, Interactivity of Dissolved Organic Matter. Academic Press/Elsevier, San Diego, 

CA, pp. 399–424.

Denton, R.W. and C. Burdon-Jones. 1982. The influence of temperature and salinity upon the 

acute toxicity of heavy metals to the banana prawn (Penaeus merguiensis de Man). Chem. Ecol. 

1(2): 131-143.

Denton, G.R.W. and C. Burdon-Jones. 1986. Environmental effects on toxicity of heavy metals 

to two species of tropical marine fish from Northern Australia. Chem. Ecol. 2(3): 233-249.

DePalma, S.G.S., W.R. Arnold, J.C. McGeer, D.G. Dixon and D.S. Smith. 2011. Effects of 

dissolved organic matter and reduced sulphur on copper bioavailability in coastal marine 

environments. Ecotoxicol. Environ. Saf. 74(3): 230-237.

De Pirro, M. and D.J. Marshall. 2005. Phylogenetic differences in cardiac activity, metal 

accumulation and mortality of limpets exposed to copper: A prosobranch-pulmonate comparison. 

J. Exp. Mar. Biol. Ecol. 322(1): 29-37.

Deruytter, D., M. Vandegehuchte, J. Garrevoet, E. Vergucht, R. Blust, K. De Schamphelaere, L. 

Vincze and C.R. Janssen. 2013. The combined effects of DOC and salinity on the accumulation 

and toxicity of copper in mussel larvae. Comm. Appl. Biol. Sci. 78(1): 15-19.

Deruytter, D., M.B. Vandegehuchte, J. Garrevoet, F. De Laender, E. Vergucht, K. Delbeke, R. 

Blust, K.A.C. De Schamphelaere, L. Vincze and C.R. Janssen. 2015. Salinity and dissolved 

organic carbon both affect copper toxicity in mussel larvae: Copper speciation or competition 

cannot explain everything. Environ. Toxicol. Chem. 34(6): 1330-1336. 

de Souza Machado, A.A., M.L.M. Hoff, R.D. Klein, J.G. Cardozo, M.M. Giacomin, G.L.L. 

Pinho and A. Bianchini. 2013. Biomarkers of waterborne copper exposure in the guppy Poecilia 

vivipara acclimated to salt water. Aquat. Toxicol. 138/139: 60-69.

Devi, K.M. and V. Gopal. 1986. Efficiency of biological heavy metal depollution technique. 

Indian J. Environ. Health 29(3): 189-193.

Ding, A. and C. Wang. 2010. Effects of accumulated copper sulfate on cellular ultrastructure in 

four tissues of Charybdis japonica. S. China Fish. Sci. 6(2): 21-28.
91

Dinnel, P.A. Q.J. Stober, J.M Link, M.W. Letourneau, W.E. Roberts, S.P. Felton and R.E. 

Nakatani. 1983. Methodology and validation of a sperm cell toxicity test for testing toxic 

substances in marine waters. Final Report – Grant R/Tox-1-FRI-UW-8306. University of 

Washington Sea Grant Program and the U.S. Environmental Protection Agency. Seattle, WA.

Dinnel, P.A., J.M. Link, Q.J. Stober, M.W. Letourneau and W.E. Roberts. 1989. Comparative 

sensitivity of sea urchin sperm bioassays to metals and pesticides. Arch. Environ. Contam. 

Toxicol. 18: 748-755.

Di Toro, D.M., E.A. Herbert, H.L. Bergman, J.S. Meyer, P.R. Paquin and R.C. Santore. 2001. 

Biotic ligand model of the acute toxicity of metals. I. Technical Basis. Environ. Toxicol. Chem.

20(10): 2383-2396.

Diz, F.R., C.V.M. Araujo, I. Moreno-Garrido, M. Hampel and J. Blasco. 2009. Short-term 

toxicity tests on the harpacticoid copepod Tisbe battagliai: Lethal and reproductive endpoints. 

Ecotoxicol. Environ. Saf. 72(7): 1881-1886.

Dodge, E.E. and T.L. Theis. 1979. Effect of chemical speciation on the uptake of copper by 

Chironomus tentans. Environ. Sci. Technol. 13(10): 1287-1288.

Dodoo, D.K., D.W. Engel and W.G. Sunda. 1992. Effect of cupric ion activity on calcium 

accumulation in juvenile flounder (Paralichthys spp.). Mar. Environ. Res. 33: 101-109.

Dorfman, D. 1977. Tolerance of Fundulus heteroclitus to different metals in salt waters. Bull. 

New Jersey Acad. Sci. 22(2): 21-23.

Dragun, Z., M. Erk, D. Ivankovic, R. Zaja, V. Filipovic Marijic and B. Raspor. 2010. 

Assessment of low-level metal contamination using the Mediterranean mussel gills as the 

indicator tissue. Environ. Sci. Pollut. Res. Intern. 17(4): 977-986.

Dung, L.Q., N.M. Cuong, N.T. Huyen and N.D. Cu. 2005. Acute toxicity test to determine the 

effects of copper, zinc and cyanide on cobia (Rachycentron canadum) resources in North 

Vietnam. Australas. J. Ecotoxicol. 11(3): 163-166.

Duran, I. and R. Beiras. 2013. Ecotoxicologically based marine acute water quality criteria for 

metals intended for protection of coastal areas. Sci. Total Environ. 463-464: 446-453.

Durkina, V.B. 1995. Morphofunctional changes in development of sea urchin offspring as a 

result of adult exposure to copper and zinc. Russ. J. Mar. Biol. (Biol. Morya) 21(6): 351-355.

Durou, C., C. Mouneyrac and C. Amiard-Triquet. 2005. Tolerance to metals and assessment of 

energy reserves in the Polychaete Nereis diversicolor in clean and contaminated estuaries. 

Environ. Toxicol. 20(1): 23-31.
92

Dwyer, F.J., L.C. Sappington, D.R. Buckler and S.B. Jones. 1995. Use of surrogate species in 

assessing contaminant risk to endangered and threatened fishes. EPA/600/R-96/029, U.S.EPA, 

Washington, DC. 78 pp.

Dwyer, F.J., F.L. Mayer, L.C. Sappington, D.R. Buckler, C.M. Bridges, I.E. Greer, D.K. 

Hardesty, C.E. Henke, C.G. Ingersoll, J.L. Kunz, D.W. Whites, T. Augspurger, D.R. Mount, K. 

Hattala and G.N. Neuderfer. 2005. Assessing contaminant sensitivity of endangered and 

threatened aquatic species: Part I. Acute toxicity of five chemicals. Arch. Environ. Contam. 

Toxicol. 48(2): 143-154.

Ebenezer, V. and J.S. Ki. 2012. Evaluation of the sub-lethal toxicity of Cu, Pb, bisphenol A and 

polychlorinated biphenyl to the marine dinoflagellate Cochlodinium polykrikoides. Algae 27(1): 

63-70.

Edullantes, B. and R.P. Galapate. 2014. Embryotoxicity of copper and zinc in tropical sea urchin 

Tripneustes gratilla. Sci. Diliman 26(1): 25-40.

Eisler, R. 1977. Acute toxicities of selected heavy metals to the softshell clam, Mya arenaria. 

Bull. Environ. Contam. Toxicol. 17(2): 138-146.

Eisler, R. 1998. Copper hazards to fish, wildlife, and invertebrates: A synoptic review. U.S. 

Geological Survey, Biological Resources Division, Biological Science Report USGS/BRD/BSR-

-1997-0002. 98 pp.

Eisler, R. and G.R. Gardner. 1973. Acute toxicology to an estuarine teleost of mixtures of 

cadmium, copper and zinc salts. J. Fish Biol. 5(2): 131-142.

Eldon, J., M. Pekkarinen and R. Kristoffersson. 1980. Effects of low concentrations of heavy 

metals on the bivalve Macoma balthica. Ann. Zool. Fenn. 17: 233-242.

Elfwing, T. and M. Tedengren. 2002. Effects of copper on the metabolism of three species of 

tropical oysters, Saccostrea cucullata, Crassostrea lugubris and C. belcheri. Aquacult. 204(1/2): 

157-166.

Elliott, N.G., D.A. Ritz and R. Swain. 1985a. Interaction between copper and zinc accumulation 

in the barnacle Elminius modestus Darwin. Mar. Environ. Res. 17(1): 13-17.

Elliott, N.G., R. Swain and D. A. Ritz. 1985b. The influence of cyclic exposure on the 

accumulation of heavy metals by Mytilus edulis planulatus (Lamarck). Mar. Environ. Res. 15(1): 

17-30.

El-Sorogy, A.S., M.A. Mohamed and H.E. Nour. 2012. Heavy metals contamination of the 

Quaternary coral reefs, Red Sea Coast, Egypt. Environ. Earth Sci. 67: 777-785.

Elumalai, M., C. Antunes and L. Guilhermino. 2005. Alterations of reproductive parameters in 

the crab Carcinus maenas after exposure to metals. Water Air Soil Pollut. 160(1-4): 245-258.
93

Engel, D.W. and B.A. Fowler. 1979. Copper and cadmium induced changes in the metabolism 

and structure of molluscan gill tissue. In: W.B. Vernberg, F.P. Thurberg, A. Calabrese and F.J. 

Vernberg (Eds.), Marine Pollution: Functional Responses, Acad., NY: 239-256.

Engel, D.W., W.G. Sunda and R.M Thuotte. 1976. Effects of copper on marine eggs and larvae. 

Environ. Health Perspect. 17: 288-289.

Engelhaupt, E. and T.S. Bianchi. 2001. Sources and composition of high-molecular-weight

dissolved organic carbon in a southern Louisiana tidal stream (Bayou Trepagnier). Limnol.

Oceanog. 46: 917–926.

Erickson, R.J. 2013. The biotic ligand model approach for addressing effects of exposure water 

chemistry on aquatic toxicity of metals: Genesis and challenges. Environ. Toxicol. Chem. 32(6): 

1212-1214. 

Erickson, S.J., N. Lackie and T.E. Maloney. 1970. A screening technique for estimating copper 

toxicity to estuarine phytoplankton. J. Water Pollut. Control Fed. 42: R270-R278.

Ettajani, H., C. Amiard-Triquet and J.C. Amiard. 1992. Experimental study of the transfer of two 

trace elements (Ag, Cu) in a marine food chain water - particles (natural sediment, microalgae) -

filter feeding molluscs (Crassostrea gigas Thunberg). Water Air Soil Pollut. 65(3): 215-236.

Evans, P. and B. Halliwell. 2001. Micronutrients: Oxidant/antioxidant status. Br. J. Nutr. 

85(Suppl. 2): S67-S74.

Fabbri, E. and A. Capuzzo. 2006. Adenylyl cyclase activity and its modulation in the gills of 

Mytilus galloprovincialis exposed to Cr6+ and Cu2+. Aquat. Toxicol. 76(1): 59-68; Erratum. 

Aquat. Toxicol. 83(2): 159.

Fabbri, R., M. Montagna, T. Balbi, E. Raffo, F. Palumbo and L. Canesi. 2014. Adaptation of the 

bivalve embryotoxicity assay for the high throughput screening of emerging contaminants in 

Mytilus galloprovincialis. Mar. Environ. Res. 99: 1-8.

Fabbrocini, A. and R. D’Adamo. 2011. Gametes and embryos of sea urchins (Paracentrotus 

lividus, Lmk., 1816) reared in confined conditions: their use in toxicity bioassays. Chem. Ecol. 

27(S2): 105-115.

Fabrizio, F. and C. Rodolfo. 2012. The response of benthic foraminiferal assemblages to copper 

exposure: A pilot mesocosm investigation. J. Environ. Protect. 3: 342-352.

Fafandel, M., N. Bihari, L. Peric and A. Cenov. 2008. Effect of marine pollutants on the acid 

DNAse activity in the hemocytes and digestive gland of the mussel Mytilus galloprovincialis. 

Aquat. Toxicol. 86(4): 508-513.
94

Fathallah, S., M.N. Medhioub, A. Medhioub, M.M. Kraiem and S. Fathallah. 2010. Toxicity of 

Hg, Cu and Zn on early developmental stages of the European clam (Ruditapes decussatus) with 

potential application in marine water quality assessment. Environ. Monit. Assess. 171(1-4): 661-

669.

Feely, R.A., C.L. Sabine, J.M. Hernandez-Ayon, D. Ianson and B. Hales. 2008. Evidence for 

upwelling of corrosive "acidified" water onto the continental shelf. Science 320(5882): 1490-

1492.

Fernandez, T.V., G. Thomas, R. Manoj Kumar and Y. Shibu Vardhanan. 1996. Toxicity of 

certain pollutants to aquatic organisms. Proc. Acad. Environ. Biol. 5(2): 165-176.

Ferreira-Cravo, M., J. Ventura-Lima, J.Z. Sandrini, L.L. Amado, L.A. Geracitano, M. Rebelo, A. 

Bianchini and J.M. Monserrat. 2009. Antioxidant responses in different body regions of the 

polychaeta Laeonereis acuta (Nereididae) exposed to copper. Ecotoxicol. Environ. Saf. 72(2): 

388-393.

Ferrer, L.D., J.S. Andrade, E.T. Contardi, R.O. Asteasuain and J.E. Marcovecchio. 2003. Copper 

and zinc concentrations in Bahia Blanca Estuary (Argentina), and their acute lethal effects on 

larvae of the crab Chasmagnathus granulata. Chem. Spec. Bioavail. 15(1): 7-14.

Ferrer, L., S. Andrade, R. Asteasuain and J. Marcovecchio. 2006. Acute toxicities of four metals 

on the early life stages of the crab Chasmagnathus granulata from Bahia Blanca Estuary, 

Argentina. Ecotoxicol. Environ. Saf. 65(2): 209-217.

Ferro, D., N. Franchi, V. Mangano, R. Bakiu, M. Cammarata, N. Parrinello, G. Santovito and L. 

Ballarin. 2013. Characterization and metal-induced gene transcription of two new copper zinc 

superoxide dismutases in the solitary ascidian Ciona intestinalis. Aquat. Toxicol. 140/141: 369-

379.

Filenko, O.F. and T.A. Samoylova. 2008. Effect of heavy metals on samples and model 

population of rotifers Brachionus plicatilis Muller at different salinity. Mosc. Univ. Biol. Sci. 

Bull. 63(2): 80-83.

Findik, O. and E. Cicek. 2011. Metal concentrations in two bioindicator fish species, Merlangius 

merlangus, Mullus barbatus, captured from the West Black Sea Coasts (Bartin) of Turkey. Bull. 

Environ. Contam. Toxicol. 87(4): 399-403.

Fitzpatrick, J.L., S. Nadella, C. Bucking, S. Balshine and C.M. Wood. 2008. The relative 

sensitivity of sperm, eggs and embryos to copper in the blue mussel (Mytilus trossulus). Comp. 

Biochem. Physiol. C. 147(4): 441-449.

Fletcher, R.L. 1989. A bioassay technique using the marine fouling green alga entermorpha. Int. 

Biodeterior. 25(6): 407-422.
95

Fokina, N.N. and N.N. Nemova. 2012. Fatty acid composition of blue mussels Mytilus edulis

changes in response to cadmium and copper effects. Comp. Biochem. Pysiol. Part A. 163: S10-

S27 (ABS).

Fokina, N.N., T.R. Ruokolainen, N.N. Nemova and I.N. Bakhmet. 2013. Changes of blue 

mussels Mytilus edulis L. lipid composition under cadmium and copper toxic effect. Biol. Trace. 

Elem. Res. 154: 217-225.

Fonseca, V., A. Serafim, R. Company, M.J. Bebianno and H. Cabral. 2009. Effect of copper 

exposure on growth, condition indices and biomarker response in juvenile sole Solea 

senegalensis. Sci. Mar. (Barcelona). 73(1): 51-58.

Forget, J., J.F. Pavillon, B. Beliaeff and F. Bocquene. 1999. Joint action of pollutant 

combinations (pesticides and metals) on survival (LC50 values) and acetylcholinesterase activity 

of Tigriopus brevicornis (Copepod, Harpacticoida). Environ. Toxicol. Chem. 18(5): 912-918.

Franchi, N., D. Ferro, L. Ballarin and G. Santovito. 2012. Transcription of genes involved in 

glutathione biosynthesis in the solitary tunicate Ciona intestinalis exposed to metals. Aquat. 

Toxicol. 114/115: 14-22.

Frazier, J.M. 1976. The dynamics of metals in the American oyster, Crassostrea virginica. II. 

Environmental effects. Chesapeake Sci. 17(3): 188-197.

Frias-Espericueta, M.G., D. Voltolina and J.I. Osuna-Lopez. 2003. Acute toxicity of copper, 

zinc, iron, and manganese and of the mixtures copper-zinc and iron-manganese to whiteleg 

shrimp Litopenaeus vannamei postlarvae. Bull. Environ. Contam. Toxicol. 71(1): 68-74.

Frias-Espericueta, M.G., S. Abad-Rosales, A.C. Nevarez-Velazquez, I. Osuna-Lopez, F. PaezOsuna, R. Lozano-Olvera and D. Voltolina. 2008a. Histological effects of a combination of 

heavy metals on Pacific white shrimp Litopenaeus vannamei juveniles. Aquat. Toxicol. 89(3): 

152-157.

Frias-Espericueta, M.G., R. Castro-Longoria, G.J. Barron-Gallardo, J.I. Osuna-Lopez, S.M. 

Abad-Rosales, F. Paez-Osuna and D. Voltolina. 2008b. Histological changes and survival of 

Litopenaeus vannamei juveniles with different copper concentrations. Aquacult. 278(1-4): 97-

100.

Freedman, J.H., M.R. Ciriolo and J. Peisach. 1989. The role of glutathione in copper metabolism 

and toxicity. J. Biol. Chem. 264: 5598-5605.

Furuta, T., N. Iwata and K. Kikuchi. 2008. Effects of fish size and water temperature on the 

acute toxicity of copper for Japanese flounder, Paralichthys olivaceus, and Red Sea bream, 

Pagrus major. J. World Aquac. Soc. 39(6): 766-773.
96

Gabbianelli, R., G. Lupidi, M. Villarini and G. Falcioni. 2003. DNA damage induced by copper 

on erythrocytes of gilthead sea bream Sparus aurata and mollusk Scapharca inaequivalvis. Arch. 

Environ. Contam. Toxicol. 45(3): 350-356.

Galindo, M.D., J.A. Jurado, M. Garcia, M.L.G. De Canales, M. Oliva, F. Lopez, M.S.A.D. 

Granado and E. Espada. 2012. Trace metal accumulation in tissues of sole (Solea senegalensis) 

and the relationships with the abiotic environment. Intern. J. Environ. Anal. Chem. 92(9): 1072-

1092.

Gall, M.L., S.P. Homes, K.A. Daffron and E.L. Johnston. 2013. Differential tolerance to copper, 

but no evidence of population-level genetic differences in a widely-dispersing native barnacle. 

Ecotoxicol. 22: 929-937.

Galletly, B.C., M.W. Blows and D.J. Marshall. 2007. Genetic mechanisms of pollution resistance 

in a marine invertebrate. Ecol. Appl. 17(8): 2290-2297.

Gama-Flores, J.L., S.S.S. Sarma and S. Nandini. 2005. Interaction among copper toxicity, 

temperature and salinity on the population dynamics of Brachionus rotundiformis (Rotifera). 

Hydrobiol. 546: 559-568.

Gambardella, C., A. De Benedictis, S.M. Guarino and M. De Nicola. 1998. Metal determination 

by atomic absorption spectrophotometry and X-ray microanalysis in Idotea baltica exposed to 

iron and copper. Ann. Chim. 88(3/4): 223-234.

Garcia, K., J.B.R. Agard and A. Mohammed. 2008. Comparative sensitivity of a tropical mysid 

Metamysidopsis insularis and the temperate species Americamysis bahia to six toxicants. 

Toxicol. Environ. Chem. 90(4): 779-785.

Gardner, G.R. and G. LaRoche. 1973. Copper induced lesions in estuarine teleosts. J. Fish. Res. 

Board Can. 30: 363.

Garr, A.L. 2012. Toxicity and availability of copper and zinc to queen conch: Implications for 

larval recruitment in the Florida Keys. Ph.D. Thesis, Florida Atlantic University, Baco Raton, 

FL.

Gentile, S.M. 1982. Memorandum to John H. Gentile. EPA, Narragansett, RI.

Gentile, S. and J. Cardin. 1982. Unpublished nickel toxicity data generated by ERL –

Narragansett. EPA Environmental Research Lab, Narragansett, RI.

Georgiades, E.T., D.C. Gillan, P. Pernet, P. Dubois, A. Temara and D.A. Holdway. 2006. Copper 

accumulation and expression of heat-stable low molecular mass proteins in Coscinasterias 

muricata. Australas. J. Ecotoxicol. 12(1): 9-19.
97

Georgopoulos, P.G., A. Roy, M.J. Yonone-Lioy, R.E. Opiekun and P.J. Lioy. 2001. 

Environmental copper: Its dynamics and human exposure issues. J. Toxicol. Environ. Health Part 

B Crit. Rev. 4(4): 341-394.

Geracitano, L., J.M. Monserrat and A. Bianchini. 2002. Physiological and antioxidant enzyme 

responses to acute and chronic exposure of Laeonereis acuta (Polychaeta, Nereididae) to copper. 

J. Exp. Mar. Biol. Ecol. 277: 145-156.

Geracitano, L.A., R. Bocchetti, J.M. Monserrat, F. Regoli and A. Bianchini. 2004. Oxidative 

stress responses in two populations of Laeonereis acuta (Polychaeta, Nereididae) after acute and 

chronic exposure to copper. Mar. Environ. Res. 58(1): 1-17.

Geret, F., A. Jouan, V. Turpin, M.J. Bebianno and R.P. Cosson. 2002a. Influence of metal 

exposure on metallothionein synthesis and lipid peroxidation in two bivalve mollusks: The oyster

(Crassostrea gigas) and the mussel (Mytilus edulis). Aquat. Liv. Res. 15(1): 61-66.

Geret, F., A. Serafim, L. Barreira and M.J. Bebianno. 2002b. Response of antioxidant systems to 

copper in the gills of the clam Ruditapes decussatus. Mar. Environ. Res. 54(3-5): 413-417.

Giarratano, E., L. Comoglio and O. Amin. 2007. Heavy metal toxicity in Exosphaeroma gigas

(Crustacea, Isopoda) from the coastal zone of Beagle Channel. Ecotoxicol. Environ. Saf. 68(3): 

451-462.

Gibson. 1976. Some effects of temperature, chlorine, and copper on the survival and growth of 

the coon stripe shrimp. In: G. Esch and R.W. McFarlane (Eds.), Thermal ecology II. Proc. of 

1975 Symp., Augusta, GA. pp. 88-92.

Gireesh, R. and C.P. Gopinathan. 2009. Effects of copper on development and survival rate of 

Paphia malabarica Chemnitz larvae under low saline condition. Environ. Monit. Assess. 155(1-

4): 455-458.

Gissi, F., M.T. Binet and M.S. Adams. 2013. Acute toxicity testing with the tropical marine 

copepod Acartia sinjiensis: Optimisation and application. Ecotoxicol. Environ. Saf. 97: 86-93.

Gissi, F., M.S. Adams, C.K. King and D.F. Jolley. 2015. A robust bioassay to assess the toxicity 

of metals to the Antarctic marine macroalga Phaeocystis antarctica. Environ. Toxicol. Chem. 

34(7): 1578-1587.

Glubokov, A.I. 1990. Growth of three species of fish during early ontogeny under normal and 

toxic conditions. J. Ichthyol. 30(2):51-59. (Originally published in Vopr. Ikhtiol. 30(1): 137-

143).

Goh, B.P.L. and L.M. Chou. 1997. Effects of the heavy metals copper and zinc on zooxanthellae 

cells in culture. Environ. Monitor. Assess. 44(1-3): 11-19.
98

Golding, C., R. Krassoi and E. Baker. 2006. The development and application of a marine 

toxicity identification evaluation (TIE) protocol for use with an Australian bivalve. Australas. J. 

Ecotoxicol. 12(1): 37-44.

Gomes, T., J.P. Pinheiro, I. Cancio, C.G. Pereira, C. Cardoso and M.J. Bebianno. 2011. Effects 

of copper nanoparticles exposure in the mussel Mytilus galloprovincialis. Environ. Sci. Technol. 

45(21): 9356-9362.

Gomes, T., C.G. Pereira, C. Cardoso, J.P. Pinheiro, I. Cancio and M.J. Bebianno. 2012. 

Accumulation and toxicity of copper oxide nanoparticles in the digestive gland of Mytilus 

galloprovincialis. Aquat. Toxicol. 118/119: 72-79.

Gomes, T., O. Araujo, R. Pereira, A.C. Almeida, A. Cravo and M.J. Bebianno. 2013. 

Genotoxicity of copper oxide and silver nanoparticles in the mussel Mytilus galloprovincialis. 

Mar. Environ. Res. 84: 51-59.

Gomiero, A. and A. Viarengo. 2014. Effects of elevated temperature on the toxicity of copper 

and oxytetracycline in the marine model, Euplotes crassus: A climate change perspective. 

Environ. Pollut. 194: 262-271.

Gomiero, A., A. Dagnino, S. Sforzini, A. Negri and A. Viarengo. 2012a. Heat stress effects on 

toxicity of copper and oxytetracycline on the marine protozoa Euplotes crassus in a climate 

change perspective. Comp. Biochem. Physiol. Part A. 163: S4-S9.

Gomiero, A., S. Sforzini, A. Dagnino, C. Nasci and A. Viarengo. 2012b. The use of multiple 

endpoints to assess cellular responses to environmental contaminants in the interstitial marine 

ciliate Euplotes crassus. Aquat. Toxicol. 114-115: 206-216.

Gopalakrishnan, S., H. Thilagam and P.V. Raja. 2007. Toxicity of heavy metals on 

embryogenesis and larvae of the marine sedentary polychaete Hydroides elegans. Arch. Environ. 

Contam. Toxicol. 52(2): 171-178.

Gorski, J. and D. Nugegoda. 2006a. Toxicity of trace metals to juvenile abalone, Haliotis rubra

following short-term exposure. Bull. Environ. Contam. Toxicol. 77(5): 732-740.

Gorski, J. and D. Nugegoda. 2006b. Sublethal toxicity of trace metals to larvae of the blacklip 

abalone, Haliotis rubra. Environ. Toxicol. Chem. 25(5): 1360-1367.

Gould, E., R.A. Greig, D. Rusanowsky and B.C. Marks. 1985. Metal-exposed sea scallops, 

Placopecten magellanicus (Gmelin): A comparison of the effects and uptake of cadmium and 

copper. In: F.J. Vernberg, F.P. Thurberg, A. Calabrese and W. Vernberg (Eds.), Marine Pollution 

and Physiology: Recent Advances. pp. 157-186. 

Gould, E., R.J. Thompson and L.J. Buckley. 1986. Exposure of the scallop Placopecten 

magellanicus (Gmelin) to sublethal copper and cadmium: Effects on the reproductive effort. 

Aquat. Sci. Fish. Abstr. 16(10): (ABS No. 16035-1Q16).
99

Govindarajan, S., C.P. Valsaraj, R. Mohan, V. Hariprasad and R. Ramasubramanian. 1993. 

Toxicity of heavy metals in aquaculture organisms: Penaeus indicus, Perna viridis, Artemia 

salina and Skeletonema costatum. Pollut. Res. 12(3): 187-189.

Gravato, C., M. Teles, M. Oliveira and M.A. Santos. 2006. Oxidative stress, liver 

biotransformation and genotoxic effects induced by copper in Anguilla anguilla L. - the 

influence of pre-exposure to beta-naphthoflavone. Chemosphere 65(10): 1821-1830.

Grosell, M. 2012. Copper. In: C.M. Wood, A.P. Farrell and C.J. Brauner (Eds.), Homeostatis and 

toxicology of essential metals: Fish Physiology, Volume 31A. Academic Press/Elsevier, 

Waltham, MA.

Grosell, M., C.M. Wood and P.J. Walsh. 2003. Copper homeostasis and toxicity in the 

elasmobranch Raja erinacea and the teleost Myoxocephalus octodecemspinosus during exposure 

to elevated water-borne copper. Comp. Biochem. Physiol. C. 135(2): 179-190.

Grosell, M., M.D. McDonald, C.M. Wood and P.J. Walsh. 2004. Effects of prolonged copper 

exposure in the marine gulf toadfish (Opsanus beta): I. Hydromineral balance and plasma 

nitrogenous waste products. Aquat. Toxicol. 68(3): 249-262.

Grosell, M., J. Blanchard, K.V. Brix and R. Gerdes. 2007. Physiology is pivotal for interactions 

between salinity and acute copper toxicity to fish and invertebrates. Aquat. Toxicol. 84(2): 162-

172.

Guida, M., M. Inglese and S. Meric. 2008. A multi-battery toxicity investigation on fungicides. 

Desalination 226(1-3): 262-270.

Guo, F., R. Tu and W.X. Wang. 2013. Different responses of abalone Haliotis discus hannai to 

waterborne and dietary-borne copper and zinc exposure. Ecotoxicol. Environ. Saf. 91: 10-17.

Guo, R. and J.S. Ki. 2012. Differential transcription of heat shock protein (HSP90) in the 

dinoflagellate Prorocentrum minimum by copper and endocrine-disrupting chemicals. 

Ecotoxicol. 21: 1448-1457.

Guo, R., V. Ebenezer and J.S. Ki. 2012. Transcriptional responses of heat shock protein 70 

(Hsp70) to thermal, bisphenol A, and copper stresses in the dinoflagellate Prorocentrum 

minimum. Chemosphere 89: 512-520.

Guo, L., P.H. Santschi and T.S. Bianchi. 1999. Dissolved organic matter in estuaries of the Gulf 

of Mexico. In: T.S. Bianchi, J. Pennock and R.R. Twilley (Eds.), Biogeochemistry of Gulf of 

Mexico Estuaries. Wiley, New York, NY, pp. 269-299.

Guo, L. and P.H. Santschi. 1997. Isotopic and elemental characterization of colloidal organic

matter from the Chesapeake Bay and Galveston Bay. Mar. Chem. 59: 1-15.
100

Hajimad, T. and V.J. Vedamanikam. 2014. Temperature effects on the toxicity of four trace 

metals to adult spotted Babylonia snails (Babylonia areolata). Toxicol. Environ. Chem. 95(8): 

1380-1387.

Hall, L.W., Jr., R.D. Anderson and J.V. Kilian. 1997. Acute and chronic toxicity of copper to the 

estuarine copepod Eurytemora affinis: Influence of organic complexation and speciation. 

Chemosphere 35(7): 1567-1597.

Hall, L.W., Jr., R.D. Anderson, B.L. Lewis and W.R. Arnold. 2008. The influence of salinity and 

dissolved organic carbon on the toxicity of copper to the estuarine copepod, Eurytemora affinis. 

Arch. Environ. Contam. Toxicol. 54(1): 44-56.

Hamelink, J., Landrum, P.F., Bergman, H. and W.H. Benson. 1994. Bioavailability: Physical, 

Chemical, and Biological Interactions. CRC Press. Boca Raton, FL. 256 pp.

Han, B.C. and T.C. Hung. 1990. Green oysters caused by copper pollution on the Taiwan coast. 

Environ. Pollut. 64(4): 347-362.

Handy, R.D. 2003. Chronic effects of copper exposure versus endocrine toxicity: Two sides of 

the same toxicological process? Comp. Biochem. Physiol. A. 135(1): 25-38.

Hanna, S.K., R.J. Miller, D. Zhou, A.A. Keller and H.S. Lenihan. 2013. Accumulation and 

toxicity of metal oxide nanoparticles in a soft-sediment estuarine amphipod. Aquat. Toxicol. 

142-143: 441-446.

Hansell, D.A. and C.A. Carlson (Eds.). 2002. Biogeochemistry of marine dissolved organic

matter. Academic Press, New York, NY, 774 pp.

Hansen, P.J. 2002. Effect of high pH on the growth and survival of marine phytoplankton:

Implications for species succession. Aquat. Microb. Ecol. 28: 279-288.

Hansen, D.J. 1983. Section on acute toxicity tests to be inserted in the April 1983 report on site 

specific FAV’s. Memorandum to W. Brungs, March 21, 1983.

Hansen, J.I., T. Mustafa and M. Depledge. 1992. Mechanisms of copper toxicity in the shore 

crab, Carcinus maenas I. Effects on Na, K-ATPase activity, haemolymph electrolyte 

concentrations and tissue. Mar. Biol. (Berlin) 114(2): 253-257.

Hare, L. 1992. Aquatic insects and trace metals: bioavailability, bioaccumulation, and toxicity. 

Critic. Rev. Toxicol. 22(5/6): 327-369.

Harrison, F.L., J.P. Knezovich and J.S. Tucker. 1981. The sensitivity of embryos of the Pacific 

oyster 'Crassostrea gigas' to different chemical forms of copper. Technical Report UCRL52725, Lawrence Livermore National Lab., CA. 30 pp.
101

Harrison, F.L., J.R. Lam and R. Berger. 1983. Sublethal responses of Mytilus edulis to increased 

dissolved copper. Sci. Total Environ. 28: 141-158.

Hasegawa, R., Y. Nakaji, Y. Kurokawa and M. Tobe. 1989. Acute toxicity tests on 113 

environmental chemicals. Sci. Rep. Res. Inst. Tohoku Univ. Ser. C Med. 36(1-4): 10-16.

Hateley, J.G., A. Grant and N.V. Jones. 1989. Heavy metal tolerance in estuarine populations of 

Nereis diversicolor. In: J.S. Ryland and P.A. Tyler (Eds.), 23rd Eur. Mar. Biol. Symp. on 

Reprod., Genetics and Distributions of Marine Organisms, Sept.5-9, 1988, Swansea, Wales, 

U.K., Olsen and Olsen, Fredensborg, Denmark. pp. 379-386.

Hebel, D.K., M.B. Jones, R.M. Moate and M.H. Depledge. 1999. Differing sensitivities of 

respiratory and osmoregulatory gill tissue of Carcinus maenas (Crustacea: Decapoda) to waterborne copper. Mar. Biol. (Berlin) 133(4): 675-681.

Hedouin, L. and R.D. Gates. 2013. Assessing fertilization success of the coral Montipora 

capitata under copper exposure: Does the night of spawning matter? Mar. Pollut. Bull. 66: 221-

224.

Hellou, J., P. Yeats, S. Steller and F. Gagne. 2003. Chemical contaminants and biological 

indicators of mussel health during gametogenesis. Environ. Toxicol. Chem. 22(9): 2080-2087.

Hem, J.D. 1989. Study and interpretation of the chemical characteristics of natural water, 3rd Ed. 

U.S. Geological Survey water-supply paper 2253. Government Printing Office.

Henry, R.P., C. Lucu, H. Onken and D. Weihrauch. 2012. Multiple functions of the crustacean 

gill: Osmotic/ionic regulation, acid-base balance, ammonia excretion, and bioaccumulation of 

toxic metals. Front Physiol. 3: 431-443.

Herzi, F., N. Jean, H. Zhao, S. Mounier, H.H. Mabrouk and A.S. Hlaili. 2013. Copper and 

cadmium effects on growth and extracellular exudation of the marine toxic dinoflagellate 

Alexandrium catenella: 3D-fluorescence spectroscopy approach. Chemosphere 93: 1230-1239.

Hetrick, F.M., B.S. Roberson and C.F. Tsai. 1982. Effect of heavy metals on the susceptibility 

and immune response of striped bass to bacterial pathogens. Office of Marine Pollution 

Assessment, National Oceanic and Atmospheric Administration, Rockville. MD. 

NOAA82112603.

Hilmy, A.M., N.F. Abdel-Hamid and K.S. Ghazaly. 1985. Toxic effects of both zinc and copper 

on size and sex of Portunus pelagicus (L.) (Crustacea: Decapoda). Bull. Inst. Oceanogr. Fish. 

Cairo ARE. 11: 207-215.

Hines, A., F.J. Staff, J. Widdows, R.M. Compton, F. Falciani and M.R. Viant. 2010. Discovery 

of metabolic signatures for predicting whole organism toxicology. Toxicol. Sci. 115(2): 369-378.
102

Ho, K.T., A. Kuhn, M.C. Pelletier, T.L. Hendricks and A. Helmstetter. 1999. pH dependent 

toxicity of five metals to three marine organisms. Environ. Toxicol. Water Qual. 14(2): 235-240.

Hodgson, A.N. and M. Hoebeke. 1984. Short-term behavioural responses of Perna perna

(Mollusca: Bivalvia) subjected to copper concentrations. Trans. R. Soc. S. Afr. 45(P2): 177-186.

Hoher, N., F. Regoli, A. Dissanayake, M. Nagel, M. Kriews, A. Kohler and K. Broeg. 2013. 

Immunomodulating effects of environmentally realistic copper concentrations in Mytilus edulis

adapted to naturally low salinities. Aquat. Toxicol. 140-141: 185-195.

Hollibaugh, J.T., D.L.R. Siebert and W.H. Thomas. 1980. A comparison of the acute toxicities of 

ten heavy metals to phytoplankton from Saanich Inlet, B.C., Canada. Estuar. Coast. Mar. Sci. 10: 

93-105.

Hook, S.E. and N.S. Fisher. 2001. Reproductive toxicity of metals in calanoid copepods. Mar. 

Biol. (Berlin) 138(6): 1131-1140.

Hook, S.E., H.L. Osborn, F. Gissi, P. Moncuquet, N.A. Twine, M.R. Wilkins and M.S. Adams. 

2014. RNA-Seq analysis of the toxicant-induced transcriptome of the marine diatom, Ceratoneis 

closterium. Mar. Genomics 16: 45-53.

Hori, H., M. Tateishi, K. Takayanagi and H. Yamada. 1996. Applicability of artificial seawater 

as a rearing seawater for toxicity tests of hazardous chemicals by marine fish species. Bull. 

Japan. Soc. Sci. Fish. (4): 614-622.

Horning, W.B. and T.W. Neiheisel. 1979. Chronic effect of copper on the bluntnose minnow, 

Pimephales notatus (Rafinesque). Arch. Environ. Contam. Toxicol. 8: 545-552.

Hornung, E., E. Fischer and S. Farkas. 1998. Isopod reproduction as a tool for sublethal-toxicity 

tests. Isr. J. Zool. 44(3/4): 445-450.

Horta-Puga, G., S. Chazaro-Olvera, I. Winfield, M. Avila-Romero and M. Moreno-Ramirez. 

2013. Cadmium, copper and lead in macroalgae from the Veracruz Reef System, Gulf of 

Mexico: Spatial distribution and rainy season variability. Mar. Pollut. Bull. 68(1-2): 127-133.

Howarth, R.S. and J.B. Sprague. 1978. Copper lethality to rainbow trout in waters of various 

hardness and pH. Water Res. 12: 455-462.

Howe, P.L., A.J. Reichelt-Brushett and M.W. Clark. 2012. Aiptasia pulchella: A tropical 

cnidarian representative for laboratory ecotoxicological research. Environ. Toxicol. Chem. 

31(11): 2653-2662.

Howe, P.L., A.J. Reichelt-Brushett and M.W. Clark. 2014. Effects of Cd, Co, Cu, Ni and Zn on 

asexual reproduction and early development of the tropical sea anemone Aiptasia pulchella. 

Ecotoxicol. 23(9): 1593-1606.
103

Howell, R. 1984. Acute toxicity of heavy metals to two species of marine nematodes. Mar. 

Environ. Res. 11(3): 153-161.

Hrovat, M., H. Segner, S. Jeram and M. Hrovat. 2009. Variability of in vivo fish acute toxicity 

data. Reg. Toxicol. Pharmacol. 54(3): 294-300.

Huang, H., J. Liang, X. Wu, H. Zhang, Q. Li and Q. Zhang. 2013. Comparison in copper 

accumulation and physiological response of Gracilaria lemaneiformis and G. lichenoides 

(Rhodophyceae). Chin. J. Oceanol. Limnol. 31(4): 803-812.

Hughes, M.M., M.A. Heber, G.E. Morrison, S.C. Schimmel and W.J. Berry. 1989. An evaluation 

of a short-term chronic effluent toxicity test using sheepshead minnow (Cyprinodon variegates) 

larvae. Environ. Pollut. 60: 1-14.

Hummel, H., P. Magni, C. Amiard-Triquet, F. Rainglet, R. Modderman, Y. Van Duijn, M. 

Herssevoort, J. De Jong, L. Snitsevorg, M. Ytsma, R. Bogaards and L. De Wolf. 1998. Influence 

of the level of oxygenation in sediment and water on copper bioavailability to marine bivalves: 

Laboratory experiments and translocation experiments in the field. Hydrobiol. 373/374(1-3): 

297-310.

Hunt, J.W., B.S. Anderson, S.L. Turpen, A.R. Coulon, M. Martin, F.H. Palmer and J.J. Janik. 

1989. Experimental evaluation of effluent toxicity testing protocols with giant kelp, mysids, red 

abalone, and topsmelt. Division of Water Quality Report NO. 89-5WQ. 144 pp.

Huovinen, P., P. Leal and I. Gomez. 2010. Interacting effects of copper, nitrogen and ultraviolet 

radiation on the physiology of three south Pacific kelps. Mar. Fresh. Res. 61(3): 330-341.

Hutchins, C.M., P.R. Teasdale, S.Y. Lee and S.L. Simpson. 2008. The influence of small-scale 

circum-neutral pH change on Cu-bioavailability and toxicity to an estuarine bivalve (Austriella cf 

plicifera) in whole-sediment toxicity tests. Sci. Total Environ. 405(1-3): 87-95.

Hutchins, C.M., P.R. Teasdale, S.Y. Lee and S.L. Simpson. 2009. Influence of sediment metal 

spiking procedures on copper bioavailability and toxicity in the estuarine bivalve Indoaustriella 

lamprelli. Environ. Toxicol. Chem. 28(9): 1885-1892.

Hutchinson, T.H., T.D. Williams and G.J. Eales. 1994. Toxicity of cadmium, hexavalent 

chromium and copper to marine fish larvae (Cyprinodon variegates) and copepods (Tisbe 

battagliai). Mar. Environ. Res. 38: 275-290.

Hwang, D.F. and Y.H. Lu. 2000. Influence of environmental and nutritional factors on growth, 

toxicity, and toxin profile of dinoflagellate Alexandrium minutum. Toxicon. 38(11): 1491-1503.

Hwang, D.S., K.W. Lee, J. Han, H.G. Park, J. Lee, Y.M. Lee, and J.S. Lee. 2010. Molecular

characterization and expression of vitellogenin (Vg) genes from the cyclopoid copepod, 

Paracyclopina nana exposed to heavy metals. Comp. Biochem. Physiol. Part C 151(3): 360-368.
104

Hyne, R.V. and D.A. Everett. 1998. Application of a benthic euryhaline amphipod, Corophium 

sp., as a sediment toxicity testing organism for both freshwater and estuarine systems. Arch. 

Environ. Contam. Toxicol. 34(1): 26-33.

Inda, J. and G.M. Cuturrufo. 1999. Valve closure by juvenile scallops as a protective mechanism 

in response to elevated levels of environmental copper. Bull. Environ. Contam. Toxicol. 63(4): 

520-523.

International Copper Association. 2003. Diffuse sources of environmental copper in the United 

States. International Copper Association, Ltd., New York, NY. 154 pp.

Isani, G., G. Sarli, G. Andreani, B. Brunetti, R. Marrocco, E. Carpene, G. Beha, F. Morandi and 

C. Benazzi. 2012. Effects of waterborne copper on gills catalase and blood biochemistry in 

gilthead seabream (Sparus aurata L.). J. Elem. S: 255-267.

Ittoop, G., K.C. George, R.M. George, K.S. Sobhana, N.K. Sanil and P.C. Nisha. 2009. Effect of 

copper toxicity on the hemolymph factors of the Indian edible oyster, Crassostrea madrasensis

(Preston). Indian J. Fish. 56(4): 301-306.

Ivanina, A.V., E. Beniash, M. Etzkorn, T.B. Meyers, A.H. Ringwood and I.M. Sokolova. 2013. 

Short-term acute hypercapnia affects cellular response to trace metals in the hard clams 

Mercenaria mercenaria. Aquat. Toxicol. 140-141: 123-133.

Jackim, E. 1973. Influence of lead and other metals on d-aminolevulinate dehydrase activity. J. 

Fish. Res. Board Can. 30: 560-562.

Janssen, C.R., G. Persoone and T.W. Snell. 1994. Cyst-based toxicity tests. VIII. Short-chronic 

toxicity tests with the freshwater rotifer Brachionus calyciflorus. Aquat. Toxicol. 28: 243-258.

Jara-Marini, M.E., J.N. Tapia-Alcaraz, J.A. Dumer-Gutierrez, L. Garcia-Rico, J. GarciaHernandez and F. Paez-Osuna. 2013. Comparative bioaccumulation of trace metals using six 

filter feeder organisms in a coastal lagoon ecosystem (of the central-east Gulf of California). 

Environ. Monit. Assess. 185(2): 1071-1085.

Jeong, C.B., B.M. Kim, R.K. Kim, H.G. Park, S.J. Lee, K.H. Shin, K.M.Y. Leung, J.S. Rhee and 

J.S. Lee. 2014. Functional characterization of P-glycoprotein in the intertidal copepod Tigriopus 

japonicus and its potential role in remediating metal pollution. Aquat. Toxicol.156: 135-147.

Jing, G., Y. Li, L. Xie and R. Zhang. 2006. Metal accumulation and enzyme activities in gills 

and digestive gland of pearl oyster (Pinctada fucata) exposed to copper. Comp. Biochem. 

Physiol. C. 144(2): 184-190.

Jiraungkoorskul, W., S. Sahaphong and N. Kangwanrangsan. 2007. Toxicity of copper in 

butterfish (Poronotus triacanthus): Tissues accumulation and ultrastructural changes. Environ. 

Toxicol. 22(1): 92-100.
105

Johnson, H.D., J.G. Grovhoug and A.O. Valkirs. 1998. Copper loading to U.S. Navy harbors: 

Norfolk, VA; Pearl Harbor, HI; and San Diego, CA. Technical Document 3052. Space and Naval 

Systems Center. Systems Center (SPAWAR), U.S. Navy, San Diego, CA.

Johnson, M.W. and J.H. Gentile. 1979. Acute toxicity of cadmium, copper, and mercury to larval 

American lobster Homarus americanus. Bull. Environ. Contam. Toxicol. 22: 258-264.

Johnson, S.K. 1974. Toxicity of several management chemicals to penaeid shrimp. Texas Agric. 

Ext. Serv. Fish Dis. Diagn. Lab Report FDDL-S3: 12 pp.

Jokela, W.E., J.P. Tilley and D.S. Ross. 2010. Manure nutrient content on Vermont dairy farms: 

Long-term trends and relationships. Comm. Soil Sci. Plant Anal. 41(5): 623-637.

Jonczyk, E., G. Gilron and B. Zajdlik. 2001. Sea urchin fertilization assay: An evaluation of 

assumptions related to sample salinity adjustment and use of natural and synthetic marine waters 

for testing. Environ. Toxicol. Chem. 20(4): 804-809.

Jones, K.H., D.M. Sanderson and D.N. Noakes. 1968. Acute toxicity data for pesticides (1968). 

World Rev. Pest Control. 7(3): 135-143.

Jones, L.H., N.V. Jones and A.J. Radlett. 1976. Some effects of salinity on the toxicity of copper 

to the polychaete Nereis diversicolor. Estuar. Coast. Mar. Sci. 4: 107-111.

Jones, M.B. 1975. Effects of copper on survival and osmoregulation in marine and brackish 

water isopods (Crustacea). In: M. Barnes (Ed.), Proceedings of the 9th European Marine Biology 

Symposium, University of Aberdeen, Scotland: 419-431.

Jorgensen, K.F. and K. Jensen. 1977. Effect of copper (II) chloride on the hatching rate of 

Artemia salina (L.). Chemosphere 6(6): 287-291.

Kalle, T. 1971. Salinity: General Introduction. In: O. Kinne (Ed.), Marine Ecology: A 

Comprehensive, Integrated Treatise on Life in Oceans and Coastal Waters, Vol. 1 (Part 2),

Wiley-Interscience, London.

Kanduc, T., D. Medakovic and B. Hamer. 2011. Mytilus galloprovincialis as a bioindicator of 

environmental conditions: The case of the eastern coast of the Adriatic Sea. Isotopes Environ. 

Health Stud. 47(1): 42-61.

Kang, J.C., S.G. Kim and S.W. Jang. 2005. Growth and hematological changes of rockfish, 

Sebastes schlegeli (Hilgendorf) exposed to dietary Cu and Cd. J. World Aquacult. Soc. 36: 188-

195.

Kannupandi, T., K. Pasupathi and P. Soundarapandian. 2001. Chronic toxicity bioassay and 

effect of endosulfan, HCH, copper and zinc on the survival and intermoult duration of larvae of 

mangrove crab Macrophthalmus erato De Man. Indian J. Exp. Biol. 39: 814-817.
106

Kapustka, L.A., W.H. Clements, L. Ziccardi, P.R. Paquin, M. Sprenger and D. Wall. 2004. Issue 

paper on the ecological effects of metals. EPA Risk Assessment Forum: Papers Addressing 

Scientific Issues in the Risk Assessment of Metals. 74 pp. Available at online: 

http://cfpub.epa.gov/ncea/cfm/recordisplay.cfm?deid=86119.

Kennish, M.J. 1998. Trace metal-sediment dynamics in estuaries: pollution assessment. Rev. 

Environ. Contam. Toxicol. 155: 69-110.

Kentouri, M., G.V. Vlachonis, P. Divanach and N. Papandroulakis. 1993. On the effect of a 

bronze pump propeller on the copper water quality and survival of sea bass (Dicentrarchus 

labrax) eggs in intensive larval aquaculture closed system. In: M. Carrillo, L. Dahle, J. Morales, 

P. Sorgeloos, N. Svennevig and J. Wyban (Eds.), From discovery to commercialization: World 

Aquaculture '93 Int. Conf., Special Publ. No. 19, European Aquacult. Soc., Oostende, Belgium. 

pp. 397 (ABS).

Ketpadung, R. and N. Tangkrock-Olan. 2006. Changes in oxygen consumption and heart rate of 

the blue swimming crab, Portunus pelagicus (Linnaeus, 1766) following exposure to sublethal 

concentrations of copper. J. Environ. Biol. 27(1): 7-12.

Khan, M.A. and M.F. Khan. 1999. Effects of copper on Aphanius dispar from mangrove area at 

Sandspit, Karachi. Pak. J. Mar. Biol. 5(2): 155-159.

Khan, S.M.M.K., C. Yoshimura, M. Arikawa, G. Omura, S. Nishiyama, Y. Suetomo, S. Kakuta 

and T. Suzaki. 2006. Axopodial degradation in the heliozoon Raphidiophrys contractilis: A 

novel bioassay system for detecting heavy metal toxicity in an aquatic environment. Environ. 

Sci. 13(4): 193-200.

Ki, J.S., S. Raisuddin, K.W. Lee, D.S. Hwang, J. Han, J.S. Rhee, I.C. Kim, H.G. Park, J.C. Ryu 

and J.S. Lee. 2009. Gene expression profiling of copper-induced responses in the intertidal 

copepod Tigriopus japonicus using a 6K oligochip microarray. Aquat. Toxicol. 93(4): 177-187.

Kiaune, L. and N. Singhasemanon. 2011. Pesticidal copper (I) oxide: Environmental fate and 

aquatic toxicity. D.M. Whitacre (Ed.). Rev. Environ. Contam. Toxicol. 213: 1-26.

Kidwai, S. and M. Ahmed. 1999. Heavy metal bioassays on selected fauna from the Karachi 

Coast (Northwest Arabian Sea). Pak. J. Zool. 30(2): 147-157.

Kim, B.M., J.S. Rhee, J.S. Seo, I.C. Kim, Y.M. Lee and J.S. Lee. 2012. 8-Oxoguanine DNA 

glycosylase 1 (OGG1) from the copepod Tigriopus japonicas: Molecular characterization and its 

expression in response to UV-B and heavy metals. Comp. Biochem. Physiol. Part C 155: 290-

299.

Kim, S.G. and J.C. Kang. 2004. Effect of dietary copper exposure on accumulation, growth and 

hematological parameters of the juvenile rockfish, Sebastes schlegeli. Mar. Environ. Res. 58: 65-

82.
107

King, C.K., S.A. Gale, R.V. Hyne, J.L. Stauber, S.L. Simpson and C.W. Hickey. 2006a. 

Sensitivities of Australian and New Zealand amphipods to copper and zinc in waters and metalspiked sediments. Chemosphere 63(9): 1466-1476.

King, C.K., S.A. Gale and J.L. Stauber. 2006b. Acute toxicity and bioaccumulation of aqueous 

and sediment-bound metals in the estuarine amphipod Melita plumulosa. Environ. Toxicol. 

21(5): 489-504.

King, C.K., M.C. Dowse and S.L. Simpson. 2010. Toxicity of metals to the bivalve Tellina 

deltoidalis and relationships between metal bioaccumulation and metal partitioning between 

seawater and marine sediments. Arch. Environ. Contam. Toxicol. 58(3): 657-665.

Kious, W.J. and R.I. Tilling. 1996. This dynamic earth: The story of plate tectonics: USGS 

general interest publication. USGS. U.S Government Printing Office. 77pp.

Klumpp, D.W. and C. Burdon-Jones. 1982. Investigations of the potential of bivalve molluscs as 

indicators of heavy metal levels in tropical marine waters. Aust. J. Mar. Fresh. Res. 33(2): 285-

300.

Knezovich, J.P., F.L. Harrison and J.S. Tucker. 1981. The influence of organic chelators on the 

toxicity of copper to embryos of the Pacific oyster, Crassostrea gigas. Arch. Environ. Contam. 

Toxicol. 10: 241-249.

Kobayashi, N. and H. Okamura. 2002. Effects of new antifouling compounds on the 

development of sea urchin. Mar. Pollut. Bull. 44: 748-751.

Kolyuchkina, G.A. and A.D. Ismailov. 2011. Morpho-functional characteristics of bivalve 

mollusks under the experimental environmental pollution by heavy metals. Oceanol. 51(5): 804-

813.

Koukouzika, N. and V.K. Dimitriadis. 2008. Aspects of the usefulness of five marine pollution 

biomarkers, with emphasis on MN and lipid content. Mar. Pollut. Bull. 56(5): 941-949.

Krang, A.S. and M. Ekerholm. 2006. Copper reduced mating behaviour in male shore crabs 

(Carcinus maenas (L.). Aquat. Toxicol. 80(1): 60-69.

Krassoi, R., I. Anderson and D. Everett. 1997. Larval abnormalities in doughboy scallops 

Chlamys (Mimachlamys) asperrima L. in response to test conditions and six reference toxicants. 

Australas. J. Ecotoxicol. 3(1): 65-74.

Krell, B., M. Moreira-Santos and R. Ribeiro. 2011. An estuarine mudsnail in situ toxicity assay 

based on postexposure feeding. Environ. Toxicol. Chem. 30(8): 1935-1942.

Krishnamurthy, S. 1994. Effects of physiochemical differences and concentration on assimilation 

and depuration of copper and silver in Crassostrea virginica. Ph.D. Thesis, Univ. of Maryland, 

Eastern Shore, MD. 98 pp.
108

Krishnani, K.K., I.S. Azad, M. Kailasam, A.R. Thirunavukkarasu, B.P. Gupta, K.O. Joseph, M. 

Muralidhar and M. Abraham. 2003. Acute toxicity of some heavy metals to Lates calcarifer fry 

with a note on its histopathological manifestations. J. Environ. Sci. Health Part A. 38(4): 645-

655.

Kulac, B., G. Atli and M. Canli. 2013. Response of ATPases in the osmoregulatory tissues of 

freshwater fish Oreochromis niloticus exposed to copper in increased salinity. Fish Physiol. 

Biochem. 39(2): 391-401.

Kumar, K.S., Y.S. Han, K.S. Choo, J.A. Kong and T. Han. 2009. Chlorophyll fluorescence based 

copper toxicity assessment of two algal species. Toxicol. Environ. Health Sci. 1(1): 17-23.

Kumar, R. 2012. Acute toxicity of cadmium, copper, lead and zinc to tiger shrimp Penaeus 

monodon postlarvae. Intern. J. Environ. Sci. 3(1): 305-311.

Kumaraguru, A.K. and K. Ramamoorthi. 1978. Toxicity of copper to three estuarine bivalves. 

Mar. Environ. Res. 1: 43-48.

Kumari, L.K. and V.R. Nair. 1992. Uptake and bioconcentration of copper and zinc by the 

molluscs Saccostrea cucullata (Born) and Cerithium rubus (Desh) from the coastal waters of 

Bombay. Indian J. Mar. Sci. 21(1): 74-76.

Kwok, C.K. and P.O. Ang Jr. 2013. Inhibition of larval swimming activity of the coral 

(Platygyra acuta) by interactive thermal and chemical stresses. Mar. Pollut. Bull. 74: 264-273.

Kwok, K.W.H. and K.M.Y. Leung. 2005. Toxicity of antifouling biocides to the intertidal 

harpacticoid copepod Tigriopus japonicus (Crustacea, Copepoda): Effects of temperature and 

salinity. Mar. Pollut. Bull. 51(8-12): 830-837.

Kwok, K.W.H., K.M.Y. Leung, V.W.W. Bao and J.S. Lee. 2008. Copper toxicity in the marine 

copepod Tigropus japonicus: Low variability and high reproducibility of repeated acute and lifecycle tests. Mar. Pollut. Bull. 57(6-12): 632-636.

Kwok, K.W.H., E.P.M. Grist and K.M.Y. Leung. 2009. Acclimation effect and fitness cost of 

copper resistance in the marine copepod Tigriopus japonicus. Ecotoxicol. Environ. Saf. 72(2): 

358-364.

Lacoue-Labarthe, T., P. Bustamante, E. Horlin, A. Luna-Acosta, A. Bado-Nilles and H. ThomasGuyon. 2009. Phenoloxidase activation in the embryo of the common cuttlefish Sepia officinalis

and responses to the Ag and Cu exposure. Fish Shellfish Immunol. 27(3): 516-521.

Lacoue-Labarthe, T., E. Le Bihan, D. Borg, N. Koueta and P. Bustamante. 2010. Acid 

phosphatase and cathepsin activity in cuttlefish (Sepia officinalis) eggs: The effects of Ag, Cd, 

and Cu exposure. ICES J. Mar. Sci. 67(7): 1517-1523.
109

Lahbib, Y., A. Mleiki, I. Marigomez and N.T. Menif. 2013. Copper, zinc, and cadmium body 

concentrations in Hexaplex trunculus collected from the Tunisian Coast. Environ. Monit. Assess. 

185(11): 8967-8975.

Laib, E. and E. Leghouchi. 2012. Cd, Cr, Cu, Pb, and Zn concentrations in Ulva lactuca, Codium 

fragile, Jania rubens, and Dictyota dichotoma from Rabta Bay, Jijel (Algeria). Environ. Monit. 

Assess. 184(3): 1711-1718.

Lan, W. and N. Chen. 1991. Acute toxicity of Hg, Cu, Cd, Zn to larvae of red sea bream, 

Chrysophrys major. Mar. Sci. (Qingdao) 5: 56-60.

Lander, L. and L. Lindeström. 1999. Copper in society and in the environment. Swedish 

Environmental Research Group, Centraltryckeriet, AB, Boras. 329 pp

Lauer, M.M. and A. Bianchini. 2010. Chronic copper toxicity in the estuarine copepod Acartia 

tonsa at different salinities. Environ. Toxicol. Chem. 29(10): 2297-2303.

Lauer, M.M., C.B. de Oliveira, N.L.I. Yano and A. Bianchini. 2012. Copper effects on key 

metabolic enzymes and mitochondrial membrane potential in gills of the estuarine crab 

Neohelice granulate at different salinities. Comp. Biochem. Physiol. Part C. 156: 140-147.

Lavolpe, M., L.L. Greco, D. Kesselman and E. Rodriguez. 2004. Differential toxicity of copper, 

zinc, and lead during the embryonic development of Chasmagnathus granulatus (Brachyura, 

Varunidae). Environ. Toxicol. Chem. 23(4): 960-967.

Lawrence, A. and C. Poulter. 1996. The potential role of the estuarine amphipod Gammarus 

duebeni in sub-lethal ecotoxicology testing. Water Sci. Technol. 34(7/8): 93-100.

Leano, E.M. and K.L. Pang. 2010. Effect of copper(II), lead(II), and zinc(II) on growth and 

sporulation of Halophytophthora from Taiwan mangroves. Water Air Soil Pollut. 213(1-4): 85-

93.

Le Cadre, V. and J.P. Debenay. 2006. Morphological and cytological responses of ammonia 

(Foraminifera) to copper contamination: Implication for the use of Foraminifera as bioindicators 

of pollution. Environ. Pollut. 143(2): 304-317.

Lee, C.H., T.K. Ryu, M. Chang and J.W. Choi. 2004. Effect of silver, cadmium, chromium, 

copper, and zinc on the fertilization of the northern Pacific asteroid, Asterias amurensis. Bull. 

Environ. Contam. Toxicol. 73(4): 613-619.

Lee, J.A., I.D. Marsden and C.N. Glover. 2010. The influence of salinity on copper accumulation 

and its toxic effects in estuarine animals with differing osmoregulatory strategies. Aquat. 

Toxicol. 99(1): 65-72.

Lee, K.M. and E.L. Johnston. 2007. Low levels of copper reduce the reproductive success of a 

mobile invertebrate predator. Mar. Environ. Res. 64(3): 336-346.
110

Lee, K.W., S. Raisuddin, D.S. Hwang, H.G. Park and J.S. Lee. 2007. Acute toxicities of trace 

metals and common xenobiotics to the marine copepod Tigriopus japonicus: Evaluation of its 

use as a benchmark species for routine ecotoxicity tests in western Pacific coastal regions. 

Environ. Toxicol. 22(5): 532-538.

Lee, K.W., S. Raisuddin, J.S. Rhee, D.S. Hwang, I.T. Yu, Y.M. Lee, H.G. Park and J.S. Lee. 

2008a. Expression of glutathione S-transferase (GST) genes in the marine copepod Tigriopus 

japonicas exposed to trace metals. Aquat. Toxicol. 89(3): 158-166.

Lee, K.W., S. Raisuddin, D.S. Hwang, H.G. Park, H.U. Dahms, I.Y. Ahn and J.S. Lee. 2008b. 

Two-generation toxicity study on the copepod model species Tigriopus japonicus. Chemosphere 

72: 1359-1365.

Lee, R. and Y. Oshima. 1998. Effects of selected pesticides, metals and organometallics on 

development of blue crab (Callinectes sapidus) embryos. Mar. Environ. Res. 46(1-5): 479-482.

Lee, R.F., S.A. Steinert, K. Nakayama and Y. Oshima. 1999. Use of DNA strand damage (comet 

assay) and embryo hatching effects to assess contaminant exposure in blue crab (Callinectes 

sapidus) embryos. In: D.S. Henshel, M.C. Black and M.C. Harrass (Eds.), Environmental 

Toxicology and Risk Assessment: Standardization of Biomarkers for Endocrine Disruption and 

Environmental Assessment, 8th Volume, ASTM STP 1364, West Conshohocken, PA. pp. 341-

349.

Lehtonen, K.K. and S. Leinio. 2003. Effects of exposure to copper and malathion on 

metallothionein levels and acetylcholinesterase activity of the mussel Mytilus edulis and the clam 

Macoma balthica from the northern Baltic Sea. Bull. Environ. Contam. Toxicol. 71(3): 489-496.

Levinton, J.S. 2001. Marine biology. Oxford University Press, Chapter 4 – The Chemical and 

Physical Environment.

Lewis, A.G. and W.R. Cave. 1982. The biological importance of copper in oceans and estuaries. 

Oceanogr. Mar. Biol. Annu. Rev. 20: 471-692.

Lewis, A.G., P.H. Whitfield and A. Ramnarine. 1972. Some particulate and soluble agents 

affecting the relationship between metal toxicity and organism survival in the calanoid copepod 

Euchaeta japonica. Mar. Biol. (Berlin). 17(3): 215-221.

Lewis, C., K. Clemow and W.V. Holt. 2013. Metal contamination increases the sensitivity of 

larvae but not gametes to ocean acidification in the polychaete Pomatoceros lamarckii

(Quatrefages). Mar. Biol. 160: 2089-2101.

Li, L., X. Huang, D. Borthakur and H. Ni. 2012b. Photosynthetic activity and antioxidative 

response of seagrass Thalassia hemprichii to trace metal stress. Acta Oceanol Sin. 31(3): 98-108.
111

Li, X., J. Li, Y. Wang, L. Fu, J. Zhu and Q. Duan. 2010. Kinetic study of the bioaccumulation of 

heavy metals (Cu, Pb, and Cd) in Chinese domestic oyster Ostrea plicatula. J. Environ. Sci. 

Health Part A 45(7): 836-845.

Li, X.B., X.L. Hou, Q. Mao, Y.L. Zhao, Y.X. Cheng and Q. Wang. 2009. Toxic effects of copper 

on antioxidative and metabolic enzymes of the marine gastropod, Onchidium struma. Arch. 

Environ. Contam. Toxicol. 56(4): 776-784.

Li, Y., Z. Gu, H. Liu, H. Shen and J. Yang. 2012a. Biochemical response of the mussel Mytilus 

coruscus (Mytiloida: Mytilidae) exposed to in vivo sub-lethal copper concentrations. Chin. J. 

Oceanol. Limnol. 30(5): 738-745.

Liao, I.C. and C.S. Hsieh. 1988. Toxicity of heavy metals to Penaeus japonicus 1. Toxicities of 

copper, cadmium and zinc to Penaeus japonicus. J. Fish. Soc. Taiwan. 15(2): 69-78.

Liess, M., O. Champeau, M. Riddle, R. Schulz and S. Duquesne. 2001. Combined effects of 

ultraviolet-B radiation and food shortage on the sensitivity of the Antarctic amphipod Paramoera 

walkeri to copper. Environ. Toxicol. Chem. 20(9): 2088-2092.

Lin, H.C. and W.A. Dunson. 1993. The effect of salinity on the acute toxicity of cadmium to the 

tropical, estuarine, hermaphroditic fish, Rivulus marmoratus: A comparison of Cd, Cu, and Zn 

tolerance with Fundulus heteroclitus. Arch. Environ. Contam. Toxicol. 25: 41-47.

Lin, Y.H., Y.Y. Shie and S.Y. Shiau. 2008. Dietary copper requirements of juvenile grouper, 

Epinephelus malabaricus. Aquacult. 274: 161-165.

Lind, D., Alto and Chatterton. 1978. Regional copper-nickel study: Aquatic toxicology study. 

Preliminary draft report, Minnesota Environmental Quality Board, St. Paul, MN.

Linder, M.C. 1991. Biochemistry of copper. Plenium Press, NY. pp. 34-45.

Liu, F., D.Z. Wang and W.X. Wang. 2012. Cadmium-induced changes in trace element 

bioaccumulation and proteomics perspective in four marine bivalves. Environ. Toxicol. Chem. 

31(6): 1292-1300.

Liu, M., G. Li, S. Zhang, W. Bao and H. Gu. 1995. Influence of toxicity of metal ions on 

survival of larval of Penaeus orientalis. Stud. Mar. Sin. (Haiyang Kexue Jikan). 36(10): 165-

174.

Liu, X.J., Z. Luo, B.X. Xiong, X. Liu, Y.H. Zhao, G.F. Hu and G.J. Lv. 2010. Effect of 

waterborne copper exposure on growth, hepatic enzymatic activities and histology in 

Synechogobius hasta. Ecotoxicol. Environ. Saf. 73(6): 1286-1291.

Long, A. and W.X. Wang. 2005. Metallothionein induction and bioaccumulation kinetics of Cd 

and Ag in the marine fish Terapon jarbua challenged with dietary or waterborne Ag and Cu. 

Mar. Ecol. Prog. Ser. 291: 215-226.
112

Lopez, J.M. and G.F. Lee. 1977. Environmental chemistry of copper in Torch Lake, Michigan. 

Water Air Soil. Pollut. 8: 373.

Lopez Greco, L.S., E.M. Rodriguez, G. Hernandez and J. Bolanos. 2002. Effects of copper on 

hatching of larvae and prezoea survival of Petrolisthes galathinus (Porcellanidae): Assays with 

ovigerous females and isolated eggs. Environ. Res. Sect. A. 90(1): 40-46.

Lorenzo, J.I., R. Beiras, V.K. Mubiana and R. Blust. 2005. Copper uptake by Mytilus edulis in 

the presence of humic acids. Environ. Toxicol. Chem. 24(4): 973-980.

Lozano, P., C. Trombini, E. Crespo, J. Blasco and I. Moreno-Garrido. 2014. ROI-scavenging 

enzyme activities as toxicity biomarkers in three species of marine microalgae exposed to model 

contaminants (copper, Irgarol and atrazine). Ecotoxicol. Environ. Saf. 104: 294-301.

Lundebye, A.K. and M.H. Depledge. 1998a. Molecular and physiological responses in shore 

crabs Carcinus maenas following exposure to copper. Mar. Environ. Res. 46(1-5): 567-572.

Lundebye, A.K. and M.H. Depledge. 1998b. Automated interpulse duration assessment (AIDA) 

in the shore crab Carcinus maenas in response to copper exposure. Mar. Biol. (Berlin). 130(4): 

613-620.

Lunz, J.D. 1972. The importance of particulate clay minerals in the uptake and accumulation of 

copper by the American oyster, Crassostrea virginica (Gmelin). M.S. Thesis, Long Island 

University, Greenvale, NY. 48 pp.

Lussier, S.M. and J.A. Cardin. 1985. Results of acute toxicity tests conducted with copper at 

ERL, Narragansett. EPA, Narragansett, RI. 3 pp.

Lussier, S.M., J.H. Gentile and J. Walker. 1985. Acute and chronic effects of heavy metals and 

cyanide on Mysidopsis bahia (Crustacea: Mysidacea). Aquat. Toxicol. 7: 25-35.

Lyla, P.S. and S.A. Khan. 2011. Pattern of accumulation of heavy metals (copper and zinc) in the 

estuarine hermit crab Clibanarius longitarsus (De Hann). Indian J. Geo-Marine Sci. 40(1): 117-

120.

Macey, B.M., M.J. Jenny, H.R. Williams, L.K. Thibodeaux, M. Beal, J.S. Almeida, C. 

Cunningham, A. Mancia, G.W. Warr, E.J. Burge, A.F. Holland, P.S. Gross, S. Hikima, K.G. 

Burnett, L. Burnett and R.W. Chapman. 2010. Modelling interactions of acid-base balance and 

respiratory status in the toxicity of metal mixtures in the American oyster Crassostrea virginica. 

Comp. Biochem. Physiol. Part A Mol. Integr. Physiol. 155(3): 341-349.

Machado, A.A.S., M.L.M. Hoff, R.D. Klein, J.G. Cardozo, M.M. Giacomin, G.L.L. Pinho and 

A. Bianchini. 2013. Biomarkers of waterborne copper exposure in the guppy Poecilia vivipara

acclimated to salt water. Aquat. Toxicol. 138-139: 60-69.
113

MacInnes, J.R. 1981. Response of embryos of the American oyster, Crassostrea virginica, to 

heavy metal mixtures. Mar. Environ. Res. 4(3): 217-227.

MacInnes, J.R. and A. Calabrese. 1978. Response of embryos of the American oyster, 

Crassostrea virginica, to heavy metals at different temperatures. In: Physiology and Behavior of 

Marine Organisms. D. S. McLusky and A. J. Berry (Eds.). Proc. 12th Eur. Mar. Biol. Symp. pp. 

195-202. Oxford, Pergammon Press.

MacInnes, J.R. and F.P. Thurberg. 1973. Effects of metals on the behavior and oxygen 

consumption of the mud snail. Mar. Pollut. Bull. 4(12): 185-186.

Macken, A., M. Giltrap, K. Ryall, B. Foley, E. McGovern, B. McHugh and M.A. Davoren. 2009. 

Test battery approach to the ecotoxicological evaluation of cadmium and copper employing a 

battery of marine bioassays. Ecotoxicol. 18(4): 470-480.

Mackereth, F.J. and W.J.P. Smyly. 1951. Toxicity of copper in solution to the stone-loach. 

Nature 168: 1130.

MacRae, R.K., D.E. Smith and N. Swoboda-Colberg. 1999. Copper binding affinity of rainbow 

trout (Oncorhynchus mykiss). Environ. Toxicol. Chem. 18(6): 1180-1189.

Maharajan, A. and M. Vijayakumaran. 2004. Copper toxicity in the spiny lobster, Panulirus 

homarus (Linnaeus). In: Proc. Natl. Sem. on New Frontiers in Marine Bioscience Research, Jan. 

22-23. pp. 205-212.

Maharajan, A., B. Vaseeharan, S. Rajalakshmi, M. Vijayakumaran, P. Kumarasamy and J.C. 

Chen. 2011. Effect of copper on morphology, weight, and chromosomal aberrations in the spiny 

lobster, Panulirus homarus (Linnaeus, 1758). Biol. Trace Elem. Res. 144: 769-780.

Maharajan, A., S. Rajalakshmi, M. Vijayakumaran and P. Kumarasamy. 2012a. Sublethal effect 

of copper toxicity against histopathological changes in the spiny lobster, Panulirus homarus

(Linnaeus, 1758). Biol. Trace Elem. Res. 145: 201-210.

Maharajan, A., S. Rajalakshmi and M. Vijayakumaran. 2012b. Effect of copper in protein, 

carbohydrate and lipid contents of the juvenile lobster, Panulirus homarus homarus (Linnaeus, 

1758). Sri Lanka J. Aquat. Sci. 17: 19-34.

Mahaut, M.L., O. Basuyaux, E. Baudiniere, C. Chataignier, J. Pain and C. Caplat. 2013. The 

porifera Hymeniacidon perlevis (Montagu, 1818) as a bioindicator for water quality monitoring. 

Environ. Sci. Pollut. Res. Int. 20(5): 2984-2992.

Mai, H., J. Cachot, J. Brune, O. Geffard, A. Belles, H. Budzinski and B. Morin. 2012. 

Embryotoxic and genotoxic effects of heavy metals and pesticides on early life stages of Pacific 

oyster (Crassostrea gigas). Mar. Pollut. Bull. 64: 2663-2670.
114

Main, W.P.L., C. Ross and G.K. Bielmyer. 2010. Copper accumulation and oxidative stress in 

the sea anemone, Aiptasia pallida, after waterborne copper exposure. Comp. Biochem. Physiol. 

C Pharmacol. Toxicol. Endocrinol. 151(2): 216-221. 

Manimaran, K., P. Karthikeyan, S. Ashokkumar, V. Ashok Prabu and P. Sampathkumar. 2012. 

Effect of copper on growth and enzyme activities of marine diatom, Odontella mobiliensis. Bull. 

Environ. Contam. Toxicol. 88: 30-37.

Manley, A.R. and J. Davenport. 1979. Behavioural responses of some marine bivalves to 

heightened seawater copper concentrations. Bull. Environ. Contam. Toxicol. 22: 739-744.

Manley, A.R., L.D. Gruffydd and P.C. Almada-Villela. 1984. The effect of copper and zinc on 

the shell growth of Mytilus edulis measured by a laser diffraction technique. J. Mar. Biol. Ass. 

U.K. 64: 417-427.

Mantoura, R.F.C. and E.M.S. Woodward. 1983. Conservative behaviour of riverine dissolved 

organic carbon in the Severn Estuary: Chemical and geochemical implications. Geochim.

Cosmochim. Acta 47: 1293-1309.

Manyin, T.A. 2008. Bioenergetic, reproductive, and population-level effects of dissolved copper 

and cadmium on the grass shrimp Palaemonetes pugio. Ph.D. Thesis. Univ. of Maryland, 

College Park, MD. 152 pp.

Manyin, T. and C.L. Rowe. 2009. Bioenergetic effects of aqueous copper and cadmium on the 

grass shrimp Palaemonetes pugio. Comp. Biochem. Phys. Part C. 150(1): 65-71.

Manyin, T. and C.L. Rowe. 2010. Reproductive and life stage-specific effects of aqueous copper 

on the grass shrimp, Palaemonetes pugio. Mar. Environ. Res. 69: 152-157.

Manzo, S., S. Buono and C. Cremisini. 2008. Predictability of copper, irgarol, and diuron 

combined effects on sea urchin Paracentrotus lividus. Arch. Environ. Contam. Toxicol. 54(1): 

57-68.

Marcano, L., O. Nusetti, J. Rodriguez-Grau and J. Vilas. 1996. Uptake and depuration of copper 

and zinc in relation to metal-binding protein in the polychaete Eurythoe complanata. Comp. 

Biochem. Physiol. C. 114(3): 179-184.

Marchan, S., M.S. Davies, S. Fleming and H.D. Jones. 1999. Effects of copper and zinc on the 

heart rate of the limpet Patella vulgata L. Comp. Biochem .Physiol. A. 123(1): 89-93.

Marshall, W.S. and M. Grosell 2005. Ion transport, osmoregulation and acid–base balance. In: D. 

Evans and J.B. Claiborne (Eds.). Physiology of Fishes, 3rd Ed. CRC Press, Boca Raton, FL: 177-

230.
115

Martin, J.M., F.M. Piltz and D.J. Reish. 1975. Studies on the Mytilus edulis community in 

Alamitos Bay, California. V. The effects of heavy metals on byssal thread production. Veliger 

18(2): 183-187.

Martin, M., M.D. Stephenson and J.H. Martin. 1977. Copper toxicity experiments in relation to 

abalone deaths observed in a power plant’s cooling waters. Calif. Fish Game. 63(2): 95-100.

Martin, M., K.E. Osborn, P. Billig and N. Glickstein. 1981. Toxicities of ten metals to 

Crassostrea gigas and Mytilus edulis embryos and Cancer magister larvae. Mar. Pollut. Bull. 

12(9): 305-308.

Martin, M., J.W. Hunt, B.S. Anderson and S.L. Turpen. 1989. Experimental evaluation of the 

mysid Holmesimysis costata as a test organism for effluent toxicity testing. Environ. Toxicol. 

Chem. 8: 1003-1012.

Martincic, D., Z. Kwokal, Z. Peharec, D. Margus and M. Branica. 1992. Distribution of Zn, Pb, 

Cd and Cu between seawater and transplanted mussels (Mytilus galloprovincialis). Sci. Total 

Environ. 119: 211-230.

Martin-Diaz, M.L, J. Blasco, M.G. De Canales, D. Sales and T.A. Del Valls. 2005. 

Bioaccumulation and toxicity of dissolved heavy metals from the Guadalquivir Estuary after the 

Aznalcollar mining spill using Ruditapes philippinarum. Arch. Environ. Contam. Toxicol. 48(2): 

233-241.

Martins, C.M.G., D.V. Almeida, L.F.F. Marins and A. Bianchini. 2011a. mRNA expression and 

activity of ion-transporting proteins in gills of the blue crab Callinectes sapidus: Effects of 

waterborne copper. Environ. Toxicol. Chem. 30(1): 206-211.

Martins, C.D.G., I.F. Barcarolli, E.J. De Menezes, M.M. Giacomin, C.M. Wood and A. 

Bianchini. 2011b. Acute toxicity, accumulation and tissue distribution of copper in the blue crab 

Callinectes sapidus acclimated to different salinities: In vivo and in vitro studies. Aquat. Toxicol. 

101(1): 88-99.

Mashroofeh, A., A.R. Bakhtiari and M. Pourkazemi. 2012. Bioaccumulation of Zn, Cu and Mn 

in the caviar and muscle of Persian sturgeon (Acipenser persicus) from the Caspian Sea, Iran. 

Bull. Environ. Contam. Toxicol. 89(6): 1201-1204.

Mathew, R. and N.R. Menon. 1984. Filtration in Perna viridis and Meretrix casta under heavy 

metal stress. Mahasagar Bull. Natl. Inst. Ocean. 17(3): 183-186.

Mathew, S. and R. Damodaran. 1997. Lipofuscin as physiological indicator of heavy metal stress 

in Sunetta scripta (yellow clam) and Perna viridis (green mussel). Indian J. Mar. Sci. 26(1): 64-

67.
116

Matranga, V., A. Pinsino, D. Randazzo, A. Giallongo and P, Dubois. 2012. Long-term

environmental exposure to metals (Cu, Cd, Pb, Zn) activates the immune cell stress response in 

the common European sea star (Asterias rubens). Mar. Environ. Res. 76: 122-127.

Mayer, F.L., D.R. Buckler, F.J. Dwyer, M.R. Ellersieck, L.C. Sappington, J.M. Besser and C.M. 

Bridges. 2008. Endangered aquatic vertebrates: Comparative and probabilistic-based toxicology. 

EPA/600/R-08/045, U.S.EPA, Washington, DC: 43 p.

Mayor, D.J., M. Solan, I. Martinez, L. Murray, H. McMillan, G.I. Paton and K. Killham. 2008. 

Acute toxicity of some treatments commonly used by the salmonid aquaculture industry to 

Corophium volutator and Hediste diversicolor: Whole sediment bioassay tests. Aquacult. 285: 

102-108.

McDuffee, A.T., G. Senisterra, S. Huntley, J.R. Lepock, K.R. Sekhar, M.J. Meredith, M.J. 

Borrelli, J.D. Morrow and M.L. Freeman. 1997. Proteins containing non-native disulfide bonds 

generated by oxidative stress can act as signals for the induction of the heat shock response. J. 

Cell Physiol. 171: 143-151.

McGee, B.L., D.J. Fisher, L.T. Yonkos, G.P. Ziegler and S. Turley. 1999. Assessment of 

sediment contamination, acute toxicity, and population viability of the estuarine amphipod 

Leptocheirus plumulosus in Baltimore Harbor, Maryland, USA. Environ. Toxicol. Chem. 18(10): 

2151-2160.

McGeer, J.C., R.C. Playle, C.M. Wood and F. Galvez. 2000. A physiologically based biotic 

ligand model for predicting the acute toxicity of waterborne silver to rainbow trout in 

freshwaters. Environ. Sci. Technol. 34: 4199-4207.

McGeer, J.C., K.V. Brix, J.M. Skeaff, D.K. DeForest, S.I. Brigham, W.J. Adams and A.S. 

Green. 2003. The inverse relationship between bioconcentration factor and exposure 

concentration for metals: Implications for hazard assessment of metals in the aquatic 

environment. Environ. Toxicol. Chem. 22(5): 1017-1037.

McGeer, J.C., S. Niyogi and D. Smith. 2011. Cadmium. Fish Physiol. 31: 125-184.

McKenzie, L.A., R. Brooks and E.L. Johnston. 2011. Heritable pollution tolerance in a marine 

invader. Environ. Res. 111(7): 926-932.

McKim, J.M., J.G. Eaton and G.W. Holcombe. 1978. Metal toxicity to embryos and larvae of 

eight species of freshwater fish - II. Copper. Bull. Environ. Contam. Toxicol. 19: 608-616.

McLeese, D.W. 1974. Toxicity of copper at two temperatures and three salinities to the 

American lobster (Homarus americanus). J. Fish. Res. Board. Can. 31: 1949-1952.

McLeese, D.W. 1976. Toxicity studies with lobster larvae and adults and a freshwater crayfish in 

1975. Manuscr. Rep. Ser. No.1384, Fish. Res. Board of Can., Environ. Can., St. Andrews, New 

Brunswick, Canada. 15 pp.
117

McLeese, D.W. and S. Ray. 1986. Toxicity of CdCl2, CdEDTA, CuCl2, and CuEDTA to marine 

invertebrates. Bull. Environ. Contam. Toxicol. 36(5): 749-755.

McLusky, D.S. and C.N.K. Phillips. 1975. Some effects of copper on the polychaete Phyllodoce 

maculate. Estuar. Coast. Mar. Sci. 3: 103-108.

McNulty, H.R., B.S. Anderson, J.W. Hunt, S.L. Turpen and M.M. Singer. 1994. Age-specific 

toxicity of copper to larval topsmelt Atherinops affinis. Environ. Toxicol. Chem. 13(3): 487-492.

Mebane, C.A. 2006. Cadmium risks to freshwater life: Derivation and validation of low-effect 

criteria values using laboratory and field studies. U.S. Geological Survey Scientific Investigation 

Report 2006-5245 (2010 rev.). Available online at: http://pubs.usgs.gov/sir/2006/5245/. 

Medesani, D.A., L.S. Lopez Greco and E.M. Rodriguez. 2004a. Disruption of endocrine 

regulation of glycemia levels by cadmium and copper in the estuarine crab Chasmagnathus 

granulata. Bull. Environ. Contam. Toxicol. 73(5): 942-946.

Medesani, D.A., L.S.L. Greco and E.M. Rodriguez. 2004b. Interference of cadmium and copper 

with the endocrine control of ovarian growth, in the estuarine crab Chasmagnathus granulata. 

Aquat. Toxicol. 69(2): 165-174.

Medina, M.H., B. Morandi and J.A. Correa. 2008. Copper effects in the copepod Tigriopus 

angulatus Lang, 1933: Natural broad tolerance allows maintenance of food webs in copperenriched coastal areas. Mar. Fresh. Res. 59(12): 1061-1066.

Menchaca, I., M.J. Belzunce, J. Franco, J.M. Garmendia, N. Montero, M. Revilla and I. 

Menchaca. 2010. Sensitivity comparison of laboratory-cultured and field-collected amphipod 

Corophium multisetosum in toxicity tests. Bull. Environ. Contam. Toxicol. 84(4): 390-394.

Mendez, N. and C. Green-Ruiz. 2005. Preliminary observations of cadmium and copper effects 

on juveniles of the polychaete Capitella sp. (Annelida: Polychaeta) from Estero del Yugo, 

Mazatlan, Mexico. Rev. Chilena Hist. Nat. 78(4): 701-710.

Mendez, N. and C. Green-Ruiz. 2006. Cadmium and copper effects on larval development and 

mortality of the polychaete Capitella sp. Y from Estero del Yugo, Mazatlan, Mexico. Water Air 

Soil Pollut. 171: 291-299.

Metaxas, A. and A.G. Lewis. 1991. Copper tolerance of Skeletonema costatum and Nitzschia 

thermalis. Aquat. Toxicol. 19(4): 265-280.

Metzger, D.C., P. Pratt and S.R. Roberts. 2012. Characterizing the effects of heavy metal and 

Vibrio exposure on HSP70 expression in Crassostrea gigas gill tissue. J. Shell. Res. 31(3): 627-

630.
118

Meyer, J.S. 2002. The utility of the terms “bioavailability” and “bioavailable fraction” for 

metals. Mar. Environ. Res. 53:417-423.

Meyer, J.S., R.C. Santore, J.P. Bobbitt, L.D. Debrey, C.J. Boese, P.R. Paquin, H.E. Allen, H.L. 

Bergman and D.M. DiToro. 1999. Binding of nickel and copper to fish gills predicts toxicity 

when water hardness varies, but free-ion activity does not. Environ. Sci. Technol. 33(6): 913-

916.

Meyer, J.S., C.J. Boese and S.A. Collyard. 2002. Whole-body accumulation of copper predicts 

acute toxicity to an aquatic oligochaete (Lumbriculus variegatus) as pH and calcium are varied. 

Comp. Biochem. Physiol. Part C 133(1-2): 99-109.

Meyer, J.S., W.J Adams, K.V. Brix, S.N. Luoma, D.R. Mount, W.A. Stubblefield and C.M.

Wood. 2005. Toxicity of dietborne metals to aquatic organisms. SETAC Press, Pensacola, FL.

Mhadhbi, L., M. Boumaiza and R. Beiras. 2010. A standard ecotoxicological bioassay using 

early life stages of the marine fish Psetta maxima. Aquat. Living Resour. 23: 209-216.

Miao, A.J., W.X. Wang and P. Juneau. 2005. Comparison of Cd, Cu, and Zn toxic effects on four 

marine phytoplankton by pulse-amplitude-modulated fluorometry. Environ. Toxicol. Chem. 

24(10): 2603-2611.

Milanovich, F.P., R. Spies, M.S. Guram and E.E. Sykes. 1976. Uptake of copper by the 

polychaete Cirriformia spirabranchia in the presence of dissolved yellow organic matter of 

natural origin. Estuar. Coast. Mar. Sci. 4: 585-588.

Miller, E. 1986. Responses of Geukensia demissa to dissolved copper at various salinities. J. 

Shellfish Res. 7(1): 127.

Miller, E.R. 1988. Physiological, exfoliative cytological, histological, and biochemical responses 

of Geukensia demissa (Mollusca) exposed to dissolved copper at various salinities. Ph.D. Thesis, 

Univ. of Connecticut, CT. 252 pp.

Millward, R.N., K.R. Carman, J.W. Fleeger, R.P. Gambrell, R.T. Powell and M.A.M. Rouse. 

2001. Linking ecological impact to metal concentrations and speciation: A microcosm 

experiment using a salt marsh meiofaunal community. Environ. Toxicol. Chem. 29(9): 2029-

2037.

Minghetti, M., M.J. Leaver, E. Carpene and S.G. George. 2008. Copper transporter 1, 

metallothionein and glutathione reductase genes are differentially expressed in tissues of sea 

bream (Sparus aurata) after exposure to dietary or waterborne copper. Comp. Biochem. Physiol. 

C. 147(4): 450-459.

Misra, S.K., A.K. Panda and S.N. Padhy. 2005. Growth performance of post larvae of Penaeus 

monodon in response to copper sulphate. J. Appl. Zool. Res. 16(1): 91-92.
119

Mizrahi, L. and Y. Achituv. 1989. Effect of heavy metals ions on enzyme activity in the 

Mediterranean mussel, Donax trunculus. Bull. Environ. Contam. Toxicol. 42(6): 854-859.

Mizrahi, L., L. Newberger-Cywiak and Y. Achituv. 1993. Effect of heavy metals ions on enzyme 

activity, mortality and behaviour of the Mediterranean white mussel Donax trunculus. In: Final 

Reports on Research Projects (Activity G), UNEP, Athens, Greece, MAP Tech. Rep. Ser. No.48. 

pp. 73-88.

Mochida, K., K. Ito, H. Harino, A. Kakuno and K. Fujii. 2006. Acute toxicity of pyrithione 

antifouling biocides and joint toxicity with copper to red sea bream (Pagrus major) and toy 

shrimp (Heptacarpus futilirostris). Environ. Toxicol. Chem. 25(11): 3058-3064.

Mochida, K., K. Ito, H. Harino, T. Onduka, A. Kakuno and K. Fujii. 2008. Early life-stage 

toxicity test for copper pyrithione and induction of skeletal anomaly in a teleost, the mummichog 

(Fundulus heteroclitus). Environ. Toxicol. Chem. 27(2): 367-374.

Mohan, M., M. Deepa, E.V. Ramasamy and A.P. Thomas. 2012. Accumulation of mercury and 

other heavy metals in edible fishes of Cochin Backwaters, southwest India. Environ. Monit. 

Assess. 184(7): 4233-4245.

Mohapatra, B.C. and K. Rengarajan. 1997. Acute toxicities of copper sulphate, zinc sulphate and 

lead nitrate to Liza parsia (Hamilton-Buchanan). J. Mar. Biol. Assoc. India 39(1/2): 69-78.

Mokhtar, M.B., S.M. Praveena, A.Z. Aris, O.C. Yong and A.P. Lim. 2012. Trace metal (Cd, Cu, 

Fe, Mn, Ni and Zn) accumulation in scleractinian corals: A record for Sabah, Borneo. Mar. 

Pollut. Bull. 64(11): 2556-2563.

Money, C., C.B. Braungardt, A.N. Jha, P.J. Worsfold, E.P. Achterberg and C. Money. 2011. 

Metal speciation and toxicity of Tamar estuary water to larvae of the Pacific oyster, Crassostrea 

gigas. Mar. Environ. Res. 72(1-2): 3-12.

Monteiro, S.C.R., G.L.L. Pinho, K. Hoffman, I.F. Barcarolli and A. Bianchini. 2013. Acute 

waterborne copper toxicity to the euryhaline copepod Acartia tonsa at different salinities: 

Influence of natural freshwater and marine dissolved organic matter. Environ. Toxicol. Chem. 

32(6): 1412-1419.

Moore, M.N. and A.R.D. Stebbing. 1976. The quantitative cytochemical effects of three metal 

ions on the lysosomal hydrolase of a hydroid. J. Mar. Biol. Assoc. U.K. 56: 995-1005.

Moore, M.N., A. Viarengo, P. Donkin and A.J.S. Hawkins. 2007. Autophagic and lysosomal 

reactions to stress in the hepatopancreas of blue mussels. Aquat. Toxicol. 84(1): 80-91.

Moraga, D., A.L. Meistertzheim, S. Tanguy-Royer, I. Boutet, A. Tanguy and A. Donval. 2005. 

Stress response in Cu2+ and Cd2+ exposed oysters (Crassostrea gigas): An 

immunohistochemical approach. Comp. Biochem. Physiol. C. 141(2): 151-156.
120

Moraitou-Apostolopoulou, M. 1978. Acute toxicity of copper to a copepod. Mar. Pollut. Bull. 9: 

278-280.

Moraitou-Apostolopoulou, M. and G. Verriopoulos. 1982. Individual and combined toxicity of 

three heavy metals, Cu, Cd and Cr for the marine copepod Tisbe holothuriae. Hydrobiol. 87: 83.

Morel, F.M., 1983. Chapter 6. Complexation: Trace metals and microorganisms. In: F.M.M. 

Morel and J.G. Hering (Eds.). Principles of Aquatic Chemistry. Wiley-Interscience Publication, 

New York, NY, pp. 301-308.

Morel, F.M. 1993. Complexation. Trace Metals and Microorganisms. In: F.M.M. Morel and J.G. 

Hering (Eds.) Principles and Applications of Aquatic Chemistry, Chapter 6, Wiley Interscience, 

NY. pp. 405-414.

Morel, F.M. and J.G. Hering (Eds.). 1983. Principles of aquatic chemistry. Wiley-Interscience 

Publication, New York, NY.

Moreno-Garrido, I., L.M. Lubian and A.M.V.M. Soares. 2000. Influence of cellular density on 

determination of EC50 in microalgal growth inhibition tests. Ecotoxicol. Environ. Saf. 47: 112-

116.

Morley, N.J., K.M.Y. Leung, D. Morritt and M. Crane. 2003. Toxicity of anti-fouling biocides to 

Parorchis acanthus (Digenea: Philophthalmidae) cercarial encystment. Dis. Aquat. Org. 54(1): 

55-60.

Morris, O.P. and G. Russell. 1973. Effect of chelation on toxicity of copper. Mar. Pollut. Bull. 

4(10): 159-160.

Moulder, S.M. 1980. Combined effect of the chlorides of mercury and copper in sea water on the 

euryhaline amphipod Gammarus duebeni. Mar. Biol. 59: 193-200.

Mouneyrac, C., O. Mastain, J.C. Amiard, C. Amiard-Triquet, P. Beaunier, A.Y. Jeantet, B.D. 

Smith and P.S. Rainbow. 2003. Trace-metal detoxification and tolerance of the estuarine worm 

Hediste diversicolor chronically exposed in their environment. Mar. Biol. (Berlin) 143(4): 731-

744.

Mukhopadhyay, M.K. 1983. Effects of copper on fish and aquatic ecosystem. Aquat. Sci. Fish. 

Abstr. 14(6 Pt.1): 264 (ABS No.14285-1Q14) (1984) / Environ. Ecol. 1(1): 53-59.

Munari, C. and M. Mistri. 2007. Effect of copper on the scope for growth of clams (Tapes 

philippinarum) from a farming area in the northern Adriatic Sea. Mar. Environ. Res. 64(3): 347-

357.

Munshi, A.B., S.Y. Quan and S.J. Li. 1996a. Acute toxicity of copper, cadmium and coppercadmium mixture to the larvae of the shrimp Penaeus monodon. Pak. J. Sci. Ind. Res. 39(1-4): 

68-71.
121

Munshi, A.B., Y.Q. Su and S.J. Li. 1996b. Acute toxicities of copper, cadmium and Cu: Cd 

mixture to larvae of the shrimp Penaeus penicillatus. Chin. J. Oceanol. Limnol. 14(2): 170-174.

Mutlu, C., M. Turkmen, A. Turkmen and Y. Tepe. 2011. Comparison of metal concentrations in 

tissues of blue crab, Callinectes sapidus from Mediterranean lagoons. Bull. Environ. Contam. 

Toxicol. 87: 282-286.

Nabavi, S.F., S.M. Nabavi, A.M. Latifi, S. Eslami and M.A. Ebrahimzadeh. 2012. Determination 

of trace elements level of pikeperch collected from the Caspian Sea. Bull. Environ. Contam. 

Toxicol. 88: 401-405.

Nadella, S.R., J.L. Fitzpatrick, N. Franklin, C. Bucking, S. Smith and C.M. Wood. 2009. 

Toxicity of dissolved Cu, Zn, Ni and Cd to developing embryos of the blue mussel (Mytilus 

trossolus) and the protective effect of dissolved organic carbon. Comp. Biochem. Physiol. C. 

149(3): 340-348.

Nair, A., Z.A. Ansari, S.N. Harkantra and A.H. Parulekar. 1977. Uptake of copper by the mussel 

Mytilus viridis L. Indian J. Mar. Sci. 6(1): 90-91.

Nassiri, Y., J.L. Mansot, J. Wery, T. Ginsburger-Vogel and J.C. Amiard. 1997. Ultrastructural 

and electron energy loss spectroscopy studies of sequestration mechanisms of Cd and Cu in the 

marine diatom Skeletonema costatum. Arch. Environ. Contam. Toxicol. 33(2): 147-155.

Naylor, G.P.L. 1987. The responses of cockles to heavy metal pollution and their use in the study 

of metal to metal uptake interactions. Ph.D. Thesis, University of Manchester, UK: 169 p.

Nebeker, A.V., C. Savonen, R.J. Baker and J.K. McCrady. 1984. Effects of copper, nickel and 

zinc on the lifecycle of the caddisfly Clistoronia magnifica (Limnephilidae). Environ. Toxicol. 

Chem. 3(4): 645-649.

Neff, J.M. 2002. Bioaccumulation in marine organisms: Effect of contaminants from oil well 

produced water. Elsevier, New York, NY. 452 pp.

Neff, J.M. and J.W. Anderson. 1977. The effects of copper (II) on molting and growth of 

juvenile lesser blue crabs Callinectes similis Williams. In: C.S. Giam (Ed.), Pollutant Effects on 

Marine Organisms, D.C. Heath and Co., Lexington, MA. pp. 155-165.

Negri, A., C. Oliveri, S. Sforzini, F. Mignione, A. Viarengo and M. Banni. 2013. Transcriptional 

response of the mussel Mytilus galloprovincialis (Lam.) following exposure to heat stress and 

copper. PLOS ONE 8(6): e66802.

Neiheisel, T.W. and M.E. Young. 1992. Use of three artificial sea salts to maintain fertile sea 

urchins (Arbacia punctulata) and to conduct fertilization tests with copper and sodium dodecyl 

sulfate. Environ. Toxicol. Chem. 11: 1179-1185.
122

Nelson, D.A., J.E. Miller and A. Calabrese. 1988. Effect of heavy metals on bay scallops, surf 

clams, and blue mussels in acute and long-term exposures. Arch. Environ. Contam. Toxicol. 17: 

595-600.

Nelson, R.W., M. Nipper, A. Lawrence and S. Watts. 2010. Parental dietary effect on 

embryological development response to toxicants with the sea urchin Arbacia punctulata. Bull. 

Environ. Contam. Toxicol. 84(1): 71-75.

Neuhoff, H.G. and H. Theede. 1984. Long-term effects of low copper concentrations at normal 

and reduced oxygen tensions. Limnologica (Berlin) 15(2): 513-521.

Ng, T.Y.T and W.X. Wang. 2007. Interactions of silver, cadmium, and copper accumulation in 

green mussels (Perna viridis). Environ. Toxicol. Chem. 26(8): 1764-1769.

Nicholson, S. 1999. Cardiac and lysosomal responses to periodic copper in the mussel Perna 

viridis (Bivalvia: Mytilidae). Mar. Pollut. Bull. 38(12): 1157-1162.

NOAA (National Oceanic and Atmospheric Administration). 1991. Contaminant trends in the 

Southern California Bight: Inventory and assessment. NOAA Technical Memorandum, NOS 

ORCA 62, National Oceanic and Atmospheric Administration, National Ocean Service, 

Rockville, MD.

NOAA (National Oceanic and Atmospheric Administration). 1994. Inventory of chemical 

concentrations in coastal and estuarine sediments. NOAA Technical Memorandum, NOS ORCA 

76, National Oceanic and Atmospheric Administration, National Ocean Service, Silver Springs, 

MD.

Norgberg-King, T. and D. Mount. 1986. Validity of effluent and ambient toxicity tests for 

predicting biological impact, Skeleton Creek, Enid, Oklahoma. Environmental Research 

Laboratory, Office of Research and Development, U.S. EPA. Duluth, MN. EPA/600/8-86/002.

Nordstrom, D.K., L.N. Plummer, T.M.L. Wigley, T.J. Wolery, J.W. Ball, E.A. Jenne, R.I. 

Bassett, R.E. McDuff, F. Morel, M.M. Reddy, G. Sposito and J. Thrailkill. 1979. Comparison of 

computerized chemical models for equilibrium calculations in aqueous systems. In: E.A. Jenne 

(Ed.) Chemical modeling in aqueous systems. ACS, Washington, DC, pp. 857-892.

Novelli, A.A., C. Losso, P.F. Ghetti and A.V. Ghirardini. 2003. Toxicity of heavy metals using 

sperm cell and embryo toxicity bioassays with Paracentrotus lividus (Echinodermata: 

Echinoidea): Comparisons with exposure concentrations in the Lagoon of Venice, Italy. Environ. 

Toxicol. Chem. 22(6): 1295-1301.

Nriagu, J.O. (Ed.) 1979. Copper in the Environment. Part I: Ecological Cycling; Part II: Health 

Effects. Wiley and Sons, Inc. New York, NY.
123

Nunes, B., R.C. Capela, T. Sergio, C. Caldeira, F. Goncalves and A.T. Correia. 2014. Effects of 

chronic exposure to lead, copper, zinc, and cadmium on biomarkers of the European eel, 

Anguilla Anguilla. Environ. Sci. Pollut. Res. 21(8): 5689-5700.

Nusetti, O., R. Salazar-Lugo, J. Rodrigues-Grau and J. Vilas. 1998. Immune and biochemical 

responses of the polychaete Eurythoe complanata exposed to sublethal concentrations of copper. 

Comp. Biochem. Physiol. 119C(2): 177-183.

O’Brien, P., H. Feldman, E.V. Grill and A.G. Lewis. 1988. Copper tolerance of the life history 

stages of the splashpool copepod Tigriopus californicus (Copepod, Harpacticoida). Mar. Ecol.

Prog. Ser. 44: 59-64.

Okazaki, R.K. 1976. Copper toxicity in the Pacific oyster Crassostrea gigas. Bull. Environ. 

Contam. Toxicol. 16: 658-665.

Okocha, R.O. and O.B. Adedeji. 2012. Overview of copper toxicity to aquatic life. Rep. Opinion 

4(8): 57-67.

Oliva, M., M.D.C. Garrido, E. Perez and M.L.G. De Canales. 2007. Evaluation of acute copper 

toxicity during early life stages of gilthead seabream, Sparus aurata. J. Environ. Sci. Health Part 

A. 42(4): 525-533.

Oliva, M., M.C. Garrido, D. Sales Marquez and M.L. Gonzalez de Canales. 2009. Sublethal and 

lethal toxicity in juvenile Senegal sole (Solea senegalensis) exposed to copper: A preliminary 

toxicity range-finding test. Exp. Toxicol. Pathol. 61(2): 113-121.

Oliveira, M., A. Serafim, M.J. Bebianno, M. Pacheco and M.A. Santos. 2008. European eel 

(Anguilla anguilla L.) metallothionein, endocrine, metabolic and genotoxic responses to copper 

exposure. Ecotoxicol. Environ. Saf. 70(1): 20-26.

Oliveira, B.L., L.F. Loureiro Fernandes, A. Bianchini, A.R. Chippari-Gomes, B.F. Silva, G.P. 

Brandao and L.C. Gomes. 2014. Acute copper toxicity in juvenile fat snook Centropomus 

parallelus (Teleostei: Centropomidae) in sea water. Neotrop. Ichthyol. 12(4): 845-852.

Olmedo, P., A.F. Hernández, A. Pla, P. Femia, A. Navas-Acien and F. Gil. 2013. Determination 

of essential elements (copper, manganese, selenium and zinc) in fish and shellfish samples. Risk 

and nutritional assessment and mercury-selenium balance. Food Chem. Toxicol. 62: 299-307.

Olsen, K.H. 2011. Effects of pollutants on olfactory mediated behaviors in fish and crustaceans. 

In: T. Breithaupt and M. Thiel (Eds.), Chemical Communication in Crustaceans, Springer, NY: 

507-529.

Olson, K.R. and R.C. Harrel. 1973. Effect of salinity on acute toxicity of mercury, copper, and 

chromium for Rangia cuneata (Pelecypoda, Mactridae). Contrib. Mar. Sci. 17: 9-13.
124

Ong, M.C., N.A.M. Shazili, D. Menier and A.W.M. Effendy. 2013. Levels of trace elements in 

tissue of Ostrea edulis and Crassostrea gigas from Quiberon Bay, Brittany, France. J. Fish. 

Aquat. Sci. 8(2): 378.

Oregon State University. 2011. Copper deficiency in beef cattle. Extension Service Coos County, 

Myrtle Point, Oregon. Available at: http://extension.oregonstate.edu/coos/ (Accessed Nov. 13, 

2013)

Oris, J.T., R.W. Winner and M.V. Moore. 1991. A four-day survival and reproduction toxicity 

test for Ceriodaphnia dubia. Environ. Toxicol. Chem. 10(2): 217-224.

Ortiz, J.B., M.L. Gonzalez de Canales and C. Sarasquete. 1999. Quantification and 

histopathological alterations produced by sublethal concentrations of copper in Fundulus 

heteroclitus. Cienc. Mar. 25(1): 119-143.

Osborn, H.L. and S.E. Hook. 2013. Using transcriptomic profiles in the diatom Phaeodactylum 

tricornutum to identify and prioritize stressors. Aquat. Toxicol. 138/139: 12-25.

Otitoloju, A.A. and K.N. Don-Pedro. 2006. Determination of types of interactions exhibited by 

binary mixtures of heavy metals tested against the hermit crab, Clibanarius africanus. Toxicol. 

Environ. Chem. 88(2): 331-343.

Owen, J.R., C.A. Morris, B. Nicolaus, J.L. Harwood and P. Kille. 2012. Induction of expression

of 14-3-3 gene in response to copper exposure in the marine alga, Fucus vesiculosus. Ecotoxicol. 

21: 124-138.

Oya, T., Y. Usui, M. Kimata and K. Isikawa. 1939. Effects of chemical substances dissolved in 

water on pisces and mollusca. I. Nippon Suisan Gakkaishi 7(5): 281-287.

Ozoh, P.T.E. 1992a. The effects of salinity, temperature and sediment on the toxicity of copper 

to juvenile Hediste (Nereis) diversicolor (O.F. Muller). Environ. Monitor. Assess. 21: 1-10.

Ozoh, P.T.E. 1992b. The importance of adult Hediste (Nereis) diversicolor in managing heavy 

metal pollution in shores and estuaries. Environ. Monitor. Assess. 21: 165-171.

Ozsuer, M. and U. Sunlu. 2013. Temporal trends of some trace metals in Lithophaga lithophaga

(L., 1758) from Izmir Bay (eastern Aegean Sea). Bull. Environ. Contam. Toxicol. 91(4): 409-

414.

Paganini, C.L. and A. Bianchini. 2009. Copper accumulation and toxicity in isolated cells from 

gills and hepatopancreas of the blue crab (Callinectes sapidus). Environ. Toxicol. Chem. 28(6): 

1200-1205.
125

Pagano, G., M. Cipollaro, G. Corsale, A. Esposito, E. Ragucci, G.G. Giordano and N.M. Trieff. 

1986. The sea urchin: Bioassay for the assessment of damage from environmental contaminants. 

In: J. Cairns, Jr. (Ed.), Community Toxicity Testing, ASTM STP 920, Philadelphia, PA. pp. 66-

92.

Pagano, G., A. de Baise, M. Iaccarino, S. Meric, D. Petruzzelli, O. Tunay, M. Warnau and N.M. 

Trieff. 2002. Bauxite manufacturing residues from Gardanne (France) and Portovesme (Italy) 

exert different patterns of pollution and toxicity to sea urchin embryos. Environ. Toxicol. Chem. 

21(6): 1272-1278.

Pagenkopf, G.K. 1983. Gill surface interaction model for trace-metal toxicity to fishes: Role of 

complexation, pH, and water hardness. Environ. Sci. Technol. 17: 342-347.

Palawski, D., J.B. Hunn and F.J. Dwyer. 1985. Sensitivity of young striped bass to organic and 

inorganic contaminants in fresh and saline waters. Trans. Am. Fish. Soc. 114(5): 748-753.

Pan, L., N. Liu, H. Zhang, J. Wang and J. Miao. 2011. Effects of heavy metal ions (Cu2+, Pb2+

and Cd2+) on DNA damage of the gills, hemocytes and hepatopancreas of marine crab, 

Charybdis japonica. J. Ocean Univ. China 10(2): 177-184.

Paquin, P.R., J.W. Gorsuch, S. Apte, G.E. Batley, K.C. Bowles, P.G.C. Campbell, C.G. Delos, 

D.M. DiToro, R.L. Dwyer, F. Galvez, R.W. Gensemer, G.G. Goss, C. Hogstrand, C.R. Janssen, 

J.C. McGeer, R.B. Naddy, R.C. Playle, R.C. Santore, U. Schneider, W.A. Stubblefield, C.M. 

Wood and K.B. Wu. 2002. The biotic ligand model: A historical overview. Comp. Biochem. 

Physiol. Part C. 133: 3-35.

Park, J., S. Kim, J. Yoo, J.S. Lee, J.W. Park, and J. Jung. 2014. Effect of salinity on acute copper 

and zinc toxicity to Tigriopus japonicus: The difference between metal ions and nanoparticles. 

Mar. Pollut. Bull. 85(2): 526-531.

Patterson, J.W., R.A. Minear, E. Gasca and C. Petropoulou. 1998. Industrial discharges of metals

to water. In: H.E. Allen, A.W. Garrison and G.W. Luther III (Eds.). Metals in Surface Waters.

Ann Arbor Press, Chelsea, MI. pp. 37-66.

Paul, J.D. and I.M. Davies. 1986. Effects of copper and tin-based anti-fouling compounds on the 

growth of scallops (Pecten maximus) and oysters (Crassostrea gigas). Aquacult. 54(3): 191-203.

Peppard, E.M., W.R. Wolters and J.W. Avault Jr. 1991. Toxicity of chelated copper to juvenile 

red drum Scianeops ocellatus. J. World Aquacult. Soc. 22(2): 101-108.

Pereira, C.D.S., D.M.D.S. Abessa, A.C.D. Bainy, L.P. Zaroni, M.R. Gasparro, M.C. Bicego, S. 

Taniguchi, T.H. Furley, E.C.P.M. De Sousa. 2007. Integrated assessment of multilevel 

biomarker responses and chemical analysis in mussels from Sao Sebastiao, Sao Paulo, Brazil. 

Environ. Toxicol. Chem. 26(3): 462-469.
126

Perez, S. and R. Beiras. 2010. The mysid Siriella armata as a model organism in marine 

ecotoxicology: Comparative acute toxicity sensitivity with Daphnia magna. Ecotoxicol. 19(1): 

196-206.

Perumal, P. and P. Subramanian. 1985. Effects of salinity and copper on larval development in 

pistol prawn, Alpheus malabaricus malabaricus Fabricius. Indian J. Mar. Sci. 14(1): 35-37.

Pesch, C.E. 1979. Influence of three sediment types on copper toxicity to the polychaete 

Neanthes arenaceodentata. Mar. Biol. (Berlin). 52(3): 237-245.

Pesch, C.E. and G.L. Hoffman. 1982. Adaptation of the polychaete Neanthes arenaceodentata to 

copper. Mar. Environ. Res. 6(4): 307-317.

Pesch, C.E. and D. Morgan. 1978. Influence of sediment in copper toxicity tests with the 

polychaete Neanthes arenaceodentata. Water Res. 12: 747-751.

Pesch, C.E., P.S. Schauer and M.A. Balboni. 1986. Effect of diet on copper toxicity to Neanthes 

arenaceodentata (Annelida: Polychaeta). ASTM Spec. Tech. Publ. 9: 369-383.

Pesch, G., N. Stewart and C. Pesch. 1979. Copper toxicity to the bay scallop (Argopecten 

irradians). Bull. Environ. Contam. Toxicol. 23: 759-765.

Petersen, R. 1982. Influence of copper and zinc on the growth of a freshwater alga, Scenedesmus 

quadricauda: The significance of chemical speciation. Environ. Sci. Technol. 16(8): 443-447.

Pillai, S. and N.R. Menon. 1998. Structural alterations accompanying acute and chronic toxicity 

of heavy metal exposure in hepatopancreas of green mussel Perna viridis (class-Pelycypoda). 

Indian J. Mar. Sci. 27(3/4): 416-420.

Pilson, M.E.Q. 1998. An Introduction to the Chemistry of the Sea. Prentice Hall Publ. Co. 431 

pp.

Pinheiro, M.A.A., P.P.G. Silva, L.F.A. Duarte, A.A. Almeida and F.P. Zanotto. 2012. 

Accumulation of six metals in the mangrove crab Ucides cordatus (Crustacea: Ucididae) and its 

food source, the red mangrove Rhizophora mangle (Angiosperma: Rhizophoraceae). Ecotoxicol. 

Environ. Saf. 81: 114-121.

Pinho, G.L. and A. Bianchini. 2010. Acute copper toxicity in the euryhaline copepod Acartia 

tonsa: Implications for the development of an estuarine and marine biotic ligand model. Environ. 

Toxicol. Chem. 29(8): 1834-1840.

Pinho, G.L.L., M.S. Pedroso, S.C. Rodrigues, S.S. De Souza and A. Bianchini. 2007. 

Physiological effects of copper in the euryhaline copepod Acartia tonsa: Waterborne versus 

waterborne plus dietborne exposure. Aquat. Toxicol. 84(1): 62-70.
127

Pinsino, A., G. Turturici, G. Sconzo and F. Geraci. 2011. Rapid changes in heat-shock cognate 

70 levels, heat-shock cognate phosphorylation state, heat-shock transcription factor, and metal 

transcription factor activity levels in response to heavy metal exposure during sea urchin 

embryonic development. Ecotoxicol. 20(1): 246-254.

Piola, R.F. and E.L. Johnston. 2006. Differential resistance to extended copper exposure in four 

introduced bryzoans. Mar. Ecol. Prog. Ser. 311: 103-114.

Piola, R.F. and E.L. Johnston. 2009. Comparing differential tolerance of native and nonindigenous marine species to metal pollution using novel assay techniques. Environ. Pollut. 157: 

2853-2864.

Playle, R.C., D.G. Dixon and K. Burnison. 1993a. Copper and cadmium binding to fish gills: 

Modification by dissolved organic carbon and synthetic ligands. Canadian J. Fish. Aquat. Sci.

50(12): 2667-2677.

Playle, R.C., D.G. Dixon and K. Burnison. 1993b. Copper and cadmium binding to fish gills: 

Estimates of metal-gill stability constants and modelling of metal accumulation. Canadian J. 

Fish. Aquat. Sci. 50(12): 2678-2687.

Pook, C., C. Lewis and T. Galloway. 2009. The metabolic and fitness costs associated with metal 

resistance in Nereis diversicolor. Mar. Pollut. Bull. 58(7): 1063-1071.

Powell, M.L., W.T. Jones, V.K. Gibbs, H.S. Hammer, J.M. Lawrence, J. Fox, A.L. Lawrence 

and S.A. Watts. 2010. Dietary copper affects survival, growth, and reproduction in the sea urchin 

Lytechinus variegatus. J. Shell. Res. 29: 1043-1049.

Prato, E. and F. Biandolino. 2005. Gammarus aequicauda (Crustacea: Amphipoda): A potential 

test species in marine sediment toxicity assessment. Aquat. Ecosyst. Health Manag. 8(4): 475-

482.

Prato, E., F. Biandolino, A.P. Bisci and C. Caroppo. 2011. Preliminary assessment of Ostreopsis

cfr. ovata acute toxicity by using a battery bioassay. Chem. Ecol. 27(S2): 117-125.

Prato, E., I. Parlapiano, G. Portacci and F. Biandolino. 2012. Contaminant sensitivity of Balanus 

perforatus and B. eburneus compared to Balanus amphitrite (Amphibalanus amphitrite). Protect.

Restor. Environ. North America. Available online at: 

http://www.pre11.org/ocs/index.php/pre/pre11/paper/view/233.

Prato, E., I. Parlapiano and F. Biandolino. 2013a. Assessment of individual and combined 

toxicities of three heavy metals (Cu, Cd and Hg) by using Tigriopus fulvus. Chem. Ecol. 29(7): 

635-642.

Prato, E., I. Parlapiano and F. Biandolino. 2013b. Sublethal effects of copper on some biological 

traits on the amphipod Gammarus aequicauda reared under laboratory conditions. Chemosphere
128

PRC Environmental Management, Inc. 1997. Report of copper loading to San Diego Bay, 

California. Prepared for California Regional Water Quality Control Board, San Diego Region 

and the San Diego Bay Interagency Water Quality Panel.

Prytherch, H.F. 1931. The role of copper in the setting and metamorphosis of the oyster. Sci. 73: 

429-431.

Pytharopoulou, S., K. Grintzalis, E. Sazakli, M. Leotsinidis, C.D. Georgiou and D.L. Kalpaxis. 

2011. Translational responses and oxidative stress of mussels experimentally exposed to Hg, Cu 

and Cd: One Pattern does not fit at all. Aquat. Toxicol. 105(1/2): 157-165.

Pytharopoulou, S., G.G. Kournoutou, M. Leotsinidis, C.D. Georgiou and D.L. Kalpaxis. 2013. 

Cadmium versus copper toxicity: Insights from an integrated dissection of protein synthesis 

pathway in the digestive glands of mussel Mytilus galloprovincialis. J. Hazard. Mat. 260: 263-

271.

Qiu, J.W., V. Thiyagarajan, S. Cheung and P.Y. Qian. 2005. Toxic effects of copper on larval 

development of the barnacle Balanus amphitrite. Mar. Pollut. Bull. 51(8-12): 688-693.

Radenac, G., D. Fichet and P. Miramand. 2001. Bioaccumulation and toxicity of four dissolved 

metals in Paracentrotus lividus sea-urchin embryo. Mar. Environ. Res. 51: 151-166.

Rainbow, P.S. 2002. Trace metal concentrations in aquatic invertebrates: Why and so what? 

Environ. Pollut. 120(3): 497-507.

Rainbow, P.S. and B.D. Smith. 2013. Accumulation and detoxification of copper and zinc by the 

decapod crustacean Palaemonetes varians from diets of field-contaminated polychaetes Nereis 

diversicolor. J. Exper. Mar. Biol. Ecol. 449: 312-330.

Rajkumar, J.S.I. 2012. Marine organisms in toxicological approach for the assessment of 

environmental risk associated with Cd, Cu, Pb and Zn. Univ. J. Environ. Res. Technol. 2(2): 19-

25.

Rajkumar, J.S.I. and M.C.J. Milton. 2011a. Biochemical markers of oxidative stress in Mugil 

cephalus exposed to cadmium, copper, lead and zinc. Int. J. Pharm. Bio. Sci. 2(3): B41- B50.

Rajkumar, J.S.I. and M.C.J. Milton. 2011b. Biochemical changes induced by cadmium, copper, 

lead and zinc exposure to Perna viridis under longterm toxicity test. Int. J. Pharm. Bio. Sci. 2(3): 

B.50-B.59.

Rajkumar, J.S.I., M.C. John Milton and T. Ambrose. 2011. Acute toxicity of water borne Cd, Cu, 

Pb, and Zn to Mugil cephalus fingerlings. Int. J. Chem. Sci. 9(2): 477-480.

Ramadan, S.E., A.N. Khalil, N.M. Dowidar and S.F. Elsonbaty. 1997. Toxicity and 

bioaccumulation of Cu2+ and Zn2+ in two isopod species (Crustacea). Bull. Natl. Inst. Ocean. 

Fish. 23: 135-154.
129

Ramakritinan, C.M., R. Chandurvelan and A.K. Kumaraguru. 2012. Acute toxicity of metals: 

Cu, Pb, Cd, Hg and Zn on marine molluscs, Cerithedia cingulate G., and Modiolus 

philippinarum H. Indian J. Geo-Mar. Sci. 41(2): 141-145.

Rao, A.J. and V.R. Nair. 2008. Effects of salinity on the toxicity of copper and zinc to the fish 

Therapon jarbua (Forsskal). Nat. Environ. Pollut. Technol. 7(2): 303-306.

Rau, M.A., J. Whitaker, J.H. Freedman and R.T. Di Giulio. 2004. Differential susceptibility of 

fish and rat liver cells to oxidative stress and cytotoxicity upon exposure to pro-oxidants. Comp. 

Biochem. Physiol. Part C 137: 335-342.

Rayburn, J.R. and W.S. Fisher. 1999. Developmental toxicity of copper chloride, methylene 

chloride, and 6-aminoniotinamide to embryos of the grass shrimp Palaemonetes pugio. Environ. 

Toxicol. Chem. 18(2): 950-957.

Raymond, P.A. and J.E. Bauer. 2001. Coupled 14C and 13C natural abundances as a tool for 

evaluating freshwater, estuarine and coastal organic matter sources and cycling. Organic

Geochem. 32: 469-485.

Raymont, J.E.G. and J. Shields. 1963. Toxicity of copper and chromium in the marine 

environment. Int. J. Air Wat. Pollut. 7: 435-443.

Reardon, I.S. and R.M. Harrell. 1990. Acute toxicity of formalin and copper sulfate to striped 

bass fingerlings held in varying salinities. Aquacult. 87: 255-270.

Reddy, P.S. 1997. Modulations in antioxidant enzymes in the gill and hepatopancreas of the 

edible crab Scylla serrata during exposure to cadmium and copper. Fresenius Environ. Bull. 

6(9/10): 589-597.

Reed, R.H. and L. Moffat. 1983. Copper toxicity and copper tolerance in Enteromorpha 

compressa (L.) Grev. J. Exp. Mar. Biol. Ecol. 69(1): 85-103.

Reeve, M.R., G.D. Grice, V.R. Gibson, M.A. Walter, K. Darcy and T. Ikeda. 1976. A controlled 

environmental pollution experiment (CEPEX) and its usefulness in the study of larger marine 

zooplankton under toxic stress. In: Effects of pollutants on aquatic organisms. Lockwood, P.M. 

(Ed.). Cambridge University Press, New York, NY. p. 145.

Regoli, F., M. Nigro, E. Bertoli, G. Principato and E. Orlando. 1997. Defenses against oxidative 

stress in the Antarctic scallop Adamussium colbecki and effects of acute exposure to metals. 

Hydrobiologia 355(1-3): 139-144.

Regoli, F., M. Nigro and E. Orlando. 1998. Lysosomal and antioxidant responses to metals in the 

Antarctic scallop Adamussium colbecki. Aquat. Toxicol. 40(4): 375-392.
130

Reichelt-Brushett, A.J. and P.L. Harrison. 1999. The effect of copper, zinc and cadmium on 

fertilization success of gametes from Scleractinian reef corals. Mar. Pollut. Bull. 38(3): 182-187.

Reichelt-Brushett, A.J. and P.L. Harrison. 2004. Development of a sublethal test to determine the 

effects of copper and lead on Scleractinian coral larvae. Arch. Environ. Contam. Toxicol. 47(1): 

40-55.

Reichelt-Brushett, A.J. and P.L. Harrison. 2005. The effect of selected trace metals on the 

fertilization success of several Scleractinian coral species. Coral Reefs. 24(4): 524-534.

Reichelt-Brushett, A.J. and K. Michalek-Wagner. 2005. Effects of copper on the fertilization 

success of the soft coral Lobophytum compactum. Aquat. Toxicol. 74(3): 280-284.

Reish, D.J. 1978. The effects of heavy metals on polychaetous annelids. Revue. Int. Oceangr. 

Med. 49: 99-104.

Reish, D.J. 1993. Effects of metals and organic compounds on survival and bioaccumulation in 

two species of marine gammaridean amphipod, together with a summary of toxicological 

research on this group. J. Nat. Hist. 27: 781-794.

Reish, D.J. and R.S. Carr. 1978. The effect of heavy metals on the survival, reproduction, 

development, and life cycles for two species of polychaetous annelids. Mar. Pollut. Bull. 9(1): 

24-27.

Reish, D.J. and J.A. Le May. 1991. Toxicity and bioconcentration of metals and organic 

compounds by polychaeta. Intern. J. Mar. Biol. 5: 653-660.

Reish, D.J., J.M. Martin, F.M. Piltz and J.Q. Word. 1976. The effect of heavy metals on 

laboratory populations of two polychaetes with comparisons to the water quality conditions and 

standards in southern California marine waters. Water Res. 10: 299-302.

Rhee, J.S., S. Raisuddin, D.S. Hwang, K.W. Lee, I.C. Kim and J.S. Lee. 2009a. Differential 

expression of metallothionein (MT) gene by trace metals and endocrine-disrupting chemicals in 

the hermaphroditic mangrove killifish, Kryptolebias marmoratus. Ecotoxicol. Environ. Saf. 

72(1): 206-212.

Rhee, J.S., S. Raisuddin, K.W. Lee, J.S. Seo, J.S. Ki, I.C. Kim, H.G. Park and J.S. Lee. 2009b. 

Heat shock protein (Hsp) gene responses of the intertidal copepod Tigriopus japonicus to 

environmental toxicants. Comp. Biochem. Physiol. Part C 149(1): 104-112.

Rhee, J.S., I.T. Yu, B.M. Kim, C.B. Jeong, K.W. Lee, M.J. Kim, S.J. Lee, G.S. Park and J.S. 

Lee. 2013. Copper induces apoptotic cell death through reactive oxygen species-triggered 

oxidative stress in the intertidal copepod Tigriopus japonicas. Aquat. Toxicol. 132-133: 182-189.

Rice, D.W. Jr. and F.L. Harrison. 1978. Copper sensitivity of Pacific herring, Clupea harengus 

pallasi, during its early life history. Fish. Bull. 76: 347-356.
131

Rice, D.W., Jr., F.L. Harrison and A. Jerald Jr. 1980. Effects of copper on early life history 

stages of northern anchovy, Engraulis mordax. Fish. Bull. 78(3): 675-683.

Ringwood, A.H. 1992. Comparative sensitivity of gametes and early developmental stages of a 

sea urchin species (Echinometra mathaei) and a bivalve species (Isognomon californicum) 

during metal exposures. Arch. Environ. Contam. Toxicol. 22: 288-295.

Ringwood, A.H., D.E. Conners and A. DiNovo. 1998. The effects of copper exposures on 

cellular responses in oysters. Mar. Environ. Res. 46(1-5): 591-595.

Rinna, F., F. Del Prete, V. Vitiello, G. Sansone and A.L. Langellotti. 2011. Toxicity assessment 

of copper, pentachlorophenol and phenanthrene by lethal and sublethal endpoints on nauplii of 

Tigriopus fulvus. Chem. Ecol. 27(S2): 77-85.

Rivera-Duarte, I., G. Rosen, D. Lapota, D.B. Chadwick, L. Kear-Padilla and A. Zirino. 2005. 

Copper toxicity to larval stages of three marine invertebrates and copper complexation capacity 

in San Diego Bay, California. Environ. Sci. Technol. 39(6): 1542-1546.

Roberts, D.A., A.G.B. Poore and E.L. Johnston. 2006. Ecological consequences of copper 

contamination in macroalgae: Effects on epifauna and associated herbivores. Environ. Toxicol. 

Chem. 25(9): 2470-2479.

Robins, R.G., R.B. Berg, K.D. Dysinger, T.E. Duaime, J.J. Metesh, F.E. Diebold, L.G. 

Twidwell, G.G. Mitman, W.H. Chatham, H.H. Huang and C.A. Young. 1997. Chemical, 

physical and biological interactions at the Berkeley Pit, Butte, Montana. Tailings and Mine 

Waste 97. Bakeman, Rotterdam.

Robinson, C.B., P.S. Wills, M.A. Riche and D.L. Straus. 2013. Tissue-specific copper 

concentrations in red drum after long-term exposure to sublethal levels of waterborne copper and 

a 21-day withdrawal. North Amer. J. Aquacult. 75: 1-6.

Rodriguez-Ortega, M.J., A. Rodriguez-Ariza, O. Amezcua and J. Lopez-Barea. 2003. Mutagenic 

activation of arylamines by subcellular fractions of Chamaelea gallina clams exposed to 

environmental pollutants. Environ. Mol. Mutagen. 41(1): 55-63.

Roesijadi, G. 1980. Influence of copper on the clam Protothaca staminea: Effects on gills and 

occurrence of copper binding proteins. Biol. Bull. 158: 233.

Romeo, M., S. Gharbi-Bouraoui, M. Gnassia-Barelli, M. Dellali and P. Aissa. 2006. Responses 

of Hexaplex (Murex) trunculus to selected pollutants. Sci. Total Environ. 359(1-3): 135-144.

Rose, A., A.M. Carruthers, J. Stauber, R. Lim and S. Blockwell. 2006. Development of an acute 

toxicity test with the marine copepod Acartia sinjiensis. Australs. J. Ecotoxicol. 12(2): 73-81.
132

Rosen, G., I. Rivera-Duarte, L. Kear-Padilla and D.B. Chadwick. 2005. Use of laboratory 

toxicity tests with bivalve and echinoderm embryos to evaluate the bioavailability of copper in 

San Diego Bay, California, USA. Environ. Toxicol. Chem. 24(2): 415-422.

Rosen, G., I. Rivera-Duarte, D.B. Chadwick, A. Ryan, R.C. Santore and P.R. Paquin. 2008a. 

Critical tissue copper residues for marine bivalve (Mytilus galloprovincialis) and echinoderm 

(Strongylocentrotus purpuratus) embryonic development: Conceptual, regulatory and 

environmental implications. Mar. Environ. Res. 66(3): 327-336.

Rosen, G., A. Osorio-Robayo, I. Rivera-Duarte and D. Lapota. 2008b. Comparison of 

bioluminescent dinoflagellate (QwikLite) and bacterial (Microtox) rapid bioassay for the 

detection of metal and ammonia toxicity. Arch. Environ. Contam. Toxicol. 54: 606-611. 

Rosko, J.J. and J.W. Rachlin. 1975. The effect of copper, zinc, cobalt and manganese on the 

growth of the marine diatom Nitzschia closterium. Bull. Torrey Bot. Club 102: 100-106.

Rueter, J.G., Jr. 1983. Effect of copper on growth, silicic acid uptake and soluble pools of silicic 

acid in the marine diatom, Thalassiosira weissflougii (Bacillariophyceae). J. Phycol. 19: 101-

104.

Ruiz-Azcona, P., O. Moreno, I. Palanco, I. Giraldez, A. Velasco and E. Morales. 2013. Temporal 

fluctuation of metals in seawater of the Piedras River estuary and the effects of copper on 

Venerupis decussata larvae. J. Shellfish Res. 32(2): 291-296.

Sabatini, S.E., G. Chaufan, A.B. Juarez, I. Coalova, L. Bianchi, M.R. Eppis and M. del Carmen 

Rios de Molina. 2009. Dietary copper effects in the estuarine crab, Neohelice (Chasmagnathus) 

granulata, maintained at two different salinities. Comp. Biochem. Physiol. Part C 150: 521-527.

Sabdono, A. 2009. Heavy metal levels and their potential toxic effect on coral Galaxea 

fascicularis from Java Sea, Indonesia. Res. J. Environ. Sci. 3(1): 96-102.

Saifullah, S.M. 1978. Inhibitory effects of copper on marine dinoflagellates. Mar. Biol. 44: 299-

308.

Sakellari, A., S. Karavoltsos, D. Theodorou, M. Dassenakis and M. Scoullos. 2013. 

Bioaccumulation of metals (Cd, Cu, Zn) by the marine bivalves M. galloprovincialis, P. radiata, 

V. verrucosa and C. chione in Mediterranean coastal microenvironments: Association with metal 

bioavailability. Environ. Monit. Assess. 185(4): 3383-3395.

Salazar, M.H. and S.M. Salazar. 1986. Acute effects of (bis)tributyltin oxide on marine 

organisms. Naval Ocean Systems Center San Diego, CA. 88 pp.

Salazar, M.H. and S.M. Salazar. 1989. Acute effects of (bis)tributyltin oxide on marine 

organisms. Summary of Work Performed - 1981 to 1983. Tech Report. No. 1299, Naval Ocean 

Systems Center. 88 pp.
133

Saliba, L.J. and R.M. Krzyz. 1976. Acclimation and tolerance of Artemia salina to copper salts. 

Mar. Biol. (Berlin) 38(3): 231-238.

Sanchez-Marin, P., J.I. Lorenzo, V.K. Mubiana, R. Blust and R. Beiras. 2012. Copper uptake by 

the marine mussel Mytilus edulis in the presence of fulvic acids. Environ. Toxicol. Chem. 31(8): 

1807-1813.

Sanders, B.M. and L.S. Martin. 1994. Copper inhibits the induction of stress protein synthesis by 

elevated temperatures in embryos of the sea urchin Strongylocentrus purpuratus. Comp. 

Biochem. Physiol. C. 109(3): 295-307.

Sanders, B.M., K.D. Jenkins, W.G. Sunda and J.D. Costlow. 1984. Free cupric ion activity in 

seawater: Effects on metallothionein and growth in crab larvae. Sci. 222: 53-55.

Santore, R.C. and C.T. Driscoll. 1995. The chess model for calculating chemical equilibria in 

soils and solutions. Chapter 17. In: Chemical Equilibrium and Reaction Models. SSSA Special 

Publication 42. Proceedings of an International Symposium Sponsored by Divisions S-1, S-2, 

and S-4 of the Soil Science Society of America, and Division a-5 of the American Society of 

Agronomy in San Antonio, Texas, 23 and 24 October 1990. R.H. Loeppert, A.P. Schwab and S. 

Goldberg (Eds.), 357-375, Soil Science Society of America, Madison, WI.

Santore, R.C., D.M. Di Toro and P.R. Paquin, H.E. Allen and J.S. Meyer. 2001. A biotic ligand 

model of the acute toxicity of metals. II. Application to acute copper toxicity in freshwater fish 

and Daphnia. Environ. Toxicol. Chem. 20(10): 2397-2402.

Sappington, L.C., F.L. Mayer, F.J. Dwyer, D.R. Buckler, J.R. Jones and M.R. Ellersieck. 2001. 

Contaminant sensitivity of threatened and endangered fishes compared to standard surrogate 

species. Environ. Toxicol. Chem. 20(12): 2869-2876.

Sastre, M.P., E. Collado, G. Collazo, S. Lebron, L. Mena, S. Morales, R. Muller, L. Perez, P. 

Rivera and Y. Velez. 2005. DNA damage in the Caribbean mussel Brachiodontes exustus: A 

comet assay evaluation. Bull. Mar. Sci. 77(1): 73-81.

Sathyanathan, B., S.M. Nair, J. Chacko and P.N.K. Nambisan. 1988. Sublethal effects of copper 

and mercury on some biochemical constituents of the estuarine clam Villorita cyprinoides var. 

cochinensis (Hanley). Bull. Environ. Contam. Toxicol. 40(4): 510-516.

Sato, M. and I. Bremner. 1993. Oxygen free radicals and metallothionein. Free Radic. Biol. Med. 

14: 325-337.

Saunders, C.E. 2012. Effects of dissolved organic matter and salinity on the toxicity of individual 

and metal mixtures of copper with zinc and silver to the saltwater rotifers, Brachionus plicatilis. 

M.S. Thesis, Stephen F. Austin State Univ.
134

Sauter, S., K.S. Buxton, K.J. Macek and S.R. Petrocelli. 1976. Effects of exposure to heavy 

metals on selected freshwater fish. Toxicity of copper, cadmium, chromium and lead to eggs and 

fry of seven fish species. EPA-600/3-76-105. National Technical Information Service, 

Springfield, VA.

Sayin, D., D.T. Cakir, N. Gencer and O. Arslan. 2012. Effects of some metals on paraoxonase 

activity from shark Scyliorhinus canicula. J. Enzyme Inhib. Med. Chem. 27(4): 595-598.

Schwarz, J.A., C.L. Mitchelmore, R. Jones, A. O’Dea and S. Seymour. 2013. Exposure to copper 

induces oxidative and stress responses and DNA damage in the coral Montastraea franksi. 

Comp. Biochem. Physiol. Part C 157: 272-279.

Science Applications International Corporation. 1993. Toxicity testing to support the New 

York/New Jersey Harbor site-specific copper criteria study. Final Rep. to EPA, Off. Wastewater 

Enforcement and Compliance (Contract No.68-C8-0066, Work Assignment C-4-94), Sci. Appl. 

Int. Corp., Narragansett, RI. 176 pp.

Scott, D.M. and C.W. Major. 1972. The effect of copper (II) on survival, respiration, and heart 

rate in the common blue mussel, Mytilus edulis. Biol. Bull. 143: 679-688.

Scott, K.J., P.P. Yevich and W.S. Boothman. Manuscript. Toxicological methods using the 

benthic amphipod Ampelisca abdita Mills. U.S. EPA, Narragansett, RI.

Scott-Fordsmand, J.J. and M.H. Depledge. 1997. Changes in the tissue concentrations and 

contents of calcium, copper and zinc in the shore crab Carcinus maenas (L.) (Crustacea: 

Decapoda) during the moult cycle and following copper exposure during ecdysis. Mar. Environ. 

Res. 44(4): 397-414.

Seim, W.K., L.R. Curtis, S.W. Glenn and G.A. Chapman. 1984. Growth and survival of 

developing steelhead trout (Salmo gairdneri) continuously or intermittently exposed to copper. 

Can. J. Fish. Aquat. Sci. 41(3): 433-438.

Selvakumar, S., S. Ajmalkhan and R. Natarajan. 1987. Copper toxicity on the ontogeny of the 

grapsid crab Neoepisesarma (Neoepisesarma) mederi (H. Milne Edwards). In: N.B. Nair (Ed.), 

Proc. Natl. Semin. Estuarine Management, June 4-5, 1987, Trivandrum, Indi. pp. 468-471.

Serafim, A. and M.J. Bebianno. 2009. Metallothionein role in the kinetic model of copper 

accumulation and elimination in the clam Ruditapes decussatus. Environ. Res. 109(4): 390-399.

Sharma, S.R.K. and S. Thomas. 2007. Hemolymph acid phosphatase activity in the green muscle 

(Perna viridis Linnaeus, 1758) exposed to copper and mercury. J. Mar. Biol. Assoc. India 49(2): 

226-229 .

Sharma, S.R.K., P.K. Asokan and A.K. Sahoo. 2006. Effect of sub-lethal level of copper and 

mercury on digestive gland cells and lysosomal enzyme activity in the green mussel (Perna 

viridis L.). J. Mar. Biol. Assoc. India 48(2): 245-248.
135

Shi, D. and W.X. Wang. 2004. Modification of trace metal accumulation in the green mussel 

Perna viridis by exposure to Ag, Cu, and Zn. Environ. Pollut. 132(2): 265-277.

Shukla, G.S., T. Hussain and S.V. Chandra. 1987. Possible role of regional superoxide dismutase 

activity and lipid peroxide levels in cadmium neurotoxicity: In vivo and in vitro studies in 

growing rats. Life Sci. 41: 2215-2221.

Shuster, C.N., Jr. and B.H. Pringle. 1968. Effects of trace metals on estuarine molluscs. In: 

Proceedings of the first Mid-Atlantic Industrial Waste Conference, November 13-15, 1967. 

Department of Civil Engineering, University of Delaware, Newark, DE. pp. 285-304.

Siddiqui, S., R.H. Goddard and G.K. Bielmyer-Fraser. 2015. Comparative effects of dissolved 

copper and copper oxide nanoparticle exposure to the sea anemone, Exaiptasia pallida. Aquat. 

Toxicol. 160: 205-213.

Sigleo, A.C. 1996. Biochemical components in suspended particles and colloids: Carbohydrates 

in the Potomac and Patuxent Estuaries. Organic Geochem. 24: 83-93.

Silva-Aciares, F., D. Moraga and C. Riquelme. 2013. Effect of copper on the immunomodulatory

activities of haemocytes in juveniles of the abalone Haliotis rufescens cultivated under hatchery 

conditions. Aquacult. 410-411: 72-78.

Simonetti, P., S.E. Botte, S.M. Fiori and J.E. Marcovecchio. 2012. Heavy-metal concentrations 

in soft tissues of the burrowing crab Neohelice granulata in Bahia Blanca Estuary, Argentina. 

Arch. Environ. Contam. Toxicol. 62(2): 243-253.

Simpson, S.L., H. Yverneau, A. Cremazy, C.V. Jarolimek, H.L. Price and D.F. Jolley. 2012. 

DGT-induced copper flux predicts bioaccumulation and toxicity to bivalves in sediments with 

varying properties. Environ. Sci. Technol. 46: 9038-9046.

Singhasemanon, N. 2008. Assessment of antifouling paint use indicators in California marinas. 

CA Department of Pesticide Regulation. Presented at: CAHMPC Annual Conference, Ventura, 

CA.

Singhasemanon, N., E. Pyatt and J. Bacey. 2009. Monitoring for indicators of antifouling paint 

pollution in California marinas. EH08-05. California Environmental Protection Agency, 

Environmental Monitoring Branch, California Department of Pesticide Regulation, Sacramento, 

CA.

Sivadasan, C.R., P.N.K. Nambisan and R. Damodaran. 1986. Toxicity of mercury, copper, and 

zinc to the prawn Metapenaeus dobsoni (Mier). Curr. Sci. 55(7): 337-340.

Skrabal, S.A., J.R. Donat and D.J. Burdige. 2000. Pore water distributions of dissolved copper 

and copper-complexing ligands in estuarine and coastal marine sediments. Geochim. Cosmoch. 

Acta 64(11): 1843-1857.
136

Sobral, P. and J. Widdows. 1997. Effects of copper exposure on the scope for growth of the clam 

Ruditapes decussatus from Southern Portugal. Mar. Pollut. Bull. 34(12): 992-1000.

Soegianto, A., B. Irawan and N. Usman. 2013. Effects of sublethal copper concentrations on gills 

of white shrimp (Litopenaeus vannamei, Boone 1931). Bull. Environ. Contam. Toxicol. 91: 630-

634.

Song, Y.F., Z. Luo, C. Huang, X. Liu, Y.X. Pan and Q.L. Chen. 2013. Effects of calcium and 

copper exposure on lipogenic metabolism, metal element compositions and histology in 

Synechogobius hasta. Fish Physiol. Biochem. 39: 1641-1656.

Song, Y.F., Z. Luo, Y.X. Pan, X. Liu, C. Huang and Q.L. Chen. 2014. Effects of copper and 

cadmium on lipogenic metabolism and metal element composition in the javelin goby 

(Synechogobius hasta) after single and combined exposure. Arch. Environ. Contam. Toxicol. 

67(2): 167-180.

Sordet, C., L. Contreras-Porcia, C. Lovazzano, S. Goulitquer, S. Andrade, P. Potin and J.A. 

Correa. 2014. Physiological plasticity of Dictyota kunthii (Phaeophyceae) to copper excess. 

Aquat. Toxicol. 150: 220-228.

Sosnowski, S.L. and J.H. Gentile. 1978. Toxicological comparison of natural and cultured 

populations of Aractia tonsa to cadmium, copper, and mercury. J. Fish. Res. Board Can. 35(10): 

1366-1369.

Sosnowski, S.L., D.J. Germond and J.H. Gentile. 1979. The effect of nutrition on the response of 

field populations of the calanoid copepod Acartia tonsa to copper. Water Res. 13: 449-452.

Soto, M., X. Lekube and I. Marigomez. 1999. Autometallographical localisation of Cu and Zn 

within target cell compartments of winkles following exposure to Cu & Zn mixtures. Eur. J. 

Histochem. 43(4): 323-334.

Sousa, A., L. Genio, S. Mendo and C. Barrosoi. 2005. Comparison of the acute toxicity of 

tributyltin and copper to veliger larvae of Nassarius reticulatus (L.). Appl. Organomet. Chem. 

19: 324-328.

S.R. Hansen and Associates. 1992. Final Report: Development of a site-specific criterion for 

copper for San Francisco Bay. Prepared for California Regional Water Quality Control Board, 

Oakland, CA. 124 pp.

SRC (Syracuse Research Corporation). 1990. Toxicological profile for copper. Prepared for the 

Agency for Toxic Substances and Disease Registry, U.S. Public Health Service. December 1990. 

Available at: http://www.atsdr.cdc.gov/toxprofiles/tp132-p.pdf.

Stagg, R. M. and T.J. Shuttleworth. 1982. The effects of copper on ionic regulation by the gills 

of the seawater-adapted flounder (Platichthys flesus L.). J. Comp. Physiol. 149: 83-90.
137

Stebbing, A.R.D. 1976. The effects of low metal levels on a colonial hydroid. J. Mar. Biol. 

Assoc. U.K. 56: 977.

Stebbing, A.R.D. 1981. Hormesis - stimulation of colony growth in Campanularia flexuosa

(Hydrozoa) by copper, cadmium and other toxicants. Aquat. Toxicol. 1(3/4): 227-238.

Steele, C.W. 1983. Comparison of the behavioural and acute toxicity of copper to sheepshead, 

Atlantic croaker and pinfish. Mar. Pollut. Bull. 14(11): 423-428.

Steele, R.L. and G.B. Thursby. 1983. A toxicity test using life stages of Champia parvula

(Rhodophyta). In: Aquatic toxicology and hazard assessment. Bishop, W.E. et al. (Eds.). ASTM 

STP 802. American Society for Testing and Materials. Philadelphia, PA. p. 73.

Steinert, S.A. and G.V. Pickwell. 1985. Multiple forms of lysozyme in copper stressed mussels 

(Mytilus edulis). Mar. Environ. Res. 17(2-4): 211-214.

Stephan, C.E., D.I. Mount, D.J. Hansen, J.H. Gentile, G.A. Chapman and W.A. Brungs. 1985. 

Guidelines for deriving numerical national water quality criteria for the protection of aquatic 

organisms and their uses. National Technical Information Service No. PB85-227049.

Stofberg, R.L., C.A. Simon and R.G. Snyman. 2011. Effects of heavy metals on the development 

and survival of abalone Haliotis midae larvae. African J. Mar. Sci. 33(2): 339-345.

Stohs, S.J. and D. Bagchi. 1995. Oxidative mechanisms in the toxicity of metal ions. Free Radic. 

Biol. Med. 18: 321-336.

Strom, D., S.L. Simpson, G.E. Batley and D.F. Jolley. 2011. The influence of sediment particle 

size and organic carbon on toxicity of copper to benthic invertebrates in oxic/suboxic surface 

sediments. Environ. Toxicol. Chem. 30(7): 1599-1610.

Stromgren, T. 1979. The effect of copper on length increase in Ascophyllum nodosum (L.) Le 

Jolis. J. Exp. Mar. Biol. Ecol. 37: 153-159.

Stuart, R.K., C.L. Dupont, D.A. Johnson, I.T. Paulsen and B. Palenik. 2009. Coastal strains of 

marine Synechococcus species exhibit increased tolerance to copper shock and a distinctive 

transcriptional response relative to those of open-ocean strains. Appl. Environ. Microbiol. 

75(15): 5047-5057.

Stumm, W. and J.T. Morgan. 1981. An introduction emphasizing chemical equilibria in natural 

waters. John Wiley and Sons Inc., New York, NY.

Sturesson, U. 1984. In situ studies of copper and zinc enrichment in shell and soft tissue of 

Mytilus edulis. In: G. Persoone, E. Jaspers and C. Claus (Eds.), Ecotoxicol. Testing for the Mar. 

Environ., Vol. 2, State Univ. Ghent and Inst. Mar. Sci. Res., Bredene, Belgium. pp. 511-533.
138

Suedel, B.C., J.A. Boraczek, R.K. Peddicord, P.A. Clifford and T.M. Dillon. 1994. Trophic 

transfer and biomagnification potential of contaminants in aquatic ecosystems. Rev. Environ. 

Contam. Toxicol. 136: 22-89.

Sulaiman, N. and W.E.W.M. Noor. 1996. Acute toxicity testing of copper, cadmium and 

ammonia to Penaeus monodon and Lates calcarifer. FRI News. 2(2): 5-7.

Sullivan, B.K., E. Buskey, D.C. Miller and P.J. Ritacco. 1983. Effects of copper and cadmium on

growth, swimming, and predator avoidance in Eurytemora affinis (Copepoda). Mar. Biol. 77: 

299-306.

Sun, F., Q. Zhou, M. Wang and J. An. 2009. Joint stress of copper and petroleum hydrocarbons 

on the polychaete Perinereis aibuhitensis at biochemical levels. Ecotoxicol. Environ. Saf. 72(7): 

1887-1892.

Sunda, W.G. and P.A. Gillespie. 1979. The response of a marine bacterium to cupric ion and its 

use to estimate cupric ion activity in seawater. J. Mar. Res. 37(4): 761-777.

Sunda, W. and R.R.L. Guillard. 1976. The relationship between cupric ion activity and the 

toxicity of copper to phytoplankton. J. Mar. Res. 34(4): 511-529.

Sunda, W.G. and J.A.M. Lewis. 1978. Effect of complexation by natural organic ligands on the 

toxicity of copper to a unicellular alga, Monochrysis lutheri. Limnol. Oceanog. 23(5): 870-876.

Sunda, W.G., P.A. Tester and S.A. Huntsman. 1990. Toxicity of trace metals to Acartia tonsa in 

the Elizabeth River and southern Chesapeake Bay. Estuar. Coast. Shelf Sci. 30: 207-221.

Sunila, I. 1988. Acute histological responses of the gill of the mussel, Mytilus edulis, to exposure 

by environmental pollutants. J. Invert. Pathol. 52(1): 137-141.

Sunila, I. and R. Lindstrom. 1986. Effects of copper and cadmium on the shell morphology, 

length growth and survival of the mussel Mytilus edulis L. In: 3rd Finnish-Swedish Semin. on 

the Gulf of Bothnia, Aug. 20-21, 1984, Pori, Finland, Vesientutkimuslaitoksen Julk. 68: 211-214.

Sutherland, J. and C.W. Major. 1981. Internal heavy metal changes as a consequence of exposure 

of Mytilus edulis, the blue mussel, to elevated external copper (II) levels. Comp. Biochem. 

Physiol. C 68(1): 63-67.

Sverdrup, H.U., M.W. Johnson and R.H. Fleming. 1942. The oceans, their physics, chemistry

and general biology. Prentice-Hall, NY.

Swedmark, M. and A. Granmo. 1981. Effects of mixtures of heavy metals and a sufactant on the 

development of cod (Gadus morhua L.). Rapp. P.V. Reun. Cons. Int. Explor. Mer. 178: 95-103.

Syasina, I.G., M.A. Vaschenko and V.B. Durkina. 1992. Histopathological changes in the gonads 

of sea urchins exposed to heavy metals. Russ. J. Mar. Biol. (Biol. Morya). 17: 244-251.
139

Sze, P.W.C. and S.Y. Lee. 1995. The potential role of mucus in the depuration of copper from 

the mussels Perna viridis (L.) and Septifer virgatus (Wiegmann). Mar. Pollut. Bull. 31(4-12): 

390-393.

Tait, T.N. 2013. Determination of copper speciation, bioavailability and toxicity in saltwater 

environments. M.S. Thesis, Wilfrid Laurier University, Waterloo, Ontario, Canada: 208 p.

Tanguy, A., I. Boutet, F. Bonhomme, P. Boudry and D. Moraga. 2002. Polymorphism of 

metallothionein genes in the Pacific oyster Crassostrea gigas as a biomarker of response to metal 

exposure. Biomarkers 7(6): 439-450.

Taylor, D.A., E.L. Thompson, S.V. Nair and D.A. Raftos. 2013. Differential effects of metal 

contamination on the transcript expression of immune- and stress-response genes in the Sydney 

Rock oyster, Saccostrea glomerata. Environ. Pollut. 178: 65-71.

TDC Environmental. 2004. Copper sources in urban runoff and shoreline activities: Information 

update. Prepared for the Clean Estuary Partnership. 72 pp.

Teles, M., M. Pacheco and M.A. Santos. 2005. Physiological and genetic responses of European 

eel (Anguilla anguilla L.) to short-term chromium or copper exposure-influence of preexposure 

to a PAH-like compound. Environ. Toxicol. 20(1): 92-99.

Thiagarajan, R., S. Gopalakrishnan and H. Thilagam. 2006. Immunomodulation in the marine 

green mussel Perna viridis exposed to sub-lethal concentrations of Cu and Hg. Arch. Environ. 

Contam. Toxicol. 51(3): 392-399.

Thiyagarajan, D., K.V. Dhaneesh, T.T. Ajith Kumar, S. Kumaresan and T. Balasubramanian. 

2012. Metals in fish along the southeast coast of India. Bull. Environ. Contam. Toxicol. 88(4): 

582-588.

Thomas, A. 1915. Effects of certain metallic salts upon fishes. Trans. Am. Fish. Soc. 44: 120-

124.

Thomas, K.V. and S. Brooks. 2010. The environmental fate and effects of antifouling biocides. 

Biofoul. 26(1): 73-88.

Thurberg, F.P., M.A. Dawson and R.S. Collier. 1973. Effects of copper and cadmium on 

osmoregulation and oxygen consumption in two species of estuarine crabs. Mar. Biol. (Berlin) 

23(3): 171-175.

Thurman, E.M. 1985. Organic geochemistry of natural waters. Martinus-Nijhoff, Dr. W. Junk 

Publishers, Dordrecht, the Netherlands, 497 pp.
140

Tipping, E. 1994. WHAM - a chemical equilibrium model and computer code for waters, 

sediments, and soils incorporating a discrete site/electrostatic model of ion-binding by humic 

substances. Computers Geosci. 20(6): 973-1023.

Tisdale, S.L., W.L. Nelson and J.D. Beaton. 1985. Soil fertility and fertilizers (4th ed.) Macmillan 

Publishing Company, NY.

TOXSCAN Incorporated. 1991a. Results of provision E5F spiked metals toxicity testing 14 to 21 

February 1991. Prepared for Kinnetic Lab. Inc. for "Site-Specific Water Quality Objectives for 

South San Francisco Bay" Report by Larry Walker Assoc. and Kinnetic Lab. Under Subcontract 

to CH2M Hill, 27 pp.

TOXSCAN Incorporated. 1991b. Results of provision E5F spiked metals toxicity testing 27 

February to 6 March 1991. Prepared for Kinnetic Lab. Inc. for "Site-Specific Water Quality 

Objectives for South San Francisco Bay" Report by Larry Walker Assoc. and Kinnetic Lab.

under Subcontract to CH2M Hill, 27 pp.

TOXSCAN Incorporated. 1991c. Results of provision E5F spiked metals toxicity testing 2 to 9 

April 1991. Prepared for Kinnetic Lab. Inc. for "Site-Specific Water Quality Objectives for 

South San Francisco Bay" Report by Larry Walker Assoc. and Kinnetic Lab. Under Subcontract 

to CH2M Hill, 27 pp.

Trevisan, R., D.F. Mello, A.S. Fisher, P.M. Schuwerack, A.L. Dafre and A.J. Moody. 2011. 

Selenium in water enhances antioxidant defenses and protects against copper-induced DNA 

damage in the blue mussel Mytilus edulis. Aquat. Toxicol. 101(1): 64-71.

Truchot, J.P. and A. Rtal. 1998. Effects of long-term sublethal exposure to copper on subsequent 

uptake and distribution of metal in the shore crab Carcinus maenas. J. Crustac. Biol. 18(2): 224-

231.

Trueman, E.R. and H.B. Akberali. 1981. Responses of an estuarine bivalve, Scrobicularia plana

(Tellinacea) to stress. Malacologia 21(1/2): 15-21.

Tullis, R.E. 1980. Effect of copper on Mytilus californianus and Mytilus edulis. Annual Report. 

Lawrence Livermore Laboratory (Subcontract #3567903). California State University, Hayward, 

CA, Department of Biological Sciences. 33 pp.

Turekian, K.K. 1968. Oceans. Prentice-Hall, Englewood Cliffs, NJ. 120 pp.

Turner, A. 2010. Marine pollution from antifouling paint particles. Mar. Pollut. Bull. 60: 159-

171.

UC Davis. 1997. Copper nutrition of beef cattle. Vet Views, California Cattleman, May 1997. 

Available at: http://www.vetmed.ucdavis.edu/vetext/INF-BE_cca/INF-BE_cca97/INFBE_cca9705.html.
141

Umarani, R., A.K. Kumaraguru and N. Nagarani. 2012. Investigation of acute toxicity of heavy 

metals in Artemia salina acclimated to different salinity. Toxicol. Environ. Chem. 94(8): 1547-

1556.

University of Minnesota. 2009. Extension Fact Sheet: Copper for crop production. WW-06790-

GO. July 2009. Available at:

http://www.extension.umn.edu/distribution/cropsystems/DC6790.html.

Untersee, S. and J.A. Pechenik. 2007. Local adaptation and maternal effects in two species of 

marine gastropod (Genus Crepidula) that differ in dispersal potential. Mar. Ecol. Prog. Ser. 347: 

79-85.

U.S. EPA. 1980. Ambient water quality criteria for copper. U.S. Environmental Protection 

Agency Report 440/5-80-036.162 pp.

U.S. EPA. 1983a. Water quality standards regulation. Federal Regist. 48:51400-51413.

U.S. EPA. 1983b. Water quality standards handbook. Office of Water Regulations and 

Standards, Washington, D.C.

U.S. EPA. 1984. Ambient Water Quality Criteria for Copper - 1984. EPA 440-5-84-031.

U.S. EPA. 1985. Technical support document for water quality-based toxics control. Office of 

Water, Washington, D.C. 

U.S. EPA 1986a. Guidance for the reregistration of pesticide products containing copper sulfate 

as the active ingredient. Office of Pesticides and Toxic Substances. Washington, D.C.

U.S. EPA. 1986b. Quality criteria for water 1986. EPA 440/5-86-001. Office of Water, 

Regulation and Standards, Washington, DC..

U.S. EPA. 1987. Guidance for the reregistration of pesticide products containing group II copper 

compounds as the active ingredient. Office of Pesticides and Toxic Substances. Washington, 

D.C.

U.S. EPA. 1991. Technical support document for water quality-based toxics control. EPA-505/2-

90-001 or PB91-127415. National Technical Information Service, Springfield, VA.

U.S. EPA. 1993. Wildlife Exposure Factors Handbook, 2 vols. EPA/600/R-93/187. Washington, 

D.C.: Office of Research and Development. 

U.S. EPA. 1994a. Water quality standards handbook: 2nd ed. EPA-823-B-94-005a, b. National 

Technical Information Service, Springfield, VA.
142

U.S. EPA. 1994b. Technical document: Acid mine drainage prediction. U.S. Environmental 

Protection Agency, Office of Solid Waste, Special Waste Branch. Washington, DC. EPA 530-R94-036. 

U.S. EPA. 1995a. Ambient water quality criteria - saltwater copper addendum. Draft, April 14, 

1995. EPA 440-5-80-036. U.S. EPA, Environmental Research Laboratory, Narragansett, RI.

U.S. EPA. 1995b. Short-term methods for estimating the chronic toxicity of effluents and 

receiving waters to west coast marine and estuarine organisms. EPA/600/R-95/136.

U.S. EPA. 1996. 1995 Updates: Water quality criteria documents for the protection of aquatic 

life in ambient water. Office of Water. EPA-820-B-96-001. 

U.S. EPA. 1998. Guidelines for ecological risk assessment. United States Environmental 

Protection Agency. Risk Assessment Forum. Office of Research and Development, Washington, 

D.C. EPA/630/R-95/002F.

U.S. EPA. 1999. Integrated Approach to Assessing the Bioavailability and Toxicity of Metals in 

Surface Waters and Sediments, a report to the EPA Science Advisory Board, Office of Water, 

Office of Research and Development, Washington, DC, USEPA-822-E-99-001.

U.S. EPA. 2000. An SAB Report: Review of the Biotic Ligand Model of the Acute Toxicity of 

Metals, prepared by the Ecological Processes and Effects Committee of the Science Advisory 

Board, EPA-SAB-EPEC-00- 0006.

U.S. EPA. 2002. Total maximum daily loads for toxic pollutants, San Diego Creek and Newport 

Bay, California. EPA Region IX. San Francisco, CA.

U.S. EPA. 2003. 2003 Draft update of ambient water quality criteria for copper. Available at: 

http://www.epa.gov/waterscience/criteria/copper/2003/master.pdf.

U.S. EPA. 2004. Overview of the ecological risk assessment process in the Office of Pesticide 

Programs. United States Environmental Protection Agency. Environmental Fate and Effects 

Division. Office of Pesticide Programs. Available online at:

http://www.epa.gov/espp/consultation/ecorisk-overview.pdf.

U.S. EPA. 2007. Aquatic life ambient freshwater quality criteria – Copper. EPA-822-R-07-001.

Available online at: http://www.epa.gov/waterscience /criteria/copper /2007/criteria-full.pdf.

U.S. EPA. 2009. Revised reregistration eligibility decision for coppers. Available at: 

http://www.epa.gov/oppsrrd1/REDs/copper_red_amend.pdf.

U.S. EPA. 2010a. Registration review: Preliminary problem formulation for ecological risk, 

environmental fate, and endangered species assessments for coppers. Office of Chemical Safety 

and Pollution Prevention. Washington, D.C. 105 pp.
143

U.S. EPA. 2010b. Report to Congress: Study of discharges incidental to normal operation of 

commercial fishing vessels and other non-recreational vessels less than 79 feet. Office of Water, 

Washington, D.C. EPA 833-R-10-005. 598 pp. 

U.S. EPA. 2012a. Liquid assets 2000: Americans pay for dirty water. Available at: 

http://water.epa.gov/lawsregs/lawsguidance/cwa/economics/liquidassets/dirtywater.cfm.

U.S. EPA. 2012b. Chromated arsenicals. Available at: https://www.epa.gov/ingredients-usedpesticide-products/chromated-arsenicals-cca

USDHHS (U.S. Department of Health and Human Services). 2004. Toxicological profile for 

copper. Public Health Service. Agency for Toxic Substances and Disease Registry. 272 pp.

Valarmathi, S. and J. Azariah. 2002. Biochemical changes in tissues of crab Sesarma quadratum

(Decapoda) exposed to CuCl2. Indian J. Mar. Sci. 31(3): 246-248.

Valdovinos, C. and M. Zuniga. 2002. Copper acute toxicity tests with the sand crab Emerita 

analoga (Decapoda: Hippidae): A biomonitor of heavy metal pollution in Chilean coastal 

seawater? Bull. Environ. Contam. Toxicol. 69(3): 393-400.

van Leeuwen, C.J., J.L. Buchner and H. van Dijk. 1988. Intermittent flow system for population 

toxicity studies demonstrated with Daphnia and copper. Bull. Environ. Contam. Toxicol. 40(4):

496-502.

Vardy, D.W., A.R. Tompsett, J.L. Sigurdson, J.A. Doering, X.W. Zhang, J.P. Giesy and M. 

Hecker. 2011. Effects of subchronic exposure of early life stages of white sturgeon (Acipenser 

transmontanus) to copper, cadmium, and zinc. Environ. Toxicol. Chem. 30(11): 2497-2505.

Varo, I., B. Nunes, F. Amat, A. Torreblanca, L. Guilhermino and J.C. Navarro. 2007. Effect of 

sublethal concentrations of copper sulphate on seabream Sparus aurata fingerlings. Aquat. Liv. 

Res. 20(3): 263-270.

Varshney, P.K. and S.A.H. Abidi. 1988. Toxicity of mercury, copper and lead in the polychaete 

Namanereis merukensis Horst. Indian J. Mar. Sci. 17: 83-84.

Vasil'eva, V.S., A.A. Zhuchikhina, L.N. Propp and E.P. Sergeeva. 1979. Effect of copper on the 

organism, tissue, and some enzyme systems of the bivalve mollusk Glycymeris yessoensis. Sov. 

J. Mar. Biol. 5(6): 504-510.

Vaz, C., S.P. Melegari, C.H.D. Costa, R. Popovic, T. Kleine, R.F.S. Bohm, T.M.N.D. Oliveira 

and W.G. Matias. 2011a. The effects of copper oxide nanoparticles on Mysidopsis juniae. 

Abstracts of the 47th Congress of the European Societies of Toxicology (EUROTOX). Toxicol. 

Letters 205(Supplement 0): S290.

Vaz, C., S.P. Melegari, C.H.D. Costa, R. Popovic, T. Kleine, R.F.S. Bohm, T.M.N.D. Oliveira 

and W.G. Matias. 2011b. The effects of copper oxide nanoparticles on Mysidopsis juniae. 

Toxicol. Lett. 205S: S290.
144

Vedamanikam, V.J. and T. Hayimad. 2014. Effect of mixtures of metals on the spotted Babylon 

snail (Babylonia areolata) under different temperature conditions. Toxicol. Environ. Chem. 

95(8): 1388-1394.

Venn, A.A., J. Quinn, R. Jones and A. Bodnar. 2009. P-glycoprotein (multi-xenobiotic 

resistance) and heat shock protein gene expression in the reef coral Montastraea franksi in 

response to environmental toxicants. Aquat. Toxicol. 93(4): 188-195.

Viant, M.R., J.H. Walton, P.L. TenBrook and R.S. Tjeerdema. 2002. Sublethal actions of copper 

in abalone (Haliotis rufescens) as characterized by in vivo 31P NMR. Aquat. Toxicol. 57(3): 

139-151.

Viarengo, A., R. Accomando, I. Ferrando, F. Beltrame, M. Fato and G. Marcenaro. 1996. Heavy 

metal effects on cytosolic free Ca2+ level in the marine protozoan Euplotes crassus evaluated by 

confocal laser scanning microscopy. Comp. Biochem. Physiol. C. 113(2): 161-168.

Vieira, L.R., C. Gravato, A.M.V.M. Soares, F. Morgado and L. Guilhermino. 2009. Acute effects 

of copper and mercury on the estuarine fish Pomatoschistus microps: Linking biomarkers to 

behaviour. Chemosphere 76: 1416-1427.

Vijayavel, K., S. Gopalakrishnan, H. Thilagam and M.P. Balasubramanian. 2006. Dietary 

ascorbic acid and alpha-tocopherol mitigates oxidative stress induced by copper in the thornfish 

Terapon jarbua. Sci. Tot. Environ. 372(1): 157-163.

Villar, C.A., S.E. Gomez and C.A. Bentos. 2004. Acute Cu toxicity, metal bioaccumulation and 

ion loss in the neotropical cyprinodontiform Jenynsia multidentata. Rev. Mus. Argent. Cienc. 

Nat. Nueva Ser. 6(1): 191-195.

Virginia Institute of Marine Science (VIMS). 2016. Shallow water habitats. Available online at: 

http://web.vims.edu/bio/shallowwater/physical_characteristics/salinity.html.

Vlahogianni, T.H. and A. Valavanidis. 2007. Heavy-metal effects on lipid peroxidation and 

antioxidant defense enzymes in mussels Mytilus galloprovincialis. Chem. Ecol. 23(5): 361-371.

Vosloo, D., J. Sara, A. Vosloo and D. Vosloo. 2012. Acute responses of brown mussel (Perna 

perna) exposed to sub-lethal copper levels: Integration of physiological and cellular responses. 

Aquat. Toxicol. 106-107: 1-8.

Vranken, G., R. Vanderhaeghen and C. Heip. 1991. Effects of pollutants on life-history of the 

marine nematode Monhystera disjuncta. ICES J. Mar. Sci. 48(3): 325-334.

Waddell, D.C. and M.L. Kraus. 1990. Effects of CuCl2 on the germination responses of two 

populations of the saltmarsh cordgrass, Spartina alterniflora. Bull. Environ. Contam. Toxicol. 

44: 764-769.
145

Wahbeh, M.I. and M.B. Zughul. 1995. Toxicity and accumulation of cadmium, copper and zinc 

in two bivalve species from Aqaba, Jordan. Dirasat Ser. B Pure Appl. Sci. 22(6): 1573-1590.

Wang, B., L. Axe, Z.H. Michalopoulou and L. Wei. 2012. Effects of Cd, Cu, Ni, and Zn on 

brown tide alga Aureococcus anophagefferens growth and metal accumulation. Environ. Sci. 

Technol. 46: 517-524.

Wang, H., Y. Li, H. Huang, X. Xu, Y. Wang and H. Wang. 2011a. Toxicity evaluation of single 

and mixed antifouling biocides using the Strongylocentrotus intermedius sea urchin embryo test. 

Environ. Toxicol. Chem. 30(3): 692-703.

Wang, T., X. Long, Y. Cheng, Z. Liu and S. Yan. 2014. The potential toxicity of copper 

nanoparticles and copper sulphate on juvenile Epinephelus coioides. Aquat. Toxicol. 152: 96-

104.

Wang, W.X. and N.S. Fisher. 1996. Assimilation of trace elements and carbon by the mussel 

Mytilus edulis: Effects of food composition. Limnol. Oceanogr. 41(2): 197-207.

Wang, W.X. and N.S. Fisher. 1998. Accumulation of trace elements in a marine copepod. 

Limnol. Oceanogr. 43(2): 273-283.

Wang, W., K. Mai, W. Zhang, Q. Ai, C. Yao, H. Li and Z. Liufu. 2009. Effects of dietary copper 

on survival, growth and immune response of juvenile abalone, Haliotis discus hannai Ino. 

Aquacult. 297(1-4): 122-127.

Wang, Y., J. Fang, S.S. Leonard and K.M. Rao. 2004. Cadmium inhibits the electron transfer 

chain and induces reactive oxygen species. Free Radic. Biol. Med. 36: 1434-1443.

Wang, Z.S., H.N. Kong and D.Y. Wu. 2007a. Reproductive toxicity of dietary copper to a 

saltwater cladoceran, Moina monogolica Daday. Environ. Toxicol. Chem. 26(1): 126-131.

Wang, Z., H. Kong and D. Wu. 2007b. Acute and chronic copper toxicity to a saltwater 

cladoceran Moina monogolica Daday. Arch. Environ. Contam. Toxicol. 53(1): 50-56.

Wang, Z.H., X.N. Wang and Q. Lin. 2011b. The content variation characteristics and risk 

analysis for cadmium, copper, lead and zinc in some species of shellfish. J. Agro-Environ. Sci. 

30(6): 1208-1213.

Ward, D.J., V. Perez-Landa, D.A. Spadaro, S.L. Simpson and D.F. Jolley. 2011. An assessment 

of three harpacticoid copepod species for use in ecotoxicological testing. Arch. Environ. Contam. 

Toxicol. 61(3): 414-425.

Warnau, M., M. Iaccarino, A. DeBiase, A. Temara, M. Jangoux, P. Dubois and G. Pagano. 1996. 

Spermiotoxicity and embryotoxicity of heavy metals in the echinoid Paracentrotus lividus. 

Environ. Toxicol. Chem. 15(11): 1931-1936.
146

Waterman, A.J. 1937. Effect of salts of heavy metals on development of the sea urchin, Arbacia 

punctulata. Biol. Bull. 73(3): 401-420.

Watling, H. 1981. The effects of metals on mollusc filtering rates. Trans. R. Soc. S. Afr. 44(3): 

441-451.

Wei, L., B. Wang, R. Kang, R. Huo and V. Randhawa. 2013. Aureococcus anophagefferens

growth potential affected by coastal water toxicants. J. Appl. Phycol. 25(1): 145-152.

Wendt, I., A. Arrhenius, T. Backhaus, A. Hilvarsson, K. Holm, K. Langford, T. Tunovic and H. 

Blanck. 2013. Effects of five antifouling biocides on settlement and growth of zoospores from 

the marine macroalga Ulva lactuca L. Bull. Environ. Contam. Toxicol. 91: 426-432.

WHOI (Woods Hole Oceanographic Institution). 1952. Marine fouling and its prevention. 

Contribution No. 580. Woods Hole Oceanographic Institution. United States Naval Institute, 

Annapolis, MD.

Williams, P.L. and D.B. Dusenbery. 1990. Aquatic toxicity testing using the nematode, 

Caenorhabditis elegans. Environ. Toxicol. Chem. 9(10): 1285-1290.

Wilson, R.W. and E.W. Taylor. 1993. Differential responses to copper in rainbow trout 

(Oncorhynchus mykiss) acclimated to sea water and brackish water. J. Comp. Physiol. B. 163: 

239-246.

Winner, R.W. 1985. Bioaccumulation and toxicity of copper as affected by interactions between 

humic acid and water hardness. Water Res. 19(4): 449-455.

Won, E.J., J.S. Rhee, R.O. Kim, K. Ra, K.T. Kim, K.H. Shin and J.S. Lee. 2012. Susceptibility to 

oxidative stress and modulated expression of antioxidant genes in the copper-exposed polychaete 

Perinereis nuntia. Comp. Biochem. Physiol. Part C Toxicol. Pharmacol. 155(2): 344-351.

Wong, V.W.T. and P.S. Rainbow. 1986. Apparent and real variability in the presence and metal 

contents of metallothioneins in the crab Carcinus maenas including the effects of isolation 

procedure and metal induction. Comp. Biochem. Physiol. 83A(1): 157-177.

Wood, C.M., A.P. Farrell and C.J. Brauner. 2012. Homeostatis and toxicology of essential 

metals: Volume 31A. Fish Physiology, Academic Press/Elsevier, Waltham, MA.

Worboys, M.A., K.M.Y. Leung, E.P.M. Grist and M. Crane. 2002. Time should be considered in 

developmental ecotoxicity test. Mar. Pollut. Bull. 45: 92-99.

Wright, D.A. and C.D. Zamuda. 1987. Copper accumulation by two bivalve molluscs: Salinity 

effect is independent of cupric ion activity. Mar. Environ. Res. 23(1): 1-14.

Wu, H. and W.X. Wang. 2010. NMR-based metabolomic studies on the toxicological effects of 

cadmium and copper on green mussels Perna viridis. Aquat. Toxicol. 100(4): 339-345.
147

Xie, Z.C., N.C. Wong, P.Y. Qian and J.W. Qiu. 2005. Responses of polychaete Hydroides 

elegans life stages to copper stress. Mar. Ecol. Prog. Series 285: 89-96.

Xu, J. and T. Jing. 1995. Effects of temperature, salinity, copper and ammonia on prawn 

(Penaeus orientalis kishinouye) postlarvae and clams (Potamocorbula laevis). In: M. Munawar 

(Ed.), Ecovision World Monogr. Ser., Aquatic Ecosystems of China: Environmental and 

Toxicological Assessment, SPB Acad. Publ., The Hague, Netherlands, pp. 89-94.

Xu, X., X. Wang, Y. Li, Y. Wang and Y. Wang. 2010. Acute toxicity and synergism of binary 

mixtures of antifouling biocides with heavy metals to embryos of sea urchin Glyptocidaris 

crenularis. Human Exper. Toxicol. 30(8): 1009-1021.

Xu, X., Y. Li, Y. Wang, Y. Wang and X. Xu. 2011. Assessment of toxic interactions of heavy 

metals in multi-component mixtures using sea urchin embryo-larval bioassay. Toxicol. In Vitro. 

25(1): 294-300. 

Yaffe, P.L. 1979. Examination of the effects of 50 ppb copper on the black abalone, Haliotis 

cracherodii. Lawrence Livermore Laboratory, University of California, Livermore, CA: 47 p.

Yang, D., Y. Zhou, H. Zhao, X. Zhou, Na Sun, B. Wang and X. Yuan. 2012. Molecular cloning, 

sequencing, and expression analysis of cDNA encoding metalloprotein II (MP II) induced by 

single and combined metals (Cu(II), Cd (II)) in polychaeta Perinereis aibuhitensis. Environ. 

Toxicol. Pharmacol. 34: 841-848.

Young, J.S. 1982. Toxic and adaptive response to copper by the sabellid polychaete, Eudistylia 

vancouveri. In: W.B. Vernberg, A. Calabrese, F.P. Thurberg and F.J. Vernberg (Eds.), 

Physiological Mechanisms of Marine Pollutant Toxicity, Academic Press, Inc., NY. pp. 53-73.

Young, J.S., J.M. Gurtisen, C.W. Apts and E.A. Crecelius. 1979. The relationship between the 

copper complexing capacity of sea water and copper toxicity in shrimp zoeae. Mar. Environ. 

Res. 2: 265-273.

Young, L.G. and L. Nelson. 1974. The effects of heavy metal ions on the motility of sea urchin 

spermatozoa. Biol. Bull. 147(1): 236-246.

Ytreberg, E., J. Karlsson and B. Eklund. 2010. Comparison of toxicity and release rates of Cu 

and Zn from anti-fouling paints leached in natural and artificial brackish seawater. Sci. Total 

Environ. 408(12): 2459-2466.

Zang, W., X. Xu, X. Dai, Z. Zhu, G. Xu and R. Xu. 1993. Toxic effects of Zn2+, Cu2+, Cd2+ 

and NH3 on Chinese prawn. Chin. J. Oceanol. Limnol. 11(3): 254-259.

Zapata, V., L.L. Greco and E.M. Rodriguez. 2001. Effect of copper on hatching and 

development of larvae of the estuarine crab Chasmagnathus granulata (Decapoda, Brachyura). 

Environ. Toxicol. Chem. 20(7): 1579-1583.
148

Zaroogian, G.E. and M. Johnson. 1983. Copper accumulation in the bay scallop, Argopecten 

irradians. Arch. Environ. Contam. Toxicol. 12: 127-133.

Zhang, L., J. Gan, C. Ke, X. Liu, J. Zhao, L. You, J. Yu and H. Wu. 2012. Identification and 

expression profile of a new cytochrome P450 isoform (CYP414A1) in the hepatopancreas of 

Venerupis (Ruditapes) philippinarum exposed to benzo[a]pyrene cadmium and copper. Environ. 

Toxicol. Pharmacol. 33: 85-91.

Zhang, Z. and Q. Zhang. 2012. Molecular cloning, characterization and expression of heat shock 

protein 70 gene from the oyster Crassostrea hongkongensis responding to thermal stress and 

exposure of Cu2+ and malachite green. Gene 497(2): 172-180.

Zheng, G., Y. Wang and J. Qin. 2012. Microalgal motility measurement microfluidic chip for 

toxicity assessment of heavy metals. Anal. Bioanal. Chem. 404: 3061-3069.

Zhu, X., D. Zou and H. Du. 2011. Physiological responses of Hizikia fusiformis to copper and 

cadmium exposure. Bot. Mar. 54(5): 431-439.

Zimmer, A.M., I.F. Barcarolli, C.M. Wood and A. Bianchini. 2012. Waterborne copper exposure 

inhibits ammonia excretion and branchial carbonic anhydrase activity in euryhaline guppies 

acclimated to both fresh water and sea water. Aquat. Toxicol. 122-123: 172-180.

Zitko, P., V.W. Carson and W.G. Carson. 1973. Prediction of incipient lethal levels of copper to 

juvenile Atlantic salmon in the presence of humic acid by cupric electrode. Bull. Environ. 

Contam. Toxicol. 10(5): 265-271.

Zizza, M., M. Canonaco and R.M. Facciolo. 2014. ORX neuroreceptor system and HSP90 are 

linked to recovery strategies against copper toxicity in Thalassoma pavo. Toxicol. Sci. 137(1): 

135-146.

Zuniga, M., P. Vallejos, A. Larrain and E. Bay-Schmith. 2003. Toxicity of copper on four 

Chilean marine mussels. Bull. Environ. Contam. Toxicol. 71(6): 1167-1174.
A-1

Appendix A Acceptable Estuarine/Marine Acute Toxicity Data
A-2

Appendix Table A-1. Acceptable Estuarine/Marine Acute Toxicity Data.

Species

Organism 

Age, Size or 

Lifestage Methoda Chemicalb

Reported 

LC50/EC50

(total μg/L)c

Reported

LC50/EC50

(dissolved μg/L)d

BLM 

Data 

Label

BLM 

Normalized 

LC50/EC50

(μg/L)e

Species 

Mean Acute 

Value 

(μg/L)f Reference

Sea anemone,

Aiptasia pallida - R, M N 148 134.5 12 72.63 72.63 Main et al. 2010

Rotifer,

Brachionus plicatilis

Neonate, 

0-3 hr S, M N - 13.4 50 16.55 - Arnold et al. 2010b

Rotifer,

Brachionus plicatilis

Neonate, 

0-3 hr S, M N - 20.8 51 26.58 - Arnold et al. 2010b

Rotifer,

Brachionus plicatilis Neonate, <4hr S, M N - <12.80 53 <34.12 - Arnold et al. 2010c

Rotifer,

Brachionus plicatilis Neonate, <4hr S, M N - <12.60 54 <31.66 - Arnold et al. 2010c

Rotifer,

Brachionus plicatilis Neonate, <4hr S, M N - <12.90 55 <29.67 - Arnold et al. 2010c

Rotifer,

Brachionus plicatilis Neonate, <4hr S, M N - <12.50 56 <26.19 - Arnold et al. 2010c

Rotifer,

Brachionus plicatilis Neonate, <4hr S, M N - 10.1 57 20.41 - Arnold et al. 2010c

Rotifer,

Brachionus plicatilis Neonate, <4hr S, M N - 119.1 58 57.15 - Arnold et al. 2010c

Rotifer,

Brachionus plicatilis Neonate, <4hr S, M N - 173.4 59 54.09 - Arnold et al. 2010c

Rotifer,

Brachionus plicatilis Neonate, <4hr S, M N - 80.7 60 58.41 - Arnold et al. 2010c

Rotifer,

Brachionus plicatilis Neonate, <4hr S, M N - 45.5 61 30.52 - Arnold et al. 2010c

Rotifer,

Brachionus plicatilis

Neonate, 

0-2 hr S, M - - 27.7 745 62.17 - Saunders 2012

Rotifer,

Brachionus plicatilis

Neonate, 

0-2 hr S, M - - 23.3 746 29.42 - Saunders 2012

Rotifer,

Brachionus plicatilis

Neonate, 

0-2 hr S, M - - 11.2 747 8.347 - Saunders 2012

Rotifer,

Brachionus plicatilis

Neonate, 

0-2 hr S, M - - 19.7 748 31.19 - Saunders 2012

Rotifer,

Brachionus plicatilis

Neonate, 

0-2 hr S, M - - 46.8 749 17.47 - Saunders 2012

Rotifer,

Brachionus plicatilis

Neonate, 

0-2 hr S, M - - 48.9 750 8.115 - Saunders 2012
A-3

Species

Organism 

Age, Size or 

Lifestage Methoda Chemicalb

Reported 

LC50/EC50

(total μg/L)c

Reported

LC50/EC50

(dissolved μg/L)d

BLM 

Data 

Label

BLM 

Normalized 

LC50/EC50

(μg/L)e

Species 

Mean Acute 

Value 

(μg/L)f Reference

Rotifer,

Brachionus plicatilis

Newly 

hatched, <6 hr S, M S 42.07 38.24 760 8.034 - Tait 2013

Rotifer,

Brachionus plicatilis

Newly 

hatched, <6 hr S, M S 49.44 44.94 761 21.89 - Tait 2013

Rotifer,

Brachionus plicatilis

Newly 

hatched, <6 hr S, M S 62.28 56.61 762 7.599 - Tait 2013

Rotifer,

Brachionus plicatilis

Newly 

hatched, <6 hr S, M S 46.07 41.88 763 8.182 - Tait 2013

Rotifer,

Brachionus plicatilis

Newly 

hatched, <6 hr S, M S 25.1 22.82 764 16.92 - Tait 2013

Rotifer,

Brachionus plicatilis

Newly 

hatched, <6 hr S, M S 21.16 19.23 765 15.25 - Tait 2013

Rotifer,

Brachionus plicatilis

Newly 

hatched, <6 hr S, M S 58.15 52.86 766 26.75 - Tait 2013

Rotifer,

Brachionus plicatilis

Newly 

hatched, <6 hr S, M S 26.82 24.38 767 43.03 - Tait 2013

Rotifer,

Brachionus plicatilis

Newly 

hatched, <6 hr S, M S 35.52 32.29 768 29.01 23.03 Tait 2013

Polychaete,

Anaitides maculata - S, U S 120 100.6 505 53.80 53.80 McLusky and Phillips 1975

Polychaete,

Eurythoe complanata

Immature, 

1.0 g S, U - 1,300 1,089 170 1,675 1,675 Marcano et al. 1996

Polychaete,

Hediste (Nereis) diversicolor - S, U S 200 167.6 193 125.3 - Jones et al. 1976

Polychaete,

Hediste (Nereis) diversicolor - S, U S 445 372.9 194 792.4 - Jones et al. 1976

Polychaete,

Hediste (Nereis) diversicolor - S, U S 480 402.2 195 726.9 - Jones et al. 1976

Polychaete,

Hediste (Nereis) diversicolor - S, U S 410 343.6 196 403.9 - Jones et al. 1976

Polychaete,

Hediste (Nereis) diversicolor Juvenile R, U N 357 299.2 197 505.9 - Ozoh 1992a

Polychaete,

Hediste (Nereis) diversicolor Juvenile R, U N 357 299.2 198 475.6 - Ozoh 1992a

Polychaete,

Hediste (Nereis) diversicolor Juvenile R, U N 247 207.0 199 177.4 - Ozoh 1992a
A

-4

Species

Organism 

Age, Size or 

Lifestage Method

a Chemicalb

Reported 

LC50/EC50

(total μg/L)

c

Reported

LC50/EC50

(dissolved μg/L)

d

BLM 

Data 

Label

BLM 

Normalized 

LC50/EC50

(μg/L)

e

Species 

Mean Acute 

Value 

(μg/L)

f Reference

Polychaete,

Hediste (Nereis) diversicolor Juvenile R, U

N 307 257.3 200 279.7- Ozoh 1992a

Polychaete,

Hediste (Nereis) diversicolor Juvenile R, U

N 400 335.2 201 485.9- Ozoh 1992a

Polychaete,

Hediste (Nereis) diversicolor Juvenile R, U

N 462 387.2 202 597.2- Ozoh 1992a

Polychaete,

Hediste (Nereis) diversicolor Juvenile R, U

N 375 314.3 203 386.0- Ozoh 1992a

Polychaete,

Hediste (Nereis) diversicolor Juvenile R, U

N 362 303.4 204 340.1- Ozoh 1992a

Polychaete,

Hediste (Nereis) diversicolor Juvenile R, U

N 480 402.2 205 539.9- Ozoh 1992a

Polychaete,

Hediste (Nereis) diversicolor Juvenile R, U

N 512 429.1 206 602.1- Ozoh 1992a

Polychaete,

Hediste (Nereis) diversicolor Juvenile R, U

N 360 301.7 207 302.0- Ozoh 1992a

Polychaete,

Hediste (Nereis) diversicolor Juvenile R, U

N 500 419.0 208 508.2- Ozoh 1992a

Polychaete,

Hediste (Nereis) diversicolor Adult R, U

N 402 336.9 209 660.1- Ozoh 1992b

Polychaete,

Hediste (Nereis) diversicolor Adult R, U

N 724 606.7 210 1,718- Ozoh 1992b

Polychaete,

Hediste (Nereis) diversicolor Adult R, U

N 339 284.1 211 389.5- Ozoh 1992b

Polychaete,

Hediste (Nereis) diversicolor Adult R, U

N 776 650.3 212 1,533- Ozoh 1992b

Polychaete,

Hediste (Nereis) diversicolor Adult R, U

N 723 605.9 213 1,286- Ozoh 1992b

Polychaete,

Hediste (Nereis) diversicolor Adult R, U

N 725 607.6 214 1,192- Ozoh 1992b

Polychaete,

Hediste (Nereis) diversicolor Adult R, U

N 900 754.2 215 1,539- Ozoh 1992b

Polychaete,

Hediste (Nereis) diversicolor Adult R, U

N 754 631.9 216 1,127- Ozoh 1992b

Polychaete,

Hediste (Nereis) diversicolor Adult R, U

N 870 729.1 217 1,262- Ozoh 1992b

Polychaete,

Hediste (Nereis) diversicolor Adult R, U

N 890 745.8 218 1,302- Ozoh 1992b

Polychaete,

Hediste (Nereis) diversicolor Adult R, U

N 763 639.4 219 988.6- Ozoh 1992b
A-5

Species

Organism 

Age, Size or 

Lifestage Methoda Chemicalb

Reported 

LC50/EC50

(total μg/L)c

Reported

LC50/EC50

(dissolved μg/L)d

BLM 

Data 

Label

BLM 

Normalized 

LC50/EC50

(μg/L)e

Species 

Mean Acute 

Value 

(μg/L)f Reference

Polychaete,

Hediste (Nereis) diversicolor Adult R, U N 825 691.4 220 1,016 - Ozoh 1992b

Polychaete,

Hediste (Nereis) diversicolor - R, U - 921.5 772.2 221 569.7 623.4 Mouneyrac et al. 2003

Polychaete,

Neanthes arenaceodentata Adult F, M N 77 69.99 469 50.01 -

Pesch and Morgan 

1978

Polychaete,

Neanthes arenaceodentata Adult F, M N 200 181.8 470 158.3 -

Pesch and Morgan 

1978

Polychaete,

Neanthes arenaceodentata - F, M N 222 201.8 472 181.1 112.8 Pesch and Hoffman 1982

Polychaete,

Hydroides elegans Larva R, U S 100 83.8 230 87.98 87.98 Bao et al. 2011

Black abalone,

Haliotis cracherodii Adult R, U S 50 41.9 187 21.24 21.24 Martin et al. 1977

Red abalone,

Haliotis rufescens Adult R, U S 65 54.47 189 27.77g

- Martin et al. 1977

Red abalone,

Haliotis rufescens Larva S, U S 114 95.53 190 49.87g

- Martin et al. 1977

Red abalone,

Haliotis rufescens Embryo S, M C 8.8 8 191 3.944 3.944 Hunt et al. 1989

Whelk,

Turbo coronatus

2.36 cm, 

7.42 g R, U S 3,790 3,176 577 1,416 1,416 Kidwai and Ahmed 1999

Gastropod,

Crepidula convexa Juvenile R, U C 325 272.4 114 1,105 1,105 Untersee and Pechenik 2007

Gastropod,

Crepidula fornicata Larva R, U C 636.3 533.2 116 2,141 2,141 Untersee and Pechenik 2007

Grooved snail,

Planaxis sulcatus

1.92 cm, 

1.38 g R, U S 1,010 846.38 507 1,089 1,089 Kidwai and Ahmed 1999

Blue mussel,

Mytilus edulis

Juvenile, 

15.8 mm R, U C 122 - 333 72.69g

- Nelson et al. 1988
A

-6

Species

Organism 

Age, Size or 

Lifestage Method

a Chemicalb

Reported 

LC50/EC50

(total μg/L)

c

Reported

LC50/EC50

(dissolved μg/L)

d

BLM 

Data 

Label

BLM 

Normalized 

LC50/EC50

(μg/L)

e

Species 

Mean Acute 

Value 

(μg/L)

f Reference

Blue mussel,

Mytilus edulis Embryo S, U

S 5.8 4.86 331 2.445- Martin et al. 1981

Blue mussel,

Mytilus edulis Embryo S, M

S 8.92 8.11 334 4.181- TOXSCAN, Inc. 1991a

Blue mussel,

Mytilus edulis Embryo S, M

S 8.19 7.44 335 3.851- TOXSCAN, Inc. 1991b

Blue mussel,

Mytilus edulis Embryo S, M

S 8.29 7.54 336 3.843- TOXSCAN, Inc. 1991c

Blue mussel,

Mytilus edulis Embryo R, M

S 13.1 12.5 337 8.719-

Science Applications 

International 

Corporation 1993

Blue mussel,

Mytilus edulis Embryo R, M

S 14.1 14.1 338 10.40-

Science Applications 

International 

Corporation 1993

Blue mussel,

Mytilus edulis Embryo R, M

S 12.2 11.3 339 7.863-

Science Applications 

International 

Corporation 1993

Blue mussel,

Mytilus edulis Embryo R, M

S 12.8 11.9 340 8.265-

Science Applications 

International 

Corporation 1993

Blue mussel,

Mytilus edulis Embryo S, M

S 7.16 5.95 341 3.524- City of San Jose 1998

Blue mussel,

Mytilus edulis Embryo S, M

S 5.85 5.21 342 3.059- City of San Jose 1998

Blue mussel,

Mytilus edulis Embryo S, M

S 5.03 5.05 343 3.022- City of San Jose 1998

Blue mussel,

Mytilus edulis Embryo S, M

S 3.82 3.75 344 2.230- City of San Jose 1998

Blue mussel,

Mytilus edulis Embryo S, M

S 5.86 5.45 345 3.204- City of San Jose 1998

Blue mussel,

Mytilus edulis Embryo S, M

S 4.7 3.8 346 2.241- City of San Jose 1998

Blue mussel,

Mytilus edulis Embryo S, M

S 6.42 4.97 347 2.949- City of San Jose 1998

Blue mussel,

Mytilus edulis Embryo S, M

S 6.22 5.72 348 3.355- City of San Jose 1998

Blue mussel,

Mytilus edulis Embryo S, M

S 6.21 5.84 349 3.423- City of San Jose 1998

Blue mussel,

Mytilus edulis Embryo S, M

S 5.87 5.44 350 3.187- City of San Jose 1998
A

-7

Species

Organism 

Age, Size or 

Lifestage Method

a Chemicalb

Reported 

LC50/EC50

(total μg/L)

c

Reported

LC50/EC50

(dissolved μg/L)

d

BLM 

Data 

Label

BLM 

Normalized 

LC50/EC50

(μg/L)

e

Species 

Mean Acute 

Value 

(μg/L)

f Reference

Blue mussel,

Mytilus edulis Embryo S, M

S 5.4 4.75 351 2.797- City of San Jose 1998

Blue mussel,

Mytilus edulis Embryo S, M

S6 5.1 352 3.053- City of San Jose 1998

Blue mussel,

Mytilus edulis Embryo S, M

S 9.05 8.3 353 4.912- City of San Jose 1998

Blue mussel,

Mytilus edulis Embryo S, M

S 6.92 5.34 354 3.138- City of San Jose 1998

Blue mussel,

Mytilus edulis Embryo S, M

S 7.19 5.02 355 2.946- City of San Jose 1998

Blue mussel,

Mytilus edulis Embryo S, M

S 5.56 4.39 356 2.548- City of San Jose 1998

Blue mussel,

Mytilus edulis Embryo S, M

S 8.48 7.5 357 4.434- City of San Jose 1998

Blue mussel,

Mytilus edulis Embryo S, M

S 7.36 6.79 358 3.995- City of San Jose 1998

Blue mussel,

Mytilus edulis Embryo S, M

S 7.85 5.29 359 3.090- City of San Jose 1998

Blue mussel,

Mytilus edulis Embryo S, M

S 8.02 6.82 360 3.989- City of San Jose 1998

Blue mussel,

Mytilus edulis Embryo S, M

S 9.5 7.81 361 4.649- City of San Jose 1998

Blue mussel,

Mytilus edulis Embryo S, M

S 7.29 5.59 362 3.270- City of San Jose 1998

Blue mussel,

Mytilus edulis Embryo S, M

S 8.93 6.35 363 3.792- City of San Jose 1998

Blue mussel,

Mytilus edulis Embryo S, M

S 4.54 3.94 364 2.316- City of San Jose 1998

Blue mussel,

Mytilus edulis Embryo S, M

S 4.73 3.9 365 2.315- City of San Jose 1998

Blue mussel,

Mytilus edulis Embryo S, M

N- 3.52 369 7.142- Arnold et al. 2008

Blue mussel,

Mytilus edulis Embryo S, M

N- 4.66 370 5.259- Arnold et al. 2008

Blue mussel,

Mytilus edulis Embryo S, M

N- 21.6 371 4.284- Arnold et al. 2008

Blue mussel,

Mytilus edulis Embryo S, M

N- 25.2 372 4.907- Arnold et al. 2008

Blue mussel,

Mytilus edulis Embryo S, M

N- 8.03 373 4.057- Arnold et al. 2008
A

-8

Species

Organism 

Age, Size or 

Lifestage Method

a Chemicalb

Reported 

LC50/EC50

(total μg/L)

c

Reported

LC50/EC50

(dissolved μg/L)

d

BLM 

Data 

Label

BLM 

Normalized 

LC50/EC50

(μg/L)

e

Species 

Mean Acute 

Value 

(μg/L)

f Reference

Blue mussel,

Mytilus edulis Embryo S, M

N- 9.9 374 4.552- Arnold et al. 2008

Blue mussel,

Mytilus edulis Embryo S, M

N- 14 375 4.048- Arnold et al. 2008

Blue mussel,

Mytilus edulis Embryo S, M

N- 17.5 376 4.665- Arnold et al. 2008

Blue mussel,

Mytilus edulis

Embryo, 4 hr 

post fert S, M

S 17.46 17.83 366 13.350- CH2M Hill 1999b

Blue mussel,

Mytilus edulis

Embryo, 4 hr 

post fert S, M

S 22.81 21.35 367 16.11- CH2M Hill 1999b

Blue mussel,

Mytilus edulis

Embryo, 4 hr 

post fert S, M

S 27.37 26.1 368 19.88 4.238 CH2M Hill 1999b

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 8.3 380 5.606- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 8.1 381 5.471- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 9.5 382 15.94- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

--6 383 10.08- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 6.9 384 6.984- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 7.1 385 5.993- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 9.4 386 4.761- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 6.8 387 22.14- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 12.4 388 17.88- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 21.7 389 8.459- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 25 390 7.919- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 19.1 391 8.415- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 21.3 392 21.65- Arnold 2005
A

-9

Species

Organism 

Age, Size or 

Lifestage Method

a Chemicalb

Reported 

LC50/EC50

(total μg/L)

c

Reported

LC50/EC50

(dissolved μg/L)

d

BLM 

Data 

Label

BLM 

Normalized 

LC50/EC50

(μg/L)

e

Species 

Mean Acute 

Value 

(μg/L)

f Reference

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 19.4 393 13.13- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 19.3 394 9.315- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 18.9 395 8.705- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 17 396 17.25- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 20.1 397 10.19- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 27.8 398 8.809- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 17.3 399 6.740- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 16.3 400 4.713- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 19.4 401 4.266- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 30.9 402 9.499- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 19.6 403 8.275- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 14.7 404 14.90- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 20.3 405 13.75- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 20.7 406 9.538- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 16.8 407 8.958- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 16.4 408 16.64- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 17.8 409 12.04- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 15.3 410 9.116- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 16.9 411 10.07- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 12.4 412 12.55- Arnold 2005
A

-10

Species

Organism 

Age, Size or 

Lifestage Method

a Chemicalb

Reported 

LC50/EC50

(total μg/L)

c

Reported

LC50/EC50

(dissolved μg/L)

d

BLM 

Data 

Label

BLM 

Normalized 

LC50/EC50

(μg/L)

e

Species 

Mean Acute 

Value 

(μg/L)

f Reference

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 18.2 413 8.782- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 24.2 414 5.001- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 13.8 415 6.655- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 14.5 416 8.158- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 16.7 417 11.29- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 24.8 418 3.085- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 20.1 419 7.274- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 19.2 420 9.731- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 22.4 421 7.567- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 50.5 422 5.686- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 23.3 423 5.901- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 22.7 424 10.01- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 14.2 425 8.459- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 30.3 426 6.397- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 16.5 427 7.597- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 21.1 428 8.224- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 14.5 429 6.385- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 23.4 430 5.266- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 18.4 431 7.457- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 19.7 432 9.075- Arnold 2005
A

-11

Species

Organism 

Age, Size or 

Lifestage Method

a Chemicalb

Reported 

LC50/EC50

(total μg/L)

c

Reported

LC50/EC50

(dissolved μg/L)

d

BLM 

Data 

Label

BLM 

Normalized 

LC50/EC50

(μg/L)

e

Species 

Mean Acute 

Value 

(μg/L)

f Reference

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 21.1 433 12.60- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 33.3 434 3.502- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 21.3 435 7.443- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 14 436 7.089- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 30.2 437 3.043- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 11.1 438 3.501- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 14.8 439 10.72- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 13 440 11.98- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 71 441 8.327- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 24.8 442 7.663- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 17.1 443 11.57- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 16.6 444 12.03- Arnold 2005

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 52.9 295 10.60- Arnold et al. 2006

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 59.4 296 7.044- Arnold et al. 2006

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 47.9 297 5.029- Arnold et al. 2006

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 48.2 298 10.26- Arnold et al. 2006

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 54 299 8.348- Arnold et al. 2006

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 47.8 300 4.867- Arnold et al. 2006

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 19.6 301 13.37- Arnold et al. 2006

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 34.4 302 4.797- Arnold et al. 2006
A

-12

Species

Organism 

Age, Size or 

Lifestage Method

a Chemicalb

Reported 

LC50/EC50

(total μg/L)

c

Reported

LC50/EC50

(dissolved μg/L)

d

BLM 

Data 

Label

BLM 

Normalized 

LC50/EC50

(μg/L)

e

Species 

Mean Acute 

Value 

(μg/L)

f Reference

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 56.8 303 5.261- Arnold et al. 2006

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 15.9 304 11.60- Arnold et al. 2006

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 33.8 305 5.555- Arnold et al. 2006

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 20 306 10.21- Arnold et al. 2006

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 22.5 307 4.874- Arnold et al. 2006

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 54.4 308 4.614- Arnold et al. 2006

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 14.7 309 8.814- Arnold et al. 2006

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 16.1 310 4.820- Arnold et al. 2006

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 41.6 311 4.273- Arnold et al. 2006

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 11.8 312 11.95- Arnold et al. 2006

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 11.7 313 9.874- Arnold et al. 2006

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 12.3 314 4.296- Arnold et al. 2006

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

-- 14.1 315 4.464- Arnold et al. 2006

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

N- 9.7 316 1.614- Arnold et al. 2007

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

N- 8.6 317 21.80- Arnold et al. 2007

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

N- 7.5 318 58.07- Arnold et al. 2007

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

N- 5.13 446 7.443- Arnold et al. 2008

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

N- 3.56 447 3.602- Arnold et al. 2008

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

N- 30.6 448 6.329- Arnold et al. 2008

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

N- 21.7 449 3.847- Arnold et al. 2008
A

-13

Species

Organism 

Age, Size or 

Lifestage Method

a Chemicalb

Reported 

LC50/EC50

(total μg/L)

c

Reported

LC50/EC50

(dissolved μg/L)

d

BLM 

Data 

Label

BLM 

Normalized 

LC50/EC50

(μg/L)

e

Species 

Mean Acute 

Value 

(μg/L)

f Reference

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

N- 12.2 450 6.503- Arnold et al. 2008

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

N- 6.91 451 3.164- Arnold et al. 2008

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

N- 20.2 452 6.206- Arnold et al. 2008

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

N- 11.5 453 3.053- Arnold et al. 2008

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

S- 6.36 454 4.824- Rosen et al. 2008

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

S- 8.68 455 5.051- Rosen et al. 2008

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

N- 6.28 456 8.040- Arnold et al. 2010a

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

N- 14.4 457 5.646- Arnold et al. 2010a

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

N- 28.2 458 7.341- Arnold et al. 2010a

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

N- 34.8 459 6.205- Arnold et al. 2010a

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

N- 10.9 460 9.118- Arnold et al. 2010a

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

N- 21 461 10.06- Arnold et al. 2010a

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

N- 31.6 462 9.065- Arnold et al. 2010a

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

N- 37.2 463 7.459- Arnold et al. 2010a

Mediterranean mussel,

Mytilus galloprovincialis Embryo, 4 cell S, M

N- 12.66 319 11.87- DePalma et al. 2011

Mediterranean mussel,

Mytilus galloprovincialis Embryo, 4 cell S, M

N- 22.72 320 6.452- DePalma et al. 2011

Mediterranean mussel,

Mytilus galloprovincialis Embryo, 4 cell S, M

N- 19.01 321 8.304- DePalma et al. 2011

Mediterranean mussel,

Mytilus galloprovincialis Embryo, 4 cell S, M

N- 20.67 322 6.237- DePalma et al. 2011

Mediterranean mussel,

Mytilus galloprovincialis Embryo, 4 cell S, M

N- 16.04 323 9.176- DePalma et al. 2011

Mediterranean mussel,

Mytilus galloprovincialis Embryo, 4 cell S, M

N- 20.45 324 6.781- DePalma et al. 2011
A

-14

Species

Organism 

Age, Size or 

Lifestage Method

a Chemicalb

Reported 

LC50/EC50

(total μg/L)

c

Reported

LC50/EC50

(dissolved μg/L)

d

BLM 

Data 

Label

BLM 

Normalized 

LC50/EC50

(μg/L)

e

Species 

Mean Acute 

Value 

(μg/L)

f Reference

Mediterranean mussel,

Mytilus galloprovincialis Embryo, 4 cell S, M

N- 31.58 325 4.646- DePalma et al. 2011

Mediterranean mussel,

Mytilus galloprovincialis Embryo, 4 cell S, M

N- 30.96 326 9.895- DePalma et al. 2011

Mediterranean mussel,

Mytilus galloprovincialis Embryo, 4 cell S, M

N- 15.96 327 10.27- DePalma et al. 2011

Mediterranean mussel,

Mytilus galloprovincialis Embryo, 4 cell S, M

N- 31.19 328 4.748- DePalma et al. 2011

Mediterranean mussel,

Mytilus galloprovincialis 20

-39 mm S, US 1,670 1,399 730 2,285

g

- Bat et al. 2013

Mediterranean mussel,

Mytilus galloprovincialis 40

-59 mm S, US 1,450 1,215 731 1,946

g

- Bat et al. 2013

Mediterranean mussel,

Mytilus galloprovincialis 60

-79 mm S, US 1,180 988.8 732 1,529

g

- Bat et al. 2013

Mediterranean mussel,

Mytilus galloprovincialis 50

-80 mm S, US 800.0 670.4 733 944.8

g

- Bat et al. 2013

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

C- 8.9 769 4.345- Fabbri et al. 2014

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

C- 8.7 770 4.258- Fabbri et al. 2014

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

C- 12.2 752 4.321- Deruytter et al. 2015

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

C- 10.1 753 8.568- Deruytter et al. 2015

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

C- 13.4 754 3.556- Deruytter et al. 2015

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

C- 4.1 755 7.452- Deruytter et al. 2015

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

C- 13.6 756 2.946- Deruytter et al. 2015

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

C- 10.3 757 3.734- Deruytter et al. 2015

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

C- 11.0 758 3.990- Deruytter et al. 2015

Mediterranean mussel,

Mytilus galloprovincialis Embryo S, M

C- 5.0 759 3.385 7.338 Deruytter et al. 2015

Asian green mussel,

Perna viridis

Juvenile, 

1.6 cm, 0.12 g R, M

C- 500.0 771 646.9 646.9 Rajkumar 2012
A

-15

Species

Organism 

Age, Size or 

Lifestage Method

a Chemicalb

Reported 

LC50/EC50

(total μg/L)

c

Reported

LC50/EC50

(dissolved μg/L)

d

BLM 

Data 

Label

BLM 

Normalized 

LC50/EC50

(μg/L)

e

Species 

Mean Acute 

Value 

(μg/L)

f Reference

Bay scallop,

Argopecten irradians

Juvenile, 

21.2 mm

R, UC 29 24.30 32 15.35 15.35 Nelson et al. 1988

Pacific oyster,

Crassostrea gigas

Adult, 

13-17 cm F, M

S 560.00- 88 662.0

g

- Okazaki 1976

Pacific oyster,

Crassostrea gigas Embryo S, U

C 11.5 9.640 89 4.918-

Coglianese and Martin 

1981

Pacific oyster,

Crassostrea gigas Embryo S,M

C 12.06 10.96 90 6.871- Harrison et al. 1981

Pacific oyster,

Crassostrea gigas Embryo S, M

C 12 10.91 93 12.88- Knezovich et al. 1981

Pacific oyster,

Crassostrea gigas Embryo S, U

S 5.3 4.440 94 2.237- Martin et al. 1981

Pacific oyster,

Crassostrea gigas Embryo S, M Copper 25.8 23.45 96 50.05

-

S.R. Hansen & 

Associates 1992

Pacific oyster,

Crassostrea gigas Embryo S, M Copper 30.5 27.72 97 59.35 11.94 S.R. Hansen & Associates 1992

Eastern oyster,

Crassostrea virginica Embryo S, U

C 15.1 12.65 106 6.699-

MacInnes and 

Calabrese 1978

Eastern oyster,

Crassostrea virginica Embryo S, U

C 18.7 15.67 107 8.284-

MacInnes and 

Calabrese 1978

Eastern oyster,

Crassostrea virginica Embryo S, U

C 18.3 15.34 108 8.110-

MacInnes and 

Calabrese 1978

Eastern oyster,

Crassostrea virginica Embryo S, M

N- 11.2 109 14.40- Arnold et al. 2010a

Eastern oyster,

Crassostrea virginica Embryo S, M

N- 22.4 110 8.791- Arnold et al. 2010a

Eastern oyster,

Crassostrea virginica Embryo S, M

N- 30.7 111 7.994- Arnold et al. 2010a

Eastern oyster,

Crassostrea virginica Embryo S, M

N- 40.7 112 7.259 8.537 Arnold et al. 2010a

Coot clam,

Mulinia lateralis Embryo R, M

S 25.2 21 286 14.84-

Science Applications 

International 

Corporation 1993

Coot clam,

Mulinia lateralis Embryo R, M

S 19.1 14.9 287 10.49-

Science Applications 

International 

Corporation 1993
A-16

Species

Organism 

Age, Size or 

Lifestage Methoda Chemicalb

Reported 

LC50/EC50

(total μg/L)c

Reported

LC50/EC50

(dissolved μg/L)d

BLM 

Data 

Label

BLM 

Normalized 

LC50/EC50

(μg/L)e

Species 

Mean Acute 

Value 

(μg/L)f Reference

Coot clam,

Mulinia lateralis Embryo R, M S 18.4 17.3 288 12.12 -

Science Applications 

International 

Corporation 1993

Coot clam,

Mulinia lateralis Embryo R, M S 18.6 16.9 289 11.70 -

Science Applications 

International 

Corporation 1993

Coot clam,

Mulinia lateralis Embryo R, M S 18.9 19.3 290 13.49 -

Science Applications

International 

Corporation 1993

Coot clam,

Mulinia lateralis Embryo R, M S 18.4 17.4 291 12.09 12.38

Science Applications 

International 

Corporation 1993

Clam,

Rangia cuneata - S, U S 8,000 6,704 526 66,022 - Olson and Harrel 1973

Clam,

Rangia cuneata - S, U S 7,400 6,201 527 28,918 43,694 Olson and Harrel 1973

Surf clam,

Spisula solidissima

Juvenile, 

15.9 mm R, U C 51 42.74 536 28.35 28.35 Nelson et al. 1988

Hard clam,

Mercenaria mercenaria

Larva, 

160-180 μm S, U S 398.2 333.7 274 350.2 350.2 Becerra-Huencho 1984

Softshell clam,

Mya arenaria

38-49 mm, 

3.6-6.0 g S, U C 39 32.68 293 23.03 23.03 Eisler 1977

Squid,

Loligo opalescens

Post-hatch 

larva S, M C 309 280.9 243 222.9 222.9 Dinnel et al. 1989

Copepod,

Pseudodiaptomus coronatus - S, U C 235.4 197.3 509 127.8 - Gentile 1982

Copepod,

Pseudodiaptomus coronatus - S, U - 138 115.6 510 62.64 -

Gentile and Cardin 

1982

Copepod,

Pseudodiaptomus coronatus Adult S, U C 235.4 197.3 511 129.5 101.2 Lussier and Cardin 1985

Copepod,

Eurytemora affinis - S, U C 928.0 - 151 1,361g

- Gentile 1982
A

-17

Species

Organism 

Age, Size or 

Lifestage Method

a Chemicalb

Reported 

LC50/EC50

(total μg/L)

c

Reported

LC50/EC50

(dissolved μg/L)

d

BLM 

Data 

Label

BLM 

Normalized 

LC50/EC50

(μg/L)

e

Species 

Mean Acute 

Value 

(μg/L)

f Reference

Copepod,

Eurytemora affinis

- S, U- 526.0- 152 632.5

g

-

Gentile and Cardin 

1982

Copepod,

Eurytemora affinis Nauplii, 24 hr R, M

N 30.6 27.82 153 14.27- Sullivan et al. 1983

Copepod,

Eurytemora affinis Nauplii, 24 hr R, M

N 31.1 28.27 154 14.50- Sullivan et al. 1983

Copepod,

Eurytemora affinis Nauplii, 24 hr R, M

N 28.7 26.09 155 13.36- Sullivan et al. 1983

Copepod,

Eurytemora affinis Nauplii, 24 hr R, M

N 7.5 6.82 156 3.453- Sullivan et al. 1983

Copepod,

Eurytemora affinis Nauplii, 24 hr R, M

N 33.7 30.63 157 15.74- Sullivan et al. 1983

Copepod,

Eurytemora affinis Nauplii, 24 hr S, M

C- 69.4 158 22.99- Hall et al. 1997

Copepod,

Eurytemora affinis Nauplii, 24 hr S, M

C- 71 161 28.51- Hall et al. 2008

Copepod,

Eurytemora affinis Nauplii, 24 hr S, M

C- 104 162 54.19- Hall et al. 2008

Copepod,

Eurytemora affinis Nauplii, 24 hr S, M

C- 67.6 163 44.69- Hall et al. 2008

Copepod,

Eurytemora affinis Nauplii, 24 hr S, M

C- 58.1 164 45.39- Hall et al. 2008

Copepod,

Eurytemora affinis Nauplii, 24 hr S, M

C- 76.2 165 37.25- Hall et al. 2008

Copepod,

Eurytemora affinis Nauplii, 24 hr S, M

C- 108 166 34.92- Hall et al. 2008

Copepod,

Eurytemora affinis Nauplii, 24 hr S, M

C- 111 167 24.40- Hall et al. 2008

Copepod,

Eurytemora affinis Nauplii, 24 hr S, M

C- 166 168 23.81 22.44 Hall et al. 2008

Copepod,

Acartia clausi

- S, UC 48.80 40.891 21.15- Gentile 1982

Copepod,

Acartia clausi

- S, U- 52.00 43.582 22.59 21.86 Gentile and Cardin 

1982

Copepod,

Acartia tonsa

- S, UC 17 14.254 8.367-

Sosnowski and Gentile 

1978

Copepod,

Acartia tonsa

- S, UC 55 46.095 28.36-

Sosnowski and Gentile 

1978
A

-18

Species

Organism 

Age, Size or 

Lifestage Method

a Chemicalb

Reported 

LC50/EC50

(total μg/L)

c

Reported

LC50/EC50

(dissolved μg/L)

d

BLM 

Data 

Label

BLM 

Normalized 

LC50/EC50

(μg/L)

e

Species 

Mean Acute 

Value 

(μg/L)

f Reference

Copepod,

Acartia tonsa

- S, UC 31 25.986 13.31-

Sosnowski and Gentile 

1978

Copepod,

Acartia tonsa

- S, U- 17 14.257 7.262-

Gentile and Cardin 

1982

Copepod,

Acartia tonsa

Mixed ages R, MC- 41.80 734 609.2

g

- Monteiro et al. 2013

Copepod,

Acartia tonsa

Mixed ages R, MC- 67.40 735 533.7

g

- Monteiro et al. 2013

Copepod,

Acartia tonsa

Mixed ages R, MC- 108.7 736 470.8

g 12.31 Monteiro et al. 2013

Copepod,

Amphiascoides atopus Adult, female S, M

C 334.24 303.8 737 1,192- Caramujo et al. 2012

Copepod,

Amphiascoides atopus Adult, female S, M

C 538.67 489.7 738 1,905- Caramujo et al. 2012

Copepod,

Amphiascoides atopus

Adult, female S, MC 741.83 674.3 739 2,614- Caramujo et al. 2012

Copepod,

Amphiascoides atopus Adult, female S, M

C 857.19 779.2 740 3,017 2,057 Caramujo et al. 2012

Copepod, 

Tigriopus californicus Egg/Embryo R, U

N 229 191.9 557 108.6

g

- O'Brien et al. 1988

Copepod, 

Tigriopus californicus

Nauplii, 

Stage 1 R, U

N 76 63.69 558 31.78

g

- O'Brien et al. 1988

Copepod, 

Tigriopus californicus

Nauplii, 

Stage 2 R, U

N 19 15.92 559 7.847- O'Brien et al. 1988

Copepod, 

Tigriopus californicus

Nauplii, 

Stage 3 R, U

N 159 133.24 560 69.79

g

- O'Brien et al. 1988

Copepod, 

Tigriopus californicus

Nauplii, 

Stage 4 R, U

N 184 154.19 561 82.66

g

- O'Brien et al. 1988

Copepod, 

Tigriopus californicus

Nauplii, 

Stage 5 R, U

N 261 218.72 562 129.6

g

- O'Brien et al. 1988

Copepod, 

Tigriopus californicus

Nauplii, 

Stage 6 R, U

N 305 255.59 563 161.9

g

- O'Brien et al. 1988

Copepod, 

Tigriopus californicus

Copepodite, 

Stage 1 R, U

N 375 314.25 564 218.7

g

- O'Brien et al. 1988

Copepod, 

Tigriopus californicus

Copepodite, 

Stage 2 R, U

N 496 415.65 565 322.7

g

- O'Brien et al. 1988

Copepod, 

Tigriopus californicus

Copepodite, 

Stage 3 R, U

N 413 346.09 566 250.9

g

- O'Brien et al. 1988
A-19

Species

Organism 

Age, Size or 

Lifestage Methoda Chemicalb

Reported 

LC50/EC50

(total μg/L)c

Reported

LC50/EC50

(dissolved μg/L)d

BLM 

Data 

Label

BLM 

Normalized 

LC50/EC50

(μg/L)e

Species 

Mean Acute 

Value 

(μg/L)f Reference

Copepod, 

Tigriopus californicus

Copepodite, 

Stage 4 R, U N 394 330.2 567 234.7g

- O'Brien et al. 1988

Copepod, 

Tigriopus californicus

Copepodite, 

Stage 5 R, U N 394 330.2 568 234.7g

- O'Brien et al. 1988

Copepod, 

Tigriopus californicus Adult R, U N 762 638.56 569 557.4g 7.847 O'Brien et al. 1988

Copepod,

Tisbe furcata

Newborn 

nauplii R, M S - 178 571 99.77 99.77 Bechmann 1994

Copepod,

Nitokra spinipes Adult S, U C 1,800 1,508 478 2,781 - Bengtsson 1978

Copepod,

Nitokra spinipes - S, U C 2,100 1,760 772 4,961 3,715 Ytreberg et al. 2010

Barnacle,

Balanus amphitrite

Nauplii, Stage 

2

S, U S 145 121.5 44 64.73 - Qiu et al. 2005

Barnacle,

Balanus amphitrite

Nauplii, Stage 

4

S, U S 156 130.7 45 70.50 - Qiu et al. 2005

Barnacle,

Balanus amphitrite

Nauplii, Stage 

6

S, U S 213 178.5 46 105.6 - Qiu et al. 2005

Barnacle,

Balanus amphitrite

Nauplii, Stage 

2

S, U S 720 603.4 741 791.1 139.7 Prato et al. 2012

Barnacle,

Balanus eburneus

Nauplii, Stage 

2

S, U S 750 628.5 742 835.4 835.4 Prato et al. 2012

Mysid,

Americamysis bahia 24 hr F, M N 181 164.5 16 96.60 - Lussier et al. 1985

Mysid,

Americamysis bahia 2-30 hr R, M S 209 164.0 17 153.7h

-

Science Applications 

International 

Corporation 1993

Mysid,

Americamysis bahia

Juvenile, 

<24 hr R, U C 72.32 60.60 18 32.34h

- Cripe 1994

Mysid,

Americamysis bahia <48 hr S, M - 110 99.99 19 99.37h

- Ho et al. 1999

Mysid,

Americamysis bahia <48 hr S, M - 250 227.3 20 189.0h

- Ho et al. 1999

Mysid,

Americamysis bahia <48 hr S, M - 360 327.2 21 39.29h 96.60 Ho et al. 1999
A-20

Species

Organism 

Age, Size or 

Lifestage Methoda Chemicalb

Reported 

LC50/EC50

(total μg/L)c

Reported

LC50/EC50

(dissolved μg/L)d

BLM 

Data 

Label

BLM 

Normalized 

LC50/EC50

(μg/L)e

Species 

Mean Acute 

Value 

(μg/L)f Reference

Mysid,

Americamysis bigelowi 24 hr F, M N 141 128.2 23 70.57 70.57 Gentile 1982

Mysid,

Holmesimysis costata <3 d S, M C 27 24.54 223 12.08 - Hunt et al. 1989

Mysid,

Holmesimysis costata Juvenile, 3 d S, M C 17 15.45 224 7.588 9.572 Martin et al. 1989

Mysid,

Neomysis mercedis Neonate, >5 d F, M S 28.27 25.7 474 16.73 - Brandt et al. 1993

Mysid,

Neomysis mercedis

Juvenile, 

>15 d F, M S 87.58 79.61 475 52.85 - Brandt et al. 1993

Mysid,

Neomysis mercedis

Juvenile, 

>15 d F, M S 63.7 57.9 476 39.19 32.60 Brandt et al. 1993

Isopod,

Sphaeroma serratum - S, U S 1,980 1,659 534 1,672 1,672 Bat et al. 1999a

Amphipod,

Corophium volutator Adult, 4-7 mm S, U S 20,740 17,380 79 81,550 81,550 Bat et al. 1998

Amphipod,

Echinogammarus olivii - S, U S 250 209.5 137 130.1 130.1 Bat et al. 1999a

Amphipod,

Gammarus duebeni

Adult, 

60-90 mg R, U C >10,000 >8,380 185 >29,733 >29,733 Moulder 1980

Amphipod,

Allorchestes compressa - F, M S 480 436.3 14 515.7 515.7 Ahsanullah et al. 1988

Amphipod,

Elasmopus rapax

Juvenile, 

0.54 mm R, U S 78 65.36 141 75.57 - Bao et al. 2008

Amphipod,

Elasmopus rapax Juvenile R, U S 77 64.53 142 74.97 75.27 Bao et al. 2011

Amphipod,

Orchomenella pinguis Adult R, U - 179.8 150.7 773 85.48 85.48 Bach et al. 2014
A-21

Species

Organism 

Age, Size or 

Lifestage Methoda Chemicalb

Reported 

LC50/EC50

(total μg/L)c

Reported

LC50/EC50

(dissolved μg/L)d

BLM 

Data 

Label

BLM 

Normalized 

LC50/EC50

(μg/L)e

Species 

Mean Acute 

Value 

(μg/L)f Reference

Pink shrimp,

Farfantepenaeus duorarum

Post-larva, 

3-5 d R, U C 393.3 329.6 503 260.8 260.8 Cripe 1994

Tiger shrimp,

Penaeus monodon Post-larva R, U C 660 553.1 743 746.8 - Kumar 2012

Tiger shrimp,

Penaeus monodon

Post-larva, 

Stage 12 R, M C - 950.0 774 1,498 1,058 Rajkumar 2012

Whiteleg shrimp,

Litopenaeus vannamei 1.2 cm R, U C 37,000 4,200 239 3,014 3,014 Frias-Espericueta et al. 2003

Shrimp,

Metapenaeus sp.

2.45 cm, 

3.905 g R, U S 220 184.36 276 106.8 106.8 Kidwai and Ahmed 1999

Decapod,

Palaemon elegans - S, U S 2,520 2,112 487 2,163 2,163 Bat et al. 1999a

Grass shrimp,

Palaemonetes pugio Embryo, 9 d S, U C 860.3 720.9 489 2,590 2,590 Rayburn and Fisher 1999

Shrimp,

Crangon crangon Larva, 1-3 d S, U S 330 276.5 85 255.4 255.4 Connor 1972

Lobster,

Homarus americanus

Larva stage 1, 

24 hr S, U N 48 40.22 226 28.37 28.37 Johnson and Gentile 1979

Dungeness crab,

Cancer magister Larva S, U S 49 41.06 68 20.60 - Martin et al. 1981

Dungeness crab,

Cancer magister Zoea S, M C 96 87.26 69 61.93 35.72 Dinnel et al. 1989

Blue crab,

Callinectes sapidus

Juvenile, 

8.3 cm R, M C - 337.2 65 6,403 - Martins et al. 2011

Blue crab,

Callinectes sapidus

Juvenile, 

8.3 cm R, M C - 3,365 66 12,583 8,976 Martins et al. 2011

Shore crab,

Carcinus maenas Larva, 1-3 d S, U S 600 502.8 71 730.8 730.8 Connor 1972
A-22

Species

Organism 

Age, Size or 

Lifestage Methoda Chemicalb

Reported 

LC50/EC50

(total μg/L)c

Reported

LC50/EC50

(dissolved μg/L)d

BLM 

Data 

Label

BLM 

Normalized 

LC50/EC50

(μg/L)e

Species 

Mean Acute 

Value 

(μg/L)f Reference

Sand crab,

Emerita analoga

Immature, 

8-10 mm S, U C 2,000 1,676 144 2,492 2,492 Valdovinos and Zuniga 2002

Horseshoe crab,

Limulus polyphemus

Embryo, 

Stage 20, 

Sandy Hook

R, U S 2,000 1,676 775 3,473 Botton et al. 1998

Horseshoe crab,

Limulus polyphemus

Embryo, 

Stage 20, 

Delaware Bay

R, U S 171,000 143,298 776 289,605 Botton et al. 1998

Horseshoe crab,

Limulus polyphemus

Larva, 

Sandy Hook R, U S 637,000 533,806 777 1,066,174g 31,716 Botton et al. 1998

Bristle star,

Ophionereis dubia 0.14 g R, U S 960 804.48 483 589.5 589.5 Kidwai and Ahmed 1999

Sea urchin,

Arbacia punctulata Embryo S, M S 30 27 778 13.85 13.85 Nelson et al. 2010

Green sea urchin,

Strongylocentrotus droebachiensis Embryo S, M C 21 19.09 538 13.29 13.29 Dinnel et al. 1989

Purple sea urchin, 

Strongylocentrotus purpuratus Embryo S, M C 6.3 5.73 543 3.966 - Dinnel et al. 1989

Purple sea urchin, 

Strongylocentrotus purpuratus Embryo S, M S 14.38 13.52 547 8.030 - City of San Jose 1998

Purple sea urchin, 

Strongylocentrotus purpuratus Embryo S, M S 15.05 12.77 548 7.593 - City of San Jose 1998

Purple sea urchin, 

Strongylocentrotus purpuratus Embryo S, M S - 14.3 549 5.768 - Rosen et al. 2008

Purple sea urchin, 

Strongylocentrotus purpuratus Embryo S, M N - 14.8 550 12.41 - Arnold et al. 2010a

Purple sea urchin, 

Strongylocentrotus purpuratus Embryo S, M N - 24.3 551 11.66 - Arnold et al. 2010a

Purple sea urchin, 

Strongylocentrotus purpuratus Embryo S, M N - 30.2 552 8.661 - Arnold et al. 2010a

Purple sea urchin, 

Strongylocentrotus purpuratus Embryo S, M N - 46.4 553 9.320 7.971 Arnold et al. 2010a

Sand dollar,

Dendraster excentricus Embryo S, M C 33 30 125 21.43 - Dinnel et al. 1989
A-23

Species

Organism 

Age, Size or 

Lifestage Methoda Chemicalb

Reported 

LC50/EC50

(total μg/L)c

Reported

LC50/EC50

(dissolved μg/L)d

BLM 

Data 

Label

BLM 

Normalized 

LC50/EC50

(μg/L)e

Species 

Mean Acute 

Value 

(μg/L)f Reference

Sand dollar,

Dendraster excentricus Embryo S, M N - 18.9 129 15.89 - Arnold et al. 2010a

Sand dollar,

Dendraster excentricus Embryo S, M N - 36.4 130 17.57 - Arnold et al. 2010a

Sand dollar,

Dendraster excentricus Embryo S, M N - 46.2 131 13.31 - Arnold et al. 2010a

Sand dollar,

Dendraster excentricus Embryo S, M N - >75.80 132 >15.32 16.49 Arnold et al. 2010a

Long-spined sea urchin,

Diadema antillarum Adult, ~1 yr F, M S - 25 134 12.58 12.58 Bielmyer et al. 2005b

Coho salmon,

Oncorhynchus kisutch

Smolt, 

132 mm F, M C 601 546.3 481 445.6 445.6 Dinnel et al. 1989

Mangrove killifish,

Rivulus marmoratus

4-6 week F, M S - 1,250 529 7,419 - Lin and Dunson 1993

Mangrove killifish,

Rivulus marmoratus 4-6 week F, M S - 1,610 530 9,563 8,423 Lin and Dunson 1993

Leon Springs pupfish,

Cyprinodon bovinus 0.42 g S, U S 1306 1094.4 781 5,304

Sappington et al. 2001; 

Dwyer et al. 2005; 

Mayer et al. 2008

Leon Springs pupfish,

Cyprinodon bovinus 0.42 g S, U S >204 >171.0 782 >114.1 778.0

Sappington et al. 2001; 

Dwyer et al. 2005; 

Mayer et al. 2008

Sheepshead minnow,

Cyprinodon variegatus

Larva, 

>24 hr F, M S/C 368 334.5 120 337.2 - Hughes et al. 1989

Sheepshead minnow,

Cyprinodon variegatus

Juvenile, 

0.24 g S, U S 630 527.9 779 1,946h

-

Sappington et al. 2001; 

Dwyer et al. 2005; 

Mayer et al. 2008

Sheepshead minnow,

Cyprinodon variegatus

Juvenile, 

0.24 g S, U S >204 >171.0 780 >114.1h 337.2

Sappington et al. 2001; 

Dwyer et al. 2005; 

Mayer et al. 2008

Mummichog,

Fundulus heteroclitus 2.7 g S, U S 3,100 2,598 172 10,647g

- Dorfman 1977

Mummichog,

Fundulus heteroclitus 2.7 g S, U S 2,000 1,676 173 3,452g

- Dorfman 1977
A-24

Species

Organism 

Age, Size or 

Lifestage Methoda Chemicalb

Reported 

LC50/EC50

(total μg/L)c

Reported

LC50/EC50

(dissolved μg/L)d

BLM 

Data 

Label

BLM 

Normalized 

LC50/EC50

(μg/L)e

Species 

Mean Acute 

Value 

(μg/L)f Reference

Mummichog,

Fundulus heteroclitus 2.7 g S, U C 2,300 1,927 174 7,401g

- Dorfman 1977

Mummichog,

Fundulus heteroclitus 2.7 g S, U C 400 335.2 175 386.2g

- Dorfman 1977

Mummichog,

Fundulus heteroclitus 4-6 week F, M S - 1,690 176 10,040g

- Lin and Dunson 1993

Mummichog,

Fundulus heteroclitus 7 d R, M S ~360.00 ~327.20 178 578.9 - Grosell et al. 2007

Mummichog,

Fundulus heteroclitus 7 d R, M S ~640.00 ~581.80 179 1,837 - Grosell et al. 2007

Mummichog,

Fundulus heteroclitus 7 d R, M S >937.00 >851.70 180 >2,345 - Grosell et al. 2007

Mummichog,

Fundulus heteroclitus 7 d R, M S ~500.00 ~454.50 181 476.9 - Grosell et al. 2007

Mummichog,

Fundulus heteroclitus 7 d R, M S ~340.00 ~309.10 182 190.8 - Grosell et al. 2007

Mummichog,

Fundulus heteroclitus 7 d R, M S 294 267.25 183 130.6 556.3 Grosell et al. 2007

Topsmelt,

Atherinops affinis Larva, 8 d S, M C 288 261.8 36 249.8 - Anderson et al. 1991

Topsmelt,

Atherinops affinis Larva, 8 d S, M C 212 192.7 37 145.5 - Anderson et al. 1991

Topsmelt,

Atherinops affinis Larva, 8 d S, M C 235 213.6 38 174.1 185.0 Anderson et al. 1991

Inland silverside,

Menidia beryllina - S, M S 115.41 104.9 262 55.31 - TOXSCAN, Inc. 1991a

Inland silverside,

Menidia beryllina - S, M S 63.05 57.31 263 29.97 - TOXSCAN, Inc. 1991b

Inland silverside,

Menidia beryllina - S, M S 123 111.8 264 58.77 46.01 TOXSCAN, Inc. 1991c

Atlantic silverside,

Menidia menidia Larva, 3 wk F, M N 66.6 60.54 266 42.95 - Cardin 1982; 1985

Atlantic silverside,

Menidia menidia Larva, 1 wk F, M N 216.5 196.8 267 176.4 - Cardin 1982; 1985

Atlantic silverside,

Menidia menidia Larva, 3 d F, M N 97.6 88.72 268 64.33 - Cardin 1982; 1985
A-25

Species

Organism 

Age, Size or 

Lifestage Methoda Chemicalb

Reported 

LC50/EC50

(total μg/L)c

Reported

LC50/EC50

(dissolved μg/L)d

BLM 

Data 

Label

BLM 

Normalized 

LC50/EC50

(μg/L)e

Species 

Mean Acute 

Value 

(μg/L)f Reference

Atlantic silverside,

Menidia menidia Larva, 2 wk F, M N 155.9 141.7 269 112.1 85.97 Cardin 1982; 1985

Tidewater silverside,

Menidia peninsulae Larva, 19 d S, U N 140 117.3 271 67.46 - Hansen 1983

Tidewater silverside,

Menidia peninsulae 19 d S, U - 141 118.2 272 68.00 67.73 D'Asaro 1985

Striped mullet,

Mugil cephalus

Fingerling, 

1.5 cm, 0.13 g R, M C - 2,740 744 4,898 4,898 Rajkumar 2012

Shiner perch,

Cymatogaster aggregata Adult, 97 mm F, M C 418 380.0 118 611.0 611.0 Dinnel et al. 1989

Mud-skipper,

Boleophthalmus sp.

2.84 cm, 0.13 

g

R, U S 3,710 3,109 48 3,690 3,690 Kidwai and Ahmed 

1999

Striped bass,

Morone saxatilis 45.6-60.6 mm F, M C 8,400 7,636 280 74,083g

- Hetrick et al. 1982

Striped bass,

Morone saxatilis 70 d S, U S 69.4 58.16 281 229.9 - Palawski et al. 1985

Striped bass,

Morone saxatilis

Fingerling, 

1-2 mo. S, U S 2,680 2,246 282 656.4g

-

Reardon and Harrell 

1990

Striped bass,

Morone saxatilis

Fingerling, 

1-2 mo. S, U S 8,080 6,771 283 2,207g

-

Reardon and Harrell 

1990

Striped bass,

Morone saxatilis

Fingerling, 

1-2 mo. S, U S 7,880 6,603 284 16,706g 229.9 Reardon and Harrell 1990

Spot,

Leiostomus xanthurus

Adult, 

0.5-0.6 g S, U N 280 234.6 236 189.3 - Hansen 1983

Spot,

Leiostomus xanthurus 0.5-0.6 g S, U - 282 236.3 237 191.9 190.6 D'Asaro 1985

Atlantic croaker,

Micropogonias undulatus 16-19 cm S, U C 5,660 4,743 278 8,863 8,863 Steele 1983

Sheepshead,

Archosargus probatocephalus 18-21 cm S, U C 1,140 955.3 30 1,534 1,534 Steele 1983
A-26

Species

Organism 

Age, Size or 

Lifestage Methoda Chemicalb

Reported 

LC50/EC50

(total μg/L)c

Reported

LC50/EC50

(dissolved μg/L)d

BLM 

Data 

Label

BLM 

Normalized 

LC50/EC50

(μg/L)e

Species 

Mean Acute 

Value 

(μg/L)f Reference

Pinfish,

Lagodon rhomboides 13-17 cm S, U C 2,750 2,305 234 4,145 4,145 Steele 1983

Thornfish,

Terapon jarbua

Juvenile, 

10 cm, 25 g R, U - 2,500 2,095 555 2,512 2,512 Vijayavel et al. 2006

Pompano,

Trachinotus carolinus

Juvenile, 

0.25 g, 25 mm S, U S 557.3 467.0 573 920.9 -

Birdsong and Avault 

1971

Pompano,

Trachinotus carolinus

Juvenile, 

0.25 g, 25 mm S, U S 597.2 500.5 574 770.0 -

Birdsong and Avault 

1971

Pompano,

Trachinotus carolinus

Juvenile, 

0.25 g, 25 mm S, U S 796.2 667.2 575 947.0 875.7 Birdsong and Avault 1971

Summer flounder,

Paralichthys dentatus

Juvenile, 46 d, 

18-22 mm S, M S 610 586.0 499 2,265h

- CH2M Hill 1999a

Summer flounder,

Paralichthys dentatus

Juvenile, 48 d, 

20-24 mm S, M S 1,029 928.0 500 3,990h

- CH2M Hill 1999a

Summer flounder,

Paralichthys dentatus

Juvenile, 57 d, 

24-28 mm S, M S 606 597.0 501 1,775h

- CH2M Hill 1999a

Summer flounder,

Paralichthys dentatus

Embryo -

Early cleavage F, M C 16.3 14.82 496 10.36 - Cardin 1982; 1985

Summer flounder,

Paralichthys dentatus

Embryo -

Early cleavage F, M C 11.9 10.82 497 7.556 - Cardin 1982; 1985

Summer flounder,

Paralichthys dentatus

Embryo -

Blastula F, M C 111.8 - 498 75.97g 8.848 Cardin 1982; 1985

Winter flounder,

Pseudopleuronectes americanus Blastula F, M N 167.3 152.1 513 129.8 - Cardin 1982; 1985

Winter flounder,

Pseudopleuronectes americanus Blastula F, M N 158 143.6 514 121.0 - Cardin 1982; 1985

Winter flounder,

Pseudopleuronectes americanus

Blastula -

Embryo F, M C 173.7 157.9 515 135.7 - Cardin 1982; 1985

Winter flounder,

Pseudopleuronectes americanus

Fertilization/ 

Pre-cleavage F, M C 132.8 120.7 516 94.46 - Cardin 1982; 1985

Winter flounder,

Pseudopleuronectes americanus

Blastula -

Embryo F, M N 148.2 134.7 517 109.3 - Cardin 1982; 1985

Winter flounder,

Pseudopleuronectes americanus

Early cleavage 

- Embryo F, M N 98.2 89.26 518 65.94 106.4 Cardin 1982; 1985
A-27

Species

Organism 

Age, Size or 

Lifestage Methoda Chemicalb

Reported 

LC50/EC50

(total μg/L)c

Reported

LC50/EC50

(dissolved μg/L)d

BLM 

Data 

Label

BLM 

Normalized 

LC50/EC50

(μg/L)e

Species 

Mean Acute 

Value 

(μg/L)f Reference

Gulf toadfish,

Opsanus beta 22-53 g F, M S >21,607 >19,641 485 >33,000 >33,000 Grosell et al. 2004

Cabezon,

Scorpaenichthys marmoratus

Post-hatch 

larva S, M C 95 86.36 532 64.20 64.20 Dinnel et al. 1989

Fat snook,

Centropomus parallelus

Juvenile, 3.5 

g, 6.8 cm S, M C 1,880 1,709 751 4,428 4,428 Oliveria et al. 2014

a S=static, R=renewal, F=flow-through, U=unmeasured, M=measured.

b S=copper sulfate, N=copper nitrate, C=copper chloride.

c Values in this column are total copper LC50 or EC50 values as reported by author.

d Values in this column are dissolved copper LC50 or EC50 values either reported by the author, or if the author did not report a dissolved value, then a conversion factor (CF) 

was applied to the total copper LC50 to estimate dissolved copper values (If copper was unmeasured, the total copper was multiplied by 0.838, if it was measured, it was 

multiplied by 0.909).

e Normalization Chemistry (only Temp, pH, DOC, and Salinity are needed for the model, but values for other ions are shown for reference).

Temperature

(°C) pH DOC

(mg/L)

Salinity

(ppt)

Ca

(mg/L)

Mg

(mg/L)

Na

(mg/L)

K

(mg/L)

SO4

(mg/L)

Cl

(mg/L)

Alkalinity

(mg/L)

22 8 1.0 32 367.2 1144.0 9607.5 355.7 2417.0 17244.3 89.8

f Bolded BLM Normalized values were used in the SMAV calculation.

g Value not used in the SMAV calculation, only the most sensitive life stage of the species.

h Value not used in the SMAV calculation because flow-through measured tests available.
B-1

Appendix B Acceptable Chronic Toxicity Data
B-2

Appendix Table B-1. Acceptable Estuarine/Marine Chronic Toxicity Data.

Species Testa Chemicalb Endpoint

Salinity

(g/kg)

Chronic 

Limits 

(μg/L)

Chronic 

Value

(total μg/L)

Chronic Value

(dissolved μg/L)

BLM

Data

Label

BLM 

Normalized

Chronic Value 

(Dissolved μg/L)c Reference

Rotifer,

Brachionus plicatilis LC N

Intrinsic rate of 

rotifer population 15 6.1-10.3 -

10.9

(EC20)

C1 13.23 Arnold et al. 2010b

Sheepshead minnow,

Cyprinodon variegatus ELS C Growth 30 172-362 249.5 226.8 C2 204.1 Hughes et al. 1989

a LC=life-cycle; PLC=partial life-cycle; ELS=early life stage.

b S=copper sulfate, N=copper nitrate, C=copper chloride.

c Normalization Chemistry (only Temp, pH, DOC, and Salinity are needed for the model, but values for other ions are shown for reference).

Temperature

(°C) pH DOC

(mg/L)

Salinity

(ppt)

Ca

(mg/L)

Mg

(mg/L)

Na

(mg/L)

K

(mg/L)

SO4

(mg/L)

Cl

(mg/L)

Alkalinity

(mg/L)

22 8 1.0 32 367.2 1144.0 9607.5 355.7 2417.0 17244.3 89.8

Appendix Table B-2. Acute-Chronic Ratios.

Species

Hardness

(mg/L as 

CaCO3)

Acute Value 

(μg/L)

Chronic Value

(μg/L)

Acute to Chronic 

Ratio Reference

Species Mean 

ACR

Used in 

FACR 

calculation

FRESHWATER

Snail,

Campeloma decisum 35-55 1,673a 8.73 191.6 Arthur and Leonard 1970

171.2 Snail,

Campeloma decisum 35-55 1,673a 10.94 153.0 Arthur and Leonard 1970

Pond snail,

Lymnaea stagnalis 123 24.9 5.307 4.692 Ng et al. 2011 4.692

Oyster mussel,

Epioblasma capsaeformis 162 26 7.530 3.453 Wang et al. 2007b 3.453

Fatmucket,

Lampsilis siliquoidea 165 34 7.201 4.722 Wang et al. 2007b 4.722
B

-3

Species

Hardness

(mg/L as 

CaCO

3

)

Acute Value 

(μg/L)

Chronic Value

(μg/L)

Acute to Chronic 

Ratio Reference

Species Mean 

ACR

Used in 

FACR 

calculation

Rainbow mussel,

Villosa iris 171 27 7.679 3.516 Wang et al. 2007b

2.733

Rainbow mussel,

Villosa iris

101

(DOC=0.5) 15 8.3 1.807 Wang et al. 2011a

Rainbow mussel,

Villosa iris

100

(DOC=10) 72 35 2.057 Wang et al. 2011a

Rainbow mussel,

Villosa iris

98

(DOC=2.5) 32 7.5 4.267 Wang et al. 2011a

Cladoceran,

Ceriodaphnia dubia 179 28.42

b 7.9 3.597 Belanger et al. 1989

3.268x

Cladoceran,

Ceriodaphnia dubia 94.1 63.33

b 19.36 3.271 Belanger et al. 1989

Cladoceran,

Ceriodaphnia dubia 57 13.4 24.5 0.5469

g Oris et al. 1991

Cladoceran,

Ceriodaphnia dubia

- 17.974

c 9.17 1.960 Carlson et al. 1986

Cladoceran,

Ceriodaphnia dubia 54

-72 4.16 29.34 0.1418

g Harmon et al. 2003

Cladoceran,

Ceriodaphnia dubia 82.4 18 3.641 4.944 Cooper et al. 2009

Cladoceran,

Daphnia ambigua 54

-72 6.53 22.38 0.2918

g Harmon et al. 2003

-

Cladoceran,

Daphnia magna 51 26 12.58 2.067 Chapman et al. (Manuscript)

3.419x

Cladoceran,

Daphnia magna 104 33.76

d 19.89 1.697 Chapman et al. 

(Manuscript)

Cladoceran,

Daphnia magna

211 69 6.06 11.39 Chapman et al. 

(Manuscript)

Cladoceran,

Daphnia pulex 57.5 25.737 2.83 9.094 Winner 1985

4.814x

Cladoceran,

Daphnia pulex 115 27.6 7.07 3.904 Winner 1985

Cladoceran,

Daphnia pulex 230 28.79 9.16 3.143 Winner 1985

Rainbow trout,

Oncorhynchus mykiss 120 80 27.77 2.881 Seim et al. 1984 2.357

x
B-4

Species

Hardness

(mg/L as 

CaCO3)

Acute Value 

(μg/L)

Chronic Value

(μg/L)

Acute to Chronic 

Ratio Reference

Species Mean 

ACR

Used in 

FACR 

calculation

Rainbow trout,

Oncorhynchus mykiss 104 83 35.08 2.366 Besser et al. 2007

Rainbow trout,

Oncorhynchus mykiss 100 61.48h 32 1.921

Wang et al. 2014; 

Ingersoll and Mebane 

2014

Chinook salmon,

Oncorhynchus tshawytscha 20-45 33.1 5.92 5.591 Chapman 1975, 1982 5.591 x

White sturgeon,

Acipenser transmontanus 100 8.06 1.4 5.757

Wang et al. 2014; 

Ingersoll and Mebane 

2014

5.757 x

Mottled sculpin,

Cottus bairdii 102 45 28.47 1.581 Besser et al. 2007

2.075 x Mottled sculpin,

Cottus bairdii 104 12 4.408 2.722 Besser et al. 2007

Bluntnose minnow,

Pimephales notalus 172 - 230 231.9e 18 12.88 Horning and Neiheisel 1979 12.88

Fathead minnow,

Pimephales promelas 200 449.6i 12.86 34.96 Mount 1968

21.25

Fathead minnow,

Pimephales promelas 202 474.8j 19.72 24.08 Pickering et al. 1977

Fathead minnow,

Pimephales promelas 45 106.9f 9.38 11.40 Lind et al. 1978

Fathead minnow,

Pimephales promelas - 250 <61 >4.098k Scudder et al. 1988

Bluegill,

Lepomis macrochirus 21-40 1,100 27.15 40.52 Benoit 1975 40.52

Species

Salinity

(g/kg)

Acute Value 

(μg/L)

Chronic Value 

(μg/L)

Acute to Chronic 

Ratio Reference

Species Mean 

ACR

Used in 

FACR 

calculation

ESTUARINE/MARINE WATER

Rotifer,

Brachionus plicatilis 15 13.4(unfed) 10.9 1.229 Arnold et al. 2010b 1.229(unfed) x
B-5

Species

Salinity

(g/kg)

Acute Value 

(μg/L)

Chronic Value 

(μg/L)

Acute to Chronic 

Ratio Reference

Species Mean 

ACR

Used in 

FACR 

calculation

Rotifer,

Brachionus plicatilis 15 20.8(fed) 10.9 1.908 Arnold et al. 2010b 1.908(fed)

Sheepshead minnow,

Cyprinodon variegatus 30 368 249.5 1.475 Hughes et al. 1989 1.475 x

a Geometric mean of two values from Arthur and Leonard (1970).

b Geometric mean of five values from Belanger et al. (1989). ACR is based on dissolved metal measurements.

c Geometric mean of two values from Carlson et al. (1986).

d Geometric mean of two values from Chapman et al. (Manuscript).

e Geometric mean of three values from Horning and Neiheisel (1979).

f Geometric mean of three values from Lind et al. (1978).

g ACR from Oris et al. (1991) and Harmon et al. (2003) not used in calculating overall ratio for species it is <1.

h Geometric mean of two values from Wang et al. 2014; Ingersoll and Mebane 2014.

i Geometric mean of two values from Mount 1968.

j Geometric mean of two values from Pickering et al. 1977.

k ACR from Scudder et al. (1988) not used in calculating overall ratio for species since it is non-definitive.

Freshwater FACR (from Copper Freshwater AWQC 2007 Document) = 3.22

Estuarine/Marine FACR (geometric mean of values with an x) = 3.022
C-1

Appendix C Estuarine/Marine Plant Toxicity Data
C-2

Appendix Table C-1. Estuarine/Marine Plant Toxicity Data.

Species Methoda Chemical

Salinity

(g/kg)

Duration

(days) Effect

Result

(total μg/L)

Result

(dissolved μg/L) Reference

Dinoflagellate,

Amphidinium carteri S, U Copper chloride 21 21 83% reduction in growth <50 Erickson et al. 1970

Dinoflagellate,

Cochlodinium polykrikoides S, U Copper sulfate - 3 EC50 12,740 Ebenezer and Ki 2012

Dinoflagellate,

Cochlodinium polykrikoides S, U Copper sulfate - 3 EC50 5,030 Ebenezer and Ki 2012

Dinoflagellate,

Gymnodinium splendens S, U Copper sulfate 31.6-33.3 5

LOEC

(growth) 20 18.18 Saifullah 1978

Dinoflagellate,

Prorocentrum micans S, U Copper sulfate 31.6-33.3 8

LOEC

(growth) 5 4.545 Saifullah 1978

Dinoflagellate,

Prorocentrum minimum S, U Copper sulfate 30-35 3

EC50

(biomass) 1,074 Guo and Ki 2012

Dinoflagellate,

Prorocentrum minimum S, U Copper - 3

EC50

(cell #) 1,070 Guo et al. 2012

Dinoflagellate,

Scrippsiella faeroense S, U Copper sulfate 31.6-33.3 5

LOEC

(growth) 5 4.545 Saifullah 1978

Dinoflagellate,

Simbiodinium microadriaticum S, M Copper sulfate

Full strength 

seawater

23 46% reduction in growth 

(significant) 40 Goh and Chou 1997

Dinoflagellate,

Simbiodinium microadriaticum S, M Copper sulfate

Full strength 

seawater 23 26% reduction in growth (not significant) 42 Goh and Chou 1997

Golden/brown flagellate,

Isochrysis sp. S, U Copper sulfate 36 4

IC50

(growth) 2 1.8 Garr 2012

Brown alga,

Hizikia fusiformis S, U Copper sulfate - 7

NOEC-LOEC

(relative growth rate) 25-50 Zhu et al. 2011

Cyanobacterium,

Cyanobium sp. S, M Coppersulfate 33 3

EC50

(cell #) 500 Alquezar and Anastasi 2013

Alga,

Platymonas helgolandica var. 

tsingtaoensis

S, U Copper 

sulfate - 1.5 hr EC50(% motile cells) 848.4 Zheng et al. 2012

Alga,

Platymonas subcordiformis S, U Copper sulfate - 1.5 hr EC50(% motile cells) 320.9 Zheng et al. 2012

Green alga,

Chlorella stigmatophora S, M Copper chloride 35 21 EC50(cell volume) 70 Christensen et al. 1979

Green alga (zoospores),

Enteromorpha intestinalis S, U - - 5

EC50

(development to 2+ cell stage) 10 Fletcher 1989

Green alga,

Olisthodiscus luteus S, U Copper chloride 21 14 74% reduction in growth <50 Erickson et al. 1970

Alga,

Ulva pertusa S, U - 26-35 4

EC50

(chlorophyll fluorescence) 711 Kumar et al. 2009
C

-3

Species Method

a Chemical

Salinity

(g/kg)

Duration

(days) Effect

Result

(total μg/L)

Result

(dissolved μg/L) Reference

Alga,

Ulva lactuca R, M Copper chloride 32

3

EC50

(growth) 127 Wendt et al. 2013

Diatom,

Odontella mobiliensis S, M Copper chloride 30

3

EC50

(growth) 298.4 Manimaran et al. 2012

Diatom,

Nitzschia closterium

---4

EC50

(growth) 33 Rosko and Rachlin 1975

Diatom,

Nitzschia thermalis S, U Copper sulfate 35.7 Several No growth 38.1 Metaxas and Lewis 1991

Diatom,

Skeletonema costatum S, U Copper chloride 21 14 58% reduction in growth 50 Erickson et al. 1970

Diatom,

Skeletonema costatum S, U Copper sulfate 35.7 Several LOEC(no growth) 31.8 Metaxas and Lewis 1991

Diatom,

Skeletonema costatum S, U Copper chloride

-4

EC50

(growth) 45 Nassiri et al. 1997

Diatom,

Thalassiosira aestevallis S, U Copper chloride

- 3.0 -4 Reduced growth 19 Hollibaugh et al. 1980

Red alga,

Ceramium tenuicorne S, U Copper chloride

77

EC50

(growth) 6.4 Ytreberg et al. 2010

Red alga (tetrasporophyte),

Champia parvula R, M Copper chloride 30 11 Reduced growth 4.6 4.181 Steele and Thursby 1983

Red alga (tetrasporophyte),

Champia parvula R, M Copper chloride 30 11 Reduced production 13.3 12.09 Steele and Thursby 1983

Red alga (mature),

Champia parvula R, M Copper chloride 30 14 Reduced female growth 4.7 4.272 Steele and Thursby 1983

Red alga (mature),

Champia parvula R, M Copper chloride 30 14 Stopped sexual reproduction 7.3 6.636 Steele and Thursby 1983

Red seaweed,

Gracilaria lemaneiformis S, U Copper sulfate 25

6

LOEC

(growth rate) 50 Huang et al. 2013

Red seaweed,

Gracilariopsis longissima S, U Copper sulfate 33

7

EC50

(growth)

Plants collected from clean and 

polluted sites-April

31.1 28.27 Brown et al. 2012

Red seaweed,

Gracilariopsis longissima S, U Copper sulfate 33

7

EC50

(growth)

Plants collected from clean and 

polluted sites-Oct.

25.8 23.45 Brown et al. 2012

Red seaweed,

Gracilariopsis longissima S, U Copper sulfate 33

7

EC20

(growth)

Plants collected from clean and 

polluted sites-April

12.6 11.45 Brown et al. 2012
C-4

Species Methoda Chemical

Salinity

(g/kg)

Duration

(days) Effect

Result

(total μg/L)

Result

(dissolved μg/L) Reference

Red seaweed,

Gracilariopsis longissima S, U Copper sulfate 33 7

EC20

(growth)

Plants collected from clean and 

polluted sites-Oct.

11.3 10.27 Brown et al. 2012

Kelp (meiospore),

Laminaria saccharina R, U Copper sulfate - 21 Reduced gametophyte development rate 5

Chung and Brinkhuis 

1986

Kelp (1-3 cm sporophyte),

Laminaria saccharina S, U Copper sulfate - 9

LOEC

(100% mortality) 100 Chung and Brinkhuis 1986

Kelp (8-10 cm sporophyte),

Laminaria saccharina S, U Copper sulfate - - 23% decrease in blade growth 10 Chung and Brinkhuis 1986

Giant kelp,

Macrocystis pyrifera S, U - - 4

EC50

(photosynthesis) 60 Clendenning and North 1959

Giant kelp,

Macrocystis pyrifera R, M Copper chloride 36 19-20 NOEC(sporophyte production) <10.2 <9.2718 Anderson et al. 1990

Giant kelp,

Macrocystis pyrifera R, M Copper chloride 36 19-20 LOEC(sporophyte production) 10.2 9.2718 Anderson et al. 1990

a S=static, R=renewal, F=flow-through, U=unmeasured, M=measured.
D-1

Appendix D Acceptable Estuarine/Marine Bioaccumulation Data
D-2

Appendix Table D-1. Acceptable Estuarine/Marine Bioaccumulation Data.

Species Chemical

Concentration 

in water

(μg/L)

Salinity

(g/kg)

Duration 

(days) Tissue

BCF 

or 

BAF Reference

Polychaete,

Phyllodoce maculata

Copper 

sulfate 40 Full strength seawater 35 Whole body 2,500 McLusky and Phillips 1975

Polychaete,

Neanthes arenaceodentata

Copper 

nitrate 40 31 28 Whole body 2,950 Pesch and Morgan 1978

Polychaete,

Eudistylia vancouveri

Copper 

chloride 6 30.4 29 Body (less radioles) 1,006 Young et al. 1979

Blue mussel (0.45 cm),

Mytilus edulis

Copper 

chloride 3 25 550 Soft tissue 7,730 Calabrese et al. 1984

Blue mussel (0.45 cm),

Mytilus edulis

Copper 

chloride 7.9 25 550 Soft tissue 4,420 Calabrese et al. 1984

Blue mussel (0.45 cm),

Mytilus edulis

Copper 

chloride 12.7 25 550 Soft tissue 5,320 Calabrese et al. 1984

Mediterranean mussel 

(6.02-6.34 cm),

Mytilus galloprovincialis

Field study 0.285 37-38 266 Soft tissue 3,263 Martincic et al. 

1992

Mediterranean mussel 

(6.02-6.34 cm),

Mytilus galloprovincialis

Field study 0.446 37-38 266 Soft tissue 2,491 Martincic et al. 

1992

Mediterranean mussel

(6.02-6.34 cm),

Mytilus galloprovincialis

Field study 0.203 37-38 266 Soft tissue 4,384 Martincic et al. 

1992

Mediterranean mussel

(6.02-6.34 cm),

Mytilus galloprovincialis

Field study 0.177 37-38 266 Soft tissue 4,915 Martincic et al. 

1992

Bay scallop (5.12-6.26 cm),

Argopecten irradians

Copper 

chloride 4.56 29-32 56 Muscle 185 Zaroogian and Johnson 1983

Bay scallop (5.12-6.26 cm),

Argopecten irradians

Copper 

chloride 4.56 29-32 56 Viscera 3,816 Zaroogian and Johnson 1983

Pacific oyster,

Crassostrea gigas Field study 25.45 - 32 Soft tissue 34,600 Han and Hung 1990

Pacific oyster,

Crassostrea gigas Field study 9.66 - 32 Soft tissue 57,000 Han and Hung 1990

Pacific oyster,

Crassostrea gigas Field study 10.37 - 32 Soft tissue 33,400 Han and Hung 1990
D-3

Species Chemical

Concentration 

in water

(μg/L)

Salinity

(g/kg)

Duration 

(days) Tissue

BCF 

or 

BAF Reference

Eastern oyster,

Crassostrea virginica Field study 25 31 140 Soft tissue 27,800 Shuster and Pringle 1968

Soft-shell clam,

Mya arenaria Field study 100 31 35 Soft tissue 790 Shuster and Pringle 1968
E-1

Appendix E Other Estuarine/Marine Toxicity Data
E-2

Appendix Table E-1. Other Estuarine/Marine Toxicity Data.

Species Chemical

Duration 

(days) Effect

Effect 

Concentration

(total μg/L)

Effect 

Concentration

(dissolved μg/L) Reference

Ciliate,

Euplotes crassus - 8 hr NOEC(survival) 31,775 - Gomiero et al. 2012b

Bacterium,

Vibrio fischeri

Copper 

sulfate 15 min EC50(luminescence) 397 - Rosen et al. 2008

Bacterium,

Vibrio fischeri

Copper 

chloride 15 min EC50(luminescence) 800 - Ytreberg et al. 2010

Dinoflagellate,

Ceratocorys horrida

Copper 

sulfate 1

EC50

(luminescence) 166 - Rosen et al. 2008

Dinoflagellate,

Lingulodinium polyedrum

Copper 

sulfate 1

EC50

(luminescence) 90 - Rosen et al. 2008

Dinoflagellate,

Pyrocystis noctiluca

Copper 

sulfate 1

EC50

(luminescence) 185 - Rosen et al. 2008

Fungus,

Halophytophthora elongata

Copper 

chloride 5

NOEC-LOEC

(biomass) 10,000 - 100,000 - Leano and Pang 2010

Fungus,

Halophytophthora spinosa

Copper 

chloride 5

NOEC-LOEC

(biomass) 1,000 - 10,000 - Leano and Pang 2010

Fungus,

Halophytophthora vesicula

Copper 

chloride 5

NOEC-LOEC

(biomass) 1,000 - 10,000 - Leano and Pang 2010

Green alga,

Chlorella autotrophyca

Copper 

sulfate 3

EC50

(biomass)

(initial cell density=103cells/ml)

9.6 -

Moreno-Garrido et al. 

2000

Green alga,

Chlorella autotrophyca

Copper 

sulfate 3

EC50

(biomass)

(initial cell density =5x103cells/ml)

19.3 -

Moreno-Garrido et al. 

2000

Green alga,

Chlorella autotrophyca

Copper 

sulfate 3

EC50

(biomass)

(initial cell density=104cells/ml)

38.3 -

Moreno-Garrido et al. 

2000

Green alga,

Isochrysis galbana

Copper 

sulfate 3

EC50

(biomass)

(initial cell density=103cells/ml)

0.4 -

Moreno-Garrido et al. 

2000

Green alga,

Isochrysis galbana

Copper 

sulfate 3

EC50

(biomass)

(initial cell density=5x103cells/ml)

3.6 -

Moreno-Garrido et al. 

2000

Green alga,

Isochrysis galbana

Copper 

sulfate 3

EC50

(biomass)

(initial cell density=104cells/ml)

4.4 -

Moreno-Garrido et al. 

2000

Green alga,

Nannochloris atomus

Copper 

sulfate 3

EC50

(biomass)

(initial cell density=103cells/ml)

16.7 -

Moreno-Garrido et al. 

2000
E

-3

Species Chemical

Duration 

(days) Effect

Effect 

Concentration (total μg/L)

Effect 

Concentration

(dissolved μg/L) Reference

Green alga,

Nannochloris atomus

Copper 

sulfate

3

EC50

(biomass)

(initial cell density=5x10

3

cells/ml)

27.3-

Moreno-Garrido et al. 

2000

Green alga,

Nannochloris atomus

Copper 

sulfate

3

EC50

(biomass)

(initial cell density=10

4

cells/ml)

46.2-

Moreno-Garrido et al. 

2000

Diatom,

Ceratoneis closterium

Copper 

sulfate

3

IC50

(growth rate) 7.1

- Hook et al. 2014

Diatom,

Cylindrotheca closterium

Copper 

sulfate 72 hr EC50(growth) 29

- Araujo et al. 2008

Diatom,

Cylindrotheca closterium

Copper 

sulfate 72 hr EC50(growth) 22

- Araujo et al. 2008

Diatom,

Cylindrotheca closterium

Copper 

sulfate 72 hr EC50(growth) 23

- Araujo et al. 2008

Diatom,

Cylindrotheca closterium

Copper 

sulfate 72 hr EC50(growth) 23

- Araujo et al. 2008

Diatom,

Phaeodactylum tricornutum

Copper 

sulfate

3

EC50

(biomass)

(initial cell density=10

3

cells/ml)

9.8-

Moreno-Garrido et al. 

2000

Diatom,

Phaeodactylum tricornutum

Copper 

sulfate

3

EC50

(biomass)

(initial cell density=5x10

3

cells/ml)

34.4-

Moreno-Garrido et al. 

2000

Diatom,

Phaeodactylum tricornutum

Copper 

sulfate

3

EC50

(biomass)

(initial cell density=10

4

cells/ml)

35.0-

Moreno-Garrido et al. 

2000

Diatom,

Phaeodactylum tricornutum

Copper 

sulfate

3

IC50

(growth) 8.5

-

Osborn and Hook 

2013

Coral (explants),

Montastraea franksi

Copper 

sulfate 8 hr NOEC(paling/tissue loss) 100

- Venn et al. 2009

Coral (explants),

Montastraea franksi

Copper 

sulfate 8 hr

NOEC-LOEC

(increase hsp70, hsp90 & P-gp 

expression)

10.0 - 30- Venn et al. 2009

Bryzoan,

Bugula neritina

-2 100% mortality 500-

Piola and Johnston 

2006

Bryzoan,

Watersipora subtorquata

-2 100% mortality 500-

Piola and Johnston 

2006

Bryzoan,

Schizoporella errata

-2 100% mortality 500-

Piola and Johnston 

2006

Bryzoan,

Tricellaria occidentalis

-2 100% mortality 500-

Piola and Johnston 

2006
E

-4

Species Chemical

Duration 

(days) Effect

Effect 

Concentration (total μg/L)

Effect 

Concentration

(dissolved μg/L) Reference

Hydroid,

Campanularia flexuosa

- 11 Growth rate inhibition 10.0 - 13- Stebbing 1976

Hydroid,

Campanularia flexuosa

-- Enzyme inhibition 1.43-

Moore and Stebbing 

1976

Hydromedusa,

Phlalldium sp.

-1 LC50 36- Reeve et al. 1976

Ctenophore,

Pleurobrachia pileus

-1 LC50 33- Reeve et al. 1976

Ctenophore,

Mnemiopsis mccrdayi

-1 LC50 17 - 29- Reeve et al. 1976

Rotifer,

Brachionus plicatillis

-1 LC50 100- Reeve et al. 1976

Polychaete,

Phyllodoce maculata

-9 LC50 80-

McLusky and Phillips 

1975

Polychaete (adult),

Neanthes arenaceodentata

Copper 

nitrate 28 LC50 44 40 Pesch and Morgan 1978

Polychaete,

Neanthes arenaceodentata

Copper 

nitrate

7 LC50 137-

Pesch and Hoffman 

1982

Polychaete,

Neanthes arenaceodentata

Copper 

nitrate 10 LC50 98

-

Pesch and Hoffman 

1982

Polychaete,

Neanthes arenaceodentata

Copper 

nitrate 28 LC50 56

-

Pesch and Hoffman 

1982

Polychaete (larva, 0.10 mg),

Neanthes arenaceodentata

Copper 

chloride

4 LC50 311- Pesch et al. 1986

Polychaete (larva, 0.10 mg),

Neanthes arenaceodentata

Copper 

chloride

4 LC50 252- Pesch et al. 1986

Polychaete (larva, 0.10 mg),

Neanthes arenaceodentata

Copper 

chloride

4 LC50 224- Pesch et al. 1986

Polychaete (larva, 0.10 mg),

Neanthes arenaceodentata

Copper 

chloride 28 LC50 83

- Pesch et al. 1986

Polychaete (larva, 0.10 mg),

Neanthes arenaceodentata

Copper 

chloride 28 LC50 81

- Pesch et al. 1986

Polychaete (larva, 0.10 mg),

Neanthes arenaceodentata

Copper 

chloride 28 LC50 86

- Pesch et al. 1986

Polychaete,

Nereis virens

Copper

sulfate

8 LC50 20.97- Caldwell et al. 2011

Polychaete,

Cirriformia spirabranchia

Copper 

nitrate 26 LC50 40

- Milanovich et al. 1976

Polychaete (adult),

Hydroides elegans

Copper 

sulfate

2 LC50 715 649.9 Xie et al. 2005
E-5

Species Chemical

Duration 

(days) Effect

Effect 

Concentration

(total μg/L)

Effect 

Concentration

(dissolved μg/L) Reference

Polychaete (larva),

Hydroides elegans

Copper 

sulfate 2 LC50 120 100.6 Bao et al. 2008

Flatworm,

Parorchis acanthus

Copper 

sulfate 2

NOEC-LOEC

(successful encystment) 10-100 Morley et al. 2003

Nematode (adult, 3-4 d),

Caenorhabditis elegans

Copper 

chloride 4 LC50 256 214.5 Williams and Dusenbery 1990

Annelids (mixed species, larva) - 1 LC50 89 - Reeve et al. 1976

Black abalone,

Hailotis cracherodil - 4 Histopathological gill abnormalities >32 - Martin et al. 1977

Barnacle (nauplii),

Amphibalanus variegatus - 1

EC50

(swimming) 81.29 - Gall et al. 2013

Red abalone,

Hailotis rufescens - 4 Histopathological gill abnormalities >32 - Martin et al. 1977

Channeled whelk,

Busycon canaliculatum - 77 LC50 470 -

Betzer and Yevich 

1975

Mud snail,

Nassarius obsoletus - 3 Decrease in oxygen consumption 100 -

MacInnes and 

Thurberg 1973

Blue mussel,

Mytilus edulis

Copper 

chloride 7

LOEC

(mortality) 200 167.6 Scott and Major 1972

Blue mussel (10-15 mm),

Mytilus edulis - 3

LOEC

(growth) 10 8.38 Manley et al. 1984

Blue mussel (51-58 mm),

Mytilus edulis

Copper 

sulfate 5

LOEC

(mortality) 100 83.8 Al-Subiai et al. 2011

Mediterranean mussel (adult, 5 cm),

Mytilus galloprovincialis

Copper 

chloride 5

LOEC

(lysosomal membrane stability) 2.3 1.927 Bolognesi et al. 1999

Mediterranean mussel (50-80 mm),

Mytilus galloprovincialis - 28 LC50(no sediment present) 100 Bat et al. 2013

Mediterranean mussel (50-80 mm),

Mytilus galloprovincialis - 28 LC50(sediment present) 250 Bat et al. 2013

Mediterranean mussel (5-6 cm),

Mytilus galloprovincialis -

4

(16°C)

NOEC-LOEC

(decrease lysosomal membrane 

stability in digestive gland)

20 - 40 Negri et al. 2013

Mediterranean mussel (5-6 cm),

Mytilus galloprovincialis -

4

(20°C)

NOEC-LOEC

(decrease lysosomal membrane 

stability in digestive gland)

20 - 40 Negri et al. 2013

Pacific blue mussel (sperm),

Mytilus trossulus

Copper 

chloride 100 min. Reduced sperm swimming speed 100 90.9 Fitzpatrick et al. 2008

Pacific blue mussel (sperm),

Mytilus trossulus

Copper 

chloride 100 min. Reduced fertilization success 100 90.9 Fitzpatrick et al. 2008

Pacific blue mussel (embryo),

Mytilus trossulus

Copper 

chloride 2 Increased abnormal larval development 10 9.09 Fitzpatrick et al. 2008
E

-6

Species Chemical

Duration 

(days) Effect

Effect 

Concentration (total μg/L)

Effect 

Concentration

(dissolved μg/L) Reference

Bay scallop,

Argopecten irradians

- 42 EC50

(growth) 5.8 Pesch et al. 1979

Bay scallop,

Argopecten irradians

- 119 100% mortality5

Zaroogian and Johnson 

1983

Pacific oyster (embryo),

Crassostrea gigas

Copper 

chloride

2

EC50

(development) 10 9.09 Harrison et al. 1981

Pacific oyster (embryo),

Crassostrea gigas

Copper 

chloride

2

EC50

(development)

(2 mg/L humic matter added)

28 25.45 Harrison et al. 1981

Pacific oyster (embryo),

Crassostrea gigas

Copper 

chloride

2

NOEC

(development)

2 1.676 Coglianese 1982

Pacific oyster (embryo, ≤4 hr),

Crassostrea gigas

Copper 

sulfate

3

EC50

(arrested development) 4.46 3.737 Worboys et al. 2002

Pacific oyster (embryo),

Crassostrea gigas

Copper 

chloride

1

EC50

(normal D-stage larval development) 20.77 18.88 Brooks et al. 2007

Pacific oyster (embryo),

Crassostrea gigas

Copper 

chloride

1

EC50

(normal D-stage larval development) 24.33 22.12 Brooks et al. 2007

Pacific oyster (embryo),

Crassostrea gigas

Copper 

chloride

1

EC50

(normal D-stage larval development) 41.09 37.35 Brooks et al. 2007

Pacific oyster (embryo),

Crassostrea gigas

Copper 

chloride

1

EC50

(normal D-stage larval development) 37.87 34.42 Brooks et al. 2007

Pacific oyster (embryo),

Crassostrea gigas

Copper 

chloride

1

EC50

(normal D-stage larval development) 38.17 34.70 Brooks et al. 2007

Pacific oyster (embryo),

Crassostrea gigas

Copper 

chloride

1

EC50

(normal D-stage larval development) 40.52 36.83 Brooks et al. 2007

Eastern oyster (larva),

Crassostrea virginica

- 12 LC50 46- Calabrese et al. 1977

Common rangia,

Rangla cuneata

-4

LC50

(<1 g/kg salinity) 210

- Olson and Harrel 1973

Quahog clam (larva),

Mercenaria mercenaria

- 8.0 - 10 LC50 30- Calabrese et al. 1977

Quahog clam (larva),

Mercenaria mercenaria

- 77 LC50 25-

Shuster and Pringle 

1968

Common Pacific littleneck,

Protothaca staminea

- 17 LC50 39- Roesijadi 1980

Soft-shell clam,

Mya arenaria

-7 LC50 35- Eisler 1977

Copepod,

Undinula vulgaris

-1 LC50 192- Reeve et al. 1976

Copepod,

Euchaeta marina

-1 LC50 188- Reeve et al. 1976
E

-7

Species Chemical

Duration 

(days) Effect

Effect 

Concentration (total μg/L)

Effect 

Concentration

(dissolved μg/L) Reference

Copepod,

Metridia pacifica

-1 LC50 176- Reeve et al. 1976

Copepod,

Labidocera scotti

-1 LC50 132- Reeve et al. 1976

Copepod, 

Acartia clausi

-2 LC50 34-82-

Moraitou-

Apostolopoulou 1978

Copepod, 

Acartia tonsa

-6 LC50 9.0 - 7.3- Sosnowski et al. 1979

Copepod, 

Acartia tonsa

-1 LC50 104 - 311- Reeve et al. 1976

Copepod (adult), 

Acartia tonsa

Copper 

chloride

2 LC50 ~40 36.36 Pinho and Bianchini 

2010

Copepod (adult), 

Acartia tonsa

Copper 

chloride

2 LC50 ~90 81.81 Pinho and Bianchini 

2010

Copepod (adult), 

Acartia tonsa

Copper 

chloride

2 LC50 ~110 99.99 Pinho and Bianchini 

2010

Copepod (adult), 

Nitokra spinipes

Copper 

sulfate

3 LC50 323 293.6 Ward et al. 2011

Copepod (nauplii, 24 hr), 

Eurytemora affinis

Copper 

chloride

2 LC50- 83.0 Hall et al. 1997

Copepod (nauplii, 24 hr), 

Eurytemora affinis

Copper 

chloride

8 LC50- 64.0 Hall et al. 1997

Copepod (nauplii, <24 hr), 

Tisbe battagliai

Copper 

sulfate

2 LC50 83.1- Diz et al. 2009

Copepod (adult gravid female), 

Tisbe battagliai

Copper 

sulfate

3 LC50 157- Diz et al. 2009

Copepod (adult gravid female), 

Tisbe battagliai

Copper 

sulfate

3

EC50

(fecundity) 30.8

- Diz et al. 2009

Copepod,

Tisbe holothuriae

-2 LC50 80-

Moraitou-

Apostolopoulou and 

Verriopoulos 1982

Copepod (mixed species, nauplii)-1 LC50 90- Reeve et al. 1976

Amphipod,

Ampelisca abdita

-7 LC50 90-

Scott et al. 

(Manuscript)

Euphauslid,

Euphausia pacifica

-1 LC50 14 - 30- Reeve et al. 1976

Grass shrimp,

Palaemonetes pacifica

-4 LC50 12,600-

Curtis et al. 1979; 

Curtis and Ward 1981

Coon stripe shrimp

(larva/zoea, stage 1),

Pandalus danae

Copper 

sulfate 46 Development 13.42 12.20 Young et al. 1979
E-8

Species Chemical

Duration 

(days) Effect

Effect 

Concentration

(total μg/L)

Effect 

Concentration

(dissolved μg/L) Reference

Sand shrimp (adult, 61 mm),

Crangon sp.

Copper 

chloride 4 LC50 898 - Dinnel et al. 1989

Shrimp (adult), 

Crangon crangon 

Copper 

sulfate 2 LC50 29,500 24,721 Connor 1972

Whiteleg shrimp 

(juvenile, 5-6.5 cm),

Litopenaeus vannamei

Copper 

chloride 28 Gill alterations 186.5 156.3 Frias-Espericueta et al. 2008a

Whiteleg shrimp (juvenile, 1.5-2 g), 

Litopenaeus vannamei

Copper 

sulfate 4 LC50 35,120 29,431 Frias-Espericueta et al. 2008b

Whiteleg shrimp

(juvenile, 11.74 cm, 9.40 g),

Litopenaeus vannamei

Copper 

chloride 4

NOEC-LOEC

(increase hemolymph clotting time) 370-3,730 -

Bautista-Covarrubias 

et al. 2015

Pacific asteroid (sperm/egg), 

Asterias amurensis

Copper 

chloride 80 min. EC50(fertilization) 200 167.6 Lee et al. 2004

Sand dollar (gamete), 

Dendraster excentricus

Copper 

sulfate 40 min. NOEC(fertilization) 10 8.380 Bailey et al. 1995

Sand dollar (gamete), 

Dendraster excentricus

Copper 

sulfate 40 min. NOEC(fertilization) 13.1 10.98 Bailey et al. 1995

Sand dollar (sperm), 

Dendraster excentricus

Copper 

chloride 80 min. EC50(fertilization) 26 23.63 Dinnel et al. 1989

Blue crab (juvenile, 8.3 cm, 43.4 g),

Callinectes sapidus

Copper 

chloride 4 LC50 - 33.75 Martins et al. 2011b

Blue crab (juvenile, 8.3 cm, 43.4 g),

Callinectes sapidus

Copper 

chloride 4 LC50 - 3,367 Martins et al. 2011b

Shore crab (adult), 

Carcinus maenas

Copper 

sulfate 2 LC50 109,000 91,342 Connor 1972

Long-spined sea urchin (embryo),

Diadema antillarum

Copper 

sulfate ~ 40 hr EC50(abnormal development) - 11 Bielmyer et al. 2005b

Sea urchin (sperm), 

Arbacia punctulata - - 58% decrease in sperm motility 300 -

Young and Nelson 

1974

Sea urchin (sperm/egg), 

Arbacia punctulata - 80 min. IC50(fertilization) 27.7 23.21 Neiheisel and Young 1992

Sea urchin (sperm/egg), 

Arbacia punctulata - 80 min. IC50(fertilization) 34.6 28.99 Neiheisel and Young 1992

Sea urchin (sperm/egg), 

Arbacia punctulata - 80 min. IC50(fertilization) 47.7 39.97 Neiheisel and Young 1992

Sea urchin (embryo, 1 hpf), 

Arbacia punctulata

Copper 

sulfate 2

IC50

(fertilization) 28.0 21.4

Science Applications 

International 

Corporation 1993

Green sea urchin (sperm), 

Strongylocentrotus droebachiensis

Copper 

chloride 80 min. EC50(fertilization) 59 53.63 Dinnel et al. 1989
E

-9

Species Chemical

Duration 

(days) Effect

Effect 

Concentration (total μg/L)

Effect 

Concentration

(dissolved μg/L) Reference

Red sea urchin (sperm), 

Strongylocentrotus franciscanus

Copper 

chloride 80 min. EC50(fertilization) 1.9 1.727 Dinnel et al. 1989

Sea urchin (embryo), 

Paracentrotus lividus

-2 LC50 >500 >419.0 Radenac et al. 2001

Sea urchin (embryo), 

Paracentrotus lividus

-2

LOEC

(development) 50 41.9 Radenac et al. 2001

Purple sea urchin (sperm), 

Strongylocentrotus purpuratus

Copper 

chloride 80 min. EC50(fertilization) 25 22.73 Dinnel et al. 1989

Purple sea urchin (gamete), 

Strongylocentrotus purpuratus

Copper 

sulfate 40 min. NOEC(fertilization) 20 16.76 Bailey et al. 1995

Purple sea urchin (gamete), 

Strongylocentrotus purpuratus

Copper 

sulfate 40 min. NOEC(fertilization) 19.7 16.51 Bailey et al. 1995

White sea urchin (egg/sperm), 

Lytechinus pictus

Copper 

sulfate 20 min. IC50(fertilization) 180 150.8 Jonczyk et al. 2001

White sea urchin (egg/sperm), 

Lytechinus pictus

Copper 

sulfate 20 min. IC50(fertilization) 90.9 76.17 Jonczyk et al. 2001

White sea urchin (egg/sperm), 

Lytechinus pictus

Copper 

sulfate 20 min. IC50(fertilization) 277 232.1 Jonczyk et al. 2001

White sea urchin (egg/sperm), 

Lytechinus pictus

Copper 

sulfate 20 min. IC50(fertilization) 120 100.6 Jonczyk et al. 2001

White sea urchin (egg/sperm), 

Lytechinus pictus

Copper 

sulfate 20 min. IC50(fertilization) 122 102.2 Jonczyk et al. 2001

White sea urchin (egg/sperm), 

Lytechinus pictus

Copper 

sulfate 20 min. IC50(fertilization) 152 127.4 Jonczyk et al. 2001

White sea urchin (egg/sperm), 

Lytechinus pictus

Copper 

sulfate 20 min. IC50(fertilization) 135 113.1 Jonczyk et al. 2001

White sea urchin (egg/sperm), 

Lytechinus pictus

Copper 

sulfate 20 min. IC50(fertilization) 249 208.7 Jonczyk et al. 2001

White sea urchin (egg/sperm), 

Lytechinus pictus

Copper 

sulfate 20 min. IC50(fertilization) 33.4 27.99 Jonczyk et al. 2001

White sea urchin (egg/sperm), 

Lytechinus pictus

Copper 

sulfate 20 min. IC50(fertilization) 51.8 43.41 Jonczyk et al. 2001

White sea urchin (egg/sperm), 

Lytechinus pictus

Copper 

sulfate 20 min. IC50(fertilization) 243 203.6 Jonczyk et al. 2001

White sea urchin (egg/sperm), 

Lytechinus pictus

Copper 

sulfate 20 min. IC50(fertilization) 20.8 17.43 Jonczyk et al. 2001

White sea urchin (egg/sperm), 

Lytechinus pictus

Copper 

sulfate 20 min. IC50(fertilization) 20.9 17.51 Jonczyk et al. 2001

White sea urchin (egg/sperm), 

Lytechinus pictus

Copper 

sulfate 20 min. IC50(fertilization) 55.7 46.68 Jonczyk et al. 2001
E

-10

Species Chemical

Duration 

(days) Effect

Effect 

Concentration (total μg/L)

Effect 

Concentration

(dissolved μg/L) Reference

White sea urchin (egg/sperm), 

Lytechinus pictus

Copper 

sulfate 20 min. IC50(fertilization) 126 105.6 Jonczyk et al. 2001

White sea urchin (egg/sperm), 

Lytechinus pictus

Copper 

sulfate 20 min. IC50(fertilization) >200 >167.6 Jonczyk et al. 2001

Arrow worm,

Sagitta hispida

-1 LC50 43 - 460- Reeve et al. 1976

Cuttlefish (egg),

Sepia officinalis

Copper 

chloride 50 NOEC

-LOEC

(hatchling weight) 2.3 

- 23-

Lacoue-Labarthe et al. 

2010

Atlantic menhaden,

Brevoortia tyrannus

- 14 LC50 610- Engel et al. 1976

Topsmelt (larva, 9d), 

Atherinops affinis

Copper 

chloride

7

LC50

(test species fed) 162 147.3 Anderson et al. 1994

Topsmelt (larva, 9d), 

Atherinops affinis

Copper 

chloride

7

LC50

(test species fed) 55.7 50.63 Anderson et al. 1994

Topsmelt (larva), 

Atherinops affinis

Copper 

chloride

7 LC50 365 331.8 McNulty et al. 1994

Topsmelt (larva, 9d), 

Atherinops affinis

Copper 

chloride

7 LC50 134 121.8 McNulty et al. 1994

Pacific herring (embryo),

Clupea harengus pallasi

-6 Incipient LC50 33-

Rice and Harrison 

1978

Pacific herring (larva),

Clupea harengus pallasi

-2 Incipient LC50 900-

Rice and Harrison 

1978

Atlantic cod (embryo),

Gadus morhua

- 14 LC50 10-

Swedmark and 

Granmo 1981

Mummichog,

Fundulus heteroclitus

- 21 Histopathological lesions <500-

Gardner and La Roche 

1973

Mummichog,

Fundulus heteroclitus

-4 Enzyme inhibition 600- Jackim 1973

Atlantic silverside,

Menidia menidia

-4 Histopathological lesions <500-

Gardner and La Roche 

1973

Sheepshead minnow (larva, ≤24 hr), 

Cyprinodon variegatus 

Copper 

nitrate

4

LC50

(test species fed) >220 >200.0 Hutchinson et al. 1994

Sheepshead minnow (larva, ≤24 hr), 

Cyprinodon variegatus 

Copper 

nitrate

7 Survival 160 145.4 Hutchinson et al. 1994

Northern anchovy (embryo), 

Engraulis mordax

Copper 

chloride 32 hr LC50 185 168.2 Rice et al. 1980

Northern anchovy (larva), 

Engraulis mordax

Copper 

chloride 46 hr LC50 372 338.1 Rice et al. 1980

Pinfish,

Lagodon rhomboides

- 14 LC50 150- Engel et al. 1976
E-11

Species Chemical

Duration 

(days) Effect

Effect 

Concentration

(total μg/L)

Effect 

Concentration

(dissolved μg/L) Reference

Spot,

Leiostomus xanthurus - 14 LC50 160 - Engel et al. 1976

Atlantic croaker,

Micropogonias undulatus - 14 LC50 210 - Engel et al. 1976

Winter flounder,

Pseudopleuronectes americanus - 14 Histopathological lesions 180 - Baker 1969

Cobia (egg), 

Rachycentron canadum

Copper 

sulfate 1 LC50 91 76.26 Dung et al. 2005

Cobia (larva, 1 d), 

Rachycentron canadum

Copper 

sulfate 4 LC50 60 50.28 Dung et al. 2005

Cobia (juvenile, 20 d), 

Rachycentron canadum

Copper 

sulfate 4 LC50 87 72.91 Dung et al. 2005

Cobia (young, 40 d), 

Rachycentron canadum

Copper 

sulfate 4 LC50 240 201.1 Dung et al. 2005

Mahi mahi (4 hpf, blastula stage), 

Coryphaena hippurus

Copper 

chloride 2 LC50 15.5 14.09 Adema-Hannes and Shenker 2008

Mangrove killifish

(adult, 2.5 cm, 0.5 g), 

Kryptolebias marmoratus

Copper 

chloride 2

LOEC

(MT transcript induction) 10 8.380 Rhee et al. 2009
F-1

Appendix F Data Not Used in the Development of the Aquatic Life Ambient 

Estuarine/Marine Water Quality Criteria for Copper
F-2

Appendix Table F-1. Unused Studies Along with Reason.

Species Reference Reason Data Classified as Unused

Green mussel,

Perna viridis Aanand et al. 2010 Only one exposure concentration

Herring,

Clupea harengus Abbasi and Sheckley 1995 Only three exposure concentrations

Oyster,

Crassostrea virginica 

Abbe and Sanders 1986 Mixture

Oyster,

Crassostrea virginica 

Abbe and Sanders 2000 Mixture, Field exposure

Bivalve,

Malcoma balthica Absil et al. 1993 Steady state not reached for bioaccumulation study; Exposed in situ

Blue mussel,

Mytilus edulis Adema et al. 1972 Lack of detail (foreign language)

Sheepshead minnow,

Cyprinodon variegatus Adeyemi and Klerks 2012 Only one exposure concentration

Sheepshead minnow,

Cyprinodon variegatus Adeyemi et al. 2012 Only one exposure concentration

Mediterranean sponge,

Crambe crambe Agel et al. 2001 Pre-exposure to toxicant

European eel,

Anguilla anguilla Ahmad et al. 2005 Only two exposure concentrations

European eel,

Anguilla anguilla Ahmad et al. 2008 Only two exposure concentrations

Crab,

Scylla serrata Ahmed et al. 1997 Only one exposure concentration

Amphipod,

Allorchestes compressa Ahsanullah and Williams 1991 Low control survival (77.5%)

Teleost,

Trematomus bernacchii

Teleost,

Chionodraco hamatus

Albergoni et al. 2000 Mixture; Survey, so prior exposure to many 

chemicals

Various species Alekseev et al. 2010 Dilution water not characterized

Cyanobacteria,

Cyanobium sp. Alquezar and Anastasi 2013 Algal study

Turbot,

Scophthalmus maximus Alvarado et al. 2005 Only two exposure concentrations; No information on seawater

Turbot,

Scophthalmus maximus Alvarado et al. 2006 Only two exposure concentrations

Sea urchin,

Paracentrotus lividus Amaroli et al. 2013 Only one exposure concentration

Polychaete,

Nereis diversicolor

Peppery furrow shell,

Scrobicularia plana

Common shrimp,

Crangon crangon

European flounder,

Platichthys flesus 

Amiard et al. 1985 No control information; No information on 

dilution water

Blue mussel,

Mytilus edulis Amiard-Triquet et al. 1986 Bioaccumulation: steady state not documented (16 day exposure)

Potworm,

Enchytraeus albidus

Amorim and Scott-Fordsmand 

2012 Terrestrial exposure
F-3

Species Reference Reason Data Classified as Unused

Various species Anderson and Norberg-King 

1991

Lack of exposure details; dilution water not 

characterized

Diatom,

Phaeodactylum tricornutum Angel et al. 2015 Only one exposure; Pulsed exposure

Anemone,

Bunodosoma cangicum Anjos et al. 2014 Not North American species; Only two exposure concentrations

Mediterranean mussel,

Mytilus galloprovincialis Arnold et al. 2005 Modeling study (BLM)

Mussel,

Mytilus sp. Arnold and Cotsifas 2008 Review and analysis of previously reported data

Green Mussel,

Perna viridis Arockia Vasanthi et al. 2012 Field survey, exposure concentration not known

Flathead mullet,

Mugil cephalus Arockia Vasanthi et al. 2013 Field survey, exposure concentration not known

Mangrove crab,

Scylla serrata

Arumugam and Ravindranath 

1987 Not North American species; No LC50 data

Oyster,

Crassostrea virginica Ayling 1974 Mixture

Blue mussel,

Mytilus edulis Bakhmet et al. 2012 Only three exposure concentrations

Polychaete,

Hydroides elegans Bao et al. 2010 Effect of copper on biofilm development and larval settlement

Copepod,

Tigriopus japonicus Bao et al. 2013 Not North American species

Brown mussel,

Perna perna Baraj et al. 2011 Only one exposure concentration

Copepod,

Tigriopus brevicornis Barka 2007 Only three exposure concentrations

Copepod,

Tigriopus brevicornis Barka et al. 2010 Only three exposure concentrations

Blue shark,

Prionace glauca Barrera-Garcia et al. 2013 Field survey, exposure concentration not known

Isopod,

Idotea baltica Bat et al. 199b LT50 is the endpoint

Sea urchin,

Strongylocentrotus purpuratus Bay et al. 1983 Only two exposure concentrations

Echinoid,

Phylum Echinodermata Bay et al. 1993 Review 

Coral Berry et al. 2013 Field survey, exposure concentration not 

known

Amphipod,

Parhalella natalensis Bhat and Vamsee 1993 Discrepancy in results; No control information

Hybrid striped bass,

Morone chrysops x Morone 

saxatilis

Bielmyer et al. 2005a Bioaccumulation: steady state not documented

Hybrid striped bass,

Morone chrysops x Morone 

saxatilis

Bielmyer et al. 2006a Only two fish per concentration

Copepod,

Acartia tonsa Bielmyer et al. 2006b Dietary exposure
F-4

Species Reference Reason Data Classified as Unused

Coral,

Acropora cervicornis

Coral,

Pocillopora damicornis

Coral,

Montastrea faveolata

Dinoflagellate,

Symbiodinium sp.

Bielmyer et al. 2010 Exposed coral and algal species at the same 

time

Sea urchin,

Strongylocentrotus 

droebachiensis

Bielmyer et al. 2012 Dietary exposure

Sydney rock oyster,

Saccostrea commercialis Birch and Hogg 2011 Not North American species; Sediment exposure

Amphipod,

Gammarus annulatus Bisbal 1987 Only two exposure concentrations

Oyster,

Saccostrea cucullata Biswas et al. 2013 Field survey, exposure concentration not known

Killifish,

Fundulus heteroclitus Blanchard and Grosell 2005 Bioaccumulation: steady state not documented

Killifish,

Fundulus heteroclitus Blanchard and Grosell 2006 Only two exposure concentrations

Oyster,

Crassostrea virginica Blanchard et al. 2009 Bioaccumulation: steady state not documented

Plaice,

Pleuronectes platessa

Herring,

Clupea harengus

Blaxter 1977 Only one exposure concentration

Striped bass,

Morone saxatilis Bodammer 1985 No control information; Culture water contained 57 ug/L copper

American sand lance,

Ammodytes americanus Bodammer 1987 Only two exposure concentrations

Atlantic horseshoe crab,

Limulus polyphemus Botton and Itow 2009 Review

Brown mussel,

Perna perna Boudjema et al. 2014 Only three exposure concentrations

Crab,

Neohelice granulata

Clam,

Mesodesma mactroides

Boyle et al. 2013 Not North American species; Only one 

exposure concentration

Ostracod,

Diacypris compacta Brooks et al. 1995 Hypersaline conditions in exposure media

Three Mytlius species Brooks et al. 2015 Bioaccumulation: unmeasured exposure

Red seaweed,

Gracilariopsis longissima Brown et al. 2012 Algal study

Gastropod,

Littorina littoralis

Brown seaweed,

Fucus vesiculosus

Bryan 1983 Mixture

Peppery furrow shell,

Scrobicularia plana

Polychaete,

Hediste diversicolor

Buffet et al. 2011 Only one exposure concentration

Polychaete,

Hediste diversicolor Burlinson and Lawrence 2007a Mixture (field exposure)
F-5

Species Reference Reason Data Classified as Unused

Polychaete,

Hediste diversicolor Burlinson and Lawrence 2007b Prior exposure (sequentially exposed to increasing copper)

Amphipod,

Melita plumulosa

Copepod,

Nitocra spinipes

Campana et al. 2012 Sediment exposure

Sheepshead,

Archosargus probatocephalus Cardeilhac et al. 1979 Only one exposure concentration

Polychaete,

Arenicola marina Casado-Martinez et al. 2010 Sediment exposure

Mediterranean mussel,

Mytilus galloprovincialis Casas et al. 2008 Mixture

Starfish,

Asterias rubens

White sea urchin,

Echinus acutus

Catarino et al. 2008 Mixture

Mediterranean sponge,

Chondrosia reniformis Cebrian et al. 2006 Mixture

Mediterranean sponge,

Crambe crambe

Mediterranean sponge,

Scopalina lophyropoda

Cebrian and Uriz 2007a Only one exposure concentration

Mediterranean sponge,

Scopalina lophyropoda Cebrian and Uriz 2007b Only one exposure concentration

Sponge cell Cebrian and Uriz 2007c Only two exposure concentrations

Wedge sole,

Dicologlossa cuneata

Brill,

Scophthalmus rhombus

Senegalese sole,

Solea senegalensis 

Chairi et al. 2010 Injected toxicant; Not North American species

Oyster,

Saccostrea cucullata Chaharlang et al. 2012 Field survey, exposure concentration not known

Oyster,

Crassostrea virginica

Oyster,

Crassostrea gigas

Chang 1995 Exposure via biofilm

Oyster,

Crassostrea virginica

Oyster,

Crassostrea gigas

Chang et al. 1996 Exposure via biofilm

Mussel,

Mytilus trossulus Chelomin et al. 1998 Mixture

Goby,

Synechogobius hasta Chen et al. 2013 Not North American species; Only two exposure concentrations

Oyster,

Crassostrea gigas Cheng 1988a Only one exposure concentration

Oyster,

Crassostrea gigas Cheng 1988b Only one exposure concentration

Gastropod,

Babylonia lutosa Cheung and Wong 1998 Only three exposure concentrations

Hagfish Chiu and Mok 2011 Field survey, exposure concentration not 

known
F-6

Species Reference Reason Data Classified as Unused

Rockbream,

Oplegnathus fasciatus Cho et al. 2006 Only three exposure concentrations

Red alga,

Porphya yezoensis Choi et al. 2005 Lack of exposure details; number of exposure concentrations not provided

Snail,

Bulinus rohlfsi Chu 1976 Formulation (50% copper sulfate)

Alga,

Colpomenia sinuosa Cirik et al. 2012 Adsorption study

Mussel,

Echyridella menziesii Clearwater et al. 2014 Not North American species

Bivalve,

Bathymodiolus azoricus Company et al. 2008 Only one exposure concentration

Brown seaweed,

Ascophyllum nodosum

Brown seaweed,

Fucus vesiculosus

Connan and Stengel 2011 Only three exposure concentrations

Snail,

Ilyanassa obsoleta Conrad 1988 Mixture (copper and antibiotic)

Kelp,

Lessonia nigrescens Contreras et al. 2007 Not North American species

Amphipod,

Gammarus locusta Correia et al. 2002a Only three exposure concentrations

Amphipod,

Gammarus locusta Correia et al. 2002b Only three exposure concentrations

Sea bass,

Dicentrarchus labrax Cotou et al. 2009 Mixture (source of copper was antifouling painted nets); Not North American species

European sea bass,

Dicentrarchus labrax Cotou et al. 2012 Inappropriate form of toxicant (copper-treated nets)

Black-chinned tilapia,

Sarotherodon melanotheron Coulibaly et al. 2012 Field survey, exposure concentration not known

Epibionts Crespo et al. 2014 Only one exposure concentration

Blue mussel,

Mytilus edulis Curtis et al. 2000 Only four organisms per concentration

Rough periwinkle,

Littorina saxatilis Daka and Hawkins 2004 Mixture

Pacific oyster,

Crassostrea gigas Damiens et al. 2006 Only three exposure concentrations

Black sea bream,

Acanthopagrus schlegeli Dang et al. 2009 Prior exposure 

Blackhead seabream,

Acanthopagrus schlegelii 

schlegelii

Dang et al. 2012 Not North American species

Scallop,

Pecten maximus

Pacific oyster,

Crassostrea gigas

Davies and Paul 1986 Inappropriate form of toxicant (copper oxidebased anti-fouling paint)

Spiny dogfish,

Squalus acanthias De Boeck et al. 2007 Only three exposure concentrations

Spotted dogfish,

Scyliorhinus canicula De Boeck et al. 2010 Only one exposure concentration; Not North American species

Mediterranean mussel,

Mytilus galloprovincialis Deruytter et al. 2013 Test results not reported, only the model developed

Guppy,

Poecilia vivipara de Souza Machado et al. 2013 Not North American species
F-7

Species Reference Reason Data Classified as Unused

Snakehead catfish,

Channa striata Devi and Gopal 1986 Not North American species

Asian paddle crab,

Charybdis japonica Ding and Wang 2010 Not North American species; Text in foreign language

Mediterranean mussel,

Mytilus galloprovincialis Dragun et al. 2010 Mixture; Survey, so prior exposure to many chemicals

Duran and Beiras 2013 Review of previously published studies

Sea urchin,

Strongylocentrotus intermedius

Sea urchin,

Strongylocentrotus nudus

Durkina 1995 Only three exposure concentrations

Polychaete,

Nereis diversicolor Durou et al. 2005 LT50 is the endpoint

Dinoflagellate,

Cochlodinium polykrikoides Ebenezer and Ki 2012 Algal study

Sea urchin,

Tripneustes gratilla Edullantes and Galapate 2014 Not North American species

Mummichog,

Fundulus heteroclitus Eisler and Gardner 1973 Mixture

Clam,

Macoma balthica Eldon et al. 1980 Dilution water not characterized

Oyster,

Saccostrea cucullata

Oyster,

Crassostrea lugubris

Oyster,

Crassostrea belcheri

Elfwing and Tedengren 2002 Only one exposure concentration

Barnacle,

Elminius modestus Elliott et al. 1985a Bioaccumulation: static, unmeasured exposure

Mussel,

Mytilus edulis planulatus Elliott et al. 1985b Bioaccumulation: steady state not achieved

Crab,

Carcinus maenas Elumalai et al. 2005 Only nine animals per concentration

Coral El-Sorogy et al. 2012 Field survey, exposure concentration not 

known

Oyster Engel and Fowler 1979 Only two exposure concentration

Mediterranean mussel,

Mytilus galloprovincialis Fabbri and Capuzzo 2006 Only one exposure concentration

Sea urchin,

Paracentrotus lividus Fabbrocini and D'Adamo 2011 Not North American species; Lack of details (no control information/procedures)

Benthic foraminiferal 

assemblages Fabrizio and Rodolfo 2012 Sediment present in media

Mediterranean mussel,

Mytilus galloprovincialis Fafandel et al. 2008 Only three exposure concentrations

Fish,

Etroplus maculatus

Clam,

Villorita cyprinoides var.

cochinensis

Prawn,

Macrobranchium idella idella

Crab,

Paratelphusa hydrodromus

Fernandez et al. 1996 Dilution water not characterized
F-8

Species Reference Reason Data Classified as Unused

Polychaete,

Laeonereis acuta 

Ferreira-Cravo et al. 2009 Only one exposure concentration

Ascidian,

Ciona intestinalis Ferro et al. 2013 Only one exposure concentration

Rotifer,

Brachionus plicatilis Filenko and Samoylova 2008 Dilution water not characterized

Whiting,

Merlangius merlangus

Goatfish,

Mullus barbatus

Findik and Cicek 2011 Field survey, exposure concentration not 

known

Blue mussel,

Mytilus edulis Fokina and Nemova 2012 Lack of detail (abstract only)

Blue mussel,

Mytilus edulis Fokina et al. 2013 Only three exposure concentrations

Sole,

Solea senegalensis Fonseca et al. 2009 Only three exposure concentrations

Copepod,

Tigriopus brevicornis Forget et al. 1999 Mixture

Ascidian,

Ciona intestinalis Franchi et al. 2012 Only one exposure concentration

Oyster,

Crassostrea gigas Frazier 1976 Mixture

Japanese flounder,

Paralichthys olivaceus

Red Sea bream,

Pagrus major

Furuta et al. 2008 Not North American species

Seam bream,

Sparus aurata

Bivalve,

Scapharca inaequivalvis

Gabbianelli et al. 2003 Only one exposure concentration

Sole,

Solea senegalensis Galindo et al. 2012 Field survey, exposure concentration not known

Barnacle,

Amphibalanus variegatus Gall et al. 2013 Not North American species

Sea squirt,

Styela plicata Galletly et al. 2007 Only three exposure concentrations

Rotifer,

Brachionus rotundiformis Gama-Flores et al. 2005 Not North American species

Isopod,

Idotea baltica Gambardella et al. 1998 Only acclimated one day

Brown flagellate,

Isochvysis sp. Garr 2012 Algal study

Asteroid,

Coscinasterias muricata Georgiades et al. 2006 Only three exposure concentrations

Polychaete,

Laeonereis acuta Geracitano et al. 2002 Only two exposure concentrations

Polychaete,

Laeonereis acuta Geracitano et al. 2004 Only two exposure concentrations

Oyster,

Crassostrea gigas

Mussel,

Mytilus edulis

Geret et al. 2002a Bioaccumulation: unmeasured exposure and 

steady state not achieved

Clam,

Ruditapes decussatus Geret et al. 2002b Only three exposure concentrations
F-9

Species Reference Reason Data Classified as Unused

Isopod,

Exosphaeroma gigas Giarratano et al. 2007 Only 24 hour acclimation

Coon stripe shrimp,

Pandalus danae Gibson 1976 Acclimated to one temperature and tested at another

Clam,

Paphia malabarica Gireesh and Gopinathan 2009 Only one exposure concentration

Copepod,

Acartia sinjiensis Gissi et al. 2013 Not North American species

Alga,

Phaeocystis antarctica Gissi et al. 2015 Not North American species

Coho salmon,

Oncorhynchus kisutch

Masu salmon,

Oncorhynchus masou

Siberian sturgeon,

Acipenser baeri

Glubokov 1990 No dose response

Doughboy scallop,

Mimachlamys asperrima Golding et al. 2006 No toxicity information; Not North American species

Mediterranean mussel,

Mytilus galloprovincialis Gomes et al. 2011 Only one exposure concentration

Mediterranean mussel,

Mytilus galloprovincialis Gomes et al. 2013 Only one exposure concentration

Protozoa,

Euplotes crassus Gomiero et al. 2012a Protozoa; Lack of details (abstract only)

Protozoa,

Euplotes crassus Gomiero et al. 2014 Protozoa

Polychaete,

Hydroides elegans Gopalakrishnam et al. 2007 Prior exposure

Abalone,

Haliotis rubra Gorski and Nugegoda 2006b Lack of detail (not sure what units the effect concentration is in)

Giant sea scallop,

Placopecten magellanicus Gould et al. 1985 Bioaccumulation: steady state not achieved

Giant sea scallop,

Placopecten magellanicus Gould et al. 1986 Lack of details (abstract only)

White prawn,

Penaeus indicus

Green mussel,

Perna viridis

Brine shrimp,

Artemia salina

Govindarajan et al. 1993 Lack of details (procedure)

European eel,

Anguilla anguilla Gravato et al. 2006 Prior exposure

Skate,

Raja erinacea

Sculpin,

Myoxocephalus 

octodecemspinosus

Grosell et al. 2003 Only two exposure concentrations

Brine shrimp,

Artemia franciscana

Cladoceran,

Daphnia magna

Alga,

Selenastrum capricornutum

Guida et al. 2008 Mixed species exposure
F-10

Species Reference Reason Data Classified as Unused

Dinoflagellate,

Prorocentrum minimum Guo and Ki 2012 Algal study

Dinoflagellate,

Prorocentrum minimum Guo et al. 2012 Algal study

Abalone,

Haliotis discus Guo et al. 2013 Not North American species

Babylon snail,

Babylonia areolata

Hajimad and Vedamanikam 

2014 Not North American species

Handy 2003 Review

Amphipod Hanna et al. 2013 Inappropriate form of toxicant (nanoparticles)

Shore crab,

Carcinus maenas Hansen et al. 1992 Only one exposure concentration

Blue mussel,

Mytilus edulis Harrison et al. 1983 Only three exposure concentrations

Rats and Mice Hasegawa et al. 1989 Non-aquatic organisms

Polychaete,

Nereis diversicolor Hateley et al. 1989 Mixture (field exposure)

Shore crab,

Carcinus maenas Hebel et al. 1999 Only five organisms per concentration

Coral,

Montipora capitata Hedouin and Gates 2013 Not North American species

Blue mussel,

Mytilus edulis Hellou et al. 2003 Mixture

Dinoflagellate,

Alexandrium catenella Herzi et al. 2013 Contaminated dilution water

Flower crab,

Portunus pelagicus Hilmy et al. 1985 Dilution water not characterized; Not North American species

Blue mussel,

Mytilus edulis Hines et al. 2010 Only two exposure concentrations

Brown mussel,

Perna perna Hodgson and Hoebeke 1984 Only five organisms per concentration

Blue mussel,

Mytilus edulis Hoher et al. 2013 Only three exposure concentrations

Hori et al. 1996 Lack of details (foreign language)

Isopod,

Porcellio scaber Hornung et al. 1998 Sediment present in media

Alga Horta-Puga et al. 2013 Field survey, exposure concentration not 

known

Sea anemone,

Aiptasia pulchella Howe et al. 2012 Not North American species

Sea anemone,

Aiptasia pulchella Howe et al. 2014 Not North American species

Nematode,

Enoplus brevis Howell 1984 LT50 is the endpoint

Various species Hrovat et al. 2009 Review

Red alga,

Gracilaria lemaneiformis

Red alga,

Gracilaria lichenoides

Huang et al. 2013 Algal study

Baltic clam,

Macoma balthica

Cockle,

Cerastoderma edule

Hummel et al. 1998 Sediment present in media

Pacific kelps Huovinen et al. 2010 Only one exposure concentration
F-11

Species Reference Reason Data Classified as Unused

Bivalve,

Austriella cf plicifera Hutchins et al. 2008 Sediment present in media

Bivalve,

Indoaustriella lamprelli Hutchins et al. 2009 Sediment present in media

Protozoa,

Alexandrium minutum Hwang and Lu 2000 Protozoa

Copepod,

Paracyclopina nana Hwang et al. 2010 Only one exposure concentration

Amphipod,

Corophium sp. Hyne and Everett 1998

No control survival information, and author 

suggests poor control survival if no sediment 

present

Seabream,

Sparus aurata

Isani et al. 2012 Not North American species

Indian edible oyster,

Crassostrea madrasensis Ittoop et al. 2009

Not North American species; Only three 

exposure concentrations; Dilution water not 

characterized

Hard clam,

Mercenaria mercenaria Ivanina et al. 2013 Only two exposure concentrations

Filter feeders Jara-Marini et al. 2013 Field survey, exposure concentration not 

known

Copepod,

Tigriopus japonicus Jeong et al. 2014 Not North American species

Pearl oyster,

Pinctada fucata Jing et al. 2006 Only two exposure concentrations

Butterfish,

Poronotus triacanthus Jiraungkoorskul et al. 2007 Only one exposure concentration

Pink shrimp,

Penaeus duorarum

Shrimp,

Penaeus stylirostris

Shrimp,

Penaeus setiferus

Johnson 1974 Only two or three exposure concentrations; 

Purity of test material questionable

Jones et al. 1968 Review

Isopods Jones 1975 Only two exposure concentrations

Brine shrimp,

Artemia salina Jorgensen and Jensen 1977 Brine shrimp used

Mediterranean mussel,

Mytilus galloprovincialis Kanduc et al. 2011 Field survey, exposure concentration not known

Mangrove crab,

Macrophthalmus erato Kannupandi et al. 2001 Only three exposure concentrations

Sea bass,

Dicentrarchus labrax Kentouri et al. 1993 Only one exposure concentration

Killifish,

Aphanius dispar Khan and Khan 1999 Dilution water not characterized; Not North American species

Heliozoon,

Raphidiophrys contractilis Khan et al. 2006 Lack of exposure details; dilution water not characterized

Copepod,

Tigriopus japonicus Ki et al. 2009 Only one exposure concentration; Not North American species

Copepod,

Tigriopus japonicus Kim et al. 2012 Not North American species; Lack of exposure details

Various bivalves Klumpp and Burdon-Jones 

1982 Mixture (field exposure)
F-12

Species Reference Reason Data Classified as Unused

Sea urchin,

Hemicentrotus pulcherrimus

Sea urchin,

Anthocidaris crassispina

Kobayashi and Okamura 2002 Inappropriate form of toxicant (copper 

pyrithione)

Black sea bivalve mollusks,

Anadara inaequivalvis &

Chamelea gallina

Kolyuchlina and Ismailov 2011 Not North American species

Mediterranean mussel,

Mytilus galloprovincialis

Koukouzika and Dimitriadis 

2008 Only one exposure concentration

Shore crab,

Carcinus maenas Krang and Ekerholm 2006 Only two exposure concentrations

Eastern oyster,

Crassostrea virginica Krishnamurthy 1994 Bioaccumulation: static exposure

Nile tilapia,

Oreochromis niloticus Kulac et al. 2013 Only one exposure concentration

Oyster,

Saccostrea cucullata

Snail,

Cerithium rubus

Kumari and Nair 1992 Bioaccumulation: static, unmeasured exposure

Coral,

Platygyra acuta Kwok and Ang 2013 Not North American species

Copepod,

Tigriopus japonicus Kwok et al. 2009 Prior exposure; Not North American species

Cuttlefish,

Sepia officinalis Lacoue-Labarthe et al. 2009 Only one exposure concentration; Not North American species

Sea snail,

Hexaplex trunculus Lahbib et al. 2013 Field survey, exposure concentration not known

Green alga,

Ulva lactuca

Seaweed,

Codium fragile

Seaweed,

Jania rubens

Alga,

Dictyota dichotoma

Laib and Leghouchi 2012 Field survey, exposure concentration not 

known

Red sea bream,

Chrysophrys major Lan and Chen 1991 Lack of detail (text in foreign language)

Copepod,

Acartia tonsa Lauer and Bianchini 2010 Intermittent exposure (12hr exposed and 12hr clean)

Estuarine crab,

Neohelice granulata Lauer et al. 2012 Not North American species; Only one exposure concentration

Crab,

Chasmagnathus granulatus Lavolpe et al. 2004 Only two exposure concentrations

Ammonia (foraminifera) Le Cadre and Debenay 2006 Protozoa

Flatworm,

Stylochus pygmaeus

Lee and Johnston 2007 Only two exposure concentrations

Blue crab,

Callinectes sapidus Lee and Oshima 1998 Lack of exposure details; dilution water not characterized

Blue crab,

Callinectes sapidus Lee et al. 1999 Dilution water not characterized

Copepod,

Tigriopus japonicus Lee et al. 2008a Only two exposure concentrations; Not North American species
F-13

Species Reference Reason Data Classified as Unused

Hairy-handed crab,

Hemigrapsus crenulatus

Shield shell limpet,

Scutus breviculus

Lee et al. 2010 Only two exposure concentrations; Not North 

American species

Blue mussel,

Mytilus edulis

Clam,

Macoma balthica

Lehtonen and Leinio 2003 Only two exposure concentrations

Copepod,

Euchaeta japonica Lewis et al. 1972 Only three exposure concentrations

Polychaete,

Spirobranchus lamarckii Lewis et al. 2013 Not North American species

Gastropod,

Onchidium struma Li et al. 2009 Sediment present in media

Chinese oyster,

Ostrea plicatula Li et al. 2010 Not North American species

Mussel,

Mytilus coruscus Li et al. 2012a Not North American species

Seagrass,

Thalassia hemprichii Li et al. 2012b Not North American species; Only three exposure concentrations

Shrimp,

Penaeus japonicus Liao and Hsieh 1988

LT50 is the endpoint in the acute exposure; 

Chronic and bioaccumulation exposure was 

not measured

Shrimp,

Penaeus chinensis Liu 1995 Lack of detail (text in foreign language)

Fish,

Synechogobius hasta 

Liu et al. 2010 Not North American species; Only two 

exposure concentrations

Four marine bivalves Liu et al. 2012 Mixture

Crescent-banded tigerfish,

Terapon jarbua Long and Wang 2005 Prior exposure

Crab,

Petrolisthes galathinus Lopez Greco et al. 2002 Only two exposure concentrations

Blue mussel,

Mytilus edulis Lorenzo et al. 2005 Bioaccumulation: steady state not achieved

Diatoms Lozano et al. 2014 Only two exposure concentrations

Shore crab,

Carcinus maenas Lundebye and Depledge 1998a Only six organisms per concentration

Shore crab,

Carcinus maenas Lundebye and Depledge 1998b Only six organisms per concentration

Eastern oyster,

Crassostrea virginica Lunz 1972 River water used as dilution water; Bioaccumulation: steady state not achieved

Hermit crab,

Clibanarius longitarsus Lyla and Khan 2011 Not North American species

Eastern oyster,

Crassostrea virginica Macey et al. 2010 Only four organisms per concentration; Only three exposure concentrations

Guppy,

Poecilia vivipara Machado et al. 2013 Not North American species; Only three exposure concentrations

Eastern oyster,

Crassostrea virginica MacInnes 1981 Mixture

Mud snail,

Nassarius obsoletus MacInnes and Thurberg 1973 Too few organisms per exposure concentration (n=5)

Stone-loach,

Nemacheilus barbatulus Mackereth and Smyly 1951 Lack of details (abstract only)
F-14

Species Reference Reason Data Classified as Unused

Spiny lobster,

Panulirus homarus Maharajan et al. 2011 Not North American species; Only two exposure concentrations

Spiny lobster,

Panulirus homarus Maharajan et al. 2012a Not North American species; Only two exposure concentrations

Spiny lobster,

Panulirus homarus Maharajan et al. 2012b Not North American species

Sponge,

Hymeniacidon perlevis Mahaut et al. 2013 Field survey, exposure concentration not known

Pacific oyster,

Crassostrea gigas Mai et al. 2012 Only three exposure concentrations

Diatom,

Odontella mobiliensis Manimaran et al. 2012 Algal study

Various bivalves Manley and Davenport 1979 Review

Grass shrimp,

Palaemonetes pugio Manyin 2008 Only acclimated for 24 hours; Only two exposure concentrations

Grass shrimp,

Palaemonetes pugio Manyin and Rowe 2009 Only three exposure concentrations

Grass shrimp,

Palaemonetes pugio Manyin and Rowe 2010 Only two exposure concentrations

Limpet,

Patella vulgata Marchan et al. 1999 Surgically altered test species

Blue mussel,

Mytilus edulis Martin et al. 1975 Chelating agent used in exposure media

Shore clam,

Ruditapes philippinarum Martin-Diaz et al. 2005 Only one exposure concentration

Blue crab,

Callinectes sapidus Martins et al. 2011a Only one exposure concentration

Persian sturgeon,

Acipenser persicus Mashroofeh et al. 2012 Field survey, exposure concentration not known

Clam,

Sunetta scripta

Mussel,

Perna viridis

Mathew and Damodaran 1997 Only one exposure concentration

Mussel,

Perna viridis

Clam,

Meretrix casta

Mathew and Menon 1984 Insufficient acclimation time

European sea star,

Asterias rubens Matranga et al. 2012 Mixture; Not North American species

Amphipod,

Corophium volutator

Polychaete,

Hediste diversicolor

Mayor et al. 2008 Sediment toxicity test

Amphipod,

Leptocheirus plumulosus McGee et al. 1999 Mixture and sediment exposure

Bryzoa,

Watersipora subtorquata McKenzie et al. 2011 Only two exposure concentrations

Lobster,

Homarus americanus McLeese 1974 LT50 is the endpoint; Only five organisms per concentration

McLeese 1976 Species name not given
F-15

Species Reference Reason Data Classified as Unused

Clam,

Macoma balthica

Shrimp,

Crangon septemspinosa

Shrimp,

Pandalus montagui

Polychaete,

Nereis virens

McLeese and Ray 1986 Only six organisms per concentration

Crab,

Chasmagnathus granulata Medesani et al. 2004a Only one exposure concentration

Crab,

Chasmagnathus granulata Medesani et al. 2004b Only one exposure concentration

Amphipod,

Corophium multisetosum Menchaca et al. 2010 Not North American species; Sediment exposure

Polychaete,

Capitella sp. Mendez and Green-Ruiz 2005 Only three exposure concentrations

Polychaete,

Capitella sp. Mendez and Green-Ruiz 2006 Only three exposure concentrations

Pacific oyster,

Crassostrea gigas Metzger et al. 2012 Only one exposure concentration

Turbot,

Psetta maxima Mhadhbi et al. 2010 Not North American species

Blue-green alga,

Synechococcus sp.

Diatom,

Thalassiosira weissflogii

Dinoflagellate,

Prorocentrum minimum

Miao et al. 2005 Algal study; Excessive NTA in the media

Ribbed mussel,

Geukensia demissa Miller 1986 Lack of details (abstract only)

Ribbed mussel,

Geukensia demissa Miller 1988 Only two exposure concentrations

Meiofaunal community Millward et al. 2001 Mixture

Sea bream,

Sparus aurata Minghetti et al. 2008 Prior exposure

Diatom,

Haslea ostrearia Minier et al. 1998 Algal study

Shrimp,

Penaeus monodon Misra et al. 2005 Not North American species; Dilution water not characterized

White mussel,

Donax trunculus Mizrahi and Achituv 1989 Not North Americans species; Only five organisms per concentration

White mussel,

Donax trunculus Mizrahi et al. 1993 Not North Americans species; Only three exposure concentrations

Mummichog,

Fundulus heteroclitus Mochida et al. 2008 Mixture

Fish Mohan et al. 2012 Field survey, exposure concentration not 

known

Coral Mokhtar et al. 2012 Field survey, exposure concentration not 

known

Pacific oyster,

Crassostrea gigas Money et al. 2011 Mixture
F-16

Species Reference Reason Data Classified as Unused

Mediterranean mussel,

Mytilus galloprovincialis

Blue mussel,

Mytilus edulis

Moore et al. 2007 Only one exposure concentration

Oyster,

Crassostrea gigas Moraga et al. 2005 Only two exposure concentrations

Brown alga,

Ectocarpus siliculosus Morris and Russell 1973 Algal study; Prior exposure (tolerant strain)

Mozambique tilapia,

Oreochromis mossambica Mukhopadhyay 1983 Lack of details (abstract only)

Clam,

Tapes philippinarum Munari and Mistri 2007 Only one exposure concentration; Possible prior exposure

Shrimp,

Penaeus monodon Munshi et al. 1996a Not North American species; Variable time for LC50 values

Shrimp,

Penaeus penicillatus Munshi et al. 1996b Only acclimated for one hour

Blue crab,

Callinectes sapidus Mutlu et al. 2011 Field survey, exposure concentration not known

Pikeperch Nabavi et al. 2012 Field survey, exposure concentration not

known

Mussel,

Mytilus trossolus Nadella et al. 2009 Only acclimated for 24 hours 

Mussel,

Mytilus viridis Nair et al. 1977 Only eight animals per concentration

Common cockle,

Cerastoderma edule Naylor 1987 Not North American species

Blue crab,

Callinectes similis Neff and Anderson 1977 Only three exposure concentrations

Polychaete,

Pectinaria koreni

Polychaete,

Nephthys ciliata

Mussel,

Mytilus calcarea

Mussel,

Mytilus baltica

Neuhoff and Theede 1984 Lack of details (procedure)

Mussel,

Perna viridis Nicholson 1999 Only three exposure concentrations

Green mussel,

Perna viridis Ng and Wang 2007 Mixture

European eel,

Anguilla anguilla Nunes et al. 2014 Only three exposure concentrations

Polychaete,

Eurythoe complanata Nusetti et al. 1998 Only one exposure concentration

Senegal sole,

Solea senegalensis Oliva et al. 2009 Not North American species; Only acclimated for 24 hours

European eel,

Anguilla anguilla Oliveira et al. 2008 Only one exposure concentration

Fish and shellfish Olmedo et al. 2013 Field survey, exposure concentration not 

known

Fish and crustaceans Olsen 2011 Review of previously published studies
F-17

Species Reference Reason Data Classified as Unused

Flat oyster,

Ostrea edulis

Pacific oyster,

Crassostrea gigas

Ong et al. 2013 Field survey, exposure concentration not 

known

Mummichog,

Fundulus heteroclitus Ortiz et al. 1999 Bioaccumulation: static, unmeasured exposure, steady state not achieved

Hermit crab,

Clibanarius africanus Otitoloju and Don-Pedro 2006 Sediment present in media

Alga,

Fucus vesiculosus Owen et al. 2012 Algal study; Only two exposure concentrations

Fish and mollusks Oya et al. 1939 Text in foreign language

Mussel,

Lithophaga lithophaga Ozsuer and Sunlu 2013 Field survey, exposure concentration not known

Blue crab,

Callinectes sapidus Paganini and Bianchini 2009 Excised cells

Sea urchin,

Paracentrotus lividus

Sea urchin,

Echinus esculentus

Pagano et al. 1986 Lack of details (procedures; dilution water not 

characterized)

Sea urchin Pagano et al. 2002 Mixture

Crab,

Charybdis japonica Pan et al. 2011 Not North American species

Copepod,

Tigriopus japonicus Park et al. 2014 Not North American species

Scallop,

Pecten maximus

Oyster,

Crassostrea gigas

Paul and Davies 1986 Formulation (Hard Racing Red)

Red drum,

Sciaenops ocellatus Peppard et al. 1991 Formulation (Copper Control®, 8.5% copper)

Mussel,

Perna perna Pereira et al. 2007 Mixture

Pistol prawn,

Alpheus malabaricus malabaricus

Perumal and Subramanian 

1985 Excessive control mortality (20%)

Polychaete,

Neanthes arenaceodentata Pesch 1979 Only one exposure concentration

Green mussel,

Perna viridis Pillai and Menon 1998 Excised tissue 

Mangrove crab,

Ucides cordatus Pinheiro et al. 2012 Mixture

Copepod,

Acartia tonsa Pinho et al. 2007 Only one exposure concentration

Sea urchin,

Paracentrotus lividus Pinsino et al. 2011 Only one exposure concentration

Bryzoans Piola and Johnston 2009 Surgically altered test species

Polychaete,

Nereis diversicolor Pook et al. 2009 Prior exposure

Amphipod,

Gammarus aequicauda Prato and Biandolino 2005 Sediment toxicity test

Copepod,

Tigriopus fulvus Prato et al. 2013a Not North American species

Amphipod,

Gammarus aequicauda Prato et al. 2013b Only two exposure concentrations

Oyster Prytherch 1931 Mixture (field exposure)
F-18

Species Reference Reason Data Classified as Unused

Mediterranean mussel,

Mytilus galloprovincialis Pytharopoulou et al. 2011 Only three exposure concentrations

Mediterranean mussel,

Mytilus galloprovincialis Pytharopoulou et al. 2013 Only one exposure concentration

Decapod,

Palaemonetes varians Rainbow and Smith 2013 Not North American species

Mullet,

Mugil cephalus Rajkumar and Milton 2011a Dilution water not characterized

Green mussel,

Perna viridis Rajkumar and Milton 2011b Dilution water not characterized

Snail,

Cerithidae cingulata

Bivalve,

Modiolus philippinarum

Ramakritinan et al. 2012 Not North American species

Polychaete,

Nereis sp. Raymont and Shields 1963 Inappropriate form of toxicant (copper sodium citrate)

Crab,

Scylla serrata Reddy 1997 Only one exposure concentration

Green alga,

Enteromorpha compressa Reed and Moffat 1983 Plant study

Antarctic scallop,

Adamussium colbecki Regoli et al. 1997 Only one exposure concentration

Antarctic scallop,

Adamussium colbecki Regoli et al. 1998 Only two exposure concentrations

Coral,

Goniastrea aspera

Reichelt-Brushett and Harrison 

1999 Only three exposure concentrations

Coral,

Lobophytum compactum

Reichelt-Brushett and 

Michalek-Wagner 2005

Not North American species; Lack of details 

(exposure duration not given)

Polychaetes Reish 1978 Lack of details (procedure)

Amphipod,

Corophium insidiosum

Amphipod,

Elasmopus bampo

Reish 1993 No control survival information

Polychaete,

Ctenodrilus serratus

Polychaete,

Ophryotrocha diadema

Reish and Carr 1978 Citrate added to dilution water

Polychaetes Reish and LeMay 1991 Dilution water not characterized

Polychaete,

Neanthes arenaceodentata

Polychaete,

Capitella capitata

Reish et al. 1976 Citrate added to dilution water

Copepod,

Tigriopus japonicus Rhee et al. 2009 Not North American species

Copepod,

Tigriopus japonicus Rhee et al. 2013 Not North American species; Only three exposure concentrations

Eastern oyster,

Crassostrea virginica Ringwood et al. 1998 Only two exposure concentrations

Copepod,

Tigriopus fulvus Rinna et al. 2011 Not North American species
F-19

Species Reference Reason Data Classified as Unused

Mediterranean mussel,

Mytilus galloprovincialis

Sand dollar,

Dendraster excentricus

Purple sea urchin,

Strongylocentrotus purpuratus

Rivera-Duarte et al. 2005 Lack of exposure details; dilution water not 

characterized

Amphipod,

Peramphithoe parmerong Roberts et al. 2006 Not North American species

Red drum,

Sciaenops ocellatus Robinson et al. 2013 Prior exposure to pollutant

Clam,

Chamaelea gallina Rodriguez-Ortega et al. 2003 Only three exposure concentrations

Sea snail,

Hexaplex (Murex) trunculus Romeo et al. 2006 Only three exposure concentrations

Mediterranean mussel,

Mytilus galloprovincialis

Purple sea urchin,

Strongylocentrotus purpuratus

Sand dollar,

Dendraster excentricus 

Rosen et al. 2005 Mixture

Clam,

Venerupis decussata Ruiz-Azcona et al. 2013 Not North American species

Bivalves Sakellari et al. 2013 Field survey, exposure concentration not 

known

Various organisms Salazar and Salazar 1986 Only three exposure concentrations

Various organisms Salazar and Salazar 1989 Not applicable, No copper toxicity information

Brine shrimp,

Artemia salina Saliba and Krzyz 1976 Brine shrimp used

Blue mussel,

Mytilus edulis Sanchez-Marin et al. 2012 Bioaccumulation study: steady state not achieved

Purple sea urchin,

Strongylocentrus purpuratus Sanders and Martin 1994 Inappropriate form of toxicant (Cu-NTA)

Crab,

Rhithropanopeus harrisii Sanders et al. 1984 Lack of details (procedure)

Mussel,

Brachiodontes exustus Sastre et al. 2005 Only three exposure concentrations

Clam,

Villorita cyprinoides var. 

cochinensis

Sathyanathan et al. 1988 Only two exposure concentrations; Not North 

American species

Shark,

Scyliorhinus canicula Sayin et al. 2012 In vitro

Coral,

Montastraea franksi Schwarz et al. 2013 Only three exposure concentrations

Shore crab,

Carcinus maenas

Scott-Fordsmand and Depledge 

1997 Bioaccumulation: unmeasured exposure 

Crab, 

Neoepisesarma mederi Selvakumar et al. 1987 Lack of details (procedure)

Green mussel,

Perna viridis Sharma et al. 2006 Only one exposure concentration

Green mussel,

Perna viridis Sharma et al. 2007 Only one exposure concentration

Green mussel,

Perna viridis Shi and Wang 2004 Prior exposure
F-20

Species Reference Reason Data Classified as Unused

Sea anemone,

Exaiptasia pallida Siddiqui et al. 2015 Only two exposure concentrations

Abalone,

Haliotis rufescens Silva-Aciares et al. 2013 Only two exposure concentrations

Burrowing crab,

Neohelice granulata Simonetti et al. 2012 Field survey, exposure concentration not known

Bivalve,

Tellina deltoidalis Simpson et al. 2012 Not North American species; Sediment exposure

Prawn,

Metapenaeus dobsoni Sivadasan et al. 1986 Not North American species; Test species fed

Clam,

Ruditapes decussatus Sobral and Widdows 1997 Bioaccumulation: unmeasured exposure, steady state not achieved

White shrimp,

Litopenaeus vannamei Soegianto et al. 2013 Only three exposure concentrations

Javelin goby,

Synechogobius hasta Song et al. 2013 Not North American species; Only three exposure concentrations

Javelin goby,

Synechogobius hasta Song et al. 2014 Not North American species

Brown alga,

Dictyota kunthii Sordet et al. 2014 Only one exposure concentration

Winkle,

Littorina littorea Soto et al. 1999 Excised tissue 

Snail,

Nassarius reticulatus Sousa et al. 2005 Not North American species

Hydroid,

Campanularia flexuosa Stebbing 1981 Colony exposure

Blue mussel,

Mytilus edulis Steinert and Pickwell 1985 Excised tissue 

Abalone,

Haliotis midae Stofberg et al. 2011 Not North American species; Poor control survival (≤20%)

Amphipod,

Melita plumulosa

Bivalve,

Spisula trigonella

Bivalve,

Tellina deltoidalis

Strom et al. 2011 Sediment exposure

Brown alga,

Ascophyllum nodosum Stromgren 1979 Algal study

Alga,

Synechococcus Stuart et al. 2009 Inappropriate form of toxicant (Cu-EDTA)

Blue mussel,

Mytilus edulis Sturesson 1984 Bioaccumulation: unmeasured exposure

Polychaete,

Perinereis aibuhitensis Sun et al. 2009 Not North American species

Copepod,

Acartia tonsa Sunda et al. 1990 Mixture

Blue mussel,

Mytilus edulis Sunila 1988 Only one exposure concentration

Blue mussel,

Mytilus edulis Sutherland and Major 1981 Only one exposure concentration

Sea urchin,

Strongylocentrotus intermedius

Sea urchin,

Strongylocentrotus nudus

Syasina et al. 1992 Only two exposure concentrations
F-21

Species Reference Reason Data Classified as Unused

Green mussel,

Perna viridis

Mussel,

Septifer virgatus

Sze and Lee 1995 Only one exposure concentration

Pacific oyster,

Crassostrea gigas Tanguy et al. 2002 Only one exposure concentration

Sydney rock oyster,

Saccostrea glomerata Taylor et al. 2013 Only one exposure concentration

European eel,

Anguilla anguilla Teles et al. 2005 Only two exposure concentrations

Green mussel,

Perna viridis Thiagarajan et al. 2006 Only one exposure concentration

Fish Thiyagarajan et al. 2012 Field survey, exposure concentration not 

known

Mummichog,

Fundulus heteroclitus Thomas 1915 Only one exposure concentration

Green crab,

Carcinus maenas

Rock crab,

Cancer irroratus

Thurberg et al. 1973 Copper level high in dilution water

Blue mussel,

Mytilus edulis Trevisan et al. 2011 Only one exposure concentration

Shore crab,

Carcinus maenas Truchot and Rtal 1998 Bioaccumulation: steady state not achieved

Mussel,

Mytilus californianus

Blue mussel,

Mytilus edulis

Tullis 1980 Only four organisms per concentration

Brine shrimp,

Artemia salina Umarani et al. 2012 Brine shrimp used

Crab,

Sesarma quadratum Valarmathi and Azariah 2002 Only two exposure concentrations

Gilthead seabream,

Sparus aurata Varo et al. 2007 Only three exposure concentrations

Bivalve,

Glycymeris yessoensis Vasil'eva et al. 1979 Bioaccumulation: unmeasured exposure

Mysid,

Mysidopsis juniae Vaz et al. 2011a Lack of details (procedure); Not North American species

Mysid,

Mysidopsis juniae Vaz et al. 2011b Inappropriate form of toxicant (nanoparticles); Not North American species

Babylon snail,

Babylonia areolata

Vedamanikam and Hayimad 

2014 Not North American species

Abalone,

Haliotis rufescens Viant et al. 2002 Only two exposure concentrations

Protozoa,

Euplotes crassus Viarengo et al. 1996 Protozoa

Brown mussel,

Perna perna Vosloo et al. 2012 Bioaccumulation study: steady state not achieved

Nematode,

Monhystera disjuncta Vranken et al. 1991 Agar media used

Saltmarsh cordgrass,

Spartina alterniflora Waddell and Kraus 1990 Terrestrial exposure

Cladoceran,

Moina monogolica Wang et al. 2007a Dietary exposure
F-22

Species Reference Reason Data Classified as Unused

Abalone,

Haliotis discus hannai Wang et al. 2009 Not North American species

Sea urchin,

Strongylocentrotus intermedius Wang et al. 2011a Not North American species; Mixture

Bivalves Wang et al. 2011b Field survey, exposure concentration not 

known

Grouper,

Epinephelus coioides Wang et al. 2014 Only two exposure concentration

Alga,

Aureococcus anophagefferens Wange et al. 2012 Algal study; Excessive EDTA in the media

Rock sea urchin,

Paracentrotus lividus Warnau et al. 1996 Not North American species; Dilution water not characterized

Sea urchin,

Arbacia punctulata Waterman 1937 Lack of details (procedure)

Mollusks Watling 1981 Lack of exposure details; dilution water not 

characterized

Brown alga,

Aureococcus anophagefferens Wei et al. 2013 Only three exposure concentrations

Macroalga,

Ulva lactuca Wendt et al. 2013 Algal study

Polychaete,

Perinereis nuntia Won et al. 2012 Only one exposure concentration; Not North American species

Shore crab,

Carcinus maenas Wong and Rainbow 1986 Method paper

Soft shell clam,

Mya arenaria

Eastern oyster,

Crassostrea virginica

Wright and Zamuda 1987 Bioaccumualtion: steady state not achieved; 

Chelator (NTA) added to dilution water

Green mussel,

Perna viridis Wu and Wang 2010 Only one exposure concentration

Prawn,

Penaeus orientalis kishinouye

Clam,

Potamocorbula laevis

Xu and Jing 1995 Dilution water not characterized

Sea urchin,

Glyptocidaris crenularis Xu et al. 2010 Not North American species; Lack of exposure details

Black abalone,

Haliotis cracherodii Yaffe 1979 Only one exposure concentration; No true control croup

Polychaeta,

Perinereis aibuhitensis Yang et al. 2012 Only three exposure concentrations

Sea urchin,

Arbacia punctulata Young and Nelson 1974 Only one exposure concentration

Chinese prawn,

Penaeus orientalis Zang et al. 1993 Dilution water not characterized; Not North American species

Oyster,

Crassostrea hongkongensis Zhang and Zhang 2012 Not North American species

Clam,

Venerupis (Ruditapes) 

philippinarum

Zhang et al. 2012 Only two exposure concentrations

Guppy,

Poecilia vivipara Zimmer et al. 2012 Not North American species; Only one exposure concentrations

Ornate wrasse,

Thalassoma pavo Zizza et al. 2014 Not North American species
G-1

Appendix G Species Numbers Used in BLM Analysis
G-2

Appendix Table G-1. Species Numbers Used in BLM Analysis.

Organism Species

Species 

Number

Blue mussel Mytilus edulis 1

Mussel Mytilus galloprovincialis 2

Copepod Tigriopus californicus 3

Summer flounder Paralichthys dentatus 4

Red abalone Haliotis rufescens 5

Black abalone Haliotis cracherodii 6

Mysid Holmesimysis costata 7

Eastern oyster Crassostrea virginica 8

Pacific oyster Crassostrea gigas 9

Purple sea urchin Strongylocentrotus purpuratus 10

Green sea urchin Strongylocentrotus droebachiensis 11

Coot clam Mulinia lateralis 12

Long-spined sea urchin Diadema antillarum 13

Sea urchin Arbacia punctulata 14

Bay scallop Argopecten irradians 15

Copepod Acartia tonsa 16

Copepod Acartia clausi 17

Sand dollar Dendraster excentricus 18

Copepod Eurytemora affinis 19

Softshell clam Mya arenaria 20

Rotifer Brachionus plicatilis 21

Surf clam Spisula solidissima 22

Lobster Homarus americanus 23

Mysid Neomysis mercedis 24

Dungeness crab Cancer magister 25

Polychaete Anaitides maculata 26

Cabezon Scorpaenichthys marmoratus 27

Inland silverside Menidia beryllina 28

Tidewater silverside Menidia peninsulae 29

Atlantic silverside Menidia menidia 30

Sea anemone Aiptasia pallida 31

Amphipod Elasmopus rapax 32

Mysid Americamysis bigelowi 33

Mysid Americamysis bahia 34

Amphipod Orchomenella pinguis 35

Polychaete Hydroides elegans 36

Copepod Tisbe furcata 37

Copepod Pseudodiaptomus coronatus 38

Winter flounder Pseudopleuronectes americanus 39

Shrimp Metapenaeus sp. 40

Polychaete Neanthes arenaceodentata 41

Amphipod Echinogammarus olivii 42

Topsmelt Atherinops affinis 43

Spot Leiostomus xanthurus 44

Squid Loligo opalescens 45
G-3

Organism Species

Species 

Number

Striped bass Morone saxatilis 46

Shrimp Crangon crangon 47

Pink shrimp Farfantepenaeus duorarum 48

Barnacle Balanus amphitrite 49

Barnacle Balanus eburneus 50

Hard clam Mercenaria mercenaria 51

Coho salmon Oncorhynchus kisutch 52

Sheepshead minnow Cyprinodon variegatus 53

Leon Springs pupfish Cyprinodon bovinus 54

Amphipod Allorchestes compressa 55

Mummichog Fundulus heteroclitus 56

Bristle star Ophionereis dubia 57

Shiner perch Cymatogaster aggregata 58

Polychaete Hediste diversicolor 59

Asian green mussel Perna viridis 60

Shore crab Carcinus maenas 61

Pompano Trachinotus carolinus 62

Tiger shrimp Penaeus monodon 63

Grooved snail Planaxis sulcatus 64

Whelk Turbo coronatus 65

Sheepshead Archosargus probatocephalus 66

Gastropod Crepidula convexa 67

Gastropod Crepidula fornicata 68

Isopod Sphaeroma serratum 69

Polychaete Eurythoe complanata 70

Copepod Amphiascoides atopus 71

Decapod Palaemon elegans 72

Sand crab Emerita analoga 73

Thornfish Terapon jarbua 74

Grass shrimp Palaemonetes pugio 75

Whiteleg shrimp Litopenaeus vannamei 76

Mud-skipper Boleophthalmus sp. 77

Copepod Nitokra spinipes 78

Pinfish Lagodon rhomboides 79

Fat snook Centropomus parallelus 80

Striped mullet Mugil cephalus 81

Mangrove killifish Rivulus marmoratus 82

Atlantic croaker Micropogonias undulatus 83

Blue crab Callinectes sapidus 84

Amphipod Gammarus duebeni 85

Horseshoe crab Limulus polyphemus 86

Gulf toadfish Opsanus beta 87

Clam Rangia cuneata 88

Amphipod Corophium volutator 89
H-1

Appendix H Water Chemistry Used in BLM Analysis
H-2

Normalizing the toxicity data with the marine BLM requires four water chemistry 

parameters in seawater: salinity, pH, DOC, and temperature. The marine BLM calculation uses 

all the same ions that are needed in the freshwater BLM (i.e., Ca, Mg, Na, K, SO4, Cl, and 

alkalinity), but these ion concentrations are calculated from salinity with the assumption that ion 

composition of marine waters is constant. To normalize the toxicity data included in this 

document the complete BLM chemistry for each reported value is needed. If any of the four 

marine BLM parameters were missing from the data source, values for the missing parameters 

were estimated.

Several strategies were used to in the process for determining suitable estimates for 

missing parameters. 

1. If the missing data were from a natural water body and other data were reported for the 

same or similar location, then an average value from the reported values was used as an 

estimate for missing values. Similarly, if the missing data were from a study in artificial

seawater and other studies reported chemistry for the same type of artificial seawater, 

then an average value from the reported chemistry was used to estimate missing values.

2. For DOC in artificial seawaters, the reported DOC concentrations in Arnold et al. (2007) 

were used for any test conducted in either Instant Ocean or Tropic Marine salts. 

3. If there were no other data for a location or artificial water, or the location was not given, 

then default values were used. These values were 30 ppt of salinity, pH of 7.8, 2.00 mg 

C/L of DOC, and a temperature of 20°C. These values were chosen based on the typical 

composition of seawater, and the average conditions reported in other toxicity tests.
H-3

Appendix Table H-1. Water Chemistry Used in BLM Analysis.

BLM 

Data 

Label

Genus

Reported chemistry Reported plus assumed chemistrya

Source water type Salinity, 

g/kg pH DOC, mg C/L

Temp, 

°C

Salinity, 

g/kg pH DOC, mg C/L

Temp,

°C

1 Acartia 30 30.00 7.80 2.00 20.00

2 Acartia Artificial saltwater 30 10 30.00 7.80 2.00 10.00

4 Acartia Natural saltwater (location not given) 10 10.00 7.80 2.00 20.00

5 Acartia Natural saltwater (location not given) 10 10.00 7.80 2.00 20.00

6 Acartia Natural saltwater (location not given) 30 30.00 7.80 2.00 20.00

7 Acartia Natural saltwater (location not given) 30 20 30.00 7.80 2.00 20.00

12 Aiptasia Natural seawater, filtered (SW; Whitney Laboratory) 35.00 23.00 35.00 7.80 2.00 23.00

14 Allorchestes Natural saltwater (location not given) 34.1 7.8 20.3 34.10 7.80 2.00 20.30

16 Americamysis Natural saltwater (location not given) 30 22.5 30.00 7.80 2.00 22.50

17 Americamysis Natural saltwater (Narragansett Bay, Narragansett, RI) 31 7.755 20 31.00 7.76 1.45 20.00

18 Americamysis Natural saltwater (Santa Rosa Sound, FL) 25 7.95 25 25.00 7.95 2.00 25.00

19 Americamysis Natural saltwater (Narragansett Bay, RI) 30 7 20 30.00 7.00 1.45 20.00

20 Americamysis Natural saltwater (Narragansett Bay, RI) 30 8 20 30.00 8.00 1.45 20.00

21 Americamysis Natural saltwater (Narragansett Bay, RI) 30 9 20 30.00 9.00 1.45 20.00

23 Americamysis 30 30.00 7.80 2.00 20.00

30 Archosargus Artificial saltwater (Sea Lakes Systems, Euclid, OH) 30 22 30.00 7.80 2.00 22.00

32 Argopecten Natural saltwater (location not given) 25 7.2 20 25.00 7.20 2.00 20.00

36 Atherinops Natural saltwater (Granite Canyon, Monterey County, CA) 35 7.8 21 35.00 7.80 1.74 21.00

37 Atherinops Natural saltwater (Granite Canyon, Monterey County, CA) 35 7.8 21 35.00 7.80 1.74 21.00

38 Atherinops Natural saltwater (Granite Canyon, Monterey County, CA) 35 7.8 21 35.00 7.80 1.74 21.00

44 Balanus Artificial saltwater 34 24 34.00 7.80 2.00 24.00

45 Balanus Artificial saltwater 34 24 34.00 7.80 2.00 24.00

46 Balanus Artificial saltwater 34 24 34.00 7.80 2.00 24.00

48 Boleophthalmus Natural saltwater (location not given) 37.54 7.92 20 37.54 7.92 2.00 20.00

50 Brachionus Artificial saltwater (Instant Ocean®) 15 7.45 <1.0 25 15.00 7.45 1.00 25.00

51 Brachionus Artificial saltwater (Instant Ocean®) 15 7.45 <1.0 25 15.00 7.45 1.00 25.00

53 Brachionus Artificial saltwater (Instant Ocean®) 6 7.6 <0.5 25.05 6.00 7.60 0.50 25.05

54 Brachionus Artificial saltwater (Instant Ocean®) 11 7.6 <0.5 25.05 11.00 7.60 0.50 25.05

55 Brachionus Artificial saltwater (Instant Ocean®) 15 7.8 <0.5 25.05 15.00 7.80 0.50 25.05

56 Brachionus Artificial saltwater (Instant Ocean®) 24 7.9 <0.5 25.05 24.00 7.90 0.50 25.05

57 Brachionus Artificial saltwater (Instant Ocean®) 29 7.9 <0.5 25.05 29.00 7.90 0.50 25.05

58 Brachionus Natural saltwater (Little Egg Harbor, NJ) 7 6.8 4.1 25.05 7.00 6.80 4.10 25.05

59 Brachionus Natural saltwater (Little Egg Harbor, NJ) 7 8.3 4 25.05 7.00 8.30 4.00 25.05

60 Brachionus Natural saltwater (Little Egg Harbor, NJ) 13 7.6 1.7 25.05 13.00 7.60 1.70 25.05

61 Brachionus Natural saltwater (Little Egg Harbor, NJ) 13 8.6 1.7 25.05 13.00 8.60 1.70 25.05

65 Callinectes Natural saltwater (Cassino Beach, Rio Grande, Brazil) 2.00 7.12 0.41 20.10 2.00 7.12 0.41 20.10

66 Callinectes Natural saltwater (Cassino Beach, Rio Grande, Brazil) 30 7.28 5.20 20.30 30.00 7.28 5.20 20.30
H-4

BLM 

Data 

Label

Genus

Reported chemistry Reported plus assumed chemistrya

Source water type Salinity, 

g/kg pH DOC, mg C/L

Temp, 

°C

Salinity, 

g/kg pH DOC, mg C/L

Temp,

°C

68 Cancer Natural saltwater (Big Sur, Monterey County, CA) 33.79 8.1 15 33.79 8.10 2.00 15.00

69 Cancer Natural saltwater (Puget Sound at West Point, Seattle, WA) 30 8.1 8.5 30.00 8.10 1.46 8.50

71 Carcinus Natural saltwater (location not given) 15 30.00 7.80 2.00 15.00

79 Corophium Natural saltwater (Ythan estuary, Aberdeenshire, Scotland) 32 7.2 11 32.00 7.20 2.00 11.00

85 Crangon Natural saltwater (location not given) 15 30.00 7.80 2.00 15.00

88 Crassostrea Natural seawater, unfiltered 33 8 13 33.00 7.80 2.00 20.00

89 Crassostrea Natural saltwater (Monterey, CA) 33 8.2 20 33.00 8.20 2.00 20.00

90 Crassostrea Natural saltwater (Bodega Bay, CA) 30 7.6 1.68 

(TOC) 20 30.00 7.60 1.68 20.00

93 Crassostrea Natural saltwater (Bodega Bay, CA) 30 7.6 20 30.00 7.60 0.89 20.00

94 Crassostrea Natural saltwater (Big Sur, Monterey County, CA) 33.79 8.1 20 33.79 8.10 2.00 20.00

96 Crassostrea Natural saltwater (U.C. Marine Laboratory, Bodega Bay, CA) 30 <0.5 16 30.00 7.60 0.50 16.00

97 Crassostrea Natural saltwater (U.C. Marine Laboratory, Bodega Bay, CA) 30 <0.5 16 30.00 7.60 0.50 16.00

106 Crassostrea Natural saltwater (location not given) 26 7.7 20 26.00 7.70 2.00 20.00

107 Crassostrea Natural saltwater (location not given) 26 7.7 25 26.00 7.70 2.00 25.00

108 Crassostrea Natural saltwater (location not given) 26 7.7 30 26.00 7.70 2.00 30.00

109 Crassostrea Natural and Artificial saltwater 29.8 7.75 0.8 25 29.80 7.75 0.80 25.00

110 Crassostrea Natural and Artificial saltwater 29.6 7.82 2.6 25 29.60 7.82 2.60 25.00

111 Crassostrea Natural and Artificial saltwater 29.7 7.92 3.9 25 29.70 7.92 3.90 25.00

112 Crassostrea Natural and Artificial saltwater 29.6 7.97 5.7 25 29.60 7.97 5.70 25.00

114 Crepidula Artificial saltwater (Instant Ocean) 30 20 30.00 7.43 0.20 20.00

116 Crepidula Artificial saltwater (Instant Ocean) 30 20 30.00 7.43 0.20 20.00

118 Cymatogaster Natural saltwater (Puget Sound at West Point, Seattle, WA) 29.5 7.8 13.2 29.50 7.80 1.46 13.20

120 Cyprinodon Natural saltwater (ERLN, Narragansett, RI) 30 25 30.00 7.92 1.45 25.00

125 Dendraster Natural saltwater (Puget Sound at West Point, Seattle, WA) 30 8.5 12.75 30.00 8.50 1.46 12.75

129 Dendraster Natural and Artificial saltwater 32 7.85 1.2 15 32.00 7.85 1.20 15.00

130 Dendraster Natural and Artificial saltwater 32 7.84 2.1 15 32.00 7.84 2.10 15.00

131 Dendraster Natural and Artificial saltwater 32 7.88 3.5 15 32.00 7.88 3.50 15.00

132 Dendraster Natural and Artificial saltwater 32 7.89 5 15 32.00 7.89 5.00 15.00

134 Diadema Natural saltwater 33 33.00 7.80 2.00 20.00

137 Echinogammarus Natural saltwater (location not given) 17 8.1 15 17.00 8.10 2.00 15.00

141 Elasmopus Artificial saltwater (Tropic Marine) 33 8.25 25 33.00 8.25 0.60 25.00

142 Elasmopus Artificial seawater (FAS; sea salt: Tropic Marine, Germany) 33.00 8.25 25.00 33.00 8.25 0.60 25.00

144 Emerita Natural saltwater (Pingueral Beach, Concepcion, Chile) 30 7.9 15 30.00 7.90 2.00 15.00

151 Eurytemora 30 30.00 7.80 2.00 20.00

152 Eurytemora Artificial saltwater 30 20 30.00 7.80 2.00 20.00

153 Eurytemora Natural saltwater (location not given) 30.00 7.80 2.00 20.00

154 Eurytemora Natural saltwater (location not given) 30.00 7.80 2.00 20.00

155 Eurytemora Natural saltwater (location not given) 30.00 7.80 2.00 20.00
H-5

BLM 

Data 

Label

Genus

Reported chemistry Reported plus assumed chemistrya

Source water type Salinity, 

g/kg pH DOC, mg C/L

Temp, 

°C

Salinity, 

g/kg pH DOC, mg C/L

Temp,

°C

156 Eurytemora Natural saltwater (location not given) 30.00 7.80 2.00 20.00

157 Eurytemora Natural saltwater (location not given) 30.00 7.80 2.00 20.00

158 Eurytemora Natural estuarine water (Choptank River, Cambridge, MA) 15.5 8.35 24.55 15.50 8.35 3.63 24.55

161 Eurytemora Natural estuarine water (Choptank River, Cambridge, MA) 2.5 7.95 3.31 25 2.50 7.95 3.31 25.00

162 Eurytemora Natural estuarine water (Choptank River, Cambridge, MA) 5 8.28 2.39 25 5.00 8.28 2.39 25.00

163 Eurytemora Natural estuarine water (Choptank River, Cambridge, MA) 15 8.38 1.68 25 15.00 8.38 1.68 25.00

164 Eurytemora Natural estuarine water (Choptank River, Cambridge, MA) 25 8.09 1.34 25 25.00 8.09 1.34 25.00

165 Eurytemora Natural estuarine water (Choptank River, Cambridge, MA) 10 8.1 2.48 25 10.00 8.10 2.48 25.00

166 Eurytemora Natural estuarine water (Choptank River, Cambridge, MA) 10 8.17 3.8 25 10.00 8.17 3.80 25.00

167 Eurytemora Natural estuarine water (Choptank River, Cambridge, MA) 10 8.17 5.6 25 10.00 8.17 5.60 25.00

168 Eurytemora Natural estuarine water (Choptank River, Cambridge, MA) 10 7.94 8.47 25 10.00 7.94 8.47 25.00

170 Eurythoe Natural saltwater (location not given) 36 7.8 36.00 7.80 2.00 20.00

172 Fundulus Natural saltwater (Horseshoe Cove or Asbury Park, NJ) 5.5 20 5.50 7.80 2.00 20.00

173 Fundulus Natural saltwater (Horseshoe Cove or Asbury Park, NJ) 23.6 20 23.60 7.80 2.00 20.00

174 Fundulus Natural saltwater (Horseshoe Cove or Asbury Park, NJ) 6.1 20 6.10 7.80 2.00 20.00

175 Fundulus Natural saltwater (Horseshoe Cove or Asbury Park, NJ) 24 20 24.00 7.80 2.00 20.00

176 Fundulus Artificial saltwater (Instant Ocean TM) 14 26.5 14.00 7.43 0.20 26.50

178 Fundulus Natural saltwater (Bear Cut, FL) 2.5 7.67 2.497 25 2.50 7.67 2.50 25.00

179 Fundulus Natural saltwater (Bear Cut, FL) 5 7.72 2.33 25 5.00 7.72 2.33 25.00

180 Fundulus Natural saltwater (Bear Cut, FL) 10 7.74 2.395 25 10.00 7.74 2.40 25.00

181 Fundulus Natural saltwater (Bear Cut, FL) 15 7.88 2.588 25 15.00 7.88 2.59 25.00

182 Fundulus Natural saltwater (Bear Cut, FL) 22 7.96 2.438 25 22.00 7.96 2.44 25.00

183 Fundulus Natural saltwater (Bear Cut, FL) 35 8.07 2.308 25 35.00 8.07 2.31 25.00

185 Gammarus Natural saltwater (location not given) 33 7.5 15 33.00 7.50 2.00 15.00

187 Haliotis Natural saltwater (location not given) 33 14 33.00 7.80 2.00 14.00

189 Haliotis Natural saltwater (location not given) 33 14 33.00 7.80 2.00 14.00

190 Haliotis Natural saltwater (location not given) 30.4 8 13 30.40 8.00 2.00 13.00

191 Haliotis Natural saltwater (location not given) 34.5 7.875 14.75 34.50 7.88 2.00 14.75

193 Hediste Natural saltwater (location not given) 5 7 5.00 7.80 2.00 7.00

194 Hediste Natural saltwater (location not given) 10 7 10.00 7.80 2.00 7.00

195 Hediste Natural saltwater (location not given) 17.5 7 17.50 7.80 2.00 7.00

196 Hediste Natural saltwater (location not given) 34 7 34.00 7.80 2.00 7.00

197 Hediste Natural saltwater (location not given) 7.3 12 7.30 7.80 2.00 12.00

198 Hediste Natural saltwater (location not given) 7.3 17 7.30 7.80 2.00 17.00

199 Hediste Natural saltwater (location not given) 7.3 22 7.30 7.80 2.00 22.00

200 Hediste Natural saltwater (location not given) 14.6 12 14.60 7.80 2.00 12.00

201 Hediste Natural saltwater (location not given) 14.6 17 14.60 7.80 2.00 17.00

202 Hediste Natural saltwater (location not given) 14.6 22 14.60 7.80 2.00 22.00

203 Hediste Natural saltwater (location not given) 21.9 12 21.90 7.80 2.00 12.00
H-6

BLM 

Data 

Label

Genus

Reported chemistry Reported plus assumed chemistrya

Source water type Salinity, 

g/kg pH DOC, mg C/L

Temp, 

°C

Salinity, 

g/kg pH DOC, mg C/L

Temp,

°C

204 Hediste Natural saltwater (location not given) 21.9 17 21.90 7.80 2.00 17.00

205 Hediste Natural saltwater (location not given) 21.9 22 21.90 7.80 2.00 22.00

206 Hediste Natural saltwater (location not given) 29.2 12 29.20 7.80 2.00 12.00

207 Hediste Natural saltwater (location not given) 29.2 17 29.20 7.80 2.00 17.00

208 Hediste Natural saltwater (location not given) 29.2 22 29.20 7.80 2.00 22.00

209 Hediste Natural saltwater (location not given) 7.6 12 7.60 7.80 2.00 12.00

210 Hediste Natural saltwater (location not given) 7.6 17 7.60 7.80 2.00 17.00

211 Hediste Natural saltwater (location not given) 7.6 22 7.60 7.80 2.00 22.00

212 Hediste Natural saltwater (location not given) 15.25 12 15.25 7.80 2.00 12.00

213 Hediste Natural saltwater (location not given) 15.25 17 15.25 7.80 2.00 17.00

214 Hediste Natural saltwater (location not given) 15.25 22 15.25 7.80 2.00 22.00

215 Hediste Natural saltwater (location not given) 22.8 12 22.80 7.80 2.00 12.00

216 Hediste Natural saltwater (location not given) 22.8 17 22.80 7.80 2.00 17.00

217 Hediste Natural saltwater (location not given) 22.8 22 22.80 7.80 2.00 22.00

218 Hediste Natural saltwater (location not given) 30.5 12 30.50 7.80 2.00 12.00

219 Hediste Natural saltwater (location not given) 30.5 17 30.50 7.80 2.00 17.00

220 Hediste Natural saltwater (location not given) 30.5 22 30.50 7.80 2.00 22.00

221 Hediste Artificial saltwater (Tropic Marin Neu) 16.3 10 16.30 8.25 0.60 10.00

223 Holmesimysis Natural saltwater (location not given) 37 7.8 14 37.00 7.80 2.00 14.00

224 Holmesimysis Natural saltwater (Big Sur, Monterey County, CA) 36.5 7.8 13 36.50 7.80 2.00 13.00

226 Homarus Natural seawater (Narragansett Bay, RI) 30.5 20 30.50 7.92 1.45 20.00

230 Hydroides Artificial seawater (FAS; sea salt: Tropic Marine, Germany) 33.00 8.25 25.00 33.00 8.25 0.60 25.00

234 Lagodon Artificial saltwater (Sea Lakes Systems, Euclid, OH) 30 22 30.00 7.80 2.00 22.00

236 Leiostomus Natural saltwater (location not given) 20 25 20.00 7.80 2.00 25.00

237 Leiostomus Natural saltwater (location not given) 20 25.15 20.00 7.80 2.00 25.15

239 Litopenaeus Natural saltwater (Mazatlan Bay, Mexico) 34 8.05 27.2 34.00 8.05 2.00 27.20

243 Loligo Natural saltwater (Puget Sound at West Point, Seattle, WA) 30 8.1 8.6 30.00 8.10 1.46 8.60

262 Menidia Artificial saltwater 27.5 8.05 24.9 27.50 8.05 2.00 24.90

263 Menidia Artificial saltwater 28 8.125 24.45 28.00 8.13 2.00 24.45

264 Menidia Artificial saltwater 29 8.03 24.4 29.00 8.03 2.00 24.40

266 Menidia Natural saltwater (ERL, Narragansett, RI) 31 19 31.00 7.92 1.45 19.00

267 Menidia Natural saltwater (ERL, Narragansett, RI) 30.4 18.5 30.40 7.92 1.45 18.50

268 Menidia Natural saltwater (ERL, Narragansett, RI) 31 20 31.00 7.92 1.45 20.00

269 Menidia Natural saltwater (ERL, Narragansett, RI) 30 20 30.00 7.92 1.45 20.00

271 Menidia Natural saltwater (location not given) 20 25 20.00 7.80 2.00 25.00

272 Menidia Natural saltwater (location not given) 20 25.25 20.00 7.80 2.00 25.25

274 Mercenaria Natural saltwater (location not given) 30.00 7.80 2.00 20.00

276 Metapenaeus Natural saltwater (location not given) 38 7.81 28 38.00 7.81 2.00 28.00

278 Micropogonias Artificial saltwater (Sea Lakes Systems, Euclid, OH) 30 22 30.00 7.80 2.00 22.00
H-7

BLM 

Data 

Label

Genus

Reported chemistry Reported plus assumed chemistrya

Source water type Salinity, 

g/kg pH DOC, mg C/L

Temp, 

°C

Salinity, 

g/kg pH DOC, mg C/L

Temp,

°C

280 Morone Natural saltwater (location not given) 10 7.1 22 10.00 7.10 2.00 22.00

281 Morone Artificial saltwater (Instant Ocean) 5 7.9 20 5.00 7.90 0.20 20.00

282 Morone Artificial saltwater (Rila® Marine mix) 5 8.5 26 5.00 8.50 2.00 26.00

283 Morone Artificial saltwater (Rila® Marine mix) 10 8.4 26 10.00 8.40 2.00 26.00

284 Morone Artificial saltwater (Rila® Marine mix) 15 7.8 26 15.00 7.80 2.00 26.00

286 Mulinia Natural saltwater (Narragansett Bay, Narragansett, RI) 31 7.755 20 31.00 7.76 1.45 20.00

287 Mulinia Natural saltwater (Narragansett Bay, Narragansett, RI) 29 8.03 20 29.00 8.03 1.45 20.00

288 Mulinia Natural saltwater (Narragansett Bay, Narragansett, RI) 30 8.035 20 30.00 8.04 1.45 20.00

289 Mulinia Natural saltwater (Narragansett Bay, Narragansett, RI) 32 8.035 20 32.00 8.04 1.45 20.00

290 Mulinia Natural saltwater (Narragansett Bay, Narragansett, RI) 30.5 8.04 20 30.50 8.04 1.45 20.00

291 Mulinia Natural saltwater (Narragansett Bay, Narragansett, RI) 31.5 8.045 20 31.50 8.05 1.45 20.00

293 Mya Natural saltwater (Narragansett, RI) 30 7.95 22 30.00 7.95 1.45 22.00

295 Mytilus Natural saltwater (Calleguas Creek 1, Ventura County, CA) 30 5.1 30.00 7.80 5.10 20.00

296 Mytilus Natural saltwater (Calleguas Creek 1, Ventura County, CA) 30 8.6 30.00 7.80 8.60 20.00

297 Mytilus Natural saltwater (Calleguas Creek 1, Ventura County, CA) 30 9.7 30.00 7.80 9.70 20.00

298 Mytilus Natural saltwater (Calleguas Creek 2, Ventura County, CA) 30 4.8 30.00 7.80 4.80 20.00

299 Mytilus Natural saltwater (Calleguas Creek 2, Ventura County, CA) 30 6.6 30.00 7.80 6.60 20.00

300 Mytilus Natural saltwater (Calleguas Creek 2, Ventura County, CA) 30 10 30.00 7.80 10.00 20.00

301 Mytilus Natural saltwater (Mugu Lagoon 3, Ventura County, CA) 30 1.5 30.00 7.80 1.50 20.00

302 Mytilus Natural saltwater (Mugu Lagoon 3, Ventura County, CA) 30 7.3 30.00 7.80 7.30 20.00

303 Mytilus Natural saltwater (Mugu Lagoon 3, Ventura County, CA) 30 11 30.00 7.80 11.00 20.00

304 Mytilus Natural saltwater (Mugu Lagoon 4, Ventura County, CA) 30 1.4 30.00 7.80 1.40 20.00

305 Mytilus Natural saltwater (Mugu Lagoon 4, Ventura County, CA) 30 6.2 30.00 7.80 6.20 20.00

306 Mytilus Natural saltwater (Mugu Lagoon 5, Ventura County, CA) 30 2 30.00 7.80 2.00 20.00

307 Mytilus Natural saltwater (Mugu Lagoon 5, Ventura County, CA) 30 4.7 30.00 7.80 4.70 20.00

308 Mytilus Natural saltwater (Mugu Lagoon 5, Ventura County, CA) 30 12 30.00 7.80 12.00 20.00

309 Mytilus Natural saltwater (Mugu Lagoon 6, Ventura County, CA) 30 1.7 30.00 7.80 1.70 20.00

310 Mytilus Natural saltwater (Mugu Lagoon 6, Ventura County, CA) 30 3.4 30.00 7.80 3.40 20.00

311 Mytilus Natural saltwater (Mugu Lagoon 6, Ventura County, CA) 30 9.9 30.00 7.80 9.90 20.00

312 Mytilus Natural saltwater (Granite Canyon, Ventura County, CA) 30 1 30.00 7.99 1.00 15.70

313 Mytilus Natural saltwater (Granite Canyon, Ventura County, CA) 30 1.2 30.00 7.99 1.20 15.70

314 Mytilus Natural saltwater (Granite Canyon, Ventura County, CA) 30 2.9 30.00 7.99 2.90 15.70

315 Mytilus Natural saltwater (Granite Canyon, Ventura County, CA) 30 3.2 30.00 7.99 3.20 15.70

316 Mytilus Artificial saltwater (Crystal Sea Marinemix) 30 5.9 30.00 7.80 5.90 20.00

317 Mytilus Artificial saltwater (HW Marinemix) 30 0.4 30.00 7.80 0.40 20.00

318 Mytilus Artificial saltwater (General-Purpose salt) 30 0.1 30.00 7.80 0.10 20.00

319 Mytilus Artificial saltwater (Kent Marine) 30.6 8.17 1.087 18 30.60 8.17 1.09 18.00

320 Mytilus Natural saltwater (Chesapeake Bay) 29.9 8.1 3.606 18 29.90 8.10 3.61 18.00

321 Mytilus Natural saltwater (San Diego Bay) 29.9 8.02 2.326 18 29.90 8.02 2.33 18.00
H-8

BLM 

Data 

Label

Genus

Reported chemistry Reported plus assumed chemistrya

Source water type Salinity, 

g/kg pH DOC, mg C/L

Temp, 

°C

Salinity, 

g/kg pH DOC, mg C/L

Temp,

°C

322 Mytilus Natural saltwater (Tomales Bay) 30.2 7.8 3.374 18 30.20 7.80 3.37 18.00

323 Mytilus Natural saltwater (Puget Sound) 29.5 7.52 1.88 18 29.50 7.52 1.88 18.00

324 Mytilus Natural saltwater (Coal Harbour) 30.2 7.44 3.327 18 30.20 7.44 3.33 18.00

325 Mytilus Natural saltwater (Arthur Kill) 29.9 7.78 6.936 18 29.90 7.78 6.94 18.00

326 Mytilus Natural saltwater (Potomac River) 29.9 8.02 3.183 18 29.90 8.02 3.18 18.00

327 Mytilus Natural saltwater (Halifax Harbour) 29.9 7.65 1.619 18 29.90 7.65 1.62 18.00

328 Mytilus Natural saltwater (Albemarle Sound) 30.2 7.58 6.934 18 30.20 7.58 6.93 18.00

331 Mytilus Natural saltwater (Big Sur, Monterey County, CA) 33.79 8.1 17 33.79 8.10 2.00 17.00

333 Mytilus Natural saltwater (location not given) 25 6.9 - 7.5 20 25.00 7.20 2.00 20.00

334 Mytilus Artificial saltwater 27.5 8.05 24.9 27.50 8.05 2.00 24.90

335 Mytilus Artificial saltwater 28 8.125 24.45 28.00 8.13 2.00 24.45

336 Mytilus Artificial saltwater 29 8.03 24.4 29.00 8.03 2.00 24.40

337 Mytilus Natural saltwater (Narragansett Bay, Narragansett, RI) 30.5 8.025 20 30.50 8.03 1.45 20.00

338 Mytilus Natural saltwater (Narragansett Bay, Narragansett, RI) 31.5 8.5 20 31.50 8.50 1.45 20.00

339 Mytilus Natural saltwater (Narragansett Bay, Narragansett, RI) 31.5 8.075 20 31.50 8.08 1.45 20.00

340 Mytilus Natural saltwater (Narragansett Bay, Narragansett, RI) 31.5 8.05 20 31.50 8.05 1.45 20.00

341 Mytilus Natural saltwater (Granite Canyon, CA) 28 8.1 15.25 28.00 8.10 1.74 15.25

342 Mytilus Natural saltwater (Granite Canyon, CA) 28 8.05 15.45 28.00 8.05 1.74 15.45

343 Mytilus Natural saltwater (Granite Canyon, CA) 28 8.2 15.05 28.00 8.20 1.74 15.05

344 Mytilus Natural saltwater (Granite Canyon, CA) 28 8.2 15 28.00 8.20 1.74 15.00

345 Mytilus Natural saltwater (Granite Canyon, CA) 28 8.05 15.15 28.00 8.05 1.74 15.15

346 Mytilus Natural saltwater (Granite Canyon, CA) 28 8.15 14.9 28.00 8.15 1.74 14.90

347 Mytilus Natural saltwater (Granite Canyon, CA) 28 8.15 15.4 28.00 8.15 1.74 15.40

348 Mytilus Natural saltwater (Granite Canyon, CA) 28 8 15.7 28.00 8.00 1.74 15.70

349 Mytilus Natural saltwater (Granite Canyon, CA) 28 7.85 15.4 28.00 7.85 1.74 15.40

350 Mytilus Natural saltwater (Granite Canyon, CA) 28 8 15.45 28.00 8.00 1.74 15.45

351 Mytilus Natural saltwater (Granite Canyon, CA) 28 8.1 15.15 28.00 8.10 1.74 15.15

352 Mytilus Natural saltwater (Granite Canyon, CA) 28 8.2 15.05 28.00 8.20 1.74 15.05

353 Mytilus Natural saltwater (Granite Canyon, CA) 28 8.05 15 28.00 8.05 1.74 15.00

354 Mytilus Natural saltwater (Granite Canyon, CA) 28 8.05 15.2 28.00 8.05 1.74 15.20

355 Mytilus Natural saltwater (Granite Canyon, CA) 27.9 8.05 14.85 27.90 8.05 1.74 14.85

356 Mytilus Natural saltwater (Granite Canyon, CA) 27.5 7.85 15.6 27.50 7.85 1.74 15.60

357 Mytilus Natural saltwater (Granite Canyon, CA) 27.5 7.85 15.45 27.50 7.85 1.74 15.45

358 Mytilus Natural saltwater (Granite Canyon, CA) 28 7.85 14.95 28.00 7.85 1.74 14.95

359 Mytilus Natural saltwater (Granite Canyon, CA) 28 7.95 15.1 28.00 7.95 1.74 15.10

360 Mytilus Natural saltwater (Granite Canyon, CA) 28.75 7.9 14.85 28.75 7.90 1.74 14.85

361 Mytilus Natural saltwater (Granite Canyon, CA) 28 7.75 15.35 28.00 7.75 1.74 15.35

362 Mytilus Natural saltwater (Granite Canyon, CA) 28 7.95 15.3 28.00 7.95 1.74 15.30

363 Mytilus Natural saltwater (Granite Canyon, CA) 28 8.15 14.8 28.00 8.15 1.74 14.80
H-9

BLM 

Data 

Label

Genus

Reported chemistry Reported plus assumed chemistrya

Source water type Salinity, 

g/kg pH DOC, mg C/L

Temp, 

°C

Salinity, 

g/kg pH DOC, mg C/L

Temp,

°C

364 Mytilus Natural saltwater (Granite Canyon, CA) 34 8.2 14.55 34.00 8.20 1.74 14.55

365 Mytilus Natural saltwater (Granite Canyon, CA) 34 8.25 14.55 34.00 8.25 1.74 14.55

366 Mytilus Natural diluted saltwater (Narragansett, RI) 20 7.85 16 20.00 7.85 1.45 16.00

367 Mytilus Natural diluted saltwater (Narragansett, RI) 20 7.85 16 20.00 7.85 1.45 16.00

368 Mytilus Natural diluted saltwater (Narragansett, RI) 20 7.85 16 20.00 7.85 1.45 16.00

369 Mytilus Natural saltwater (Granite Canyon Marine Lab., Carmel, CA) 30 7.82 0.5 30.00 7.82 0.50 15.70

370 Mytilus Natural saltwater (Granite Canyon Marine Lab., Carmel, CA) 30 7.82 0.9 30.00 7.82 0.90 15.70

371 Mytilus Natural saltwater (South San Francisco Bay, San Francisco, CA) 30 7.95 5.1 30.00 7.95 5.10 20.00

372 Mytilus Natural saltwater (South San Francisco Bay, San Francisco, CA) 30 7.95 5.2 30.00 7.95 5.20 20.00

373 Mytilus Natural saltwater (Granite Canyon and San Francisco Bay water) 30 7.91 2 30.00 7.91 2.00 15.70

374 Mytilus Natural saltwater (Granite Canyon and San Francisco Bay water) 30 7.91 2.2 30.00 7.91 2.20 15.70

375 Mytilus Natural saltwater (Granite Canyon and San Francisco Bay water) 30 7.98 3.5 30.00 7.98 3.50 15.70

376 Mytilus Natural saltwater (Granite Canyon and San Francisco Bay water) 30 7.98 3.8 30.00 7.98 3.80 15.70

380 Mytilus Natural saltwater (Granite Canyon, CA) 30 <1.5 30.00 7.99 1.50 15.70

381 Mytilus Natural saltwater (Granite Canyon, CA) 30 <1.5 30.00 7.99 1.50 15.70

382 Mytilus Natural saltwater (Granite Canyon, CA) 30 0.6 30.00 7.99 0.60 15.70

383 Mytilus Natural saltwater (Granite Canyon, CA) 30 0.6 30.00 7.99 0.60 15.70

384 Mytilus Natural saltwater (Granite Canyon, CA) 30 1 30.00 7.99 1.00 15.70

385 Mytilus Natural saltwater (Granite Canyon, CA) 30 1.2 30.00 7.99 1.20 15.70

386 Mytilus Natural saltwater (Granite Canyon, CA) 30 High 30.00 7.99 2.00 15.70

387 Mytilus Natural saltwater (Granite Canyon, CA) 30 0.3 30.00 7.99 0.30 15.70

388 Mytilus Natural saltwater (Granite Canyon, CA) 30 0.7 30.00 7.99 0.70 15.70

389 Mytilus Natural saltwater (Redwood Creek, San Francisco, CA) 30 2.6 30.00 7.95 2.60 20.00

390 Mytilus Natural saltwater (Redwood Creek, San Francisco, CA) 30 3.2 30.00 7.95 3.20 20.00

391 Mytilus Natural saltwater (Redwood Creek, San Francisco, CA) 30 2.3 30.00 7.95 2.30 20.00

392 Mytilus Natural saltwater (Redwood Creek, San Francisco, CA) 30 Low 30.00 7.95 1.00 20.00

393 Mytilus Natural saltwater (San Bruno, San Francisco, CA) 30 <1.5 30.00 7.95 1.50 20.00

394 Mytilus Natural saltwater (San Bruno, San Francisco, CA) 30 2.1 30.00 7.95 2.10 20.00

395 Mytilus Natural saltwater (San Bruno, San Francisco, CA) 30 2.2 30.00 7.95 2.20 20.00

396 Mytilus Natural saltwater (San Bruno, San Francisco, CA) 30 Low 30.00 7.95 1.00 20.00

397 Mytilus Natural saltwater (Central Bay-midpoint, San Francisco, CA) 30 2 30.00 7.95 2.00 20.00

398 Mytilus Natural saltwater (Central Bay-midpoint, San Francisco, CA) 30 3.2 30.00 7.95 3.20 20.00

399 Mytilus Natural saltwater (Central Bay-midpoint, San Francisco, CA) 30 2.6 30.00 7.95 2.60 20.00

400 Mytilus Natural saltwater (Central Bay-midpoint, San Francisco, CA) 30 3.5 30.00 7.95 3.50 20.00

401 Mytilus Natural saltwater (Central Bay-nearshore, San Francisco, CA) 30 4.6 30.00 7.95 4.60 20.00

402 Mytilus Natural saltwater (Central Bay-nearshore, San Francisco, CA) 30 3.3 30.00 7.95 3.30 20.00

403 Mytilus Natural saltwater (Central Bay-nearshore, San Francisco, CA) 30 2.4 30.00 7.95 2.40 20.00

404 Mytilus Natural saltwater (Central Bay-nearshore, San Francisco, CA) 30 Low 30.00 7.95 1.00 20.00

405 Mytilus Natural saltwater (Oyster Point, San Francisco, CA) 30 <1.5 30.00 7.95 1.50 20.00
H-10

BLM 

Data 

Label

Genus

Reported chemistry Reported plus assumed chemistrya

Source water type Salinity, 

g/kg pH DOC, mg C/L

Temp, 

°C

Salinity, 

g/kg pH DOC, mg C/L

Temp,

°C

406 Mytilus Natural saltwater (Oyster Point, San Francisco, CA) 30 2.2 30.00 7.95 2.20 20.00

407 Mytilus Natural saltwater (Oyster Point, San Francisco, CA) 30 1.9 30.00 7.95 1.90 20.00

408 Mytilus Natural saltwater (Oyster Point, San Francisco, CA) 30 Low 30.00 7.95 1.00 20.00

409 Mytilus Natural saltwater (Yerba Beuna Island, San Francisco, CA) 30 <1.5 30.00 7.95 1.50 20.00

410 Mytilus Natural saltwater (Yerba Beuna Island, San Francisco, CA) 30 1.7 30.00 7.95 1.70 20.00

411 Mytilus Natural saltwater (Yerba Beuna Island, San Francisco, CA) 30 1.7 30.00 7.95 1.70 20.00

412 Mytilus Natural saltwater (Yerba Beuna Island, San Francisco, CA) 30 Low 30.00 7.95 1.00 20.00

413 Mytilus Natural saltwater (San Pablo Bay, San Francisco, CA) 30 2.1 30.00 7.95 2.10 20.00

414 Mytilus Natural saltwater (San Pablo Bay, San Francisco, CA) 30 4.9 30.00 7.95 4.90 20.00

415 Mytilus Natural saltwater (San Pablo Bay, San Francisco, CA) 30 2.1 30.00 7.95 2.10 20.00

416 Mytilus Natural saltwater (San Pablo Bay, San Francisco, CA) 30 1.8 30.00 7.95 1.80 20.00

417 Mytilus Natural saltwater (San Pablo Bay B15-B20, San Francisco, CA) 30 1.5 30.00 7.95 1.50 20.00

418 Mytilus Natural saltwater (San Pablo Bay B15-B20, San Francisco, CA) 30 8.1 30.00 7.95 8.10 20.00

419 Mytilus Natural saltwater (San Pablo Bay B15-B20, San Francisco, CA) 30 2.8 30.00 7.95 2.80 20.00

420 Mytilus Natural saltwater (San Pablo Bay B15-B20, San Francisco, CA) 30 2 30.00 7.95 2.00 20.00

421 Mytilus Natural saltwater (Petaluma River, San Francisco, CA) 30 3 30.00 7.95 3.00 20.00

422 Mytilus Natural saltwater (Petaluma River, San Francisco, CA) 30 9 30.00 7.95 9.00 20.00

423 Mytilus Natural saltwater (Petaluma River, San Francisco, CA) 30 4 30.00 7.95 4.00 20.00

424 Mytilus Natural saltwater (Petaluma River, San Francisco, CA) 30 2.3 30.00 7.95 2.30 20.00

425 Mytilus Natural saltwater (East San Pablo Bay-midpoint, San Francisco, 

CA) 30 1.7 30.00 7.95 1.70 20.00

426 Mytilus Natural saltwater (East San Pablo Bay-midpoint, San Francisco, 

CA) 30 4.8 30.00 7.95 4.80 20.00

427 Mytilus Natural saltwater (East San Pablo Bay-midpoint, San Francisco, 

CA) 30 2.2 30.00 7.95 2.20 20.00

428 Mytilus Natural saltwater (East San Pablo Bay-midpoint, San Francisco, 

CA) 30 2.6 30.00 7.95 2.60 20.00

429 Mytilus Natural saltwater (East San Pablo Bay-nearshore, San Francisco, 

CA) 30 2.3 30.00 7.95 2.30 20.00

430 Mytilus Natural saltwater (East San Pablo Bay-nearshore, San Francisco, 

CA) 30 4.5 30.00 7.95 4.50 20.00

431 Mytilus Natural saltwater (East San Pablo Bay-nearshore, San Francisco, 

CA) 30 2.5 30.00 7.95 2.50 20.00

432 Mytilus Natural saltwater (East San Pablo Bay-nearshore, San Francisco, 

CA) 30 2.2 30.00 7.95 2.20 20.00

433 Mytilus Natural saltwater (Pacheco Creek, San Francisco, CA) 30 1.7 30.00 7.95 1.70 20.00

434 Mytilus Natural saltwater (Pacheco Creek, San Francisco, CA) 30 9.6 30.00 7.95 9.60 20.00

435 Mytilus Natural saltwater (Pacheco Creek, San Francisco, CA) 30 2.9 30.00 7.95 2.90 20.00

436 Mytilus Natural saltwater (Grizzly Bay, San Francisco, CA) 30 2 30.00 7.95 2.00 20.00
H-11

BLM 

Data 

Label

Genus

Reported chemistry Reported plus assumed chemistrya

Source water type Salinity, 

g/kg pH DOC, mg C/L

Temp, 

°C

Salinity, 

g/kg pH DOC, mg C/L

Temp,

°C

437 Mytilus Natural saltwater (Grizzly Bay, San Francisco, CA) 30 10 30.00 7.95 10.00 20.00

438 Mytilus Natural saltwater (Grizzly Bay, San Francisco, CA) 30 3.2 30.00 7.95 3.20 20.00

439 Mytilus Natural saltwater (Puget Sound SUZ001, Bangor, WA) 30 1.4 30.00 7.99 1.40 11.00

440 Mytilus Natural saltwater (Puget Sound HCB002, Bangor, WA) 30 1.1 30.00 7.99 1.10 11.00

441 Mytilus Natural saltwater (Galveston Bay- Horsepen Bayou, Clear Lake, 

TX) 30 8.7 30.00 7.80 8.70 20.00

442 Mytilus Natural saltwater (West Galveston Bay, Clear Lake, TX) 30 3.3 30.00 7.80 3.30 20.00

443 Mytilus Natural saltwater (Narragansett Bay-USEPA Dock Low Tide, 

Narragansett, RI) 30 1.5 30.00 7.92 1.50 17.00

444 Mytilus Natural saltwater (Narragansett Bay-USEPA Dock High Tide, 

Narragansett, RI) 30 1.4 30.00 7.92 1.40 17.00

446 Mytilus Natural saltwater (Granite Canyon Marine Lab., Carmel, CA) 30 7.82 0.7 30.00 7.82 0.70 15.70

447 Mytilus Natural saltwater (Granite Canyon Marine Lab., Carmel, CA) 30 7.82 1 30.00 7.82 1.00 15.70

448 Mytilus Natural saltwater (South San Francisco Bay, San Francisco, CA) 30 7.95 4.9 30.00 7.95 4.90 20.00

449 Mytilus Natural saltwater (South San Francisco Bay, San Francisco, CA) 30 7.95 5.7 30.00 7.95 5.70 20.00

450 Mytilus Natural saltwater (Granite Canyon and San Francisco Bay water) 30 7.91 1.9 30.00 7.91 1.90 15.70

451 Mytilus Natural saltwater (Granite Canyon and San Francisco Bay water) 30 7.91 2.2 30.00 7.91 2.20 15.70

452 Mytilus Natural saltwater (Granite Canyon and San Francisco Bay water) 30 7.98 3.3 30.00 7.98 3.30 15.70

453 Mytilus Natural saltwater (Granite Canyon and San Francisco Bay water) 30 7.98 3.8 30.00 7.98 3.80 15.70

454 Mytilus Natural saltwater (San Diego Bay, CA) 34.3 7.89 1.3 15.5 34.30 7.89 1.30 15.50

455 Mytilus Natural saltwater (San Diego Bay, CA) 34.1 7.85 1.7 15.3 34.10 7.85 1.70 15.30

456 Mytilus Natural and Artificial saltwater 29.8 7.75 0.8 25 29.80 7.75 0.80 25.00

457 Mytilus Natural and Artificial saltwater 29.6 7.82 2.6 25 29.60 7.82 2.60 25.00

458 Mytilus Natural and Artificial saltwater 29.7 7.92 3.9 25 29.70 7.92 3.90 25.00

459 Mytilus Natural and Artificial saltwater 29.6 7.97 5.7 25 29.60 7.97 5.70 25.00

460 Mytilus Natural and Artificial saltwater 32 7.85 1.2 15 32.00 7.85 1.20 15.00

461 Mytilus Natural and Artificial saltwater 32 7.84 2.1 15 32.00 7.84 2.10 15.00

462 Mytilus Natural and Artificial saltwater 32 7.88 3.5 15 32.00 7.88 3.50 15.00

463 Mytilus Natural and Artificial saltwater 32 7.89 5 15 32.00 7.89 5.00 15.00

469 Neanthes Natural saltwater (Narragansett Bay, Narragansett, RI) 31 17 31.00 7.92 1.45 17.00

470 Neanthes Natural saltwater (Narragansett Bay, Narragansett, RI) 31 17 31.00 7.92 1.45 17.00

472 Neanthes Natural saltwater (Narragansett Bay, Narragansett, RI) 31 19 31.00 7.92 1.45 19.00

474 Neomysis Artificial saltwater (Marine Environment®) 2 17 2.00 7.80 2.00 17.00

475 Neomysis Artificial saltwater (Marine Environment®) 2 17 2.00 7.80 2.00 17.00

476 Neomysis Artificial saltwater (Marine Environment®) 2 17 2.00 7.80 2.00 17.00

478 Nitokra Natural brackish water (location not given) 7 8 20 7.00 8.00 2.00 20.00

481 Oncorhynchus Natural saltwater (Puget Sound at West Point, Seattle, WA) 28.6 8.1 13 28.60 8.10 1.46 13.00

483 Ophionereis Natural saltwater (location not given) 41.7 8.01 23 41.70 8.01 2.00 23.00

485 Opsanus Natural saltwater (Bear Cut, FL) 30 23 30.00 7.84 2.43 23.00
H-12

BLM 

Data 

Label

Genus

Reported chemistry Reported plus assumed chemistrya

Source water type Salinity, 

g/kg pH DOC, mg C/L

Temp, 

°C

Salinity, 

g/kg pH DOC, mg C/L

Temp,

°C

487 Palaemon Natural saltwater (location not given) 17 8.1 15 17.00 8.10 2.00 15.00

489 Palaemonetes Natural saltwater (Santa Rosa Sound, Gulf Breeze, FL) 20 7.4 27 20.00 7.40 2.00 27.00

496 Paralichthys Natural saltwater (ERL, Narragansett, RI) 30 14 30.00 7.92 1.45 14.00

497 Paralichthys Natural saltwater (ERL, Narragansett, RI) 30 13 30.00 7.92 1.45 13.00

498 Paralichthys Natural saltwater (ERL, Narragansett, RI) 30 12 30.00 7.92 1.45 12.00

499 Paralichthys Natural diluted saltwater (Narragansett, RI) 22 7.4 20 22.00 7.40 1.45 20.00

500 Paralichthys Natural diluted saltwater (Narragansett, RI) 22 7.4 20 22.00 7.40 1.45 20.00

501 Paralichthys Natural diluted saltwater (Narragansett, RI) 22 7.6 20 22.00 7.60 1.45 20.00

503 Farfantepenaeus Natural saltwater (Santa Rosa Sound, FL) 25 7.95 25 25.00 7.95 2.00 25.00

505 Anaitides Natural saltwater (location not given) 10 30.00 7.80 2.00 10.00

507 Planaxis Natural saltwater (location not given) 36.91 7.8 27 36.91 7.80 2.00 27.00

509 Pseudodiaptomus 30 30.00 7.80 2.00 20.00

510 Pseudodiaptomus Artificial saltwater 30 20 30.00 7.80 2.00 20.00

511 Pseudodiaptomus Artificial saltwater (Kester) 30 15 30.00 7.80 2.00 15.00

513 Pseudopleuronectes Natural saltwater (ERL, Narragansett, RI) 30 5 30.00 7.92 1.45 5.00

514 Pseudopleuronectes Natural saltwater (ERL, Narragansett, RI) 28 5 28.00 7.92 1.45 5.00

515 Pseudopleuronectes Natural saltwater (ERL, Narragansett, RI) 30 8 30.00 7.92 1.45 8.00

516 Pseudopleuronectes Natural saltwater (ERL, Narragansett, RI) 30 5 30.00 7.92 1.45 5.00

517 Pseudopleuronectes Natural saltwater (ERL, Narragansett, RI) 30 4.5 30.00 7.92 1.45 4.50

518 Pseudopleuronectes Natural saltwater (ERL, Narragansett, RI) 30 5 30.00 7.92 1.45 5.00

526 Rangia Artificial saltwater (Instant Ocean) 5.5 24 5.50 7.43 0.20 24.00

527 Rangia Artificial saltwater (Instant Ocean) 22 24 22.00 7.43 0.20 24.00

529 Rivulus Artificial saltwater (Instant Ocean TM) 14 26.5 14.00 7.43 0.20 26.50

530 Rivulus Artificial saltwater (Instant Ocean TM) 14 26.5 14.00 7.43 0.20 26.50

532 Scorpaenichthys Natural saltwater (Puget Sound at West Point, Seattle, WA) 27 7.9 8.3 27.00 7.90 1.46 8.30

534 Sphaeroma Natural saltwater (location not given) 17 8.1 15 17.00 8.10 2.00 15.00

536 Spisula Natural saltwater (location not given) 25 7.2 20 25.00 7.20 2.00 20.00

538 Strongylocentrotus Natural saltwater (Puget Sound at West Point, Seattle, WA) 30 7.95 8.3 30.00 7.95 1.46 8.30

543 Strongylocentrotus Natural saltwater (Puget Sound at West Point, Seattle, WA) 30 7.95 8.3 30.00 7.95 1.46 8.30

547 Strongylocentrotus Natural saltwater (Granite Canyon, CA) 33.5 8.3 14.85 33.50 8.30 1.74 14.85

548 Strongylocentrotus Natural saltwater (Granite Canyon, CA) 33.5 8.3 14.95 33.50 8.30 1.74 14.95

549 Strongylocentrotus Natural saltwater (San Diego Bay, CA) 34.2 8.09 2.47 15.8 34.20 8.09 2.47 15.80

550 Strongylocentrotus Natural and Artificial saltwater 32 7.85 1.2 15 32.00 7.85 1.20 15.00

551 Strongylocentrotus Natural and Artificial saltwater 32 7.84 2.1 15 32.00 7.84 2.10 15.00

552 Strongylocentrotus Natural and Artificial saltwater 32 7.88 3.5 15 32.00 7.88 3.50 15.00

553 Strongylocentrotus Natural and Artificial saltwater 32 7.89 5 15 32.00 7.89 5.00 15.00

555 Terapon Natural saltwater (location not given) 7.9 28 30.00 7.90 2.00 28.00

557 Tigriopus Artificial saltwater (AQUIL) 35 8 16 35.00 8.00 2.00 16.00

558 Tigriopus Artificial saltwater (AQUIL) 35 8 16 35.00 8.00 2.00 16.00
H-13

BLM 

Data 

Label

Genus

Reported chemistry Reported plus assumed chemistrya

Source water type Salinity, 

g/kg pH DOC, mg C/L

Temp, 

°C

Salinity, 

g/kg pH DOC, mg C/L

Temp,

°C

559 Tigriopus Artificial saltwater (AQUIL) 35 8 16 35.00 8.00 2.00 16.00

560 Tigriopus Artificial saltwater (AQUIL) 35 8 16 35.00 8.00 2.00 16.00

561 Tigriopus Artificial saltwater (AQUIL) 35 8 16 35.00 8.00 2.00 16.00

562 Tigriopus Artificial saltwater (AQUIL) 35 8 16 35.00 8.00 2.00 16.00

563 Tigriopus Artificial saltwater (AQUIL) 35 8 16 35.00 8.00 2.00 16.00

564 Tigriopus Artificial saltwater (AQUIL) 35 8 16 35.00 8.00 2.00 16.00

565 Tigriopus Artificial saltwater (AQUIL) 35 8 16 35.00 8.00 2.00 16.00

566 Tigriopus Artificial saltwater (AQUIL) 35 8 16 35.00 8.00 2.00 16.00

567 Tigriopus Artificial saltwater (AQUIL) 35 8 16 35.00 8.00 2.00 16.00

568 Tigriopus Artificial saltwater (AQUIL) 35 8 16 35.00 8.00 2.00 16.00

569 Tigriopus Artificial saltwater (AQUIL) 35 8 16 35.00 8.00 2.00 16.00

571 Tisbe Natural saltwater (Drobak, Oslofjord, Norway) 34 8 13 34.00 8.00 2.00 13.00

573 Trachinotus Natural saltwater (Grand Isle, LA) 10 22.5 10.00 7.81 2.00 22.50

574 Trachinotus Natural saltwater (Grand Isle, LA) 20 22.5 20.00 7.81 2.00 22.50

575 Trachinotus Natural saltwater (Grand Isle, LA) 30 7.81 22.5 30.00 7.81 2.00 22.50

577 Turbo Natural saltwater (location not given) 37.43 8.17 27 37.43 8.17 2.00 27.00

730 Mytilus Natural uncontaminated seawater (assumed collected from the 

Sinop Coast of the Black Sea, Turkey) 17.5 7.95 1.92% -TOC 15 17.50 7.95 2.00 15.00

731 Mytilus Natural uncontaminated seawater (assumed collected from the 

Sinop Coast of the Black Sea, Turkey) 17.5 7.95 1.92% -TOC 15 17.50 7.95 2.00 15.00

732 Mytilus Natural uncontaminated seawater (assumed collected from the 

Sinop Coast of the Black Sea, Turkey) 17.5 7.95 1.92% -TOC 15 17.50 7.95 2.00 15.00

733 Mytilus Natural uncontaminated seawater (assumed collected from the 

Sinop Coast of the Black Sea, Turkey) 17.5 7.95 15 17.50 7.95 2.00 15.00

734 Acartia Artificial salt water 5 6.88 <0.1 20 5.00 6.88 0.10 20.00

735 Acartia Artificial salt water 15 7.21 <0.1 20 15.00 7.21 0.10 20.00

736 Acartia Artificial salt water 30 7.49 <0.1 20 30.00 7.49 0.10 20.00

737 Amphiascoides Artificial salt water, Instant Ocean Sea Salt, USA 30 23 30.00 7.43 0.20 23.00

738 Amphiascoides Artificial salt water, Instant Ocean Sea Salt, USA 30 23 30.00 7.43 0.20 23.00

739 Amphiascoides Artificial salt water, Instant Ocean Sea Salt, USA 30 23 30.00 7.43 0.20 23.00

740 Amphiascoides Artificial salt water, Instant Ocean Sea Salt, USA 30 23 30.00 7.43 0.20 23.00

741 Balanus Filtered natural sea water (assumed collected at Ionian Sea, 

southern Italy) 37 20 37.00 7.80 2.00 20.00

742 Balanus Filtered natural sea water (assumed collected at Ionian Sea, 

southern Italy) 37 20 37.00 7.80 2.00 20.00

743 Penaeus

Filtered natural saltwater (collected from unpolluted site in 

Neelangarai, India) 28 7.78 28 28.00 7.78 2.00 28.00

744 Mugil Natural filtered seawater (source ) 28 7.78 28 28.00 7.78 2.00 28.00

745 Brachionus Artificial salt water, Instant Ocean Sea Salt, USA 4 6.3 1.4 25 4.00 6.30 1.40 25.00
H-14

BLM 

Data 

Label

Genus

Reported chemistry Reported plus assumed chemistrya

Source water type Salinity, 

g/kg pH DOC, mg C/L

Temp, 

°C

Salinity, 

g/kg pH DOC, mg C/L

Temp,

°C

746 Brachionus Artificial salt water, Instant Ocean Sea Salt, USA 14 6.9 1.4 25 14.00 6.90 1.40 25.00

747 Brachionus Artificial salt water, Instant Ocean Sea Salt, USA 26 7.8 1.4 26 26.00 7.80 1.40 26.00

748 Brachionus Artificial salt water, Instant Ocean Sea Salt, USA 14 6.6 1.4 25 14.00 6.60 1.40 25.00

749 Brachionus Artificial salt water, Instant Ocean Sea Salt, USA 14 6.7 5 25 14.00 6.70 5.00 25.00

750 Brachionus Artificial salt water, Instant Ocean Sea Salt, USA 14 6.9 10 25 14.00 6.90 10.00 25.00

751 Centropomus Natural filtered estuarine water from the Piraqueacu River, Brazil 32.2 7.58 24.6 32.20 7.58 2.00 24.60

752 Mytilus Natural estuarine water (Nieuwpoort, Belgium) + DI water + 

artificial sea water 22.9 3 16 22.90 7.80 3.00 16.00

753 Mytilus Natural estuarine water (Nieuwpoort, Belgium) + DI water + 

artificial sea water 24.7 1.24 16 24.70 7.80 1.24 16.00

754 Mytilus Natural estuarine water (Nieuwpoort, Belgium) + DI water + 

artificial sea water 25.1 3.92 16 25.10 7.80 3.92 16.00

755 Mytilus Natural estuarine water (Nieuwpoort, Belgium) + DI water + 

artificial sea water 29.8 0.56 16 29.80 7.80 0.56 16.00

756 Mytilus Natural estuarine water (Nieuwpoort, Belgium) + DI water + 

artificial sea water 29.8 4.66 16 29.80 7.80 4.66 16.00

757 Mytilus Natural estuarine water (Nieuwpoort, Belgium) + DI water + 

artificial sea water 29.9 2.8 16 29.90 7.80 2.80 16.00

758 Mytilus Natural estuarine water (Nieuwpoort, Belgium) + DI water + 

artificial sea water 30 2.8 16 30.00 7.80 2.80 16.00

759 Mytilus Natural estuarine water (Nieuwpoort, Belgium) + DI water + 

artificial sea water 34.9 1.46 16 34.90 7.80 1.46 16.00

760 Brachionus Recon saltwater + natural saltwater (Bouctouche) 30.1 8 4.83 25 30.1 8 4.83 25

761 Brachionus Recon saltwater + natural saltwater (Petit Rocher) 30.2 8 2.1 25 30.2 8 2.1 25

762 Brachionus Recon saltwater + natural saltwater (Major Kollock Creek) 29.9 8 7.57 25 29.9 8 7.57 25

763 Brachionus Recon saltwater + natural saltwater (Naufrage Harbour) 29.9 8 5.2 25 29.9 8 5.2 25

764 Brachionus Recon saltwater + natural saltwater (Rathtrevor Beach) 30.1 8 1.37 25 30.1 8 1.37 25

765 Brachionus Recon saltwater + natural saltwater (Hawke's Bay) 30 8 1.28 25 30 8 1.28 25

766 Brachionus Recon saltwater + natural saltwater (Blackberry Bay) 29.9 8 2.03 25 29.9 8 2.03 25

767 Brachionus Recon saltwater + natural saltwater (Chesterman Beach) 30.1 8 0.55 25 30.1 8 0.55 25

768 Brachionus Recon saltwater + natural saltwater (Jimbo) 30.1 8 1.13 25 30.1 8 1.13 25

769 Mytilus Artificial seawater (ASTM 2004) 36 7.9-8.1 16 36 8 2 16

770 Mytilus Artificial seawater (ASTM 2004) 36 7.9-8.1 16 36 8 2 16

771 Perna Natural seawater (Neelangarai, India) 28 7.78 28 28 7.78 2 28

772 Nitokra Natural seawater 7

4.7 

(TOC) 22 7 7.8 4.7 22

773 Orchomenella Natural seawater (source not defined) 33 10 33 7.8 2 10

774 Penaeus Natural seawater (Neelangarai, India) 28 7.78 28 28 7.78 2 28

775 Limulus Artificial seawater (Instant Ocean) 20 6.7-9.0 18-29 20 7.85 0.2 23.5
H-15

BLM 

Data 

Label

Genus

Reported chemistry Reported plus assumed chemistrya

Source water type Salinity, 

g/kg pH DOC, mg C/L

Temp, 

°C

Salinity, 

g/kg pH DOC, mg C/L

Temp,

°C

776 Limulus Artificial seawater (Instant Ocean) 20 6.7-9.0 18-29 20 7.85 0.2 23.5

777 Limulus Artificial seawater (Instant Ocean) 20 6.7-9.0 18-29 20 7.85 0.2 23.5

778 Arbacia Natural seawater (source not provided) 30 8.01-8.06 20 30 8.035 2 20

779 Cyprinodon Natural seawater (Gulf of Mexico) + DI water 2 20 2 7.8 2 20

780 Cyprinodon Natural seawater (Gulf of Mexico) + DI water 15 20 15 7.8 2 20

781 Cyprinodon Natural seawater (Gulf of Mexico) + DI water 2 20 2 7.8 2 20

782 Cyprinodon Natural seawater (Gulf of Mexico) + DI water 15 20 15 7.8 2 20

C1 Brachionus Artificial saltwater (Instant Ocean) 15 7.3-7.6 <1.0 23.9-

26.1 15 7.45 1 25

C2 Cyprinodon Natural saltwater (ERLN, Narragansett, RI) 28-32 23-27 30 7.92 1.45 25

a Given the relatively constant composition of marine waters, average values were reasonable estimates for missing parameters in a given toxicity test.
H-16

Appendix Table H-2. Summary Statistics of the Reported Water Chemistry for the 

Acceptable Toxicity Tests.

Salinity

(g/kg) pH

DOC

(mg C/L)

Temperature

(°C)

Minimum 2.0 6.3 0.1 4.5

Maximum 41.7 9.0 12.0 30.0

Average 26.5 7.9 3.3 19.0

Appendix Table H-3. Average Chemistry

Location

Salinity 

(g/kg) pH

DOC 

(mg C/L)

Temperature

(°C)

Narragansett 7.92 1.45 17

Puget 7.99 1.46 11

Granite Canyon 7.99 1.74 15.7

Grand Isle 7.81

Bodega 7.6 0.893

San Francisco 7.95

Black Sea 2

Cambridge 3.63

Bear Cut 7.84 2.43

Instant Ocean1 7.43 0.2

Tropic Marin1 8.25 0.6

default 30 7.8 2 20

1 Based on Arnold et al. 2007.
I-1

Appendix I Discussion of BLM Water Quality Parameters in the 

Estuarine/Marine Environment and Example Numeric 

Criteria Values
I-2

The pH of marine environments is relatively stable, where pH typically remains between 

7.5 and 8.4 (Sverdrup et al. 1942). However, regional factors can temporarily affect pH in these 

systems. For example, the upwelling of deeper more acidic waters along the west coast of North 

America can temporarily lower the pH of surface waters (Feely et al. 2008). In comparison, pH 

is much more variable in estuaries, embayments, harbors, and other semi-enclosed coastal 

systems. The influx of freshwater from rivers, groundwater, and surficial runoff can lower the 

pH of these systems, based on the typically lower pH of freshwater (around 7) (Caldeira and 

Wickett 2003). Photosynthesis, meanwhile, can increase pH levels and algal blooms have been 

reported to increase pH levels above 9 in some estuaries, to the point where pH becomes lethal to 

aquatic species (Hansen 2002).

The salinity of marine systems is also relatively stable, with an average salinity of 35 ppt 

and range of 32 to 38 ppt across the world’s oceans (Kalle 1971). Salinity within coastal waters 

can have greater variability, due primarily to the input of freshwater from rivers, surficial runoff, 

groundwater input, and tidal and coastal currents. Salinity can also vary as a result of diurnal, 

seasonal, and annual cycles and episodic occurrences (e.g, storm events). Salinity in semienclosed systems, including estuaries, embayments, and harbors can have extreme variability 

over space and time, and can have salinity ranging from saline to freshwater (<2 ppt). In the 

Cheseapeake Bay, for example, average salinity ranges from freshwater (<0.5 ppt) in the upper 

reaches of the Bay to full marine salinity adjacent to the Atlantic Ocean (VIMS 2016). Salinity 

typically decreases in the Chesapeake Bay during the spring, with increased freshwater inputs 

resulting from rain and snowmelt, and increases during the summer with increasing levels of 

evaporation (Levinton 2001). Inputs (e.g., municipal discharges) and changes in water flow 

patterns as a result of anthropogenic activity can also significantly affect the salinity of estuarine 

and marine systems.

DOC in estuarine and marine systems in most cases reflects a diversity of inputs from

allochthonous and autochthonous sources that can originate from both terrestrial and aquatic 

autotrophs (inclusive of unicellular algae and vascular plants) and heterotrophs (inclusive of 

bacteria, fungi, and multicellular organisms) (Bauer and Bianchi 2011; Cloern 1996; Raymond 

and Bauer 2001; Cauwet 2002; Aitkenhead-Peterson et al. 2003; Bertilsson and Jones 2003). The 

highest DOC concentrations are generally found in estuarine and associated riverine systems, 

with DOC concentrations generally decreasing with movement from the estuarine to marine 
I-3

environment (Bauer and Bianchi 2011). DOC concentrations within estuarine and riverine

systems can vary greatly, with some of the highest known DOC concentrations occurring in 

estuaries within the Gulf of Mexico, where DOC concentrations of greater than 1,000 μM 

(equivalent to approximately 12 mg/L) have been reported (Bauer and Bianchi 2011; Guo et al. 

1999; Engelhaupt and Bianchi 2001). Although variable both spatially and temporally, 

representative DOC values reported for most other estuarine and riverine systems are lower, 

examples of which include Galveston Bay (145-469 μM, equivalent to approximately 1.7-5.6 

mg/L), Chesapeake Bay (118-215 μM, equivalent to approximately 1.4-2.6 mg/L), and 

Potomac/Patuxent River (92-333 μM, equivalent to approximately 1.1-4.0 mgL) (Guo and 

Santschi 1997; Sigleo 1996). 

Riverine systems and adjacent wetlands frequently represent important sources of DOC 

to estuarine and adjacent coastal ecosystems (Del Giorgio and Pace 2008). The magnitude of 

temporal variability in DOC loading within these systems has been shown to be related to the 

predominant source of DOC (Bianchi et al. 1998, Mantoura and Woodward 1983, Thurman 

1985). For example, fringing wetlands have been demonstrated to provide a more consistent 

source of DOC than phytoplankton blooms (Bianchi et al. 1998; Mantoura and Woodward 1983;

Thurman 1985). Anthropogenic inputs of DOC via municipal and industrial discharge can also 

alter the DOC present in estuarine and near coastal environments, either directly through the 

discharge of DOC or indirectly, such as via the discharge of nutrients which can then increase 

primary productivity. 

Removal of DOC via flocculation typically occurs with the increasing ionic strength of 

higher salinity environments (Guo et al. 1999). In coastal and marine environments, DOC is 

mostly produced by biological processes (primary and secondary production) in the upper ocean, 

and is then mixed downward and diluted by physical processes (Hansell and Carlson 2001). 

Seasonal increases in DOC concentrations can occur as a result of phytoplankton blooms, 

particularly in areas with stratification that receive nutrient inputs during the winter (Hansell and 

Carlson 2001). Deep ocean waters generally have the lowest DOC concentrations, reaching

levels of 2 μM (equivalent to approximately 0.02 mg/L) or less. DOC concentrations thus tend to

be reduced in upwelling areas where deep waters dilute the surface water concentrations, even 

when primary production levels are relatively high (Hansell and Carlson 2001).
I-4

Marine water temperatures generally range from -2°C to 28°C, with some higher 

temperatures occurring seasonally in estuarine systems. Temperature is, in general, a function of 

solar input, with higher temperatures typically occurring at lower latitudes and during the 

summer. Water temperatures in near coastal environments and semi-enclosed systems such as 

estuaries, embayments, and harbors typically have some of the greatest variability. This 

variability is due primarily to the input of freshwater from rivers, surficial runoff, groundwater 

discharge, the shallower waters frequently present in these systems, and tidal and coastal 

currents. Temperatures in coastal and open water marine environments often vary with different, 

frequently stratified water layers that are characterized by differing temperature and salinity. 

Upwelling and current patterns in these stratified systems can lead to local and regional alteration 

in the temperature profile, such as observed with the California Current, where cooler deeper 

waters are brought to the surface and significantly reduce the surface water temperature profile.

The following tables provide representative example saltwater BLM CMC and CCC 

values determined with different temperature, pH, salinity, and DOC conditions.
I-5

Appendix Table I-1. Example BLM Numeric Criteria Values at 20°C and pH 7.8.

Salinity 

(ppt)

DOC

(mg C/L)

FAV 

(μg/L)

CMC 

(μg/L)

CCC 

(μg/L)

5

1 3.294 1.6 1.1

2 6.585 3.3 2.2

4 13.16 6.6 4.4

6 19.75 9.9 6.5

8 26.33 13 8.7

10 32.91 16 11

10

1 3.423 1.7 1.1

2 6.847 3.4 2.3

4 13.68 6.8 4.5

6 20.52 10 6.8

8 27.37 14 9.1

10 34.21 17 11

15

1 3.545 1.8 1.2

2 7.090 3.5 2.3

4 14.17 7.1 4.7

6 21.26 11 7.0

8 28.35 14 9.4

10 35.44 18 12

20

1 3.662 1.8 1.2

2 7.318 3.7 2.4

4 14.64 7.3 4.8

6 21.96 11 7.3

8 29.27 15 9.7

10 36.59 18 12

25

1 3.776 1.9 1.2

2 7.550 3.8 2.5

4 15.09 7.5 5.0

6 22.64 11 7.5

8 30.17 15 10

10 37.72 19 12

30

1 3.887 1.9 1.3

2 7.771 3.9 2.6

4 15.54 7.8 5.1

6 23.29 12 7.7

8 31.07 16 10

10 38.84 19 13
I-6

Appendix Table I-2. Example BLM Numeric Criteria Values at 20°C and pH 8.0.

Salinity 

(ppt)

DOC

(mg C/L)

FAV 

(μg/L)

CMC 

(μg/L)

CCC 

(μg/L)

5

1 3.324 1.7 1.1

2 6.647 3.3 2.2

4 13.29 6.6 4.4

6 19.93 10 6.6

8 26.58 13 8.8

10 33.20 17 11

10

1 3.446 1.7 1.1

2 6.886 3.4 2.3

4 13.77 6.9 4.6

6 20.66 10 6.8

8 27.54 14 9.1

10 34.41 17 11

15

1 3.563 1.8 1.2

2 7.121 3.6 2.4

4 14.24 7.1 4.7

6 21.36 11 7.1

8 28.48 14 9.4

10 35.60 18 12

20

1 3.678 1.8 1.2

2 7.352 3.7 2.4

4 14.70 7.3 4.9

6 22.04 11 7.3

8 29.38 15 9.7

10 36.73 18 12

25

1 3.790 1.9 1.3

2 7.574 3.8 2.5

4 15.14 7.6 5.0

6 22.70 11 7.5

8 30.26 15 10

10 37.84 19 13

30

1 3.900 1.9 1.3

2 7.794 3.9 2.6

4 15.58 7.8 5.2

6 23.36 12 7.7

8 31.16 16 10

10 38.95 19 13
I-7

Appendix Table I-3. Example BLM Numeric Criteria Values at 20°C and pH 8.2.

Salinity 

(ppt)

DOC

(mg C/L)

FAV 

(μg/L)

CMC 

(μg/L)

CCC 

(μg/L)

5

1 3.279 1.6 1.1

2 6.550 3.3 2.2

4 13.10 6.5 4.3

6 19.65 9.8 6.5

8 26.20 13 8.7

10 32.75 16 11

10

1 3.387 1.7 1.1

2 6.769 3.4 2.2

4 13.53 6.8 4.5

6 20.28 10 6.7

8 27.04 14 8.9

10 33.78 17 11

15

1 3.494 1.7 1.2

2 6.978 3.5 2.3

4 13.94 7.0 4.6

6 20.91 10 6.9

8 27.87 14 9.2

10 34.85 17 12

20

1 3.600 1.8 1.2

2 7.187 3.6 2.4

4 14.37 7.2 4.8

6 21.55 11 7.1

8 28.72 14 9.5

10 35.90 18 12

25

1 3.705 1.9 1.2

2 7.396 3.7 2.4

4 14.78 7.4 4.9

6 22.17 11 7.3

8 29.55 15 9.8

10 36.94 18 12

30

1 3.810 1.9 1.3

2 7.606 3.8 2.5

4 15.20 7.6 5.0

6 22.79 11 7.5

8 30.39 15 10

10 37.95 19 13