EQUILIBRIUM PARTITIONING SEDIMENT
GUIDELINES (ESGs) FOR THE PROTECTION OF
BENTfflC ORGANISMS:
PAH MIXTURES
U. S. Environmental Protection Agency:
Office of Science and Technology and
Office of Research and Development
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1 FOREWORD
2
3 Under the Clean Water Act (CWA), the U.S. Environmental Protection Agency (EPA) and the
4 States develop programs for protecting the chemical, physical, and biological integrity of the nation's
5 waters. To meet the objectives of the CWA, EPA has periodically issued ambient water quality criteria
6 (WQC) beginning with the publication of "Water Quality Criteria, 1972" (NAS, 1973). The development
7 of WQC is authorized by Section 304(a)( 1), which directs the Administrator to develop and publish "criteria"
8 reflecting the latest scientific knowledge on (1) kind and extent of effects on human health and welfare,
9 including effects on plankton, fish, shellfish, and wildlife, mat may be expected from the presence of
10 pollutants in any body of water, including ground water; and (2) concentration and dispersal of pollutants
11 on biological community diversity, productivity, and stability. All criteria guidance through late 1986 was
12 summarized hi an EPA document entitled "Quality Criteria for Water, 1986" (U.S. EPA, 1987). Updates
13 on WQC documents for selected chemicals and new criteria recommendations for other pollutants have
14 been more recently published as "National Recommended Water Quality Criteria-Correction" (U.S. EPA,
15 1999). The EPA will continue to update the nationally recommended WQC as needed in the future.
16 In addition to the development of WQC and to continue to meet the objectives of the CWA, EPA
* 17 has conducted efforts to develop and publish equilibrium partitioning sediment guidelines (ESGs) for some
18 of the 65 toxic pollutants or toxic pollutant categories. Toxic contaminants in bottom sediments of the
19 nation's lakes, rivers, wetlands, and coastal waters create the potential for continued environmental
20 degradation even where water column contaminant levels meet applicable water quality standards. In
21 addition, contaminated sediments can lead to water quality impacts, even when direct discharges to the
22 receiving water have ceased. These guidelines are authorized under Section 304(a)(2) of the CWA, which
23 directs the Administrator to develop and publish information on, among other things, the factors necessary
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1 to restore and maintain the chemical, physical, and biological integrity of all navigable waters.
2 The ESGs and associated methodology presented in this document are EPA's best recommendation
3 as to the concentrations of a substance that may be present in sediment while still protecting benthic
4 organisms from the effects of that substance. These guidelines are applicable to a variety of freshwater
5 and marine sediments because they are based on the biologically available concentration of the substance
6 in the sediments. These ESGs are intended to provide protection to benthic organisms from direct toxicity
7 due to this substance. In some cases, the additive toxicity for specific classes of toxicants (e.g., metal
8 mixtures or polycyclic aromatic hydrocarbon mixtures) is addressed. The ESGs do not protect against
9 synergistic or antagonistic effects of contaminants or bioaccumulative effects to benthos. They are not
10 protective of wildlife or human health endpoints.
11 EPA recommends that ESGs be used as a complement to existing sediment assessment tools, to help
12 assess the extent of sediment contamination, to help identify chemicals causing toxicity, and to serve as
13 targets for pollutant loading control measures. EPA is developing guidance to assist in the application of
14 these guidelines in water-related programs of the States and this Agency. This document provides guidance
15 to EPA Regions, States, the regulated community, and the public. It is designed to implement national
16 policy concerning the matters addressed. It does not, however, substitute for the CWA or EPA's
17 regulations, nor is it a regulation itself. Thus, it cannot impose legally binding requirements on EPA,
18 States, or the regulated community. EPA and State decision makers retain the discretion to adopt
19 approaches on a case-by-case basis that differ from this guidance where appropriate. EPA may change this
20 guidance in the future.
21 This document has been reviewed by EPA's Office of Science and Technology (Health and
22 Ecological Criteria Division, Washington, D.C.) and Office of Research and Development (Mid-Continent
23 'Ecology Division, Duluth, MN; Atlantic Ecology Division, Narragansett, RI; Western Ecology Division.
24 Corvallis, OR), and approved for publication.
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1 Mention of trade names or commerc ial products does not constitute endorsement or recom mendation
2 of use.
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1 2.1 SECTION OVERVIEW 2-1
2 2.2 NARCOSIS MODEL BACKGROUND 2-2
3 2.3 BODY BURDEN MODEL 2-3
4 2.4 TARGET LIPID MODEL : . . 2-5
5 2.5 ACUTE LETHALITY DATABASE COMPILATION 2-9
6 2.5.1 Aqueous Solubility 2-10
7 2.5.2 Exposure Duration 2-10
8 2.6 DATA ANALYSIS . . . . 2-11
9 2.6.1 Regression Model 2-12
10 2.6.2 Testing The Model Assumptions 2-14
11 2.6.3 Volume Fraction Hypothesis 2-15
12 2.6.4 Chemical Classes 2-16
13 2.6.4.1 Statistical Analysis of ^oW-Toxicity Relationships 2-16
14 2.6.4.2 Standard Errors And Residuals • 2-18
15 2.6.4.3 Chemical Class Corrections 2-19
16 2.7 UNIVERSAL NARCOSIS SLOPE 2-20
17 2.8 COMPARISON TO OBSERVED BODY BURDENS 2-22
18 2.9 MIXTURES AND ADDnTVITY 2-23
19 2.10 AQUEOUS SOLUBILITY CONSTRAINT 2-24
20
21 SECTION 3 3-1
22 TOXICITY OF PAHs IN WATER AND
23 DERIVATION OF PAH-SPECIFIC FCVs 3-1
24 3.1 NARCOSIS THEORY, EqP THEORY AND WQC GUIDELINES:
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1 CONTENTS
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3 FOREWORD i
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5 ACKNOWLEDGMENTS x
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7 EXECUTIVE SUMMARY xi
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9 TABLES xiv
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11 FIGURES xvi
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13 GLOSSARY OF ABBREVIATIONS xxi
• r
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15 SECTION : 1-1
16 INTRODUCTION 1-1
17 1.1 LEGISLATIVE MANDATE AND NEED FOR ESGs 1-1
18 1.2 EQUILIBRIUM PARTITIONING AS A TECHNICAL BASIS FOR
19 DERIVATION OF AN ESG FOR MIXTURES OF PAHs 1-2
20 1.3 OVERVIEW 1-4
21
22 SECTION 2 2-1
23 NARCOSIS THEORY: MODEL DEVELOPMENT AND APPLICATION FOR PAH
24 MIXTURES 2-1
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1 DERIVATION OF PAH-SPECIFIC FCVs FOR INDIVIDUAL PAHs ... 3-1
2 3.2 ACUTE TOXICITY OF INDIVIDUAL PAHS: WATER EXPOSURES . 3-3
3 3.2.1 Acute Toxicity of PAHs 3-3
4 3.2.2 Acute Values 3-3
5 3.3 CHRONIC TOXICITY OF INDIVIDUAL PAHS: WATER EXPOSURES 3-5
6 3.3.1 Acenaphthene 3-5
7 3.3.2 Anthracene 3-7
8 3.3.3 Fluoranthene 3-8
9 3.3.4 Phenanthrene 3-8
10 3.3.5 Pyrene 3-9
11 3.3.6 Naphthalene 3-10
12 3.3.7 Derivation of the Final Acute Chronic Ratio 3-10
13 3.4 APPLICABILITY OF THE WQC AS THE EFFECTS CONCENTRATION
14 FOR BENTHIC ORGANISMS .3-11
15 3.5 DERIVATION OF FCVs 3-13
16 3.5.1 Derivation of the FCV at a ATOW of 1.0 3-13
17 3.5.2 Derivation of the PAH-Specific FCVs 3-14
18 •
19 SECTION 4 4-1
20 DERIVATION OF ESGs 4-1
21 4.1 DERIVATION OF POTENCIES FOR INDIVIDUAL PAHs IN SEDIMENTS
22 (Q)C.PAHi.FCw) • ^-l
23 4.2 DERIVATION OF THE ESG FOR PAH MIXTURES . . . 4-2
24 4.3 AQUEOUS SOLUBILITY CONSTRAINT 4-3
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1 4.4 COMPARISON OF THE EESGTUFCV FOR MIXTURES OF PAHs IN
2 SEDIMENTS FROM CALIFORNIAN, VIRGINIAN, LOUSIANIAN
3 PROVINCES, NY/NJ HARBOR, EMAP AND REMAP AND NOAA
4 _ DATABASES 4-4
5 4.5 EXAMPLE CALCULATION OF ESG FOR PAHs AND EqP-BASED
6 INTERPRETATION . 4-6
7
8 SECTION 5 .5-1
9 TOXICITY OF PAHs
10 PAHs IN SPIKED AND FIELD SEDIMENTS 5-1
11 5.1 INTRODUCTION 5-1
12 5,2 SPIKED SEDIMENT TOXICITY TESTS . 5-1
13 5.2.1 Interstitial Water Concentrations and Sediment Toxicity: Relevance to
14 Water-Only Toxicity Tests and WQC FCVs 5-1
15 5.2.2 Sediment Toxicity: Prediction Using Water-Only Toxicity and KQC 5-3
16 5.2.3 Toxicity of Individual PAH Compounds 5-4
17 5.2.4 Comparison of Sediment Toxicity to COC.PAHI.FCV/ 5-5
18 . 5.2.5 PAH Mixtures 5-7
19 5.2.6 Additivity of PAH Mixtures 5-8
20 5.2.7 PAH Additivity Demonstrated Using the Universal Narcosis Slope 5-10
21 5.2.8 Additivity of Mixtures of High ^Tow PAH Compounds 5-11
22 5.3 FIELD SEDIMENTS VS ESG FOR PAH MIXTURES . . 5-15
23 5.3.1 Toxicity to R. abronius of Field Sediments Containing PAH Mixtures
24 vs. PSTUs Derived from Narcosis Theory 5-16
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1 5.3.2 Organism Abundance vs. ESG for PAH Mixtures 5-17
2
3 SECTION 6 . . 6-1
4 IMPLEMENTATION 6-1
5 6.1 INTRODUCTION 6-1
6 6.2 DEFINING TOTAL PAH CONCENTRATION IN FIELD COLLECTED
7 SEDIMENTS 6-1
8 6.2.1 Introduction 6-3
9 6.2.2 Data Collection 6-4
10 6.2.3 Methodology 6-5
11 6.2.4 Uncertainty in Predicting SESGTUFCViTOT : ... 6-6
12 6.3 INTERPRETING ESGs IN COMBINATION WITH TOXICITY TESTS . 6-8
13 6.4 PHOTO-ACTIVATION 6-11
14 6.4.1 Overview 6-11
15 6.4.2 Implications to Derivation of ESG 6-13
16 6.5 TERATOGENICITY AND CARCINOGENICITY 6-13
17 6.5.1 Calculations 6-15
18 6.5.2 Critical Sediment Concentrations for Teratogenic and Carcinogenic
19 Effects versus ESGs for PAH Mixtures 6-16
20 6.6 EQUILIBRIUM AND ESGs 6-17
21 6.7 OTHER PARTITIONING PHASES 6-18
22 6.7.1 Overview 6-18
23 6.7.2 Implications to Derivation of ESG 6-20
24 6.8 AQUEOUS SOLUBILITY UNDER NON-STANDARD CONDITIONS . 6-21
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1
2 SECTION 7 7_!
3 SEDIMENT GUIDELINE STATEMENT 7-1
4 7.1 SEDIMENT GUIDELINE STATEMENT 7-1
5 7.2 SPECIAL CONSIDERATIONS 7-2
6
7 SECTION 8 8-1
8 REFERENCES 8-1
9
10 Appendix A A-l
11 Appendix B B-l
12 Appendix C C-l
13 Appendix D D-l
14 Appendix E E-l
15 Appendix F F-l
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1 ACKNOWLEDGMENTS
2 Coauthors
3 David J. Hansen HydroQual, Inc., Mahwah, NJ; Great Lakes Environmental Center, Traverse
4 City, MI (formerly with U.S. EPA)
5 Dominic M. DiToro Manhattan College, Bronx, NY; HydroQual, Inc., Mahwah, NJ
6 Joy A. McGrath HydroQual, Inc., Mahwah, NJ
7 Richard C. Swartz Environmental consultant (formerly with U.S. EPA)
8 David R. Mount* U.S. EPA, NHEERL, Mid-continent Ecology Division, Duluth, MN
9 Robert M. Burgess* U.S. EPA, NHEERL, Atlantic Ecology Division, Narragansett, RI
10 Robert J. Ozretich U.S. EPA, NHEERL, Pacific Ecology Division, Newport, OR
11 Heidi E. Bell* U.S. EPA, Office of Water, Washington, DC
12 Mary C. Reiley U.S. EPA, Office of Water, Washington, DC
13 Tyler K. Linton Great Lakes Environmental Center, Columbus, OH
14
15 Significant Contributors to the Development of the Approach and Supporting Science
16 David J. Hansen HydroQual, Inc., Mahwah, NJ; Great Lakes Environmental Center, Traverse
17 City, MI (formerly with U.S. EPA)
18 Dominic M. Di Toro Manhattan College, Bronx, NY; HydroQual, .Inc., Mahwah, NJ
19 Joy A. McGrath HydroQual, Inc., Mahwah, NJ
20 Richard C. Swartz Environmental consultant (formerly with U.S. EPA)
21 David R. Mount U.S. EPA, NHEERL, Mid-continent Ecology Division, Duluth, MN
22 Robert M. Burgess U.S. EPA, NHEERL, Atlantic Ecology Division, Narragansett, RI
23 Robert J. Ozretich U.S. EPA, NHEERL, Pacific Ecology Division, Newport, OR
24 Robert L. Spehar U.S. EPA, NHEERL, Mid-continent Ecology Division, Duluth, MN
25
26 Technical Support and Document Review
27 Walter J. Berry U.S. EPA, NHEERL, Atlantic Ecology Division, Naragansett, RI
28 Tyler K. Linton Great Lakes Environmental Center, Columbus, OH
29 Robert L. Spehar U.S. EPA, NHEERL, Mid-continent Ecology Division, Duluth, MN
30
31 *Principle U.S. EPA contact
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1 EXECUTIVE SUMMARY
2
3 This equilibrium partitioning sediment guideline (ESG) document recommends an approach for
4 summing the lexicological contributions of mixtures of 34 PAHs in sediments to determine if their
5 concentrations in any specific sediment would be protective of benthic organisms from their direct
6 toxicity. The combination of the equilibrium partitioning (EqP), narcosis theory, and additivity provide
7 the technical foundation for this guideline. These approaches were required because PAHs occur in
8 sediments in a variety of proportions as mixtures and can be expected to act jointly under a common
9 mode of action. Therefore, their combined toxicological contributions must be predicted on a
10 sediment-specific basis. This overall approach provides for the derivation of an ESG that is causally
11 linked to the specific mixtures of PAHs in a sediment, yet is applicable across sediments and
12 appropriately protective of benthic organisms.
13 The EqP approach was chosen because it takes into account the varying biological availability
14 of chemicals in different sediments and allows for incorporation of the appropriate biological effects
15 concentration to predict the concentration of a nonionic organic chemical in sediment diat is protective
16 of benthic organisms. In its assertion, EqP theory holds that nonionic chemicals in sediment partition
17 between sediment organic carbon, interstitial water and benthic organisms. At equilibrium, if the
18 concentration in any one phase is known then the concentration in the others can be predicted. The
19 ratio of the concentration in water to the concentration in organic carbon is termed the organic carbon
20 partition coefficient (K^, which is a constant for each chemical. The ESG Technical Basis Document
21 demonstrates that biological responses of benthic organisms to nonionic organic chemicals in sediments
22 are different across sediments when the sediment concentrations are expressed on a dry weight basis,
23 but similar when expressed on a jug chemical/g organic carbon (g^) basis. Responses were also
24 similar across se diments when interstitial water concentrations were used to normalize biological
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1 using the recommended uncertainty limits. The ESG for total PAH is the sum of the quotients of each
2 of the 34 individual PAHs in a specific sediment divided by the Qx- PAH/ FCV(. of that particular PAH.
3 This sum is termed the Equilibrium Partitioning Sediment Guideline Toxic Unit (SESGTUFCV) which is
4 based on the final chronic value. Sediments exhibiting < 1.0 SESGTUFCV of the mixture of the 34
5 PAHs are acceptable for the protection of benthic organisms. This provides for the derivation of a
6 guideline that is causally linked to the specific mixtures of PAHs in a sediment, applicable across
7 sediments, and appropriately protective of benthic organisms.
8 This guideline does not protect against additive, synergistic or antagonistic effects of other
9 contaminants or bioaccumulative effects of PAHs to other aquatic life, wildlife or humans. Research is
10 needed to characterize the toxicological importance of PAHs not measured in this definition of total
11 PAH. It is the position of the Agency and the EPA Science Advisory Board (SAB) that the use of
12 equilibrium partitioning sediment guidelines as stand-alone, pass-fail criteria is not recommended for all
13 applications and should frequently trigger additional studies at sites under investigation. This ESG
14 applies only to sediments having iO.2% organic carbon.
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1 availability. The ESG Technical Basis Document further demonstrates that if the effect concentration
2 in water is known, the effect concentration in sediments on a Mg/goc Dasis can De accurately predicted
3 by multiplying the effect concentration in water by the chemical's KQC. Because the water quality
4 criteria final chronic value (WQC FCV) is the concentration of a chemical in water that is protective of
5 the presence of aquatic life, and is appropriate for benthic organisms, the product of the WQC FCV
6 and K^ is the concentration in sediments that on an organic carbon basis is protective of benthic
7 organisms.
8 Narcosis theory was used to (1) demonstrate that the slope of the acute toxicity-ATow
9 relationship was similar across species; (2) normalize the acute toxicity of all PAHs in water to an
10 aquatic species to a reference ^Tow of 1.0 (where the concentration in water and lipid of the organism
11 would be essentially the same); (3) establish an acute sensitivity ranking for individual species at the
12 ATOW of 1.0; and (4) to use the rankings and water-only acute-chronic ratios to calculate protective
13 concentrations of specific PAHs in tissues Og/g lipid) and water (FCV, Aig/L) using the U.S. EPA
14 National Guidelines (Stephan et al., 1985). The EqP approach was then used to calculate the effect
15 concentration for these specific PAHs in sediment (Cocp^^f^/i, fig/g organic carbon) from the product
16 of the PAH-specific FCV and K^.
17 Importantly, because PAHs occur in sediments as mixtures and their toxicities in water, tissues,
18 and sediments are additive or nearly additive, the consideration of their toxicities on an individual basis
19 would result in guidelines that are under-protective. For this reason the combined toxicological
20 contributions of the PAH mixture must be used. The U.S. EPA recommends the use of the 34 PAHs
21 monitored hi the EMAP program to derive a concentration of "total PAH." Many monitoring and
22 assessment efforts measure a smaller group of PAHs, such as 13 or 23 PAHs; adjustment factors have
23 been calculated to relate these smaller subsets to the expected concentration of the 34 PAHs, although
24 use of these factors will result in a substantial incidence of false positives when total PAH is estimated
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Table 5-2. Percent mortality of benthic invertebrates in relation to the sum of the equilibrium
partitioning sediment guideline toxic units (SESGTUs) of mixtures of PAHs spiked into
sediment.
Table 5-3. Chemicals included in the high /Tow PAH mixture experiment conducted by Spehar et
al. (2000).
Table 6-1. Relative distribution of ZESGTUFCV,TOT to SESGTUpcv.u and SESGTUFCVr23 for the
combined EMAP dataset.
Table 6-2. PAHs measured in various sediment monitoring programs.
Table 6-3. Teratogenic and carcinogenic effects of benzo(a)pyrene (BaP) and anthracene on
freshwater and saltwater fishes.
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TABLES
Table 2-1. Regression results: y-intercepts and chemical class corrections.
Table 2-2. Comparison of body burdens observed in aquatic organisms acutely exposed to narcotic
chemicals and body burdens predicted from target lipid narcosis theory.
Table 3-1. Summary of the chronic sensitivity of freshwater and saltwater organisms to PAHs;
test-specific data.
Table 3-2. Summary of acute and chronic values, acute-chronic ratios and derivation of the final
acute values, final acute-chronic ratios, and final chronic values.
Table 3-3. Results of the approximate randomization (AR) tests for the equality of freshwater and
saltwater FAV distributions at a K^, of 1.0 and AR tests for the equality of benthic and
combined benthic and water column FAVs for freshwater and saltwater distributions.
Table 3-4. Qx:,pAHi.Fcv; concentrations and properties required for their derivation.
Table 4-1. ESGs for PAH mixtures: Example calculations for three sediments
Table 5-1. Water-only and spiked-sediment LC50 values used to test the applicability of narcosis
and EqP theories to the derivation of ESG for PAHs.
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1 corrections included in the regression.
2
3 Figure 2-7. The coefficient of variation of the estimated species-specific body burdens versus the
4 number of data points for that species (A), the log probability plot of the residuals (B),
5 and the residuals versus log10ATow (C).
6
7 Figure 2-8. Log10LC50 versus Iog10£"ow for (A) Lepomis macrochirus, (B) Daphnia pulex, and (C)
8 Gambusia affinis. The line connects the individual estimates of the log10LC50 values,
9 including the chemical class correction.
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11 Figure 2-9. Comparison of target lipid model, line-of-fit and observed LC50 data for individual
12 PAHs, by species.
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14 Figure 2-10. Predicted and observed body burdens for five species.
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16 Figure 2-11. Additivity of type I narcosis toxicity. Comparison of the observed TU concentrations
17 calculated from four studies to the predicted TU of 1.0.
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19 Figure 3-1. GMAVs at a logloKOVf of 1.0 from water-only acute toxicity tests using freshwater and
20 saltwater genera versus percentage rank of their sensitivity.
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22 Figure 3-2. Probability distributions of FAV difference statistics to compare water-only toxicity
23 data from (A) freshwater versus saltwater genera and (B) benthic versus WQC.
24
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1 FIGURES
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3 Figure 2-1. Schematic diagram of the log10LC50 versus Iog10^ow relationship. At Iog10^ow = 0
4 (£ow = 1). the concentration in water equals the concentration in octanol.
5
6 Figure 2-2. Comparisons of (A) loglQKow predicted by SPARC versus measured logloKow using
7 slow stir method and (B) reported log,0LC50 values versus the aqueous solubility
8 estimated by SPARC. The diagonal line represents equality.
9
10 Figure 2-3. Ratios of (A) 48- to 96-hour LC50 values and (B) 24- to 96-hour LC50 values versus
11 Iog10£ow. The line in (B) is the regression used to correct the 24-hour LC50 to 96-hour
12 LC50.
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14 Figure 2-4. Log10LC50 versus Iog10£ow for the indicated species. The line has a constant slope of
15 -0.945. The y-intercepts vary for each species. Outliers are denoted by a plus symbol
16 (+).
17
18 Figure 2-5. Statistical comparison of slopes fitted to individual species to the universal slope of
19 -0.945 showing (A) the probability that the difference occurred by chance (filled bars)
20 and number of data points in the comparison (hatched bars) for each species in the
21 database, and (B) the deviations of the individual estimates from the universal slope.
22 -
23 Figure 2-6. Chemical class comparisons. (A) Residuals from the regression grouped by class with
24 mean ± 2 standard errors. (B)Residuals grouped by class with chemical class
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1 sediment spiked with a mixture of high Kovf PAH.
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3 Figure 5-7. Response ofHyalella azteca exposed for 28 days under flow-through conditions to
4 sediment spiked with a mixture of high Kovf PAH.
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6 Figure 5-8. Survival (after 28 days) and growth (after 10 days) ofHyalella azteca expressed on the
7 basis of measured PAH concentrations in tissues (lipid normalized).
8
9 Figure 5-9. Response ofHyalella azteca exposed for 10 days (3 renewals) to sediment spiked with
10 a mixture of high Kow PAH.
11
12 Figure 5-10. Response of Leptocheirus plumulosus exposed for 10 days under static conditions to
13 sediment spiked with a mixture of high Kow PAH.
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15 Figure 5-11. Amphipod (Ampelisca abdita) abundance versus 2ESGTUFCV.
16 .
17 Figure 6-1. Comparison of observed SESGTUFCv.Toi to observed SESGTUpcv^ from 13 PAHs (A)
18 and SESGTUFCV23 from 23 PAHs (B) for the combined dataset including U.S. EPA
19 EMAP Louisian and Carolinian Provinces.
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21 Figure 6-2. Probability distribution of the (A) 2ESGTUFCVpl3 and (B) EESGTUFCV-23 values for each
22 sediment from the entire database.
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24 Figure 6-3. BaP concentration of 539 sediment samples from the EMAP and Elliott Bay datasets
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1 Figure 4-1. Probability distribution of the SESGTUFCV for PAH mixtures in sediments from
2 individual coastal and estuarine locations in the United States.
3
4 Figure 4-2. Probability distribution of the SESGTUFCV for PAH mixtures in sediments from all of
5 the coastal and estuarine locations in the United States.
6
7 Figure 5-1. Percent mortality versus predicted interstitial water toxic units for six chemicals and
8 three sediments per chemical.
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10 Figure 5-2. Percent mortality versus predicted sediment toxic units for seven chemicals and three
11 sediments per chemical.
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13 Figure 5-3. Percent mortality of Rhepoxynius abronius in sediments spiked with acenaphthene,
14 phenanthrene, fluoranthene, or pyrene concentrations in sediment normalized to
15 ESGTUFCV(,
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17 Figure 5-4. Percentage rank, based on ESGTUpcv,, of the sensitivities of genera of benthic
18 organisms from spiked sediment toxicity tests.
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20 Figure 5-5. Mortality of the amphipod, Rhepoxynius abronius, from 10-day sediment toxicity tests
21 with four parent PAHs separately (triangles) and in combination (closed circles) versus
22 predicted sediment toxic units.
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24 Figure 5-6. Response ofHyalella azteca exposed for 10 days under flow-through conditions to
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1 versus the EESGTUFCV values of 34 PAHs (A) and a probability plot of these BaP
2 concentrations at an SESGTUFCV =1.0 (B).
3
4 Figure 6-4. Anthracene concentration of 539 sediment samples from the EMAP and Elliott Bay
5 datasets versus the SESGTUFCV values of 34 PAHs (A) and a probability plot of these
6 anthracene concentrations at an SESGTUFCV =1.0 (B).
7
8 Figure 6-5. Computed solubilities of nine PAHs relative to their 25 °C solubilities as a function of
9 temperature.
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GLOSSARY OF ABBREVIATIONS (continued)
Coefficient of Variation
Clean Water Act
Dtssolved Organic Carbon
Concentration affecting 50% of the test organisms
Environmental Monitoring and Assessment Program
United States Environmental Protection Agency
Equilibrium partitioning
Equilibrium Partitioning Sediment Guideline(s)
Equilibrium Partitioning Sediment Guideline Toxic Unit for PAH,- based on the FCV
Equilibrium Partitioning Sediment Guideline Toxic Unit for PAH, based on the LC50
of Rhepoxynius abronius.
Sum of Equilibrium Partitioning Sediment Guideline Toxic Units, where the units are
based on FCV values
Fraction of lipid in the organism
Fraction of organic carbon hi sediment
Fraction of soot carbon in sediment
Final Acute-Chronic Ratio
Final Acute Value
Final Chronic Value
Genus Mean Acute Value
Interstitial Water Toxic Unit
IWTUFCV Interstitial water toxic unit calculated by dividing the dissolved interstitial water
concentration by the FCV
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ev
CWA
DOC
EC50
EMAP
EPA
EqP
ESG
ESGTUFCV|
ESGTU^
SESGTUrcv
Aipid
foe
fsc
FACR
FAV
FCV
GMAV
IWTU
IWTUFCV
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8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
ACR
AR
ASTM
BaP
BCF
Q
Q
a
Qx;
Q)C,PAHi
r1
'-'octanol
Co*
^Org
ciw
COCPXK,
^OC,PAHi.i
('OC.PAHi.i
GLOSSARY OF ABBREVIATIONS
Acute-Chronic Ratio
Approximate Randomization
American Society for Testing and Materials
Benzofajpyrene
Bioconcentration factor
Freely-dissolved interstitial water concentration of contaminant
Chemical concentration in target lipid
Critical body burden in the lipid fraction of the organism
Chemical concentration in sediments on an organic carbon basis
PAH-specific chemical concentration in sediment on an organic carbon basis
Chemical concentration in octanol
Chemical concentration in the organism
Critical body burden in the organism
Total interstitial water concentration of contaminant
Effect concentration of a PAH in sediment on an organic carbon basis calculated from
the product of its FCV and
0Sediment LC50 concentration on an organic carbon basis for a specific PAH for
Khepoxinus calculated from the product of its LC50 value at a Kovf of 1.0 and K^
Maximum solubility limited PAH concentration in sediment on an organic carbon basis
Final Draft PAH Mixtures ESG Document
xxi
5 April 2000
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1 GLOSSARY OF ABBREVIATIONS (continued)
2 S Aqueous Solubility
3 SAB U.S. EPA Science Advisory Board
4 SE Standard Error
5 SMAV Species Mean Acute Value
6 SPARC SPARC Performs Automated Reasoning in Chemistry
7 TOC Total Organic Carbon
8 TU Toxic Unit
9 WQC Water Quality Criteria
10 WQCTUFCYl Water Quality Criteria Toxic Unit based on the FCV
Final Draft PAH Mixtures ESG Document xxiv 5 April 2000
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1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
^LW
KOC
^OW
K*
Ks
^sc
LC50
LFER
MV
NA
ND
NOAA
NOEC
NTU
OEC
PAH
PAHoc
PCB
POC
PSTU
QSAR
REMA]
GLOSSARY OF ABBREVIATIONS (continued)
Lipid: water partition coefficient
Organic carbon: water partition coefficient
Octanol: water partition coefficient
Sediment: water partition coefficient
Setschenow constant
Soot carbon: water partition coefficient
Concentration estimated to be lethal to 50 % of the test organisms within a specified
time period
Linear free energy relationship
Molar Volume
Not Applicable, Not Available
Not Determined, Not Detected
National Oceanographic and Atmospheric Administration
No Observed Effect Concentration
Narcotic Toxic Units
Observable Effect Concentration
Polycyclic aromatic hydrocarbon
Organic carbon-normalized PAH concentration in sediment
Polychlorinated Biphenyl
Particulate Organic Carbon
Predicted Sediment Toxic Units
Quantitative Structure Activity Relationship
Regional Environmental Monitoring and Assessment Program
Final Draft PAH Mixtures ESG Document xxiii 5 April 2000
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1 contaminated sediments, to establish pollution prevention strategies, and to identify, prioritize and
2 implement appropriate clean up activities and source controls.
3
4 1.2 EQUILIBRIUM PARTITIONING AS A TECHNICAL BASIS FOR DERIVATION OF AN
5 ESG FOR MIXTURES OF PAHs
6
7 As a result of this need for technically defensible sediment guidelines to assist regulatory
8 agencies in making decisions concerning contaminated sediment problems and their prevention, a U.S.
9 EPA Office of Science and Technology and Office of Research and Development research team was
10 established to review alternative approaches (Chapman, 1987). All of the approaches reviewed had
11 both strengths and weaknesses and no single approach was found to be applicable for the derivation of
12 sediment guidelines hi all situations (U.S. EPA, 1989a,b; U.S. EPA, 1992). The equilibrium
13 partitioning (EqP) approach was selected and first applied to nonionic organic chemicals because it
14 presented the greatest promise for generating defensible national numerical chemical specific guidelines
15 applicable across a broad range of sediment types (U.S. EPA, 2000a). Three principal observations
16 form the basis of the EqP method of deriving sediment guidelines for nonionic organic chemicals:
17 1. The concentration of nonionic organic chemicals in sediments, expressed on an organic
18 carbon basis, and in interstitial water correlate to observed biological effects on
19 . sediment-dwelling organisms across a range of sediments.
20
21 2. Partitioning models can relate sediment concentrations for nonionic organic chemicals
22 on an organic carbon basis to freely-dissolved concentrations in interstitial water.
23
24 3. The distribution of sensitivities of benthic and water column organisms to chemicals are
25 similar; thus, the currently established WQC. final chronic values (FCV) can be used to
26 define the acceptable effects concentration of a chemical freely-dissolved in interstitial
27 water.
28
Final Draft PAH Mixtures ESG Document 1 -2 5 April 2000
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i SECTION 1
2 INTRODUCTION
3
4 1.1 LEGISLATIVE MANDATE AND NEED FOR ESGs
5
6 Under the Clean Water Act (CWA) the U.S. Environmental Protection Agency (EPA) is
7 responsible for protecting the chemical, physical and biological integrity of the nation's waters. In
8 keeping with this responsibility, U.S. EPA published ambient national water quality criteria (WQC) in
9 1980 for 64 of the 65 toxic pollutants or pollutant categories designated as toxic in the CWA.
10 Additional water quality documents that update criteria for selected consent decree chemicals and new
11 . criteria have been published since 1980. These national WQC are numerical concentration limits that
12 are the U.S. EPA's best estimate of the concentrations in water that are protective of human health and
13 of aquatic life. While these WQC play an important role in assuring a healthy aquatic environment,
14 they alone are not sufficient to ensure the protection of environmental or human health.
15 Toxic pollutants in bottom sediments of the nation's lakes, rivers, wetlands, estuaries and
16 marine coastal waters pose many ecological and human health risks throughout the United States (U.S.
17 EPA, 1997a,b,c). Contaminated sediments create the potential for continued environmental
18 degradation even where water column concentrations comply with established human health and aquatic
19 life WQC. In addition, contaminated sediments can be a significant pollutant source that may cause
20 water quality degradation to persist, even when other pollutant sources are controlled (Larsson, 1985;
21 Salomons et al., 1987; Burgess and Scott, 1992; U.S. EPA, 1997a,b,c). The development of
22 defensible numerical chemical specific concentration limits of substances applicable across a range of
23 sediment types (sediment guidelines) is needed to accurately assess the extent of the ecological risks of
Final Draft PAH Mixtures ESG Document 1-1 5 April 2000
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1 Over the past 15 years, the U. S. EPA research team and others have been working together to
2 investigate the toxicity and bioavailability of sediment contaminants to benthic organisms. As a result
3 of this effort, the Agency has developed the "Technical Basis for the Derivation of Equilibrium
4 Partitioning Sediment Guidelines (ESGs) for the Protection of Benthic Organisms: Nonionic Organics
5 (U.S. EPA, 2000a). In addition, U. S. EPA has developed a document describing the further use of
6 the EqP method for deriving ESGs for mixtures of the metals cadmium, copper, lead, nickel, silver
7 and zinc (U.S. EPA, 2000b). This methodology has been reviewed both by the U.S. EPA Science
8 Advisory Board and through the public comment process. The Agency also has developed ESGs for
9 the pesticides dieldrin and endrin (U.S. EPA, 2000c,d) and proposed ESGs for the individual
10 polycyclic aromatic hydrocarbons (PAHs) acenaphthene, fluoranthene and phenanthrene (U.S. EPA
11 1993a,b,c). Because PAHs occur in the environment as mixtures, rather than single chemicals, ESGs
12 for individual PAHs have the potential to be substantially under-protective because they do not account
13 for other co-occurring PAHs. The ESGs for individual PAHs have therefore been withdrawn.
14 Numerous efforts have previously sought to address and estimate the toxicity of PAH mixtures
15 (PTI Environmental Services, 1991; Long et al., 1995). However, the resultant sediment guidelines
16 have engendered considerable controversy over such issues as the correlative versus causal relations
17 between dry weight sediment chemistry and biological effects, the bioavailability of sediment
18 contaminants, the effects of covarying chemicals and mixtures, and ecological relevance (Swartz et al.,
19 1999). The U. S. EPA research team has concluded, based upon additional investigation, that issuance
20 of sediment guidelines for PAHs based on EqP was necessary to resolve these outstanding issues. Most
21 importantly, the ESGs must be based on mixtures of PAHs to be adequately protective of benthic
22 organisms, as well as ecologically relevant.
23 The SPAH model developed by Swartz et al. (1995) and based upon a combination of the EqP
24 approach, quantitative structure activity relationships (QSAR), narcosis theory, and concentration
Final Draft PAH Matures ESG Document 1 -3 5 April 2000
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1 addition models provided initial insight into a technical approach for resolving these complexities. This
2 EqP-based SPAH model provides a method to address causality, account for bioavailability, consider
3 mixtures, and predict toxicity and ecological effects. The most significant contribution to the
4 development of the scientific basis for deriving ESGs for PAH mixtures is described by Di Toro et al.
5 (2000) and Di Toro and McGrath (2000). This pioneering research forms major portions of this
6 document.
7
8 1.3 OVERVIEW OF THIS DOCUMENT
9
10 This document presents the theoretical basis and supporting data relevant to the derivation of
11 ESGs for mixtures of PAHs.
12 Section 2 of this document "Narcosis Theory: Model Development and Application for PAH
13 Mixtures" contains an analysis of the narcosis and EqP models to demonstrate the scientific basis for
14 the derivation of WQC and ESGs for mixtures of narcotic chemicals, including PAHs. Data are
15 presented that demonstrate that the toxicity of narcotic chemicals increase with ^Tow and that the slope
16 of the ATow-toxicity relationship is not different across species. The universal slope of this relationship
17 (-0.945) is applicable for all narcotic chemical classes, whereas the intercept is chemical class-specific.
18 The intercept of this slope at a Kow of 1.0 predicts the tissue effect concentration. The toxicities of
19 mixtures of narcotic chemicals in water are shown to be approximately additive, thus the toxic unit
20 concept is applicable to mixtures. The toxicities of narcotic chemicals are shown to be limited by their
21 solubilities in water, hence their toxicities in sediments are limited.
22 Section 3 of this document "Toxicity of PAHs in Water and Derivation of National PAH-
23 specific FCVs" presents an analysis of acute and chronic water-only toxicity data for freshwater and
24 saltwater aquatic organisms exposed to individual PAHs. It examines (I) the relative sensitivities of
Final Draft PAH Mixtures ESG Document 1-4 5 April 2000
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1 freshwater and saltwater organisms to determine if separate FCVs are required, and (2) the relative
2 sensitivities of benthic organisms and organisms used to derive WQC to determine if the WQC FCV
3 should be based only on benthic organisms. These data are used with the narcosis model presented in
4 Section 2, the EqP approach (U.S. EPA, 2000a), and the U.S. EPA National WQC Guidelines
5 (Stephan et al., 1985) to derive the WQC FCV for individual PAHs (PAH-specific FCV.
6 Section 4 "Derivation of ESG" contains the approach used for deriving the ESGs for mixtures
7 of PAHs. The Cocpwifcvi is derived for each individual PAH as the product of the PAH-specific FCV
8 and the respective K^ value as recommended by the EqP approach. The use of the Qcj,^ FCV|- value
9 for individual PAHs is inappropriate for use as the ESG because PAHs occur as mixtures. The
10 toxicities of mixtures of narcotic chemicals have been shown to be approximately additive, therefore,
11 combined toxic contributions of all PAHs in the mixture can be determined by summing the quotients
12 of the concentration of each PAH in the sediment divided by its CQC^AH, FCV, to determine the sum of
13 these Equilibrium Partitioning Sediment Guideline Toxic Units (SESGTUFCV). If the SESGTUpcv is
14 sl.O, the sediment guideline for the PAH mixture is not exceeded and the PAH concentration in the
15 sediment is protective of benthic organisms. If the SESGTUFCV exceeds 1.0, the sediment guideline for
16 the PAH mixture is exceeded and sensitive benthic organisms may be affected by the PAHs. The ESG
17 derived for PAH mixtures is compared to concentrations of PAH mixtures in sediments from national
18 monitoring programs to reveal the incidence of sediment guideline exceedences. An example
19 calculation is provided to explain the conversion of concentrations of individual PAHs on a dry weight
20 basis into the guideline.
21 Section 5 "Toxicity of PAHs: PAHs in Spiked and Field Sediments" examines the applicability
22 of the EqP methodology for Qc PAHi FCV(. and ESG derivation. The Q^ PAH, FCV, and ESG are compared
23 to (1) databases of observed sediment toxicity and benthic community impacts in sediments spiked with
24 PAHs, and (2) sediments from the field where PAHs are the probable contaminants of concern.
Final Draft PAH Mixtures ESG Document \-5 5 April 2000
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1 Section 6 "Implementation" defines the PAHs to which the ESG apply and examines the photo-
2 activation of PAHs in UV sunlight and teratogenicity and carcinogenicity of certain PAHs in the
3 mixture. The importance of equilibrium and the partitioning of PAHs to other organic carbon phases
4 (e.g. soot and coal) is described. An approach for calculating PAH solubilities for temperatures or
5 salinities at a specific site is provided. The implementation of the PAH mixture ESG by various U.S.
6 EPA Program Offices using different regulatory mandates is addressed separately in the
7 "Implementation Framework for Use of Equilibrium Partitioning Sediment Guidelines" (U.S. EPA,
8 2000e).
9 Section 7 "Sediment Guideline Statement" presents the sediment guideline statement
10 recommended by U. S. EPA. Concerns that the user will need to be aware of are listed.
11 Section 8 "References" lists references cited in all sections of this document.
Final Draft PAH Mixtures ESG Document 1-6 5 April 2000
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1 SECTION 2
2 NARCOSIS THEORY: MODEL DEVELOPMENT AND APPLICATION
3 FOR PAH MIXTURES
4
5 2.1 SECTION OVERVIEW
6
7 This section of the ESG document presents a model of the toxicity of narcotic chemicals to
8 aquatic organisms that is applicable to the derivation of WQC and ESGs for mixtures of narcotic
9 chemicals, including PAHs. Both the model and this section of the document are largely excerpted
10 from the pioneering publications of Di Toro et al. (2000) and Di Toro and McGrath (2000) which
11 should be consulted for components of the overall model that are not included in this ESG document.
12 The narcosis model includes a scientific analysis of the toxicities of narcotic chemicals fundamental to
13 the derivation of WQC and ESGs for their mixtures. The ESG for PAH mixtures described in Section
14 4 of this document is derived using this model and toxicity data exclusively for PAHs (see Section 3).
15 The narcosis model is used to describe the toxicity of all type I narcotic chemicals. Since
16 PAHs are expected to be type I narcotic chemicals (Hermens, 1989; Verhaar et al., 1992), the
17 toxicological principles that apply to them should be more accurately characterized by an analysis of
18 the principles that apply to narcotic chemicals overall. Model development utilizes a database of LC50
19 values comprising 156 chemicals and 33 species, including fish, amphibians, arthropods, molluscs,
20 annelids, coelenterates and echinoderms. The analysis detailed hi this section is used to demonstrate
21 that (1) the toxicities of narcotic chemicals, and therefore PAHs, are dependant on the chemical's ATOW;
22 (2) the slope of the #ow-toxicity relationship is the same for all species of aquatic organisms and classes
23 of narcotic chemicals with the intercepts being species and chemical class-specific; (3) the species-
24 . specific LC50 values normalized to a #ow =1.0 permit ranking of species sensitivities and are
Final Draft PAH Matures ESG Document 2-1 5 April 2000
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1 equivalent to the body burden LC50 on a lipid basis; and (4) the toxicities of mixtures of narcotic
2 chemicals are additive.
3 The analysis of narcotic chemical toxicity data presented in this section shows that the proposed
4 model accounts for the variations in toxicity due to differing species sensitivities and chemical
5 differences. The model is based on the idea that the target lipid is the site of action in the organism.
6 Further, it is assumed that target lipid has the same lipid-octanol linear free energy relationship for all
7 species. This implies that the log10LC50 vs logloKow slope is the same for all species. However,
8 individual species may have varying target lipid body burdens of narcotic chemicals that cause
9 mortality. The target lipid LC50 body burdens estimated by extrapolations from the water-only acute
10 toxicity data and ^w values are compared to measured total lipid LC50 body burdens for five species.
11 They are essentially equal, indicating that the extrapolation in the model is appropriate for estimation of
12 LC50 body burdens, i.e., that the target lipid concentration is equal to the total extracted lipid
13 concentration. The precise relationship between target lipid and octanol is established.
14
15 2.2 NARCOSIS MODEL BACKGROUND
16
17 A comprehensive model of type I narcosis chemicals that considers multiple species has been
18 presented by Van Leeuwen et al. (1992). They developed QSARs for individual species and performed
19 species sensitivity analysis. A similar analysis is presented in Di Toro et al. (2000). The key
20 differences in the Di Toro et al. (2000) model are the use of a single universal slope for the log,0LC50
21 versus logioATow QSAR for all the species, the inclusion of corrections for chemical classes, such as
22 PAHs, that are slightly more potent than baseline narcotics, and the interpretation of the y-intercepts as
23 the species-specific critical body burdens for narcosis mortality.
24
Final Draft PAH Mixtures ESG Document 2-2 5 April 2000
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1 2.3 BODY BURDEN MODEL
2
3 The initial quantitative structure-activity models for narcotic toxicity relied on correlations of
4 log10LC50 and log10K"ow (Konemann, 1981; Veith et al., 1983). An interesting and important
5 interpretation of this inverse relationship that relates the toxicity to chemical body burden has been
6 presented by McCarty et al. (1991), and proceeds as follows. The relationship between the LC50
7 (mmol/L) and Kow for fish is approximately
8
9 logtoLC50--loglo£oW+1.7 (2-1)
10
11 For each LC50, a fish body burden on a wet weight basis corresponding to narcosis mortality can be
12 computed using a bioconcentration factor BCF (L/kg) which is -defined as the ratio of the chemical
13 concentration in the organism C0rg (mmel/kg) to the chemical concentration dissolved in the water Cd
14 (mmol/L)
15
16 BCF= (2-2)
Cxi
17 Using the BCF the organism concentration corresponding to the LC50, which is referred to as the
18 critical body burden and denoted by Corg, can be computed using
19
20 Cg = BCF x LC50 (2-3)
21
22 The superscript * indicates that it is a critical body burden corresponding to the LC50. The BCF also
Final Draft PAH Mixtures ESG Document 2-3 5 April 2000
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1 varies with Kovf. For fish, the relationship is
2
3 log10BCF«logIOKow-1.3 (2-4)
5 Therefore, the critical body burden corresponding to the LC50 for fish narcosis can be computed using
6 the narcosis LC50 and the BCF
7
8 log,0Cg = log10BCF + log10LC50
- 1.3 -Iog10/i:ow +1.7
10 - 0.4 (2-5)
11 or
12 C£rg - 2.5 A^mdl/g wet wt (2-6)
13
14 Thus, McCarty et al. (1991) rationalize the relationship between LC50 values and £"ow by suggesting
15 that mortality is caused as a result of a constant body burden of the narcotic chemical.
16 The reason the critical body burden is a constant concentration for all the narcotic chemicals
17 represented by the narcosis LC50 is a consequence of the unity slopes for log10XoW in Equations 2-1
18 and 2-4. If the fraction of Hpid in the fish is assumed to be 5% (/Upid = 0.05), then the critical body
19 burden in the lip id fraction of the fish is
™ -_=
20 fuad (2-7)
Final Draft PAH Mixtures ESG Document 2-4 5 April 2000
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1 which is the estimate of the chemical concentration in the lipid of these fish that causes 50% mortality.
2 The model presented below is an extension of this idea.
3
4 2.4 TARGET LIPID MODEL
5
6 The body burden model relates the narcosis concentration to a whole body concentration using
7 a BCF. If different species are tested, then species-specific BCFs would be required to convert the
8 LC50 concentration to a body burden for each species. A more direct approach is to relate narcotic
9 lethality to the concentration of the chemical in the target tissue of the organism, rather than to the
10 concentration hi the whole organism. If the partitioning into the target tissue is independent of species,
. 11 then the need for species-specific BCFs is obviated. The identity of the target tissue is still being
12 debated (Abernethy et al., 1988; Franks and Lieb, 1990), but we assume that the target is a lipid
13 fraction of the organism. Hence the name, target lipid.
14 The target lipid model is based on the assumption that mortality occurs when the chemical
15 concentration in the target lipid reaches a threshold concentration'. This threshold is assumed to be
16 species-specific rather than a universal constant that is applicable to all organisms (e.g., 50 /zmol/g
17 lipid, see Equation 2-7). The formulation follows the body burden model (McCarty et al., 1991). The
18 target lipid-water partition coefficient ATLW (L/kg lipid) is defined as the ratio of chemical concentration
19 in target lipid, CL 0"mol/g lipid = mmol/kg lipid), to the freely-dissolved aqueous concentration Cd,
20 (mmol/L)
21
22 KLW = — (2-8)
Cd
Final Draft PAH Mixtures ESG Document 2-5 5 April 2000
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1 This equation can be used to compute the chemical concentration in the target lipid phase producing
2 narcotic mortality, i.e., the critical body burden in the lipid fraction CL , when the chemical
3 concentration in the water phase is equal to the LC50
4
5
-------
1 Equations 2-11 and 2-12 yields the following linear relationship between log,0LC50 and log,(>Kow
2
3 log10LC50 = log,0C£ -do - at log10/sTow (2-13)
4
5 where log10C? - a0 IS me 7 intercept and -a, is the slope of the line.
6 This derivation produces the linear relationship between log,0LC50 and log10ATow which is found
7 experimentally (see, for example, Table 4 in Hermens et al., 1984)
8
9 log10LC50 = m log10Kow + b (2-14)
10
11 where m and b are the slope and intercept of the regression, respectively. In addition, it identifies the
12 meanings of the parameters of the regression line. The slope of the line m is the negative of the slope
13 of the LFER between target lipid and octanol, a,. The intercept of the regression b — log10C£ - Op is
14 composed of two parameters: CL is the target lipid concentration at narcosis mortality, and 0$ is the
15 constant in Equation 2-12.
16 The difference between the target lipid model and the McCarty et al. (1991) body burden
17 model is that for the latter, the coefficients a,, and a, for fish are assumed to be known: OQ = -1.3 and
18 a, = 1.0. It is interesting to examine the consequences of a similar assumption applied to the target
19 lipid model. If it is assumed that the partitioning of narcotic chemicals in lipid and octanol are equal,
20 i.e., that lipid is octanol, a common first approximation, then a, = 1 and o<, = 0 and the y-intercept
21 becomes
22
23 b = loglocrL (2-15)
Final Draft PAH Mixtures ESG Document 2-7 5 April 2000
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1 which is the target-lip id concentration producing 50% narcosis mortality.
2 This result can be understood by examining Figure 2-1. The ^-intercept b is the LC50 value for
3 a chemical with a log{0Kow = 0 or KQW = 1. The ATOW is the ratio of the chemical's concentration in
4 octanol to its concentration in water. Hence, for this hypothetical chemical (an example would be 2-
5 chloroethanol for which Iog10£ow = -0.048 = 0) the chemical's concentration in water is equal to its
6 concentration in octanol. However, if the KLW equals the Kov, i.e., lipid is octanol, then its
7 concentration in water must be equal to its concentration in the target lipid of the organism. Therefore,
8 the j-intercept is the target lipid phase concentration at which 50% mortality is observed. That is
9
10 LCSO)^, = b = Co^ = Ci (2-16)
11
12 Note that this interpretation is true only if a,, = 0 (see Equation 2-13).
13 Thus the target lipid narcosis model differentiates between the chemical and biological
14 parameters of the logIOLC50 - loglQKovf regression coefficients in the following way
15
16 Regression Coefficients Chemical Biological
17 Slope: m — -a,
18 Intercept: b = -a^ + log,0C^
19 ~~ ~ (2-17)
20 The chemical parameters a,, and a, are associated with the LFER between octanol and target lipid
21 (Equation 2-12). The biological parameter is the critical target lipid concentration CL. This result is
22 important because it suggests that the slope m = -a, of the log,0LC50- log10ATow relationship should be
23 the same regardless of the species tested since it is a chemical property of the target lipid - the slope of
24 the LFER. Of course this assumes that the target lipid of all species have the same LFER relative to
Final Draft PAH Mixtures ESG Document 2-8 5 April 2000
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1 octanol. This seems to be a reasonable expectation since the mechanism of narcosis is presumed to
2 involve the phospholipids in the cell membrane and it appears to be a ubiquitous mode of action.
3 However, the biological component of the intercept C?L (Equations 2-13 and 2-17) should vary with
4 species sensitivity to narcosis since it is commonly found that different species have varying sensitivity
5 to the effects of exposure to the same chemical. The expectations that follow from the target lipid
6 model - that the slope should be constant among species and that the intercepts should vary among
7 species - is the basis for the data analysis presented below.
8
9 2.5 ACUTE LETHALITY DATABASE COMPILATION
10
11 An acute lethality (LC50) database for type I narcotics from water-only toxicity tests was
12 compiled from available literature sources. The principal criterion for acceptance was that a number of
13 chemicals were tested using the same species so that the slope and intercept of the log10LC50 -Iog10£"ow
14 relationship could be estimated. The data were restricted to acute exposures and a mortality end point
15 to limit the sources of variability. A total of 33 species including amphibians, fishes, arthropods
16 (insects and crustaceans), molluscs, annelids, coelenterates and protozoans were represented. Seventy-
17 four individual datasets were selected for inclusion in the database which provided a total of 796
18 individual data points. Details are provided in Appendix A. The individual chemicals which comprise
19 the database are listed in Appendix B. There are 156 different chemicals including halogenated and
20 non-halogenated aliphatic and aromatic hydrocarbons, PAHs, alcohols, ethers, furans, and ketones.
21 The log10ATow values and aqueous solubilities of these chemicals were determined using SPARC
22 (SPARC Performs Automated Reasoning in Chemistry) (Karickhoff et al., 1991), which utilizes the
23 chemical's structure to estimate various properties. The reliability of SPARC was tested using log10K"ow
24 values measured using the slow stir flask technique (de Bruijn et al., 1989). Fifty three compounds
Final Draft PAH Mixtures ESG Document 2-9 5 April 2000
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1 such as phenols, anilines, chlorinated monobenzenes, PAHs, PCBs and pesticides were employed. A
2 comparison of the logloKov values measured using the slow stir flask technique to the SPARC estimates
3 demonstrates that SPARC can be used to reliably estimate measured \og10Kov/ values over nearly a
4 seven order of magnitude range of loglQKow (Figure 2-2A). Note that this comparison tests both
5 SPARC and the slow stir measurements, since SPARC is not parameterized using octanol-water
6 partition coefficients (Hilaletal., 1994).
7
8 2.5.1 Aqueous Solubility
9
10 The toxicity data were screened by comparing the LC50 value to the aqueous solubility, S, of
11 the chemical (Figure 2-2B). (Note: For this and other figures in this document where a large number
12 of data points are available, the plotting procedure limits the actual number of data plotted.) Individual
13 LC50 values were eliminated from the database if the LC50 > S, which indicated the presence of a
14 separate chemical phase in the experiment. For these cases, mortality must have occurred for reasons
15 other than narcosis - for example the effect of the pure liquid on respiratory surfaces - since the target
16 lipid concentration cannot increase above that achieved at the water solubility concentration. A total of
17 55 data points were eliminated, decreasing the number to 736 and the number of individual chemicals
18 to 145 (Appendix B).
19
20 2.5.2 Exposure Duration
21
22 The duration of exposure varies in the dataset from 24 to 96 hours (Appendix A). Before the
23 data can be combined for analysis, the individual datasets need to be adjusted to account for this
24 difference. The required equilibration time may vary with both organism and chemical. An increase
Final Draft PAH Mixtures ESG Document 2-10 5 April 2000
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1 in either organism body size or chemical hydrophobicity may increase the time to reach equilibrium.
2 To determine if acute lethality for narcotic chemicals varied with exposure time, data were
3 selected where toxicity was reported at multiple exposure times for the same organism and the same
4 chemical. For seven fish species, data were available for 96 hours and either 24, 48 or both 24 and 48
5 hours exposure. Arithmetic ratios of the LC50 values for 48 and 96 hours and for the 24 and 96 hours
6 exposures are compared to log10ATow. The 48 to 96 hour ratio is 1.0 for essentially all the data (Figure
7 2-3A). The 24 to 96 hour ratio is larger, approaching 2.0 for the higher ATOW chemicals (Figure 2-3B).
8 A linear regression is used to fit the relationship in Figure 2-3B.
9
10 LC50a4/LC50(96) = 0.0988 Iog10/i:ow + 0.9807 (2-18)
11
12 where LC50C4) and LC50(96) are the LC50 values for 24 and 96 hour exposures. Since the majority of
13 the data points, approximately 46%, in the overall database represent narcosis mortality after exposure
14 to a chemical for 96 hours, the 24-hour fish toxicity data are converted to a 96 hour LC50 value using
15 Equation 2-18 for chemicals having logI&Rrow values where the ratio is > 1. No correction factor is
16 applied to 24 hour toxicity data for invertebrates and fishes exposed to chemicals having log10XoW
17 values where the ratio is < 1 (Di Toro et ah, 2000).
18
19 2.6 DATA ANALYSIS
20
21 The analysis of the toxicity data is based on the target lipid model assumption diat the slope of
22 the logloLC50-loglo£ow is the same for all species. This assumption was tested using a linear
23 regression model to estimate the species-specific body burdens and the universal narcosis slope.
24
Final Draft PAH Mixtures ESG Document 2-11 • 5 April 2000
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1 2.6.1 Regression Model
2
3 Consider a species k and a chemical j. The LC50* y for that species-chemical pair is
4 ' _
5 logujLCSO^ = log,0C^(A;) - QO - a, log10^oW(j) (2-19)
6 = bk - a, logIOXow(J) (2-20)
7
8 where
9
10 bk = log,0Ct(*) - OQ (2-21)
11
12 is the y-intercept. The problem to be solved is: how to include all the bk, k = 1,...,NS corresponding to
13 the Ns = 33 species and a single slope a, in one multiple linear regression model equation.
14 The solution is to use a set of indicator variables 6a that are either zero or one depending on the
15 species associated with the observation being considered. The definition is
16
17 6U = 1 k = i (2-22)
18 du =1 k* i
19
20 which is the Kronecker delta (Kreyszig, 1972). The regression equation can be formulated using 6a as
21 follows
Ns
22 logloLC50y = a,logioKow(/) + £ bkSu ^23>
k=\
Final Draft PAH Mixtures ESG Document 2-12 5 April 2000
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1 Equation 2-23 is now a linear equation with Ns+ 1 independent variables: log10ATow(/) and 6U, k =
2 l,...,Ns. There are Ns+l coefficients to be fit: a, and bk, k = l,...,Ns. For each LC50,y
3 corresponding to species / and chemical j, one of the bk corresponding to the appropriate species k = i
4 has a unity coefficient du = 1 while the others are zero. The way to visualize this situation is to
5 realize that each row of data consists of the LC50 and these -Ns+ 1 independent variables, for example
6 for/ = 1 and i = 3
7
8
9 0.788 1.175 0 0 1 0 0
10 (2-24)
11 which is actually the first of the 736 records in the database. The result is that b3 is entered into the
12 regression equation as the intercept term associated with species / = 3 because that dti is one for that
13 record. By contrast, the slope term allogloKOVf(D is always included in the regression because there is
14 always ah entry in the Iog10/Tow(/) column (Equation 2-24). Hence the multiple linear regression
15 estimates the common slope a, and the species-specific intercepts bk,k — l,...,Ns.
16 A graphical comparison of the results of fitting Equation 2-23 to the full dataset are shown in
17 Figure 2-4 for each of the 33 species. The regression coefficients are tabulated and discussed
18 subsequently after a further refinement is made to the model. The lines appear to be representative of
19 the data as a whole. There appear to be no significant deviations from the common slope. A few
20 outliers, which are plotted as +, were not included in the regression analysis. An outlier is identified if
21 the difference between predicted and observed LC50 value is greater than one log unit when they are
22 included in the regression. This decreases the total number of data points from 736 to 722.
23
24
Final Draft PAH Mixtures ESG Document 2-13 5 April 2000
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1 2.6.2 Testing The Model Assumptions
2
3 The adequacy of the regression model is tested by answering three questions:
4 1. Are the data consistent with the assumption that the slope is the same for each species
5 tested?
6 2. Does the volume fraction hypothesis (Abemnethy et al., 1988) provide a better fit?
7 3. Are there systematic variations for particular chemical classes?
8 The first assumption, that the slope estimated for a particular species is statistically
9 indistinguishable from the universal slope a, = -0.97 without chemical class correction (see Section
10 2.6.4), can be tested using conventional statistical tests for linear regression analysis (Wilkinson, 1990).
11 The method is to fit the data for each species individually to determine a species-specific slope. Then,
12 that slope is tested against the universal slope al = -0.97 without chemical class correction to determine
13 the probability that this difference could have occurred by chance alone. The probability and the
14 number of data points for each species are shown in Figure 2-5A. The slope deviations are shown in
15 Figure 2-5B. Some of the slope deviations are quite large. However, only three species equal or
16 exceed the conventional significance level of 5 % for rejecting the equal slope hypothesis.
17 Testing at the 5% level of significance is misleading, however, because there is more man an
18 even chance of rejecting one species falsely when 33 species are being tested simultaneously. The
19 reason is that the expected number of rejections for a 5% level of significance would be 33 x 0.05 =
20 1.65, i.e., more than one species on average would be rejected due to statistical fluctuations even
21 though all the slopes are actually equal. In fact, only 20 tests at 5% would, on average, yield one slope
22 that would be incorrectly judged as different. The correct level of significance is (l/33)( 1/20) =
23 0.152% so that the expected number of rejections is 33 x 0.00152 = 0.05 or 5% (Wilkinson, 1990).
24 This level of significance is displayed together with the slope data presented in Figure 2-5A. As can be
Final Draft PAH Mixtures ESG Document 2-14 5 April 2000
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1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
seen, there is no statistical evidence for rejecting the claim of equal slopes for the tested species. As
would be expected, when 5% was used as the level of significance two species were identified as
having unique
slopes. When the current level of significance (0.00152) was used for the
33 samples
none were different.
2.6.3 Volume Fraction Hypothesis
The volume fraction hypothesis asserts that narcotic mortality occurs at a constant volume
fraction of chemical at the target site of the organism (Abernethy et al., 1988). Basically
expressing the
LC50 as a volume fraction of chemical rather than a molar concentration.
, this involves
This is done
using the molar volume of the chemicals (see column MV in Appendix B). The LC50 on a molar
volume basis is
LC50(cm3 /L)
= LC50 (mmol/L) x MV (cmVmmol)
(2-25)
The question is: does using molar volume as the concentration unit improve the regression analysis?
The results are
LC50
Slope
R2
shown below
mmol/L cm3/L
-0.97 ±0.012 -0.90 ± 0.012
0.94 0.96
The R2 value for the volume fraction analysis (0.96) is slightly greater than that for concentrations
based on more
document uses
standard units of concentration (0.94). Because they are essentially the same this
the standard units of concentration rather than those based on the volume
fraction.
Final Draft PAH Matures ESG Document 2-15 5 April 2000
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1 Importantly, the slope for both volume and weight units of concentration is not unity.
2 -
3 2.6.4 Chemical Classes
4
5 The analysis presented above assumes that all the 145 chemicals listed in Appendix B are
6 narcotic chemicals. That is, the only distinguishing chemical property that affects their toxicity is Kow.
7 A criteria has been suggested that can be used to determine whether a chemical is a narcotic (Bradbury
8 et al., 1989), namely that it demonstrates additive toxicity with a reference narcotic. However, it is not
9 practical to test each possible chemical. The more practical test is whether the toxicity can be predicted
10 solely from the log,0LC50 - log10XoW regression. In fact, this is used hi methods that attempt to
11 discriminate baseline narcotics from other classes of organic chemicals (Verhaar et al., 1992).
12 Using this approach, differences in toxicity among chemical classes would be difficult to detect
13 if differing species were aggregated or different slopes were allowed hi the regression analysis.
14 However, with the large dataset employed above, these differences can be seen by analyzing the
15 residuals grouped by chemical class.
16 The criteria for choosing the relevant classes are not obvious without a detailed understanding
17 of the mechanism of narcotic toxicity. Hence, the conventional organic chemical classes based on
18 structural similarities, e.g. ethers, alcohols, ketones, etc., are used. The results are shown in Figure 2-
19 6A. The means ±2 standard error (SE) of the means are shown for each class. Although not a
20 rigorous test, the ±2 SE range does not encompass zero for certain classes. Thus, it is likely that there
21 are statistically significant chemical class effects.
22
23 2.6.4.1 Statistical Analysis of ATow-Toxicity Relationships
24
Final Draft PAH Mixtures ESG Document 2-16 5 April 2000
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1 A rigorous test is conducted by including correction constants for each of the chemical classes
2 in a manner that is analogous to Equation 2-23. The model equation is formulated using Nc - 1
3 corrections, Ac,, corresponding to the ? = 1,...,NC -1 chemical classes. These are interpreted as
4 corrections relative to the baseline class that is chosen to be aliphatic non-halogenated hydrocarbons.
5 The regression equation is formulated as before with a variable ^ that is one if chemical j is in
6 chemical class ? and zero otherwise
7
8 ^ = 1 if chemical j is in class /
9 £t - 0 otherwise (2-26)
10
11 The regression equation that results is
Ns Nc-l
12 log10LC50ty. = a,log10KoW(/) + £&*<&+ £ A«£y (2-27)
k=i t=i
13
14 -
15 Each data record now contains the dependent variable log^LCSO^-, the independent variables loglo£ow
16 log10£ow(/)> and the <5>fa, k = l,...,Ns and ^,
-------
1 l,...,Afc - 1 are then the differential toxicity of chemical class 0 relative to the reference class. This is
2 the reason for the Ac notation.
3 The requirement for a chemical class correction is decided using a statistical test that compares
4 the Ac, values that result from the regression to the hypothesis Ac, = 0. For the classes which are not
5 statistically different, they are included in the baseline class and the parameters are re-estimated. This
6 is continued until all the remaining Ac, values are statistically different from zero. After a number of
7 trials, it was found that treating halogen substitutions as a separate additive correction gave the least
8 number of statistically significant class corrections. Thus chemical class corrections are applied to the
9 base structure if necessary and an additional correction is made if any substitute is a halogen. Thus for
10 halogenated chemicals it is possible that two ^ = 1 in Equation 2-27. The chemical classes are listed
11 in Appendix B.
12 The results of the final regression analysis are listed in Table 2-1. Both the logarithmic bt and
13 arithmetic 10*1 values of the intercepts are included together with their standard errors. Chemical
14 classes that demonstrate higher potency than the reference class are ketones and PAHs. Halogenation
15 increases the potency as well. After accounting for different potencies in the chemical classes, the
16 mean residuals are statistically indistinguishable from zero (Figure 2-6B).
17
18 2.6.4.2 Standard Errors And Residuals
19 * '
20 The standard errors of the body burdens SE(£>,) found from the regression (Equation 2-27) are
21 in an almost one-to-one correspondence with the number of data points for that species. Thus the b( for
22 Pimephales with 182 data points has a 10% coefficient of variation, CV(b) = SE (&,) lbt, while the b,
23 for Neanthes with 4 data points has a 50% coefficient of variation (Table 2-1). The relationship of the
24 sample size (A/) to the coefficient of variation of the estimated critical body burden, CV(b), is shown in
Final Draft PAH Mixtures ESC Document 2-18 5 April 2000
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1 Figure 2-7A.
2 The residuals are log normally distributed (Figure 2-7B) and exhibit no trend with respect to
3 KQW (Figure 2-7FC) which confirms the assumption underlying the use of regression analysis. The
4 reason they are restricted to ± 1 order of magnitude is that 14 data points outside that range were
5 originally excluded as outliers (for some values previously less than ± one order of magnitude,
6 chemical class corrections produced values slightly greater than one order of magnitude as shown in
7 Figure 2-7G).
8
9 2.6.4.3 Chemical Class Corrections
10
11 The corrections due to chemical classes reduce the critical body burden by a factor of
12 approximately one-half for ketones and PAHs. Halogenation reduces it further by 0.570 (Table 2-1).
13 Thus a chlorinated PAH would exhibit a critical body burden of approximately one-third of a baseline
14 narcotic. The coefficients of variation for these corrections are approximately 10%.
15 The chemical class differences among the type I narcotics affect the LC50-jSTow relationship.
16 The model no longer predicts a single straight line for the logjoLCSO-log^ow relationship for all
17 narcotic chemicals. What is happening is that the y-intercepts are changing due to the changing Ac,.
18 values. The model (Equation 2-27) when applied to a single species k is
19
Nc-1
20 log10LC50tJ. = a,log10£ow(/) + bt+ £ Aw&j (2-28)
t=\
21
22
23 This is a straight line if only baseline narcotics are considered Ac, = 0 or if only one chemical class
24 correction is involved, e.g., all halogenated baseline narcotics. Otherwise more than one .Ac, enter into
Final Draft PAH Mixtures ESG Document 2-19 5 April 2000
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1 Equation 2-28 and the line is jagged. Figure 2-8 presents three examples. The deviations from the
2 baseline narcosis straight line are caused by the different chemical class potencies.
3
4 2.7 UNIVERSAL NARCOSIS SLOPE
5
6 The universal narcosis slope: m = -0.945 ±0.014 that results from the final analysis .that
7 includes chemical class corrections (Table 2-1) is smaller than that determined above without chemical
8 class corrections (-0.97+0.012). It is close to unity, a value commonly found (Hansch and Leo,
9 1995), and larger than the average of individual slopes (-0.86±0.14) reported by Van Leeuwen et al.
10 (1992), but comparable with a recent estimate for fathead minnows of -0.94 (Russom et al., 1997).
11 The fact that the slope is not exactly one suggests that octanol is not quite lipid. However, it is
12 also possible that for the more hydrophobic chemicals hi the database, the exposure time may not have
13 been long enough for complete equilibration of water and lipid to have occurred. To test this
14 hypothesis, the regression analysis is restricted to successively smaller upper limits of Iog10^row. The
15 results are listed below
16
17
18
19
20 The variation is within the standard errors of estimation, indicating that there is no statistically
21 significant difference if the higher logloATow data are removed from the .regression. This suggests that
22 the universal narcosis slope is not minus one but is actually -0.945 ±0.014.
23 One consequence of the use of a universal narcosis slope is that the species sensitivity ranking
24 derived from comparing either the water-only LC50 values or the critical body burdens of various
Final Draft PAH Mixtures ESG Document 2-20 5 April 2000
Maximum Iog10£ow 3.5
Slope
Standard Error
-0.959
0.018
4.0
-0.970
0.015
4.5
-0.958
0.015
5.0
-0.950
0.014
5.5
-0.945
0.015
-------
1 species are the same. This occurs because the critical body burden is calculated from the LC50 value
2 and the universal slope (Equations 2-14 and 2-15)
3
4 log,0Ct = log10LC50 + 0.9451ogio/i:ow (2-29)
5
6 If this were not the case, then the species sensitivity order could be reversed if LC50 values or C£ were
7 considered.
8 Equation 2-29 is important because it can be used to compute the critical body burden of any
9 type I narcotic chemical. Thus it predicts what the critical body burden should be for a particular
10 species at its LC50 value. This would be the concentration that would be compared to a directly
11 measured critical body burden. It can be thought of as a normalization procedure that corrects type I
12 narcotics for the varying Kov/ and places them on a common footing, namely, the critical body burden.
13 The motivation for the development of the target lipid model was to apply it to mixtures of
14 PAHs and other persistent narcotic chemicals hi sediments. The narcosis database used to determine
15 the universal narcosis slope and the critical body burdens consists of 145 chemicals, of which 10 are
16 un-substituted and substituted PAHs (Di Toro and McGrath, 2000). A comparison of the LC50 data
17 for just these chemicals and the target lipid model is shown in Figure 2-9. The solid log10LC50 -
18 log10ATow lines are computed using the universal narcosis slope and the appropriate body burdens for
19 PAHs for each organism listed. The dotted lines apply to the chloronaphthalenes which have a slightly
20 lower critical body burden due to the halogen substitution. The lines are an adequate fit of the data,
21 although the scatter in the Daphnia data is larger than some of the other species with multiple sources
22 of data and there is a clear outlier for Americamysis. It is for this reason that the slope representing all
23 data for narcosis chemicals is used to derive the target lipid concentration from water-only toxicity data
24 for PAHs in Section 3 of this document.
Final Draft PAH Mixtures ESG Document 2-21 5 April 2000
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1 2.8 COMPARISON TO OBSERVED BODY BURDENS
2
3 The target lipid model predicts the concentration in octanol (the y-intercept) that causes 50%
4 mortality in 96 hours. The question is: how do these compare to measured critical body burdens? The
5 species-specific y-intercepts, b,, are related to the target lipid concentration by the relationship
6
7 y-intercept = bt = log,0C£(z) - a0 (2-30)
8
9 or, with chemical class corrections,
10
11 y-intercept = bt + Ac, = logloCL(i)~ o0 (2-31)
12
13 for species / and chemical class {, where OQ is the parameter in the LFER between octanol and target
14 lipid (Equation 2-12).
15 . The relationship between the predicted concentration in octanol, b{ + Ac,, to the concentration
16 measured in extracted lipid, log,0C£, is examined in Table 2-2 which lists observed LC50 body burdens
17 (/zmol/g lipid) and predicted critical body burdens (^mol/g octanol) for organisms in the database for
18 which measured lipid-normalized critical body burdens were available. Three fish species: Gambusia
19 affinis (mosquito fish), Poecilia reitculata (guppy) and Pimephales promelas (fathead minnow), and two
20 crustaceans: Leptocheirus plumulosus (amphipod) and Portunus pelagicus (crab) are compared in
21 Figure 2-10. The predicted and measured body burdens differ by less than a factor of 1.6. The fish
22 were observed to have higher critical body burdens than the crustaceans, which the model reproduces,
23 The apparent near equality between the estimated and measured critical body burdens, which
24 come from two independent sets of data, strongly suggest that in fact
Final Draft PAH Mixtures ESG Document 2-22 5 April 2000
-------
1 a0' = 0 (2-32)
2
3 so that
4
5 logioC£(0 = fc, + Ac, = y-intercept (2-33)
6
7 This relationship implies that the target lipid is the lipid measured by the extraction technique used in
8 the body burden datasets. This is an important practical result since it suggests that body burdens
9 normalized to extracted lipid are expressed relative to the appropriate phase for narcotic toxicity. Since
10 the intercepts appear to be the organism's lipid concentration, the ^-intercepts (bt + Ac<) in the
11 discussion presented below are referred to as body burden lipid concentrations although the units
12 Cumol/g octanol) are retained since these are, in fact, the actual units of the intercepts.
13
14 2.9 MIXTURES AND ADDITIVITY
15
16 Narcotic chemicals, including PAHs, occur in the environment as mixtures, therefore, their
17 mixture effects need to be appropriately resolved. If the toxicity of mixtures is additive, mixture
18 effects can be assessed using the concept of toxic units. A toxic unit TU is defined as the ratio of the
19 concentration in a medium to the effect concentration in that medium.
20 The additivity of the toxicity of narcotic chemicals in water has been demonstrated by a number
21 of investigators. The results of mixture experiments which employed a large enough number of
22 narcotic chemicals so that non-additive behavior would be detected is presented in Figure 2-11 as
23 adopted from Hermens (1989). Three of the four experiments demonstrated essentially additive
24 behavior and the fourth, a chronic exposure, was almost additive.
Final Draft PAH Mixtures ESG Document 2-23 5 April 2000
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1
2 2.10 AQUEOUS SOLUBILITY CONSTRAINT
3
4 The existence of the need for a solubility cutoff for toxicity was suggested by Veith et al.
5 (1983) based on data from fathead minnows (P. promelas) and guppies (P. reticulata). The highest
6 dissolved concentration in water that can be achieved by a chemical is its aqueous solubility, S.
7 Therefore, the maximum lipid concentration that can be achieved is limited as well. It is for this
8 reason that the LC50 database is limited to chemicals with Iog10£ow <:5.3. This is also the reason that
9 the LC50 database that was used to generate the FCVs for specific PAHs in Section 3 of this document,
10 was screened initially for LC50 values < 5, using the solubilities from Mackay et al. (1992), rather than
11 Iog10^ow ^5.3 used by Di Toro et al. (2000).
12 For sediments, a solubility constraint should be applied as well. This is readily calculated using
13 the relationship between interstitial water and the organic carbon-normalized sediment concentration.
14 Since the interstitial water concentration is limited by S, the sediment concentration should be limited
15 by the. concentration hi sediment organic carbon that is in equilibrium with the interstitial water at the
16 aqueous solubility. Therefore, observed sediment concentrations are limited by the condition
17
18
19 CQC < Coc^ = tfocS (2-34)
Final Draft PAH Mixtures ESG Document 2-24 5 April 2000
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1 SECTION 3
2 TOXICITY OF PAHs IN WATER AND
3 DERIVATION OF PAH-SPECIFIC FCVs
4
5 3.1 NARCOSIS THEORY, EqP THEORY AND WQC GUIDELINES: DERIVATION OF PAH-
6 SPECIFIC FCVs FOR INDIVIDUAL PAHs
7
8
9 Polycyclic aromatic hydrocarbons occur in the environment as mixtures. Therefore, in order to
10 adequately protect aquatic life the approach used to derive a WQC FCV or sediment guideline for
11 PAHs must account for their interactions as a mixture. In this section we present an approach for
12 deriving FCVs for individual PAHs which can be used to derive the ESG for mixtures of PAHs.
13 Concepts developed by Di Toro et al. (2000) and presented in Section 2 of this document
14 provide the technical framework for screening and analyzing aquatic toxicity data on PAHs. In
15 particular, Section 2 demonstrated that: (1) the universal slope of the ^Tow-toxicity relationship for
16 narcotic chemicals is the same for all aquatic species; and (2) the intercept of the slope at a Jfow of 1.0
17 for each species provides the LC50/EC50 in /^mol/g octanol that indicates the critical body burden in
18 and relative sensitivities of each species.
19 These concepts permit the use of the U.S. EPA National WQC Guidelines (Stephan et al.,
20 1985) to derive WQC FCVs for individual PAHs and PAH mixtures. The universal slope is used with
21 PAH-specific LC50/EC50 values to derive test-specific ATOW normalized reference acute values at a ^Tow
22 of 1.0. (This is analogous to the hardness normalization used to derive WQC for metals). These
23 values are used to calculate species mean acute values (SMAVs) and genus mean acute values
24 (GMAVs): (1) because only acute and chronic toxicity data from water-only tests with freshwater and
25 saltwater species exposed to individual PAHs are used, a PAH chemical class correction is not needed;
26 (2) the data are screened for acceptability following the requirements for use of species resident to
Final Draft PAH Mixtures ESG Document 3-1 5 April 2000
-------
1 North America, test durations, test quality, etc. of the U.S. EPA National WQC Guidelines (Stephan et
2 al., 1985); (3) the individual acute values are adjusted using the universal slope of the ATow-toxicity
3 relationship from the narcotic chemical analysis that was shown to apply to all aquatic species in
4 Section 2 to derive- the acute value at a Kovf of 1.0 (Appendix C); (4) the intercept of the slope at a Kow
5 of 1.0 for each species provides the LC50/EC50 in ^mol/g octanol that indicates the relative sensitivity
6 of each species, which was used to calculate SMAVs and GMAVs in ^mol/g octanol, which are
7 indicative of critical tissue concentrations in organisms on a /-zrnol/g lipid basis. The GMAVs are used
8 to calculate the final acute value (FAV) applicable to PAHs at a KOVf of 1.0 (Stephaa et al., 1985).
9 This FAV at a Kovf of 1.0, when divided by the Final Acute-Chronic Ratio (FACR), becomes the FCV
10 at a ATOW of 1.0. Importantly, the FCV for any specific PAH can then be derived by back calculating
11 using its specific A^w and the universal narcosis slope. When the PAH-specific FCV exceeds the
12 known solubility of that PAH, the maximum contribution of that PAH to the toxicity of the mixture is
13 set at the K^ multiplied by the solubility of that PAH.
14 The FCV for PAH mixtures derived in this section of the document differs slightly from that
15 which would be derived for other narcotic chemicals in that it: (1) is derived using only acute and
16 chronic toxicity data from water-only tests with freshwater and saltwater species exposed to individual
17 PAHs, therefore, the data do not require the PAH chemical class correction; (2) the data are rigorously
18 screened for acceptability following the requirements for the use of species resident to North America,
19 test durations, test quality, etc. of the U.S. EPA National WQC Guidelines (Stephan et al., 1985). The
20 last search of the literature on the toxicity of PAHs was completed in January 2000.
21 .
22
23
24
Final Draft PAH Mixtures ESG Document 3-2 5 April 2000
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1 3.2 ACUTE TOXICITY OF INDIVIDUAL PAHS: WATER EXPOSURES
2
3 3.2.1 Acute Toxicity of PAHs
4
5 One hundred and four acute water-only toxicity tests with 12 different PAHs have been
6 conducted on 24 freshwater species from 20 genera that meet the requirements of the U.S. EPA
7 National WQC Guidelines (Stephan et al. 1985, see Appendix C). The tested life-stages of 15 of the
8 genera were benthic (infaunal or epibenthic). The most commonly tested freshwater species were the
9 cladocerans (Daphnia magnd) and (Daphniapulex), rainbow trout (Oncorhynchus mykiss), fathead
10 minnow (P. promelas) and bluegill (Lepomis macrochirus). The most commonly tested PAHs with
11 freshwater organisms were acenaphthene, fluoranthene, fluorene, naphthalene, phenanthrene and
12 pyrene.
13 Seventy-seven acute water-only toxicity tests with 8 different PAHs have been conducted on 30
14 saltwater species from 29 genera (Appendix C). The tested life-stages of 21 of the genera were benthic
15 (infaunal or epibenthic). The most commonly tested saltwater species were the annelid worm
16 (Neanthes arenaceodentata), mysid (Americamysis bahia), grass shrimp (Palaemonetes pugio), pink
17 salmon (Oncorhynchus gorbuscha), and sheepshead minnow (Cyprinodon variegatus). The most
18 commonly tested PAHs with saltwater organisms were acenaphthene, fluoranthene, naphthalene,
19 phenanthrene and pyrene.
20
21 3.2.2 Acute Values at a Kovf of 1.0
22
23 The LC50 values or EC50 values where the effect is likely lethal, (^g/L) from individual acute
24 toxicity tests from Appendix C were used to derive the GMAV 0"mol/g octanol) at a #ow of 1.0. The
Final Draft PAH Mixtures ESG Document 3-3 5 April 2000
-------
1 goal of this process was to convert individual LC50 or EC50 values that vary for a species across
2 PAHs into PAH-specific GMAVs at a /sTow of 1.0. The use of normalizing factors in WQC derivation
3 is not unique to this document. It is analogous to the hardness adjustment applied to the freshwater
4 WQC for cadmium, copper, lead, nickel and zinc and the pH and temperature adjustments applied to
5 the freshwater WQC for ammonia. For multiple PAHs tested against one species, the £ow
6 normalization should result in similar PAH-specific SMAVs. Initially, the LC50 or EC50 values in
7 A^g/L were compared to the known solubility in water of the PAH tested. If the published LC5Q or
8 EC50 concentration exceeded the solubility of the tested PAH, the concentration of the PAH at
9 solubility is listed in bold in Appendix C as a "greater than" acute value to indicate that the actual
10 toxicity of the dissolved PAH was unknown, though likely greater than solubility. For these tests, this
11 greater than solubility value, and not the published LC50 or EC50 value which is enclosed in
12 parentheses in Appendix C, was used in further calculations only when there were no acute values for
13 that species at concentrations less than the solubility. Next, the LC50, EC50 or greater than solubility
14 value was converted to ^mol of the tested PAH/L. When the same PAH was tested more than once
15 against a species, the geometric mean of all LC50 or EC50 values was calculated to determine the
16 PAH-specific SMAV. The -0.945 universal slope of the toxicityAKow relationship (Equation 2-29) was
17 applied to the PAH-Specific SMAVs (fj.rn.oirL) to calculate the PAH-specific SMAV Cumol/g octanol)
18 at a ATOW=1.0. This should result in similar PAH-specific SMAVs for each of the PAHs tested. The
19 SMAV for all tested PAHs is the geometric mean of the PAH-Specific SMAVs at a Kov of 1.0. The
20 GMAV (^mol/g octanol) at a /sTow of 1.0 is the geometric mean of the SMAVs at a KOVf of 1.0.
21 The SMAVs at a Kov of 1.0 were similar for multiple PAHs (Appendix C). For 21 freshwater
22 and saltwater species, two to nine different PAHs were tested. The range in ratios of the highest to
23 lowest acute values for multiple PAHs tested against an individual species before normalization was
24 1.98 to 186; an average ratio of 43.2. In contrast, the range in the ratios of the highest to lowest PAH-
Final Draft PAH Mixtures ESG Document 3-4 5 April 2000
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1 specific SMAVs at a Kov/ of 1.0 was 1.14 to 12.2; average ratio of 4.80. For 10 of the 21 (56%)
2 species tested against multiple PAHs, the ratio of high to low SMAVs at a Kov of 1.0 was 4.0 or less.
3 This compares favorably with the factor of four or less difference in the acute values for 12 of 19
4 (63%) of the same species hi multiple tests with the same PAH. Therefore, the variability of SMAVs
5 at a KQW of 1.0 across PAHs is similar to the variability inherent in acute toxicity testing with only one
6 PAH. This suggests that the GMAVs provide data across PAHs that indicate the relative sensitivity of
7 that species that can be used to describe species at risk and to calculate the FAV.
8 The acute sensitivities of freshwater and saltwater genera and the sensitivities of benthic and
9 benthic plus water column genera do not differ (see Section 3.4). Therefore, GMAVs at a ATOW of 1.0
10 can be used to indicate the relative sensitivities for all freshwater and saltwater genera (Figure 3-1).
11 The £ow-normalized GMAVs (not including values greater than the solubility of the tested PAH) range
12 from 7.66 jtmol/g octanol for Americamysis to 187 /xmol/g octanol for Tanytarsus, a factor of only
13 24.4. Saltwater genera constitute four of the five genera with GMAVs at a Kow of 1.0 within a factor
14 of two of the most sensitive genus (Americamysis'). Of the 49 genera, the most sensitive one-third
15 include a freshwater hydra, two amphipods, an insect, saltwater fish, a crab, two mysids, two shrimp,
16 and three saltwater amphipods. All of these 16 genera have GMAVs at a Kow of 1.0 that are within a
17 factor of three, and 14 of the genera are benthic. Benthic and water column genera are distributed
18 throughout the sensitivity distributions indicating that they have similar sensitivities. Genera that are
19 benthic have been tested more frequently than water column genera.
20
21 3.3 CHRONIC TOXICITY OF INDIVIDUAL PAHS: WATER EXPOSURES
22
23 3.3.1 Acenaphthene
24
Final Draft PAH Mixtures ESC Document 3-5 5 April 2000
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1 Chronic life-cycle toxicity tests have been conducted with acenaphthene with the freshwater
2 midge (Paratanytarsus sp.) and the saltwater mysid (A. bahia), and early life-stage tests have been
3 conducted with the fathead minnow (P. promelas) and sheepshead minnow (C. vafiegatus) (Table 3-1).
4 For each of these species, one or more benthic life-stages were exposed. Other chronic toxicity tests
5 have been conducted with the freshwater chironomid (Paratanytarsus sp.) and P. promelas (Lemke et
6 al., 1983; Lemke, 1984; Lemke and Anderson, 1984) but insufficient documentation is available to
7 permit use of these results (Thursby, 199la).
8 Two acceptable life-cycle toxicity tests have been conducted with Paratanytarsus sp.
9 (Northwestern Aquatic Sciences, 1982). In the first test, 575 ^ug/L reduced survival 90%, reduced
10 growth 60%, and all eggs failed to hatch (Table 3-1). No adverse effects occurred at acenaphthene
11 concentrations up to 295 A*g/L acenaphthene. In the second test, survival was reduced 20% and growth
12 30% at 315 ^g/L- Egg hatchability was not affected in the highest concentration of 676 ,ug/L; although
13 survival of hatched larvae was reduced "60%. No significant effects were observed at acenaphthene
14 concentrations up to 164 ng/L.
15 A total of six early life-stage toxicity tests have been conducted with the P. promelas as part of
16 a round-robin test series; two each from three laboratories (Table 3-1) (Academy of Natural Sciences,
17 1981; ERGO, 1981; Cairns and Nebeker, 1982). The lowest observed effect concentrations (LOEC)
18 across laboratories and tests ranged from 98 to 509 f^gfL, a factor of 5.2. Growth (dry weight),
19 survival, or both growth and survival were reduced. Only one of diese test pairs had a suitable
20 measured acute value that allowed calculation of an acute-chronic ratio, or ACR (Cairns and Nebeker,
21 1982). The concentration-response relationships were similar for the two tests of Cairns and Nebeker
22 (1982). In the first test, the early life-stages of this fish were unaffected in acenaphthene concentrations
23 ranging from 67 to 332 jug/L, but 495 ^g/L reduced growth 54% relative to control fish. In the second
24 test, growth was reduced 30% at 509 Aig/L, but no effects were detected in fish exposed to 197 to 345
Final Draft PAH Mixtures ESG Document 3-6 5 April 2000
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1
2 Data from saltwater chronic toxicity tests with acenaphthene are available for A. bahia and C.
3 variegatus. Reproduction of A. bahia was affected by acenaphthene in two life-cycle tests from two
4 different laboratories. In the first test (Home et al., 1983), 340 Aig/L reduced reproduction 93%
5 relative to controls and all A. bahia died at 510 ^g/L. No effects were observed on the parental
6 generation at 100 to 240 ^g/L and second generation juveniles were not affected at <, 340 /ug/L. In the
7 second test (Thursby et al., 1989b), no effects were observed at ^ 44.6 Atg/L, but a concentration of
8 91.8 jug/L reduced reproduction 91 %. No reproduction occurred at higher concentrations, and growth
9 was reduced 34% at 168 ^g/L and survival 96% at 354 Atg/L.
10 A test with early life-stages of C. variegatus showed that 240 to 520 //g/L had no effects, but
11 that concentrations of 970, 2,000 and 2,800 Aig/L, respectively, reduced survival of embryos and
12 larvae by 2:70% (Table 3-1; Ward et al., 1981).
13 In general, the above results show that the difference between acute and chronic toxicity of
14 acenaphthene is small and differed minimally between species (Table 3-2). Species mean acute-chronic
15 ratios for acenaphthene are 6.68 for Paratanytarsus sp., 1.48 for P. promelas, 3.42 for A. bahia and
16 4.36 for C variegatus.
17
18 3.3.2 Anthracene
19
20 A single life-cycle toxicity test has been conducted with D. magna exposed to only three
21 concentratipns of anthracene (Hoist and Geisey, 1989). Minimal decreases were observed on the
22 number of broods produced in all three of the concentrations tested: 2.1 jug/L (5.3 %), 4.0 /^g/L (8.0%)
23 • and 8.2 jug/L (13.8%). No acute toxicity tests were conducted by the authors. Therefore, an acute
24 chronic ratio could not be derived for anthracene.
Final Draft PAH Mixtures ESG Document 3-7 5 April 2000
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1 3.3.3 Fluoranthene
2
3 Fluoranthene has been tested in life-cycle toxicity tests with the freshwater cladoceran, D.
4 magna (Spehar et al., 1999) and the saltwater mysid, A. bahia (U.S. EPA, 1978, Spehar et al., 1999),
5 and early life-stage tests have been conducted with the fathead minnow (Spehar et al., 1999) (Table 3-
6 1). No effects were observed with D. magna at < 17 ^ug/L, but growth was reduced 17% at 35 ngfL
1 and 25% at 73 jug/L. There were 37% fewer young per adult at 73 ng/L and no daphnids survived at
8 148 Mg/L. An early life-stage toxicity test conducted with the fathead minnow showed no effects at
9 < 10.4 //g/L, but reduced survival (67%) and growth (50%) at 21.7 uglL.
10 Saltwater mysids (A. bahia) were tested in two life-cycle toxicity tests. In the first test the
11 mysids were exposed to fluoranthene for 28 days (U.S. EPA, 1978). There was no effect on survival
12 or reproduction (growth was not measured) in concentrations ranging from 5-12 ptg/L. At a
13 fluoranthene concentration of 21 Aig/L, survival was reduced 26.7% and reproduction 91.7%, relative
14 to the controls. At the highest concentration of fluoranthene, 43 jwg/L, all A. bahia died. In the second
15 test, A. bahia were exposed to fluoranthene for 31 days (Spehar et al., 1999). Effect concentrations
16 were similar to those in the U.S. EPA (1978) test. A. bahia were not affected at fluoranthene
17 concentrations from 0.41-11.1 jug/L. At the highest concentration tested, 18.8 /ug/L, survival was
18 reduced 23% relative to controls and there was no reproduction. Reproduction was reduced by 77% in
19 11.1 Mg/L, but this was not significantly different from controls even at a=0.1.
20 The difference between acute and chronic sensitivity to fluoranthene varied minimally between
21 species (Table 3-2). Three species mean ACRs are available for fluoranthene: 4.78 for D. magna,
22 4.60 for P. promelas, and 2.33 for A. bahia.
23
24 3.3.4 Phenanthrene
Final Draft PAH Mixtures ESG Document 3-8 5 April 2000
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1 Phenanthrene has been tested in life-cycle toxicity tests with D. magna and A. bahia and an
2 early life-stage test has been conducted with rainbow trout (O. mykiss) (Table 3-1). There were no
3 effects of phenanthrene on D. magna at <57 jug/L, but survival was reduced 83% and reproduction
4 98% at 163 //g/L (Call et al., 1986). In a test with O. mykiss, no effects were observed at 5 /ug/L.
5 The percentage of abnormal and dead fry at hatch was significantly increased at the highest exposure
6 concentration of 66 /ug/L and survival of hatched fry was reduced with increase in exposure
7 concentration (Call et al., 1986). Mortality was 41, 48, 52 and 100% at 8, 14, 32, and 66 vg/L,
8 respectively. Wet weight was reduced 33, 44, and 75% at 8, 14 and 32 jug/L, respectively.
9 A life-cycle toxicity test with A. bahia exposed to phenanthrene showed that the effect
10 concentrations were similar to those that affected O. mykiss (Kuhn and Lussier, 1987)(Table 3-1).
11 Survival, growth and reproduction were not affected at <5.5 /ugfL. However, at the highest test
12 concentration of phenanthrene (11.9 /^g/L), all mysids died.
13 The difference between acute and chronic sensitivity to phenanthrene varied minimally between
14 D. magna (PAH-specific ACR= 1.21), O. mykiss (ACR=7.90) and A. bahia (ACR= 3.33). The
15 ACR for O. mykiss (Call et al., 1986) was derived using the EC50 for immobilization (50 A*g/L) and
16 not the 96-hour LC50 of 375 ugl'L as was required in Stephan et al. (1985).
17
18 3.3.5 Pyrene
19
20 A life-cycle toxicity test with A. bahia exposed to pyrene was conducted by Champlin and
21 Poucher (1992d). There were no effects at 3.82 ^g/L, but 20.9 uglL reduced survival 37% and no
22 mysids survived at the next higher concentration of 38.2 f^gfL (Table 3-1). Reproduction was
23 significantly reduced in k5.37 ng/L. The ACR for from this test with pyrene is 6.24.
24
Final Draft PAH Mixtures ESG Document 3-9 5 April 2000
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1 3.3.6 Naphthalene
2
3 Fathead minnows were exposed to naphthalene in an early life-stage toxicity test (DeGraeve et
4 al., 1982). Hatching of fry was significantly reduced in 4.38 and 8.51 f^g/L and none were alive in
5 these concentrations at the end of the 30-day test. Weight and length of fish surviving the test were
6 significantly reduced in 0.85 and 1.84 /ug/L. No significant effects were detected in concentrations
7 <0.45 yug/L. Control survival was only 42%, which does not meet requirements according to the
8 American Society of Testing and Materials (ASTM)(1998). Also, the carrier methanol was absent
9 from the control and it was diluted in proportion to the dilution of naphthalene in other treatments.
10 These data are summarized in the text for completeness, but the ACR of 12.7, chronic value of 0.62
11 Mg/L, and 96-hour LC50 of 7.9 ^ig/L for naphthanlene are not included in Tables 3-1 and 3-2.
12 The calanoid copepod (Eurytemora qffinis) was exposed to 14.21 jug/L naphthalene, 15.03
13 ng/L 2-methylnaphthalene, 8.16 ^g/L 2,6-dimethylnaphthalene and 9.27 pig/L 2,3,5-trimethyl-
14 naphthalene in life-cycle toxicity tests (Ott et al., 1978). Survival and reproduction were affected by
15 each of the naphthalenes, but ACRs could not be derived because the duration of the acute test was too
16 short (24 hours) according to guidelines (Stephan et al., 1985), and no other concentrations were tested
17 chronically.
18
19 3.3.7 Derivation of the Final Acute Chronic Ratio
20
21 The FACR for the six PAHs is 4.16. This FACR is the geometric mean of all species mean
22 ACRs for Daphnia (2.41), Paratanytarsus (6.68), Pimephales(2.6l), Oncorhynchus (7.90),
23 Americamysis (3.59), and Cyprinodon (4.37).
24
Final Draft PAH Mixtures ESC Document 3-10 5 April 2000
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1 3.4 APPLICABILITY OF THE WQC AS THE EFFECTS CONCENTRATION FOR BENTHIC
2 ORGANISMS
3
4 The use of the FCV as the effects concentration for calculation of ESGs assumes that benthic
5 (infaunal and epibenthic) species, taken as a group, have sensitivities similar to all aquatic (benthic and
6 water column) species used to derive the WQC FCV. The data supporting the reasonableness of this
7 assumption over all chemicals for which there were published or draft WQC documents were presented
8 in Di Toro et al. (1991), and the "Technical Basis for the Derivation of Equilibrium partitioning
9 Sediment Guidelines (ESGs) for the Protection of Benthic Species: Nonionic Organics" (U.S. EPA,
10 2000a). The conclusion of similarity of sensitivity was supported by comparisons between (1) acute
11 values for the most sensitive benthic species and acute values for the most sensitive water column
12 species for all chemicals; (2) acute values for all benthic species and acute values for all species in the
13 WQC documents across all chemicals after standardizing the LC50 values; (3) FAVs calculated for
14 benthic species alone and FAVs in the WQC documents; and (4) individual chemical comparisons of
15 benthic species versus all species. The following analysis examines the data on the similarity of
16 sensitivity of benthic and all aquatic species for PAHs.
17 For PAHs, benthic life-stages were tested for 15 of 20 freshwater genera and 21 out of 29
18 saltwater genera (Appendix C). An initial test of the difference between the freshwater and saltwater
19 FAVs for all species (water column and benthic) exposed to PAHs was performed using the
20 Approximate Randomization (AR) Method (Noreen, 1989). The AR Method tests the significance
21 level of a test statistic when compared to a distribution of statistics generated from many random sub-
22 samples. The test statistic in this case was the difference between the freshwater FAV (computed from
23 the GMAVs at a #ow of 1.0 for combined water column and benthic for freshwater aquatic life) and the
24 saltwater FAV (computed from the GMAVs at a Kow of 1.0 for combined water column and benthic
25 for saltwater aquatic life) (Appendix C). In the AR Method, the freshwater and the saltwater GMAVs
Final Draft PAH Mixtures ESG Document 3-11 5 April 2000
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1 at a Kov/ of 1.0 were combined into one dataset. The dataset was shuffled, then separated back so that
2 randomly generated "freshwater" and "saltwater" FAVs could be computed. The LC50 values were
3 re-separated such that the number of GMAVs at a Kov/ of 1.0 used to calculate the sample FAVs were
4 the same as the number used to calculate the original FAVs. These two FAVs were subtracted and the
5 difference used as the sample statistic. This was done iteratively so that the sample statistics formed a
6 probability distribution representative of the population of FAV differences (Figure 3-2A). The test
7 statistic was compared to this distribution to determine its level of significance. The null hypothesis
8 was that the GMAVs at a Kovf of 1.0 that comprise the freshwater and saltwater data bases were not
9 different. If this was true, the difference between the actual freshwater and saltwater FAVs should be
10 common to the majority of randomly generated FAV differences. For PAHs, the test-statistic occurred
11 at the 93.5 percentile of the generated FAV differences (Table 3-3). This percentile suggests that
12 saltwater genera may be somewhat more sensitive than freshwater genera as illustrated in Figure 3-1
13 and Appendix C. However, since the probability was less than 95% hi the AR analysis, the null
14 hypothesis of no significant difference in sensitivity for freshwater and saltwater species was accepted
15 (Table3-3).
16 Since freshwater and saltwater species showed no significant differences in sensitivity, the AR
17 Method was applied jointly for the analysis of the difference in sensitivity for benthic and all aquatic
18 organisms (benthic and water column species are always combined to derive WQC, therefore, the
19 complete GMAV dataset is hereafter referred to as "WQC"). Using the criteria in U.S. EPA (2000a),
20 each life stage of each test organism, hence each GMAV at a ATOW of 1.0, was assigned a habitat
21 (Appendix C). The test statistic in this case was the difference between the WQC FAV, computed
22 from the WQC GMAVs at a £ow of 1.0, and the benthic FAV, computed from the benthic organism
23 GMAVs at a tfow of 1.0. The approach used to conduct this analysis was slightly different than that
24 used in the previous test for freshwater and saltwater GMAVs. The difference was that freshwater and
Final Draft PAH Mixtures ESG Document 3-12 5 April 2000
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1 saltwater GMAVs in the first test represented two separate groups. In this test, the GMAVs at a Kov/ of
2 1.0 for benthic organisms were a subset of the QMAVs at a Kow of 1.0 in the entire WQC dataset. In
3 the AR analysis for this test, the number of data points coinciding with the number of benthic
4 organisms were selected from the WQC dataset to compute each "benthic" FAV. The original WQC
5 FAV and the "benthic" FAV were then used to compute the difference statistic. This was done
6 iteratively and the distribution that results was representative of the population of FAV difference
7 statistics. The test statistic was compared to this distribution to determine its level of significance. The
8 probability distributions of the computed FAV differences are shown in Figure 3-2B. The test statistic
9 for this analysis occurred at the 82.8 percentile and the null hypothesis of no difference in the
10 sensitivities between benthic species and species used to derive the WQC FCV was accepted (Table 3-
11 3). This analysis supports the derivation of the FCV for PAHs based on all GMAVs at a ATOW of 1.0.
12
13 3.5 DERIVATION OF FCVs
I4
15 3.5.1 Derivation of the FCV at a KO}H of 1.0
16
17 The FCV is the value that should protect 95% of the tested species. The FCV is the quotient of
18 the FAV and the FACR for the substance. The FAV is an estimate of the acute LC50 or EC50
19 concentration corresponding to a cumulative probability of 0.05 for the genera from eight or more
20 families for which acceptable acute tests have been conducted on the substance. The ACR is the mean
21 ratio of acute to chronic toxicity for three or more species exposed to the substance that meets
22 minimum database requirements. For more information on the calculation of ACRs, FAVs, and FCVs
23 see the U.S. EPA National WQC Guidelines (Stephan et al., 1985).
24 The FCV at a £ow of 1.0 for PAHs is derived using the GMAVs at a Kow of 1.0 from water-
Final Draft PAH Mixtures ESG Document 3-13 5 April 2000
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1 only acute toxicity tests (Appendix C) to calculate the FAV at a KQV/ of 1.0 which is then divided by the
2 Final ACR.
3 The FAV at a Kov/ of 1.0 is calculated using the GMAVs at a Kov/ of 1.0 of 7.66 ^mol/g
4 octanol for Americamysis, 8.50 /^mol/g octanol for Grandidierella, 9.80 //mol/g octanol for Crangon,
5 11.0 ^mol/g octanol for Oncorhynchus, and the number of genera tested (N = 49). The Final Acute
6 Value at a Kovf of 1.0 is 9.32 ^mol/g octanol. This FAV is greater than the GMAVs of the two most
7 acutely sensitive genera as would be expected given the calculation procedure and the presence of 31
8 GMAVs.
9 The FAV at a Kovf of 1.0 of 9.32 yumol/g octanol is divided by the Final ACR of 4.16 to obtain
10 a FCV at a KQW of 1.0 of 2.24 ^mol/g octanol (Table 3-3). Because nonionic organic chemicals
11 partition similarly into octanol and Upid of organisms, the FCV at a ^Tow of 1.0 in /tmol/g octanol
12 approximately equals tissue-based "acceptable" concentration of about 2.24 jumol/g lipid.
13
14 3.5.2 Derivation of the PAH-Specific FCVs
15
16 The PAH-specific FCVs G"g/L) (Table 3-4) are calculated from the FCV at a Kow of 1.0
17 (/imol/g octanol), the slope of the KQ^-KQC relationship, the universal narcotic slope of the ATow-acute
18 toxicity relationship, and the PAH-specific Kow values (Equation 3-1, 3-2, and 3-3).
19
20 log10PAH-specific FCV = (slope) * log^ow + logio FCV at a £ow of 1.0 (3-1)
21
22 log10PAH-specific FCV = -0.945 Iog10£ow -f log,0(2.24) (3-2)
23
24 log,0PAH-specific FCV (^mol/L) = 1000(antilog(-0.9451og10K0w +0.3502)) (3-3)
Final Draft PAH Mixtures ESG Document 3-14 5 April 2000
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i SECTION 4
2 DERIVATION OF ESGs
3
4 4.1 DERIVATION OF POTENCIES FOR INDIVIDUAL PAHs IN SEDIMENTS (QXTJ.AHI.FCVJ)
5
6 The critical concentration of a PAH in sediment (Cocj.^ FCV|) that is related to the FCV is
7 derived following the EqP method (U.S. EPA, 2000a; Di Toro et al., 1991) because the interstitial
8 water-sediment partitioning of PAHs follows that of other nonionic organic chemicals. Therefore, a
9 sediment effects concentration for any measure of effect can be derived from the product of the water-
10 only effects concentration for that effect and the K^ for that particular PAH. The use of K^ to derive
11 a sediment effects concentration for PAHs is applicable because partitioning for these chemicals is
12 primarily determined by the organic carbon concentration of the sediment.
13 The partitioning equation between the organic carbon-normalized sediment concentration, Coc
14 Omol/goc = mmol/kgoc), and the free interstitial water concentration, Cd (mmol/L), is given by the
15 equation
16
17 Coc^ocC,, (4-1)
18
19 where K^ (L/kggc), defined above, can be calculated from a Kovt obtained from SPARC (Hilal et al.,
20 1994) using the following equation from Di Toro (1985)
21
22 log10Koc = 0.00028+0.983 Iog10^0w («)
Final Draft PAH Mixtures ESC Document 4-1 5 April 2000
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1 Qx:.pAHi.Fcvi f°r individual PAHs are then calculated using Equation 4-1 with the FCV as the water
2 concentration
3
4 Coc.pAHi.Fev,- = *oc FCV,. <4'3>
5
6 Since KQC is presumed to be independent of sediment type for nonionic organic chemicals, so
7 also is CQC PAH/ FCV,-.
8 Table 3-4 contains the Cocffiaifci[ G"g/goc) for 74 PAHs found in sediments, including the 34
9 PAHs (in bold) analyzed by the U.S. EPA in their EMAP program (U.S. EPA, 1996B; 1998).
10 COC,PAH«.FCV« values for PAHs not hi Table 3-4 can be calculated in a similar manner (see Section 6.2 for
11 discussion on the PAHs to which the ESG applies). The range in the C^,pAH,-,Fcvi values for the 74
12 PAHs listed in Table 3-4, which were derived using only data for PAHs is from 349 to 1435 /^g/goc-
13 In contrast, the range of the same value, termed the Cs ^ by Di Toro and McGrath (2000), was about
14 the same (766 to 1887 //g/goc) for the 23 PAHs when derived by using the database for narcotic
15 chemicals with a PAH correction.
16
17 4.2 DERIVATION OF THE ESG FOR PAH MIXTURES
18
19 The correct derivation of the ESG for a mixture of PAHs is based on the approximate additivity
20 of narcotic chemicals in water and tissue (Di Toro et al., 2000; Section 2.9 of this document) and in
21 sediment (Section 5.2). Because WQC and ESGs are based on FCVs they are not intended to cause
22 toxicity to most species, the term toxic unit could be misleading. Therefore, we refer to the quotient of
23 the concentration of a specific chemical in water and its WQC FCV as water quality criteria toxic units
24 (WQCTUFCV/). Similarly, the quotient of the sediment concentration for a specific PAH (COC.PAH.) and
Final Draft PAH Mixtures ESG Document 4-2 5 April 2000
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Common Name,
Scientific Name
Sheepshead minnow,
Cyprinodon variegatus
Total Data Points
Test Conditions
No. of Data
Test Duration (hr) Method' Concentration1" Points'
96 ' FT M 2
736 (796)
References
Wardetal., 1981; Battelle, 1987
'Method: S=static, FT=flow-through, R=-renewal
'Concentration: U=>unmeasured (nominal), M-chemical measured, I=initial
'Number of data points used; () = number of data before screening for concentration> solubility and outliers.
A-8
-------
Test Conditions
Common Name,
Scientific Name
Mysid,
Americamysis bahia
Grass shrimp,
Palaemonetes pugio
Grass shrimp,
Palaemonetes pugio
Grass shrimp,
Palaemonetes pugio
Grass shrimp,
Palaemonetes pugio
Crab,
Portunus pelagicus
Inland silverside,
Menidia beryllina
Inland silverside,
Menidia beryllina
Sheepshead minnow,
Cyprinodon variegatus
Sheepshead minnow,
Cyprinodon variegatus
Sheepshead minnow,
Test Duration (hr)
96
96
96
96
96
96
96
96
24
48
96
Method1
FT
R
S
FT
S
S
R
S
S
S
S
Concentration11
M
U
U
M
M
M
U
U
U
U
U
No. of Data
Points'
8(9)
2
4
1
1
4
1
7(8)
7(8)
11(12)
13(15)
References
Battelle, 1987; Champlin and Poucher, 1992a;
Horneetal., 1983; EG&G Bionomics, 1978; U.S.
EPA, 1978; Kuhn and Lussier, 1987; Thursby,
1991b
Battelle, 1987; Thursby et al., 1989a
Champlin and Poucher, 1992a; Home et al., 1983;
Thursby, 1991b; Tatem et al., 1978
Battelle, 1987
Tatem, 1977
Mortimer and Cornell, 1994
Thursby et al., 1989a
Champlin and Poucher, 1992a; Dawson et al., 1977;
Horneetal., 1983
Heitmulleretal., 1981
Heitmulleretal., 1981
Heitmulleretal., 1981:
Cyprinodon variegatus
U.S. EPA, 1978
A-7
-------
Test Conditions
Common Name,
Scientific Name
Bluegill,
Lepomis macrochlrus
Tadpole,
Rana catesbeiana
Clawed toad,
Xenopus laevis
Mexican axolotl,
Ambystoma mexicanum
Saltwater
Annelid worm,
Neanthes arenaceodentata
Annelid worm,
Neanthes arenaceodentata
Copepod,
Nitocra spinipes
Amphipod,
Leptocheirus plumulosus
Mysid,
Americatnysis baliia
Mysid,
Americamysls bahia
Mysid,
Test Duration (hr)
96
96
48
48
96
96
96
96
96
96
96
Method'
S
FT
S
S
S
R
S
FT
S
S
R
Concentration11
U
M
U
U
U
U
I
M
U
M
U
No. of Data
Points'
36(40)
5
5
5
4(5)
(1)
6
4
20(23)
1
1
References
Pickering and Henderson, 1966; U.S. EPA, 1978;
LeBlanc, 1980b; ; Buccafusco et al., 1981; Bently et
al., 1975; Dawson et al., 1977. i
Thurston et al., 1985
SlooffandBaerselman, 1980
SlooffandBaerselman, 1980
Home et al., 1983; Rossi and Neff, 1978
Thursbyeta!., 1989a
Bengtssonetal., 1984
Swartz, 1991a; Champlin and Poucher, 1992a;
Boeseetal., 1997
U.S. EPA, 1978; Champlin and Poucher, 1992a;
Zaroogianetal., 1985
EG&G Bionomics, 1982
Thursby et al., 1989b
Americamysis baliia
8(9)
A-6
-------
Test Conditions
Common Name,
Scientific-Name
Mosquitofish,
Gambusia affinis
Mosquitofish,
Gambusia affinis
Mosquitofish,
Gambusia affinis
Mosquitofish,
Gambusia affinis
Gappy,
Poecilia reticulata
Guppy,
Poecilia reticulata
Guppy,
Poecilia reticulata
Bluegill,
Lepomis macrochirus
Bluegil!,
Lepomis macrochirus
Bluegill,
Lepomis macrochirus
Bluegill,
Lepomis macrochirus
Bluegill,
Test Duration (hr)
24
48
96
96
24
48
96
24
24
48
48
96
Method"
S
S
FT
S
S
S
S
S
FT
FT
S
FT
Concentration1"
U
U
M
U
U
U
U
U
M
M
U
M
No. of Data
Points'
(3)
(3)
5(6)
3
(1)
10(11)
4
18(19)
1
1
6(7)
8
References
Thurstonetal., 1985
i
Thurstonetal., 1985
Thurston et al., 1985;
Wallen et al., 1957
Wallenetal., 1957
Pickering and Henderson, 1966
Slooff et al., 1983; Pickering and Henderson, 1966
Slooffetal., 1983
Pickering and Henderson, 1966; Buccafusco et al.,
1981;BentlyetaI., 1975
Call eta!., 1983
Calletal., 1983
Pickering and Henderson, 1966; Bently et al., 1975
Thurston et al., 1985; Bently et al., 1975; Call et
Lepomis macrochirus
al., 1983; Holcombe et al., 1987
A-5
-------
Test Conditions
Common Name,
Scientific Name
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Channel catfish,
Ictalurus punctatus
Medaka,
Oryzias latipes
American flagfish,
Jordaneltafloridae
American flagfish,
Jordanella floridae
American flagfish,
Test Duration (hr) Method'
48 FT
96 FT
96 S
96 R
96 S
96 FT,S
48 S
24 FT
48 FT
96 FT
Concentration'
M
M
M
U
U
M
U
M
M.
M
No. of Data
Points'
8
141(146)
3(4)
1
4
7
4(5)
6
6
6
References
Ahmad etal., 1984
f.
Veith et al., 1983; Thurston et al., 1985; Holcombe
et al., 1987; Ahmad et al., 1984; Dill, 1980;
DeGraeve et al., 1982; Alexander et a!., 1978;
Broderius and Kahl, 1985; Cairns and Nebeker,
1982; Hall et al., 1989; Hall et al., 1984; Call et al.,
1985; CLSES, 1984; CLSES, 1985; CLSES, 1986;
CLSES, 1988; CLSES, 1990; Kimball, 1978
Bridie et al., 1979; EG&G Bionomics, 1982;
Gendussa, 1990; Hornc et al., 1983
Academy Natural Sci., 19&1
Pickering and Henderson, 1966
Thurston etaf., 1985; Holcombe etal., 1983;
Gendussa, 1990
Slooff etal., 1983
Smith et al., 1991
Smith etal., 1991
Smith etal. ,1991
Jordanella floridae
A-4
-------
Test Conditions
Common Name,
Scientific Name
Bleak,
Albumus albumus
Goldfish,
Carasius auratus
Goldfish,
Carasius auratus
Goldfish,
Carasius auratus
Goldfish,
Carasius auratus
Goldfish,
Carasius auratus
Goldfish,
Carasius auratus
Goldfish,
Carasius auratus
Golden orfe,
Leuciscus idus melanotus
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow.
Test Duration (hr)
96
24
24
24
96
96
48
48
24
24
24
48
Method'
S
s
S
FT
S
FT
S
FT
S
S
FT
S
Concentration1"
I
M
U
M
U
M
U
M
i(ns)
U
M
U
No. of Data
Points'
7
26(28)
5(6)
1(2)
4
1(2)
5(6)
1(2)
26'
6
8
11
References
Bengtssonetal., 1984
Bridie etal., 1979 '
Pickering and Henderson, 1966
Brenniman et al., 1976
Pickering and Henderson, 1966
Brenniman et al., 1976
Pickering and Henderson, 1966
Brenniman etal., 1976
Juhnke and Ludemann, 1978
Pickering and Henderson, 1966
Ahmad et al., 3984
Pickering and Henderson, 1966
Pimephales promelas
A-3
-------
Test Conditions
Common Name,
Scientific Name
Brine shrimp,
Anemia salina
Crayfish,
Orconectes immunis
Mosquito,
Aedes aegypli
Mosquito,
Culex pipiens
Midge,
Tanytarsus dissimilis
Rainbow trout,
Oncorhynchus mykiss
Rainbow trout,
Oncorhynchus mykiss
Rainbow trout,
Oncorhynchus mykiss
Rainbow trout,
Oncorhynchus niykiss
Rainbow trout,
Oncorhynchus mykiss
Rainbow trout,
Oncorhynchus mykiss
Rainbow trout,
Test Duration (hr)
24
96
48
48
. 48
48
24
24
48
96
96
96
Method'
S
FT
S
S
S
FT
FT
S
S
FT
S
S
Concentration*
N
M
U
U
M
M
M
U
U
M
M
U
No. of Data
Points'
32(34)
6
5
5
9
7
6
1(2)
6
22
1
1
References
Abernethy et ai., 1988; Abernethy et al., 1986
i
Thurston et al., 1985; Holcombe et al., 1987
Slooffetal., 1983
Slooffetal., 1983
Thurston et al., 1985; Call et al., 1983
Holcombe et al., 19.87; Call et al., 1983
Calletal., 1983
Bently etal., 1975
Slooff et al., 1983; Bently et al.. 1975
Thurston et al., 1985; Call et al., 1983; Holcombe et
al., 1987; Call et al., 1986; DeGraeve et al., 1982;
Hodsonetal., 1988
Home etal., 1983
Bently etal., 1975
Oncorhynchus mykiss
A-2
-------
Appendix A. Individual datasets which comprise the acute lethality data base. Table from Di Toro et al. (2000).
Test Conditions
Common Name,
Scientific Name
Freshwater
Paramecium,
Tetrahymena elliotti
Hydra,
Hydra oligactis
Snail,
Lymnae stagnalis
Cladoceran,
Daphnia cucullata
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia pulex
Cladoceran,
Daphnia pulex
Test Duration (hr)
24
48
48
48
24
48
48
48
. 48
48
Method"
S
S
S
S
S
S
S
FT.R
S
S
Concentration11
U
U
U
U
U
U
U
M
M
U
No. of Data
Points'
10(12)
5
5
5
21(28)
72(78)
19
1(2)
(1)
6
References
i
Rogersonetal., 1983
Slooff etal., 1983
Slooffetal., 1983
Canton and Adema, 1978
LeBlanc, 1980a
Abernethy et al., 1988; U.S. EPA, 1978; Canton
and Adema, 1978 Rogerson et al., 1983; Bringman
and Kuhn, 1959; Eastman et al., 1984; Dili, 1980
EG&G Bionomics, 1982; Thurston et al., 1985;
Adema, 1978; Oris et al., 1991; Brooke, 1991;
Millemann et ah, 1984; Munkrittrick et al., 1991
EG&G Bionomics, 1982; Brooke, 1994
Trucco et al., 1983
Canton and Adema, 1978; Passino and Smith, 1987
A-l
-------
Table 6-3. Teratogenic and carcinogenic effects of benzo(a)pyrene (BaP) and anthracene on freshwater and saltwater fishes. Measured concentrations of
exposure are converted to sediment concentrations (Coc) likely to result in the equivalent effect using EqP and SAR methodology.
Organism
Chemical
Log|0 tfow Log KK
Measured
C *
fog/L)
Cd-derived
(A3.81C
(1,000)
0.21
-
0.10
>3.81
(5)
>3.81
(24)
>3.81C
. (869)
-
>3810
210
-
100
>3810
>3810
>3810
8.8 0.06
9 0.06
1.9 0.05
157 0.03
2.1 0.03
1 0.03
10.5 0.03
20.0 0.03
147 219 Hall and Oris, 1991
150 256 Goddard et al., 1987
38:6 66 Hannah etal., 1982
Hose et al., 1984
5233" 8,937" Hoseet al., 1981
70 120 Hose etal., 1982
33.3 57 Winkleretal., 1983
350 598 Winkleretal., 1983
666 1,137 Winkleretal., 1983
CARCINOGENIC EFFECTS
FRESHWATER
Japanese medaka
guppy
BaP
BaP
6.11
6.11
6.00
6.00
•
>3.81C
(261)
>3.81C
(209)
>3840
>3840
-
-
' If the concentration of BaP exceeded its solubility of 3.81 A
-------
Table 6-2.
PAH measured in various sediment monitoring programs. See Di Tcro and McGrath
(2000) for data sources.
Parameter NOAA
Acenaphthene x
Acenaphthylene x
Anthracene x
Chrysene x
Fluoranthene ~ x
Fluorene x
naphthalene x
phenanthrene x
pyrene x
Benzo(k)fluoranthene x
Benzo(b)fluoranthene x
Benzo(a)pyrene x
Benzo(a)anthracene x
Benzo(e)pyrene x
Benzo(g,h,i)perylene x
Dibenz(a,h)anthracene x
2,6-dimethylnaphthalene x
Indeno(l,2,3-cd)pyrene x
1-methylnaphthalene x
2-methylnaphthalene x
perylene x
I-methylphenanthrene x
2,3,5-trimethylnaphthalene x
2-methylanthracene
2-methylphenanthrene
3 ,6-dimethylphenanthrene
9-methylanthracene
9, 10-dimethylanthracene
Cl-benzo{a)anthracenes /chrysenes
C2-benzo(a)anthracenes /chrysenes
C3-benzo(a)anthracenes /chrysenes
C4-benzo(a)anthracenes /chrysenes
Cl-fluoranthenes/pyrenes
C2-fluoranthenes/pyrenes
Cl-fluorenes
C2-fluorenes
C3-fluorenes
Cl-naphthalenes
C2-naphthalenes
C3-naphthalenes
C4-naphthalenes
Cl-phenanthrenes/anthracenes
C2-phenanthrenes/anthracenes
C3-phenanthrenes/anthracenes
C4-phenanthrenes/anthracenes
Total Number of PAHs8 23
J^umber of data points 640
SFEI
x
x
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
25
137
San
Diego
x
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
23
182
Southern
California
x
x
x
x
x
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
23
40
NY/NJ
REMAP*
x
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
23
153
Virginian
EMAP8
x
x
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
23
318
Elliott
Bay
x
x
x
x
x
x
x
x
x
x
x
x
x
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
33C
30
Carolinian
EMAP
x
x
X
X
X
X
X
X
X
X
X
X
X
X
X •
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
34
2841
Louisian
EMAP
x
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
34
22i
A Benzo(b)fluoranthene and benzo(k)flouranthene were measured together.
8 A specific Cl-PAH was not included in the total if the Cl alkylated PAH series was measured.
For example, 1-methylnaphthalene was not included in the total if the Cl-naphthalenes were measured.
c For this dataset, the Cl-Naphthalenes were not measured. As a result, the 1-methylnaphthalene and 2-methylnaphthalene
were considered when determining the total number of PAHs.
-------
Table 6-1. Relative Distribution of SESGTUFCV>TOT to SESGTUFCV „ and SES
Combined EMAP Dataset (N =488).
Percentile
50
80
90
95
99
SESGTUFCViTOT/SESGTUFCV,,3 SESGTUFCV
2.75
6.78
8.45
11.5
16.9
'GTUpcv.23 for
TOT/SESGTU
1.64
2.80
3.37
4.14
6.57
the
FCV.23
-------
Table 5-3. Chemicals included in the high £ow PAH mixture experiment (Spehar et al., 2000).
Chemical Name
3,6-Dimethylphenanthrene
2-Ethylanthracene
2-(tert-butyl)anthracene
2,3 Benzofluorene
Benzo(a)anthracene
Triphenylene
9-Phenylanthracene
Benzo(b) fl uoranthene
Benzo(k)fluoranthene
7, 12-Dimethylbenz(a)anthracene
Benzo(a)pyrene
3-Methylcholanthrene
7-Methylbenzo(a)pyrene
TOTAL PAH- WATER CONCENTRATION
Molecular
Weight
(e/mol)
206.29
206.29
234.34
216.28
228.29
228.30
254.33
252.32
252.32
256.35
252.31
268.38
266.35
log,n KnJ
5.52
5.36
5.88
5.54
5.67
5.75
6.31
6.27
6.29
6.58
6.11
6.76
6.54
lOBm KrJ
5.42
5.27
5.78
5.44
5.58
5.65
6.20
6.16
6.18
6.46
6.00
6.64
6.43
Estimated
Solubility'
77.98
59.62
33.04
25.30
12.28
5.110
3.640
8.280
8.350
13.41
2.880
3.110
1.460
Target
Sediment
Concentration
42.38
39.32
50.91
42.88
45.80
47.66
64.22
62.75
63.64
75.04
57.46
83.92
73.37
749.4
Solubility Limited
Nominal Water Nominal Water
Concentration11 Concentration
CwB/L) («R/L)
33.12 '
43.94
19.78 ,
33.27
27.70
24.11
10.30
10.96
10.50
6.620
14.38
5.100
7.320
247.1
33.12
43.94
19.78
25.30
12.28
5.110
3.640
8.280
8.350
6.620
2.880
3.110
1.460
173.9
"Predicted by SPARC in distilled water at 25°C.
"Predicted from Di Toro et al. (1991).
'Nominal concentration predicted by KQC, regardless of solubility limits; highest concentration only.
dTarget sediment concentration//^.
-------
Table 5-2.
Percent mortality of benthic invertebrates in relation to the SESGTUFCV values of mixtures of polycyclic aromatic hydrocarbons spiked into
sediment.
Species*
Diporeia sp.
Diporeia sp.
Diporeia sp.
Diporeia sp.
R. ibronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
A. abdita
A. abdita
A. abdita
A. bahia
A. bahia
A. bahia
LESGTUpcv
PAHtfow <5.5
0.01
0.21
0.49
1.37
10.32
,5.80
5.12
3.25
2.50
1.80
1.42
2.77
4.91
5.88
5.71
2.71
2.06
0.63
1.91
0.58
1.55
0.90
5.41
0
5.41
5.41
0
5.41
£ESGTUFCV
PAH Kbw >5.5
0.02
0.36
0.60
1.71
0
0
0
0
0
0
0
0
5.02
0
0
2.23
0.79
1.57
25.89
8.03
8.03
3.40
0.64
2.58
3.22
0.64
2.58
3.22
SESGTUFCV
AH PAHs
0.03
0.57
1.10
3.08
10.3
5.80
5.12
3.25
2.50
1.80
1.42
2.77
9.93
5.88
5.71
4.94
2.84
2.20
27.8
8.61
9.58
4.30
6.05
2.58
8.63
6.05
2.58
8.63
Percent
Mortality
3
10
0
12
100
38
8
11
4
2
3
5
3
5
2
3
2
1
4
5
9
0
7
7
10
3
7
7
PAH Mixture8
fluor, phen, anthr, flu, pyr, chry, b(b)flu, b(e)pyr, b(a)pyr, pery, b(ghi)pery
fluor, phen, anthr, flu, pyr, chry, b(b)flu, b(e)pyr, b(a)pyr, pery, b(ghi)pery
fluor, phea, anthr, flu, pyr, chry, b(b)flu, b(e)pyr, b(a)pyr, pery, b(ghi)pery
fluor, phen, anthr, flu, pyr, chry, b(b)flu, b(e)pyr, b(a)pyr, pery, b(ghi)pery
ace; phen; flu; pyr
ace; phen; flu; pyr
ace; phen; flu; pyr
ace; phen; flu; pyr
ace; phen; flu; pyr
ace; phen; flu; pyr
ac'e; phen; flu; pyr
anthr; flu
b(a)anthr; flu
2-methyIanthr; flu
9,10-dimethylanth; flu
b(b)flu; flu
chf; flu
3,6-dimethylphen; flu
anthr; b(a)anthr; 2-methylanthr; b(b)flu; chr; 3,6-dimethylphen
anthr; b(a)anthr; 2-methylanthr; b(b)flu; chr; 3,6-dimethylphen
anthr; b(a)anthr; 2-methylanthr; b(b)flu; chry; 3,6-dimethylphen; flu
anthr; b(a)anthr; 2-methylanthr; b(b)flu; chry; 3,6-dimethylphen; flu
9,10-dimethylanthr; chry
b(a)pyr, cor
9, 10-dimethylanthr; chry; b(a)pyr; cor
9,10-dimethylanthr; chry
b(a)pyr; cor
9.10-dimethvlanthr: chry. Watovr; cor
Reference
Landrumetal., 1991
Landrum et al., 1991
Landrum et al., 1991
Landrum et al., 1991
Swartzetal., 1997
Swartzetal., 1997
Swartz et al., 1997
Swartzetal., 1997
Swartzetal.. 1997
Swartz et al., 1997
Swartzetal., 1997
Boeseetal., 1999
Boeseetal., 1999
Boese et al., 1999
Boeseetal., 1999
Boeseetal., 1999
Boeseetal., 1999
Boeseetal., 1999
Boeseetal., 1999
Boese et al., 1999
Boeseetal., 1999
Boeseetal., 1999
Burgess etal., 2000
Burgess etal., 2000
Burgess etal., 2000
Burgess etal., 2000
Burgess et al., 2000
Burgess et al., 2000
vTest Species: amphipods: Diporeia sp., Rhepoxynius abronius, Ampelisca abdita; mysids: Americamysis bahia
"PAH Code: ace - acenaphthene; anthr - anthracene; b(a)anthr - benz(a)amhracene; b(a)pry - benzo(a)pyrene; b(ghi)pery - benzo(ghi)perylene; b(b)flu - benzo(b)fluoranthene; chry - chrysene; cor
- coronene; 9,10-dimethylanth - 9,10-dimethylanthracene; 3,6-dimethylphen - 3,6dimethy!phenamhrene; flu - fluoranthene; fluor - fluorene; 2-methylanthr - 2-methylanthracene; pery - perylene;
phen - phenanthrene; pyr - pyrene.
-------
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Rhegoxy_nius abronius
Fluoranthene
Fluoranthene
Fluoranthene
Fluoranthene
Fluoranthene
Fluoranthene
Fluoranthene
Fluoranthene
Test conditions for water-only toxicity tests: S
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
= static, FT -
13
13
13
13
13
13
13
13
flow-tl
.9E
.9E
.96
.9E
.9E
.9*
.9E
.9E
iron
22.7
29.4
24.2
> 315
14.1
• 26.6
19,2
9.38
Mean LC50 ratio -
igh, M = measured, 10
1.63
2.12
1.74
> 22.66°
1.01
1.91
1.38
0.67
1.60
• 10-d duration.
1890
2100
2230
>4360
4410
3080
3150
2790
Mean
•1390
1390
1390
1390
1390
1390
1390
1390
LC50 ratio =
1.36
1.51
1.60
4.04°
3.17
2.22
2.26
2.01
1.91
Swartz et al.
Swartz et al.
Swartz et al.
DeWitt et al
DeWitt et al
DeWitt et al
DeWitt et al
DeWitt et a!
, 1990
, 1990
, 1990
., 1992
., 1992
., 1992
.. 1992
., 1992
"Prt dieted LC50 Wgoc> = water-only LC50 (ug/L) x KK (L/kgoc) x 1
•Sediments spiked with fluoranthene by Suedel et al. (1993) were not at equilibrium, therefore, are not included in the mean.
'Source of organic carbon was fresh plant material, not naturally aged organic matter, therefore, value was not included in the mean.
'] 0-day LC50 value from Swartz (2000). .
-------
CO
Slow
U
•
O
I-}
2
1
0
-1
-2
-3
-4
-5
-6
-7
-8
B
-7-^-5-4 -3 -2-10 1 2
Log Aqueous Solubility (mol/L)
-------
Log ,«LC50 (mmol/L)
-------
-------
Figure 6-5. Computed solubilities of nine PAHs relative to their 25°C solubilities as a function of
temperature. The solid line is the least-squares regression line (Equation 6-10).
-------
are treatments with effects significantly different from controls.
Figure 5-11. Amphipod (Ampelisca abdita) abundance versus 2ESGTUrcv. Vertical line is the ESG
of r.O SESGTUFCV. Data are from the Virginian and Louisianian province EMAP
(U.S. EPA, 1996a,b) and the New York/New Jersey Harbor REMAP (Adams et al.,
1996).
Figure 6-1. Comparison of observed SESGTUFCVtTOT to observed SESGTUpcv.ja from 13 PAHs
(A) and EESGTUFCVJ3 from 23 PAHs (B) for the combined dataset including U.S.
EPA EMAP Louisian and Carolinian Provinces (N=490). The line shows the
resulting log-log linear regression equation.
Figure 6-2. Probability distribution of the (A) SESGTUFCV,i3 and 03) 2ESGTUFCV>23 values for
each sediment from the entire database. Symbols are as described in text.
Figure 6-3. BaP concentration of 539 sediment samples from the EMAP and Elliot Bay datasets
versus the £ESGUs of 34 PAHs (A) and a probability plot of these BaP concentrations
at an £ESGU = 1 (B). The solid line in both plots is the BaP critical sediment
concentration for teratogenic and carcinogenic effects
Figure 6-4. Anthracene concentration of 539 sediment samples from the EMAP and Elliot Bay
datasets versus the £ESGUs of 34 PAHs (A) and a probability plot of these
Anthracene concentrations at an £ESGU = 1 (B). The solid line in both plots is the
Anthracene critical sediment concentration for teratogenic effects
-------
spiked with a mixture of high KOW PAH. Acute TUs were calculated based on
measured sediment PAH concentrations and the GMAV from Appendix C. Asterisks
indicate significant reduction compared to the control (a=0.05).
Figure 5-7. Response of H. azteca exposed for 28 days under flow-through conditions to sediment
spiked with a mixture of high KQW PAH. Acute TUs were calculated based on
measured sediment PAH concentrations and the GMAV from Appendix C. Asterisks
indicate significant reduction compared to the control (a=0.05).
Figure 5-8. Survival (after 28 days) and growth (after 10 days) of H. azteca expressed on .the basis
of measured PAH concentrations in tissues (Hpid normalized). Effect concentrations
were calculated from acute water-only effect data for fluoranthene, methanol, ethanol,
and 2-propanone using the narcosis model, Acute TUs were calculated by dividing the
lipid-normalized concentration of PAH in tissue by the GMAV, assuming lipid =
octanol. The chronic threshold is represented by the GMAV divided by the ACR.
Data are from Di Toro et al. (1999).
Figure 5-9. Response of H. azteca exposed for 10 days (3 renewals) to sediment spiked with a
mixture of high KQW PAH. Acute TUs were calculated based on measured sediment
PAH concentrations and the GMAV from Appendix C. Asterisks indicate significant
reduction compared to the control (a=0.05).
Figure 5-10. Response of L. plumulosus exposed for 10 days under static conditions to sediment
spiked with a mixture of high KQW PAH. Acute TUs were calculated based on
measured sediment PAH concentrations and the GMAV from Appendix C. Asterisks
-------
three sediments per chemical. Sediment types are indicated by open symbols (lowest
organic carbon content), doubled symbols (intermediate organic carbon content) and
filled symbols (highest organic carbon content). Uncertainty error bars are represented
by~solid vertical lines (see U.S. EPA, 1999a for source of KQC values).
Figure 5-3. Percent mortality of Ehepoxynius abronius in sediments spiked with acenaphthene,
phenanthrene, fluoranthene, or pyrene (see Appendix D for data).
Figure 5-4. Percentage rank, based on ESGTUFCVj, of the sensitivities of genera of benthic
organisms from spiked sediment toxicity tests with individual PAHs.
Figure 5-5. Mortality of the amphipod, Rhepoxynius abrowus, from tests 10-day sediment toxicity
tests with four parent PAHs separately (triangles) and in combination (circles) from
(Swartz et al., 1997) versus predicted sediment toxic units (PSTUs). PSTUs are the
sediment concentrations in each treatment divided by the predicted PAH-specific
*
sediment LC50 values. The predicted PAH-specific sediment LC50 values are derived
from the interstitial water 10-day LC50 values from spiked sediment toxicity tests and
the universal narcosis slope to derive the PAH-specific critical tissue concentrations.
The geometric mean of the critical tissue concentrations, the universal narcosis slope
and the PAH-specific £"ow and AT^ were used to derive PAH-specific sediment LC50
values. For the mixture experiment the toxic units are the sum of the sediment
concentrations for each of the four PAHs divided by their respective PAH-specific
sediment LC50 values.
Figure 5-6. Response of H. azteca exposed for 10 days under flow-through conditions to sediment
-------
the tested mixtures are as indicated (adopted from Hermens et al., 1984).
Figure 3-1. GMAVs at a logloK(yff of 1.0 from water-only acute toxicity tests using freshwater and
saltwater genera versus percentage rank of their sensitivity. Freshwater genera are
indicated by open symbols and saltwater genera are indicated by closed symbols.
Figure 3-2. Probability distributions of FAY difference statistics to compare water-only toxicity
data from (A) freshwater versus saltwater genera and (B) benthic versus WQC.
Figure 4-1. Probability distribution of the 2ESGTUFCV for PAH mixtures in sediments from
coastal and estuarine locations in the United States (NOAA, 1991; Adams et al., 1996;
Anderson et al., 1996; Fairey et al., 1996; U.S. EPA, 1996a, b, 1998; Hunt et al.,
1998). Horizontal line indicates a toxic unit of 1.0.
Figure 4-2. Probability distribution of the 2ESGTUFCV for PAH mixtures in sediments from all the
A
coastal and estuarine locations in the United States from Figure 4-1 (NOAA, 1991;
Adams et al., 1996; Anderson et al., 1996; Fairey et al., 1996; U.S. EPA, 1996a, b,
1998; Hunt et al., 1998). Horizontal line indicates a toxic unit of 1.0.
Figure 5-1. Percent mortality versus predicted interstitial water toxic units for six chemicals and
three sediments per chemical. Sediment types are indicated by open symbols (lowest
organic carbon content), doubled symbols (intermediate organic carbon content) and
filled symbols (highest organic carbon content).
Figure 5-2. Percent mortality versus predicted interstitial water toxic units for seven chemicals and
-------
FIGURES
Figure 2-1 . Schematic diagram of the log10LC50 versus logloKOVf relationship. At log10Kow = 0,
= 1, the concentration in water equals the concentration in octanol.
Figure 2-2. Comparisons of (A) logj^^, predicted by SPARC versus measured log,,,/^ using
slow stir method and (B) reported log10LC50 values versus the aqueous solubility
estimated by SPARC. The diagonal line represents equality.
Figure 2-3. Ratios of (A) 48- to 96-hour LC50 values and (B) 24- to 96-hour LC50 values versus
logioA^w. The line in (B) is the regression used to correct the 24-hour LC50 to 96-
hour LC50.
Figure 2-4. Logi0LC50 versus logio^ow for the indicated species. The line has a constant slope of
-0.945. The y-intercepts vary for each species. Outliers are denoted by a plus symbol
Figure 2-5. Statistical comparison of slopes fitted to individual species to the universal slope of
-0.945 showing (A) the probability that the difference occurred by chance (filled bars)
and number of data points in the comparison (hatched bars) for each species in the
database, and (B) the deviations of the individual estimates from the universal slope.
Abbreviations are based on the first letter of the genus and either the first or second
letters of the species names given in Appendix A (e.g., Aae =Aedes aegypti and Am
=Ambystoma mexicanuni).
-------
Figure 2-6. Chemical class comparisons. (A) Residuals from the regression grouped by class with
mean + 2 standard errors. (B) Residuals grouped by class with chemical class
corrections included in the regression.
Figure 2-7. The coefficient of variation of the estimated species-specific body burdens versus the
number of data points for that species (A), the log probability plot of the residuals (B),
and the residuals versus log10/i^)W (C).
Figure 2-8. Logi0LC50 versus log10^Tow for (A) L. macrochints, (B) D. pulex, and (C) G. qffinis.
The line connects the individual estimates of the LC50 values, including the chemical
class correction.
Figure 2-9. Comparison of target lipid model, line-of-fit and observed LC50 data for individual
PAHs, by species. The PAHs included are: naphthalene (3.36), 1-methylnaphthalene
(3.84), 2- methylnaphthalene (3.86), 2-chloronaphthalene (3.88), l-chloronaphthalene
(3.88), acenaphthene (4.01), phenanthrene (4.57), pyrene (4.92), 9-methylanthracene
(5.01), fluoranthene (5.08). Number in parentheses = log,^,^. Solid line and filled
symbols are for non-halogenated PAHs. Dotted lines and unfilled symbols are for the
halogenated (i.e., chlorinated) PAHs. Plus symbols (+) denote outliers. Data are
from Di Toro et al. (2000) and were used for toxicity test screening criteria.
Figure 2-10. Predicted and observed body burdens for five species.
Figure 2-11. Additivity of type I narcosis toxicity. Comparison of the observed TU concentrations
calculated from four studies to the predicted TU of 1.0. The number of chemicals in
-------
Species
Poeciliopsis lucida and
Poeciliopsis monadia
(1-7 months old)
Poeciliopsis lucida and
Poeciliopsis monacha
(1-6 weeks old)
Bullheads
Japanese Medaka,
°oecilia reticulata
6-10 d old)
Rainbow trout
embryos),
Jncorhynchus inykiss
Mode
of
Exposure
water;
acetone
carrier
water;
acetone
carrier
Direct skin
(river
sediment
extract)
Water via
Sediment
extract re-
dissolved in
acetone
injection of
sediment
extract into
yolk sac
Method
Lab: (multiple
exposures) 3
to 4 exposure
periods of 5-
20 hours each
week
Lab: (multiple
exposures) .5
exposures
periods of 6
hours each
week
Lab
Lab
Lab
Exposure Cone
Associated
PAH with Effect
'7,12- 5ppm(per
dimethylbehz(a)- exposure)
anthracene
*
7, 12- 5 ppm (per
dimethylbenz(a)- exposure)
anthracene
Field Mixture* 5 % RSE painted
once per week
Field Mixture8 182 ppb TPAH
Black River, OH
extract;
254 ppb TPAH
Fox River, WI
extract
Field Mixture0 Doses0:
(Expl) 0.006 g
(Exp II) 0.012 g
0.006 g
nnrn jr
1 ' -
Exposure
Time
7-8
months
(from
initial
exposure)
6-7
months
18 months
24 h
1 year
Tissue
Toxic EffecUs): Cone
incidence of hepatic
tumors = 48%
Incidence of hepatic
tumors = 41.8%
23% of survivors
hyperplastic
9% with multiple
papiltomas
hepatocellular
carcinoma - Black
River Ex. (2/15 fish);
Pancreatic-duct cell
adenoma - Fox River
Ex. (1/15 fish)
Hepatic carcinomas
(I) 8.9% (11/123)
(II) 8.1% (12/148)
4.0% (5/148)
i i <%, n/fiV>
Comments: Reference
only survivors Schultz and
examined = Schullz 1982
(55% mortality in 5
ppm treatment)
(13% mortality in
control)
22% mortality in Schultz and
treatment Schultz 1982
16% mortality in
control
Tumor-bearing livers
enlarged, yellow- white
to greenish and
granular.
Survival of control and Black, 1983
experimental fish was
31%.
No incidence of
carcinomas in controls Fabacher et al . ,
up to 270 days post- 1991
exposure; one incidence
of lymphoma after 360
days of exposure.
Note; PCBs also Metcalfe et a)
present sediment from 1988
Hamilton Harbour
Buffalo River, NY; total no. PAHs measured = 13, total no. of carcinogenic PAHs = 6.
.lack River, OH. And Fox River, WI; full compliment of measured PAHs.
lamilton Harbor, ON, Canada; total no. PAHs measured = 13, total no. of carcinogenic PAHs = 6.
>oses are calculated as gram equivalent wet weight of sediment represented by the volume of extract micro-injected into each trout sac-fry.
F-2
-------
Appendix F. Carcinogenic effects from laboratory and field exposure to PAHs and PAH mixtures,
Species
Japaness Medaka,
Oryzia . atipes
(6-10 d old)
Mode
of
Exposure Method
Water; Lab; static
dimethyl-
formamide
carrier.
Exposure Cone
Associated
PAH with Effect
BaP 261 Mg/L
Exposure
Time
2 x 6!i, 1
week apart
Toxic EffccUs):
Neoplastic lesions in
livers and other
tissues after 36 weeks
• 36%vsl%
(controls); 20 fish
with adenoma, 6 with
hepatocellular
carcinoma
Tissue
Cone Comments:
Exposures carried out
at26°Cinthedark;
concentration exceeds
saturation solubility of
BaP
Reference
Hawkins et al.
1988;
Hawkins et al.,
1990
guppy,
Poedlia reticulata
(6-10 d old)
Rainbow trout
(fmgerlings),
Oncorliynchus mykiss
Rainbow trout
(juvenile),
Oncorliynclius mykiss
(10 mo)
Water;
dimethyl-
formamide
carrier.
Lab; static
BaP
209
2x6h, 1
week apart
oral
Lab
BaP
1,000 ppmper
feeding
12 and 18
months
ip injection
Lab
BaP
1 nig B(a)P in
0.4 ml PG
(I/month for 12
months)
18 months
(6 months
after final
injection)
Neoplastic lesions in
livers and other
tissues after 52 weeks
23%vsO%
(controls); 1 altered
foci, 5 adenoma, 4
with hepatocellular
carcinoma
Incidence of
neoplasms on liver
15%(1.0/liver)atl2
months
25%(7.7/liver)at 18
months
Incidence of
neoplasms in various
organs'"= 46% (x =
7.7 tumors/organ)
Studies carried out
longer because
tumorigenic response in
guppy is slower than in
medaka
MFO info also
available
0% at 6 months
0% on other organs
Organs examined =
gonads, swim bladder,
liver, spleen, head and
trunk kidneys,
pancreas, intestines,
and stomach
Hawkins et al,
1988;
Hawkins et al.
1990
Hendricks et
al., 1985
Hendricks et
al., 1985
F-l
-------
Species
Pacific herring
(embryos),
Clupt j pallasi
Mode
of
Exposure Method
seawater lab;
contaminated state
by contact
with oiled
gravel -
experiment 2;
more
weathered
Exposure
Cone
Associated
PAH with Effect
Field 0.41 nlL to
Mixture* 0.72 /u/L
Exposure
Time Toxic Effect(s): Tissue Cone
16 days - yolk sac edema 0.022 A
-------
Species
Calif, grunion
(embryos),
Leures, ties
tenuis
Calif, grunion
(embryos),
Leuresthes
tennis
Pacific herring
(embryos),
Clupca pattasi
Mode
of
Exposure Method PAH
water lab; BaP
static
water lab; BaP
static
seawater lab; Field
contaminated static Mixture*
by contact
with oiled
gravel -
experiment 1 ;
less weathered
Exposure
Cone
Associated Exposure
with Effect Time
measured: 15 days
5-24 f^g/L
(steady
state); 24-
361 ^g/L
(initial)
measured: 15 days
869 ppb
(initial);
steady-state
not reached
9.1^/L 16 days
Toxic Effects):
-retarded growth (14d)
-sporadic heart beat
-displaced head relative
to yolk-sac
-absence of
melanophores near
lateral lines
-absence of lens
formation
-lesions as larvae
(above)
-retarded growth (14d)
-lateral curvature mid-
body
-absent melanophores
-unused yolk sac
-lesions as larvae
(above)
-yolk sac edema
Tissue Cone
day 15:
0.92 to 10.48 ,ug/g
wet weight; 6.87 to
62.80- Mg/g (dry
weight)
day 15 - 19.98 Mg/g
wet weight; 112.03
Mg/g dry weight
13.7 Mg/g wet weight
Comments: Reference
-steady state W i nkler et al . ,
concentration 1983
reached in 4 to 10 days
steady-state
concentration never Winkler et al.,
reached 1983
Crude Oil characterized Carls et al., 1999
for PAHs only;
concentrations of
individual PAHs not
given
E-5
-------
Species
coho salmon,
(24 h Post
fertili ation),
Oncothynchus
'. kisutch
coho salmon,
(32 d post
fertilization),
Oncorhynchus
kisutdi
Calif, grunion
(embryos),
Leurestlies
tennis
Mode
of
Exposure Method
water; 0.5% lab;
DMSO static
cxposur
e then
flow-
through
water; 0.5% lab;
DMSO static
exposur
e then
flow-
through
water lab;
static
Exposure
Cone
Associated Exposure
PAH with Effect Time Toxic EffecUs):
BaP 25,000 Mg/L 24 h None
•
BaP 25,000 >g/L 24 h None
BaP measured: 15 days -reduction in % hatch
5 ^g/L -lateral folding of tail
(steady- -absence of caudal fin
state); folds
Tissue Cone
0.54 decreasing to
0. 15 nmol/mg protien
from 2 to 68 d post
fertilization
4.47 decreasing to
0.33 nmol/mg protien
from 2 to 68 d post
fertilization
day 15: 0.992 ppm
(wet weight); 6.872
ppm (dry weight)
Comments: Reference
Cone, of BaP in tissue Ostrander et al..
are not converted 1989
because wet weights
were not given; only
the mg protein/animal.
Can possibly borrow
weights from earlier
paper.
Cone, of BaP in tissue Ostrander et al.,
are not converted 1989
because wet weights
were not given; only
the mg protein/animal.
Can possibly borrow
weights from earlier
paper.
-steady state
concentration Winkler et al.,
reached in 4 to 10 days 1 983
(initial)
-hemorrhagic lesion or
congested vasculature in
caudal region
E-4
-------
Species
gizzard shad,
Doroscma
cepedi, mum
estuarine
clams,
Rangia cuneaia
estuarine
clams,
Rangia cuneata
coho salmon
(24 h Post
fertilization),
Oncorhynchus
kisutch
coho salmon,
(32 d post
fertilization),
Oncorhynchus
kisutch
Mode
of
Exposure
water and/or
sediment
ingestion
water; acetone
carrier
water; acetone
carrier
water; 0.5%
DMSO
water; 0.5%
DMSO
Method
lab;
static
lab;
static
lab;
static
lab;
static
exposur
e then
flow-
through
lab;
static
exposur
e then
flow-
through
Exposure
Cone
Associated Exposure
PAH with Effect Time Toxic Effcctts):
BaP 1.02,ug/g 22 days none
sediment
(initial);
0.63 //g/g
sediment
(mean of
days 4,8, and
15)
BaP 30.5,ug/L 24 h none
BaP 30.5 //g/L 24 h none
BaP 25,000 /ug/L 24 h None
BaP 25,OOO^g/L 24 h None
Tissue Cone Comments:
ligated fish: 0.010 -50 shad, 30 ligated; 20
A/g/g wet weight non-ligated, in 500 L
(n=4) H20 with 3. 15 kg
non- ligated: 0.012 sediment
Mg/g wet weight -no sig. decline in
(n= 14) sediment cone, after
day 4
-all other tissue cones.
BDL (n=26 ligated;
n=6 non- ligated)
7 .2 ,ug/g -majority of BaP
wet weight concentrated in the
viscera ('75 %)
-n=5
5 .7 /ug/g -majority of BaP
wet weight concentrated in the
viscera ("65%)
-n-8
Effects on hatching,
orientation, and
foraging only.
Effects on hatching,
orientation, and
foraging only.
Reference
Koloketa!., 1996
Neffand
Anderson, 1975
Neffand
Anderson, 1975
Ostrander et al.,
1988
Ostrander et al.,
1988
E-3
-------
Species
Sand sole
(embryos),
Psettit httys
rnelanosticlius
Flathead sole
(embryis),
Hippoglossoide
s elassodon
English sole
(embryos),
Parophrys
vetulus
gizzard shad,
Dorosoma
cepedianwn
Mode
of
Exposure
water;
static
water;
static
water
water via
treated
sediment
Exposure
Cone
Associated
Method PAH with Effect
lab BaP 0.1 uglL
measured;
range
(0.08-0.12)
lab BaP 4.2 /zg/L
bound to decreasing to
bovine <0.05 uglL
serum (DL)
albumin
lab BaP 2.1 ^g/L
measured
lab; BaP 1.38^g/g
static sediment
(initial);
0.74 Mg/g
sediment
(mean of
days 4,8 and
15)
Exposure
Time
through to
yolk-sac
absorption
(7 -10 d)
through to
yolk-sac
absorption
(7 -10 d)
through to
yolk-sac
absorption
(7 -10 d)
22 d
Toxic Effects): Tissue Cone
-overgrowth of tissues '2. 1 uglg
-arrested development wet weight
-twinning;
Effects only after 48 h,
i.e., during
organogenesis
-hatching success sig.
decrease
-nuclear pycnosis and
general disruption of •
neural and ocular
tissues
none
none BDL in all but 2 fish
on day 4 -
(0.001 and 0.0002
^g/g wet weight)
Comments:
effects only exhibited
in 5% of animals;
average hatching
success of controls only
57% versus 28% BaP-
treated
very low hatching
success In controls and
experimentals; 5.5 and
11.5%, respectively
.
-40 ligated shad in 250
LH1Owith4.15kg
sediment
-no sig. decline in
sediment cone.
after day 4.
Reference
Hose eta!., 1982
Hose et al., 1982
Hoseetal., 1982
Koloketal., 1996
E-2
-------
Appendix E. Teratogenic effects from laboratory exposure to PAHs.
Species
fathead minnow
(embryos),
Pimephdes
promelas
freshwater
topminnows,
Poeciliopsis
monacha
Poeciliopsis
lucida
English sole
(embryos),
Parophrys
vetulus
Rainbow trout
(embryos),
Oncorhynchus
nrykiss
Mode
of
Exposure
maternal
via water
water;
acetone carrier
maternal
via oral
aqueous from
BaP spiked to
sediment
Method
lab;
flow-
through
lab;
static
renewal
lab;
wild-
caught
lab;
static
renewal
(7-10d)
Exposure
Cone
Associated
PAH with Effect
Anthracen 6.66 ^g/L
e 11.6^g/L
BaP l.OOOAfg/L
nominal;
l,250pg/L
was acutely
lethal
BaP 8,000 ,ug/L
(8 mg/kg
force-fed)
BaP 0.21 jug/L
measured
Exposure
Time
6 wks
3 wks
24 h
followed by
6 mo. of
monitoring
-
through to
36 d
post-hatch
Toxic Effcct(s):
-yolk-sac malformations
-edema
-eye deformities
-increased AHH and
EROD activities
-malformation of tail
regions
-insufficient yolk-sac
-reduced fin-fold size
-reduced hatching
success
-nuclear pycnosis
-lack of body pigment
-insufficient yolk-sac
-abnormalities of eyes
-increased mortality (at
2.40 uglL in aqueous)
-muscle necrosis
-abnormal mitosis in
eyes and brains
Tissue Cone
8.8a ^g/g (eggs)
9.0 uglg
converted from
35.7 nmol/g
wet wt.
5 1.2 and 263
l*g/g (eggs) -
avg. = 157;
Tissue cone, from 80
mg/kg i.p. maternal
injection
1.93Mg/g(eggs),
12.34 Mg/g (alevins),
from exposure to 2.40
pg/L BaP
Comments: Reference
i
Effects on embryos Hall and Oris,
incubated with solar 1991
ultraviolet light
radiation
Implied effect - Goddard et al . ,
increased AHH and 1987
EROD activity
indicative of
carcinogenic and
teratogenic metabolites
formed during
metabolism of BaP by
MFC-system
-Eggs maintained 1 1 Hose et al., 1981
days until yolk-sac
absorbed; static.
-Incidence of effect 4
times greater than
controls (Chai-square
df=3.81)
Poor control survival Hannah etal.,
(52% mortality) 1982;
Hose etal., 1984
E-l
-------
-------
Spiked sediments from Suedel et al. (1993) were unlikely at equilibrium; i.e., organisms were tested al'ter only 18 to 24 hours after spiking.
D-5
-------
Common Name,
Scientific Name
Eohaustorius estuarius
Amphipod,
Eohaustorius estuarius
Amphipod,
Eohaustorius estuarius
Amphipod,
Eohaustorius estuarius
Amphipod,
Eohaustorius estuarius
Amphipod,
Eohaustorius estuarius
Amphipod,
Eoliaustorius estuarius
Amphipod,
Eohaustorius estuarius
Midge,
Chironomus teutons
Midge,
Chironomus teutons
Midge,
Chironomus teutons
Amphipod,
Diporeia sp.
Amphipod,
Diporeia so.
Chemical
acenapthene
phenanthrene
phenanthrene
phenanthrene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
pyrene
fluoranthene
Response
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
31dLC50
10 d LC50
Median
Response
Conc.A
(wR/poc)
1920
4210
3760
4060
3100
3930
3570
1590
1740
682
>9090
(147000)
> 23900
(29300)
£•
(wc/eoc)
489
593
593
593
704
704
704
704
704
704
694
704
Test-
Specific
ESGUPCVIn
(Unitless)
3.93
7.10
6.34
6.85
4.40
5.59
5.07
-
-
-
>34.0
PAH-
Specific
SMAVC GMAVP References*
4.82 - Swartzetal.,
Swartzetal.,
i
Swartzetal.,
6.75 - Swartzetal.,
DeWitt et a!.,
DeWittetal.,
5.00 5.46 DeWittetal.,
Suedel et al.,
Suedel etal.,
Suedel etal..
1991a
199 la
1991a
1991a
1989
1989
1989
1993
1993
1993
Landrum etal,, 1994
>34.0 >34.0 Driscoll et al., 1997a
A Bolded median response concentration (acute) values are the Oxy.^.,*.,, based on the water solubilities of the PAH (Mackay et al., 1992). For these tests the interstitial water concentration at
the median response concentration exceeded solubility. Therefore, solubilities are used instead of the acute value for further calculations.
B Test-specific ESGUs: Quotient of the median response concentration (^g/goc) and CQCf/M{fCvi (from Table 3-4),
c PAH-specific SMAV: Geometric mean of the test-specific ESGTUFCvi values from 10-d LC50 tests by species and PAH. Test-specific ESGTUFCVI values greater that solubility included only if
they are the sole 10-d LC50 for the species.
D GMAV: Geometric mean of the PAH-specific SMAVs for all species within a genus.
D-4
-------
Common Name,
Scientific Name
Amphipod,
Riiepoxynius abronius
Amphipod,
Rhepoxynius abronius
Amphipod,
R 'lepoxynius abronius
Amphipod,
Rhepoxynius abronius
Amphipod,
Rhepoxynius abronius
Amphipod,
Rhepoxynius abronius
Amphipod,
Rhepoxynius abronius
Amphipod,
Rhepoxynius abronius
Amphipod,
Rhepoxynius abronius
Amphipod,
Rhepoxynius abronius
Amphipod,
Riiepoxynius abronius
Amphipod,
Riiepoxynius abronius
Amphipod,
Rhepoxynius abronius
Amphipod,
Eoliaustorius estuarius
Amphipod,
Chemical
pyrene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
acenapthene
acenapthene
Response
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
lOdLCSO
10 d LC50
10 d LC50
10dLC50
Median
Response
Cone/
(l/E/COC)
2810
>4360
4410
3080 .
2230
3150
1890
2790
2320
1700
1030
2100
3310
1630
4180
(WR/EOC)
694
704
704
704
704
704
704
704
704
704
704
704
704
489
489
Test-
Specific
ESGUPCVln
(Unitless)
4.05
>6.19
6.26
4.38
3.17
4.50
2.68
3.96
3.30
2.41
1.47
2.98
4.70
. 3,33
8.55
PAH-
Specific
SMAVC GMAV1-1 References''
2.67 - Swartzetal.,
DeWittetal.,
DeWiltctal.,
i
DeWittetal.,
Swartzetal.,
DeWittetal.,
Swartz et al.,
De Witt et al.
Swartzetal.,
DeWittetal.,
Swartz et al . ,
Swartzetal.,
3.56 3:67 Swartzetal.,
Swartzetal.,
Swartzetal.,
1997
1992
1992
1992
1990
1992
1990
, 1992
1997
1989
1988
1990
1997
1991a
1991a
D-3
-------
Common Name,
Scientific Name
Amphipod,
Hyalella azteca
Amphipod,
Corophiuin spinicorne
Amphipod,
Cvropluum spinicorne
Amphipod,
Leptocheirus plumulosus
Amphipod,
Leptocheirus plumulosus
Amphipod,
Leptocheints plumulosus
Amphipod,
Leptocheirus plumulosus
Amphipod,
Leptocheirus pltamilosus
Amphipod,
Leptocheirus plumulosus
Amphipod,
Rliepoxynius abronius
Amphipod,
Rhepoxynius abronius
Amphipod,
Rliepoxynius abronius
Amphipod,
Rliepoxynius abronius
Amphipod,
Chemical
fluoranthene
fluoranthene
fluoranthene •
acenapthene
acenapthene
acenapthene
phenanthrene
phenanthrene
phenantlirene
acenapthene
acenapthenc
phenanthrene
phenanthrene
pyrene
Response
10 d LC50
. 10dLC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
Median
Response
Conc.A
(jUE/UOC)
• 5130
2830
4390
10900
23500
8450
6870
8080
8180
2310
2110
3080
2220
1220
(wB/COc)
704
704
704
489
489
489
593
593
593
489
489
593
593
694
Test-
Specific
ESGUPCViB
(Unitlcss)
7.29
4.02
6.23
22.3
48.1
17.3
11.59
13.63
13.8
4.72
4.31
5.19
3.74
1.76
PAH-
Specific
SMAV(: GMAV" References'"1
15.1 15.1 DeWittetal.,
Swartzetal.,
5.01 5.01 Swartzetal.,
Swartz et al.,
Swartzetal.,
26.4 - Swartzetal.,
Swartzetal.,
Swartz et al.,
13.0 18.5 Swartzetal.,
Swartzetal,,
4.51 - Swartzetal.,
Swartzetal.,
4.41 - Swartzetal.,
Swartzetal.,
1989
1990
1990
1991a
1991a
1991a
1991a
199 la
1991a
1997
1997
1997
1997
1997
Rliepoxynius abronius
D-2
-------
APPENDIX D. Comparison of PAH-specific equilibrium partitioning sediment guidelines (ESGs) derived from narcosis theory and the median response concentration of
benthic species for individual PAHs in spiked-sediment toxicity tests.
Common Name,
Scientific Name
Oligochaete,
Lumbriculus variegatus
01 gochaete,
Lumbriculus variegatus
Oligochaete,
Umnodrilus hoffmeisteri
Oligochaete,
Limnodrilus hoffmeisteri
Oligochaete,
Umnodrilus hoffmeisteri
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Amphipod,
Hyalella azteca
Amphipod,
Hyalella azteca
Amphipod,
Hyalella azteca
Amphipod,
Hyalella azteca
Amphipod,
Hyalella azteca
Chemical
pyrene
pyrene
phenanthrene
phenanthrene
pyrene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
Response
7 d LC50
7 d EC50-SA
10 d LC50
28 d EC25-R
28 d EC25-R
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
Median
Response
Cone/
(we/sbc)
>9090
(61100)
>9090
(51400)
> 34300
(42500)
5790
8440
2380
955
3260
> 23900
(37649)
1250
1480
500
22000
(^B/ROC)
694
694
593
593
694
704
704
704
704
704
704
704
704
Test-
Specific PAH-
ESGUrcv,D Specific
(Unitless) SMAVC GMAV" References6
>13.1 - - Kukkonen and Landrum, 1994
>13.1 - - Kukkonen and Landrum, 1994
>57.8 >57.8 >57.8 Lotufo and Fleeger, 1996
9.80 - - Lotufo and Fleeger, 1996
12.2 - - Lotufo and Fleeger, 1996
Suedel et a!., 1993
Suedeletal., 1993
Suedel et al., 1993
Driscolletal., 1997a
Suedeletal., 1993
Suedeletal., 1993
Suedeletal., 1993
31.3 - - Harkey et al., 1997
D-l
-------
-------
COMMON/SCIENTIFI LIFE-
CNAME STAGE" HABITAT"
Inland silverside, X W
Menidia beryllina
Inland silverside, J W
Menidia beryllina
l.iland silverside, J W
Menidia beryllina
Inland silverside, J W
Menidia beryllina
Atlantic silverside, A W
Menidia menidia
Winter flounder, J
PAH
TESTED LOG
(CAS ft K™,c •
acenaphthenc 4.01
(83-32-9)
acenaphthene 4.01
(83-32-9)
pyrene 4.92
(192-00-0)
fluoramhene 5.08
(206-44-0)
phenanthrene 4.57
(85-01-8)
fluoranthene 5.08
(206-44-0)
CONCEN-
METHOD" TRATION"
S U
R U
FT M • •
S U
FT M
S M
LC50/EC501'
(WK/U
2300
>3800
(5564)
>132
>260
108
>188
PAH
SPECIFIC
LC50/EC50" SMAV"
(wmoI/L) (ymoI/L)
14.9
>24.6 >19.2
> 0.653 > 0.653
>1.29 >1.29
0.606 0.606
> 0.929 > 0.929
Kow
NORMALIZED
PAH SPECIFIC SPECIES
SMAV1 SMAV1 GMAV*
(ymoI/e/vO (yinol/E/v) (wmol/^-v) REFERENCES
Home ct al.. 1983
>150 _ _ Thursby e( al., 1989a
1
>29.2 _ _ Champlin and Poucher, 1992c
>82.0 >65.8 _ Speharetal., 1999
12.6 12.6 28.8 Battelle Ocean Sciences, 1987
>59.2 >59.2 >59.2 Spehar eta!.. 1999
I .iff-SfflPfV A = flfllllt I = inVf*nilf* T. K InrVOA P = #»mV\T"wr> TT — 1ifA_Ot*n» rtr\A hoKUot lit-i1r«/A%t,»t V — lifo r.tnna umlrn^iim KM* K^UIfof lr,irt«rv»
e-stage and habitat unknown, X = life-stage
BHabitat: I = infauna, E — epibenthic, W = water column.
clog ATOW: Predicted using SPARC (Karickoff et al, 1991).
DMethod: S= static, R = renewal, FF= flow-tlirough.
E Concentration: U = unmeasured (nominal), M = chemical measured.
F Acute Values: 96 hour LC50 or EC50, except for Daphnia and Tanyiarsus which are 48 hours duration.
0 Bolded acute values are the water solubilities of the PAH (Mackay et al., 1992). For these tests the acute values exceeded solubility. Therefore, solubilities are used instead
of the acute value for further calculations.
11 PAH-specific SMAV: Geometric mean of the acute values by PAH and species.
1 PAH-specific SMAVs at a log ATOW = 1.0; calculated as antilog (log,0LC50 + 0.9451oglo/row)/1000 (see Equation 2-33).
J Species SMAV: Geometric mean of tfow-normalized SMAVs for a species across PAHs.
K GMAV: Geometric mean of SMAVs for all species within a genus.
L Not used in calculations.
C-15
-------
COMMON/SCIENTIFI
CNAME
Pink salmon,
Oticorhynclius gorbusdia
Pink salmon,
Oncorhynchus gorbuscha
I ink salmon,
Oncorhynchus gorbuscha
Pink salmon,
Oncorhynchtis gorbuscha
Pink salmon,
OncorhyncJuis gorbuscha
Sheepshead minnow,
Cyprinodon variegatus
Sheepshead minnow,
Cyprinodon variegatus
Sheepshead minnow,
Cyprinodon variegatus
Sheepshead minnow,
Cyprinodon variegatus
Sheepshead minnow,
Cyprinodon variegatus
Sheepshead minnow,
Cyprinodon variegatus
Sheepshead minnow,
Cyprinodon variegatus
LIFE-
STAGE*
Fry
Fry
Fry
Fry
Fry
J
J
A
J
J
J
J
HABITAT"
W
W
W
W
W
E,W
E,W
E.W
E,W
E.W
E.W
E,W
PAH
TESTED LOG
(CAS *> K™,c
naphthalene 3.36
(91-20-3)
naphthalene 3,36
(91-20-3)
naphthalene 3.36
(91-20-3)
naphtlialene 3.36
(91-20-3)
naphthalene 3.36
(91-20-3)
acenaphlhene 4.01
(83-32-9)
acenaphtliene 4.01
(83-32-9)
acenaphthene 4.01
(83-32-9)
phenanthrene 4.57
(85-01-8)
phenantlirene 4.57
(85-01-8)
pyrene 4.92
(129-00-0)
fluoranthene 5.08
(206-44-0)
CONCEN- LC50/EC50"
METHOD" TRATION6 (ws/L)
FT M 960
FT M 900
FT M 990
FT M 1010
FT M 890
S U 2200
R U >3800
(50000)
FT M 3100
R U >245
FT M 429.4
FT M > 132
(>640)
S U >260
(> 20000)
KOW
PAH NORMALIZED
SPECIFIC PAH SPECIFIC
LC50/EC5Q" SMAV" SMAV1
(wmol/L) (wmol/L) (wmol/e^-)
7.49
7.02
7.72
7.88
6.94 7.40 U.O
14.3
>25
20.1 20.1 124
>1.37
2.41 2.41 50.0
> 0.653 > 0.653 >29.2
>1.29
SPECIES
SMAV1 GMAVK
(ymol/e^) (wmol/e,.-) REFERENCF.S
Rice and Thomas, 1989
Rice and Thomas, 1989
i
Rice and Thomas, 1989
Rice and Thomas, 1989
11 .0 1 1 .0 Riee and Thomas, 1989
Heitmulleretal., 1981
Thursby eta!.. 1989a
Ward eta!., 1981
Battelle Ocean Sciences, 1987
Battellc Ocean Sciences, 1987
Cliamplin and Poucher, 1992b
Champlin aixf Poucher, 1992a;
Speharetal., 1999
Sheepshead minnow, J
Cyprinodon variegatus
E.W fluoranthene 5.08 S
(206-44-0)
(> 560000)
>1.29 >1.29 >82L
78.7 78.7 Heitmuller elal., 1981;U.S
EPA. 1978
C-14
-------
COMMON/SCJENT1FI LIFE-
C NAME STAGED
Enalis suckleyi
Grass shrimp, X
Palaemonetes pugio
Gt iss shrimp, X
PaMemonetcs pugio
Grass shrimp, L
Palaemonetes pugio
Grass shrimp, A
Palaemonetes pugio •
Grass shrimp, A
Palaemonetes pugio
Grass shrimp, J
Palaemonetes pugio
Sand shrimp, X
Crangon septenispinosus
American Lobster, L
Homarus americanus
Hermit crab, A
Paqurus longicarpus
Slipper limpet, L
Crepidula fornicata
Sea urchin, E
Arbacia puncialaia
Sea urchin. E
Arbacia punctalata
PAH
TESTED LOG
HABITAT" fCAS H) K_..,c
(91-20-3)
E.W naphthalene 3.36
(91-20-3)
E.W acenaphthene 4.01
(83-32-9)
E.W acenaphthene 4.01
(83-32-9)
E.W phenanthrene 4.57
(85-01-8)
E.W phenanthrene 4.57
(85-01-8)
E.W fluoranthene 5.08
(206-44-0)
E acenaphthene 4.01
(83-32-9)
fluoranthene 5.08
(206-44-0)
E phenanthrene 4.57
(85-01-8)
W acenaphthene 4.01
(83-32-9)
W acenaphthene 4.01
(83-32-9)
W fluoramhene 5.08
(206-44-0)
PAH NORMALIZED
SPECIFIC PAH SPECIFIC
CONCEN- LC50/EC50" LC50/EC50P SMAV" SMAV1
METHOD" TRATION" (uitlL) (umol/L) fwmol/U <«mol/e~.)
S M 2350 18.3 18.3 27.2
S U 676.8 4.39
R U 1697 11.0 6.95 43.0
R U 200.8 1.127
FT M 145.4 0.816 0.816 17.0
S U 142 0.702 0.702 44.7
S U 245 1.59 1.59 4.80
R U >260 1.29 1.29 81.9
(317)
FT M 163.7 0.918 0.918 19.2
R U 3436 22.3 22.3 138
S U >3800 >24.6 >24.6 >152
(8163)
S U >260 >1.3 >1.3 >82
(20000)
SPEQIHS
SMAV1 GMAVK
(wmol/jLv) 117 >117 Spehar etal., 1999
1987
C-13
-------
COMMON/SCIENT1FI LIFE-
C NAME STAGE*
Isopod J
Excirolana
\wicouverensis
\mphipod, J
. \mpelisca abdiia
Amphipod, J
Ampelisca abdita
A.mphipod, ' A
Leptocheirus plumulosus
Amphipod, A
Leptocheirus pliunulosus
Amphipod, J
Leptocheirus plumulosus
Amphipod, X
Leptocheirus plumulosus
Amphipod, J
Rhepoxyniiu abronius
Amphipod, . J
Eohaustorius estuarius
Amphipod, J
Crandidierella japonica
Amphipod, J
Corophium insidiosum
Amphipod, J
Emerita analpga
Kelp shrimp X
PAH
TESTED
HABITAT" (CAS #>
I,E fluoranthene
(206-44-0)
1 acenaphthene
(83-32-9)
I fluoranthene
(206-44-0)
E,I acenaphthene
(83-32-9)
E,I phenanthrene
(85-01-8)
E,I pyrene
(129-00-0)
E,I fluoranthene
(206-44-0)
1 fluoranthene
(206-44-0)
I fluoranthene
(206-44-0)
1 tluoranthene
(206-44-0)
I fluoranthene
(206-44-0)
I,E fluoranthene
(206-44-0)
W naphthalene
LOG CONCEN- LCSO/ECSO"
K™c METHOD" TRATIONU (*n>./L>
5.08 . R M >70
4.01 R U 1125
5.08 S U 67
4.01 FT M 589.4
4.57 FT M 198.4
4.92 FT M 66.49
5.08 R M 51
5.08 R M 63
5.08 R M >70
5.08 R M 27
5.08 R M 54
5.08 R M 74
3.36 FT M 1390
LC50/EC50"
(witol/L)
>0.346
7.30
0.33
3.82
1.11
0.329
0.252
0.311
> 0.346
0.133
0.267
0.366 .
10.8
PAH
SPECIFIC
SMAV"
> 0.346
7.30
0,33
3.82
1.11
0.329
0.252
0.311
> 0.346
. 0.133
0.267
0.366
10.8
KOW
NORMALIZED
PAH SPECIFIC
SMAV1
>22.1
45.1
21.1
23.6
23.2
14.7
16.1
19.9
>22.1
8.5
17.0
23.3
16.1
SPECIES
SMAV' GMAV*
(umol/Krtr") (umol/e~.1 REFERENCES
>22.1 >22.1 Boese etal., 1997
i
Thursby etal., 1989a
30.8 30.8 Spehar etal., 1999
Swam, 1991a
Swartz, 1991a
Champlin and Poucher , I992c
19.0 19.0 Boese et al., 1997
19.9 19.9 Boese et al., 1997
>22.1 >22.1 Boese etal., 1997
8,5 8.5 Boese etal., 1997
17.0 17.0 Boese et al., 1997
23.3 23.3 Boese eta)., 1997
16.1 16.1 Rice and Thomas, 1989
C-12
-------
COMMON/SCIENTIFI LIFE-
CNAME STAGE* HASH' AT8
Mysid, J E
Americamysis baltia
Mysid, J E
A •iiericamysis baliia
Mysid, J E
Americamysis baliia
M;y^id, J E
Americamysis bahia
Mysid, J E
Americamysis bafiia
Mysid, J E
Americamysis bahia
Mysid, J E
Americamysis bahia
Mysid, J E
Americamysis bahia
Mysid, J E
Americamysis bahia
Mysid, J E
Americamysis balua
Mysid, J E
Americamysis bahia
Mysid, X E
Neomysis americana
Mysid, X E
Neomysis americana
KOW
PAH NORMALIZED
PAH SPECIFIC PAH SPECIFIC
TESTED LOO CONCEN- LC50/EC50P LC50/EC50' SMAV" SMAV1
(CAS //) K^c METHOD0 TRATION8 Oic/L) fumot/L) (unrnl/L) (wmol/av)
acenaphthene 4.01 FT M 460 2.98
(83-32-9) . " . "
acenaphthene 4.01 FT M 190 1,23
(83-32-9)
acenaphthene 4.01 FT M 466.1 3.02
(83-32-9)
acenaphthene 4.01 FT M 271.9 1.76 2,10 13.0
(83-32-9)
phenanthrene 4.57 FT M 27.1 0.152
(85-01-8)
phenanthrene 4.57 FT M 17,7 0.099 0.123 2.60
(85-01-8)
pyrene 4.92 FT M 28.28 0.140 0,140 6.30
(129-00-0)
fluoranthene 5.08 S U 31 0.153
(206-44-0)
fluoranthene 5.08 S U 40 0.198
(206-44-0)
fluoranthene 5.08 Ff M 30.53 0.151
(206-44-0)
fluoranthene 5.08 FT M 87 0.430 0.255 16.2
(206-44-0)
naphthalene 3.36 S M 1250 9.75
(91-20-3)
naphthalene 3.36 S M 1420 11,1 10.4 15.4
(91-20-3)
SPECIES
SMAV' GMAV*
(^mol/En,-) (wmol/av) REFERENCES
Thursbyetal., 1989b
EG&G Bionomics, 1982
i
Home eta!,, 1983;Thursby,
199U
Home et al., 1983;Thursby,
1991a
Kuhn and Lussier, 1987
Battelle Ocean Sciences, 1987
Champlin and Poucher, 1992c
Spehar et al., 1999
U.S. EPA, 1978
Champlin and Poucher, 1992b;
Spehar ctal., 1999
7.66 7.66 EG&G Bionomics, 1978
Hargreaves et al., 1982
15.4 15.4 Hargreaves etal., 1982
C-ll
-------
COMMON/SCIENTIFI LIFE-
C NAME STAGE*
Blue mussel, A
Mytihts edulis
Pacific oyster, E/L
( 'rassostrea gigas
Coot clam, J
Mulinia latcralis
Coot clam. 1
Mulinia laieralis
Soft-shell clam, A
Mya arenaria
Calanoid copepod A
Eurytemora qffinis
Calanoid copepod A
Eurytemora qffinis
Calanoid .copepod A
Eurytemora qffinis
Calanoid copepod A
Eurytemora qffinis
Mysid, I
Americamysis bahia
Mysid, I
Americamysis bahia
Mysid, J
Americamysis bahia
HABITAT8
E,W
W
E
E
I
X
X
X
X
E
E
E
PAH
TESTED LOG
(CAS /C) K™c
phenantlirene 4.57
(85-01-8)
naphthalene 3.36
(91-20-3)
pyrene 4.92
(129-00-0)
fluoranthene 5.08
(206-44-0)
phenanthrene 4.57
(85-01-8)
naphthalene 3.36
(91-20-3)
2-methyl 3.86
naphtlialene
(91-57-6)
2,6-dimediyl 4.37
naphthalene
(581-42-0)
2,3,5- 4.86
trimethyl
naphthalene
(2245-38-7)
acenaphthene 4.01
(83-32-9)
acenaphthene 4.01
(83-32-9)
acenaphthene 4.01
(83-32-9)
"ow
PAH NORMALIZED
SPECIFIC PAH SPECIFIC
CONCEN- LC50/IJC50" LC50/EC50' SMAV" SMAV1
METHOD0 TRATJON0 (wc/L) taol/L) (wmol/L) (wnol/enr)
R M >245 >1.37 >1.37 >28.7
S U > 31000 >242 >242 >359
(199000) .
FT M >132 >0.653 > 0.653 >29.2
(>240)
S U >260 >1.29 >1.29 >82.0
(10710)
R M >245 >1.37 >U7 >28.7
S U 3798 22.6 22.6 33.5
S U 1499 7.74 7.74 34.2
S M 852 3.9 3.9 52.0
S M 31C 1.3 1.3 50.0
S U 970 6.29
S M 160 1.04
R U. 1190 7.72 .
SPECIES
SMAV1 GMAV"
(wmol/E,,) (wmol/R,,) REFERENCES
>28.7 >28.7 Battelle Ocean Sciences,
>359 , >359 U.S. EPA, 1980
Champlin and Poucher,
>48.9 >48.9 Spehar etal., 1999
>28.7 >28.7 Battelle Ocean Sciences,
Ott, et al.. 1978
Ott, etal., 1978
Ott, et al., 1978
41.5 41.5 On,- et al.. 1978
1987
1992c
1987
U.S. EPA, 1978;\Vardetal..
1981
EG&G Bionomics, 1982
. _ Thursby etal., 1989a
C-1.0
-------
COMMON/SCIENTIF1 LIFE-
C NAME STAGE*
Bluegill, J
Lepontis macrocliirus
Bluegill, J
Lcpomis macrocliiriu
South african clawed frog L
Xenopus laevis
South african clawed frog L
Xenopus laevis
SALTWATER
Annelid worm, J
Neanlhes
arenaceodeniata
Annelid worm, X
Neanthes
arenaceodentata
Annelid worm, J
Neanlhes
arenaceodentata
Annelid worm,
Neanlhes A
arenaceodeniata
Annelid worm, J
Neanlhes
arenaceodeniata
Annelid worm, J
Neanlhes
arenaceodentata
Archiannelid, J
Dinophilus gyrodliatus
Mud snail, A
Nassarius obsolenis
PAH
TESTED LOG
HABITAT" (CAS #1 K~,,,c
W fluoranthene 5.08
(206-44-0)
W fluoramhene 5.08
(206-44-0)
W naphthalene 3.36
(91-20-3)
W naphthalene 3.36
(91-20-3)
I naphthalene 3.36
(91-20-3)
I acenaphthene 4.01
(83-32-9)
I acenaphthene 4.01
(83-32-9)
I phenanthrene
(85-01-8) 4.57
I fluoranthene 5.08
(206-44-0)
I fluoranthene 5.08
(206-44-0)
1 phenamhrene 4.57
(85-01-8)
I,E phenanthrene 4.57
(85-01-8)
KOW
PAH NORMALIZED
SPECIFIC PAH SPECIFIC
CONCEN- LC50/EC50" LCSO/ECSO11 SMAV" SMAV1
METHOD" TRATION" («e/U (umol/L) (umol/L) (umol/E~)
S U >260 >1.3
(4000)
FT M 44 0.218 0.218 13.9
FT M 2100 16.38
FT M 2100 16.38 16.38 24.3
S U 3800 29.6 29.6 44.0
S U 3600 23.3
R U >3800 >24.6 23.3 144
(16440)
S U 600 3.37 3.37 70.0
S U >260 >1.29
(500)
S U >260 >1.29 >1.29 >82L
(20000)
R U 185.40 1.04 1.04 21.7
R M >245 >1.37 >1.37 >28.7
SPECIES
SMAV1 GMAVK
(umol/e,^) fumol/B«-) REFERENCES
Buccafusco el al., 1981; EPA,
1978
34.0 34.0 Speharetal., 1999
i
Edmisten and Bantle, 1982
24.3 24.3 Edmisten and Bantle, 1982
Rossi and Neff. 1978
Horneetal., 1983
Thursby etal,, 1989a
Rossi and Neff. 1978
Rossi and Neff, 1978
76.3 76.3 Speharetal., 1999
21.7 21.7 Battelle Ocean Sciences, 1987
>28.7 >28.7 Battelle Ocean Sciences, 1987
C-9
-------
COMMON/SC1ENTIF1 LIFE-
C NAME STAGE*
Pimcphales promelas
Fathead minnow, J
Pimephales promelas
'athead minnow, X
Pimephales promelas
Fathead minnow, 3
Pimephales promelas
Fathead minnow, I
Pimephales promelas
Fathead minnow, J
Pimephales promelas
Fathead minnow, A
Pimephales promelas
Fathead minnow, I
Pimephales promelas
Channel catfish, J
laalurus punctatus
Channel catfish, J
Ictaturus punctatus
BluegiU, I
Lepomis macrocfiirus
Bluegill, X
Lepomis macrochirus
Bluegill, J
Lepomis macrochirus
PAH
TESTED LOO
HABITAT" (CAS ft) K™c
(83-32-9)
W acenaphthene 4.01
(83-32-9)
W fluorene 4.21
(86-73-7)
W phenanthrene 4.57
(85-01-8)
W fluoranthene 5.08
(206-44-0)
W fluorantliene 5.08
(206-44-0)
W fluoranthene 5.08
(206-44-0)
W fluoranthene 5.08
(206-44-0)
E acenaphthene 4.01
(83-32-9)
E fluoranthene 5,08
(206-44-0)
W acenaphthene 4.01
(83-32-9)
W fluorene 4.21
(86-73-7)
W phenanthrene 4.57
(85-01-8)
KOW
PAH NORMALIZED
SPECIFIC PAH SPECIFIC
CONCEN- LC50/EC501' LC50/EC50f SMAV" SMAV1
METHOD" TRATIONB fuc/L) (wmol/U (umoUU (wmol/n™.)
FT. M 1600 10 7.71 48.0
S U >1900 >11.4 >11.4 >108L
(100000)
S . M >1100 >6.17 >6.17 >129L
O1150)
S M 95 0.470
S M 7.71 0.0381
FT U >260 >1.29
(>1000)
FT M 69 0.34 0.34 22.0
FT M 1720 11.2 11.2 69.0
S M 37.40 0.185 0,185 12.0
S U 1700 11.0 11.0 68
S U 910 5.47 5.47 51.8
Ff M 234 1.31 ' 1.31 27.4
SPECIES
SMAV1 GMAVK
(umol/kv) (umol/e^) REFERENCES
Holcombeetal., 1983
t
Finger et al., 1985
. U.S. EPA, 1978
Home and Oblad, 1983
Gendusa, 1990
Birgeetal., 1982
68.3 68.3 Spehar et al., 1999
Holcombeetal., 1983
28.8 28.8 Gendusa, 1990
Buccafuscoetal., 1981
Finger etal., 1985
Call et at., 1980
C-8
-------
COMMON/SC1ENTIFI LIFE-
CNAME STAGE* HABITAT8
Fathead minnow, J W
Pimephales promelas
Fathead minriow, J W
P 'mephales promelas
Fathead minnow, X W
Pimepltales promelas
Fathead minnow, J W
Pimephales promelas
Fathead minnow, J W
Pimephales promelas
Fatliead minnow, J W
Pimephates promelas
Fathead minnow, J W
Pimephales promelas
Fathead minnow, J W
Pimephales promelas
Fathead minnow, J W
Pimepliales promelas
Fathead minnow, A W
Pimephales promelas
Fatliead minnow, J W
Pimephales promelas
Fathead minnow, J W
Pimephales promelas
Fatliead minnow, J W
PAH
TESTED LOG
(CAS « K™c
naphthalene 3.36
(91-20-3)
naphthalene 3.36
(91-20-3)
naphthalene 3.36
(91-20-3)
naphthalene 3.36
(91-20-3)
naphthalene 3.36
(91-20-3)
naphthalene 3.36
(91-20-3)
1-methyl 3.84
naphthalene
(90-12-0)
acenaphthene 4.01
(83-32-9)
acenaphthcne 4.01
(83-32-9)
acenaphthene 4.01
(83-32-9)
acenaphthene 4.01
(83-32-9)
acenaphthene 4.01
(83-32-9)
acenaplithene 4.01
Kow
PAH NORMALIZED
SPECIFIC PAH SPECIFIC
CONCEN- LC50/EC50r LC50/EC50r SMAV" SMAV1
METHOD" TRATION* (we/L) (wnol/L) (umol/U (wmol/c~->
S M 1990 15.5
FT M 7900 61.6
FT M 4900 38.2
FT M 6140 47.9
Ft M 8900 69.4
FT M 6080 47.4 51.8 76.8
S U 9000 63.4 63.4 268
S M 3100 20
S M 1500 9.7
R U 3700 24
FF M 1730 11.2
FT M 608 3.94 '
FT M >1400 >9.1
C-7
SPECIES
SMAV' GMAV"
(wmol/B™.) (wmol/B,,) REFERENCES
Millemannetal., 1984
DeGraeveetal., 1982
I
DeGraeve etat., 1980
Geiger et al., 1985
DeGraeveetal.. 1980
Holcombe et al., 1984
Mattson et al., 1976
_ Marine Bioassay Lab., 1981
EG&G Bionomics, 1982
Academy of Natural Sci., 1981
Geiger etal., 1985
Cairns and Nebeker, 1982
EG&G Bionomics, 1982
-------
COMMON/SCIENTIFI
C NAME
Rainbow trout
Onoorhyndiiu mykiss
Rainbow trout
Oi corhynchus mykiss
Rainbow trout
Oncorhynchus mykiss
Rainbow trout
OniVfftynchtu mykiss
Rainbow trout
Oncorhynchus mykiss
Rainbow trout
Oncorhynchus mykiss
Rainbow trout
Oncorhynchus mykiss
Rainbow trout
Oncorhynchus mykiss
Rainbow trout
Oncorhynchus mykiss
Rainbow trout
Oncorhynchus myldss
Rainbow trout
Oncorhynchus mykiss
Rainbow trout
Oncorhynchus myldss
Drown trout,
Salmo trutta
LIFE-
STAGE*
preSU
preSU
preSU
J
X
J
J
preSU
L
J
X
J
J
HABITAT"
I
I
I
W
W
W
W
I
W
W
W
W
W
PAH
TESTED LOG
(CAS /H K^c
naphthalene 3.36
(91-20-3)
naphthalene 3.30
(91-20-3)
naphthalene 3.36
(91-20-3)
naphthalene 3.36
(91-20-3)
naphthalene 3.36
(91-20-3)
acenaphthene 4.01
(83-32-9)
fluorene 4.21
(86-73-7)
1.3-dimethyl 4.37
naphthalene
(575-41-7)
phenantlirene 4.57
(85-01-8)
phenanthrene 4.57
(85-01-8)
fluoranthene 5.08
(206-44-0)
fluoranthene 5.08
(206-44-0)
acenaphthene 4.01
(83-32-9)
"OW
PAH NORMALIZED
SPECIFIC PAH SPECIFIC
CONCEN- LC50/EC501' LC50/EC50F SMAV" SMAV1
METHOD0 TRAT1ON8 («e/U fomot/U (wmoI/U (wmol/e,^
S U 2600 20.3
S U 4400 34.3
S U • 5500 42.9
FT M 1COO 12.5
FT M 2300 17.9 15.0 22.2
FT M 670 4.34 4.34 26.9
S U 820 4.93 4.93 46.7
S U 1700 10.9 14.0 188L
s u >noo >c.2
(3200)
FT M 375 2.10 2.10 43.9
S M 187 0.925
FT M 26.0 0.129 0.129 8.19
Ft M 580 3.76 3.76 23.3
SPECIES
SMAV1 GMAV*
(Aimol/E«-) r«mol/R«0 REFERENCES
Edsall.C.C, 1991
i _ Edsall, C.C., 1991
Edsall. C.C.. 1991
DcGraeve et al., 1982
DeGraeve et al., 1980
Holcombeetal., 1983
Finger et al., 1985
Edsall, C.C., 1991
Edsall, C.C., 1991
Call etal., 1986
Home and Oblad, 1983
25.1 40.4 Spehareial., 1999
23.3 23.3 Holcombeetal., 1983
C-6
-------
COMMON/SCmNTIFI
C NAME
Stonefly,
Peltoperla maria
MHge,
Cli ronomus tentans
Midge, '
Chironomus tentans
Mids.e,
Qiirononuis tentans
Midge,
Chironomus riparius
Midge,
Paraianytarsus sp.
Midge,
Paraianytarsus sp.
Midge
Tanytarstu dissimilis
Midge
Tanytarsus dissimilis
Coho salmon
Oncorhyndtus kistadi
Coho salmon
Oncorhyndws kisutdi
Rainbow trout
Oncorhyndius mykiss
Rainbow trout
Oncorlwndms mykiss
LIFE-
STAGE*
X
L
L
L
L
X
X
L
L
E
F
preSU
preSU
HABITAT"
E
I
I
I
1
E
E
I
I
I
W
I
I
PAH
TESTED LOO
(CAS It) K™c
fluoranthene 5.08
(206-44-0)
naphthalene 3.36
(91-20-3)
phenanthrene 4.57
(85-01-8)
fluoranthene 5.08
(206-44-0)
fluorene 4.21
(86-73-7)
acenaphthene 4.01
(83-32-9)
acenaphthene 4.01
(83-32-9)
naphthalene 3.36
(91-20-3)
naphthalene 3.36
(91-20-3)
naphthalene 3.36
(91-20-3)
naphthalene 3.36
(91-20-3)
naphthalene 3.36
(91-20-3)
naphthalene 3.36
(91-20-3)
KOW
PAH NORMALIZED
SPECIFIC PAH SPECIFIC
CONCEN- LC50/EC501' LCSO/EC50r SMAV" SMAV1
METHOD" TRAT10N" (uB/L) (timol/L) (wtnol/L) (wmol/o~.)
S U 135 0.667 0.667 42.5
S M 2810 21.9 21.9 32.5
S M 490 2.75 2.75 57.0
S M >250 >1.24 >1.24 >79L
S U >1900 > 11.42 > 11.42 >108
(2350)
S M 2000 13.0
S M 2090 13.6 13.3 82
S U 20700 162
S U 12600 98.31 126 187
R M > 11800 >92.1
R . M 5600 43.7 43.7 65.0
S U 1800 14.0
S U 6100 47.6
SPECIES
SMAV' GMAV*
(wmol/H,,,.) (;/mol/B/,r) REFERENCliS
20.2 20.2 Home and Oblad, 1983
i _ Millemannctal., 1984
_ _ Millemann et a!., 1984
43.0 _ Suedel ad Rodgers, 1996
>108 >68.2 Finger eta!., 1985
Northwestern Aquatic Science
Inc., 1982
82 82 Northwestern Aquatic Science
Inc., 1982
Darville and Wilhm, 1984
187 187 Darville and Wilhm, 1984
Korn and Rice, 1981
65.0 _ Korn and Rice, 1981
Edsall, C.C., 1991
Edsall. C.C., 1991
C-5
-------
COMMON/SCIENTIFI
CNAME
Cladoceran,
Daphnia pulex
Cladoceran,
Daphnia pulex
Cladoceran,
Daphnia pulex
ClivJoceran,
Daphnia pulex
Amphipod,
Gammarus minus
Amphipod,
Gammarus minus
Amphipod,
Gammarus
pseudolimnaeus
Amphipod,
Gammarus
pseudolimnaeus
Amphipod,
Gammarus
pseudolimnaeus
Amphipod,
HyaleUa aaeca
Dragonfly,
Ophiogomphus sp.
Stonefly,
Peltoperla maria
PAH
LIFE- TESTED LOO
STAGE* HABITAT9 {CAS I) 1C,.,C
X W phenanthrene 4.57
(85-01-8)
X W phenanmrene 4.57
(85-01-8)
X W phenanthrene 4.57
(85-01-8)
X W 2-methyI 4.99
anthracene
(613-12-7)
X E acenaphthene 4.01
(83-32-9)
A E fluoranthene 5.08
(206-44-0)
X E fluorene 4.21
(86-73-7)
X ' E phenanthrene 4.57
(85-01-8)
A E fluoranthene 5.08
(206-44-0)
J E fluoranthene 5.08
(206-44-0)
N E fluoranthene. 5.08
(206-44-0)
X E acenaphdiene 4.01
(83-32-9)
PAH NORMALIZED
SPECIFIC PAH SPECIFIC SPECIES
CONCEN- LC50/EC50P LC50/EC50r SMAV" SMAV1 SMAV1
METHOD0 TRAT10NE (wu/L)_ ... (wmol/L) (wmol/L) (wmol/iw) 0,mol/E~-)
S U >HOO >6.17
(>U50)
S U 350 1.96
S M - 100 0.56 1.66 34,6
S U >30 >0.156 >0.156 >8.1L 30.2
(96)
S U 460 '3.0 3.0 18.4
S U 32 0.16 0.16 10.1 13.6
S U 600 3.61 3.61 34.2
FT M 126 0.707 0.707 14.8
FT M 43 0.213 0.213 13.5 19.0
FT M 44 0.218 0.218 13.9 13.9
FT M >178 >0.880 >0.880 >56 >56
S U 240 1.6 1.6 9.6
OMAVK
(wmol/p,,.) REFERENCES
Gciger and Buikcma, 1981, 1982
Smith etal., 1988
i
Truccoetal., 1983
27.6 Smith etal., 1988
Home et al., 1983
Home and Oblad, 1983
Finger etal., 1985
Call et al., 1986
16.1 Spehar eta!., 1999
13.9 Spehar etal., 1999
>56 Spehar etal., 1999
Home etal., 1983
C-4
-------
COMMON/SCIENTIFI LIFE-
CNAME STAGBA HABITAT"
Cladoceran, J W
Daphnia magna
Cladoceran, J W
Dai hnia magna
Cladoceran, J W
Daphnia magna
Cladoceran, J W
Daphnia magna
*
Cladoceran, J W
Daphnia magna
Cladoceran, X W
Daphnia magna
Cladoceran, X W
Daphnia pitlex
Cladoceran, X W
Daplmia pulex
Cladoceran, X W
Daplmia putcx
Cladoceran, X W
Daphnia pulex
Cladoceran, X W
Daphnia pulex
Cladoceran, Neonate W
Daphnia pitlex
PAH
TESTED LOO
(CAS/f) K_c
pyrene 4.92
(129-00-0)
9-methyl 5.01
anthracene
(779-02-2)
fluoranthene 5.08
(206-44-0)
fluoranthene 5.08
(206-44-0)
fluoranthene 5.08
(206-44-0)
fluoranthene 5.08
(206-44-0)
naphthalene 3.36
(91-20-3)
fluorene 4.21
(86-73-7)
1,3-dimethyl 4.37
naphthalene
(575-41-7)
2,6-dimethyl 4.37
naphthalene
(581-42-0)
anthracene 4.53
(120-12-7)
phenanthrene 4.57
(85-01-8)
KQW
PAH NORMALIZED
SPECIFIC PAH SPECIFIC
CONCEN- LCSO/ECSOF LC50/EC50" SMAV" SMAV1
METHOD0 TRATION" fu«/D (wn.ol/L) (umolfU tumM^)
S U 90.9 0.45 0.45 20.1
S U 124,8 0,65 0.65 34.9
S U >260 >1.29
(320000)
S M 45 0.222
R M 117 0.578
S M 105.7 0.523 0.407 25.9
S U 4663 36.4 36.4 54.0
S U 212 1.27 1.27 12.1
S U 767 4.92 4.92 66
S U 193 1.24 1.24 16.8
S U >45 >0.25 >0.25 >4.9L
(754)
S U 734 4.12 '
SPECIES
SMAV' GMAV*
(wmol/e^) (wmol/a,,.) REFERENCES
Abernethy etal., 1986
Abernethy eta!., 1986
i
LeBIanc. 1980a
Oris etal., 1991
Spelur et al., 1999
25.2 Suedel ad Rodgers,
Smith etal., 1988
Smith etal., 1988
Smith etal., 1988
Smith etal., 1988
Smith etal., 1988
Passino and Smith,
1996
1987
C-3
-------
COMMON/SCtENTlFI
C NAME
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Danhnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
LIFE-
STAGE* HABITAT9
J W
X W
X W
X W
X W
X W
X W
J W
X W
, Neonate W
Neonate W
Neonate W
X W
PAH
TESTED LOG CONCEN-
(CAS #) K™,c METHOD" TRAT10N*
2-methyl 3.86 S U
naphthalene
(91-57-6)
acenaphthene 4.01 S U
(83-32-9)
acenaphthene 4.01 S U
(83-32-9)
acenaphthene 4.01 S M
(83-32-9)
acenaphthene 4.01 S M
(83-32-9)
acenaphthene 4.01 FT M
(83-32-9)
fluorene 4.21 S U
(86-73-7)
phenanthrene 4.57 S U
(85-01-8)
phenanthrene 4.57 S U
(85-01-8)
phenanthrene 4.57 S M
(85-01-8)
phenanthrene 4.57 S.R M
(85-01-8)
phenanthrene 4.57 FT M
• (85-01-8)
phenantlirene 4.57 FT M
(85-01-8)
KOW
PAH NORMALIZED
SPECIFIC PAH SPECIFIC SPECIES
LC50/EC50" LC50/EC50r SMAV" SMAV1 SMAV1
(KE/L) (nmol/L) (umol/LI (umol/av) (//mol/Enr)
1491 10.5 10.5 46.3
3450 22.4
->3800 ' >24.6
(41000)
320 2.08
1300 8.43
120 0.778 0.778 4.80
430 2.59 2.59 24.5
207 1.16
843 4.73
700 3.93
212 1.19 _
230 1.29
117 0.656 0.920 19.2
GMAVK
(«mol/e~-) REFERENCES
Abcrnethy etal., 1986
Randall and Knopp, 1980
LcBlanc, 1980s
EG&G Bionomics, 1982
EG&G Bionomics, 1982
EG&G Bionomics, 1982
Finger etal., 1985
Abcrnethy etal., 1986
Eastmond etal., 1984
Millemanneial., 1984
Brooke, 1994
Brooke, 1993
Call etal., 1986
C-2
-------
Appendix C. Summary of data on the acute toxicity of PAHs to freshwater and saltwater species and the derivation of genus mean acute values.
COMMON/SCIENTIFI
CNAME
FRESHWATER
Hydra,
Hydra americana
Hyara,
Hydra sp.
Annelid,
Lumbriculus variegatus
Annelid,
Lumbriculus variegatus
Snail,
Mudalia potosensis
Snail,
Aplexa hypnorum
Snail,
Physa heterostropha
Snail,
Physella virgata
Cladoceran,
Daplmia magna
Cladoceran,
Daplmia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daplmia magna
PAH
LIFE- TESTED LOG
STAGE* HABITAT" (CAS ff) Knw419 >2.35 >2.35 >49.0
FT M >178 >0.880 >0.880. >56 >52.4
S U >1900° >1M >11.4 >108 >108
(5600)
FT M >2040 >13.2 >13.2 >81.8 >81.8
S U 137 0.677 0.677 43.2 43.2
FT M >178 > 0.880 > 0.880 >56 >56
S U 8570 66.9
S U 4723 36.9
S M 2160 16.9 34.6 51.0
S U 1'420 9.99 • 9.99 42.2
GMAVK
(Hmol/fcv) REFERENCES
Speharetal., 1999
i
15.5 Call etal., 1986
Call etal.. 1986
>52.4 Speharetal., 1999
>108 Finger etal., 1985
>81.8 Holcombe etal., 1983
43.2 Home and Oblad, 1983
>56 Speharetal., 1999
U.S. EPA, 1978
Abernetliy etal., 1986
Milleraannetal., 1984
Abernethy etal., 1986
C-l
-------
-------
Chemical _ CASA Class6 Kowc MWD MVE SF
l-tridecanol* 112709 ao 5.75 200.36 224 0.0000793
decane* 124185 aJ 6.56 142.28 229 0.000000300
*Chemical is not included: LC50>S.
ACAS= Chemical abstract number
"Class: ao=alcohol, ar=aroraatic, ha=halogenated, et=ether, al=aliphatic, fce=ketone, pah=PAH
DMW=molecular weight (gm/mol);
EV=molar volume (cm3/mol);
FS= aqueous solubility(mol/L)
B-7
-------
Chemical
acenaphthene
2,5-dimethyl-2,4-hexadiene
methyl cyclohexane
1 ,2,4,5-tetramethylbenzene
hexane
1 ,3-diethylbenzene
1-decanol
p-tert-butyltoluene
diphenylether
amylbenzene
phenanthrene
1 ,2.4,5-tctrachlorobenzene
1 ,2,3,4-tetrachlorobenzene
1 ,2,3,5-tetrachlorobenzene
1-undecanol
pyretic
9-raethylanthracene
fluoranthene
1-dodecanol
CASA
83329
764136
108872
95932
110543
141935
112301
98511
101848
538681
85018
95943
634662
634902
112425
129000
779022
206440
112538
Class6
pah
al
al
ar
al
ar
ao
ar
et
ar
pah
ar.ha
ar.ha
ar.ha
ao
pah
pah
pah
ao
•^ow
4.01
4.10
4.10
4.11
4.12
4.17
4.19
4.26
4.36
4.52
4.57
4.64
4.64
4.64
4.70
4.92
5.01
5.08
5.20
MWD
154.21
110.20
98.19
134.22
86.18
134.22
158.28
148.25
170.21
148.25
178.23
215.89
215.89
215.89
172.31
202.26
192.26
202.26
186.34
MVE
140
146
128
152
132
156
192
173
152
173
161
136
136
136
207
182
175
197
223
SF
0.000100
0.000133
0.000155
0.000159
0.000131
0.000135
0.00181
0.0000995
0.0000595
0.0000502
0.0000340
0.0000151
0.0000145
0.0000148
0.000640
0.0000120
0.00000980.
0.0000102
0.000238
pentachlorobenzene
608935 ar.ha 5.32 250.34 147 0.00000218
octane*
111659
al
5.34 114.23
164 0.00000625
B-6
-------
Chemical
2-dodecanone
cumene
pentane
1 ,2-dibromobenzene
1 ,5-cyclooctadiene
1-nonanol
1 ,2,4-trimethylbenzene
n-propylbenzene
dipentyl ether
1 ,3,5-trimethylbenzene
hexachloroethane
2,4-dicWorotoluene
1-methy [naphthalene
2-raethylnaphthalene
2-chloroiiaphthaIene
1 -chloronaphthalene
3,4-dicWorotoluene
biphenyl
1 ,3,5-trichlorobenzene
1 ,2,3-trichIorobenzene
1 ,2,4-trichlorobenzene
CASA
6175491
98828
109660
585539
111784
143088
95636
103651
693652
108678
67721
95738
90120
91576
91587
90131
95750
92524
108703
87616
120821
Class8
ke
ar
al
ar.ha
al
ao
ar
ar
et
ar
a!, ha
ar.ha
pah
pah
pah, ha
pah, ha
ar.ha
ar
ar.ha
ar.ha
ar.ha
Jf C
Aow
3.43
3.49
3.50
3.56
3.61
3.63
3.65
3.67
3.69
3,69
3.73
3.79
3.84
3.86
3.88
3.88
3.88
3.91
3.97
3.98
4.00
MWD
184.32
120.19
72.15
235.92
108.18
144.26
120.19
120.19
158.28
120.19
236.74
161.03
142.20
142.20
.162.62
162.62
161.03
154.21
181.45
181.45
181.45
MVE
223
140
116
119
130
175
138
140
202
140
132
129
140
141
136
136
129
150
125
124
126
SF
0.0357
0.000762
0.000592
0.000196
0.000386
0.00552
0.000487
0.000467
0.000757
0.000414
0.0000936
0.000457
0.000280
0.000270
0.000100
0.000100
0.000120
0.000216
0.0000933
0.0000870
0.0000886
B-5
-------
Chemical
1 ,3 ,5-cycloheptatriene
trichloroethylene .
di-n-butyl ether
t-1 ,2-dichlorocyclohexane
pentachloroethane
2,4-hexadiene
butylphenyl ether
benzophenone
ethylbenzene
2,3-dimethyl-l ,3-butadiene
2-undecanone
1-octanol
3-chJorotoluene
4-chlorotoluene
o-xylene
m-xylene
p-xylene
1 ,4-dichlorobenzene
3 ,5,5-trimethyl-l-hexanol
1 ,2-dichlorobenzene
1 ,3-dichlorobenzene
napthalene
cyclohexane
tetrachloroethylene
CASA
544252
79016
142961
822866
76017
592461
1126790
119619
100414
513815
112129
118875
108418
106434
95476
108383
106423
106467
3452979
95501
541731
91203
110827
127184
Class8
al
al.ha
et
al.ha
al.ha
al
et
ke
ar
al
ke
ao
ar.ha
ar.ha
ar
ar
ar
ar.ha
ao
ar.ha
ar.ha
pah
al
al.ha
v C
Aow
2.77
2.81
2.89
2.90
2.95
2.98
3.00
3.05
3.06
3.06
3.08
3.10
3.12
3.13
3.13
3.19
3.21
3.24
3.29
3.31
3.31
3.36
3.38
3.38
MWD
92.14
131.39
130.23
153.05
202.29
82.145
150.22
182.22
106.17
82.145
170.29
130.23
126.59
126.59
106.17
106.17
106.17
147.00
144.26
147.00
147.00
128.17
84.16
165.83
MVE
104
90.0
170
128
121
115
160
163
123
121
207
158
118
118
121
124
124
113
172
113
115
125
109
99.0
SF
0.00377
0.00360
0.00614
0.00162
0.00111
0.00237
0.000790
0.000480
0.00219
0.00162
0.0459
0.0161
0.000834
0.000817
0.00191
0.00154
0.00146
0.000581
0.0117
0.000507
0.000524
0.00110
0.000919
0.000710
B-4
-------
Chemical
benzene
1-hexanol
2-octanone
l-chloro-3-bromopropane
5-methyl-3-heptanone
anisole
2,6-dimethyl-2,5-heptadiene
t-1 ,2-dichloroethylene
1 ,2,3-trichloroepropane
1 , 1-dichloroethylene
1 ,3-dibromopropane*
bromoform
1 , 1,2,2-tetrachloroethane
1 ,4-d ichlorobutane
1 , 1-dichloropropane
2-nonanone
1,1,1 -trichloroethane
1.1,1 ,2-tetrachloroethane
5-nonanone
1-heptanol
chlorobenzene
2-ethyl-l-hexanol
bicyclo{2,2. l)hepta-2,5-diene
toluene
styrene
tetrachloromethane
2-decanone
bromobenzene
cyclopentane
1 ,5-dichIoropemane
CASA
71432
111273
111137
109706
541855
100663
504201
156605
96184
75354
109648
75252
79345
110565
78999
821556
71556
630206
502567
111706
108907
104767
121460
108883
100425
56235
693549
108861
278923
628762
Class6
ar
ao
ke
al,ha
ke
ar
ke
al.ha
al.ha
al.ha
al,ha
al.ha
al.ha
ai.ha
al.ha
ke
al.ha
al.ha
ke
ao
ar.ha
ao
al
ar
ar
al.ha
ke
ar.ha
al
al.ha
*owC
2.00
2.02
2.02
2.04
2.05
2.06
2.07
2.10
2.13
2.19
2.24
2.25
2.31
2.33
2.36
2.38
2.38
2.43
2.44
2.57
2.58
2.58
2.60
2.62
2.72
2.73
2.73
2.75
2.76
2.76
MWD
78.11
102.18
128.21
157.44
128.21
108.14
138.21
96.94
147.43
96.94
201.9
252.73
167.85
127.01
112.99
142.24
133.4
167.85
142.24
116.2
112.56
130.23
92.14
92.14
104.15
153.82
156.27
157.01
70.134
141.04
MVE
89.0
125
157
100
156
111
164
81.0
107
81.0
103
88.0
106
113
101
174
101
110
174
142
102
155
102
107
116
97.0
190
106
95.0
130
SF
0.0260
0.159
0.111
0.0184
0.111
0.0148
0.0171
0.0202
0.0177
0.0141
0.00930
0.00650
0.0181
0.00990
0.00790
0.0801
0.00662
0.0050
0.0740
0.0487
0.00320
0.132
0.00490
0.00600
0.00550
0.00248
0.0599
0.00196
0.00260
0.00286
B-3
-------
Chemical
2-methyI-2-butanol
2-n-butoxyethanol
diethyleneglycolmono-n-butylether
3,3-dimethyl-2-butanone
diethyl ether
4-methoxy-4-methyI-2-pentane
4-methyl-2-pentanone
dichloromethane
t-butylraethyl ether
cyclohexanol
2-hexanone
1 ,2-dichloroethane
1-pentaaol
3-methyl-3-pentanol
2-phenoxyethanol
2,2,2-irichloroethanol
4-methyI-2-pentanol
3-hexanol
2-heptanone
5-raethyl-2-hexanone
214-dimetbyl-3-pentanol
6-methyl-5-heptene-2-one
2-hexanol
1 ,3-dichloropropane
1 ,2-dichloropropane
diisopropyl ether
chloroform
1 , 1 ,2-trichloroethane
1 ,4-dimethoxybenzene
2,6-dimethoxytolunene
CASA
75854
111762
112345
75978
60297
107700
108101
75092
1634044
108930
591786
107062
71410
77747
122996
115208
108112
623370
110430
110123
600362
110930
626937
142289
78875
108203
67663
79005
150787
' 5673074
Class8
ao
ao
et
k
et
k
k
al.ha
et
ao
k
al.ha
ao
ao
ao
ao
ao
ao
ke
ke
ao
ke
ao
al.ha
al.ha
et
al.ha
al.ha
ar
ar
tr c
•"•OW
1.03
1.05
1.09
1.09
1.15
1.17
1.17
1.18
1.20
1.29
1.29
1.40
1.49
1.49
1.50
1.61
1.66
1.66
1.67
1.68
1.78
1.82
1.83
1.84
1.86
1.87
1.91
1.91
1.95
1.99
MW°
88.15
118.17
162.23
100.16
74.122
130.19
100.16
84.93
88.149
100.16
100.16
98.96
88.15
102.18
138.17
149.4
102.18
102.18
114.19
114.19
116.2
126.2
102.18
112.99
112.99
102.18
119.38
133.4
138.165
152.19
MVE
110
131
170
125
105
143
124
65.0
122
103
124
79.0
109
125
122
93.0
126
125
141
141
140
151
126
97.0
99.0
138 -
81.0
94.0
132
147
SF
1.62
8.78
40.0
0.954
1.16
41.5
0.862
0.211
9.04
1.61
0.598
0.114
0.581
3.79
0.173
48.4
2.25
2.18
0.312
0.271
3.05
0.487
1.13
0.0363
0.0342
0.0918
0.0319
0.0369
0.0250
0.0283
B-2
-------
Appendix B. Chemicals which comprise the acute toxicity database for narcosis chemicals in Section 2 of this
document. Table from Di Toro et al. ( 2000).
Chemical
triethylene glycol
methanol
2,4-pentanedione*
ethanol
acetone
2-chloroethanol *
2-(2-ethoxyethoxy)ethanol
1 -chIoro-2-propanol*
1 ,3-dichloro-2-propanol*
2-methyl-2,4-pentanediol
2-butanone
2-propanol
3-chloro-l-propanol*
1-propanol
cyclopentanone
2-methyl-2-propanol
methyl chloride
2-butanol
methyl bromide*
3-methyl-2-butanone
2,3-dibromopropanol*
cyclohexanone
cyclopentanol
2-methyl-l -propanol
4-methyl-3-pente-2-one
2-pentanone
1-butanol
3-pentanone
CASA
112276
67561
123546
64175
67641
107073
111900
127004
96231
107415
78933
67630
627305
71238
120923
75650
74873
78922
74839
563804
96139
108941
96413
78831
141797
107879
71363
96220
Class8
ao
ao
k
ao
k
ao
ao
ao
ao
ao
k
ao
ao
ao
k
ao
al.ha
ao
al.ha
k
ao
k
ao
ao
k
k
ao
k .
K- c
•^ow
-1.48
-0.715
-0.509
-0.234
-0.157
-0.048
0.011
0.156
0.165
0.246
0.316
0.341
0.363
0.399
0.453
0.663
0.677
0.717
0.791
0.792
0.819
0.827
0.849
0.858
0.867
0.877
0.946
0.954
MWD
150.17
32.04
100.12
46.07
58.08
80.51
134.17
94.54
128.99
118.17
72.11
60.10
94.54
60.10
84.12
74.12
50.49
74.12
94.94
86.13
217.90
98.14
86.13
74.12
98.14
86.13
74.12
86.13
MVE
131
41.0
100
59.0
74.0
65.0
111
84.0
91.0
120
90.0
77.0
82.0
75.0
89.0
95.0
56.0
93.0
57.0
108
96.0
103
89.0
93.0
118
107
92.0
108
SF
-
13.5
7.87
11.9
13.71
9.09
-
44.8
6.30
43.0
2.81
13.6
2.00
11.2
1. 11
16.5
0.0666
14.9
0.154
1.32
5.97
0.445
5.19
10.6
2.68
1.03
3.03
0.849
B-l
-------
pcv TOT for each sediment (plotted as circles in Figure 6-2) was determined by multiplying the
2 sediment-specific SESGTUpcv 13 values by 11.5 and by multiplying the sediment-specific SESGTUFCV 23
3 by 4.14 (Table 6-1). The 95% limits on the SESGTUFCViTOT estimated from the EESGTUFCVil3
4 exceeded 1.0 for 35.5% of the 1992 sediments and the 95% limits on the 2ESGTUFCVTOT estimated
5 from the SESGTUFCVi23 exceeded 1.0 for 23.7% of the 2001 sediments. Therefore, if the 95%
6 uncertainty ratios are applied to the SESGTUFCVil3 or the SESOTUpcv^ the predicted SESGTUFCVTOT
7 for about one-third of the sediments are in excess of the ESG for PAH mixtures of 1.0 SESGTUFCV.
8 This strongly suggests that new monitoring programs should quantify a minimum of the 34 PAHs
9 monitored by the U.S. EPA EMAP program. It is important to repeat that at present the uncertainty of
10 using the 34 PAHs to estimate the total toxicological contributions of the unmeasured PAHs is unknown
11 and needs additional research.
12
13 6.3 INTERPRETING ESGs IN COMBINATION WITH TOXICITY TESTS
.14
15 Sediment toxicity tests provide an important complement to ESGs in interpreting overall risk
16 from contaminated sediments. Toxicity tests have different strengths and weaknesses compared to
17 chemical-specific guidelines, and the most powerful inferences can be drawn when both are used
18 together.
19 Unlike chemical-specific guidelines, toxicity tests are capable of detecting any toxic chemical,
20 if it is present in toxic amounts; one does not need to know what the chemicals of concern are to
21 monitor the sediment. Toxicity tests are also useful for detecting the combined effect of chemical
22 mixtures, if those effects are not considered in the formulation of the applicable chemical-specific
23 guideline.
24 On the other hand, toxicity tests have weaknesses also; they provide information only for the
Final Draft PAH Matures ESG Document 6-8 5 April 2000
-------
1 species tested, and also only for the endpoints measured. This is particularly critical given that most
2 sediment toxicity tests conducted at the time of this writing measure primarily short-term lethality;
3 chronic test procedures have been developed and published for some species, but these procedures are
4 more resource-intensive and have not yet seen widespread use. In contrast, chemical-specific
5 guidelines are intended to protect most species against both acute and chronic effects.
6 Many assessments may involve comparison of sediment chemistry (e.g., using ESG values) and
7 toxicity test results. In cases where results using these two methods agree (either both positive or both
8 negative), the interpretation is clear. In cases where the two disagree, the interpretation is more
9 complex; some investigators may go so far as to conclude that one or the other is "wrong," which is
10 not necessarily the case.
11 Individual ESGs consider only the effects of the chemical or group of chemicals for which they
12 are derived. For this reason, if a sediment shows toxicity but does not exceed the ESG for a chemical
13 of interest, it is likely that the cause of toxicity is a different chemical or chemicals.
14 In other instances, it may be that an ESG is exceeded but the sediment is not toxic. As
15 explained above, these findings are not mutually exclusive, because the inherent sensitivity of the two
16 measures is different. ESGs are intended to protect relatively sensitive species against both acute and
17 chronic effects, whereas toxicity tests are run with specific species that may or may not be sensitive to
18 chemicals of concern, and often do not encompass the most sensitive endpoints (e.g., chronic survival,
19 growth or reproduction). It is also possible for a sediment above the ESG to be non-toxic if there are
20 site-specific conditions that run counter to the equilibrium partitioning model and its assumptions (see
21 Section 7.2).
22 The first step in interpreting this situation is to consider the magnitude of the ESG exceedance
23 and the sensitivity of the test organism and endpoint to the suspect chemical. For example, the acute-
24 chronic ratio used for the PAH ESG is 4.16 (Section 3.3.7); as such, if SESGTUFCV = 4, one would
Final Draft PAH Mixtures ESG Document 6-9 5 April 2000
-------
1 expect lethal effects only for highly sensitive species. Between SESGTUFCV of 1 and 4, one would
2 expect only chronic effects, unless the test species was unusually sensitive. If SESGTUpcv for PAHs
3 was 2, for example, one would not generally expect to see lethality from PAHs in short term sediment
4 lethality tests.
5 A more precise method for evaluating the results of toxicify tests is to calculate effect
6 concentrations in sediment that are species specific. For species contained in the toxicity data for the
7 PAH ESG (Section 3.2.1), effect concentrations in sediment can be calculated that are specific for that
8 organism (using procedures in Section 4). These values could then be used to directly judge whether
9 the absence of toxicity in the toxicity test would be expected from the corresponding level of sediment
10 contamination.
11 If the exceedance of the PAH ESG is sufficient that one would expect effects in a toxiciry test
12 but they were not observed, it is prudent to evaluate the partitioning behavior of the chemical in the
13 sediment. This is done by isolation of interstitial water from the sediment and analyzing it for the same
14 PAHs measured in the solid phase. Predicted concentrations of chemicals in the interstitial water can
15 be calculated from the measured concentrations in the solid phase (normalized to organic carbon)
16
17 Q = C^ / K^ (6-4)
18
19 For chemicals with logIO£oW greater than 5,5, corrections for DOC binding in the interstitial
20 water will be necessary
21
22 Cdiw = C,w ,OC/^DOC (6-5)
23
24 If the measured chemical in the interstitial water is substantially less (e.g., 2-3 fold lower or
Final Draft PAH Mixtures ESG Document 6-10 5 April 2000
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1 more), it suggests that the organic carbon in that sediment may not partition similarly to more typical
2 organic carbon, and derivation of site-specific ESGs based on interstitial water may be warranted
3 (U.S.EPA, 2000f).
4
5 6.4 PHOTO-ACTIVATION
6
7 6.4.1 Overview
8
9 Research over the last decade has shown that the presence of ultraviolet (UV) light can greatly
10 enhance the toxicity of many PAHs. This "photo-activated" toxicity has been shown to cause rapid,
11 acute toxicity to several freshwater and marine species including fish, amphibians, invertebrates, plants
12 and phytoplankton (Bowling et al., 1983; Cody et al., 1984; Kagan et ah, 1984; Landrum et al.,
13 1984a,b; Oris et al., 1984; Allred and Giesy, 1985; Kagan et al., 1985; Oris and Giesy, 1985, 1986,
14 1987; Gala and Giesy, 1992; Huang et al., 1993; Gala and Giesy, 1994; Ren et al., 1994; Arfsten et
15 al., 1996; Boese et al., 1997; Huang et al., 1997; McConkey et al., 1997; Pelletier et al., 1997; Hatch
16 and Burton, 1998; Spehar et al., 2000). Depending on the organism and exposure regime, photo-
17 activation can increase toxicity of PAH by one to four orders of magnitude over that caused by
18 narcosis.
19 The mechanism for phototoxicity has been related to the absorption of ultraviolet radiation
20 (UV) by the conjugated bonds of selected PAH molecules
21
22 PAH + UV - PAH* + O2 - PAH + O2* (6-6)
23
24 This excites the PAH molecules to a triplet state (PAH*) which rapidly transfers the absorbed
Final Draft PAH Mixtures ESG Document 6-11 5 April 2000
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1 energy to ground state molecular oxygen (O2) forming excited singlet oxygen intermediaries (O2*)
2 (Newsted and Giesy, 1987). Although extremely short-lived (2 to 700 ^s), oxygen free radicals are
3 highly oxidizing and can cause severe tissue damage upon contact. Despite the many different parent
4 PAHs and related alkylated forms, not all PAHs induce photo-activated toxicity. Those PAHs that are
5 photo-activated can be predicted using various molecular physical-chemical variables (Newsted and
6 Giesy, 1987; Oris and Giesy, 1987); however, the Highest Occupied Molecular Orbital - Lowest
7 Unoccupied Molecular Orbital gap model (HOMO-LUMO) has been the most successful (Mekenyan et
8 al. 1994a,b; Veith et al. 1995a,b; Ankley et al. 1996; Ankley et al. 1997). As research on the nature
9 of photo-activated toxicity has evolved, certain key elements of this phenomena have been better
10 defined including interactions of UV and PAH dose, effects of temperature, humic substances,
11 organism behavior, turbidity, dissolved oxygen, and mixtures (Oris et al., 1990; McCloskey and Oris,
12 1991; Ankley et al., 1995, 1997; Ireland et al., 1996; Hatch and Burton, 1998).
13 Eight studies have been performed with sediments contaminated with PAHs to assess the
14 importance of photo-activated toxicity in the benthos (Davenport and Spacie, 1991; Ankley et al.,
15 1994; Monson et al., 1995; Sibley et al., 1997; Swartz et al., 1997; Boese et al., 1998, 1999; Kosian et
16 al., 1998; Spehar et al., 2000). These studies conclude that photo-activated toxicity may occur in
17 shallow water environments; however, the magnitude of these effects are not as well characterized as in
18 water-only exposures and are probably not as dramatic as those observed in the water column.
19 Comparisons by Swartz et al. (1995) suggest that responses of benthic communities in PAH-
20 contaminated sites correlate well with the toxicity that is predicted based on narcosis, suggesting that
21 photo-activation was not a major confounding factor for those environments. However, Boese et al.
22 (1997) and Pelletier et al. (2000a) show that life history of benthic organisms is critical to assessing
23. whether or not photo-activated toxicity will occur. For example, several marine species that frequendy
24 encounter ultraviolet radiation during low tide are not vulnerable to photo-activated toxicity due to light
Final Draft PAH Mixtures ESC Document 6-12 5 April 2000
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1 protective adaptation (e.g., shells, pigments, borrowing). Additionally, there is evidence that maternal
2 transfer of PAHs from benthic adult bivalves to pelagic embryos does occur (Pelletier et al., 2000b).
3
4 6.4.2 Implications to Derivation of ESG
5
6 Because the total PAH ESG derived here is based on narcosis, additional toxicity caused by
7 photo-activation would cause the ESG to be underprotective. At present, the magnitude of potential
8 errors can not be specifically quantified, but are probably significant primarily for habitats in very
9 shallow or very clear water. This is because of the rapid attenuation of ultraviolet radiation in the
10 water column (Pickard and Emery 1982; Wetzel, 1983). For example, <25% of incident UV
11 penetrates below the first meter of water in productive aquatic systems. In areas where PAH-
12 contaminated sediments are present in shallow environments the risk of photo-activated toxicity is
13 greater and a site-specific ESG may need to be generated that considers this potential risk.
14
15 6.5 TERATOGENICITY AND CARCINOGENICITY
16
17 This subsection presents an analysis intended to determine if the ESG for PAH mixtures of 1.0
18 SESGTUpcv is protective for non-narcosis modes of toxic action of individual PAHs. Published
19 articles were screened for applicable data on teratogenic (Appendix E) and carcinogenic (Appendix F)
20 effects of individual PAHs and their mixtures. Five laboratory studies with benzo(a)pyrene (BaP),
21 predominantly water exposures, and one with anthracene were selected for analysis of teratogenic
22 effects; two laboratory studies with BaP were selected for analysis of carcinogenic effects (Table 6-3).
23 In the teratogen studies, typically radio-labeled BaP was used to quantify the accumulation of the PAH
24 and its metabolites in fish ranging in age from embryo to adults. The water PAH concentrations
Final Draft PAH Mixtures ESG Document 6-13 5 April 2000
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1 associated with teratogenic and carcinogenic effects were generally high and steady-state was not
2 always achieved. Hence, the solubility limit in water for BaP of 3.81 //g/L was exceeded in 6 of 8
3 experiments (Table 6-3). In contrast, for seven of the experiments, the BaP concentration in eggs or
4 fish tissue was the observed effect concentration. The theoretical solubility-limited maximum of 3840
5 p*g BaP/g lipid was exceeded only in one of the experiments. For these reasons, when the
6 concentration of BaP plus metabolites was measured in the eggs or tissue of the organism, this
7 concentration was considered the most valid representation of the true observed exposure concentration
8 and the water concentration was not used in further analysis. Elutriates from crude oil contained non-
9 PAH compounds and the relationship of total PAH concentrations in the study vs total PAH as defined
10 in mis document were difficult to determine in the Carls et al. (1999) study; therefore, these data were
11 also excluded from this analysis.
12 As indicated in Table 6-3 and Appendix F, the database for carcinogenic effects of PAHs on
13 aquatic (fish) species from laboratory studies is limited. Most of the available data are from studies of
14 epizootic outbreaks of neoplasia (tumors) from highly contaminated field sites such as the Black River,
15 Ohio (see Baumann, 1998 for review) or Puget Sound, WA (Malins et al., 1987, Myers et al., 1990),
16 to mention only a notable few. The applicability of these field studies to a causal relationship between
17 carcinogenic effects observed and PAH concentrations is limited by the possible interactive effects of
18 the PAHs with PCBs and other simultaneously occurring chemicals. The bulk of laboratory
19 experimental evidence for carcinogenic effects of PAHs is based on the distribution of neoplasms in
20 fish species exposed to PAH-enriched sediment extracts (Black, 1983; Metcalfe et al., 1988; Fabacher
21 et al., 1991), dietary exposures or inter-peritoneal injection (Hendricks et al., 1985), or intermittent
22 water exposures of 7,12-dimethylbenzanthracene (Schultz and Schultz, 1982). These studies are listed
23 in Appendix F for completeness, but were not included in Table 6-3 for further analysis. This is
24 because the exposure regime or concentrations of individual or mixtures of PAHs were not provided in
Final Draff PAH Mixtures ESG Document 6-14 5 April 2000
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1 sufficient detail to permit critical measured sediment concentrations, or sediment concentrations derived
2 from concentrations in water or tissue, to be compared to the observed carcinogenic effects. The study
3 with 7,12-dimethylbenzanthracene (Schultz and Schultz, 1982) was not considered for analysis because
4 this PAH is not commonly measured as part of the environmental monitoring programs (see Table 6-2).
5 A far more extensive database exists on the influence of PAHs on various aspects of tumor
6 biology, such as PAH-DNA adduct formation and phase I (oxidation, reduction, and hydrolysis
7 reactions) and phase n (glucuronidation and glutathione conjugation) metabolism of individual
8 compounds. However, as indicative of cytotoxicity as these biomarkers may or may not be, they have
9 been excluded from the analysis for the explicit purposes of this subsection. The methods of PAH
10 exposure that were useful for this analysis were aqueous (Hannah et al., 1982; Hose et al., 1982, 1984;
11 Winkler et al., 1983; Goddard et al., 1987; Hawkins et al., 1988, 1990), maternal (Hall and Oris,
12 1991), or inter-peritoneal injection of adult English sole (Parophrys vetulus) followed by measurement
13 of concentrations in embryos (Hose etal., 1981).
14
15 6.5.1 Calculations
16
17 When the measured concentration of the PAH dissolved hi water (Ca; /ug/L) associated with a
18 teratogenic or carcinogenic effect was available it was multiplied by its KQC (L/kgoc) x 10"3 to derive an
19 equivalent effect concentration in sediment (Cd-derived Q^; jug/goc). *$ Per me EqP methodology
20 (Table 6-3; Appendix E and F). When the measured concentration of the PAH in eggs or tissue (CL;
21 Mg PAH/g lipid) associated with an effect was available, its equivalent effect concentration in sediment
22 (CL-derived C^;>g/goc) was calculated using the following equation from Di Toro and McGrath
23 (2000)
24
Final Draft PAH Mixtures ESG Document 6-15 5 April 2000
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= 0.00028 + log,0CL + 0.038 logIOK^ (6.7)
4 6.5.2 Critical Sediment Concentrations for Teratogenic and Carcinogenic Effects versus ESGs for
5 PAH Mixtures
6
7 The critical sediment concentrations (i.e. , CA- or CL-derived C^ that would be expected to
8 cause teratogenic or carcinogenic effects on the five freshwater and three saltwater fishes exposed to
9 BaP ranged from 57 to 8,937 Aig/goo the only Q^ for anthracene was 219 Atg/goc (Table 6-3). The
10 majority of Q^ values were derived using concentrations measured in fish eggs. Six of the nine Q^
1 1 concentrations for BaP were less than the solubility-limited maximum concentration of 3,840 /ug/goc-
12 The CQC value of 8,937 jug /goc is retained because the concentrations in the eggs probably included
13 metabolites of BaP that are quantified as total BaP equivalents in the radio-label analysis. The Qc
14 values for individual PAHs in sediments were then compared to total PAH concentrations in monitored
15 field sediments to determine if teratogenic or carcinogenic effects might occur in sediments having
16 < 1 .0 £ESGTUFCV. This analysis was used to determine if the ESG derived from the narcosis mode of
17 action was protective of teratogenic or carcinogenic effects.
18 The combined databases from the U.S. EPA EMAP (U. S. EPA 1996b, 1998) and Elliott Bay
19 (Ozretich et al., 2000b) sediment monitoring programs were used to compare the BaP (Figure 6-3 A) or
20 anthracene (Figure 6-4A) concentration of 539 sediment samples where 34 PAHs, or 33 PAHs for
21 Elliott Bay, were measured versus the EESGTUFCV for all PAHs measured in those sediments. The
22 lowest critical sediment concentration for teratogentic or carcinogenic effects is indicated with a solid
23 line at 57 ^g/goc for BaP and at 219 ^g/goc for anthracene. None of the sediments having < 1 .0
24 SESGTUFCV contained BaP or anthracene at concentrations likely to cause the teratogenetic or
25 carcinogenic effects reported in Table 6-3. The same database of PAH concentrations in field
Final Draft PAH Mixtures ESG Document 6-16 5 April 2000
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1 sediments was used to calculate the sediment-specific BaP:SESGTUFCV ratio and the sediment-specific
2 anthracene.-SESGTUpcv ratio. The total PAH concentration in each of the 539 sediments was
3 multiplied by its sediment-specific ratio to determine the BaP or anthracene concentration for the
4 sediment if the SESOTUpcv was equal to 1.0. Probability plots of the calculated concentrations for the
5 BaP and anthracene at 1.0 SESGTUFCV are in Figures 6-30 and 6-4B, respectively. The solid lines
6 represent the critical sediment concentration for each respective PAH. None of the sediments for
7 anthracene and 3.53% of the sediments for BaP would be expected to produce teratogenic or
8 carcinogenic effects if the ESG for PAH mixtures in these sediments were equal to 1.0 SESGTUpcy.
9 The approach of examining these relationships individually with BaP or anthracene may be flawed
10 because it may under-represent the teratogenic of carcinogenic contributions of other PAHs with the
11 same mode of action in the PAH mixture. However, at present insufficient data are available to
12 appropriately sum the contributions of multiple teratogenic or carcinogenic PAHs.
13
14 6.6 EQUILIBRIUM AND ESGs
15
16 Care must be used in application of ESGs in disequilibrium conditions. In some instances site-
17 specific ESGs may be required to address this condition (U.S. EPA, 2000f). Guidelines based on EqP
18 theory assume that nonionic organic chemicals are in equilibrium with the sediment and interstitial
19 water, and that they are associated with the sediment primarily through adsorption into sediment
20 organic carbon. In order for these assumptions to be valid, the chemical must be dissolved in
21 interstitial water and partitioned into sediment organic carbon. The chemical must, therefore, be
22 associated with the sediment for a sufficient length of time for equilibrium to be reached. With PAHs,
23 the absence of toxicity when the ESG is exceeded may be because of the presence of less available
24 PAHs associated with soot or coal particles in sediments (see discussion in Section 6.7). Alternatively,
Final Draft PAH Mixtures ESG Document 6-17 5 April 2000
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= 0.00028 -f log,0CL + 0.038 log10KoW (6.7)
4 6.5.2 Critical Sediment Concentrations for Teratogenic and Carcinogenic Effects versus ESGs for
5 PAH Mixtures
6
7 The critical sediment concentrations (i.e. , Cd- or CL-derived Q^) that would be expected to
8 cause teratogenic or carcinogenic effects on the five freshwater and three saltwater fishes exposed to
9 BaP ranged from 57 to 8,937 ^g/goo ^ onlv Q>c for anthracene was 219 /^g/goc (Table 6-3). The
10 majority of C^ values were derived using concentrations measured in fish eggs. Six of the nine C^
1 1 concentrations for BaP were less than the solubility-limited maximum concentration of 3,840 ^g/goc-
12 The CQC value of 8,937 ^g /goc is retained because the concentrations in the eggs probably included
13 metabolites of BaP that are quantified as total BaP equivalents in the radio-label analysis. The CQC
14 values for individual PAHs in sediments were then compared to total PAH concentrations in monitored
15 field sediments to determine if teratogenic or carcinogenic effects might occur in sediments having
16 < 1 .0 SESGTUFCV. This analysis was used to determine if the ESG derived from the narcosis mode of
17 action was protective of teratogenic or carcinogenic effects.
18 The combined databases from the U.S. EPA EMAP (U. S. EPA 1996b, 1998) and Elliott Bay
19 (Ozretich et al., 2000b) sediment monitoring programs were used to compare the BaP (Figure 6-3 A) or
20 anthracene (Figure 6-4A) concentration of 539 sediment samples where 34 PAHs, or 33 PAHs for
21 Elliott Bay, were measured versus the 2ESGTUFCV for all PAHs measured in those sediments. The
22 lowest critical sediment concentration for teratogentic or carcinogenic effects is indicated with a solid
23 line at 57 /^g/goc for BaP and at 219 /^g/goc f°r anthracene. None of the sediments having < 1 .0
24 SESGTUpcv contained BaP or anthracene at concentrations likely to cause the teratogenetic or
25 carcinogenic effects reported in Table 6-3. The same database of PAH concentrations in field
Final Draft PAH Mixtures ESG Document 6-16 5 April 2000
-------
1 sediments was used to calculate the sediment-specific BaP:SESGTUFCV ratio and the sediment-specific
2 anthracene :SESGTUFCV ratio. The total PAH concentration in each of the 539 sediments was
3 multiplied by its sediment-specific ratio to determine the BaP or anthracene concentration for the
4 sediment if the SESGTUre-v was equal to 1.0. Probability plots of the calculated concentrations for the
5 BaP and anthracene at 1.0 SESGTUFCV are in Figures 6-3B and 6-4B, respectively. The solid lines
6 represent the critical sediment concentration for each respective PAH. None of the sediments for
7 anthracene and 3.53% of the sediments for BaP would be expected to produce teratogenic or
8 carcinogenic effects if the ESG for PAH mixtures in these sediments were equal to 1.0 EESCTUpcv.
9 The approach of examining these relationships individually with BaP or anthracene may be flawed
10 because it may under-represent the teratogenic of carcinogenic contributions of other PAHs with the
11 same mode of action in the PAH mixture. However, at present insufficient data are available to
12 appropriately sum the contributions of multiple teratogenic or carcinogenic PAHs.
13 ,
14 6.6 EQUILIBRIUM AND ESGs
15
16 Care must be used in application of ESGs in disequilibrium conditions. In some instances site-
17 specific ESGs may be required to address this condition (U.S. EPA, 2000f). Guidelines based on EqP
18 theory assume that nonionic organic chemicals are in equilibrium with the sediment and interstitial
19 water, and that they are associated with the sediment primarily through adsorption into sediment
20 organic carbon. In order for these assumptions to be valid, the chemical must be dissolved in
21 interstitial water and partitioned into sediment organic carbon. The chemical must, therefore, be
22 associated with the sediment for a sufficient length of time for equilibrium to be reached. With PAHs,
23 the absence of toxicity when the ESG is exceeded may be because of the presence of less available
24 PAHs associated with soot or coal particles in sediments (see discussion in Section 6.7). Alternatively,
Final Draft PAH Matures ESG Document 6-17 5 April 2000
-------
1 disequilibrium exists, and ESG may be over-protective, when PAHs occur in sediments as undissolved
2 liquids or solids; although the use of solubility limited acceptable sediment concentrations should
3 adequately account for this.
4 In very dynamic locations, with highly erosional or depositional bedded sediments, the
5 partitioning of nonionic organic chemicals between sediment organic carbon and interstitial water may
6 only attain a state of near equilibrium. Likewise, nonionic organic chemicals with high \ogtoKov/ values
7 may come to equilibrium in clean sediment only after a period of weeks or months. Equilibrium times
8 are shorter for chemicals with low logIOA^w values and for mixtures of two sediments with similar
9 organic carbon-normalized concentrations, each previously at equilibrium. This is particularly relevant
10 in tidal situations where large volumes of sediments are continually eroded and deposited, yet near
11 equilibrium conditions between sediment and interstitial water may predominate over large spatial
12 areas. For locations where times are sufficient for equilibrium to occur, near equilibrium is likely the
13 rule and disequilibrium uncommon. In many environments disequilibrium may occur intermittently,
14 but in those cases ESGs could be expected to apply when the disturbance abates, which can generally
15 be expected. In instances where long-term disequilibrium is suspected, application of site-specific
16 methodologies may be desirable (U.S. EPA, 2000f).
17
18 6.7 OTHER PARTITIONING PHASES
19
20 6.7.1 Overview
21
22 In general, laboratory studies with PAHs have shown the same partitioning behavior
23 demonstrated by many classes of nonpolar organic contaminants (Karickhoff et al., 1979; Means et al.,
24 1980; Di Toro et al., 1991). However, there are some data indicating that PAHs do not always follow
Final Draft PAH Mixtures ESG Document 6-18 5 April 2000
-------
1 equilibrium partitioning behavior in the environment. Specifically, some studies have reported larger
2 partitioning coefficients for PAHs in field-collected sediments than is predicted based on laboratory or
3 SPARC-generated log^^/Koc values (Prahl and Carpenter, 1983; Socha and Carpenter, 1987;
4 Broman et al., 1990; McGroddy and Farrington, 1995; Maruya et al., 1996; McGroddy et al., 1996).
5 The observed differences in partitioning of PAHs may relate to differences in PAH sources with the
6 speculation that PAHs from combustion sources (e.g., soot or related materials, such as coal) may be
7 more strongly associated with the particulate phase than PAHs from some petrogenic sources (Readman
8 et al., 1984; Socha and Carpenter, 1987; McGroddy and Farrington, 1995; Chapman et aL, 1996;
9 Maruya et al., 1996;-McGroddy et al., 1996; Naes and Oug, 1997; Naes et al., 1998). The result is
10 that PAH concentrations in interstitial water are lower man laboratory or SPARC-generated K^ values
11 and, presumably, exhibit correspondingly lower bioavailability. Several studies have proposed that the
12 lack of observable biological effects from sediments (and other samples) containing high concentrations
13 of presumably bioavailable PAHs is related to this phenomena (Farrington et al., 1983; Bender et al.,
14 1987; Knutzen, 1995; Chapman et al., 1996; Paine et al., 1996; Maruya et al., 1997).
15 The mechanisms causing these field observations of unusual PAH partitioning are not well
16 understood. One explanation proposes that PAHs condense into the soot matrix during particle
17 formation, and are thereby sterically inhibited from partitioning to interstitial water as would be
18 expected under equilibrium conditions. A second perspective assumes that the soot fraction represents
19 a second partitioning phase in addition to normal organic carbon. The partitioning of PAHs from this
20 phase approximate the equilibrium behavior assumed for normal organic carbon, but have a much
21 higher partitioning coefficient (K^ than biologically-derived organic carbon (represented by KQ^)
22 (Gustafsson and Gschwend, 1997). Recently, a method was published for quantifying the combustion
23 or 'soot' phase in sediments (Gustafsson et al., 1997) for derivation of a fraction soot carbon (fx). The
24 soot phase can then be incorporated into an expanded partitioning equation with two partitioning terms
Final Draft PAH Matures ESG Document 6-19 5 April 2000
-------
1 disequilibrium exists, and ESG may be over-protective, when PAHs occur in sediments as undissolved
2 liquids or solids; although the use of solubility limited acceptable sediment concentrations should
3 adequately account for this.
4 In very dynamic locations, with highly erosional or depositional bedded sediments, the
5 partitioning of nonionic organic chemicals between sediment organic carbon and interstitial water may
6 only attain a state of near equilibrium. Likewise, nonionic organic chemicals with high loglo£ow values
7 may come to equilibrium in clean sediment only after a period of weeks or months. Equilibrium times
8 are shorter for chemicals with low log10A^w values and for mixtures of two sediments with similar
9 organic carbon-normalized concentrations, each previously at equilibrium. This is particularly relevant
10 in tidal situations where large volumes of sediments are continually eroded and deposited, yet near
11 equilibrium conditions between sediment and interstitial water may predominate over large spatial
12 areas. For locations where times are sufficient for equilibrium to occur, near equilibrium is likely the
13 rule and disequilibrium uncommon. In many environments disequilibrium may occur intermittently,
14 but hi those cases ESGs could be expected to apply when the disturbance abates, which can generally
15 be expected. In instances where long-term disequilibrium is suspected, application of site-specific
16 methodologies may be desirable (U.S. EPA, 2000f).
17
is 6.7 OTHER PARTITIONING PHASES
19
20 6.7.1 Overview
21
22 In general, laboratory studies with PAHs have shown the same partitioning behavior
23 demonstrated by many classes of nonpolar organic contaminants (Karickhoff et al., 1979; Means et al.,
24 1980; Di Toro et al., 1991). However, there are some data indicating that PAHs do not always follow
Final Draft PAH Mixtures ESG Document 6-18 5 April 2000
-------
1 equilibrium partitioning behavior in the environment. Specifically, some studies have reported larger
2 partitioning coefficients for PAHs in field-collected sediments than is predicted based on laboratory or
3 SPARC-generated log^^lK^ values (Prahl and Carpenter, 1983; Socha and Carpenter, 1987;
4 Broman et al., 1990; McGroddy and Farrington, 1995; Maruya et al., 1996; McGroddy et al., 1996).
5 The observed differences in partitioning of PAHs may relate to differences in PAH sources with the
6 speculation that PAHs from combustion sources (e.g., soot or related materials, such as coal) may be
7 more strongly associated with the particulate phase than PAHs from some petrogenic sources (Readman
8 et al., 1984; Socha and Carpenter, 1987; McGroddy and Farrington, 1995; Chapman et al., 1996;
9 Maruya et al., 1996,-McGroddy et al., 1996; Naes and Oug, 1997; Naes et al., 1998). The result is
10 that PAH concentrations in interstitial water are lower than laboratory or SPARC-generated K^. values
11 and, presumably, exhibit correspondingly lower bioavailability. Several studies have proposed that the
12 lack of observable biological effects from sediments (and other samples) containing high concentrations
13 of presumably bioavailable PAHs is related to this phenomena (Farrington et al., 1983; Bender et al.,
14 1987; Knutzen, 1995; Chapman et al., 1996; Paine et al., 1996; Maruya et al., 1997).
15 The mechanisms causing these field observations of unusual PAH partitioning are not well
16 understood. One explanation proposes that PAHs condense into the soot matrix during particle
17 formation, and are thereby sterically inhibited from partitioning to interstitial water as would be
18 expected under equilibrium conditions. A second perspective assumes that the soot fraction represents
19 a second partitioning phase in addition to normal organic carbon. The partitioning of PAHs from this
20 phase approximate the equilibrium behavior assumed for normal organic carbon, but have a much
21 higher partitioning coefficient (K^ than biologically-derived organic carbon (represented by KQC)
22 (Gustafsson and Gschwend, 1997). Recently, a method was published for quantifying the combustion
23 or 'soot' phase in sediments (Gustafsson et al., 1997) for derivation of a fraction soot carbon (fx). The
24 soot phase can then be incorporated into an expanded partitioning equation with two partitioning terms
Final Draft PAH Mixtures ESG Document 6-19 5 April 2000
-------
1 ^d=/oc^oc+/sc^sc (6-8)
2
3 where, Kd is the partition coefficient for the expanded partitioning equation,^ and^- are the fraction
4 organic carbon and fraction soot carbon, respectively, and KQC and KSC are the organic carbon and soot
5 carbon partition coefficients.
6
7 6.7.2 Implications to Derivation of ESG
8
9 Irrespective of the mechanism, this issue has the potential to affect the predictive power and
10 accuracy of the total PAH ESG. Since the presence of soot or related materials are associated with
11 reduced concentrations of PAH in interstitial water, one would presume that this results in decreased
12 bioavailability of PAHs, a phenomenon demonstrated by West et al. (2000). This, in rum, would make
13 the total PAH ESG derived here overprotective, because the Xoc-based partitioning model would
14 overpredict chemical activity and, therefore, concentrations of PAH in interstitial water and organisms.
15 . Nonetheless, empirical data suggest that this error may not be pervasive; most applications of
16 the PAH mixture narcosis model to toxicity data for field-collected sediments show good predictive
17 ability for the ESG (see Section 5.3). This may be because most sediments that are sufficiently
18 contaminated to cause narcosis are contaminated by PAH sources that exhibit normal partitioning
19 behavior, such as creosote and other petiogenic sources. In their study of PAH-contaminated
20 sediments, Ozretich et al. (2000b) found that discrepancies between measured and predicted
21 partitioning behavior predominated in sediments with lower PAH concentrations, while those with
22 higher PAH concentrations showed partitioning behavior closer to that predicted from published
23 KQW/KQC relationships. This differential behavior was attributed to the presence of two PAH sources,
24 with creosote being the source causing the highest levels of contamination and toxicity.
Final Draft PAH Matures ESG Document 6-20 5 April 2000
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1 In cases where it is suspected that soot, coal, or other materials may be causing unusual
2 partitioning, direct measurement of PAH concentrations in interstitial water may be used to evaluate
3 this possibility and, where necessary, derive site-specific sediment guidelines which account for local
4 differences in partitioning behavior.
5
6 6.8 AQUEOUS SOLUBILITY UNDER NON-STANDARD CONDITIONS
7
8 It has been long established that organic compounds are generally less soluble in aqueous
9 solutions at colder temperatures than at warmer, and in salt solutions such as seawater, than in
10 freshwater, a phenomenon termed the salting-out effect (May, 1980; Schwarzenbach et al., 1993; Xie
11 et al., 1997). Setschenow (1889) derived an empirical relationship for the magnitude of the salting-out
12 effect:
13
14 log.ofSo /'S*J = *s C^ (6-9)
15
16 where 'S0 and '5%,, are the aqueous solubilities of the solute hi fresh and saltwater (hi mol/L at
17 temperature (°C), respectively, Ks is the Setschenow constant (L/mol) for the salt solution and the
18 solute of interest, and C^, is the molar salt concentration. A one molar salt solution (NaCl) is
19 approximately equivalent to 48%o sea water (Owen and Brinkley, 1941), and Ks was found to be
20 essentially invariant with temperatures from 1 to 30°C, averaging 0.28 ± 0.02 (mean ± SE) (May,
21 1980) for 9 PAHs. Temperature has been shown to have a non-linear effect on PAHs solubilities
22 (May, 1980). Concentrations of 9 compounds: naphthalene, fluorene, phenanthrene, 1-
23 methylphenanthrene, anthracene, fluoranthene, pyrene, benz(a)anthracene, and chrysene were
24 computed for distilled water at temperatures between 5 and 30°C using the relationships of May (1980)
Final Draft PAH Mixtures ESG Document 6-21 5 April 2000
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sc (6-8)
2
3 where, ATd is the partition coefficient for the expanded partitioning equation,^ and/sc are the fraction
4 organic carbon and fraction soot carbon, respectively, and K^ and K^ are the organic carbon and soot
5 carbon partition coefficients.
6
7 6.7.2 Implications to Derivation of ESG
8
9 Irrespective of the mechanism, this issue has the potential to affect the predictive power and
10 accuracy of the total PAH ESG. Since the presence of soot or related materials are associated with
11 reduced concentrations of PAH in interstitial water, one would presume that this results in decreased
12 bioavailability of PAHs, a phenomenon demonstrated by West et al. (2000). This, hi turn, would make
13 the total PAH ESG derived here overprotective, because the X^-based partitioning model would
14 overpredict chemical activity and, therefore, concentrations of PAH in interstitial water and organisms.
15 . Nonetheless, empirical data suggest that this error may not be pervasive; most applications of
16 the PAH mixture narcosis model to toxicity data for field-collected sediments show good predictive
17 ability for the ESG (see Section 5.3). This may be because most sediments that are sufficiently
18 contaminated to cause narcosis are contaminated by PAH sources that exhibit normal partitioning
19 behavior, such as creosote and other petrogenic sources. In their study of PAH-contaminated
20 sediments, Ozretich et al. (2000b) found that discrepancies between measured and predicted
21 partitioning behavior predominated in sediments with lower PAH concentrations, while those with
22 higher PAH concentrations showed partitioning behavior closer to that predicted from published
23 KQW/KQC relationships. This differential behavior was attributed to the presence of two PAH sources,
24 with creosote being the source causing the highest levels of contamination and toxicity.
Final Draft PAH Mixtures ESG Document 6-20 5 April 2000
-------
1 In cases where it is suspected that soot, coal, or other materials may be causing unusual
2 partitioning, direct measurement of PAH concentrations in interstitial water may be used to evaluate
3 this possibility and, where necessary, derive site-specific sediment guidelines which account for local
4 differences in partitioning behavior.
5
6 6.8 AQUEOUS SOLUBILITY UNDER NON-STANDARD CONDITIONS
7
8 It has been long established that organic compounds are generally less soluble in aqueous
9 solutions at colder temperatures than at warmer, and hi salt solutions such as seawater, than in
10 freshwater, a phenomenon termed the salting-out effect (May, 1980; Schwarzenbach et al., 1993; Xie
11 et al., 1997). Setschenow (1889) derived an empirical relationship for the magnitude of the salting-out
12 effect:
13
14 ••-logwCV«J=^C^ (6-9)
15
16 where CS0 and tSVn are the aqueous solubilities of the solute in fresh and saltwater (hi mol/L at
17 temperature (°C), respectively, Ks is the Setschenow constant (L/mol) for the salt solution and the
18 solute of interest, and C^, is the molar salt concentration. A one molar salt solution (NaCl) is
19 approximately equivalent to 48%o sea water (Owen and Brinkley, 1941), and Ks was found to be
20 essentially invariant with temperatures from 1 to 30°C, averaging 0.28 ± 0.02 (mean ± SE) (May,
21 1980) for 9 PAHs. Temperature has been shown to have a non-linear effect on PAHs solubilities
22 (May, 1980). Concentrations of 9 compounds: naphthalene, fluorene, phenanthrene, 1-
23 methylphenanthrene, anthracene, fluoranthene, pyrene, benz(a)anthracene, and chrysene were
24 computed for distilled water at temperatures between 5 and 30°C using the relationships of May (1980)
Final Draft PAH Mixtures ESG Document 6-21 5 April 2000
-------
1 and are compared with the compounds' concentrations at 25 °C (Figure 6-5). The least-squares
2 exponential representation of the data is as follows
3
4 (1S0 / "So) _= 0.261 x e005361, r2 - 0.959 (6-10)
5
6 where ^S,, is the commonly reported solubility of a compound. Although naphthalene's solubility has
7 the least response to temperature of PAHs, estimates from Equation 6-10 are only -f 8% and -30%
8 inaccurate for naphthalene at the temperature extremes (Figure 6-5).
9 The solubility of PAHs under environmental conditions can be estimated from the following
10 relationship that is a combination of Equations 6-9 and 6-10 using the average Setschenow constant:
11
12
% x 10 *0005«^' (6-H)
13
14 when %o is the salinity of the sea water. This correction for solubility can be used as part of the
15 procedures to modify this ESG for site-specific differences.
Final Draft PAH Matures ESG Document 6-22 5 April 2000
-------
i SECTION 7
2 SEDIMENT GUIDELINE STATEMENT
3 7.1 SEDIMENT GUIDELINE STATEMENT
4
5 The procedures described in this document and in the "Technical Basis for the Derivation of
6 Equilibrium Partitioning Sediment Guidelines (ESGs) for the Protection of Benthic Organisms:
7 Nonionic Organics" (U.S. EPA, 2000a) indicate that, except possibly where a locally important species
8 is very sensitive or benthic organisms are exposed to both significant amounts of PAHs and UV light,
9 benthic organisms should be acceptably protected from the effects of PAH mixtures in freshwater and
10 saltwater sediments if the SESGTUFCV is less than or equal to 1.0
11
12 ESG = ZESGTU = - 3 - < 1. 0 (7-1)
' » CoQPAHi,FCVi
13 If the SESGTUpcv is equal to or less than 1.0 then the sediment meets the guideline and benthic
14 organisms are acceptably protected from PAH mixture-induced sediment toxicity. If the SESGTUFCV is
15 greater than 1.0 the ESG for mixtures of PAHs is violated and there is reason to believe that specific
16 sediment may be unacceptably contaminated by the mixture of PAHs.
17 As indicated, this sediment-specific guideline is the sum of the quotients of the concentrations
18 of individual PAHs in a sediment, on an organic carbon basis, each divided by its respective
19 Qc.pAHi.Fcvi- At a minimum, the definition of total PAHs for this ESG requires quantification of the 34
20 PAHs analyzed by the U.S. EPA as part of the EMAP and REMAP programs (PAHs are identified in
21 bold in Table 3-4) or an estimate of 2ESGTUFCV based on the 95% uncertainty values (see Section 6.2,
Final Draft PAH Mixtures ESG Document 7-1 5 April 2000
-------
1 and are compared with the compounds' concentrations at 25°C (Figure 6-5). The least-squares
2 exponential representation of the data is as follows
3
4 CS0 / ^ _= 0.261 xea(K3&, r2^ 0.959 (6-10)
5
6 where ^S,, is the commonly reported solubility of a compound. Although naphthalene's solubility has
7 the least response to temperature of PAHs, estimates from Equation 6-10 are only +8% and -30%
8 inaccurate for naphthalene at the temperature extremes (Figure 6-5).
9 The solubility of PAHs under environmental conditions can be estimated from the following
10 relationship that is a combination of Equations 6-9 and 6-10 using the average Setschenow constant:
11
12 'S*. = 1S0 x 10 ^•0005«3'*° (6-H)
13
14 when %o is the salinity of the sea water. This correction for solubility can be used as part of the
15 procedures to modify this ESG for site-specific differences.
Final Draft PAH Mixtures ESG Document 6-22 5 April 2000
-------
1 SECTION 7
2 SEDIMENT GUIDELINE STATEMENT
3 7.1 SEDIMENT GUIDELINE STATEMENT
4 ~ •
5 The procedures described in this document and in the "Technical Basis for the Derivation of
6 Equilibrium Partitioning Sediment Guidelines (ESGs) for the Protection of Benthic Organisms:
7 Nonionic Organics" (U.S. EPA, 2000a) indicate that, except possibly where a locally important species
8 is very sensitive or benthic organisms are exposed to both significant amounts of PAHs and UV light,
9 benthic organisms should be acceptably protected from the effects of PAH mixtures in freshwater and
10 saltwater sediments if the SESGTUFCV is less than or equal to 1.0
11
12 ESG = XESGTU = - 9 - < 7. 0
CoQPAffi,FCVi
13 If the SESGTUpcv is equal to or less than 1.0 then the sediment meets the guideline and benthic
14 organisms are acceptably protected from PAH mixture-induced sediment toxicity. If the SESGTUFCV is
15 greater than 1.0 the ESG for mixtures of PAHs is violated and there is reason to believe that specific
16 sediment may be unacceptably contaminated by the mixture of PAHs.
17 As indicated, this sediment-specific guideline is the sum of the quotients of the concentrations
18 of individual PAHs in a sediment, on an organic carbon basis, each divided by its respective
19 Qc.pAHi.Fcv,- At a minimum, the definition of total PAHs for this ESG requires quantification of the 34
20 PAHs analyzed by the U.S. EPA as part of the EMAP and REMAP programs (PAHs are identified in
21 bold in Table 3-4) or an estimate of SESGTUFCV based on the 95% uncertainty values (see Section 6.2,
Final Draft PAH Mixtures ESG Document 7- 1 5 April 2000
-------
1 Table 6-1).
2 The ESGs are intended to protect benthic organisms from direct toxicity associated with
3 ' exposure to PAH-contaminated sediments. They are not designed to protectaquatic systems from PAH
4 release associated, for example, with the transport of PAHs into the food web either from sediment
5 ingestion or the ingestion of contaminated benthos.
6
7 7.2 SPECIAL CONSIDERATIONS
8
9 To establish a national guideline, certain assumptions are necessary. It is possible that site-
10 specific conditions may affect the applicability of the national guideline. These include:
11
12 1. ,. Fewer than 34 PAHs have been measured. Particularly in cases where historical data are
13 being examined, chemistry data may be available for fewer than the 34 PAHs recommended
14 •-. ., for this guideline. Calculating DESGTUpcv directly using fewer PAHs will generally cause the
15 guideline to be underprotective because PAH mixtures found in the environment typically
16 contain substantial concentrations of PAHs outside the suites of 13 or 23 PAHs commonly
17 . • measured in monitoring programs. EPA has conducted an analysis of PAH distributions across
18 many geographic regions and developed adjustment factors that can be used to adjust
19 SESGTUpcv based on subsets of 13 or 23 PAHs with varying degrees of certainty (see Section
20 6.2). In some applications of the PAH ESG, it may be important to minimize the frequency of
21 false negatives (sediments judged to be acceptable when they are not). For these cases, the
22 SESGTUFCV calculated from a subset of 13 PAHs (see Table 6-2 for listing) can be multiplied
23 by 11.5, or the SESGTUpcv calculated from a subset of 23 PAHs (see Table 6-2 for listing) can
24 be multiplied by 4.14 to achieve 95% confidence that the actual SESGTUFCV for all 34 PAHs
Final Draft PAH Matures ESG Document 7-2 5 April 2000
-------
1 would not be higher than the calculated value.
2
3 Use of these adjustment factors introduces uncertainty into the calculation of the £ESGTUF
4 Consequently, a conservative estimate of the 2ESGTUFCV is necessary, to accomplish this the
5 uncertainty for the 95% confidence level is applied. This means that most of the sediments
6 may contain fewer SESOTUpcv than indicated by the calculation. In cases where less
7 conservative assumptions are appropriate, factors with lower confidence can be applied, as
8 detailed in Section 6.2. In any case, avoiding the uncertainty introduced by the use of
9 adjustment factors is the primary reason EPA recommends that wherever possible, a more
10 complete PAH analysis is undertaken. In cases where adjustment factors are used and the
11 calculated SESGTUpcv are greater than the ESG, it may be particularly advantageous to
12 eliminate the uncertainty by conducting additional analyses.
13
14 2. Interaction of PAHs with UV light. Guidelines calculated in this document are based on
15 narcotic toxicity only and do not consider enhanced toxicity that can occur if PAH-exposed
16 organisms are simultaneously exposed to UV light. In environments where significant sunlight
17 penetrates to the sediment and benthic organisms are exposed to UV light, the ESG may be
18 underprotective. Consult Section 6.4 for additional details.
19
20 3. Influence of soot and coal on PAH partitioning. Literature data have indicated that soot
>
21 and/or coal particles in sediment may contain PAHs that partition less to interstitial water than
22 those associated with typical organic carbon, thereby causing the guideline to be
23 overprotective. The influence of these-phases can be assessed by measuring concentrations of
24 PAHs directly in interstitial water and comparing these measures with concentrations predicted
Final Draft PAH Mixtures ESG Document 7-3 5 April 2000
-------
1 Table 6-1).
2 The ESGs are intended to protect benthic organisms from direct toxicity associated with
3 ' exposure to PAH-contaminated sediments. They are not designed to protect aquatic systems *frorn PAH
4 release associated, for example, with the transport of PAHs into the food web either from sediment
5 ingestion or the ingestion of contaminated benthos.
6
7 7.2 SPECIAL CONSIDERATIONS
8
9 To establish a national guideline, certain assumptions are necessary. It is possible that site-
10 specific conditions may affect the applicability of the national guideline. These include:
11
12 1. . Fewer than 34 PAHs have been measured. Particularly hi cases where historical data are
13 being examined, chemistry data may be available for fewer than the 34 PAHs recommended
14 -•• . for this guideline. Calculating SESGTUpcy directly using fewer PAHs will generally, cause the
15 guideline to be underprotective because PAH mixtures found in the environment typically
16 contain substantial concentrations of PAHs outside the suites of 13 or 23 PAHs commonly
17 . • measured in monitoring programs. EPA has conducted an analysis of PAH distributions across
18 many geographic regions and developed adjustment factors that can be used to adjust
19 SESGTUFCV based on subsets of 13 or 23 PAHs with varying degrees of certainty (see Section
20 6.2). In some applications of the PAH ESG, it may be important to minimize the frequency of
21 false negatives (sediments judged to be acceptable when they are not). For these cases, the
22 SESGTUFCV calculated from a subset of 13 PAHs (see Table 6-2 for listing) can be multiplied
23 by 11.5, or the SESGTUpcv calculated from a subset of 23 PAHs (see Table 6-2 for listing) can
24 be multiplied by 4.14 to achieve 95% confidence that the actual SESGTUFCV for all 34 PAHs
Final Draft PAH Matures ESG Document 7-2 5 April 2000
-------
-*FCV-
1 would not be higher than the calculated value.
2
i
3 Use of these adjustment factors introduces uncertainty into the calculation of the SESGTUf
4 Consequently, a conservative estimate of the SESGTUFCV is necessary, to accomplish this the
5 uncertainty for the 95% confidence level is applied. This means that most of the sediments
6 may contain fewer SESGTUpcv than indicated by the calculation. In cases where less
7 conservative assumptions are appropriate, factors with lower confidence can be applied, as
8 detailed in Section 6.2. In any case, avoiding the uncertainty introduced by the use of
9 adjustment factors is the primary reason EPA recommends that wherever possible, a more
10 complete PAH analysis is undertaken. In cases where adjustment factors are used and the
11 calculated ZESGTUpcv are greater than the ESG, it may be particularly advantageous to
12 eliminate the uncertainty by conducting additional analyses.
13
14 2. Interaction of PAHs with UV light. Guidelines calculated in this document are based on
15 narcotic toxicity only and do not consider enhanced toxicity that can occur if PAH-exposed
16 organisms are simultaneously exposed to UV light. In environments where significant sunlight
17 penetrates to the sediment and benthic organisms are exposed to UV light, the ESG may be
18 underprotective. Consult Section 6.4 for additional details.
19
20 3. Influence of soot and coal on PAH partitioning. Literature data have indicated that soot
.•
21 and/or coal particles in sediment may contain PAHs that partition less to interstitial water than
22 those associated with typical organic carbon, thereby causing the guideline to be
23 overprotective. The influence of these phases can be assessed by measuring concentrations of
24 PAHs directly in interstitial water and comparing these measures with concentrations predicted
Final Draft PAH Mixtures ESG Document 7-3 5 April 2000
-------
1 by EqP. See Section 6.7 and the site-specific ESG guidelines (U.S. EPA, 20000 for further
2 discussion.
3 *
-4 4. Unusual composition of organic carbon. Partition coefficients used for calculating the
5 national PAH mixture ESG are based on measured partitioning from natural organic carbon in
6 typical field sediments. Some sediments influenced heavily by industrial activities may contain
7 sources of organic carbon whose partitioning properties are not similar, such as rubber, animal
8 processing wastes (e.g., hair or hide fragments), or wood processing wastes (bark, wood fiber
9 or chips). Relatively undegraded woody debris or plant matter (e.g., roots, leaves) may also
10 contribute organic carbon that results in partitioning different from that of typical organic
11 carbon. Sediments with large amounts of these materials may show higher concentrations of
12 chemicals in interstitial water than would be predicted using generic KQC values, making the
13 ESG underprotective. Direct analysis of interstitial water can be used to evaluate this
14 possibility (see U.S. EPA, 2000a,f).
15
16 5. Presence of additional narcotic compounds. The PAH mixture ESG is based on the
17 additivity of non-polar narcotic toxicants, such as PAHs. However, some sediments may
18 contain additional compounds that would contribute to narcotic toxicity, such as chlorobenzenes
19 or PCBs (note: PCBs may also cause adverse effects through bioaccumulation and transfer to
20 higher trophic levels; these bioaccumulative effects are not addressed by this narcosis-based
21 ESG and should be evaluated separately). The presence of additional non-polar narcotic
22 chemicals may make the PAH mixture ESG underprotective, because the ESG itself only
23 addresses that part of the narcotic potency caused by PAHs. Di Toro et al. (2000) and Di Toro
24 and McGrath, 2000) describe methods by which the contributions of other narcotic chemicals
Final Draft PAH Mixtures ESG Document 7-4 5 April 2000
-------
1 can be incorporated into an ESG-type assessment.
2
*.
3 6. Site-specific temperature and salinity corrections. Temperature and salinity both affect
4 solubility of PAHs and can therefore affect the solubility-constrained maximum contribution of
5 individual PAHs to the overall ESG. Solubilities used in this document are calculated for 25 °C
6 and salinity less than l%o. Solubilities can be recalculated to meet site specific conditions
7 using procedures described in Section 6.8. Within a range of 0 to 35°C and salinity from 0 to
8 35%o, solubility can be expected to decrease by a factor of about 30 to 40% with decrease in
9 temperature or increase in salinity. Site-specific recalculation of solubilities will only affect
10 SESOTUpcv in cases where the contribution of one or more PAHs are solubility constrained
11 (see Section 6.8).
Final Draft PAH Mixtures ESG Document 7-5 5 April 2000
-------
1 by EqP. See Section 6.7 and the site-specific ESG guidelines (U.S. EPA, 2000f) for further
2 discussion.
3 *
•4 4. Unusual composition of organic carbon. Partition coefficients used for calculating the
5 national PAH mixture ESG are based on measured partitioning from natural organic carbon in
6 typical field sediments. Some sediments influenced heavily by industrial activities may contain
7 sources of organic carbon whose partitioning properties are not similar, such as rubber, animal
8 processing wastes (e.g., hair or hide fragments), or wood processing wastes (bark, wood fiber
9 or chips). Relatively undegraded woody debris or plant matter (e.g., roots, leaves) may also
10 contribute organic carbon that results in partitioning different from that of typical organic
11 carbon. Sediments with large amounts of these materials may show higher concentrations of
12 chemicals in interstitial water than would be predicted using generic K^ values, making the
13 ESG underprotective. Direct analysis of interstitial water can be used to evaluate this
14 possibility (see U.S. EPA, 2000a,f).
15
16 5. Presence of additional narcotic compounds. The PAH mixture ESG is based on the
17 additivity of non-polar narcotic toxicants, such as PAHs. However, some sediments may
18 contain additional compounds that would contribute to narcotic toxicity, such as chlorobenzenes
19 or PCBs (note: PCBs may also cause adverse effects through bioaccumulation and transfer to
20 higher trophic levels; these bioaccumulative effects are not addressed by this narcosis-based
21 ESG and should be evaluated separately). The presence of additional non-polar narcotic
22 chemicals may make the PAH mixture ESG underprotective, because the ESG itself only
23 addresses that part of the narcotic potency caused by PAHs. Di Toro et al. (2000) and Di Toro
24 and McGrath, 2000) describe methods by which the contributions of other narcotic chemicals
Final Draft PAH Mixtures ESG Document 7-4 5 April 2000
-------
1 can be incorporated into an ESG-type assessment.
2
•*.
3 6. Site-specific temperature and salinity corrections. Temperature and salinity both affect
4 solubility of PAHs and can therefore affect the solubility-constrained maximum contribution of
5 individual PAHs to the overall ESG. Solubilities used in this document are calculated for 25°C
6 and salinity less than l%o. Solubilities can be recalculated to meet site specific conditions
7 using procedures described in Section 6.8. Within a range of 0 to 35°C and salinity from 0 to
8 35%o, solubility can be expected to decrease by a factor of about 30 to 40% with decrease in
9 temperature or increase in salinity. Site-specific recalculation of solubilities will only affect
10 SESOTUpcv in cases where the contribution of one or more PAHs are solubility constrained
11 (see Section 6.8).
Final Draft PAH Mixtures ESG Document 1-5 5 April 2000
-------
i SECTIONS
2 REFERENCES
»
3
4 Abernethy S, Bobra AM, Sliiu WY, Wells PG , Mackay D. 1986. Acute lethal toxicity of
5 hydrocarbons and chlorinated hydrocarbons to two planktonic crustaceans: the key role of
6 organism-water partitioning. AquatToxicol 8:163-174.
7
8 Abernethy S, Mackay D, McCarty L. 1988. Volume fraction correlation for narcosis in aquatic
9 organisms: the key role of partitioning. Environ Toxicol Chem 7:469-481.
10
11 Academy of Natural Sciences. 1981. Early life stage studies using the fathead minnow (Pimephales
12 protnelas) to assess the effects of isophorone and acenaphthene. Final report to U.S. EPA,
13 Cincinnati, OH. Academy of Natural Sciences, Philadelphia, PA. 26 pp.
14
15 Adams D, O'Conner J, Weisberg SB. 1996. Sediment quality of the NY/NJ harbor system. An
16 investigation under the Regional Environmental Monitoring and Assessment Program (R-
17 EMAP). Draft Final Report. United States Environmental Protection Agency.
18
19 Adams WJ, Kimerle RA, Mosher RG. 1985. Aquatic safety assessment of chemicals sorbed to
20 sediments. In Cardwell RD, 'Purdy R, Banner RC, eds. Aquatic Toxicology and Hazard
21 Assessment: Seventh Symposium. STP 854. American Society for Testing and Materials,
22 Philadelphia, PA, pp. 429-453.
23
Final Draft PAH Mixtures ESG Document 8-1 5 April 2000
-------
1 Adema, DMM. 1978. Daphnia magna as test organism in acute and chronic toxicity experiments.
2 Hydrobiol 59:125-134.
3 :
4 Ahmad N, Benoit D, Brooke L, Call D, Carlson A, DeFoe D, Huot J, Moriariry A, Richter J, Shubat
5 P, Veith G, Wallbridge C. 1984. Aquatic toxicity tests to characterize the hazard of volatile
6 organic chemicals in water: A toxicity data summary - Parts I and EL EPA-600-3-84-009.
7
8 Aitchison J, Brown J. 1957. The Lognonnal Distribution. Cambridge University Press, Cambridge,
9 England.
10
11 Alexander HC, McCarty WM, Bartlett EA. 1978. Toxicity of perchloroethylene, trichloroethylene,
12 1,1,1-trichloroethane and methylene chloride to fathead minnows. Butt Environ Contam Toxicol
13 20:344-352.
14
15 Allred PM, Giesy JP. 1985. Solar radiation-induced toxicity of anthracene to Daphnia pulex. Environ
16 Toxicol Chem 4:219-226.
17
18 American Society for Testing and Materials. 1993. Guide for conducting 10-day static sediment toxicity
19 tests with marine and estuarine amphipods. E 1367-92. In Annual Book of ASTM Standards,
20 Vol. 11.04, Philadelphia, PA, pp 1138-1163.
21
22 American Society for Testing and Materials. 1998. Standard guide for conducting early life stage
23 toxicity tests with fishes. E1241-92. In: Annual Book ASTM Standards. Philadelphia, PA. pp.
24 550-577.
final Draft PAH Mixtures ESG Document 8-2 5 April 2000
-------
i SECTION 8
2 REFERENCES
»
4 Abernethy S, BobrS AM, Sliiu WY, Wells PG , Mackay D. 1986. Acute lethal toxicity of
5 hydrocarbons and chlorinated hydrocarbons to two planktonic crustaceans: the key role of
6 organism-water partitioning. AquatToxicolS:163-174.
7
8 Abernethy S, Mackay D, McCarty L. 1988. Volume fraction correlation for narcosis in aquatic
9 organisms: the key role of partitioning. Environ Toxicol Oiem 7:469-481.
10
11 Academy of Natural Sciences. 1981. Early life stage studies using the fathead minnow (Pimephales
12 promelas) to assess the effects of isophorone and acenaphthene. Final report to U.S. EPA,
13 Cincinnati, OH. Academy of Natural Sciences, Philadelphia, PA. 26 pp.
14
15 Adams D, O'Conner J, Weisberg SB. 1996. Sediment quality of the NY/NJ harbor system. An
16 investigation under the Regional Environmental Monitoring and Assessment Program (R-
17 EMAP). Draft Final Report. United States Environmental Protection Agency.
18
19 Adams WJ, Kimerle RA, Mosher RG. 1985. Aquatic safety assessment of chemicals sorbed to
20 sediments. In Cardwell RD.'Purdy R, Banner RC, eds. Aquatic Toxicology and Hazard
21 Assessment: Seventh Symposium. STP 854. American Society for Testing and Materials,
22 Philadelphia, PA, pp. 429-453.
Final Draft PAH Matures ESG Document 8-1 5 April 2000
-------
1 Adema, DMM. 1978. Daphnia magna as test organism in acute and chronic toxicity experiments.
2 Hydrobiol 59:125-134.
$
3
4 Ahmad N, Benoit^D, Brooke L, Call D, Carlson A, DeFoe D, Huot J, Moriarity A, Richter J, Shubat
5 P, Veith G, Wallbridge C. 1984. Aquatic toxicity tests to characterize the hazard of volatile
6 organic chemicals in water: A toxicity data summary - Parts I and II. EPA-600-3-84-009.
7
8 Aitchison J, Brown J. 1957. The Lognonnal Distribution. Cambridge University Press, Cambridge,
9 England.
10
11 Alexander HC, McCarty WM, Bartlett EA. 1978. Toxicity of perchloroethylene, trichloroethylene,
12 1,1,1-trichloroethane and methylene chloride to fathead minnows. Bull Environ Contam Toxicol
13 20:344-352.
14
15 Allred PM, Giesy JP. 1985. Solar radiation-induced toxicity of anthracene to Daphnia pulex. Environ
16 Toxicol Chem 4:219*226.
17
18 American Society for Testing and Materials. 1993. Guide for conducting lO-o'ay static sediment toxicity
19 tests with marine and estuarine amphipods. E 1367-92. In Annual Book of ASTM Standards,
20 Vol. 11.04, Philadelphia, PA, pp 1138-1163.
21
22 American Society for Testing and Materials. 1998. Standard guide for conducting early life stage
23 toxicity tests with fishes. E1241-92. In: Annual Book ASTM Standards. Philadelphia, PA. pp.
24 550-577.
Final Draft PAH Mixtures ESG Document 8-2 5 April 2000
-------
1 Anderson B, Hunt J, Tudor S, Newman J, Tjeerdema R, Fairey R, Oakden J, Bretz C, Wilson C,
2 LaCaro F, Stephenson M, Puckett M, Long E, Fleming T, Summers K. 1996. Chemistry,
3 toxicity and benthic community conditions in sediments of the southern California bays and
4 estuaries. Draft Report. California State Water Resources Control Board.
5
6 Ankley GT, Collyard SA, Monson PD, Kosian PA. 1994. Influence of ultraviolet light on the toxicity
7 of sediments contaminated with polycyclic aromatic hydrocarbons. Environ Toxicol Chem
8 13:1791-1796.
9
10 Ankley GT, Erickson RJ, Phipps GL, Mattson VR, Kosian PA, Sheedy BR, Cox JS. 1995. Effects of
11 light intensity on the phototoxicity of fluoranthene to a benthic macroinvertebrate. Environ Sci
12 andTechnol 29:2828-2833.
13
14 Ankley GT, Mekenyan OG, Kosian PA, Makynen EA, Mount DR, Monson PD, Call CJ. 1996.
15 Identification of phototoxic polycyclic aromatic hydrocarbons in sediments through sample
16 fractionation and QSAR analysis. SAR and QSAR in Environ Res 5:177-183.
17
18 Ankley GT, Erickson RJ, Sheedy BR, Kosian PA, Mattson VR, Cox JSD. 1997. Evaluation of models
19 for predicting the phototoxic potency of polycyclic aromatic hydrocarbons. Aquat Toxicol
20 37:37-50.
21
22 Arfsten DP, Schaeffer DJ, Mulveny DC. 1996. The effects of near ultraviolet radiation on the toxic
23 effects of polycyclic aromatic hydrocarbons in animals and plants: a review. Ecotoxicol
24 Environ Safety 33:1-24.
Final Draft PAH Mixtures ESG Document 8-3 5 April 2000
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1 Armstrong RD, Beck PO, Kung MT. 1984. Algorithm 615. The best subset of parameters in least
2 absolute value regression. ACM Transactions on Mathmatical Software. Volume 10. pp. 202-
3 206. *
4
5 Battelle Ocean Sciences. 1987. Acute toxicity of phenanthrene to saltwater animals. Report to U.S.
6 EPA Criteria and Standards Division. Battelle Ocean Sciences, Duxbury, MA.
7
8 Bender ME, Roberts MH, deFur PO. 1987. Unavailability of polynuclear aromatic hydrocarbons from
9 coal particles to the eastern oyster. Environ Pollut 44:243-260.
10
11 Bengtsson B, Renberg L, Tarkpea M. 1984. Molecular structure and aquatic toxicity - an example with
12 Cl - C13 aliphatic alcohols. Chemo 13:613-622.
13
14 Bently RE, Heitmuller T m, Sleight BH, Parrish PR. 1975. Acute toxicity of chloroform to bluegill
15 (Lepomis macrochirus), rainbow trout (Salmo gaidneri) and pink shrimp (Penaeus duoranuri).
16 Contract no. WA-6-99-1414-b. U.S. EPA.
17
18 Birge WJ, Black JA, Ballard ST, McDonnell WE. 1982. Acute toxicity testing with freshwater fish.
19 Contract No. 68-01-6201. Final Report Task 11 and 111. U.S. EPA.
20
21 Black JJ. 1983. Field and laboratory studies of environmental carcinogenesis in Niagara River fish. J.
22 Great Lakes Res 9(2): 326-334.
23
24 Boese BL, Lamberson JO, Swartz RC, Ozretich RJ, Cole FA. 1998. Photoinduced toxicity of PAHs
Final Draft PAH Mixtures ESG Document 8-4 5 April 2000
-------
1 Anderson B, Hunt J, Tudor S, Newman J, Tjeerdema R, Fairey R, Oakden J, Bretz C, Wilson C,
2 LaCaro F, Stephenson M, Puckett M, Long E, Fleming T, Summers K. 1996. Chemistry,
3 toxicity and benthic community conditions in sediments of the southern California bays and
4 estuaries. Draft Report. California State Water Resources Control Board.
5
6 Ankley GT, Collyard SA, Monson PD, Kosian PA. 1994. Influence of ultraviolet light on the toxicity
7 of sediments contaminated with polycyclic aromatic hydrocarbons. Environ Toxicol Chem
8 13:1791-1796.
9
10 Ankley GT, Erickson RJ, Phipps GL, Mattson VR, Kosian PA, Sheedy BR, Cox JS. 1995. Effects of
11 light intensity on the phototoxicity of fluoranthene to a benthic macroinvertebrate. Environ Sci
12 andTechnol 29:2828-2833.
13
14 Ankley GT, Mekenyan OG, Kosian PA, Makynen EA, Mount DR, Monson PD, Call CJ. 1996.
15 Identification of phototoxic polycyclic aromatic hydrocarbons in sediments through sample
16 fractionation and QSAR analysis. SAR and QSAR in Environ Res 5:177-183.
17
18 Ankley GT, Erickson RJ, Sheedy BR, Kosian PA, Mattson VR, Cox JSD. 1997. Evaluation of models
19 for predicting the phototoxic potency of polycyclic aromatic hydrocarbons. Aquat Toxicol
20 37:37-50.
21
22 Arfsten DP, Schaeffer DJ, Mulveny DC. 1996. The effects of near ultraviolet radiation on the toxic
23 effects of polycyclic aromatic hydrocarbons in animals and plants: a review. Ecotoxicol
24 Environ Safety 33:1-24.
Final Draff PAH Mixtures ESG Document 8-3 5 April 2000
-------
1 Armstrong RD, Beck PO, Kung MT. 1984. Algorithm 615. The best subset of parameters in least
2 absolute value regression. ACM Transactions on Mathmatical Software. Volume 10. pp. 202-
3 206.
4
5 Battelle Ocean Sciences. 1987. Acute toxicity of phenanthrene to saltwater animals. Report to U.S.
6 EPA Criteria and Standards Division. Battelle Ocean Sciences, Duxbury, MA.
7
8 Bender ME, Roberts MH, deFur PO. 1987. Unavailability of polynuclear aromatic hydrocarbons from
9 coal particles to the eastern oyster. Environ Pollut 44:243-260.
10
11 Bengtsson B, Renberg L, Tarkpea M. 1984. Molecular structure and aquatic toxicity - an example with
12 Cl - C13 aliphatic alcohols. Chemo 13:613-622.
13
14 Benfly RE, Heitmuller T in, Sleight BH, Paxrish PR. 1975. Acute toxicity of chloroform to bluegill
15 (Lepomis macrochirus), rainbow trout (Salmo gaidneri) and pink shrimp (Penaeus duorarum).
16 Contract no. WA-6-99-1414-b. U.S. EPA.
17
18 Birge WJ, Black JA, Ballard ST, McDonnell WE. 1982. Acute toxicity testing with freshwater fish.
19 Contract No. 68-01-6201. Final Report Task 11 and 111. U.S. EPA.
20
21 Black JJ. 1983. Field and laboratory studies of environmental carcinogenesis in Niagara River fish. /.
22 Great Lakes Res 9(2): 326-334.
23
24 Boese BL, Lamberson JO, Swartz RC, Ozretich RJ, Cole FA. 1998. Photoinduced toxicity of PAHs
Final Draft PAH Mixtures ESG Document 8-4 5 April 2000
-------
1 and alkylated PAHs to a marine infaunal amphipod (Rhepoxynius abronius). Arch Environ
2 Contamin Toxicol 34:235-240.
3 : *
4 Boese BL, Ozretich RJ, Lamberson JO, Swartz RC, Cole FA, Pelletier J, Jones J. 1999. Toxicity and
5 phototoxicity of mixtures of highly lipophilic PAH compounds in marine sediments: can the
6 ZPAH model be extrapolated? Arch Environ Contamin Toxicol 36:270-280.
7
8 Bowling JW, Leversee GJ, Landrum PF, Giesy JP. 1983. Acute mortality of
9 anthracene-contaminated fish exposed to sunlight. Aquat Toxicol 3:79-90.
10
11 Bradbury S, Carlson R, Henry T. 1989. Polar narcosis in aquatic organisms. Aquat Toxicol Haz Assess
12 12:59-73.
13
14 Brenniman G, Hartung R, Weber WJ, Jr. 1976. A continuous flow bioassay method to evaluate the
15 effects of outboard motor exhausts and selected aromatic toxicants on fish. Water Res 10:165-
16 169.
17
18 Brezonik PL. 1994. Chemical Kinetics and Process Dynamics in Aquatic Systems. CRC Press, Inc.,
19 Boca Raton, Florida.
20
21 Bridie AL, Wolff CJM, Winter M. 1979. The acute toxicity of some petrochemicals to goldfish. Water
22 Res 13:623-626.
23
24 Bringman G, Kuhn R. 1959. Vergleichende wasser -= toxikologische untersuchungen an bakterien. algen
Final Draft PAH Mixtures ESG Document 8-5 5 April 2000
-------
1 and kleinkrebsen. Gesundheits Ingenieur 80:115.
2
3 Broderius S, Kahl M. 1985. Acute toxicity of organic chemical mixtures to the fathead minnow. Aquat
4 Toxicol 6:307-322.
5
6 Broman D, Naf C, Wik M, Renberg I. 1990. The importance of spheroidal carbonaceous oarticles
7 (SCPs) for the distribution of paniculate polycyclic aromatic hydrocarbons (PAHs) in an
8 estuarine-like urban coastal water area. Chemo 21:69-77.
9
10 Brooke LT. 1991. Summary of results of acute and chronic exposures of fluoranthene with and without
11 ultraviolet (UV) light to various organisms. Memorandum to Walter J. Berry, NHEERL,
12 Naragansett, RI. December 3, 1991.
13
i
14 Brooke LT. 1993. Conducting toxicity tests with freshwater organisms exposed to dieldrin,
15 fluoranthene and phenanthrene. Report to Robert L. Spehar, Project Officer, U.S. EPA.
16 Environmental Research Laboratory-Duluth, Duluth, MN. I8pp.
17
18 Brooke LT. 1994. Acute phenanthrene toxicity to Daphnia magna. Contract No. 68-C 1-0034 Report
19 to R.L. Spehar, U.S. EPA , WA No. 2-14.
20
21 Buccafusco RJ, Ells SJ, LeBlanc GA. 1981. Acute toxicity of priority pollutants to bluegill (Lepomis
22 macrochirus). Bull Environm Contain Toxicol 26:446-452.
23
24 Bunton TE. 1996. Experimental Chemical Carcinogenesis in Fish. Toxicologic Pathology.24(5): 603-
Final Draft PAH Mixtures ESG Document 8-6 5 April 2000
-------
1 and alkylated PAHs to a marine infaunal amphipod (Rhepoxynius abronius). Arch Environ
2 Contamin Toxicol 34:235-240.
3 .. ' *
4 Boese BL, Ozretich RJ, Lamberson JO, Swartz RC, Cole FA, Pelletier J, Jones J. 1999. Toxicity and
5 phototoxicity of mixtures of highly lipophilic PAH compounds in marine sediments: can the
6 ZPAH model be extrapolated? Arch Environ Contamin Toxicol 36:270-280.
7
8 Bowling JW, Leversee GJ, J^andrum PF, Giesy JP. 1983. Acute mortality of
9 anthracene-contaminated fish exposed to sunlight. Aquat Toxicol 3:79-90.
10
11 Bradbury S * Carlson R, Henry T. 1989. Polar narcosis in aquatic organisms. Aquat Toxicol Haz Assess
12 12:59-73.
13
14 Brenniman G, Hartung R, Weber WJ, Jr. 1976. A continuous flow bioassay method to evaluate the
15 effects of outboard motor exhausts and selected aromatic toxicants on fish. Water Res 10:165-
16 169.
17
18 Brezonik PL. 1994. Chemical Kinetics and Process Dynamics in Aquatic Systems. CRC Press, Inc.,
19 Boca Raton, Florida.
20
21 Bridie AL, Wolff CJM, Winter M. 1979. The acute toxicity of some petrochemicals to goldfish. Water
22 Res 13:623-626.
23
24 Bringman G, Kuhn R. 1959. Vergleichende wasser - toxikologische untersuchungen an bakterien. algen
Final Draft PAH Mixtures ESC Document 8-5 5 April 2000
-------
1 and kleinkrebsen. Gesundheits Ingenieur 80:115.
2
3 Broderius S, Kahl M. 1985. Acute toxicity of organic chemical mixtures to the fathead minnow. Aquat
4 Toadcol 6:307-322.
5
6 Etonian D, Naf C, Wik M, Renberg I. 1990. The importance of spheroidal carbonaceous oarticles
7 (SCPs) for the distribution of paniculate polycyclic aromatic hydrocarbons (PAHs) in an
8 estuarine-like urban coastal water area. Oiemo 21:69-77.
9
10 Brooke LT. 1991. Summary of results of acute and chronic exposures of fluoranthene with and without
11 ultraviolet (UV) light to various organisms. Memorandum to Walter J. Berry, NHEERL,
12 Naragansett, RI. December 3, 1991.
13
14 Brooke LT. 1993. Conducting toxicity tests with freshwater organisms exposed to dieldrin,
15 fluoranthene and phenanthrene. Report to Robert L. Spehar, Project Officer, U.S. EPA.
16 Environmental Research Laboratory-Duluth, Duluth, MN. 18pp.
17
18 Brooke LT. 1994. Acute phenanthrene toxicity to Daphnia magna. Contract No. 68-C 1-0034 Report
19 to R.L. Spehar, U.S. EPA , WA No. 2-14.
20
21 Buccafusco RJ, Ells SJ, LeBlanc GA. 1981. Acute toxicity of priority pollutants to bluegill (Lepomis
22 macrochirus). Bull Environm Contain Toxicol 26:446-452.
23
24 Bunton TE. 1996. Experimental Chemical Carcinogenesis in Fish. Toxicologic Pathology.24(5): 603-
Final Draft PAH Mixtures ESG Document 8-6 5 April 2000
-------
1 618.
2
3 Burgess RM, Scott KJ. 1992. The significance of in-place contaminated marine sediments orf the water
4 column: processes and effects. In G.A. Burton, Jr. eds. Sediment Toxicity Assessment. Lewis
5 Publishing, Boca Raton, FL. pp. 129-154.
6
7 Burgess RM, Serbst JR, Champlin DM, Kuhn A, Ryba SR. 2000. Toxicity of high molecular weight
8 PAH mixtures in sediment to Ampelisca abdita and Americamysis bahia. MS in preparation.
9
10 Cairns MA, Nebeker AV. 1982. Toxicity of acenaphthene and isophorone to early life stages of
11 fathead minnows. Arch Environ Contain Toxicol 11:703-707.
12
13 Call DJ, Brooke LT, Ahmad A, Richter JE. 1983. Toxiejty and metabolism studies with EPA priority
14 pollutants and related chemicals in freshwater organisms. Reports submitted to U.S. EPA,
15 Report no. EPA-600/3-83-095.
16
17 Call DJ, Brooke LT, Knuth ML, Poirier SH, Hoglund MD. 1985. Fish sub-chronic toxicity prediction
18 model for industrial organic chemicals that produce narcosis. Environ Toxicol Chem 4:335-34.1.
19
20 Call DJ, Brooke LT, Harting SL, Poirer SH, McCauley DJ. 1986. Toxicity of phenanthrene to several
21 freshwater species. Final report to Battelle Memorial Research Institute, Columbus, OH.
22 Center for Lake Superior Environmental Studies, University of Wisconsin Superior, Superior,
23 Wis. 18 pp. Contact no. F-4114(8834)-411. Report submitted to United States EPA.
24
Final Draft PAH Mixtures ESG Document 8-7 5 April 2000
-------
1 Canton JH, Adema DMM. 1978. Reproducibility of short-term reproduction toxicity experiments with
2 Daphnia magna and comparison of the sensitivity of Daphnia magna with Daphnia pulex and
*
3 Daphnia cucullata in short-term experiments. Hydrobiol 59:135-140.
4
5 Carls MG, Rice SD and Hose JE. 1999. Sensitivity of fish embryos to weathered crude oil: Part I. low-
6 level exposure during incubation causes malformations, genetic damage, and mortality in larval
7 pacific herring (Clupeapallasi). Environ Toxicol Chem 18(3): 481-493.
8
9 Chaisuksant, QY, Connell, D. 1997. Internal lethal concentrations of halobenzenes with fish
10 (Gambusia affinls). Ecotoxicol Environ Safety 37:66-75.
11
12 Champlin DM, Poucher SL. 1992a. PAH LC50 comparison table. Memorandum to Suzanne Lussier
13 and Dave Hansen, United States EPA, Narragansett, RI September, 24, 1992.
14
15 Champlin DM, Poucher SL. 1992b. Acute toxicity of fluoranthene to saltwater animals (UV lights).
16 Memomandum to Brian Melzian, United States EPA, Narragansett, RI, September 11, 1992,
17 9pp.
18
19 Champlin DM, Poucher S. 1992c. Acute toxicity of pyrene to saltwater animals. Memorandum to
20 Suzanne Lussier and Dave Hansen, September 15, 1992.
21
22
23 Champlin DM, Poucher S. 1992d. Chronic toxicity of pyrene to Americamysis bahia in a 28-day flow-
24 through test. Memorandum to Suzanne Lussier and Dave Hansen, September 15, 1992.
Final Draft PAH Mixtures ESG Document 8-8 5 April 2000
-------
1 618.
2
3 Burgess RM, Scott KJ. 1992. The significance of in-place contaminated marine sediments orf the water
4 column: processes and effects. In G.A. Burton, Jr. eds. Sediment Toxicity Assessment. Lewis
5 Publishing, Boca Raton, FL. pp. 129-154.
6
7 Burgess RM, Serbst JR, Champlin DM, Kuhn A, Ryba SR. 2000. Toxicity of high molecular weight
8 PAH mixtures in sediment to Ampelisca abdita and Americamysis bahia. MS in preparation.
9
10 Cairns MA, Nebeker AV. 1982. Toxicity of acenaphthene and isophorone to early life stages of
11 fathead minnows. Arch Environ Contam Toxicol 11:703-707.
12
13 Call DJ, Brooke LT, Ahmad A, Richter JE. 1983. Toxicjty and metabolism studies with EPA priority
14 pollutants and related chemicals in freshwater organisms. Reports submitted to U.S. EPA,
15 Report no. EPA-600/3-83-095.
16
17 Call DJ, Brooke LT, Knuth ML, Poirier SH, Hoglund MD. 1985. Fish sub-chronic toxicity prediction
18 model for industrial organic chemicals that produce narcosis. Environ Toxicol Chem 4:335-34.1.
19
20 Call DJ, Brooke LT, Harting SL, Poirer SH, McCauley DJ. 1986. Toxicity of phenanthrene to several
21 freshwater species. Final report to Battelle Memorial Research Institute, Columbus, OH.
22 Center for Lake Superior Environmental Studies, University of Wisconsin Superior, Superior,
23 Wis. 18 pp. Contact no. F-4114(8834)-411. Report submitted to United States EPA.
24
Final Draft PAH Mixtures ESG Document 8-7 5 April 2000
-------
1 Canton JH, Adema DMM. 1978. Reproducibility of short-term reproduction toxicity experiments with
2 Daphnia magnet and comparison of the sensitivity ofDaphnia magna with Daphnia pulex and
*
3 Daphnia cucullata in short-term experiments. Hydrobiol 59:135-140.
4
5 Carls MG, Rice SD and Hose JE. 1999. Sensitivity of fish embryos to weathered crude oil: Part I. low-
6 level exposure during incubation causes malformations, genetic damage, and mortality in larval
7 pacific herring (Clupeapallasi). Environ Toxicol Chem 18(3): 481-493.
8
9 Chaisuksant, QY, Connell, D. 1997. Internal lethal concentrations of halobenzenes with fish
10 (Gambusiaaffinis). Ecotoxicol Environ Safety 37:66-75.
11
12 Champlin DM, Poucher SL. 1992a. PAH LC50 comparison table. Memorandum to Suzanne Lussier
13 and Dave Hansen, United States EPA, Narragaiisett, RI September, 24, 1992.
14
15 Champlin DM, Poucher SL. 1992b. Acute toxicity of fluoranthene to saltwater animals (UV lights).
16 Memomandum to Brian Melzian, United States EPA, Narragansett, RI, September 11, 1992,
17 9pp.
18
19 Champlin DM, Poucher S. 1992c. Acute toxicity of pyrene to saltwater animals. Memorandum to
20 Suzanne Lussier and Dave Hansen, September 15, 1992.
21
22
23 Champlin DM, Poucher S. 1992d. Chronic toxicity of pyrene to Americamysis bahia in a 28-day flow-
24 through test. Memorandum to Suzanne Lussier and Dave Hansen, September 15, 1992.
Final Draft PAH Mixtures ESG Document 8-8 5 April 2000
-------
1 Chapman GA. 1987. Establishing sediment criteria for chemicals-Regulatory perspectives. In Dickson
2 KL, Maki AW, Brungs WA, eds, Fate and Effects of Sediment-Bound Chemicals in Aquatic
3 Systems. Pergamon Press, Elmsford, NY, pp. 355-377. t
4
5 Chapman PM, Long ER, Swartz RC, DeWitt TH, Pastorak R. 1991. Sediment toxicity tests, sediment
6 chemistry and benthic ecology do provide new insights into the significance and management of
7 contaminated sediments - a reply to Robert Spies. Environ Toxicol Chem 10:1-4.
8
9 Chapman PM, Downie J, Maynard A, Taylor LA. 1996. Coal and deoderizer residues in marine
10 sediments - contaminants or pollutants? Environ Toxicol Chem 15:638-642.
11
12 CLSES. 1984. Acute toxicities of organic chemicals to fathead minnows (Pimephales promelas). Center
13 for Lake Superior Environmental Studies, University of Wisconsin- Superior, Duluth, MN.
14
15 CLSES. 1985. Acute toxicities of organic chemicals to fathead minnows (Pimephales promelas). Center
16 for Lake Superior Environmental Studies, University of Wisconsin- Superior, Duluth, MN.
17
18 CLSES. 1986. Acute toxicities of organic chemicals to fathead minnows (Pimephales promelas). Center
19 for Lake Superior Environmental Studies, University of Wisconsin- Superior, Duluth, MN.
20
21 CLSES. 1988. Acute toxicities of organic chemicals to fathead minnows (Pimephales promelas). Center
22 for Lake Superior Environmental Studies, University of Wisconsin- Superior, Duluth, MN.
23
24 CLSES. 1990. Acute toxicities of organic chemicals to fathead minnows (Pimephales promelas). Center
Final Draft PAH Mixtures ESG Document 8-9 5 April 2000
-------
1 for Lake Superior Environmental Studies, University of Wisconsin- Superior, Duluth, MN.
2
3 Cody TE, Radike M, Warshawsky D. 1984. The phototoxicity of benzo[a]pyrene in the green alga
4 Selenastrum capricomutum. Environ Res 35:122-132.
5
6 Darville RG, Wilhm JL. 1984. The effect of naphthalene on oxygen consumption and hemoglobin
7 concentration in Chironomus attenuates and on oxygen consumption and lifecycle of
8 Tony tarsus dissimilis. Environ ToxicolChem 3:135-41.
9
10 Davenport R, Spacie A. 1991. Acute phototoxicity of harbor and tributary sediments from lower Lake
11 Michigan. / Great Lakes Res 17:51-56.
12
13 Dawson GW, Jennings AL, Drozdowski D, Rider E. 1977. The acute toxicity of 47 industrial chemical
14 to fresh and saltwater fishes. J Hazardous Materials 1:303-318.
15
16 de Bruijn J, Busser F, Seinen W, Hermens J. 1989. Determination of octanol/water partition
17 coefficients for hydrophobic organic chemicals with the "slow-stirring" method. Environ
18 Toxicol Chem 8:499-512.
19
20 DeGraeve GM et al., 1980. Effects of naphthalene and benzene on fathead minnows and rainbow trout.
21 Unpublished manuscript.
22
23 DeGraeve GM, Elder RG, Woods DC, Bergman HL. 1982. Effects of naphthalene and benzene on
24 fathead minnows and rainbow trout. Arch Environ Contain Toxicol 11:487-90.
Final Draft PAH Mixtures ESG Document 8-10 5 April 2000
-------
1 Chapman GA. 1987. Establishing sediment criteria for chemicals-Regulatory perspectives. In Dickson
2 KL, Maki AW, Brungs WA, eds, Fate and Effects of Sediment-Bound Chemicals in Aquatic
3 Systems. Pergamon Press, Elmsford, NY, pp. 355-377. t
4
5 Chapman PM, Long ER, Swartz RC, DeWitt TH, Pastorak R. 1991. Sediment toxiciry tests, sediment
6 chemistry and benthic ecology do provide new insights into the significance and management of
7 contaminated sediments - a reply to Robert Spies. Environ Toxicol Chem 10:1-4.
8
9 Chapman PM, Downie J, Maynard A, Taylor LA. 1996. Coal and deoderizer residues in marine
10 sediments - contaminants or pollutants? Environ Toxicol Chem 15:638-642.
11
12 CLSES. 1984. Acute toxicities of organic chemicals to fathead minnows (Pimephales promelas). Center
13 for Lake Superior Environmental Studies, University of Wisconsin- Superior, Duluth, MN.
14
15 CLSES. 1985. Acute toxicities of organic chemicals to fathead minnows (Pimephales promelas). Center
16 for Lake Superior Environmental Studies, University of Wisconsin- Superior, Duluth, MN.
17
18 CLSES. 1986. Acute toxicities of organic chemicals to fathead minnows (Pimephales promelas). Center
19 for Lake Superior Environmental Studies, University of Wisconsin- Superior, Duluth, MN.
20
21 CLSES. 1988. Acute toxicities of organic chemicals to fathead minnows (Pimephales promelas). Center
22 for Lake Superior Environmental Studies, University of Wisconsin- Superior, Duluth, MN.
23
24 CLSES. 1990. Acute toxicities of organic chemicals to fathead minnows (Pimephales promelas). Center
Final Draft PAH Mixtures ESG Document 8-9 5 April 2000
-------
1 for Lake Superior Environmental Studies, University of Wisconsin- Superior, Duluth, MN.
2
3 Cody TE, Radike M, Warshawsky D. 1984. The phototoxiciry of benzo[a]pyrene in the green alga
4 Selenastnm capricomutum. Environ Res 35:122-132.
5
6 Darville RG, Wilhm JL. 1984. The effect of naphthalene on oxygen consumption and hemoglobin
7 concentration in Qiironomus attenuates and on oxygen consumption and lifecycle of
8 Tanytarsus dissimlis. Environ Toxicol Chem 3:135-41.
9
10 Davenport R, Spacie A. 1991. Acute phototoxiciry of harbor and tributary sediments from lower Lake
11 Michigan. / Great Lakes Res 17:51-56.
12
13 Dawson GW, Jennings AL, Drozdowski D, Rider E. 1977. The acute toxicity of 47 industrial chemical
14 to fresh and saltwater fishes. / Hazardous Materials 1:303-318.
15
16 de Bruijn J, Busser F, Seinen W, Hermens J. 1989. Determination of octanol/water partition
17 coefficients for hydrophobic organic chemicals with the "slow-stirring" method. Environ
18 Toxicol Chem 8:499-512.
19 ' . . .
20 DeGraeve GM et al., 1980. Effects of naphthalene and benzene on fathead minnows and rainbow trout.
21 Unpublished manuscript.
22
23 DeGraeve GM, Elder RG, Woods DC, Bergman HL. 1982. Effects of naphthalene and benzene on
24 fathead minnows and rainbow trout. Arch Environ Contam Toxicol 11:487-90.
Filial Draft PAH Mixtures ESG Document 8-10 5 April 2000
-------
1 de Maagd, PG, et al. 1996. Lipid content and time-to-death explain most of the intraspecies variation in
2 lethal body burdens of napthalene and 1,2,4-trichlorobenzene in fathead minnow (Pimephales
3 promelas). Chapter 8, Part IV. PhD thesis. Univ. of Ultrech, In Polycyclic Aromatic*
4 Hydrocarbons: Fate and Effects in the Aquatic Environment.
5
6 DeWitt TH, Swartz RC, Lamberson JO. 1989. Measuring the acute toxicity of estuarine sediments.
7 Environ Toxicol Chem 8:1035-1048.
8
9 DeWitt TH, Ozretich RJ, Swartz RC, Lamberson JO, Schults DW, Ditsworth GR, Jones JKP, Hoselton
10 L, Smith LM. 1992. The influence of organic matter quality on the toxicity and partitioning of
11 sediment-associated fluoranthene. Environ Toxicol Chem 11:197-208.
12
13 Dill DC. 1980. Toxicity of 1,1-dichloroethylene (vinylidene chloride) to aquatic organisms. Technical
14 report EPA/600/3-80/057.
15
16 Di Toro DM. 1985. A particle interaction model of reversible organic chemical sorption. Chemo
17 14:1503-1538.
18
19 Di Toro DM, Zarba CS, Hansen DJ, Berry WJ, Swartz RC, Cowan CE, Pavlou SP, Allen HE,
20 Thomas NA, Paquin PR. 1991. Technical basis for the equilibrium partitioning method for
21 establishing sediment quality criteria. Environ Toxicol Chem 11:1541-1583.
22
23 Di Toro DM, McGrath JA, Hansen DJ. 2000. Technical basis for narcosis chemicals and PAH criteria.
24 I. Water and tissue. Environ Toxicol Chem (In press).
Final Draft PAH Mbaures ESG Document 8-11 5 April 2000
-------
1 Di Toro DM, JA McGrath. 2000. Technical basis for narcosis chemicals and PAH criteria. II.
2 Mixtures and sediments. Environ Toxicol Chem (In press).
t
3
4 Driscoll, S.K. and_Schaffher LC 1997. A comparison of Equilibrium Partitioning and Critical Body
5 residue approaches for predicting toxicity of fluoranthene to amphipods. SETAC 18th Annual
6 Meeting. November 1997. San Francisco, California.
7
8 Driscoll SK, Harkey GA, Landrum PF. 1997a. Accumulation and toxicokinetics of fluoranthene in
9 sediment bioassays with freshwater amphipods. Environ Toxicol Chem 16:742-753.
10
11 Driscoll SK, Landrum PF, Tigue E. 1997b. Accumulation and toxicokinetics of fluoranthene in
12 water-only exposures with freshwater amphipods. Environ Toxicol Chem 16:754-761.
13 '
14 Eastman DA, Booth GM, Lee ML. 1984. Polycyclic aromatic hydrocarbons: accumulation and
15 elimination of polycyclic aromatic sulfur heterocycles in Daphnia magna. Arch Environ
16 Contam Toxicol 13:105-111.
17
18 Edmisten GE, Bantle JA. 1982. Use ofXenopus laevis larvae hi 96-hour, flow-through toxicity tests
19 with naphthalene. Bull Environ Contam Toxicol 29:392-9.
20
21 Edsall CC 1991. Acute toxicities to larval rainbow trout of representative compounds detected in Great
22 Lakes fish. Bull Environ Contam Toxicol 46:173-8.
23
24 EG&G Bionomics. 1978. Acute and chronic toxicity of fluoranthene to mysid shrimp (Americamysis
Final Draft PAH Mixtures ESG Document 8-12 5 April 2000
-------
1 de Maagd, PG, et al. 1996. Lipid content and time-to-death explain most of the intraspecies variation in
2 lethal body burdens of napthalene and 1,2,4-trichlorobenzene in fathead minnow (Pimephales
3 promelas). Chapter 8, Part IV. PhD thesis. Univ. of Ultrech, In Polycyclic Aromatic*
4 Hydrocarbons: Fate and Effects in the Aquatic Environment.
5
6 DeWitt TH, Swartz RC, Lamberson JO. 1989. Measuring the acute toxicity of estuarine sediments.
7 Environ Toxicol Chem 8:1035-1048.
8 -
9 DeWitt TH, Ozretich RJ, Swartz RC, Lamberson JO, Schults DW, Ditsworth GR, Jones JKP, Hoselton
10 L, Smith LM. 1992. The influence of organic matter quality on the toxicity and partitioning of
11 sediment-associated fluoranthene. Environ Toxicol Chem 11:197-208.
12
13 Dill DC. 1980. Toxicity of I,l-dichloroethylene (vinylidene chloride) to aquatic organisms. Technical
14 .report EPA/600/3-80/057.
15
16 Di Toro DM. 1985. A particle interaction model of reversible organic chemical sorption. Chemo
17 14:1503-1538.
18
19 Di Toro DM, Zarba CS, Hansen DJ, Berry WJ, Swartz RC, Cowan CE, Pavlou SP, Allen HE,
20 Thomas NA, Paquin PR. 1991. Technical basis for the equilibrium partitioning method for
21 establishing sediment quality criteria. Environ Toxicol Chem 11:1541-1583.
22
23 Di Toro DM, McGrath JA, Hansen DJ. 2000. Technical basis for narcosis chemicals and PAH criteria.
24 I. Water and tissue. Environ Toxicol Chem (In press).
Final Draft PAH Matures ESC Document 8-11 5 April 2000
-------
1 Di Toro DM, JA McGrath. 2000. Technical basis for narcosis chemicals and PAH criteria. II.
2 Mixtures and sediments. Environ Toxicol Chem (In press).
*
3
4 Driscoll, S.K. and_Schaffher LC 1997. A comparison of Equilibrium Partitioning and Critical Body
5 residue approaches for predicting toxicity of fluoranthene to amphipods. SETAC 18th Annual
6 Meeting. November 1997. San Francisco, California.
7
8 Driscoll SK, Harkey GA, Landrum PF. 1997a. Accumulation and toxicokinetics of fluoranthene in
9 sediment bioassays with freshwater amphipods. Environ Toxicol Chem 16:742-753.
10
11 Driscoll SK, Landrum PF, Tigue E. 1997b. Accumulation and toxicokinetics of fluoranthene in
12 water-only exposures with freshwater amphipods. Environ Toxicol Chem 16:754-761.
13 '
14 Eastman DA, Booth GM, Lee ML. 1984. Polycyclic aromatic hydrocarbons: accumulation and
15 elimination of polycyclic aromatic sulfur heterocycles in Daphnia magna. Arch Environ
16 Contam Toxicol 13:105-111.
17
18 Edmisten GE, Bantle JA. 1982. Use ofXenopus laevis larvae in 96-hour, flow-through toxicity tests
19 with naphthalene. Bull Environ Contam Toxicol 29:392-9.
20
21 Edsall CC 1991. Acute toxicities to larval rainbow trout of representative compounds detected in Great
22 Lakes fish. Bull Environ Contam Toxicol 46:173-8.
23 .
24 EG&G Bionomics. 1978. Acute and chronic toxicity of fluoranthene to mysid shrimp (Americamysis
Final Draft PAH Mixtures ESG Document 8-12 5 April 2000
-------
1 bahia). Contract no. 68-01-4646. Preliminary research report.
2
3 EG&G Bionomics, 1982. Acute toxicity of selected chemicals to fathead minnow, water flea and mysid
4 shrimp under static and flow-through test conditions. Contract no, 807479-01-0. Final Report
5 submitted to U.S. EPA.
6
7 ERCO. 1981. Toxicity testing inter-laboratory comparison early life stage test with fathead minnow.
8 Final report to U.S. EPA, Cincinnati, OH and U.S. EPA, Duluth MN. ERCO/Energy
9 Resources Co., Inc., 185 Alewife Brook Parkway, Cambridge, MA, 47 pp.
10
11 Fabacher DL, Besser JM> Schmitt CJ. 1991. Contaminated sediments from tributaries of the Great
12 Lakes: chemical characterization and carcinogenic effects in medaka (Oryzias latipes). Arch
13 Environ Contam Toxicol 21:17-34.
14
15 Fairey R, Bretz C, Lamerdin S, Hunt J, Anderson B, Tudor S, Wilson C, LaCaro F, Stephenson M,
16 Puckett M, Long E. 1996. Chemistry, toxicity and benthic community conditions in sediments
17 of the San Diego Bay Region. Final Report. California State Water Resources Control Board.
18.
19 Farrington FW, Goldberg ED, Risebrough RW, Martin JH, Bowen VT. 1983. U.S. "Mussel Watch"
20 1976-1978: An overview of the trace-metal, DDE, PCB, hydrocarbon, and artificial
21 radionuclide data. Environ Sci Techno! 17:490-496.
22
23 Finger SE, Little EF, Henry MG, Fairchild JF, Boyle TP. 1985. Comparison of laboratory and field
24 assessment of fluorene - part 1: effects of fluorene on the survival, growth, reproduction, and
Final Draft PAH Mixtures ESG Document 8-13 5 April 2000
-------
1 behavior of aquatic organisms in laboratory tests. In Validation Predict. Lab. Methods Assess
2 Fate Eff. Contam. Aquat. Ecosyst., ASTM Spec. Tech. Publ. 865, American Society of
*
3 Testing and Materials, Philadelphia, PA., pp. 120-33.
4
5 Franks and Lieb, 1990. Mechanisms of general anesthesia. Environ Health Perspectives 87:199-205.
6
7 Gala WT, Giesy JP. 1992. Photo-induced toxicity of anthracene to the green alga, Selenastrum
8 capricornutum. Arch Environ Contam Toxicol 23:316-23.
9
10 Gala WR, Giesy JP. 1994. Flow cytometric determination of the photoinduced toxicity of anthracene to
11 the green alga Selenastrum capricornutum. Environ Toxicol Chem 13:831-840.
12
13 Geiger JG, Buikema AL, Jr. 1981. Oxygen consumption and filtering rate of Daphniapulex after
14 exposure in water-soluble fractions of naphthalene, phenanthrene, No. 2 fuel oil, and coal-tar
15 creosote. Bull Environ Contam Toxicol 27:783-789.
16
17 Geiger JG, Buikema AL, Jr. 1982. Hydrocarbons depress growth and reproduction of Daphniapulex
18 (Cladocera). Can JFish Aquat Sci 39:830-6.
19
20 Geiger DL, Northcott CE, Call DJ, Brooke LT. 1985. Acute toxicities of organic chemicals to fathead
21 minnows (Pimephalespromelas). Vol. 2. Center for Lake Superior Environmental Studies,
22 University of Wisconsin, Superior Wl, 326 pp.
23
24 Gendussa AC 1990. Toxicity of chromium and fluoranthene from aqueous and sediment sources to
Final Draft PAH Mixtures ESG Document 8-14 5 April 2000
-------
1 bahia). Contract no. 68-01-4646. Preliminary research report.
2
3 EG&G Bionomics, 1982. Acute toxicity of selected chemicals to fathead minnow, water flea and mysid
4 shrimp under static and flow-through test conditions. Contract no, 807479-01-0. Final Report
5 submitted to U.S. EPA.
6
7 ERCO. 1981. Toxicity testing inter-laboratory comparison early life stage test with fathead minnow.
8 Final report to U.S. EPA, Cincinnati, OH and U.S. EPA, Duluth MN. ERCO/Energy
9 Resources Co., Inc., 185 Alewife Brook Parkway, Cambridge, MA, 47 pp.
10
11 Fabacher DL, Besser JM> Schmitt CJ. 1991. Contaminated sediments from tributaries of the Great
12 Lakes: chemical characterization and carcinogenic effects in medaka (Oryzias latipes). Arch
13 Environ Contam Toxicol 21:17-34.
14
15 Fairey R, Bretz C, Lamerdin S, Hunt J, Anderson B, Tudor S, Wilson C, LaCaro F, Stephenson M,
16 Puckett M, Long E. 1996. Chemistry, toxicity and benthic community conditions in sediments
17 of the San Diego Bay Region. Final Report. California State Water Resources Control Board.
18
19 Farrington FW, Goldberg ED, Risebrough RW, Martin JH, Bowen VT. 1983. U.S. "Mussel Watch"
20 1976-1978: An overview of the trace-metal, DDE, PCB, hydrocarbon, and artificial
21 radionuclide data. Environ Sci Technol 17:490-496.
22
23 Finger SE, Little EF, Henry MG, Fairchild JF, Boyle TP. 1985. Comparison of laboratory and field
24 assessment of fluorene - part 1: effects of fluorene on the survival, growth, reproduction, and
Final Draft PAH Mixtures ESG Document 8-13 5 April 2000
-------
1 behavior of aquatic organisms in laboratory tests. In Validation Predict. Lab. Methods Assess.
2 Fate Eff. Contam. Aquat. Ecosyst., ASTM Spec. Tech. Publ. 865, American Society of
*
3 Testing and Materials, Philadelphia, PA., pp. 120-33.
4
5 Franks and Lieb, 1990. Mechanisms of general anesthesia. Environ Health Perspectives 87:199-205.
6
7 Gala WT, Giesy JP. 1992. Photo-induced toxicity of anthracene to the green alga, Selenastrum
8 capricomutum. Arch Environ Contam Toxicol 23:316-23.
9
10 Gala WR, Giesy JP. 1994. Flow cytometric determination of the photoinduced toxicity of anthracene to
H the green alga Selenastrum capricomutum. Environ Toxicol Chem 13:831-840.
12
13 Geiger JG, Buikema AL, Jr. 1981. Oxygen consumption and filtering rate of Daphniapulex after
14 exposure in water-soluble fractions of naphthalene, phenanthrene, No. 2 fuel oil, and coal-tar
15 creosote. Bull Environ Contam Toxicol 27:783-789.
16
17 Geiger JG, Buikema AL, Jr. 1982. Hydrocarbons depress growth and reproduction of Daphniapulex
18 (Cladocera). Can J Fish Aquat Sci 39:830-6.
19
20 Geiger DL, Northcott CE, Call DJ, Brooke LT. 1985. Acute toxicities of organic chemicals to fathead
21 minnows (Pimephalespromelas). Vol. 2. Center for Lake Superior Environmental Studies,
22 University of Wisconsin, Superior WI, 326 pp.
23
24 Gendussa AC 1990. Toxicity of chromium and fluoranthene from aqueous and sediment sources to
Final Draft PAH Mixtures ESG Document 8-14 5 April 2000
-------
1 selected freshwater fish. Ph.D. Thesis. University of North Texas, U.M.I., Ann Arbor, MI,
2 138 pp.
3 *
4 Goddard KA, Schultz JR and Stegeman JJ. 1987. Uptake, Toxicity, and distribution of benzojajpyrene
5 and monooxygenase induction in the topminnows Poeciliopsis monacha and Poeciliopsis
6 lucida. Drug MetabolDispos 15:449-455.
7
8 Gustafsson O, Gschwend PM. 1997. Soot as a strong partition medium for polycyclic aromatic
9 hydrocarbons in aquatic systems. In Eganhouse, RP, ed, Molecular Markers in Environmental
10 Geochemistry: Source Indicators and Process Probes. American Chemical Society, Washington
11 D.C.
12
13 Gustafsson O, Haghseta F, Chan C, MacFarlane J, Gschwend PM. 1997. Quantification of the dilute
14 sedimentary soot phase: Implications for PAH speciation and bioavailability. Environ Set Tech
15 31:203-209.
16
17 Hall L, Maynard E, Kier L. 1989. QSAR investigation of benzene toxicity to fathead minnow using
18 molecular connectivity. Environ Toxicol Chem 8:783-788.
19
20 Hall LH, Kier LB, Phipps G. 1984. Structure-activity relationships on the toxicity of benzene
21 derivatives: I. An additiviry model. Environ Toxicol Chem 3:355-365.
22
23 Hall TA and Oris JT. 1991. Anthracene reduces reproductive potential and is maternally transferred
24 during long-term exposure in fathead minnows. Aquat Toxicol 19: 249-264.
Final Draft PAH Mixtures ESG Document 8-15 5 April 2000
-------
1 Hannah, JB, Hose JE, Landolt ML, Miller BS, Felton, SP, and Iwaoka WT. 1982. Benzofajpyrene-
2 induced morphologic and developmental abnormalities in rainbow trout. Arch Environ Contam
3 Toxicoll 1:727-734.
4
5 Hansch C, Leo A. 1995. Exploring QSAR Fundamentals and Applications in Chemistry and Biology.
6 American Chemical Society, Washington DC.
7 -
8 Hargreaves BR, RL Smith, CQ Thompson, SS Herman. 1982. Toxicity and accumulation of
9 naphthalene hi the mysid Neomyyis americana (Smith) and effects of environmental
10 temperature. In Vernberg, WB, ed, Physiol. Mech. Mar. Pollut. Toxic., Proc. Symp. Pollut.
11 Mar. Org., Academic Press, New York, NY, pp 391-412.
12
13 Harkey GA, Driscoll SK, Landrum PF. 1997. Effect of feeding in 30-d bioaccumulation assays using
14 Hyalella azteca in fluoranthene-dosed sediment. Environ Toxicol Chem 16:762-769.
15
16 Hatch AC, Burton GA. 1998. Effects of photoinduced toxicity of fluoranthene on amphibian embryos
17 and larvae. Environ Toxicol Chem 17:1777-1785.
18
19 Hatch AC, Burton GA. 1999. Photo-induced toxicity of PAHs to Hyalella azteca and Chironomus
20 tentans: effects of mixtures and behavior. Environ Pollut 106:157-167.
21 .
22 Hawkins WE, Walker WW, Overstreet RM, Lytle TF and Lytle JS. 1988. Dose-related carcinogenic
23 effects of water-borne benzo[a]pyrene on livers of two small fish species. Ecotoxicol Environ
24 Safety 16:219-231.
Final Draft PAH Mixtures ESG Document 8-16 5 April 2000
-------
1 selected freshwater fish. Ph.D. Thesis. University of North Texas, U.M.I., Ann Arbor, MI,
2 138pp.
3 *
4 Goddard KA, Schultz JR and Stegeman JJ. 1987. Uptake, Toxicity, and distribution of benzo[a]pyrene
5 and monooxygenase induction in the topminnows Poeciliopsis monacha and Poeciliopsis
6 lucida. Drug Metabol Dispos 15: 449-455.
7
8 Gustafsson O, Gschwend PM. 1997. Soot as a strong partition medium for polycyclic aromatic
9 hydrocarbons in aquatic systems. In Eganhouse, RP, ed, Molecular Markers in Environmental
10 Geochemistry: Source Indicators and Process Probes. American Chemical Society, Washington
11 D.C.
12
13 Gustafsson O, Haghseta F, Chan C, MacFarlane J, Gschwend PM. 1997. Quantification of the dilute
14 sedimentary soot phase: Implications for PAH speciation and bioavailability. Environ Sci Tech
15 31:203-209.
16
17 Hall L, Maynard E, Kier L. 1989. QSAR investigation of benzene toxicity to fathead minnow using
18 molecular connectivity. Environ Toxicol Chem 8:783-788.
19
20 Hall LH, Kier LB, Phipps G. 1984. Structure-activity relationships on the toxicity of benzene
21 derivatives: I. An additivity model. Environ Toxicol Chem 3:355-365.
22
23 Hall TA and Oris JT. 1991. Anthracene reduces reproductive potential and is maternally transferred
24 during long-term exposure in fathead minnows. Aquat Toxicol 19: 249-264.
Final Draft PAH Mixtures ESG Document 8-15 5 April 2000
-------
1 Hannah, JB, Hose JE, Landolt ML, Miller BS, Felton, SP, and Iwaoka WT. 1982. Benzofajpyrene-
2 induced morphologic and developmental abnormalities in rainbow trout. Arch Environ Contam
3 Toxicoll 1:727-734. •»
4
5 Hansch C, Leo A. 1995. Exploring QSAR Fundamentals and Applications in Chemistry and Biology.
6 American Chemical Society, Washington DC.
7 '
8 Hargreaves BR, RL Smith, CQ Thompson, SS Herman. 1982. Toxicity and accumulation of
9 naphthalene hi the mysid Neomysis americana (Smith) and effects of environmental
10 temperature. In Vemberg, WB, ed, Physiol. Mech. Mar. Pollut. Toxic., Proc. Symp. Pollut.
11 Mar. Org., Academic Press, New York, NY, pp 391-412.
12
13 Harkey GA, Driscoll SK, Landrum PF. 1997. Effect of feeding in 30-d bioaccumulation assays using
14 Hyalella azfeca in fluoranthene-dosed sediment. Environ Toxicol Chem 16:762-769.
15
16 Hatch AC, Burton GA. 1998. Effects of photoinduced toxicity of fluoranthene on amphibian embryos
17 and larvae. Environ Toxicol Chem 17:1777-1785.
18
19 Hatch AC, Burton GA. 1999. Photo-induced toxicity of PAHs to Hyalella azteca and Chironomus
20 tentans: effects of mixtures and behavior. Environ Pollut 106:157-167.
21
22 Hawkins WE, Walker WW, Overstreet RM, Lytle TF and Lytle JS. 1988. Dose-related carcinogenic
23 effects of water-borne benzo[a]pyrene on livers of two small fish species. Ecotoxicol Environ
24 Safety 16:219-231.
Final Draft PAH Mixtures ESG Document 8-16 5 April 2000
-------
1 Hawkins, WE, Walker WW, Overstreet RM, Lytle JS and Lytle TF. 1990. Carcinogenic effects of
2 some polycyclic aromatic hydrocarbons on the Japanese medaka and guppy in waterborne
3 exposures. Sci Total Environ 94: 155-167. »
4
5 Heitmuller PT, Hollister TA, Parrish PR. 1981. Acute toxicity of 54 industrial chemicals to sheepshead
6 minnows (Cyprinodon variegatus). Bull Environ Contain Toxicol 27:596-404.
7
8 Hendricks JD, Meyers TR, Shelton DW, Casteel JL and Bailey GS. 1985. Hepatocarcinogenicity of
9 benzo[a]pyrene to Rainbow trout by dietary exposure and intraperitoneal injection. ///C774(4):
10 839-851.
11
12 HermensJLM. 1989. Quantitative structure-activity relationships of environmental pollutants. In
13 Hutzinger O, ed, Handbook of Environmental Chemistry. Vol. 2E-Reactions and processes.
14 Springer Verlag, Berlin, pp 111-162.
15
16 Hermens J, Leeuwangh P, Musch A. 1984. Quantitative structure-activity relationships and mixture
17- toxicity studies of chloro- and alkylanilines at an acute lethal toxicity level to the guppy
18 (Poecilia reticulat). Ecotoxicol Environ Safety 8:388-394.
19
20 Hilal SH, Carreira L, Karickhoff SW. 1994. Estimation of chemical reactivity and parameters and
21 physical properties of organic molecules using SPARC. In: Politzer P, Murry JS, eds,
22 Quantitative Treatments of Solute/Solvent Interactions, volume 1. Elsevier, Amsterdam, pp.
23 291-348.
24
Final Draft PAH Matures ESG Document 8-17 5 April 2000
-------
1 Hodson PV, Dixon DG, Kaiser K. 1988. Estimating the acute toxicity of water- borne chemicals in
2 trout from measurements of median lethal dose and the octanol-water partition coefficient
3 Environ Toxicol Chem 7:443-454.
4
5 Hoke R. 1992. Results of the third dieldrin sediment- spiking study. Memorandum to D. Hansen, D.
6 Di Toro and G. Ankley. December 2, 5 pp.
7
8 Holcombe GH, Phipps GL, Fiandt JT. 1983. Toxicity of selected priority pollutants to various aquatic
9 organisms. Ecotoxicol Environ Safety 7:400-409.
10
11 Holcombe GW, Phipps GL, Knuth ML, Felnaber T. 1984. The acute toxicity of selected substituted
12 phenols, benzenes and benzoic acid esters to fathead minnows (Pimephales promelas). Environ
13 Pollut 35:367-81.
14
15 Holcombe G, Phipps G, Sulaiman A, Hoffman A. 1987. Simultaneous multiple species testing: Acute
16 toxicity of 13 chemicals to 12 diverse freshwater amphibian, fish, and invertebrate. Arch
17 Environ Contam Toxicol 16:697-710.
18
19 Hoist LL, Giesy JP. 1989. Chronic effects of the photoenhanced toxicity of anthracene on Daphnia
20 magna reproduction. Environ Toxicol Chem 8:933-42.
21
22 Home JD, Oblad BR. 1983. Aquatic toxicity studies of six priority pollutants. Contract No. 68-01-
23 6201. Final Report Task II. U.S. EPA.
24
Final Draff PAH Mixtures ESG Document 8-18 5 April 2000
-------
1 Hawkins, WE, Walker WW, Overstreet RM, Lytle JS and Lytle TF. 1990. Carcinogenic effects of
2 some polycyclic aromatic hydrocarbons on the Japanese medaka and guppy in waterborne
3 exposures. Sci Total Environ 94: 155-167. 4
4
5 Heitmuller FT, Hollister TA, Parrish PR. 1981. Acute toxicity of 54 industrial chemicals to sheepshead
6 minnows (Cyprinodon variegatus). Bull Environ Contain Toxicol 27:596-404.
7
8 Hendricks JD, Meyers TR, Shelton DW, Casteel JL and Bailey GS. 1985. Hepatocarcinogeniciry of
9 benzo(a]pyrene to Rainbow trout by dietary exposure and intraperitoneal injection. JNCI74(4):
10 839-851.
11
12 Hermans JLM. 1989. Quantitative structure-activity relationships of environmental pollutants. In
13 Hutzinger O, ed, Handbook of Environmental Chemistry. Vol. 2E-Reactions and processes.
14 Springer Verlag, Berlin, pp 111-162.
15
16 Herrnens J, Leeuwangh P, Musch A. 1984. Quantitative structure-activity relationships and mixture
17- toxicity studies of chloro- and alkylanilines at an acute lethal toxicity level to the guppy
18 (Poecilia reticulat). Ecotoxicol Environ Safety 8:388-394.
19
20 Hilal SH, Carreira L, Karickhoff SW. 1994. Estimation of chemical reactivity and parameters and
21 physical properties of organic molecules using SPARC. In: Politzer P, Murry JS, eds,
22 Quantitative Treatments of Solute/Solvent Interactions, volume 1. Elsevier, Amsterdam, pp.
23 291-348.
24
Final Draft PAH Mixtures ESG Document 8-17 5 April 2000
-------
1 Hodson PV, Dixon DG, Kaiser K. 1988. Estimating the acute toxicity of water- borne chemicals in
2 trout from measurements of median lethal dose and the octanol-water partition coefficient
3 Environ Toxicol Chem 7:443-454.
4
5 Hoke R. 1992. Results of the third dieldrin sediment- spiking study. Memorandum to D. Hansen, D.
6 Di Toro and G. Ankley. December 2, 5 pp.
7
8 Holcombe GH, Phipps GL, Fiandt JT. 1983. Toxicity of selected priority pollutants to various aquatic
9 organisms. Ecotoxicol Environ Safety 7:400-409.
10
11 Holcombe GW, Phipps GL, Knuth ML, Felnaber T. 1984. The acute toxicity of selected substituted
12 phenols, benzenes and benzoic acid esters to fathead minnows (fimephales promelas). Environ
13 Polha 35:367-81.
14
15 Holcombe G, Phipps G, Sulaknan A, Hoffman A. 1987. Simultaneous multiple species testing: Acute
16 toxicity of 13 chemicals to 12 diverse freshwater amphibian, fish, and invertebrate. Arch
17 Environ Contam Toxicol 16:697-710.
18
19 Hoist LL, Giesy JP. 1989. Chronic effects of the photoenhanced toxicity of anthracene on Daphnia
20 magna reproduction. Environ Toxicol Chem 8:933-42.
21
22 Home JD, Oblad BR. 1983. Aquatic toxicity studies of six priority pollutants. Contract No. 68-01-
23 6201. Final Report Task H. U.S. EPA.
24
Final Draft PAH Mixtures ESG Document 8-18 5 April 2000
-------
1 Home JD, Swirsky MA, Hollister TA, Oblad BR, Kennedy JH. 1983. Aquatic toxicity studies of five
2 pollutants. Report no. 4398, U.S. EPA contract no. 68-01-6201. NUS Corporation, Houston,
3 TX, 93pp.
4
5 Hose JE, Hannah JE, Landolt ML, Miller BS, Felton SP and Iwaoka WT. 1981. Uptake of
6 benzo[a]pyrene by gonadal tissue of flatfish (family pleuronectidae) and its effects on
7 subsequent egg development. /. Toxicol. Environ. Health. 7: 991-1000.
8
9 Hose JE, Hannah, JB, DUulio D, Landolt ML, Miller BS, Iwaoka WT and Felton SP. 1982. Effects of
10 benzo[a]pyrene on early development of flatfish. Arch Environ Contain Toxicol 11: 167-171.
11
12 Hose JE, Hannah JB, Puffer HW and Landolt ML. 1984, Histologic and skeletal abnormalities in
13 benzo[a]pyrene-treated rainbow trout alevins. Arch Environ Contam Toxicol 13: 675-684.
I4
15 Huang X, Dixon DG, Greenberg BM. 1993. Impacts of UV radiation and photomodification on the
16 toxicity of PAHs to the higher plant, Lemna gibba (duckweed). Environ Toxicol Chem
17 12:1067-1077.
18
19 Huang X-D, McConkey BJ, Babu TS, Greenberg BM. 1997. Mechanisms of photoinduced toxicity of
20 photomodified anthracene to plants: Inhibition of photosynthesis in the aquatic higher plant
21 Lemna gibba (Duckweed). Environ Toxicol Chem 16:1707-1715.
22
23 Hunt J, Anderson B, Phillips B, Newman J, Tjeerdema R, Taberski K, Wilson C, Stephenson M,
24 Puckett HM, Fairey R, Oakden J. 1998. Sediment quality and biological effects in San
Final Draft PAH Mixtures ESG Document 8-19 5 April 2000
-------
1 Francisco Bay. Final Technical Report. California State Water Resources Control Board.
2
3 Ireland DS, Burton GA, Hess GO. 1996. In situ toxicity evaluations of turbidity and photoinduction of
4 polycyclic aromatic hydrocarbons. Environ Toxicol Chem 15:574-581.
5
6 Juhnke VI, Ludemann D. 1978. Ergebnisse der untersuchuag von 200 chemischen verbindungen auf
7 akute fischtoxizitat mit dem goldorfentest. Z Wasser und Abivasser-Forschung 111:161-164.
8
9 Kagan J, Kagan PA, Buhse HE, Jr. 1984. Light-dependent toxicity of a-terthienyl and anthracene to
10 late embryonic stages ofRanapipiens. J Chem Ecol 10:1115-1122.
11
12 Kagan J, Kagan ED, Kagan IS, .Kagan PA, Quigley S. 1985. The phototoxicity of non-carcinogenic
13 polycyclic aromatic hydrocarbons in aquatic organisms, Chemo 14:1829-1834.
14
15 Kamler, EWA. 1992. Early life history of fish: an energetics approach. Fish and Fisheries. Ser. 4.
16 Chapman and Hall, New York.
17
18 Karickhoff SW, Brown DS, Scott TA. 1979. Sorption of hydrophobic pollutants on natural sediments.
19 Water Res 13:241-248.
20
21 Karickhoff SW, McDaniel VK, Melton C, Vellino AN, Nute DE, Carreira LA. 1991. Predicting
22 chemical reactivity by computer. Environ Toxicol Chem 10:1405-1416.
23
24 Kimball G. 1978. The effects of lesser known metals and one organic to fathead minnows (Pimephales
Final Draft PAH Mixtures ESG Document 8-20 5 April 2000
-------
1 Home JD, Swirsky MA, Hollister TA, Oblad BR, Kennedy JH. 1983. Aquatic toxicity studies of five
2 pollutants. Report no. 4398, U.S. EPA contract no. 68-01-6201. NUS Corporation, Houston,
3 TX, 93pp.
4
5 Hose JE, Hannah JB, Landolt ML, Miller BS, Felton SP and Iwaoka WT. 1981. Uptake of
6 benzo[a]pyrene by gonadal tissue of flatfish (family pleuronectidae) and its effects on
7 subsequent egg development. /. Toxicol. Environ. Health. 7: 991-1000.
8
9 Hose JE, Hannah, JB, DUulio D, Landolt ML, Miller BS, Iwaoka WT and Felton SP. 1982. Effects of
10 benzo[a]pyrene on early development of flatfish. Arch Environ Contain Toxicol 11: 167-171.
11
12 Hose JE, Hannah JB, Puffer HW and Landolt ML. 1984, Histologic and skeletal abnormalities in
13 benzo[a]pyrene-treated rainbow trout alevins. Arch Environ Contam Toxicol 13: 675-684.
14
15 Huang X, Dixon DG, Greenberg BM. 1993. Impacts of UV radiation and photomodification on the
16 toxicity of PAHs to the higher plant, Lemna gibba (duckweed). Environ Toxicol Chem
17 12:1067-1077.
18
19 Huang X-D, McConkey BJ, Babu TS, Greenberg BM. 1997. Mechanisms of photoinduced toxicity of
20 photomodified anthracene to plants: Inhibition of photosynthesis in the aquatic higher plant
21 Lemna gibba (Duckweed). Environ Toxicol Chem 16:1707-1715.
22
23 Hunt J, Anderson B, Phillips B, Newman J, Tjeerdema R, Taberski K, Wilson C, Stephenson M,
24 Puckett HM, Fairey R, Oakden J. 1998. Sediment quality and biological effects in San
Final Draft PAH Matures E$G Document 8-19 5 April 2000
-------
1 Francisco Bay. Final Technical Report. California State Water Resources Control Board.
2
3 Ireland DS, Burton GA, Hess GG. 1996. In situ toxicity evaluations of turbidity and photoinduction of
4 polycyclic aromatic hydrocarbons. Environ Toxicol Chem 15:574-581.
5
6 Juhnke VI, Ludemann D. 1978. Ergebnisse der untersuchung von 200 chemischen verbindungen auf
7 akute fischtoxizitat mit dem goldorfentest. Z Wasser und Abivasser- Forschung 111:161-164.
8
9 Kagan J, Kagan PA, Buhse HE, Jr. 1984. Light-dependent toxicity of a-terthienyl and anthracene to
10 late embryonic stages of Rana pipiens. J Chem Ecol 10:1115-1122.
11
12 Kagan J, Kagan ED, Kagan IS, Xagan PA, Quigley S. 1985. The phototoxicity of non-carcinogenic
13 polycyclic aromatic hydrocarbons in aquatic organisms. Chemo 14:1829-1834.
14
15 Kamler, EWA. 1992. Early life history of fish: an energetics approach. Fish and Fisheries. Ser. 4.
16 Chapman and Hall, New York.
17
18 Karickhoff SW, Brown DS, Scott TA. 1979. Sorption of hydrophobic pollutants on natural sediments.
19 Water Res 13:241-248.
20
21 Karickhoff SW, McDaniel VK, Melton C, Vellino AN, Nute DE, Carreira LA. 1991. Predicting
22 chemical reactivity by computer. Environ Toxicol Chem 10:1405-1416.
23
24 Kimball G. 1978. The effects of lesser known metals and one organic to fathead minnows (Pimephales
Final Draft PAH Mixtures ESG Document 8-20 5 April 2000
-------
1 promelas) and Daphnia magna. Manuscript. Dept. of Entomology, Fisheries and Wildlife,
2 Univ. of Minnesota. Minneapolis, MN, 88 pages.
3 , «
4 Knutsen J. 1995. Effects of marine organisms from polycyclic aromatic hydrocarbons (PAH) and other
5 constituents of waste water from aluminum smelters with examples from Norway. Sci Total
6 Environ 163:107-122.
7 •
8 Kolok AS, Huckins JN, Petty JD and Oris JT. 1996. The role of water ventilation and sediment
9 ingestion in the uptake of benzo[a]pyrene in gizzard shad (Dorosoma cepedianum). Environ
10 Toxicol Chem 15(10): 1752-1759.
11
12 Konemann H. 1980. Structure-activity relationships and addhivity in fish toxicities of environmental
13 pollutants. Ecotoxicol Environ Safety 4:415-421.
14
15 Konemann H. 1981. Quantitative structure-toxicity relationships in fish toxicity studies. Part 1:
16 Relationship for 50 industrial pollutants. Toxicology 19:209-221.
17
18 Korn S., Rice S. 1981. Sensitivity to, and accumulation and depuration of, aromatic petroleum
19 components by early life stages of coho salmon (Oncorhynchus kisutch). Rapp. P.-V. Reun.,
20 Cons Int Explor Mer 178:87-92.
21
22 Kosian PA, Makynen EA, Monson PD, Mount DR, Spacie A, Mekenyan OG, Ankley GT. 1998.
23 Application of toxicity-based fractionation techniques and structure-activity relationship models
24 for the identification of phototoxic polycyclic aromtaic hydrocarbons in sediment pore water.
Final Draft PAH Mixtures ESG Document 8-21 5 April 2000
-------
1 Environ Toxicol Chem 17:1021-1033.
2
»
3 Kreyszig E. 1972. Advanced Engineering Mathematics. J. Wiley and Sons, New York.
4
5 Kuhn A, Lussier S. 1987. Results from acute and life-cycle tests with Americamysis bahia exposed to
6 phenanthrene. Memorandum to David J. Hansen, U.S. EPA, Narragansett, RI. August 3,
7 1987. 3 pp.
8
9 Kukkonen J, Landnim PF. 1994. Toxicokinetics and toxicity of sediment-associated pyrene to
10 Lumbriculus variegatus (Oligochaeta). Environ Toxicol Chem 13:1457-1468.
11
12 LaFlamme RE, Kites RA. 1978. The global distribution of polycyclic aromatic hydrocarbons in recent
13 sediments. Geochim Cosmo Acta 42:289-303.
14
15 Lake JL, Norwood C, Dimock C, Bowen R. 1979. Origins of polycyclic aromatic hydrocarbons in
16 estuarine sediments. Geochim Cosmo Acta 43:1847-1854.
17
18 Landrum PF. 1995. Bioavailability of fluoranthene to the amphipods, Hyalella azteca and Diporeia sp.
19 Incomplete citation.
20
21 Landrum PF, Bartell SM, Giesy JP, Leversee GJ, Bowling JW, Haddock J, LaGory K, Gerould S,
22 Bruno M. 1984a. Fate of anthracene in an artificial stream: a case study. Ecotoxicol Environ
23 Safety 8:183-201.
24
Final Draft PAH Mixtures ESG Document 8-22 5 April 2000
-------
1 promelas) and Daphnia magna. Manuscript. Dept. of Entomology, Fisheries and Wildlife,
2 Univ. of Minnesota. Minneapolis, MN, 88 pages.
3 , *
4 Knutsen J. 1995. Effects of marine organisms from polycyclic aromatic hydrocarbons (PAH) and other
5 constituents of waste water from aluminum smelters with examples from Norway. Sd Total
6 Environ 163:107-122.
7
8 Kolok AS, Huckins JN, Petty JD and Oris JT. 1996. The role of water ventilation and sediment
9 ingestion in the uptake of benzo[a]pyrene in gizzard shad (Dorosoma cepedianum). Environ
10 Toxicol Chem 15(10): 1752-1759.
11
12 Konemann H. 1980. Structure-activity relationships and additivity in fish toxicities of environmental
13 pollutants. Ecotoxicol Environ Safety 4:415-421.
I4
15 Konemann H. 1981. Quantitative structure-toxicity relationships in fish toxicity studies. Part 1:
16 Relationship for 50 industrial pollutants. Toxicology 19:209-221.
17
18 Korn S., Rice S. 1981. Sensitivity to, and accumulation and depuration of, aromatic petroleum
19 components by early life stages of coho salmon (Oncorhynchus Jdsutch). Rapp. P.-V. Reun.,
20 Cons Int Explor Mer 178:87-92.
21
22 Kosian PA, Makynen EA, Monson PD, Mount DR, Spacie A, Mekenyan OG, Ankley GT. 1998.
23 Application of toxicity-based fractionation techniques and structure-activity relationship models
24 for the identification of phototoxic polycyclic aromtaic hydrocarbons in sediment pore water.
Final Draft PAH Mixtures ESG Document 8-21 5 April 2000
-------
1 Environ Toxicol Chem 17:1021-1033.
2
£
3 Kreyszig E. 1972. Advanced Engineering Mathematics. J. Wiley and Sons, New York.
4
5 Kuhn A, Lussier S. 1987. Results from acute and life-cycle tests with Americcanysis bahia exposed to
6 , phenanthrene. Memorandum to David J. Hansen, U.S. EPA, Narragansett, RI. August 3,
7 1987. 3 pp.
8
9 Kukkonen J, Landrum PF. 1994. Toxicokinetics and toxicity of sediment-associated pyrene to
10 Lumbriculus variegatus (Oligochaeta). Environ Toxicol Chem 13:1457-1468.
11
12 LaFlamme RE, Kites RA. 1978. The global distribution of polycyclic aromatic hydrocarbons in recent
13 sediments. Geochim Cosmo Acta 42:289-303.
14
15 Lake JL, Norwood C, Dimock C, Bowen R. 1979. Origins of polycyclic aromatic hydrocarbons in
16 estuarine sediments. Geochim Cosmo Acta 43:1847-1854.
17
18 Landrum PF. 1995. Bioavailability of fluoranthene to the amphipods, Hyalella azteca and Diporeia sp.
19 Incomplete citation.
20
21 Landrum PF, Bartell SM, Giesy JP, Leversee GJ, Bowling JW, Haddock J, LaGory K, Gerould S,
22 Bruno M. 1984a. Fate of anthracene in an artificial stream: a case study. Ecotoxicol Environ
23 Safety 8:183-201.
24
Final Draft PAH Mixtures ESG Document 8-22 '5 April 2000
-------
1 Landrum PF, Giesy JP, Oris JT, Allred PM. 1984b. Photoinduced toxicity of polycyclic aromatic
2 hydrocarbons to aquatic organisms. In Vandermeulen JH, Hrudly S, eds, Oil in Freshwater:
3 Chemistry, Biology, Countermeasure Technology, Pergainon Press, New York, pp 3Cj4 - 318.
4
5 Landrum PF, Eadie BJ, Faust WR. 1991. Toxicokinetics and toxicity of a mixture of sediment-
6 associated polycyclic aromatic hydrocarbons to the amphipod Diporeia sp. Environ Toxicol
7 Chem 10:35-46.
8
9 Landrum PF, Dupuis WS, Kukkonen J. -1994. Toxicokinetics and toxicity of sediment associated
10 pyrene and phenanthrene in Diporeia spp.: Examination of equilibrium partitioning theory and
11 residue-based effects for assessing hazard. Environ Toxicol Chem 13:1769-1780.
12
13 Larsson P. 1985. contaminated sediments of lakes and oceans act as sources of chlorinated
14 hydrocarbons for release to water and atmosphere. Nature 317:347-349.
15
16 LeBlanc GA. 1980a. Acute toxicity of priority pollutants to water flea (Daphnia magna). Bull Environ
17 Contam Toxicol 24:684-691.
18
19 LeBlanc GA. 1980b. Acute toxicity of fluoranthene to various marine organisms. Personal
20 communication.
21
22 Lee GF, Jones-Lee A. 1996. Can chemically based sediment quality criteria be used as reliable
23 screening tools for water quality impacts? SETACNews 16:14-15.
24
Final Draft PAH Mixtures ESG Document 8-23 5 April 2000
-------
1 Lemke AE 1984. Inter-laboratory comparison of continuous flow, early life stage testing with fathead
2 minnows. EPA-600/3-84-005 or PB84-129493. National Technical Information Service,
3 Springfield, VA, 26 pp. *
4
5 Lemke AE, Anderson RL. 1984. Insect interlaboratory toxicity test comparison study for the
6 chironomid (Paratanytarsus sp.) procedure. EPA-600/3-84-054 or P1384-180025. National
7 Technical Information Service. Springfield, VA, 15 pp.
8
9 Lemke AE, Durban E, Felhaber T. 1983. Evaluation of a fathead minnow Pimephales promelas
10 embryo-larval test guideline using acenaphthene and isophorone. EPA-600/3-83-062 or P1383-
11 243436. National Technical Information Service, Springfield, VA, 26 pp.
12
13 Leo AJ. 1972. Relationships between partitioning solvent systems. In Biological Correlations - The
14 Hansch Approach Advances in Chemistry Series 114, American Chemical Society,
15 Washington, DC, pp 51-60.
16
17 Long ER, LG Morgan. 1990. The potential for biological effects of sediment-sorbed contaminants
18 tested in the National Status and Trends Program. NOAA Tech. Memo. NOS OMA 52,
19 National Oceanic and Atmospheric Agency, Rockville, MD, 175 pp.
20
21 Long ER, Mac Donald DD, Smith SL, Calder FD. 1995. Incidence of adverse effects within ranges of
22 chemical concentrations in marine and estuarine sediments. Environ Manag 19:81-97.
23
24 Lotufo GR, Fleeger JW. 1996. Toxicity of sediment-associated pyrene and phenanthrene to
Final Draft PAH Mixtures ESG Document 8-24 5 April 2000
-------
1 Landrum PF, Giesy JP, Oris JT, Allred PM. 19845. Photoinduced toxicity of polycyclic aromatic
2 hydrocarbons to aquatic organisms. In Vandermeulen JH, Hrudly S, eds, Oil in Freshwater:
3 Chemistry. Biology, Countermeasure Technology, Pergamon Press, New York, pp 3Q4 - 318.
4
5 Landrum PF, Eadie BJ, Faust WR. 1991. Toxicokinetics and toxicity of a mixture of sediment-
6 associated polycyclic aromatic hydrocarbons to the amphipod Diporeia sp. Environ Toxicol
7 Chem 10:35-46.
8
9 Landrum PF, Dupuis WS, Kukkonen J. -1994. Toxicokinetics and toxicity of sediment associated
10 pyrene and phenanthrene in Diporeia spp.: Examination of equilibrium partitioning theory and
11 residue-based effects for assessing hazard. Environ Toxicol Chem 13:1769-1780.
12
13 Larsson P. 1985. contaminated sediments of lakes and oceans act as sources of chlorinated
14 hydrocarbons for release to water and atmosphere. Nature 317:347-349.
15 .
16 LeBlanc GA. 1980a. Acute toxicity of priority pollutants to water flea (Daphnia magna). Bull Environ
17 Contam Toxicol 24:684-691.
18
19 LeBlanc GA. 1980b. Acute toxicity of fluoranthene to various marine organisms. Personal
20 communication.
21
22 Lee GF, Jones-Lee A. 1996. Can chemically based sediment quality criteria be used as reliable
23 screening tools for water quality impacts? SETAC News 16:14-15.
24
Final Draft PAH Mbaures ESG Document 8-23 5 April 2000
-------
1 Lemke AE 1984. Inter-laboratory comparison of continuous flow, early life stage testing with fathead
2 minnows. EPA-600/3-84-005 or PB84-129493. National Technical Information Service,
3 Springfield, VA, 26 pp. ,
4
5 Lemke AE, Anderson RL. 1984. Insect interlaboratory toxicity test comparison study for the
6 chironomid (Paratanytarsus sp.) procedure. EPA-600/3-84-054 or P1384-180025. National
7 Technical Information Service. Springfield, VA, 15 pp.
8 .
9 Lemke AE, Durban E, Felhaber T. 1983. Evaluation of a fathead minnow Pimephales promelas
10 embryo-larval test guideline using acenaphthene and isophorone. EPA-600/3-83-062 or P1383-
11 243436. National Technical Information Service, Springfield, VA, 26 pp.
12
13 Leo AJ. 1972. Relationships between partitioning solvent systems. In Biological Correlations - The
14 Hansch Approach Advances in Chemistry Series 114, American Chemical Society,
15 Washington, DC, pp 51-60.
16
17 Long ER, LG Morgan. 1990. The potential for biological effects of sediment-sorbed contaminants
18 tested in the National Status and Trends Program. NOAA Tech. Memo. NOS OMA 52,
19 National Oceanic and Atmospheric Agency, Rockville, MD, 175 pp.
20
21 Long ER, Mac Donald DD, Smith SL, Calder FD. 1995. Incidence of adverse effects within ranges of
22 chemical concentrations in marine and estuarine sediments. Environ Manag 19:81-97.
23
24 Lotufo GR, Fleeger AY. 1996. Toxicity of sediment-associated pyrene and phenanthrene to
Final Draft PAH Mixtures ESG Document 8-24 5 April 2000
-------
1 Limnodrilus hoffmeisteri (Oligochaeta: Tubificidae). Envion Toxicol Chem 15:1508-1516.
2
3 Mackay D, Bobra A, Shui WY. 1980. Relationships between aqueous solubility and octanol-water
4 partition coefficients. Chemo 9:701-711.
5 -
6 Mackay D, Shiu WY, Ma KC. 1992. Illustrated handbook of physical-chemical properties and
7 environmental fate for organic chemicals. Vol II Polynuclear aromatic hydrocarbons,
8 polychlorinated dioxins and dibenzofurans. Lewis Publishers, Chelsea, ML
9
10 Marine Bioassay Laboratories. 1981. Flow-through early-life stage toxicity tests with fathead minnows
11 (Pimephalespromelas). Final report to United States EPA, Duluth, MN. Marine Bioassay
12 Laboratories, 1234 Highway One, Watsonville, CA, 71 pp.
13
14 Maruya KA, Risebrough RW, Home AJ. 1996. Partitioning of polynuclear aromatic hydrocarbons
15 between sediments from San Francisco Bay and their porewaters. Environ Scl Technol '
16 30:2942-2947.
17
18 Maruya KA, Risenbrough RW, Home AJ. 1997. The bioaceumulation of polynuclear aromatic
19 hydrocarbons by benthic invertebrates hi an intertidal marsh. Environ Toxicol Chem
20 16:1087-1097.
21
22 Mattson VR, Arthur JW, Walbridge CT. 1976. Acute toxicity of selected organic compounds to
23 fathead minnows. EPA-600/3-76-097, United States EPA, Office of Research and
24 Development, 13 pp.
Final Draft PAH Mixtures ESG Document 8-25 5 April 2000
-------
1 May WE. 1980. The solubility behavior of polycyclic aromatic hydrocarbons in aqueous systems. In
2 Petroleum in the Marine Environment. Petrakis L, Weiss FT, eds, American Chemical Society
3 Advances in Chemistry Series. Washington, D.C., pp 143-192. *
4
5 McCarty LS, Mackay D, Smith AD, Ozbura GW, Dixon DG. 1991. Interpreting aquatic toxicity
6 QSARs: The significance of toxicant body residues at the pharmacologic end point. In QSAR
7 In Environmental Toxicology. IV. Ekevier, Amsterdam.
8
9 McCloskey JT, Oris JT. 1991. Effect of water temperature and dissolved oxygen concentration on the
10 photo-induced toxicity of anthracene to juvenile bluegill sunfish (Lepomis macrochirus). Aquat
11 Toxicol 21:145-156.
12
13 McConkey BJ, Duxbury CL, Dixon DG, Greenberg BM. 1997. Toxicity of a PAH photooxidation
14 product to the bacteria Photobacterium phosphoreum and the duckweed Lemna gibba: Effects
15 of phenethrene and its primary photoproduct, phenanthrenequinone. Environ Toxicol Chem
16 16:892-899.
17
18 McGroddy SE, Harrington JW. 1995. Sediment porewater partitioning of polycyclic aromatic
19 hydrocarbons in three cores from Boston Harbor, Massachusetts. Environ Sci Technol 29:1542-
20 1550.
21
22 McGroddy SE, Farrington JW, Gschwend PM. 1996. Comparison of the in situ and desorption
23 sediment-water partitioning of polycyclic aromatic hydrocarbons and polychlorinated biphenyls.
24 Environ Sci Technol 30:172-177.
Final Draft PAH Mixtures ESG Document 8-26 5 April 2000
-------
1 Limnodrilus hoffmeisteri (Oligochaeta: Tubificidae). Envion Toxicol Chem 15:1508-1516.
2
3 Mackay D, Bobra A, Shui WY. 1980. Relationships between aqueous solubility and octanol-water
4 partition coefficients. Chetno 9:701-711.
5 -
6 Mackay D, Shiu WY, Ma KC. 1992. Illustrated handbook of physical-chemical properties and
7 environmental fate for organic chemicals. Vol II Polynuclear aromatic hydrocarbons,
8 polychlorinated dioxins and dibenzofurans. Lewis Publishers, Chelsea, MI.
9
10 Marine Bioassay Laboratories. 1981. Flow-through early-life stage toxicity tests with fathead minnows
11 (Pimephales promelas). Final report to United States EPA, Duluth, MN. Marine Bioassay
12 Laboratories, 1234 Highway One, Watsonville, CA, 71 pp.
13
14 Maruya KA, Risebrough RW, Home AJ. 1996. Partitioning of polynuclear aromatic hydrocarbons
15 between sediments from San Francisco Bay and their porewaters. Environ Sci Technol
16 30:2942-2947.
17
18 Maruya KA, Risenbrough RW, Home AJ. 1997. The bioaceumulation of polynuclear aromatic
19 hydrocarbons by benthic invertebrates in an intertidal marsh. Environ Toxicol Chem
20 16:1087-1097.
21
22 Mattson VR, Arthur JW, Walbridge CT. 1976. Acute toxicity of selected organic compounds to
23 fathead minnows. EPA-600/3-76-097, United States EPA, Office of Research and
24 Development, 13 pp.
Final Draft PAH Mixtures ESC Document 8-25 5 April 2000
-------
1 May WE. 1980. The solubility behavior of polycyclic aromatic hydrocarbons in aqueous systems. In
2 Petroleum in the Marine Environment. Petrakis L, Weiss FT, eds, American Chemical Society
3 Advances in Chemistry Series. Washington, D.C., pp 143-192. *
4
5 McCarty LS, Mackay D, Smith AD, Ozburn GW, Dixon DG. 1991. Interpreting aquatic toxicity
6 QSARs: The significance of toxicant body residues at the pharmacologic end point. In QSAR
7 In Environmental Toxicology. IV. Elsevier, Amsterdam.
8
9 McCloskey JT, Oris JT. 1991. Effect of water temperature and dissolved oxygen concentration on the
10 photo-induced toxicity of anthracene to juvenile bluegill sunfish (Leponus macrochirus). Aquat
11 Toxicol 21:145-156.
12
13 McConkey BJ, Duxbury CL, Dixon DG, Greenberg BM. 1997. Toxicity of a PAH photooxidation
14 product to the bacteria Photobacteriwnphosphoreum and the duckweed Lemma gibba: Effects
15 of phenethrene and its primary photoproduct, phenanthrenequinone. Environ Toxicol Chem
16 16:892-899.
17
18 McGroddy SB, Farrington JW. 1995. Sediment porewater partitioning of polycyclic aromatic
19 hydrocarbons in three cores from Boston Harbor, Massachusetts. Environ Sci Technol 29:1542-
20 1550.
21
22 McGroddy SE, Farrington JW, Gschwend PM. 1996. Comparison of the in situ and desorption
23 sediment-water partitioning of polycyclic aromatic hydrocarbons and polychlorinated biphenyls.
24 Environ Sci Technol 30:172-177.
Final Draft PAH Matures ESG Document 8-26 5 April 2000
-------
1 Mekenyan OG, Ankley GT, Veith GD, Call DJ. 1994a. QSAR estimates of excited states and
2 photoinduced acute toxicity of polycyclic aromatic hydrocarbons. SAR QSAR Environ Res
3 2:237-247. t
4
5 Mekenyan OG, Ankley GT, Veith GD, Call DJ. 19945. QSARs for photoinduced toxicity: 1. Acute
6 lethality of polycyclic aromatic hydrocarbons. Chemosphere 28:567-582.
7
8 Metcalfe CD, Cairns VW and Fitzsimons JD. 198. Experimental induction of liver tumors in rainbow
9 trout (Salmo gairdneri) by contaminated sediment from Hamilton Harbour, Ontario. Can J Fish
10 AquatSci 45: 2161-2167.
11
12 Millemann RE, Birge WJ, Black JA, Cushman RM, Daniels KL, Franco PJ, Giddings JM, McCarthy
13 JF, Stewart AJ. 1984. Comparative acute toxicity to aquatic organisms of components of coal-
14 derived synthetic fuels. Trans Am Fish Soc 113:74-85.
15
16 Monson PD, Ankley GT, Kosian PA. 1995. Phototoxic response of Lumbriculus variegatus to
17 sediments contaminated by polycyclic aromatic hydrocarbons. Environ Toxicol Chem 14:891-
18 894.
19
20 Mortimer MR, Connell DW. 1994. Critical internal and aqueous lethal concentrations of
21 chlorobenzenes with the crab Portunus pelagicus (1). Ecotoxicol Environ Safety 28:298-312.
22
23 Munkittrick KR, Power EA, Sergy GA. 1991. The relative sensitivity of micro-tox, daphnid, rainbow
24 trout, and fathead minnow acute lethality tests. Environ Toxicol Water Quality 6:35-62.
Final Draft PAH Mixtures ESG Document 8-27 5 April 2000
-------
1 Naes K, Oug E. 1997. Multivariate approach to distribution patterns and fate of polycyclic aromatic
2 hydrocarbons in sediments from smelter-affected Norwegian fjords and coastal waters. Environ
3 SciTechnol 31:1253-1258.
4
5 Naes K, Axelman J, Naf C, Broman D. 1998. Role of soot carbon and other carbon matrices in the
6 distribution of PAHs among particles, DOC, and the dissolved phase in the effluent and
7 recipient waters of an aluminum reduction plant. Environ Sci Technol 32:1786-1792.
8
9 National Academy of Sciences (NAS). 1973. Water quality criteria, 1972. EPA-R3-73-033. National
10 Academy of Sciences, U.S. Environmental Protection Agency, Washington, D.C.
11
12 Nebeker AV, Schuytema GS, Griffis WL, Barbitta JA, Carey LA. 1989. Effect of sediment organic
13 carbon on survival ofHyalella a&eca exposed to DDT and endrin. Environ Toxicol Chem
14 8:705-718.
15
16 Neff JM, Bums WA. 1996. Estimation of polycyclic aromatic hydrocarbon concentrations in the water
17 column based on tissue residues in mussels and salmon: An equilibrium partitioning approach.
18 Environ Toxicol Chem 15:2240-2253.
19
20 Neff JM and Anderson JW. 1975. Accumulation, release, and distribution of benzo[a]pyrene-C14 in the
21 clam Rangia cuneata. 1975 Conference on Prevention and Control of Oil Pollution
22 proceedings. March 25-27, 1975. San Francisco, California.
23
24 Newsted JL, Giesy JP. 1987. Predictive models for photoinduced acute toxicity of polycyclic aromatic
Final Draft PAH Matures ESG Document 8-28 5 April 2000
-------
1 Mekenyan OG, Ankley GT, Veith GD, Call DJ. 1994a. QSAR estimates of excited states and
2 photoinduced acute toxicity of polycyclic aromatic hydrocarbons. SAR QSAR Environ Res
3 2:237-247. t
4
5 Mekenyan OG, Ankley GT, Veith GD, Call DJ. 1994b. QSARs for photoinduced toxicity: 1. Acute
6 lethality of polycyclic aromatic hydrocarbons. Chemosphere 28:567-582.
7
8 Metcalfe CD, Cairns VW and Fitzsimons 3D. 198. Experimental induction of liver tumors in rainbow
9 trout (Salmo gairdneri) by contaminated sediment from Hamilton Harbour, Ontario. Can J Fish
10 Aquat Sd 45: 2161-2167.
11
12 Millemann EE, Birge WJ, Black JA, Cushman RM, Daniels KL, Franco PJ, Giddings JM, McCarthy
13 JF, Stewart AJ. 1984. Comparative acute toxicity to aquatic organisms of components of coal-
14 derived synthetic fuels. Trans Am Fish Soc 113:74-85.
15
16 Monson PD, Ankley GT, Kosian PA. 1995. Phototoxic response of Lumbriculus variegatus to
17 sediments contaminated by polycyclic aromatic hydrocarbons. Environ Toxicol Chem 14:891-
18 894.
19
20 Mortimer MR, Council DW. 1994. Critical internal and aqueous lethal concentrations of
21 chlorobenzenes with the crab Portunus pelagicus (1). Ecotoxicol Environ Safety 28:298-312.
22
23 Munkittrick KR, Power EA, Sergy GA. 1991. The relative sensitivity of micro-tox, daphnid, rainbow
24 trout, and fathead minnow acute lethality tests. Environ Toxicol Water Quality 6:35-62.
Final Draft PAH Mixtures ESG Document 8-27 5 April 2000
-------
1 Naes K, Oug E. 1997. Multivariate approach to distribution patterns and fate of polycyclic aromatic
2 hydrocarbons in sediments from smelter-affected Norwegian fjords and coastal waters. Environ
3 SciTechnol 31:1253-1258. »
4
5 Naes K, Axelman J, Naf C, Broman D. 1998. Role of soot carbon and other carbon matrices in the
6 distribution of PAHs among particles, DOC, and the dissolved phase hi the effluent and
7 recipient waters of an aluminum reduction plant. Environ Sci Technol 32:1786-1792.
8
9 National Academy of Sciences (NAS). 1973. Water quality criteria, 1972. EPA-K3-73-033. National
10 Academy of Sciences, U.S. Environmental Protection Agency, Washington, D.C.
11
12 Nebeker AV, Schuytema GS, Gfiffis WL, Barbitta JA, Carey LA. 1989. Effect of sediment organic
13 carbon on survival ofHyalella a&eca exposed to DDT and endrin. Environ Toxicol Chem
14 8:705-718.
15
16 Neff JM, Bums WA. 1996. Estimation of polycyclic aromatic hydrocarbon concentrations in the water
17 column based on tissue residues in mussels and salmon: An equilibrium partitioning approach.
18 Environ Toxicol Chem 15:2240-2253.
19
20 Neff JM and Anderson JW. 1975. Accumulation, release, and distribution of benzo[a]pyrene-C14 in the
21 clam Rangia cuneata. 1975 Conference on Prevention and Control of Oil Pollution
22 proceedings. March 25-27, 1975. San Francisco, California.
23
24 Newsted JL, Giesy JP. 1987. Predictive models for photoinduced acute toxicity of polycyclic aromatic
Final Draft PAH Matures ESG Document 8-28 5 April 2000
-------
1 hydrocarbons to Daphnia magna, Strauss (Cladocera, Crustacea). Environ Toxicol Chem
2 6:445-461.
3
4 NOAA. 1991. National Status and Trends Program - Second summary of data on chemical
5 contaminants in sediments from the National Status and Trends Program. NOAA Technical
6 Memorandum NOS OMA 59. NOAA Office of Oceanography and Marine Assessment,
7 Rockville, MD, 29 pp + appendices.
8 •
9 Noreen EW. 1989. Computer intensive methods for testing hypotheses: An introduction. John Wiley
10 and Sons Inc., New York, N.Y.
11
12 Northwestern Aquatic Sciences, Inc. 1982. Round robin testing of the midge (Tanytarsus): Acute and
13 chronic toxicity tests of 2,4,6-trichlorophenol and acenaphthene. Contract No. 68-033081.
14 Report to United States EPA, ERL-Duluth, MN, Northwestern Aquatic Sciences, Inc.,
15 Newport, OR, 66 pp.
16
17 Oris JT, Giesy JP, Jr. 1985. The photoenhanced toxicity of anthracene to juvenile sunfish (Lepomis
18 spp.).Aquat Toxicol 6:133-46.
19
20 Oris JT, Giesy JP, Jr. 1986. Photoinduced toxicity of anthracene to juvenile bluegill sunfish (Lepomis
21 macrochirus Rafinesque): Photoperiod effects and predictive hazard evaluation. Environ
22 Toxicol Chem 5:761-768.
23
24 Oris JT, Giesy JP, Jr. 1987. The photo-induced toxicity of polycyclic aromatic hydrocarbons to larvae
Final Draft PAH Matures ESG Document 8-29 5 April 2000
-------
1 of the fathead minnow (Pimephales promelas). Chemos 16:1395-404.
2
3 Oris JT, Giesy JP, Allred PM, Grant DF, Landruin PF. 1984. Photoinduced toxicity of anthracene in
4 aquatic organisms: an environmental perspective. In Veziroglu TN, ed, The Biosphere:
5 Problems and Solutions, Elsevier Science Publishers B.V., Amsterdam, The Netherlands, pp
6 639 - 658.
7
8 Oris JT, Hall AT, Tylka JD. 1990. Humic acids reduce the photo-induced toxicity of anthracene to fish
9 and Daphnia. Environ Toxicol Chem 9:575-583.
10
11 Oris JT, Winner RW, Moore MV. 1991. A four-day survival and reproduction toxicity test for
12 CeriodaphiUa dubia. Environ Toxicol Chem 10:217-224.
13
14 Ostrander GK, Landolt ML and Kocan RM. 1989. Whole life history studies of coho salmon
15 (Oncorhynchus Idsutch) following embryonic exposure to benzo[a]pyrene. Aquatic Toxicol 15:
16 109-126.
17
18 Ostrander GK, Landolt ML and Kocan RM. 1988. The ontogeny of coho salmon (Oncorhynchus
19 kisutch) behavior following embryonic exposure to benzo[a]pyrene. Aquat Toxicol 13: 325-346.
20
21 Ott FS, Harris RP, O'Hara SCM. 1978. Acute and sublethal toxicity of naphthalene and three
22 methylated derivatives to the estuarine copepod, Eurytemora cffinis. Mar Environ Res 1:49-58.
23
24 Owen, B.B. and S.R. Brinkley. 1941. Calculation of the effect of pressure upon ionic equilibrium in
Final Draft PAH Mixtures ESG Document 8-30 5 April 2000
-------
1 hydrocarbons to Daphnia magna, Strauss (Cladocera, Crustacea). Environ Toxicol Chem
2 6:445-461.
3 *
4 NOAA. 1991. National Status and Trends Program - Second summary of data on chemical
5 contaminants in sediments from the National Status and Trends Program. NOAA Technical
6 Memorandum NOS OMA 59, NOAA Office of Oceanography and Marine Assessment,
7 Rockville, MD, 29 pp + appendices.
8
9 Noreen EW. 1989. Computer intensive methods for testing hypotheses: An introduction. John Wiley
10 and Sons Inc., New York, N.Y.
11
12 Northwestern Aquatic Sciences, Inc. 1982. Round robin testing of the midge (Tanytarsus): Acute and
13 chronic toxicity tests of 2,4,6-trichlorophenol and acenaphthene. Contract No. 68-033081.
14 Report to United States EPA, ERL-Duluth, MN, Northwestern Aquatic Sciences, Inc.,
15 Newport, OR, 66 pp.
16
17 Oris JT, Giesy JP, Jr. 1985. The photoenhanced toxicity of anthracene to juvenile sunfish (Lepomis
18 spp.).Aquat Toxicol 6:133-46.
19
20 Oris JT, Giesy JP, Jr. 1986. Photoinduced toxicity of anthracene to juvenile bluegill sunfish (Lepomis
21 macrochirus Rafinesque): Photoperiod effects and predictive hazard evaluation. Environ
22 Toxicol Chem 5:761-768.
23 .
24 Oris JT, Giesy JP, Jr. 1987. The photo-induced toxicity of polycyclic aromatic hydrocarbons to larvae
Final Draff PAH Mixtures ESC Document 8-29 5 April 2000
-------
1 of the fathead minnow (Pimephales promelas). Chemos 16:1395-404.
2
3 Oris JT, Giesy JP, Allred PM, Grant DF, Landrum PF. 1984. Photoinduced toxicity of anthracene in
4 aquatic organisms: an environmental perspective. In Veziroglu TN, ed, The Biosphere:
5 Problems and Solutions, Elsevier Science Publishers B.V., Amsterdam, The Netherlands, pp
6 639-658.
7
8 Oris JT, Hall AT, Tylka JD. 1990. Humic acids reduce the photo-induced toxicity of anthracene to fish
9 and Daphnia. Environ Toxicol Chem 9:575-583.
10
11 Oris JT, Winner RW, Moore MV. 1991. A four-day survival and reproduction toxicity test for
12 Ceriodaphilia dubia. Environ Toxicol Chem 10:217-224.
13
14 Ostrander GK, Landolt ML and Kocan RM. 1989. Whole life history studies of coho salmon
15 (Oncorhynchus fdsutch) following embryonic exposure to benzo[a]pyrene. Aquatic Toxicol 15:
16 109-126.
17
18 Ostrander GK, Landolt ML and Kocan RM. 1988. The ontogeny of coho salmon (Oncorhynchus
19 kisutch) behavior following embryonic exposure to benzo[a]pyrene. Aquat Toxicol 13: 325-346.
20
21 Ott FS, Harris RP, O'Hara SCM. 1978. Acute and sublethal toxicity of naphthalene and three
22 methylated derivatives to the estuarine copepod, Eurytemora affinis. Mar Environ Res 1:49-58.
*7^
24 Owen, B.B. and S.R. Brinkley. 1941. Calculation of the effect of pressure upon ionic equilibrium in
Final Draft PAH Mixtures ESG Document 8-30 5 April 2000
-------
I pure water and in salt solutions. Chem Rev 29:461-472.
2
3 Ozretich RJ, Swartz RC, Lamberson JO, Ferraro SP. 2000a. An extension of the £PAH moflel to
4 alkylated and other polynuclear aromatic hydrocarboos. (MS in preparation).
5
6 Ozretich RJ, Ferraro SP, Lamberson JO, Cole FA. 2000b. A test of the £PAH model at a creosote-
7 contaminated site in Elliott Bay, Washington. Environ Toxicol Chem (In Press).
8
9 Paine ME), Chapman PM, Allard PJ, Murdoch MH, Minifie D. 1996. Limited bioavailability of
10 sediment PAH near an aluminum smelter: Contamination does no equal effects. Environ
11 Toxicol Chem 15:2003-2018.
12
13 Parkerton TF, Connolly JP, Thomann RV, Uclirin CG. 1993. Do aquatic effects or human health end
14 points govern the development of sediment-quality criteria for nonionic organic chemicals?
15 Environ Toxicol Chem 12:507-523.
16
17 Passino DRM, Smith SB. 1987. Acute bioassays and hazard evaluation of representative contaminants
18 detected in Great Lakes fish. Environ Toxicol Chem 6:901-907.
19
20 Pelletier MC, Burgess RM, Ho KT, Kuhn A, McKinney RA, Ryba SA. 1997. Phototoxicity of
21 individual PAHs and petroleum to marine invertebrate larvae and juveniles. Environ Toxicol
22 Chem 16:2190-2199.
23
24 Pelletier MC, Burgess RM, Cantwell MG, May AJ, Serbst JR, Ho KT. 2000a. Resistance of intertidal
Final Draft PAH Mixtures ESG Document 8-31 5 April 2000
-------
1 and subtidal organisms to photo-enhanced PAH toxicity. (Manuscript).
2
3 Pelletier MC, Burgess RM, Cantwell MG, Serbst JR, Ho KT, Ryba SA. 2000b. Importance of
4 maternal transfer of photo-reactive PAHs from benthic adults to their pelagic larvae.
5 (Manuscript).
6
7 Pickard GL, Emery WJ. 1982. Descriptive Physical Oceanography, 4th Edition. Pergamon Press,
8 Oxford, U.K.
9
10 Pickering QH, .Henderson C. 1966. Acute toxicity of some important petrochemicals to fish. / Water
11 PoUut Control Fed 38:1419-1429.
12
13 Prahl FG, Carpenter R. 1983. Polynuclear aromatic hydrocarbon (PAH) - phase association in
14 Washington coastal sediment. Geochimica et Cosmo Acta 47:1013-1023.
15 '
16 PTI Environmental Services. 1991. Pollutants of concern in Puget Sound. EPA 910/9-91-003. United
17 States EPA, Region 10, Seattle, WA.
18
19 Randall TL, Knopp PV. 1980. Detoxification of specific organic substances by wet oxidation. / Water
20 Pollut Control Fed 52:2117-2130.
21
22 Readman JW, Mantoura RFC, Rhead MM. 1984. The physico-chemical speciation of polycyclic
aromatic hydrocarbons (PAH) in aquatic systems. Fresenius ZAnal Chem 319:126-131.23
24
Final Draft PAH Mixtures ESG Document 8-32 5 ApriJ 2000
-------
I pure water and in salt solutions. Chem Rev 29:461-472.
2
3 Ozretich RJ, Swartz RC, Lamberson JO, Ferraro SP. 2000a. An extension of the £PAH moSel to
4 alkylated and other polynuclear aromatic hydrocarbons. (MS in preparation).
5
6 Ozretich RJ, Ferraro SP, Lamberson JO, Cole FA. 2000b. A test of the £PAH model at a creosote-
7 contaminated site in Elliott Bay, Washington. Environ Toxicol Chem (In Press).
8
9 Paine MD, Chapman PM, Allard PJ, Murdoch MH, Minifie D. 1996. Limited bioavailability of
10 sediment PAH near an aluminum smelter: Contamination does no equal effects. Environ
11 Toxicol Chem 15:2003-2018.
12
13 Parkerton TF, Connolly JP, Thomann RV, Uclirin CG. 1993. Do aquatic effects or human health end
14 points govern the development of sediment-quality criteria for nonionic organic chemicals?
15 Environ Toxicol Chem 12:507-523.
16
17 Passino DRM, Smith SB. 1987. Acute bioassays and hazard evaluation of representative contaminants
18 detected in Great Lakes fish. Environ Toxicol Chem 6:901-907.
19
20 Pelletier MC, Burgess RM, Ho KT, Kuhn A, McKinney RA, Ryba SA. 1997. Phototoxicity of
21 individual PAHs and petroleum to marine invertebrate larvae and juveniles. Environ Toxicol
22 Chem 16:2190-2199.
23
24 Pelletier MC, Burgess RM, Cantwell MG, May AJ, Serbst JR, Ho KT. 2000a. Resistance of intertidal
Final Draft PAH Mixtures ESG Document 8-31 5 April 2000
-------
1 and subtidal organisms to photo-enhanced PAH toxicity. (Manuscript).
2
3 Pelletier MC, Burgess RM, Cantwell MG, Serbst JR, Ho KT, Ryba SA. 20005. Importance of
4 maternal transfer of photo-reactive PAHs from benthic adults to their pelagic larvae.
5 (Manuscript).
6
7 Pickard GL, Emery WJ. 1982. Descriptive Physical Oceanography, 4th Edition. Pergamon Press,
8 Oxford, U.K.
9
10 Pickering QH,.Henderson C. 1966. Acute toxicity of some important petrochemicals to fish. / Water
11 PoUut Control Fed 38:1419-1429.
12
13 Prahl FG, Carpenter R. 1983. Polynuclear aromatic hydrocarbon (PAH) - phase association in
14 Washington coastal sediment. Geochimica et Cosmo Acta 47:1013-1023.
15
16 PTI Environmental Services. 1991. Pollutants of concern in Puget Sound. EPA 910/9-91-003. United
17 States EPA, Region 10, Seattle, WA.
18
19 Randall TL, Knopp PV. 1980. Detoxification of specific organic substances by wet oxidation. / Water
20 Pottut Control Fed 52:2117-2130.
21
22 Readman JW, Mantoura RFC, Rhead MM. 1984. The physico-chemical speciation of polycyclic
aromatic hydrocarbons (PAH) in aquatic systems. Fresenius Z Anal Chem 319:126-131.23
24
Final Draft PAH Mixtures ESG Document 8-32 5 April 2000
-------
1 Ren L, Huang XD, McConkey BJ, Dixon DG, Greenberg BM. 1994. Photoinduced toxicity of three
2 polycyclic aromatic hydrocarbons (fluoranthene, pyrene and naphthalene) to the duckweed
3 Lemma gibba. Ecotoxicol Environ Safety 28:160-171. ,
4
5 Rice SD, Thomas RE. 1989. Effect of pre-treatment exposures of toluene or naphthalene on the
6 tolerance of pink salmon (Oncorhynchus gorbuscha) and kelp shrimp (Eualis suckleyi). Comp
7 BiochemPhysiol94C:289-293.
8
9 Rogerson A, Sliiu W, Huang G, Mackay D, Berger J. 1983. Determination and interpretation of
10 hydrocarbon toxicity to ciliate protozoan. Aquat Toxicol 3:215- 228.
11
12 Rossi SS, Neff JM. 1978. Toxicity of polynuclear aromatic hydrocarbons to the polychaete Neanthes
13 arenaceodetitata. Mar Pollut Bull 9:220-223.
14
15 Russom CL, Bradbury SP, Broderius DE, Hammermeister DE, Drummond RA. 1997. Predicting
16 modes of toxic action from chemical structure: acute toxicity in the fathead minnow
17 (Pimephales promelas). Environ Toxicol Chem 16:948-67.
18
19 Salomons W, de Rooij NM, Kerdijk H, Bril J. 1987. Sediments as sources of contaminants? Hydrobiol
20 149:13-30.
21
22 Schultz ME and Schultz RJ. 1982. Induction of hepatic tumors with 7,12-dimethylbenz[a]anthracene in
23 two species of viviparous fishes (genus Poepciliopsis). Environ Research 27: 337-351.
24
Final Draft PAH Mixtures ESG Document 8-33 5 April 2000
-------
1 Schuytema GS, Nebeker AV, Griffis WL, Miller CE. 1989. Effect of freezing on toxicity of sediments
2 contaminated with DDT and endrin. Environ Toxicol Chem 8:883-891.
*
3
4 Schwarzenbach RP, Gschwend PM, and Imboden DM. 1993. Environmental Organic Chemistry,
5 Wiley Interscience. John Wiley & Sons Inc., New York.
6
7 Setschenow JZ. 1889. Uber di Konstitution der Salzlosungen aur Grund ihres Verhaltens zu
8 Kohlensaure. Z. Physik. Chem 4:117
9
10 Sibley PK, Ankley GT, Mount DR. 1997. Comparison of sensitivity of several aquatic invertebrates to
11 UV light following exposure to fluoranthene-spiked sediment. Society of Environmental
12 Toxicology and Chemistry, 18* Annual Meeting, San Francisco, CA.
13
14 Sijm D, Schipper M, Opperhuizen A. 1993. Toxicokinetics of halogenated benzenes in fish: Lethal
15 body burden as a lexicological end point. Environ Set Technol 12:1117-1127.
16
17 Slooff NV, Baersehnan R. 1980. Comparison of the usefulness of the Mexican axolotl (Ambystoma
18 mexicanum) and the clawed toad (Kenopus laevis) in toxicological bioassays. Bull Environ
19 Contam Toxicol 24:439-443.
20
21 Slooff W, Canton JH, Hermens JLM. 1983. Comparison of the susceptibility of 22 freshwater species
22 to 15 chemical compounds. I. (Sub)acute toxicity tests. Aquat Toxicol 4:113-128.
23
24 Smith AD, Bharath A, Mallard C, Orr D, Smith K, Sutton JA, Vumanich J, McCarty LS, Ozbum
Final Draft PAH Mixtures ESG Document 8-34 5 April 2000
-------
1 Ren L, Huang XD, McConkey BJ, Dixon DG, Greenberg BM. 1994. Photoinduced* toxicity of three
2 polycyclic aromatic hydrocarbons (fluoranthene, pyrene and naphthalene) to the duckweed
3 Lemma gibba. Ecotoxicol Environ Safety 28:160-171. ?
4
5 Rice SD, Thomas RE. 1989. Effect of pre-treatment exposures of toluene or naphthalene on the
6 tolerance of pink salmon (Oncorhynchus gorbuscha) and kelp shrimp (Eualis stickleyi). Comp
7 BiochemPhysiol94C:289-293.
8
9 Rogerson A, Sliiu W, Huang G, Mackay D, Berger J. 1983. Determination and interpretation of
10 hydrocarbon toxicity to ciliate protozoan. Aquat Toxicol 3:215- 228.
11
12 Rossi SS, Neff JM. 1978. Toxicity of polynuclear aromatic hydrocarbons to the polychaete Neanthes
13 arenaceodemata. Mar Pollut Bull 9:220-223.
14
15 Russom CL, Bradbury SP, Broderius DE, Hammermeister DE, Drummond RA. 1997. Predicting
16 modes of toxic action from chemical structure: acute toxicity in the fathead minnow
17 (Pimephales promelas). Environ Toxicol Qiem 16:948-67.
18
19 Salomons W, de Rooij NM, Kerdijk H, Bril J. 1987. Sediments as sources of contaminants? Hydrobiol
20 149:13-30.
21
22 Schultz ME and Schultz RJ. 1982. Induction of hepatic tumors with 7,12-dimethylbenz[a]anthracene in
23 two species of viviparous fishes (genus Poepciliopsis). Environ Research 27: 337-351.
24
Final Draft PAH Matures ESG Document 8-33 5 April 2000
-------
1 Schuytema GS, Nebeker AV, Griffis WL, Miller CE. 1989. Effect of freezing on toxicity of sediments
2 contaminated with DDT and endrin. Environ Toxicol Chem 8:883-891.
?,
3 :
4 Schwarzenbach RP, Gschwend PM, and Imboden DM. 1993. Environmental Organic Chemistry,
5 Wiley Interscience. John Wiley & Sons Inc., New York.
6
7 Setscheaow JZ. 1889. Uber di {Constitution der Salzlosungen aur Grund ihres Verhaltens zu
8 Kohlensaure. Z. Physik. Chem 4:117
9
10 Sibley PK, Ankley GT, Mount DR. 1997. Comparison of sensitivity of several aquatic invertebrates to
11 UV light following exposure to fluoranthene-spiked sediment. Society of Environmental
12 Toxicology and Chemistry, 18* Annual Meeting, San Francisco, CA.
13
14 Sijm.D, Schipper M, Opperhuizen A. 1993. Toxicokinetics of halogenated benzenes in fish: Lethal
15 body burden as a lexicological end point. Environ Set Technol 12:1117-1127.
16
17 Slooff NV, Baerselman R. 1980. Comparison of the usefulness of the Mexican axolotl (Ambystoma
18 mexicanum) and the clawed toad (Kenopus laevis) in lexicological bioassays. Bull Environ
19 Contam Toxicol 24:439-443.
20
21 Slooff W, Canton JH, Hermens JLM. 1983. Comparison of the susceptibility of 22 freshwater species
22 to 15 chemical compounds. I. (Sub)acute toxicity tests. Aquat Toxicol 4:113-128.
23
24 Smith AD, Bharath A, Mallard C, Orr D, Smith K, Sutton JA, Vumanich J, McCarty LS, Ozbum
Final Draft PAH Mixtures ESG Document 8-34 5 April 2000
-------
1 GW. 1991. The acute and chronic toxicity of ten chlorinated organic compounds to the
2 American flagfish (Jordanellafloridae). Arch Environ Contam Toxicol 20:94-102.
3
4 Smith SB, Savino JF, Blouin MA. 1988. Acute toxicity to Daphnia pulex of six classes of chemical
5 compounds potentially hazardous to great lakes aquatic biota. J Great Lakes Res 14:394-404.
6
7 Socha SB, Carpenter R. 1987. Factors affecting pore water hydrocarbon concentrations in Puget Sound
8 sediments. Geochimicaet Cosmo Acta 51:1273-1284.
9
10 Spehar RL, Poucher S, Brooke LT, Hansen DJ, Champlin D, Cox DA. 1999. Comparative toxicity of
11 fluoranthene to freshwater and saltwater species under fluorescent and ultraviolet light. Arch
12 Environ Contam Toxicol. 37:496-502.
13
14 Spehar RL, Mount DR, Lukasewycz MT, Leonard EN, Burgess RM, Serbst JR, Heinis LJ, Berry WJ,
15 Mattson VR, Burkhard LP, Kuhn A. 2000. Response of freshwater and saltwater invertebrates
16 to a mixture of high KQW PAHs in sediment. (MS in preparation)
17
18 Stephan CE, Mount DI, Hansen DJ, Gentile JH, Chapman GA, Brungs WA. 1985. Guidelines for
19 deriving numerical national water quality criteria for the protection of aquatic organisms and
20 their uses. PB85-227049. National Technical Information Service, Springfield, VA, 98 pp.
21
22 Suedel BG, Rodgers JH, Jr. 1996. Toxicity of fluoranthene to Daphnia magna, Hyalella azteca,
23 Chironomus tentans, and Stylaria lacustris in water-only and whole sediment exposures. Bull
24 Environ Contam Toxicol 57:132-138.
Final Draft PAH Matures ESG Document 8-35 5 April 2000
-------
1 Suedel BC, Rodgers JH, Clifford PA. 1993. Bioavailability of fluoranthene in freshwater sediment
2 toxicity tests. Environ Toxicol Chem 12:155-165.
3
4 Swartz RC. 1991a. Acenaphthene and phenanthrene files. Memorandum to David J. Hansen, June 26,
5 1991. 160pp.
6
7 Swartz RC. 1991b. Fluoranthene experimental design: Final. Unpublished manuscript. 10pp.
8 December 31, 1991.
9
10 Swartz RC. 2000. Ten-day LC50 values for Rhepoxynius abronius. Memorandum to David Hansen,
11 Great Lakes Environmental Center, Traverse City, MI. February, 2000.
12
13 Swartz RC, Kemp PF, Schults DW, Lamberson JO. 1988. Effects of mixtures of sediment
14 . contaminants on the marine infaunal amphipod, Rhepoxynius abronius. Environ Toxicol Chem
15 7:1013-1020.
16
17 Swartz RC, Schults DW, DeWitt TH, Ditsworth GR, Lamberson JO. 1990. Toxicity of fluoranthene
18 in sediment to marine amphipods: A test of the equilibrium partitioning approach to sediment
19 quality criteria. Environ Toxicol Chem 9:1071-1080.
20
21 Swartz RC, Schults DW, Ozretich RJ, Lamberson JO, Cole FA, DeWitt TH, Redmond MS, Ferraro
22 SP. 1995. £PAH: A model to predict the toxicity of field-collected marine sediment
23 contaminated with polynuclear aromatic hydrocarbons. Environ Toxicol Chem 14:1977-1987.
24 '
Final Draft PAH Mixtures ESG Document 8-36 5 April 2000
-------
1 GW. 1991. The acute and chronic toxicity of ten chlorinated organic compounds to the
2 American flagfish (Jordanella floridae). Arch Environ Contain Toxicol 20:94-102.
3
4 Smith SB, Savino JF, Blouin MA. 1988. Acute toxicity to Daphnia pulex of six classes of chemical
5 compounds potentially hazardous to great lakes aquatic biota. J Great Lakes Res 14:394-404.
6
1 Socha SB, Carpenter R. 1987. Factors affecting pore water hydrocarbon concentrations in Puget Sound
8 sediments. Geochimica et Cosmo Acta 51:1273-1284.
9
10 Spehar RL, Poucher S, Brooke LT, Hansen DJ, Champlin D, Cox DA. 1999. Comparative toxicity of
11 fluoranthene to freshwater and saltwater species under fluorescent and ultraviolet light. Arch
12 Environ Contam Toxicol. 37:496-502.
13
14 Spehar RL, Mount DR, Lukasewycz MT, Leonard EN, Burgess RM, Serbst JR, Heinis LJ, Berry WJ,
15 Mattson VR, Burkhard LP, Kuhn A. 2000. Response of freshwater and saltwater invertebrates
16 to a mixture of high Kgw PAHs in sediment. (MS in preparation)
17
18 Stephan CE, Mount DI, Hansen DJ, Gentile JH, Chapman GA, Brungs WA. 1985. Guidelines for
19 deriving numerical national water quality criteria for the protection of aquatic organisms and
20 their uses. PB85-227049. National Technical Information Service, Springfield, VA, 98 pp.
21
22 Suedel BG, Rodgers JH, Jr. 1996. Toxicity of fluoranthene to Daphnia niagna, Hyalella azteca,
23 Chironomus tentans, and Stylaria lacustris in water-only and whole sediment exposures. Bull
24 Environ Contam Toxicol 57:132-138.
Final Draft PAH Matures ESG Document 8-35 5 April 2000
-------
1 Suedel BC, Rodgers JH, Clifford PA. 1993. Bioavailabiliry of fluoranthene in freshwater sediment
2 toxicity tests. Environ Toxicol Chem 12:155-165.
3
4 Swartz RC. 1991a. Acenaphthene and phenanthrene files. Memorandum to David J. Hansen, June 26,
5 1991. 160pp.
6
7 Swartz RC. 1991b. Fluoranthene experimental design: Final. Unpublished manuscript. 10pp.
8 December 31, 1991.
9
10 Swartz RC. 2000. Ten-day LC50 values for Rhepoxynius abronius. Memorandum to David Hansen,
11 Great Lakes Environmental Center, Traverse City, MI. February, 2000.
12
13 Swartz RC, Kemp PF, Schults DW, Lamberson JO. 1988. Effects of mixtures of sediment
14 contaminants on the marine infaunal amphipod, Rhepoxynius abronius. Environ Toxicol Chem
15 7:1013-1020.
16
17 Swartz RC, Schults DW, DeWitt TH, Ditsworth GR, Lamberson JO. 1990. Toxicity of fluoranthene
18 in sediment to marine amphipods: A test of the equilibrium partitioning approach to sediment
19 quality criteria. Environ Toxicol Chem 9:1071-1080.
20
21 Swartz RC, Schults DW, Ozretich RJ, Lamberson JO, Cole FA, DeWitt TH, Redmond MS, Ferraro
22 SP. 1995. £PAH: A model to predict the toxicity of field-collected marine sediment
23 contaminated with polynuclear aromatic hydrocarbons. Environ Toxicol Chem 14:1977-1987.
24
Final Draft PAH Mixtures ESG Document 8-36 5 April 2000
-------
1 Swartz RC, Ferraro SP, Lamberson JO, Cole FA, Ozretich RJ, Boese BL, Schults DW, Behrenfeld M,
2 Ankley GT. 1997. Photoactivation and toxicity of mixtures of PAH compounds in marine
3 sediment. Environ Toxicol Chem 16:2151-2157. *
4
5 Tatem HE. 1977. Accumulation of naphthalenes by grass shrimp: effects on respiration, hatching and
6 larval growth. In Wolfe OA, eds, Fate and Effects of Petroleum Hydrocarbons in Marine
1 Organisms and Ecosystems, Pages 201-209. Pergamon Press, New York, NY.
8
9 Tatem HE, Cox BA, Anderson JW. 1978. The toxicity of oils and petroleum hydrocarbons to estuarine
10 crustaceans. Estuar Coast Mar Sci 8:365- 373,
11
12 Tay JML, Doe KG, Wade SJ, Vaughn DA, Berrigan RE and Moore MJ. 1992. Sediment bioassessment
13 in Halifax Harbor. Environ Toxicol Chem 11:1567-1581.
14
15 Tetra Tech. 1986. Eagle Harbor preliminary investigations. Final Report EGHB-2, TC-3025-03.
16 Bellevue, WA.
17
18 Thursby GB. 1991a. Review of freshwater round-robin data for acenaphthene. Memorandum to
19 David J. Hansen, September 18, 1991. 2 pp.
20
21 Thursby GB. 1991b. Re-analyses of data from Home et al., 1983. Memorandum to David J. Hansen,
22 September 24, 1991,2pp.
23
24 Thursby GB, Berry WJ, Champlin D. 1989a. Acute toxicity of acenaphthene to saltwater animals.
Final Draft PAH Mixtures ESG Document 8-37 5 April 2000
-------
1 Memorandum to David J. Hansen, February 7, 1989, 9 pp.
2
3 Thursby GB, Berry WJ, Champlin D. 1989b. Flow-through acute and chronic tests with acenaphthene
4 using Americamysis bahia. Memorandum to David J. Hansen, September 19, 1989, 5 pp.
5
6 Thurston R, Giffoil T, Meyn E, Zajdel R, Aoki T, Veith G. 1985. Comparative toxicity often organic
7 chemicals to ten common aquatic species. Water Res 9:1145-1155.
8
9 Trucco RG, Engelhardt FR, Stacey B. 1983. Toxicity, accumulation and clearance of aromatic
10 hydrocarbons in Daphniapulex. Environ Pollut (Series A) 31:191-202.
11
12 United States Environmental Protection Agency. 1978. In-depth studies on health and environmental
13 impacts of selected water pollutants. Contract no. 68-01-4646. (Table of data available from
14 Charles E. Stephan U.S. EPA, Duluth, MN).
15
16 United States Environmental Protection Agency. 1980. Ambient water quality criteria for naphthalene.
17 EPA 440/5-80-059. Office of Water Regulations and Standards, Washington, DC.
18 United States Environmental Protection Agency. 1987. Quality Criteria for Water, 1986. EPA 440/5-
19 86-001. Office of Water Regulation and Standards, Washington, DC.
20
21 United States Environmental Protection Agency. 1989a. Sediment classification methods compendium.
22 Watershed Protection Division, U.S. EPA. 280 p.
23
24 United States Environmental Protection Agency. 1989b. Handbook: Water Quality Control
Final Draft PAH Mixtures ESG Document 8-38 5 April 2000
-------
1 Swartz RC, Ferraro SP, Lamberson JO, Cole FA, Ozretich RJ, Boese BL, Schults DW, Behrenfeld M,
2 Ankley GT. 1997. Photoactivation and toxicity of mixtures of PAH compounds in marine
3 sediment. Environ Toxicol Chem 16:2151-2157. '
4
5 Tatem HE. 1977. Accumulation of naphthalenes by grass shrimp: effects on respiration, hatching and
6 larval growth. In Wolfe OA, eds, Fate and Effects of Petroleum Hydrocarbons in Marine
7 Organisms and Ecosystems, Pages 201-209. Pergamon Press, New York, NY.
8
9 Tatem HE, Cox BA, Anderson JW. 1978. The toxicity of oils and petroleum hydrocarbons to estuarine
10 crustaceans. Estuar Coast Mar Sci 8:365- 373,
11
12 Tay K'L, Doe KG, Wade SJ, Vaughn DA, Berrigan RE and Moore MJ. 1992. Sediment bioassessment
13 in Halifax Harbor. Environ Toxicol Chem 11:1567-1581.
14
15 Tetra Tech. 1986. Eagle Harbor preliminary investigations. Final Report EGHB-2, TC-3025-03.
16 Bellevue, WA.
17
18 Thursby GB. 1991a. Review of freshwater round-robin data for acenaphthene. Memorandum to
19 David J. Hansen, September 18, 1991. 2 pp.
20
21 Thursby GB. 1991b. Re-analyses of data from Home et al., 1983. Memorandum to David J. Hansen,
22 September 24, 1991,2pp.
23
24 Thursby GB, Berry WJ, Champlin D. 1989a. Acute toxicity of acenaphthene to saltwater animals.
Final Draft PAH Mixtures ESG Document 8-37 5 April 2000
-------
1 Memorandum to David J. Hansen, February 7, 1989, 9 pp.
2
3 Thursby GB, Berry WJ, Champlin D. 1989b. Flow-through acute and chronic tests with *acenaphthene
4 using Americamysis bahia. Memorandum to David J. Hansen, September 19, 1989, 5 pp.
5
6 Thurston R, Giffoil T, Meyn E, Zajdel R, Aoki T, Veith G. 1985. Comparative toxicity often organic
7 chemicals to ten common aquatic species. Water Res 9:1145-1155.
8
9 Trucco RG, Engelhardt FR, Stacey B. 1983. Toxicity, accumulation and clearance of aromatic
10 hydrocarbons in Daphnia pulex. Environ Pollut (Series A) 31:191-202.
11
12 United States Environmental Protection Agency. 1978. In-depth studies on health and environmental
13 impacts of selected water pollutants. Contract no. 68-01-4646. (Table of data available from
14 Charles E. Stephan U.S. EPA, Duluth, MN).
15
16 United States Environmental Protection Agency. 1980. Ambient water quality criteria for naphthalene.
17 EPA 440/5-80-059, Office of Water Regulations and Standards, Washington, DC.
18 United States Environmental Protection Agency. 1987. Quality Criteria for Water, 1986. EPA 440/5-
19 86-001. Office of Water Regulation and Standards, Washington, DC.
20
21 United States Environmental Protection Agency. 1989a. Sediment classification methods compendium.
22 Watershed Protection Division, U.S. EPA. 280 p.
23
24 United States Environmental Protection Agency. 1989b. Handbook: Water Quality Control
Final Draft PAH Mixtures ESG Document 8-38 5 April 2000
-------
1 Information System, STORET. Washington, D.C., 20406.
2
3 United States Environmental Protection Agency. 1992. Sediment classification methods compendium.
4 EPA 823-R-92-006, Office of Water, 280p.
5
6 United States Environmental Protection Agency. 1993a. Sediment quality criteria for the protection of
7 benthic organisms: Acenaphthene. EPA 822-R-93-013. Office of Water, Washington, D.C;
8
9 United States Environmental Protection Agency. 1993b. Sediment quality criteria for the protection of
10 benthic organisms: Fluoranthene. EPA 822-R-93-012. Office of Water, Washington, D.C.
11
12 United States Environmental Protection Agency. 1993c. Sediment quality criteria for the protection of
13 benthic organisms: Phenanthrene. EPA 822-R-93-014. Office of Water, Washington, D.C.
14
15 United States Environmental Protection Agency. 1994. Methods for assessing the toxicity of sediment-
16 associated contaminants with estuarine and marine amphipods. EPA/600/R-94/025. Office of
17 Research and Development, Washington D.C.
18
19 United States Environmental Protection Agency. 1996a. EMAP - Estuaries Virginian Province Data
20 1990-1993. Available from: EMAP Home Page WWW site. http://www. epa.gov/emap.
21 Accessed Nov. 1998.
22
23 United States Environmental Protection Agency. 1996b. EMAP - Estuaries Louisianian Province Data
24 1991-1993. Available from: EMAP Home Page WWW site, http://www.epa.gov/emap.
Final Draft PAH Mixtures ESG Document 8-39 5 April 2000
-------
1 Accessed Nov. 1998.
2
3 United States Environmental Protection Agency. 1997a. The incidence and severity of sediment
4 contamination in surface waters of the United States. U.S. EPA, Office of Science and
5 Technology. Vol. 1: National sediment quality survey (EPA 823-R-97-006), Washington, DC.
6
7 United States Environmental Protection Agency. 1997b. The incidence and severity of sediment
8 contamination in surface waters of the United States. Vol. 2: Data summaries for areas of
9 probable concern. EPA 823-R-97-007. U.S. EPA, Office of Science and Technology,
.10 Washington, DC.
11
12 United States Environmental Protection Agency. 1997c. The incidence and severity of sediment
13 contamination in surface waters of the United States. Vol. 3: National sediment contaminant
14 point source inventory EPA 823-R-97-Q08. U.S. EPA, Office of Science and Technology,
15 . Washington, DC.
16
17 United States Environmental Protection Agency. 1998. EMAP-Estuaries Carolinian Province Data
18 1994-1997. Available from EMAP Home Page WWW site. Http://www.epa.gov/emap.
19
20 United States Environmental Protection Agency. 2000a. Technical basis for the derivation of
21 equilibrium- partitioning sediment guidelines (ESGs) for the protection of benthic species:
22 Nonionic organies contaminants. EPA-822-R-00-001. Office of Science and Technology.
23 Washington, DC.
24
25 United States Environmental Protection Agency. 2000b. Equilibrium partitioning sediment guidelines
Final Draft PAH futures ESG Document 8-40 5 April 2000
-------
1 Information System, STORET. Washington, D.C., 20406.
2
3 United States Environmental Protection Agency. 1992. Sediment classification methods compendium.
4 EPA 823-R-92-006, Office of Water, 280p.
5
6 United States Environmental Protection Agency. 1993a. Sediment quality criteria for the protection of
7 benthic organisms: Acenaphthene. EPA 822-R-93-013. Office of Water, Washington, D.C;
8
9 United States Environmental Protection Agency. 1993b. Sediment quality criteria for the protection of
10 benthic organisms: Fluoranthene. EPA 822-R-93-012. Office of Water, Washington, D.C.
11
12 United States Environmental Protection Agency. 1993c. Sediment quality criteria for the protection of
13 benthic organisms: Phenanthrene. EPA 822-R-93-Q14. Office of Water, Washington, D.C.
14
15 United States Environmental Protection Agency. 1994. Methods for assessing the toxicity of sediment-
16 associated contaminants with estuarine and marine amphipods. EPA/600/R-94/025. Office of
17 Research and Development, Washington D.C.
18
19 United States Environmental Protection Agency. 1996a. EMAP - Estuaries Virginian Province Data
20 1990-1993. Available from: EMAP Home Page WWW site. http://www. epa.gov/emap.
21 Accessed Nov. 1998.
22 '
23 United States Environmental Protection Agency. 1996b. EMAP - Estuaries Louisianian Province Data
24 1991-1993. Available from: EMAP Home Page WWW site, http://www.epa.gov/emap.
Final Draft PAH Mixtures ESG Document 8-39 5 April 2000
-------
1 Accessed Nov. 1998.
2
3 United States Environmental Protection Agency. 1997a. The incidence and severity of sediment
4 contamination in surface waters of the United States. U.S. EPA, Office of Science and
5 Technology. Vol. 1: National sediment quality survey (EPA 823-R-97-006), Washington, DC.
6
7 United States Environmental Protection Agency. 1997b. The incidence and severity of sediment
8 contamination hi surface waters of the United States. Vol. 2: Data summaries for areas of
9 probable concern. EPA 823-R-97-007. U.S. EPA, Office of Science and Technology,
10 Washington, DC.
11
12 United States Environmental Protection Agency. 1997c. The incidence and severity of sediment
13 contamination hi surface waters of the United States. Vol. 3: National sediment contaminant
14 point source inventory EPA 823-R-97-008. U.S. EPA, Office of Science and Technology,
15 . Washington, DC.
16
17 United States Environmental Protection Agency. 1998. EMAP-Estuaries Carolinian Province Data
18 1994-1997. Available from EMAP Home Page WWW site. Http://www.epa.gov/emap.
19
20 United States Environmental Protection Agency. 2000a. Technical basis for the derivation of
21 equilibrium- partitioning sediment guidelines (ESGs) for the protection of benthic species:
22 Nonionic organies contaminants. EPA-822-R-QO-001. Office of Science and Technology.
23 Washington, DC.
24
25 United States Environmental Protection Agency. 2000b. Equilibrium partitioning sediment guidelines
Final Draft PAH '.'^rures ESG Document 8-40 5 April 2000
-------
1 (ESGs) for the protection of benthic organisms: Metals mixtures cadmium, copper, lead,
2 nickel, silver and zinc. EPA-822-R-00-005. Office of Science and Technology, Washington,
3 DC. *
4
5 United States Environmental Protection Agency. 2000c. Equilibrium partitioning sediment guidelines
6 (ESGs) for the protection of benthic organisms: Endrin. EPA-822-R-00-004. Office of Science
7 and Technology, Washington, DC.
8
9 United States Environmental Protection Agency. 2000d. Equilibrium partitioning sediment guidelines
10 (ESGs) for the protection of benthic organisms: Dieldrin. EPA-822-R-003. Office of Science
11 and Technology, Washington, DC.
12
13 United States Environmental Protection Agency. 2000e. Implementation framework for the use of
14 equilibrium partitioning sediment guidelines (ESGs). Office of Science and Technology,
15 . Washington, DC.
16 .
17 United States Environmental Protection Agency. 2000f. Methods for the derivation of site-specific
18 equilibrium partitioning sediment guidelines (ESGs) for the protection of benthic organisms.
19 (In press).
20
21 van Leeuwen CJ, Van Der Zandt PTJ, Aidenberg T, Verhaar HIM, Hermens JLM. 1992. Application
22 of QSARS, extrapolation and equilibrium partitioning in aquatic effects assessment. 1. Narcotic
23 industrial pollutants. Environ Toxicol Chem 11:267-282.
24
25 van Wetzel. 1983. Limnology. 2nd Edition. Saunders College Printing, New York, U.S.A.
Final Draft PAH ?,flitres ESG Document 8-41 5 April 2000
-------
1 van Wetzel AP, de Vries DAM, Kostense S, Sijm DTHM, Opperhuizen A. 1995. Intraspecies variation
2 in lethal body burdens of narcotic compounds. Aquat Toxicol 33:325-325.
%
3
4 van Wetzel AP, de Vries DAM, Sijm DTHM, Opperhuizen A. 1996. Use of lethal body burden in the
5 evaluation of mixture toxicity. Ecotoxicol Environ Safety 35:236-241.
6
7 Varanasi U. 1989. Metabolism ofpofycyclic aromatic hydrocarbons in the aquatic environment. CRC,
8 Boca Raton, FL.
9
10 Veith GD, Call DJ, Brooke LT. 1983. Structure-toxicity relationships for the fathead minnow,
11 Pimephalespromelas: Narcotic industrial chemicals. Can J Fish Aquat Sc/40:743-748.
12
13 Veith GD, Mekenyan OG, Ankley GT, Call DJ. 1995&. QSAR evaluation of a-terthenial
14 phototoxicity. Environ Sci Technol 29:1267-1272.
15 .-
16 Veith GD, Mekenyan OG, Ankley GT, Call DJ. 1995b. A QSAR analysis of substituent effects on the
17 photoinduced acute toxicity of PAHs. Chemos 30:2129-2142.
18 .
19 Verhaar HJM, van Leeuwen CJ, Hermens JLM. 1992. Classifying environmental pollutants. 1.
20 Structure-activity relationships for prediction of aquatic toxicity. Chemos 25:471-491.
21
22 Wallen IE, Greer WC, Lasater R. 1957. Toxicity to Gambusia affinis of certain pure chemicals in
23 turbid waters. Stream Pollut 29:695-711.
24
25 Ward GS, Parrish PR, Rigby RA. 1981. Early life stage toxicity tests with a saltwater fish: Effects of
Final Draft PAH XLxures ESG Document 8-42 5 April 2000
-------
1 (ESGs) for the protection of benthic organisms: Metals mixtures cadmium, copper, lead,
2 nickel, silver and zinc. EPA-822-R-00-005. Office of Science and Technology, Washington,
3 DC. ?
4
5 United States Environmental Protection Agency. 2000c. Equilibrium partitioning sediment guidelines
6 (ESGs) for the protection of benthic organisms: Endrin. EPA-822-R-00-004. Office of Science
7 and Technology, Washington, DC.
8
9 United States Environmental Protection Agency. 2000d. Equilibrium partitioning sediment guidelines
(ESGs) for the protection of benthic organisms: Dieldrin. EPA-822-R-003. Office of Science
11 and Technology, Washington, DC.
10
12
13 United States Environmental Protection Agency. 2000e. Implementation framework for the use of
14 equilibrium partitioning sediment guidelines (ESGs). Office of Science and Technology,
15 . . Washington, DC.
16
17 United States Environmental Protection Agency. 2000f. Methods for the derivation of site-specific
18 equilibrium partitioning sediment guidelines (ESGs) for the protection of benthic organisms.
19 (In press).
20
21 van Leeuwen CJ, Van Der Zandt PTJ, Aidenberg T, Verhaar HIM, Hermens JLM. 1992. Application
22 of QSARS, extrapolation and equilibrium partitioning in aquatic effects assessment. 1. Narcotic
23 industrial pollutants. Environ Toxicol Chem 11:267-282.
24
25 van Wetzel. 1983. Limnology. 2nd Edition. Saunders College Printing, New York, U.S.A.
Final Draft PAH M~;ures ESG Document 8-41 5 April 2000
-------
1 van Wetzel AP, de Vries DAM, Kostense S, Sijm DTHM, Opperhuizen A. 1995. Intraspecies variation
2 in lethal body burdens of narcotic compounds. Aquat Toxicol 33:325-325.
s
3
4 van Wetzel AP, de Vries DAM, Sijm DTHM, Opperhuizen A. 1996. Use of lethal body burden in the
5 evaluation of mixture toxicity. Ecotoxicol Environ Safety 35:236-241.
6
7 Varanasi U. 1989. Metabolism ofpofycyclic aromatic hydrocarbons in the aquatic environment. CRC,
8 Boca Raton, PL.
9 '
10 Veith GD, Call DJ, Brooke LT. 1983. Structure-toxicity relationships for the fathead minnow,
11 Pimephales promelas: Narcotic industrial chemicals. Can J Fish Aquat Sci 40:743-748.
12
13 Veith GD, Mekenyan OG, Ankley GT, Call DJ. 1995a/ QSAR evaluation of a-terthenial
14 phototoxicity. Environ Sci Technol 29:1267-1272.
15 .-
16 Veith GD, Mekenyan OG, Ankley GT, Call DJ. 1995b. A QSAR analysis of substituent effects on the
17 photoinduced acute toxicity of PAHs. Chemos 30:2129-2142.
18 .
19 Verhaar HJM, van Leeuwen CJ, Hermens JLM. 1992. Classifying environmental pollutants. 1.
20 Structure-activity relationships for prediction of aquatic toxicity. Chemos 25:471-491.
21
22 Wallen IE, Greer WC, J-asater R. 1957. Toxicity to Gambusia affinis of certain pure chemicals in
23 turbid waters. Stream Pollut 29:695-711.
24
25 Ward GS, Parrish PR, Rigby RA. 1981. Early life stage toxicity tests with a saltwater fish: Effects of
Final Draft PAH Xzxures ESG Document 8-42 5 April 2000
-------
1 eight chemicals on survival, growth and development of sheepshead minnows (Cyprinodon
2 variegatus). J Toxicol Environ Health 8:225-240.
3 s
4 West CW, Kosian PA, Mount DR, Makynen EA , Pasha MS, Sibley PK, Ankley GT. 2000.
5 Amendment of sediments with a carbonaceous resin reduces bioavailability of polycyclic
6 aromatic hydrocarbons. Environ Toxicol Chem (In Press).
7
8 Whiteman FW, Ankley GT, Kahl MD, Rau DM, Balcer MD. 1996. Evaluation of interstitial water as a
9 route of exposure for ammonia in sediment tests with benthic macroinvertebrates. Environ
10 Toxicol Chem 15:794-801.
11
12 Wilkinson L. 1990. SYSTAT: The System for. SYSTAT, Inc., Evanston, IL.
13
14 Winkler KL, Duncan KL, Hose JE and Puffer JW. 1983. Effects of benzo[a]pyrene on the early
15 development of California grunion, Leuresthes temds (pisces, atherinidae). Fish Bull 81: 473-
16 481.
17
18 Xie W-H, Shui W-Y, and Mackay D. 1997. A review of the effects of salt on the solubility of organic
19 compounds La seawater. Mar Environ Res 44:429-4444.
20
21 Zaroogian G, Heltshe JF and Johnson M. 1985. Estimation of toxicity to marine species with structure-
22 activity models developed to estimate toxicity to freshwater fish. Aquat Toxicol 6: 251-270.
23
Final Draft PAH Mirt^res ESC Document 8-43 5 April 2000
-------
Table 2-1. Regression results: y-intercepts and chemical class corrections* (Table from Di Toro
al.,
et
Species /
Americamysis bahia
Portunus pelagicus
Leptocheirus plumulosus
Palaemonetes pugio
Oncorhynchus mykiss
Jordanettafloridae
Ictalurus punctatus
Pimephales promelas
Lepomis macrochirus
Daphnia magna
Cypnnodon variegatus
Oryzias latipes
Carassius auratus
Rana catesbtan
Tony tarsus dissimilis
Orconectes immunis
Alburnus albumus
Nitocra spinipes
Gambusia affiius
Leucisus idtts melanotus
Neanthes arenaceodentata
Anemia salina nauplii
Lymnaea stagnalis
Xenopus laevis
Hydra oligactis
Culex pipiens
Poecilia reticulata
Menidia beryllina
N
30
4
4
8
44
18
7
182
70
113
33
4
43
5
9
6
7
6
8
26
4
32
5
5
5
5
14
8
*i
1.54
1.56
1.56
1.68
1.79
1.82
1.87
2.02
2.03
2.04
2.05
2.05
2.13
2.13
2.14
2.14
2.16
2.17
2.17
2.18
2.23
2.26
2.29
2.33
2.33
2.34
2.36
2.37
SE(bJ
0.082
0.190
0.191
0.137
0.065
0.096
0.139
0.044
0.0056
0.049
0.078
0.182
0.065
0.162
0.125
0.149
0.137
0.148
0.130
0.075
0.19
0.077
0.163
0.163
0.163
0.163
0.101
0.134
10*
34.3
36.1
36.2
48.2
61.7
66.1
74.8
105
108
111
111
112
134
135
137
139
144
147
149
152
168
181
195
213
214
216
228
233
"~ •
££(10")
Atmol/g octanol
6.7
18.2
18.4
16.4
9.4
15.2
25.9
10.8
14.1
12.6
20.5
53.9
20.5
55.9
42.0
52.3
49.1
54.7
47.9
26.8
85
32.8
81.5
88.9
89.5
90.4
55.2
77.3
-------
1 eight chemicals on survival, growth and development of sheepshead minnows (Cyprinodon
2 variegatus). J Toxicol Environ Health 8:225-240.
3 "5
4 West CW, Kosian PA, Mount DR, Makynen EA , Pasha MS, Sibley PK, Ankley GT. 2000.
5 Amendment of sediments with a carbonaceous resin reduces bioavailability of polycyclic
6 aromatic hydrocarbons. Environ Toxicol Chem (In Press).
7
8 Whiteman FW, Ankley GT, Kahl MD, Rau DM, Balcer MD. 1996. Evaluation of interstitial water as a
9 route of exposure for ammonia in sediment tests with benthic macroinvertebrates. Environ
10 Toxicol Chem 15:794-801.
11
12 Wilkinson L. 1990. SYSTAT: The System for. SYSTAT, Inc., Evanston, IL.
13
14 Winkler KL, Duncan KL, Hose JE and Puffer JW. 1983. Effects of benzo[a]pyrene on the early
15 development of California grunion, Leuresthes tenuis (pisces, atherinidae). Fish Bull 81:473-
16 481.
17
18 Xie W-H, Shui W-Y, and Mackay D. 1997. A review of the effects of salt on the solubility of organic
19 compounds in seawater. Mar Environ Res 44:429-4444.
20
21 Zaroogian G, Heltshe JF and Johnson M. 1985. Estimation of toxicity to marine species with structure-
22 activity models developed to estimate toxicity to freshwater fish. Aquat Toxicol 6: 251-270.
23
Final Draft PAH Mirt'tres ESC Document 8-43 5 April 2000
-------
Table 2-1. Regression results: y-intercepts and chemical class corrections* (Table from Di
al.,2000).
Species i
Americamysis bahia
Portunus pelagicus
Leptocheirus plumulosus
Palaemonetes pugio
Oncorhynchus mykiss
Jordanettajloridae
Ictalurus punctatus
Pimephales prometas
Lepomis macrochirus
Daphnia magna
Cyprinodon variegatus
Oryzias latipes
Carassius awatus
Rana catesbian
Tony tarsus dissimilis
Orconectes immunis
Albumus albumus
Nitocra spinipes
Gambusia affinis
Leucisus idus melanotus
Neanthes arenaceodentata
Anemia salina nauptti
Lymnaea stagnate
Xenopiu laevis
Hydra oligactis
Culexpipiens
Poedlia reticulata
Menidia beryllina
N
30
4
4
8
44
18
7
182
70
113
33
4
43
5
9
6
7
6
8
26
4
32
5
5
5
5
14
8
*,
1.54
1.56
1.56
1.68
1.79
1.82
1.87
2.02
2.03
2.04
2.05
2.05
2.13
2.13
2.14
2.14
2.16
2.17
2.17
2.18
2.23
2.26
2.29
2.33
2.33
2.34
2.36
2.37
SE(bJ
0.082
.0.190
0.191
0.137
0.065
0.096
0.139
0.044
0.0056
0.049
0.078
0.182
0.065
0.162
0.125
0.149
0.137
0.148
0.130
0.075
0.19
0.077
0.163
0.163
0.163
0.163
0.101
0.134
10*
34.3
36.1
36.2
48.2
61.7
66.1
74.8
105
108
111
111
112
134
135
137
139
144
147
149
152
168
181
195
213
214
216
228
233
_
SE(10*)
A*mol/g octanol
6.7
18.2
18.4
16.4
9.4
15.2
25.9
10.8
14.1
12.6
20.5
53.9
20.5
55.9
42.0
52.3
49.1
54.7
47.9
26.8
85
32.8
81.5
88.9
89.5
90.4
55.2
77.3
-------
Species i
Daphniapulex
Ambystoma mexicanum
Daphnia cuatllata
Aedes aegypti
Tetrahymena elliotti
Chemical Class {
Aliphatics
Ethers
Alcohols
Aroma tics
Halogenated
Ketones
PAHs
Slope
. N
6
5
5
5
10
N
215
13
134
241
319
49
84
b,
2.38
2.39
2.4
2.42
2.46
Ac,
0.00
0.00
0.00
0.00
-0.244
-0.245
-0.263
-0.945
. SEW
0.150
0.163
0.163
.0.163
0.121
£E(Ac()
-
-
-
-
0.033
0.059
0.057
, 0.014
10*
240
245
249
261
286
JQACt
1.0
1-0
1.0
1.0
0.570
0.569
0.546
SEdtf*)
A*mol/g octanol
*91
103
104
109
85
SECIO4")
-
-
-
0.044
0.078
0.073
*See Equation (2-7).
N = Number of data points.
bi = ^-intercept.
SE(b,)=Stendard error of bL
Ac, =chemical class correction to the y-intercept.
5£(Ac,) = standard error of Act
t=Standard errors of 10** and lO4* are based on the assumption that the estimation errors for and
Ac, are gaussian. The formulas follow from the standard error of a log normally distributed random
variable (Aitchison and Brown, 1957). For x=&, or Ac,, jt, =2.303*. o,=2.303 x SE(x), and
-------
Table 2-2. Comparison of body burdens observed in aquatic organisms acutely exposed to narcotic chemicals and body burdens predicted
from target lipid narcosis theory (Table from DiToroetal., 2000). •
Organism
Mosquitofish,
Gambusia affinis.
Guppy,
Poecilia reticulata
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow.
Pimephales promelas
Chemical
1 ,4-dibromobebzebe
t ,2,3-trichlorobenzene
1 ,2,4-trichlorobenzene
pentachlorobenzene
1,4-difluorobenzene
1 ,2-dichlorobenzene
1 ,4-dichlorobenzene
1 ,2-dibromobenzene
1 ,4-dibromobenzene
1 ,2-dichlorobenzene
1,4-dichlorobenzene
1 ,2-dibromobenzene
1 ,4-dibromobenzene
1 ,2,4-trichlorobenzene
1 , 1 ,2,2-tetrachlorobenzene
dichlorobenzene
dichlorobenzene
1 ,2-dichlorobenzene
1 ,2-dichlorobenzene
1,4-dichlorobenzene
1 ,4-dichlorobenzene
1 ,2 + 1 ,4-dichlorobenzene
1 ,2 + 1 ,4-dichlorobenzene
1 ,2 + 1 ,4-dichlorobenzene
1 ,2 -f 1 ,4-dichlorobenzene
naphthalene
1 ,2,4-trichlorobenzene
log
3.55
3.98
4.00
5.32
2.11
3.31
3.24
3.56
3.55
3.31
3.24
3.56
3.55
4.00
2.31
3.27
3.27
3.31
3.31
3.24
3.24
3.36
4.00
time
hr
96
it
it
ti
1.5
91
41
4
60
18
10
7
10
50.2
57.2
75.5
129
62.3
Obs Mean Pred.
i
g lipid g octanol References
85.0 Chaisuksant and Connell. 1997
140.0
92.0
69.0 93.2 85.3
444.0 . Sijmetal.. 1993
34.0
400.0
24.0
120.0 110.0 130.0
78.0 Sijmetal., 1993
68.0
60.0
54.0
van Wezel et al., 1995
98.9 van Wezel et al., 1996
173
121
107
HO
138
150
123 95.0 59.9 de Maagd et al., 1996
215
-------
Species /
Daphnlapulex
Ambystotna mexicanum
Daphnia cucullata
Aedesaegypti
Tetrahymena elliotti
Chemical Class t
Aliphatics
Ethers
Alcohols
Aromatics
Halogenated
Ketones
PAHs
Slope
. N
6
5
5
5
10
N
215
13
134
241
319
49
84
bt
2.38
2.39
2.4
2.42
2.46
Ac,
0.00
0.00
0.00
0.00
-0.244
-0.245
-0.263
-0.945
SEfbf)
0.150
0.163
0.163
. 0.163
0.121
5E-(Ac()
-
-
-
-
0.033
0.059
0.057
. 0.014
10W
240
245
249
261
286
10**
1.0
1.0
1.0
1.0
0.570
0.569
0.546
S£(10")
/umol/g octanol
\>i
103
104
109
85
cry 1 /"i^"\
OZM i \f }
-
-
-
0.044
0.078
0.073
*See Equation (2-7).
N = Number of data points.
b( = ^-intercept.
SE(3y=Standard error of bL
Ac, =chemical class correction to the y-intercept.
5£(Ac,) = standard error of Act
f=Standard errors of lO" and 10^ are based on the assumption that the estimation errors for and
Ac, are gaussian. The formulas follow from the standard error of a log normally distributed random
variable (Aitchison and Brown, 1957). For x=&, or Ac,, fit =2.303*. o,=2.303 x SE(x), and
-------
Table 2-2. Comparison of body burdens observed in aquatic organisms acutely exposed to narcotic chemicals and body burdens predicted
from target lipid narcosis theory (Table from DiToroetal., 2000). •
Organism
Mosquitofish,
Gambusta afftn'ss.
Guppy,
Poecilia reticulata
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Chemical
1 ,4-dibromobebzebe
1 ,2,3-trichlorobenzene
1 ,2,4-trichlorobenzene
pentachlorobenzene
1,4-difluorobenzene
1 ,2-dichlorobenzene
1 ,4-dichlorobenzene
1 ,2-dibromobenzene
1 ,4-dibromobenzene
1,2-dichlorobenzene
1,4-dichlorobenzene
1 ,2-dibromobenzene
1 ,4-dibromobenzene
1 ,2,4-trichlorobenzene
1 , 1 ,2,2-tetrachlorobenzene
dichlorobenzene
dichlorobenzene
1,2-dichtorobenzene
1,2-dichlorobenzene
1,4-dichlorobenzene
1,4-dichlorobenzene
1 ,2 + 1 ,4-dichlorobenzene
1 ,2+ 1 ,4-dichlorobenzene
1 ,2 4- 1 ,4-dichlorobenzene
1 ,2 + 1 ,4-dichlorobenzene
naphthalene
1 ,2,4-trichlorobenzene
log
3.55
3.98
4.00
5.32
2.11
3.31
3,24
3.56
3.55
3.31
3.24
3.56
3.55
4.00
2.31
3.27
3.27
3.31
3.31
3.24
3.24
3.36
4.00
time
hr
96
"
11
n
1.5
91
41
4
60
18
10
7
10
50.2
57.2
75.5
129
62.3
Obs Mean Pred.
i
g lipid g octanol References
85.0 Chatsuksant and Connell. 1997
140.0
92.0
69.0 93.2 85.3
444.0 Sijm et at., 1993
34.0
400.0
24.0
120.0 110.0 130.0
78.0 Sijm eta!., 1993
68.0
60.0
54.0
vanWezeletal., 1995
98.9 vanWezeletal., 1996
173
121
107
aw
138
150
123 95.0 59.9 de Maagdet al., 1996
215
-------
Obs
Mean
Pred.
Organism
Amphipod,
Leptocheirus
plumtilosus
Crab,
Ponunus pelagicus
Chemical
Fluoranthene
Fluoranthene
1 ,4-dichlorobenzene
1 ,2,3-trichIorobenzene
1 ,2,3,4-tetrachlorobenzene
pentachlorobenzene
log
5.08
5.08
3.24
3.98
4.64
5.32
time
hr
24
24
96
96
96
96
14.0
48.8
9.6
45.0
119
111
jumol/
g lipid
2(5.1
49.9
/wmol/
g octanol References
19.8 Driscoll, S.K. and L.C. Schaffner,
1997 '
Mortimer and Connell, 1994
20.6
-------
Table 3-1. Summary of the chronic sensitivity of freshwater and saltwater organisms to PAHs; test-specific data.
Common Name,
Species Name
Gadoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Midge,
Paratanytarsus sp.
Midge,
Paratanytarsns sp.
Chronic
NOEC OEC Observed Effects Value
Test* Habitat" PAH tested Duration O^g/L) (>ug/L) (Relative to Controls) 0*g/L) Reference
i
LC W Anthracene 21d 2.1 5.3% fewer broods <2.1 Hoist and Giesy, 1989
4.0 8.0% fewer broods
8.2 13.8% fewer broods
LC W Fluoranthene 21d 6.9-17 35 17% reduction in length 24.5 Speharet al., 1999
73 25% reduction in length,
37% fewer young/adult
148 No survival
LC W Phenanthrene 21d 46-57 163 Survival reduced 83%, 96.39 Call et al., 1986
98% fewer broods
LC B Acenaphthene 26d 32-295 575 Survival reduced "90%, 411.8 Northwestern Aquatic
-60% reduction in Sciences, 1982
growth, no reproduction
<#*
LC B Acenaphthene 26d 27-164 315 Survival reduced -20%, 227.3 Northwestern Aquatic
-30% reduction in Sciences, 1982; Thursby,
growth
1991a
-------
Obs
Mean
Pred.
Organism
Amphipod,
Leptocheirus
plumulosus
Crab,
Ponunus petagicus
Chemical
Fluoranthene
Fluoranthene
1,4-dichlorobenzene
1 ,2,3-trichlorobenzene
1 ,2,3,4-tetrachIorobenzene
pentachlorobenzene
log
5.08
5.08
3.24
3.98
4.64
5.32
time
hr
24
24
96
96
96
96
14.0
48.8
9.6
45.0
119
111
jumol/
g lipid
26.1
49.9
A
-------
Table 3-1. Summary of the chronic sensitivity of freshwater and saltwater organisms to PAHs; test-specific data.
Common Name,
Species Name
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Midge,
Paratanytarsus sp.
Midge,
Paratanytarsus sp.
NOEC OEC
Test" Habitat1" PAH tested Duration (^g/L) O'g/L)
LC W Anthracene 21d 2.1
4.0
8.2
LC W Fiuoranthene 21d 6.9-17 35
73
148
LC W Phenanthrene 21d 46-57 163
LC B Acenaphthene 26d 32-295 575
LC B Acenaphthene 26d 27-164 315
Observed Effects
(Relative to Controls)
5.3% fewer broods
8.0% fewer broods
13.8% fewer broods
17% reduction in length
25% reduction in length,
37% fewer young/adult
No survival
Survival reduced 83%,
98% fewer broods
Survival reduced *90%,
-60% reduction in
growth, no reproduction
Survival reduced ~20%,
-30% reduction in
Chronic
Value
(^g/L) Reference
i
<2.1 Hoist and Giesy, 1989
24.5 Spcharetal., 1999
96.39 Call etal., 1986
411.8 Northwestern Aquatic
Sciences, 1982
*>
227.3 Northwestern Aquatic
Sciences, 1982; Thursby,
« f\f\ i _
growth
1991a
-------
Common Name,
Species Name
Test1 Habitat* PAH tested ' Duration
NOEC
(//g/L)
OEC
Observed Effects
(Relative to Controls)
Chronic
Value
(^g/L) Reference
Fathead minnow, ELS
Pimephales promelas
Fathead minnow,
Pimephales promelas
ELS
W Acenaphthene 32d
W Acenaphthene 32d
50
50-109
676 Survival reduced -60%
109 5% reduction in growth 73.82
410 26% reduction in growth,
Survival reduced 45%
630 No survival
410 20% reduction in growth, 211.4
Survival reduced 66%
630 No survival
Academy of Natural
Sciences, 1981; Thursby,
1991a
Academy of Natural
Sciences, 1981; Thursby,
1991a
Fathead minnow,
Pimephales promelas
ELS W Acenaphthene 32-35d 67-332 495 54% reduction in growth 405.4 Cairns and Nebeker, 1982
Fathead minnow, ELS
Pimephales promelas
W Acenaphthene 32-35
-------
Common Name,
Species Name
Test"
Habitatb
PAH tested ' Duration
NOEC OEC Observed Effects
(^g/L) (Mg/L) (Relative to Controls)
Chronic
Value
O^g/L) Reference
Fathead minnow,
Pimepttales promelas
Fathead minnow,
Pimephales promelas
ELS
ELS
W
W
Acenaphthene
32d
Acenaphthene 32d
64
50-91
98
Survival reduced 24%
149. Survival reduced 65%
271 Survival reduced 75 %
441 Survival reduced 80%
139 Survival reduced 20%
290 Survival reduced 50%
426 Survival reduced 52%
79.20 ERGO. 1981
112.5 ERCO, 1981
Fathead minnow,
Pimephales promelas
ELS W Fluoranthene 32d 3.7-10.4 21.7 Survival reduced 67%, 15.02
50% reduction in growth
Speharetal., 1999
Rainbow trout,
Oncorhynchus mykiss
ELS
B/W
Phenanthrene
90d
8 Survival reduced 41%,
33% reduced growth
14 Survival reduced 48 %,
44% reduced growth
32 Survival reduced 52%,
75% reduced growth
66 No survival
6.325
Call et al., 1986
-------
Common Name,
Species Name
Test1 Habitat11 PAH tested ' Duration
NOEC
OEC Observed Effects
Oug'/L) (Relative to Controls)
Chronic
Value
(^g/L) Reference
Fathead minnow, ELS
Pimephales promelas
Fathead minnow,
Pimephales promelas
ELS
W Acenaphthene 32d
W Acenaphthene 32d
50
50-109
676 Survival reduced -60%
109 5% reduction in growth 73.82
410 26% reduction in growth.
Survival reduced 45%
630 No survival
410 2096 reduction in growth, 211.4
Survival reduced 66%
630 No survival
Academy of Natural
Sciences, 1981;Thursby,
1991a
Academy of Natural
Sciences, 1981; Thursby,
1991a
Fathead minnow,
Pimephales promelas
ELS
W Acenaphthene 32-35d 67-332 495 54% reduction in growth 405.4 Cairns and Nebeker, 1982
Fathead minnow,
Pimephales promelas
ELS W Acenaphthene 32-35d 197-345 509 30% reduction in growth 419.0 Cairns and Nebeker, 1982
682 52% reduction in growth.
Survival reduced 45%
1153 87 % reduction in growth,
Survival reduced 97%
-------
Common Name,
Species Name
Test" Habitat" PAH tested
NOEC OEC Observed Effects
Duration C"g/L) (Mg/L) (Relative to Controls)
Chronic
Value
Reference
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
ELS
ELS
W
Acenaphthene
W Acenaphthene
32d
32d
64
50-91
98
Survival reduced 24%
149 Survival reduced 65%
271 Survival reduced 75%
441 Survival reduced 80 %
139 Survival reduced 20%
290 Survival reduced 50%
426 Survival reduced 52%
79.20 ERCO, 1981
112.5 ERCO, 1981
Fathead minnow,
Pimephales promelas
ELS W Fluoranthene 32d 3.7-10.4 21.7 Survival reduced 67%, 15.02
50% reduction in growth
Spehar et al., 1999
Rainbow trout,
Oncorhynchus myk'tss
ELS
B/W
Phenanthrene
90d
8 Survival reduced 41 %,
33% reduced growth
14 Survival reduced 48%,
44% reduced growth
32 Survival reduced 52%,
75% reduced growth
66 No survival
6.325 Call et al., 1986
-------
Common Name,
Species Name
Test1 Habitat" PAH tested ' Duration
NOEC OEC Observed Effects
Oug/L) (Mg/L) (Relative to Controls)
Chronic
Value
Reference
Mysid,
Americamysis bahia
LC B/W Acenaphthene 35d 100-240 340 93% reduction in young 285.7 Home etal., 1983
510 No survival i
Mysid,
Americamysis bahia
LC B/W Acenaphthene 25d 20.5-44.6 91.8 91% reduction in young 63.99 Thursby etal., I989b
168 No reproduction, 34%
reduction in growth
354 Survival reduced 96%, no
reproduction
Mysid,
Americamysis bahia
LC B/W Fluoranthene 28d
5-12
21 Survival reduced 26.7%,
91.7% reduction in young
43 No survival
15.87 U.S. EPA, 1978
Mysid,
Americamysis bahia
LC B/W Fluoranthene 3 Id
0.41-11.1 18.8 Survival reduced 23%, no 14.44 Spehar et al,, 1999
reproduction
Mysid,
Americamysis bahia
LC B/W Phenanthrene 32d 1,5-5,5 11.9 No survival
8.129 Kuhn and Lussier, 1987
Mysid,
Americamysis bahia
LC B/W Pyrene 28d 3.82 5.37 46% reduction in young 4.53 "Champlin and Poucher,
1992c
6.97 47% reduction in young
-------
Common Name,
Species Name Test* Habitat11 PAH tested ' Duration
Sheepsheacl minnow, ELS B/W Acenaphthene 28d
Cyprinodon varlegatus
NOEC OEC
(MB/L) (^g/L)
9.82
15.8
20.9
38.2
240-520 970
2000
2800
Chronic
Observed Effects Value
(Relative to Controls) 0"6/U Reference
73% reduction in young
85% reduction in young
90% reduction in young, •
Survival reduced 37%
No survival
Survival reduced 70% 710.2 Ward eial., 1981
No survival
No survival
a TEST: LC = life-cycle, PLC * partial life-cycle, ELS - early life-stage
b HABITAT: I = infauna, E = epibenthic, W « water column
c NOEC = Concentrations where no significant effects were detected.
d OEC = Concentrations where significant effects were detected on survival, growth, or reproduction.
-------
Common Name,
Species Name
Test' Habitat* PAH tested Duration
NOEC
OEC Observed Effects
0-
-------
Common Name,
Species Name Test* Habitatb PAH tested ' Duration
Sheepshead minnow, ELS B/W Acenaphthcne 28d
Cyprinodon variegatus
NOEC OEC
fog/L) fog/L)
9.82
15.8
20.9
38.2
240-520 970
2000
2800
Chronic
Observed Effects Value
(Relative to Controls) (Mg/L) Reference
73% reduction in young
85% reduction in young
90% reduction in young,
Survival reduced 37%
No survival
Survival reduced 70% 710.2 Ward etal., 1981
No survival
No survival
* TEST: LC = life-cycle, PLC = partial life-cycle, ELS = early life-stage
" HABITAT: I * infauna, E = epibenthic, W — water column
c NOEC » Concentrations where no significant effects were detected.
d OEC = Concentrations where significant effects were detected on survival, growth, or reproduction.
-------
Table 3-2. Acute and chronic values, acute-chronic ratios and derivation of the final acute values, final acute-chronic values and final
chronic values.
Common Name,
Scientific name
FRESHWATER SPECIES
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Midge,
Paratanytarsus sp.
Midge,
Paratanytarsus sp.
Fathead Minnow,
Pimephales promelas
Fathead Minnow,
Pimephales promelas
Fathead Minnow,
Pimephales promelas
Fathead Minnow,
Pimephales promelas
Fathead Minnow,
Pimephales promelas
Fathead Minnow,
Pimephales promelas
Fathead Minnow,
Acute
Value
PAH Tested ^g/L
Anthracene
Fluoramhene 117
Phenanthrene 117
Acenaphthene 2,040'
Acenaphthene 2,040'
Acenaphthene 608
Acenaphthene 608
Acenaphthene
Acenaphthene
Acenaphthene
Acenaphthene
Fluoramhene 69"
Chronic
Value
<2.1
24.5
96.4
411
227
405
419
73.82
211
79.2
112
15.0 .
PAH-Specific Species Mean
Acute- Mean Acute- Acute-
Chronic Ratio Chronic Ratio Chronic Ratio Reference
i
Hoist and Giesy, 1989
4.78 4.78 - Spehar et al., 1999
1.21 1.21 2.41 Call et al., 1986
4.96 - - . Northwestern Aquatic Sciences, 1982
9.00 6.68 6.68 Northwestern Aquatic Sciences,
1982;Thursby,1991a
1.50 - - Cairns and Nebeker, 1982; Thursby,
1991a
1.45 1.4 - Cairns and Nebeker, 1982
Academy of Natural Sciences, 1981
Academy of Natural Sciences, 1981
ERGO, 1981
ERCO, 1981
4,60 4.60 2.61 Spehar et al., 1999
I'imephales promelas
-------
Common Name,
Scientific name
Rainbow trout,
Oncorhynchus mykiss
SALTWATER SPECIES
Mysid,
Americamysis bahia
Mysid,
Americamysis bahia
Mysid,
Americamysis bahia
Mysid,
Americamysis bahia
Mysid,
Americamysis bahia
Mysid,
Americamysis bahia
Sheepshead minnow,
Cyprinodon vartegatus
PAH Tested
Phenanthrene
Acenaphthene
Acenaphthene
Fluoranthene
Fluoranthene
Phenanthrene
Pyrene
Acenaphthene
Acute
' Value
Hl/L
50°
466
460
40
31
27.1
28.3
3,100"
Chronic
Value
Hg'L
6.32
286
64.0
15.9
14.4
8.13
4.53
710
Acute-
Chronic Ratio
7.90
1.63
7.19
2.52
2.15
3.33
6.24
4.37
PAH-Specific
Mean Acute-
Chronic Ratio
7.90
-
3.42
-
2.33
3.33
6.24
4.37
Species Mean
Acute-
Chronic Ratio Reference
7.90 Call et al., 1986
i
Horneetal., 1983
Thursbyetal., 1989b
U.S. EPA, 1978
Speharetal., 1999
Kuhn and Lussier, 1987
3.59 Champlin and Poucher, 1992c
4.37 Ward et al., 1981
' Geometric mean of two flow-through measured tests from the same laboratory as conducted the life-cycle tests.
b LC50 concentration slightly greater than acenaphthene" s water solubility.
c EC50 based on immobilization used as the acute value instead of the LC50.
Final Acute Value = 9.32 jimol/g octanol
Final Acute-chronic Ratio = 4.16
Final Chronic Value - 2.24 //.rnol/g octanol
-------
Table 3-2. Acute and chronic values, acute-chronic ratios and derivation of the final acute values, final acute-chronic values and final
chronic values.
Common Name,
Scientific name
FRESHWATER SPECIES
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Midge,
Paratanytarsus sp.
Midge,
Paratanytarsus sp.
Fathead Minnow,
Pimephales promelas
Fathead Minnow,
Pimephales promelas
Fathead Minnow,
Pimephales promelas
Fathead Minnow,
Pimephales promelas
Fathead Minnow,
Pimephales promelas
Fathead Minnow,
Pimephales promelas
Fathead Minnow,
Acute
Value
PAH Tested //g/L
Anthracene
Fluoranthene 1 17
Phenanthrene 117
Acenaphthene 2,040'
Acenaphthene 2,040'
Acenaphthene 608
Acenaphthene 608
Acenaphthene
Acenaphthene
Acenaphthene
Acenaphthene
Fluoranthene 69"
Chronic
Value
<2.1
24.5
96.4
411
227
405
419
73.82
211
79.2
112
15.0
PAH-Specific Species Mean
Acute- Mean Acute- Acute-
Chronic Ratio Chronic Ratio Chronic Ratio Reference
i
Hoist and Giesy, 1989
4.78 4.78 - Spehar etal., 1999
1.21 1.21 2.41 Call etal., 1986
4.96 - - . Northwestern Aquatic Sciences, 1982
9.00 6.68 6.68 Northwestern Aquatic Sciences,
1982; Thursby,1991a
1.50 - - Cairns and Nebeker, 1982; Thursby,
1991a
1.45 1.4 - Cairns and Nebeker, 1982
Academy of Natural Sciences, 1981
Academy of Natural Sciences, 1981
ERGO, 1981
ERCO, 1981
-,•3*
4,60 4.60 2.61 Spehar et al., 1999
I'imepliales promelas
-------
Common Name,
Scientific name
Rainbow trout,
Oncorftynchus myklss
SALTWATER SPECIES
Mysid,
Americamysis bahia
Mysid,
Americamysls bahta
Mysid,
Americamysls bahia
Mysid,
Americamysls bahia
Mysid,
Americamysls bahia
Mysid,
Americamysls bahia
Sheepshead minnow,
Cyprinodon variegatus
PAH Tested
Phenanthrene
Acenaphthene
Acenaphthene
Fluoranthene
Fluoranthene
Phenanthrene
Pyrene
Acenaphthene
Acute
' Value
H&'L
50°
466
460
40
31
27.1
28.3
3,100"
Chronic
Value
Mg/L
6.32
286
64.0
15.9
14.4
8.13
4.53
710
Acute-
Chronic Ratio
' 7.90
1.63
7.19
2.52
2.15
3.33
6.24
4.37
PAH-Specific
Mean Acute-
Chronic Ratio
7.90
-
3.42
-
2.33
3.33
6.24
4.37
Species Mean
Acute-
Chronic Ratio Reference
7.90 Call et al., 1986
i
Horneetal., 1983
Thursby et al., 1989b
U.S. EPA, 1978
Speharetal., 1999
Kuhn and Lussier, 1987
3.59 Champlm and Poucher, 1992c
4.37 Ward etal., 1981
a Geometric mean of two flow-through measured tests from the same laboratory as conducted the life-cycle tests.
b LC50 concentration slightly greater than acenaphthene^s water solubility.
c EC50 based on immobilization used as the acute value instead of the LC50.
Final Acute Value = 9.32 /wnol/g octanol
Final Acute-chronic Ratio = 4.16
Final Chronic Value « 2.24 /*mol/g octanol
-------
Table 3-3. Results of approximate randomization (AR) test for the equality of the freshwater and
saltwater FAV distributions at a KOVf of 1.0 and AR test for the equality of benthic and
combined benthic and water column FAVs for freshwater and saltwater distributions.
Comparison Habitat or Water TypeA AR Statistic8 Probability0
Fresh vs Salt Fresh (20) Salt (29) 5.746. 93.5
Freshwater: Benthic vs WQCP WQC (49) Benthic (33) 0.862 82.8 L
A Values in parentheses are the number of GMAVS at a KQV of 1.0 used in the comparison.
BAR statistic = FAV difference between original compared groups.
Probability that the theoretical AR statistic <. the observed AR statistic given that all samples came
from the same population.
DCombined Freshwater and Saltwater.
-------
Table 3-4. COC.PAHI.FCV/ concentrations at a Kov/ of 1.0 and properties required for their derivation*
PAH"
indan
naphthalene
Cl-naphthalenes
1 -tnethy tniaphthalene
2-r letnylnaphthalene
act.naphthylene
acenaphthene
1-ethy {naphthalene
2-ethylnaphthalene
C2-naphthalenes
1 ,4-Oimethylnaphthalene
1 ,3-dimethylnaphthalene
2,6-dimeihylnaphthalene
2,3-dimethylnaphthaIene
1 ,5-dtmethylnaphthalene
fluorene
C3-naphthaIcnes
2 , 3 , 5-trimethylnaphthalene
1 ,4,5-trimethyJnaphthalene
anthracene
phenanthrene
Cl-fluorenes
1 -methyl fluorene
C4-naphthaJenes
2-methylanthracene
1-methylanthracene
9-methylanthracene
2-methylphenanthrene
1 -methylphenanthrene
C 1-phenanthrene/anthracenes
9-eihylfluorene
C2-fluorenes
pyrcne
fluoranthene
2-eihylamhracene
C2-phenanthrene/anthraccnes
9 , 10-dimethylamhracene
3,6-dimethylphenanthrene
C3-fluorenes
Cl-pyrenc/fluoranthenes
2,3-bcnzofluorene
benzo(a)fluorene
C3-phenanthrcne/anthracenes
CAS#°
496117
91203
-
90120
91576
208968
83329
1127760
939275
-
571584
575417
581420
581408
571619
86737
-
2245387
213411
120127
85018
•
1730376
.
613127
610480
779022
2531842
832699
-
2294828
-
129000
206440
52251715
-
781431
1576676
-
-
243174
238843
-
Molecular
Weight
(wB/Mmoft
118.18
128.17
142.20
142.20
142.20
152.2
154.21
156.23
156.23
156.23
156.23
156.23
156.23
156.23
156.23
166.22
170.25
170.26
170.2
178.12
178.23
180.25
180.25
184.28
192.26
192.26
192.26
192.26
192.26
192.26
194.28
194.27
202.26
202.26
206.29
206.29
206,29
206.29
208.30
216.29
216.28
216.29
220.32
Mackay
Solid
Solubility0
(we/U
100000
30995
??
28001
25000
16314
3800
10100
8001
??
11400
8001
1700
2500
3100
1900
??
??
2100
45
1100
??
1090
??
29.99
??
261.1
??
269.9
??
1?
??
131.9
239.9
??
??
55.9
??
??
??
2.001
45.00
??
SPARC*.
lOZtftKnw
3.158
3.356
3.800
3.837
3.857
3.223
4.012
4.221
4.283
4.300
4.300
4.367
4.373
4.374
4.378
4.208
4.800
4.858
4.872
4.534
4.571
4.720
4.739
5.300
4.991
4.998
5.006
5.029
5.037
5.040
4.973
5.200
4.922
5.084
5.357
5.460
5.494
5.515
5.700
5.287
5.539
5.539
5.920
FCV
loEiXv (wtnol/a octanol)
3.105
3.299
3.736
3.772
3.792
3.168
3.944
' 4.150
4.210
4.227
4.227
4.293
4.299
4.300
4.304
4.137
4.719
4.776
4.789
4.457
4.494
4.640
4.659
5.210
4.906
4.913
4.921
4.944
4.952
4.955
4.889
5.112
4.839
4.998
5.266
5.367
5.401
5.422
5.603
5,197
5.445
5.445
5.820
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
PAH specific
FCV
(wmol/D
2.322
1.509
0.5744
0.5300
0.5074
2.016
0.3622
0.2298
0.2008
0.1935
0.1935
0.1673
0.1651
0.1647
0,1633
0.2364
0.06520
0.05747
0.05575 .
0.1163
0.1073
0.07760
0.07445
0.02197
0.04303
0.04238
0.04165
0.03961
0.03893
0.03868
0.04475
0.02731
0.05000
0.03515
0.0.1940
0.01551
0.01440
0.01376
0.009199
0.02260
0.01306
0.01306
0.005700
PAH specific
FCV
(UE/L)
274.5
193.5
81.69
75.37 '
72.16 i
306.9
55.85
35.91
31.37
30.24
30.24
26.13
25.79
25.74
25.52
39.30
11.10
9.785
9.488
20.73
19.13
13.99
13.42
4.048
8.273
. 8.148
8.007
7.616
7.485
7.436
8.693
5.305
10.11
7.109
4.003
3.199
2.971
2.838
1.916
4.887'
2.824
2.824
1.256
^•OC.CAW.PCVK
(tt£/£OC)
349
385
444
446
447
452
491
507
509
510
510
513
513
513
514
538
581
584
584
594
596
611
612
657
667
667
668
669
670
670
673
686
697
TOJ
739
746
748
749
769
770
787
787
829
C T
cOC,PiU«,M4rt
(we/eoc)
127200
61700
.
165700
154800
24000
33400
142500
129900
.
192300
157100
33800
49900
62400
26000
.
.
129300
1300
34300
.
49700
*
2420
.
21775
-
24100
.
-
.
9090
23870
•
-
14071
•
-
.
558
12500
-
-------
Table 3-3. Results of approximate randomization (AR) test for the equality of the freshwater and
saltwater FAV distributions at a Kow of 1.0 and AR test for the equality of benthic and
combined benthic and water column FAVs for freshwater and saltwater distributions.
Comparison
Fresh vs Salt
Freshwater: Benthic vs WQCD
Habitat or Water Type*
Fresh (20)
WQC (49)
Salt (29)
Benthic (33)
AR Statistic6
5.746.
0.862
*
Probabilityc
93.5
82.8
A Values in parantheses are the number of GMAVS at a KQV of 1.0 used in the comparison.
BAR statistic = FAV difference between original compared groups.
"••Probability that the theoretical AR statistic <. the observed AR statistic given that all samples came
from the same population.
DCombined Freshwater and Saltwater.
-------
Table 3-4. Coc.pAHi.Fcv/ concentrations at a /fow of 1.0 and properties required for their derivatipnA.
PAH"
indan
naphthalene
Cl-naphthalenes .
1 -methylnaphthalene
2-nethyInaphthalene
act.naphthylene
acenaphthene
1 -ethy Inaphlhalene
2-ethylnaphthalehe
C2-naphthalenes
1 ,4-tvimethylnaphthalene
1 ,3-dimethylnaphthalene
2 ,6-dimethytnaphthalene
2,3-dimethylnaphthalcne
1 ,5-diraethylnaphthalene
fiuorene
C3-naphthalcnes
2,3,5-trimethylnaphthalene
1 ,4,5-trimethylnaphthalene
anthracene
phenanthrene
Cl-fiuorenes
1 -methyl fluorene
C4-naphthaJenes
2-methylanthracene
1-methylanthracene
9-methyIanthracene
2-methylphenanthrene
1-methylphenanthrene
Cl-phenanthrene/anthracenes
9-ethylfluorene
C2-fiuorenes
pyrene
fluoranthene
2-ethylanthracene
C2-phenanthrene/anthraccnes
9 , 10-dimethylamhracene
3 ,6-i)imeihytphenamhrene
C3-fluorenes
C 1 -pyrenc/fluoranthones
2,3-benzofluorene
benzo(a)fluorene
C'3-phenanthrene/anthracenes
CAS*0
496117
91203
-
90120
91576
208968
83329
1127760
939275
-
571584
575417
581420
581408
571619
86737
-
2245387
213411
120127
85018
•
1730376
•
613127
610480
779022
2531842
832699
-
2294828
-
129000
206440
52251715
-
781431
1576676
-
-
243174
238843
-
Molecular
Weight
(HE/ymol)
118.18
128.17
142.20
142.20
142.20
152.2
154.21
156.23
156.23
156.23
156.23
156.23
156.23
156.23
156.23
166.22
170.25
170.26
170.2
178.12
178.23
180.25
180.25
184.28
192.26
192.26
192.26
192.26
192.26
192.2
-------
PAH"
riaphthacene
benz(a)an(hraccne
chrysene
iriphenylene
C2-pyrene/fluoranthenes
C4-phenanthrenes/ anthracenes
Cl-benzanthracene/chrysenes
C3 -pyrene/fluoranthenes
benzo(a)pyrene
perylene
benzo(e)pyrene
benzo(b)nuoranth«ne
benzoG)fluoramhenc
benzo(k}fluoranthene
C2-benzanthracene/chrysenes
9, 10-dirnethylbenz(a)anthracene
7, l2-dimethylbenz(a)anthracene
7-methylbenzo(a)pyrcne
benzo(ghi)perylcne
C3-benzanthracene/chrysenes
indeno(l ,2,3-cd)pyrene
djbenz(a,h)anthracene
dibenz(a,j)anthracene
dibenz(a,c)anthracene
C4-bertzanthracene/chrysenes
C 1 -dibenz(a,h)anthracenes
coronene
C2-dibenz(a,h)anthracenes
C3-diben2(a.h)amhracenes
CAS^
92240
56553
218019
217594
-
-
-
-
50328
198550
192972
205992
205822
207089
-
56564
57976
63041770
191242
-
193395
53703
58703
215587
-
-
191071
-
-
Molecular
Weight
(uzlumol)
228.3
228.29
228.29
228.3
230.13
234.23
242.32
244.32
252.31
252.31
252.32
252.32
252.32
252.32
256.23
256.35
256.35
266.35
276.23
270.36
.276.23
278.35
278.35
278.35
284.38
292.37
300.36
306.39
320.41
Mackay
Solid
Solubility0
(utlU
0.6000
11.00
2.000
43.00
??
??
??
??
3.810
0.4012
4.012
1.501
2.500
0.7999
??
43.5
49.99
??
0.2600
??
??
0.6012
12.00
1.601
??
??
0.1400
??
??
SPARCE
lOC.rJC/Mn/
5.633
,5.673
5.713
5.752
5.800
6.320
6.140
6.284
6.107
6.135
6.135
6.266
6.291
6.291
6.429
6.567
6.575
6.537
6.507
6.940
6.722
6.713
6.713
6.780
7.360
7.113
6.885
7.513
7.913
FCV
Ioe,ftfcv- (umol/a octanol)
5.538
5.577
5.616
5.654
5.702
6.213
6.036
6.177
6.003
6.031
6.031
6.160
6.184
6.184
6.320
6.456
6.464
6.426
6.397
6.822
6.608
6.599
6.599
6.665
7.235
6.992
6.768
7.386
7.779
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
PAH specific
FCV
(ttmol/L)
0.01064
0.009756
0.008943
0.008215
0.007400
0.002387
0.003531
0.002581
0.003794
0.003570
0.003570
0.002685
0.002542
0.002542
0.001883
0.001395
0.001370
0.001489
0.001589
0.0006194
0.0009953
0.001015
0.001015
0.0008773
0.0002483
0.0004251
0.0006981
0.0001780
0.00007455
PAH specific
FCV
(ue/D
2.430
2.227
2.042
1.875
1.703
0.5594
0.8557
0.6307
0.9573
0.9008
0.9008
0.6774
0.6415
0.6415
0.4827
0.3575
0.3513
0.3965
0.4391
0.1675
0.2750
0.2825
0.2825
0.2442
0.07062
0.1243
0.2097
0.05454
0.02389
Coc.rAHi.rcvi
(US/ROC)
838 ,
841
844
846
857
913
929
949
965
967
967
979
981.
981
1008
1021
1021
1058
1095
1112
1115
1123
1123
1129
1214
1221
1230
1325
1435
r r
**OC.PAlll,M COC.PAHI.MU!' tnen lllis value rep'aces COCJAHI.PCVI in all calculations.
'.''.'Solubility is unknown
-------
Table 4-1. ESGs for PAH mixtures: Example calculations for three sediments.
PAH1
acenaphthene
a' '.enaphthylene
anthracene
bcnz(a)anthracene
beczo(a)pyrene
benzo(e)pyrene
benzo(b)fluoranthene
benzo(k)fluoranthcne
benzo(g,h, i)perylene
chrysene
dibenzo(a,h)anthracene
flouranthene
fluorene
indeno(l ,2,3-cd)pyrene
naphthalene
perylene
phenamhrene
pyrene
Cl chrysenes
Cl fluoramhenes .
Cl flourenes
Cl naphthalenes
Q)C, PAHI,
FCVI
(^g/goc)"
491
452
594
841
965
967
979
981
1095
844
1123
707
538
1115
385
967
596
697
929
770
611
444
Ox. PAHI,
M»l
O'g/goc)
33400
24000
1300
4153
3840
4300
2169
1220
648
826
2389
23870
26000
-
61700
431
34300
9090
-
-
-
-
croo
Cone.
0*g/g dry wt.)
0.000
0.0348
0.628
0.0709
0.164
0.139
0.139
0.157
0.0806
0.0722
0.0894
0.139
0.171
Sediment A
0.81%; /«.-
Coc '
fcg/goc)
0.00
4.29
77.6
8.75
20.3
.17.2
17.2
19.4
9.96
8.91
n.o
17.1
21.1
0.0081)
ESGTUFCV|
0.00000
0.00950
0.1306
0.0104
0.0210
0.0175
0.0175
0.0235
0.0141
0.0166
0.0287
0.0287
0.0303
(TOOO
Cone.
(wg/g dry wt.)
0.0401
0.0165
0.0507
0.2011
0.1817
0.1673
0.1708
0.1962
0.1504
0.2574
0.0423
0.3244
0.3702
0.1473
0.2703
0.3511
0.5679
0.4080
0.2987
0.3824
0.9362
1.2084
Sediment B
.886%; /oc-
. Coc
(Mg/goc)
4.53
1.86
5.72
22.69
20.51
18.89
19.28
22.15
16.97
29.05
4.77
36.62
41.78
16.63
30.51
39.63
64.09
46.05
33.72
43,16
105.67
136.39
0.00886)
ESGTUFCV1
(TOC-
Cone.
0/g/g dry wt.
0.00922 0.806
0.00412 2.040
0.00962 3.695
0.02698 8.293
0.02125 10.97
0.01953 8.920
0.01969 18.14
0.02258 5.500
0.02619 5.583
. 0.03518 9.197
0.00425 2.499
0.05180
0.07766
0.01491
0.07925
0.09194
0.1075
0.06606
0.03629
0.05605
0.17294
2.519
1.387
10.80
2.193
28.23
4.208
20.14
5.240
11.73
1.030
0.30719 1.37
Sediment C
=6.384%; /oc=
Coc
) (Mg/goc)
12.6
32.0
57.9
129.9
171.8
139.7
284.1
86.2
., 87.5
144.1
39.1
39.5
21.7
169.2
34.4
442.2
65.9
315.5
• 3**
82.1
183.7
16.1
21.9
0.06384)
ESGTUFCVI
0.0257
0.0707
0.0974
0.1545
0.1781
0.1445 •
0.2902
0.0878
0.1350
0.1744
0.0349
0.0558
0.0404
0.1517
0.0892
1.0259
0.1106
0.4526
0.0884
0.2386
0.0264
0.0493
-------
PAH"
tuptuhacene
benz(a)anthraccne
chrysen«
iriphenylene
C2-pyrene/fluoranthenes
C4-phenanthrenes/anthracenes
Cl -benzanthracene/chrysenes
C3 -pyrene/fluoranthenes
benzo(a)pyrene
perylene
benzo(e)pyrene
benzo(b)fluoranthene
benzo(j)fluoranthene
benzo(k)fluoranthene
C2- benzanthracene/chrysenes
9, 10"dirnethylben2(a)antnracene
7, 12-dimethylbenz(a)anthracene
7-methyIbenzo(a)pyrcne
benzo(ghi)perylcne
C3-benzanthracene/chrysenes
indeno(l,2,3-cd)pyrene
dibenz(a,h)anthracene
d ibenz(a ,j)amhracene
dibenz(a,c)anthracene
C4-bertzanthracene/chrysenes
C 1 -dibenz(a,h)anthracenes
coronene
C2-dibenz(a,h)anthracenes
C3-dibenz(aYh)anthracenes
CAS^
92240
56553
218019
217594
-
-
-
-
50328
198550
192972
205992
205822
207089
-
56564
57976
63041770
191242
-
193395
53703
58703
215587
-
-
191071
-
-
Molecular
Weight
(uz/umol)
228.3
228.29
228.29
228.3
230.13
234.23
242.32
244.32
252.31
252.31
252.32
252.32
252.32
252.32
256.23
256.35
256.35
266.35
276.23
270.36
.276.23
278.35
278.35
278.35
284.38
292.37
300.36
306.39
320.41
Mackay
Solid
Solubility"
(uzlU
0.6000
11.00
2.000
43.00
??
??
??
??
3.810
0.4012
4.012
1.501
2.500
0.7999
??
43.5
49.99
. ??
0.2600
??
??
0.6012
12.00
1.601
??
??
0.1400
??
??
SPARC6
loe.JfrMi,
5.633
.5.673
5.713
5.752
5.800
6.320
6.140
6.284
6.107
6.135
6.135
6.266
6.291
6.291
6.429
6.567
6.575
6.537
6.507
6.940
6.722
6.713
6.713
6.780
7.360
7.113
6.885
7.513
7.913
FCV
foe.jr™- (amol/g octanol)
5.538
5.577
5.616
5.654
5.702
6.213
6.036
6.177
6.003
6.031
6,031
6.160
6.184
6.184
6.320
6.456
6.464
6.426
6.397
6.822
6.608
6.599
6.599
6.665
7.235
6.992
6.768
7.386
7.779
2.240
2,240
2.240
2,240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
2.240
PAH specific
FCV
(Mtnol/L)
0.01064
0.009756
0.008943
0.008215
0.007400
0.002387
0.003531
0.002581
0.003794
0.003570
0.003570
0.002685
0.002542
0.002542
0.001883
0.001395
0.001370
0.001489
0.001589
0.0006194
0.0009953
0.001015
0.001015
0.0008773
0.0002483
0.0004251
0.0006981
0.0001780
0.00007455
PAH specific
FCV
(uc/L)
2.430
2.227
2.042
1.875
1.703
0.5594
0.8557
0.6307
0.9573
0.9008
0.9008
0.6774
0.6415
0.6415
0.4827
0.3575
0.3513
0.3965
0.4391
0.1675
0.2750
0.2825
0.2825
0.2442
0.07062
0.1243
0.2097
0.05454
0.02389
QX7.MHI.PCW
tee/eoc)
838 „
841
844
846
857
913
929
949
965
967
967
979
981
981
1008
1021
1021
1058
1095
1112
1115
1123
1123
1129
1214
1221
1230
1325
1435
r F
^OC.ftUW.MMI
(UB/EOC)
207
4153
826
19400
-
-
-
.
3840
431
4300
2169
3820
1220
.
124200
145300
.
648
.
.
2389
47680
7400
„
.
821
.
-
"Four significant figures are used even when fewer are appropriate for the parameter to limit the effects of rounding error when calculating SESGTUFCV which lias two significant figures.
"PAHs in bold are the 34 that constitute the minimum required to constitute "total PAH" for use in this PAH mixture ESG without correction for unmeasured PAHs.
cFor C#-PAHs, a CAS is not available.
"Mackay et al., 1992. Illustrated handbook of physical chemical properties and Environmental Fate for organic chemicals. Volume 2.
11 For C#-PAHs, reported logloKow values are the average log(0KQW values of several possible structural isomers.
' QcpAifi.pcvi based on solubility; if COCPAHLFCVI 's > CoctWMnn tnen 'h'8 va'ue replaces COC.PAHI.I'CVI in all calculations.
'.''.'Solubility is unknown
-------
Table 4-1. ESGs for PAH mixtures: Example calculations for three sediments.
PAH1
acenaphthene
a- :enaphthylene
anthracene
bcnz(a)anthracene
benzo(a)pyrene
bcnzo(e)pyrene
benzo(b)fluoranthene
benzo(k)fluoranthene
benzo(g,h,i)perylene
clirysene
dibenzo(a,h)anthracene
flouranthene
fluorene
indeno(l ,2,3-cd)pyrene
naphthalene
perylene
phenanthrene
pyrene
Cl chrysenes
Cl nuoramhenes .
Cl flourenes
Cl naphthalenes
Q)C. PAHI,
FCVl t
(Mg/goc)"
491
452
594
841
965
967
979
981
1095
844
1123
707
538
1115
385
967
596
697
929
770
611
444
Mwl
33400
24000
1300
4153
3840
4300
2169
1220
648
826
2389
23870
26000
•
61700
431
34300
9090
-
-
-
-
Sediment A
(TOC=0.81%;/OC»
Cone. CQC
(Mg/g dry wt.) fcg/goc)
0.000
0.034S
0.628
0.0709
0.164
0.139
0.139
0.157
0.0806
0.0722
0.0894
0.139
0.171
0.00
4.29
77.6
8.75
20.3
.17.2
17.2
19.4
9.96
8.91
11.0
17.1
21.1
0.0081)
ESGTUFCVI
0.00000
0.00950
0.1306
0.0104
0.0210
0.0175
0.0175
0.0235
'
0.0141
0.0166
0.0287
0.0287
0.0303
(TOC-0
Cone.
(Mg/g dry wt.)
0.0401
0.0165
0.0507
0.2011
0.1817
0.1673
0.1708
0.1962
0.1504
0.2574
0.0423
0.3244
0.3702
0.1473
0.2703
0.3511
0.5679
0.4080
0.2987
0.3824
0.9362
1.2084
Sediment B
Ox:
(Mg/goc)
4.53
1.86
5.72
22.69
20.51
18.89
19.28
22.15
16.97
29.05
4.77
36.62
41.78
16.63
30.51
39.63
64.09
46.05
33.72
43.16
105.67
136.39
).00886)
ESGTUFCV1
0.00922
0.00412
0.00962
0.02698
0.02125
0.01953
0.01969
0.02258
0.02619
. 0^03518
0.00425
0.05180
0.07766
0.01491
0.07925
0.09194
0.1075
0.06606
0.03629
0.05605
0.17294
0.30719
(TOC=
Cone.
0/g/g dry wt.)
0.806
2.040
3.695
8.293
10.97
8.920
18.14
5.500
5.583
9.197
2.499
2.519
1.387
10.80
2.193
28.23
4.208
20.14
5.240
11.73
1.030
1.37
Sediment C
6.384%; /oc-t
Coc
12.6
32.0
57.9
129.9
171.8
139.7
284.1
86.2
.. 87.5
144.1
39.1
39.5
21.7
169.2
34.4
442.2
65.9
315.5
- a**
82.1
183.7
16,1
21.9
106384)
ESGTUFCVi
0.0257
0.0707
0.0974
0.1545
0.1781
0.1445 •
0.2902
0.0878
0.1350
0.1744
0.0349
0.0558
0.0404
0.1517
0.0892
1.0259
0.1106
0.4526
0.0884
0.2386
0.0264
0.0493
-------
Cl phenanthrenes
C2 chrysenes
C2 flourenes
C2 naphthalenes
C2 phenanthrenes
C3 chrysenes
C3 flourenes
C3 naphthalenes
C3 phenanthrenes
C4 chrysenes
C4 naphthalenes
C4 phenanthrenes
670
1008
686
510
746
1112
769
581
829
1214
657
913
Sum total of ESGTUprvi
'
SBSGTUrv n -0.348
0.9267
0.2242
1.2384
3.2691
1.0645
0.0279
1.2664
5.1079
0.8100
0.1196
3.3088
0.5644
104.6 •
25.30
139.77
368.98
120.15
3.15
142.94
576.51
91.43
13.5
373.46
63.71
SESGTU
0.15611
0.02510
0.20375
0.72348
0,16106
0.00283
0.18587
0.99227
0.11028
0.01112
0.56843
0.06978
FTV.TOT " 4.470
4.559
4.753
1.928
1.448
4.789
0.398
3.419
1.979
5.378
1.581
2.009
4.674
71.4
74.5
30.2
22.7
75.0
6.2
53.6
31.0
84.2
24.8
31.5
73.2
SESGTU
0.1066
0.0739
0.0440
0.0445
0.1006
0.0056
0.0696
0.0533
0.1016
0.0204
0.0479
0.0802
FfYTOT - 4.470
a PAHs and corresponding COC.PAHI.FCV/ ancl Qx: .PAHI x«i values are from Table 3-4 (bold).
b COC,PAH/,FCV< based on solubility, if CQC^H^CV, exceeds the COC.PMM.MMI 0-e" benzo(g,h,i)perylene, chrysene, and perylene) then
's used to calculate ESGTU
FCV(
-------
Table 5-1. Water-only and spiked-sediment LC50 values used to test the applicability of narcosis and equilibrium partitioning theories to the derivation of
ESGsforPAHs.
Test Species
Freshwater
Diporeia sp.
Hyalella azteca
Hy ilella azieca
Hyalella azteca
Hyalella azteca
Chironomus tentans
Chironomus tentans
Chironomus tentans
Saltwater
Eohaustorius estuarius
Eohaustorius estuarius
Eohaustorius estuarius
Leptochelrus plurnulosus
Leptocheirus plurnulosus
Leptocheirus plurnulosus
Eoliaustorius estuarius
Eohaustorius estuarius
Eohaustorius estuarius
Leptocheirus plumulosus
Leptocheirus plumulosus
Leptocheirus plumulosus
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Chemical
Fluoranthene
Fluoranthene
Fluoranthene
Fluoranthene
Fluoranthene
Fluoranthene
Fluoranthene
Fluoranthene
Acenaphthene
Acenaphthene
Acenaphthene
Acenaphthene
Acenaphthene
Acenaphthene
Phenanthrene
Phenanthrene
Phenanthrene
Phenanthrene
Phenanthrene
Phenanthrene
2,6-dimethylnaphthlene
2,3,5-trimethylnaphthlene
1 -methyl fluorene
2-methylphenanthrene
9-methylanthracene
Acenaphthene
Acenaphthene
Naphthalene
Phenanihrene
Phenanthrene
Pyrene
Pyrene
Pyrene
Fluoranthene
Fluoranthene
Method*
FT.M/10
FT.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
FT.M/10
FT.M/10
FT.M/10
FT.M/10
FT.M/10
FT.M/10
FT.M/10
FT.M/10
FT.M/10
FT.M/10
FT.M/10
FT.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
Ratio:
Water-only Interstitial Water Interstitial Water .
LC50 • LC50 LC50/Water-only
(Wg/U («e/U LC50
>194
130.7
44.9
44.9
44.9
31.9
31.9
31.9
374
374
374
678
678
678
• 131
131
131
185
185
185
-
-
•
•
-
-
-
-
-
-
-
-
•
13.9E
13.9E
>381.3
>75.4
45.9
236.5
97.6
91.2
251
75.7
800
609
542
• > 1,720
1410
1490
138
139
146.
387
306
360
200
153
44
70
32
-
-
10440
-
-
28.1
-
-
-
-
-
> 0.58
1.02C
5.27C
2.17C
2.86°
7.87C
2.37C
2.14
1.63
1.45
> 2.54
2.08
2.20
1.05
1.06
1.11
2.09
1.65
1.95 .
-
-
•
-
-
•
-
-
-
-
-
'
-
-
-
Organic Carbon-Normalized LC50 (wE/e,vO
Observed
-
-
500
1480
1250
1587
1740
682
4330
1920
1630
> 23,500
7730 •
11200
4050
3920
3820
8200
6490
8200
8120
3190
1950
2270
6840
2110
2310
31000
3080
2220
1610
1220
2810
2320
3310
Predicted8
.
.
4490
4490
4490
3190
3190
3190
2152
2152
2152
3900
3900
3900
3778
3778
3778
5335
5335
5335
-
-
-
-
-
-
-
.
-
-
-
.
.
1390
1390
LC50 Ratio
Obs/Pred
.
1
0.1 lc
0.33C
0.28C
0.50C
0.55C
0.21C
2.01
0.89
0.76
> 6.02
1.98
2.87
. 1.07
1.04
1.01
1.54
1.22
1.54
-
-
'
.
-
.
.
-
.
.
-
.
.
1.66
2.38
Reference
Landrum, 1995
Landrum, 1995
Suedeletal., 1993
Suedel et al., 1993
Suedeletal., 1993
Suedeletal., 1993
Suedeletal.. 1993
Suedeletal., 1993
Swartz, 1991a
Swartz, 1991a
Swartz, 1991a
Swartz, 1991a
Swartz, 199 la
Swartz, I991a
Swartz, 199 la
Swartz, 199 la
Swartz, 199 la
Swartz, 1991a
Swartz, 1991a
Swartz, 1991a
Ozretichetal.,2000a
Ozretichetal., 2000a
Ozretichetal.,2000a
Ozretichetal.,2000a
Ozretichetal.,2000a
Swartz et al., 1997
Swartz etal., 1997
OzreticKet al., 2000a
Swartz etal., 1997
Swartz etal., 1997
Ozretichetal., 2000a
Swartz et «!., 1997
Swartz et al., 1997
Swartz etal., 1997
Swartz et al., 1997
-------
Cl phenanthrenes
C2 chrysenes
C2 flourenes
C2 naphthalenes
C2 phenanthrenes
C3 chrysenes
C3 flourenes
C3 naphthalenes
C3 phenanthrenes
C4 chrysenes
C4 naphthalenes
C4 phenanthrenes
670
1008
686
510
746
1112
769
581
829
1214
657
913
Sum total of ESGTUFrVi
I
1
SESGTU.rrv „ - 0.348
0.9267
0.2242
1.2384
3.2691
1.0645
0.0279
1.2664
5.1079
0.8100
0.1196
3.3088
0.5644
104.6
25.30
139.77
368.98
120.15
3.15
142.94
576.51
91.43
13.5
373.46
63.71
SESGTU
1
0.15611 j
0.02510 1
0.20375
0.72348
0.16106
0.00283
0.18587
0.99227
0.11028
0.01112
0.56843
0.06978
prv.Trrr - 4.470
4.559
4.753
1.928
1.448
4.789
0.398
t
3.419
1.979
5.378
1.581
2.009
4.674
71.4
74.5
30.2
22.7
75.0
6.2
53.6
31.0
84.2
24.8
31.5
73.2
SESGTU
0.1066
0.07.39
0.0440
0.0445
0.1006
0.0056
0.0696
0.0533
0.1016
0.0204
0.0479
0.0802
FCVTOT = 4.470
a PAHs and corresponding CQC^HUW and COC.PAH/JM«I values are from Table 3-4 (bold).
b Cf* based on solubility, \f Co^ruufoti exceeds the Coc^,,,^,,, (i.e., benzo(g,h(i)perylene, chrysene, and perylene) then COC,PAH/.M«I >1S used to calculate ESGTUFCV|
-------
Table 5-1. Water-only and spiked-sediment LC50 values used to test the applicability of narcosis and equilibrium partitioning theories to the derivation of
ESGs for PAHs.
Test Species
Freshwater
Diporeia sp.
Hyalella azteca
Hy ilella aaeca
Hyalella azteca
Hyalella azteca
Chironomus tertians
Chironomus tentans
Chironomus tentans
Saltwater
Eohaustorius estuarius
Eohauslorius estuarius
Eohaustorius estuarius
Leptocheirus plumulosus
Leptocheirus plumulosus
Leptocheirus plumulosus
Eohaustorius estuarius
Eohaustorius estuarius
Eohaustorius estuarius
Leptocheirus plumulosus
Leptocheirus plumulosus
Leptocheirus plumulosus
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Chemical
Fluoranthene
Fluoramhene
Fluoranthene
Fluoranthene
Fluoranthene
Fluoranthene
Fluoranthene
Fluoranthene
Acenaphthene
Acenaphthcne
Acenaphthene
Acenaphthene
Acenaphthene
Acenaphthene
Phenanthrene
Phenanthrene
Phenanthrene
Phenanthrene
Phenanthrene
Phenanthrene
2,6-dimethylnaphthlene
2,3,5-trimethyInaphthlene
1 -methyl fluorene
2-methylphenanthrene
9-methylanthracene
Acenaphthene
Acenaphthene
Naphthalene
Phenanthrene
Phenanthrene
Pyrene
Pyrene
Pyrene
Fluoranthene
Fluoranthene
Water-only
LC50
Method* (MB/U
FT.M/10
FT.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
FT.M/10
FT,M/10
FT.M/10
FT.M/10
FT.M/10
FT.M/10
FT.M/10
FT.M/10
FT,M/10
FT,M/10
FT.M/10
FT.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
>194
130.7
44.9
44.9
44.9
31.9
31.9
31.9
374
374
374
678
678
678
• 131
131
131
185
185
185
•
•
•
•
-
•
-
-
•
-
-
-
-
13.9H
13.9E
Interstitial Wate
• LC50
(WE/U
>381.3
>75.4
45.9
236.5
97.6
91.2
251
75.7
800
609
542
> 1,720
1410
1490
138
139
146.
387
306
360
200
153
44
70
32
-
-
10440
-
-
28.1
-
•
-
-
Ratio:
r Interstitial Water .
LC50/Water-only
LC50
-
> 0.58
1.02C
5.27C
2.17C
2.86C
7.87°
2.37C
2.14
1.63
1.45
> 2.54
2.08
2.20
1.05
1.06
1.11
2.09
1.65
1.95
•
-
-
-
-
•
-
-
-
-
-
-
-
-
Organic Carbon-Normalized LC50 (ue/v^
Observed
-
.
500
1480
1250
1587
1740
682
4330
1920
1630
> 23,500
7730 •
11200
4050
3920
3820
8200
6490
8200
8120
3190
1950
2270
6840
2110
2310
31000
3080
2220
1610
1220
2810
2320
3310
Predicted8
.
.
4490
4490
4490
3190
3190
3190
2152
2152
2152
3900
3900
3900
3778
3778
3778
5335
5335
5335
-
-
-
-
-
-
-
.
-
-
-
.
.
1390
1390
LC50 Ratio
Obs/Pred
.
»
O.llc '
0.33C
0.28°
0.50C
0.55C
0.21C
2.01
0.89
0.76
> 6.02
1.98
2.87
. 1.07
1.04
L01
1.54
1.22
1.54
.
.
'
.
.
.
.
-
.
.
-
.
.
1.66
2.38
Reference
Landrum, 1995
Landrum, 1995
Suedeletal., 1993
Suedel et al., 1993
Suedeletal., 1993
Suedeletal., 1993
Suedeletal., 1993
Suedel et al., 1993
Swartz, 199 la
Swartz, 1991a
Swartz, 1991a
Swartz, 1991a
Swartz, 199 la
Swartz, 1991a
Swartz, 1991a
Swartz, 1991a
Swartz, 199 la
Swartz, 199 la
Swartz, 199 la
Swartz, 1991a
Ozretichetal., 2000a
Ozretichetal., 2000a
Ozretichetal., 2000a
Ozretichetal., 2000a
Ozreticheta!., 2000a
Swartz etal., 1997
Swartz etal., 1997
OzreticKet al,, 2000a
Swartz etal., 1997
Swartz etal., 1997
Ozretichetal., 2000a
Swartz etal., 1997
Swartz etal., 1997
Swartz etal., 1997
Swartz et al., 1997
-------
Rhepoxynius abronius
Itiiepoxynius abronius
Rliepoxynius abronius
R/iepoxynius abronius
Rliepoxynius abronius
Rliepoxynius abronius
Rhepoxynius abronius
Rliegoxyjiius abronius
Fluoranthene
Fluoranihene
Ftuoranthene
Fluoranthene
Fluoranthene
Fluoranthene
Fluoranthene
Fluoranthene
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
13. 9E 22.7
13.96 29.4
13. 9E 24.2
13.9E > 315
13.9E 14.1
13. 9e ' 26.6
13.9H 19.2
13.9E 9.38
Mean LC50 ratio ««
1.63
2.12
1.74
> 22.66°
1.01
1.91
1.38
0.67
1.60
1890 • 1390
2100 1390
2230 1390
. >4360 1390
4410 1390
3080 1390
3150 1390
2790 1390
Mean LC50 ratio «
1.36
1.51
1.60
4.04°
3.17
2.22
2.26
2.01
1.91
Swartzetal., 1990
Swartzet al,, 1990
Swartz et al-, 1990
DeWitt etal., 1992
DeWitt et al., 1992
DeWittetal., 1992
DeWitt etal., 1992
DeWitt eta!., 1992
Test conditions for water-only toxicity tests: S = static, FT » flow-through, M » measured, 10 •* 10-d duration.
"Prt dieted LC50 (Mg/goc) * water-only LC50
-------
['able 5-2. Percent mortality of benthic invertebrates in relation to the SESGTUFCV values of mixtures of polycyclic aromatic hydrocarbons spiked into
sediment.
Species*
Diporeia sp.
Diporeia sp.
Diporeia sp.
Dipnreia sp.
R. c.bronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
A. abdila
A. abdila
A. abdila
A. bahia
A. bahia
A. bahia
SESGTUFCV
PAHATow <5.5
0.01
0.21
0.49
1.37
10.32
5.80
5.12
3.25
2.30
1.80
1.42
2.77
4.91
5.88
5.71
2.71
2.06
0.63
1.91
0.58
1.55
0.90
5.41
0
5.41
5.41
0
5.41
SESGTUFCV
PAH /Tow >5.5
0.02
0.36
0.60
1.71
0
0
0
0
0
0
0
0
5.02
0
0
2.23
0.79
1.57
25.89
8.03
8.03
3.40
0.64
2.58
3.22
0.64
2.58
3.22
SESGTUFCV
All PAHs
0.03
0.57
1.10
3.08
10.3
5.80
5.12
3.25
2.50
1.80
1.42
2.77
9.93
5.88
5.71
4.94
2.84
2.20
27.8
8.61
9.58
4.30
6.05
2.58
8.63
6.05
2.58
8.63
Percent
Mortality
3
10
0
12
100
38
8
11
4
2
3
5
3
5
2
3
2
1
4
5
9
0
7
7
10
3
7
7
PAH Mixture8
fluor, phen, anthr, flu, pyr, chry, b(b)flu, b(e)pyr, b(a)pyr, pery, b(ghi)pery
fluor, phen, anthr, flu, pyr, chry, b(b)flu, b(e)pyr, b(a)pyr, pery, b(ghi)pery
fluor, pheu, anthr, flu, pyr, chry, b(b)flu, b(e)pyr, b(a)pyr, pery, b(ghi)pery
fluor, phen, anthr, flu, pyr, chry, b(b)flu, b(e)pyr, b(a)pyr, pery, b(ghi)pery
ace; phen; flu; pyr
ace; phen; flu; pyr
ace; phen; flu; pyr
ace; phen; flu; pyr
ace; phen; flu; pyr
ace; phen; flu; pyr
ace; phetv, flu; pyr
anthr; flu
b(a)anthr; flu
2-methylanthr; flu
9,10-dimethyIanth; flu
b(b)flu; flu
chr; flu
3,6-dimethylphen; flu
anthr; b(a)anthr; 2-methylanthr; b(b)fiu; chr; 3,6-dimethylphen
anthr; b(a)anthr; 2-methylanthr; b(b)flu; chr; 3,6-dimethylphen
anthr; b(a)anthr; 2-methylanthr; b(b)flu; chry; 3,6-dimethylphen; flu
anthr; b(a)anthr; 2-methylanthr; b(b)flu; chry; 3,6-dimethylphen; flu
9,10-dimethylanthr; chry
b(a)pyr; cor
9,10-dimethylanthr; chry; b(a)pyr; cor
9,10-dimethylanthr; chry
b(a)pyr; cor
9.10-dimethvlanthr: chrv: b(a)ovr: cor
Reference
Landrumetal., 1991
Landrumeta!., 1991
Landrumetal., 1991
Landrumetal., 1991
Swartzetat., 1997
Swartzet al., 1997
Swartz et al., 1997
Swartzetal., 1997
Swartz etal., 1997
Swartzetal., 1997
Swartzetal., 1997
Boeseetal., 1999
Boese et al., 1999
Boese et al., 1999
Boeseetal., 1999
Boeseetal., 1999
Boese eta!., 1999
Boeseetal., 1999
Boeseetal., 1999
Boeseetal., 1999
Boeseetal., 1999
Boeseetal., 1999
Burgess etal., 2000
Burgess etal., 2000
Burgess etai., 2000
Burgess etal., 2000
Burgess etal., 2000
Bureesset al., 2000
'Test Species: amphipods: Diporeia sp., Rhepoxynlus abronius, Ampelisca abdita; mysids: Americamysis bahia
"PAH Code: ace - acenaphthene; anthr - anthracene; b(a)anthr - benz(a)anthracene; b(a)pry • benzo(a)pyrene; b(ghi)pery - benzo(ghi)perylene; b(b)flu - benzo(b)fluoranthene; chry - chrysene; cor
• coronene; 9,10-dimethylanth - 9,10-dimethylanthracene; 3,6-dimethylphen - 3,6dimethylphenanthrene; flu • fluoranthene; fluor - fluorene; 2-methylanthr - 2-methytanthracene; pery - perylene;
phen - phenanthrene; pyr - pyrene.
-------
fOtepoxynius abronius
Kliepoxynius abronius
Khepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Rhepoxynius abronius
Rhej>oxy_nius abronius
Fluoramhene
Fluoranthene
Fluoranthene
Fluoranthene
Fluoranthene
Fluoranthene
Fluoranthene
Fluoranthene
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
S.M/10
13.9E
13.9E
13.9E
13.9E
13.9E
13.9E
13.9e
13.9E
22.7
29.4
24.2
> 315
14.1
• 26.6
19.2
9.38
Mean LC50 ratio «
1.63
2.12
1.74
> 22.66°
1.01
1.91
1.38
0.67
1.60
1890
2100
2230
>4360
4410
3080
3150
2790
Mean
•1390
1390
1390
1390
1390
1390
1390
1390
LC50 ratio «=
1.36
1.51
1.60
4.04°
3.17
2.22
2.26
2.01
1.91
Swartzet al,,
Swartzet al,,
Swartzet al.,
DeWittetal.,
DeWittetal.,
DeWittetal.,
DeWittetal.,
DeWittetal.,
1990
1990
1990
1992
1992
1992
1992
1992
Tent conditions for water-only toxicity tests: S = static, FT « flow-through, M » measured, 10 «• 10-d duration.
"Prt dieted LC50 fcg/goc) - water-only LC50 (ng/L) x Kx (L/kgoc) x 1 kgoc/lOOOgoc.
Sediments spiked with fluoranthene by Suedel et al. (1993) were not at equilibrium, therefore, are not included in the mean.
'Source of organic carbon was fresh plant material, not naturally aged organic matter, therefore, value was not included in the mean.
'•10-day LC50 value from Swartz (2000).
-------
Table 5-2. Percent mortality of benthic invertebrates in relation to the SESGTUFcv values of mixtures of polycyclic aromatic hydrocarbons spiked into
sediment.
Species*
Diporeia sp.
Diporeia sp.
Diporeia sp.
Diporeia sp.
R. ibronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
R. abronius
A. abdita
A. abdita
A, abdita
A. bahia
A. bahia
A. bahia
SESGTUFCv
PAHAbw <5.5
0.01
0.21
0.49
1.37
10.32
5.80
5.12
3.25
2.50
1.80
1.42
2.77
4.91
5.88
5.71
2.71
2.06
0.63
1.91
0.58
1.55
0.90
5.41
0
5.41
5.41
0
5.41
SESGTUFCV
PAH Kbw >5.5
0.02
0.36
0.60
1.71
0
0
0
0
0
0
0
0
5.02
0
0
2.23
0.79
1.57
25.89
8.03
8.03
3.40
0.64
2.58
3.22
0.64
2.58
3.22
SESGTUpcv
AH PAHs
0.03
0.57
1.10
3.08
10.3
5.80
5.12
3.25
2.50
1.80
1.42
2.77
9.93
5.88
5.71
4.94
2.84
2.20
27.8
8.61
9.58
4.30
6.05
2.58
8.63
6.05
2.58
8.63
Percent
Mortality
3
10
0
12
100
38
8
11
4
2
3
5
3
5
2
3
2
1
4
5
9
0
7
7
10
3
7
7
PAH Mixture8
fluor, phen, anthr, flu, pyr, chry, b(b)flu, b(e)pyr, b(a)pyr, pery, b(ghi)pery
fluor, phen, anthr, flu, pyr, chry, b(b)flu, b(e)pyr, b(a)pyr, pery, b(ghi)pery
fluor, pheu, anthr, flu, pyr, chry, b(b)flu, b(e)pyr, b(a)pyr, pery, b(ghi)pery
fluor, phen, anthr, flu, pyr, chry, b(b)flu, b(e)pyr, b(a)pyr, pery, b(ghi)pery
ace; phen; flu; pyr
ace; phen; flu; pyr
ace; phen; flu; pyr
ace; phen; flu; pyr
ace; phen; flu; pyr
ace; phen; flu; pyr
ace; phen; flu; pyr
anthr; flu
b(a)anthr; flu
2-methylanthr; flu
9,10-dimethyIanth; flu
b(b)flu; flu
chf ; flu
3,6-dimethylphen; flu
anthr; b(a)anthr; 2-methylanthr; b(b)flu; chr; 3,6-dimethylphen
anthr; b(a)anthr; 2-methylanthr; b(b)flu; chr; 3,6-dimethylphen
anthr; b(a)anthr; 2-methylanthr; b(b)flu; chry; 3,6-dimethylphen; flu
anthr; b(a)anthr; 2-methylanthr; b(b)flu; chry; 3,6-dimethylphen; flu
9,10-dimethylanthr; chry
b(a)pyr; cor
9,10-dimethylanthr; chry; b(a)pyr; cor
9,10-dimethylanthr; chry
b(a)pyr; cor
9,10-dimethvlanthr; chry; b(a)ovr: cor
Reference
Landrumetal., 1991
Landrum et al., 1991
Landrumetal., 1991
Landrum et al., 1991
Swartzetal., 1997
Swartzetal., 1997
Swartz et al., 1997
Swartz et al., 1997
Swartz et al., 1997
Swartz eta!., 1997
Swartz et al,, 1997
Boese et al., 1999
Boese et al., 1999
Boese et al., 1999
Boese etal., 1999
Boese et al., 1999
Boese et al., 1999
Boese etal., 1999
Boese etal., 1999
Boese et al., 1999
Boese etal., 1999
Boese etal., 1999
Burgess etal., 2000
Burgess etal., 2000
Burgess etal. ,2000
Burgess eta!., 2000
Burgess etal., 2000
Bureess et al., 2000
KTest Species: amphipods: Diporeia sp., Rhepoxynius abronius, Ampellsca abdita; mysids: Americamysis bahia
"PAH Code: ace - acenaphthene; anthr - anthracene; b(a)anthr - benz(a)anthracene; b(a)pry • benzo(a)pyrene; b(ghi)pery • benzo(ghi)perylene; b(b)flu - benzo(b)fluoranthene; chry - chrysene; cor
- coronene; 9,10-dimethylanth - 9,10-dimeihylanthracene; 3,6-dimethylphen - 3,6dlmethylphenanthrene; flu - fluoranthene; fluor - fluorene; 2-methylanthr - 2-metliylanthracene; pery - perylene;
phen • phenanthrene; pyr - pyrene.
-------
Table 5-3. Chemicals included in the high KQW PAH mixture experiment (Spehar et al., 2000).
Chemical Name
3 ,6-Dimethylphenanthrene
2-Ethylamhracene
2-(tert-butyi)anthracene
2,3 Benzofluorene
Benzo(a)anthracene
Triphenylene
9-Phenylanthracene
Benzo(b)fluoramhene
Benzo(k)fluoranthene
7, 12-Dimethylbenz(a)anthracene
Benzo(a)pyrene
3-MethylchoIanthrene
7-Methylbenzo(a)pyrene
TOTAL PAH- WATER CONCENTRATION
Molecular
Weight
(a/mol)
206.29
206.29
234^34
216.28
228.29
228.30
254.33
252.32
252.32
256.35
252.31
268.38
266.35
lORm £,„,*
5.52
5.36
5.88
5.54
5.67
5.75
6.31
6.27
6.29
6.58
• 6.11
6.76
6.54
lOR.n Knrb
5.42
5.27
5.78
5.44
5,58
5.65
6.20
6.16
6.18
6,46
6.00
6.64
6.43
Estimated •
Solubility'
77.98
59.62
33.04
25.30
12.28
5.110
3.640
8.280
8.350
13.41
2.880
3.110
1.460
Target
Sediment
Concentration
42.38
39.32
50.91
42.88
45.80
47.66
64.22
62.75
63.64
75.04
57.46
83.92
73.37
749.4
Nominal Water
Concentration11
(ue/L)
33.12 '
43.94
19.78 ,
33.27
27.70
24.11
10.30
10.96
10.50
6.620
14.38
5.100
7.320
247.1
Solubility Limited
Nominal Water
Concentration
(UR/D
33.12
' 43.94
19.78
25.30
12.28
5.110
3.640
8.280
8.350
6.620
2.880
3.110
1.460
173.9
'Predicted by SPARC in distilled water at 25°C.
"Predicted from Di Toro et al. (1991).
'Nominal concentration predicted by KQC, regardless of solubility limits; highest concentration only.
dTarget sediment concentration/^oc-
-------
Table 6-1. Relative Distribution of SESGTUFCViTOT to SESGTUFCV13 and SESGTUFCV-23 for the
Combined EMAP Dataset (N=488).
Percentile
50
80
' 90
95
99
ZiESOXUpcy^-j-Q-c /ZjESGXUpQv 13
2.75
6.78
8.45
11.5
16.9
SESGTUFCV,TOT /SESGTUFCV-23
1.64
2.80*
3.37
4.14
6.57
-------
Table 5-3. Chemicals included in the high KQV PAH mixture experiment (Spehar et al., 2000).
Chemical Name
3 ,6-Dimethylphenanthrene
2-Ethylanthracene
2-(tert-butyl)anthracene
2,3 Benzofluorene
Benzo(a)anthracene
Triphenylene
9-Phenylanthracene
Benzo(b)fluoranthene
Benzo(k)fluoranthene
7, 12-Dimethylbenz(a)anthracene
Benzo(a)pyrene
3-Methylcholanthrene
7-Methylbenzo(a)pyrene
TOTAL PAH- WATER CONCENTRATION
Molecular
Weight
(e/moD
206.29
206.29
234^34
216.28
228.29
228.30
254.33
252.32
252.32
256.35
252.31
268.38
266.35
loe,n Kn«?
5.52
5.36
5.88
5.54
5.67
5.75
6.31
6.27
6.29
6.58
• 6.11
6.76
6.54
5.42
5.27
5.78
5.44
5.58
5.65
6.20
6.16
6.18
6.46
6.00
6.64
6,43
Estimated •
Solubility'
(we/L)
77.98
59.62
33.04
25.30
12.28
5,110
3.640
8.280
8.350
13.41
2.880
3.110
1.460
Target
Sediment
Concentration
42.38
39.32
50.91
42.88
45.80
47.66
64.22
62.75
63.64
75.04
57.46
83.92 .
73.37
749.4
Nominal Water
Concentration*1
(ME/L)
33.12 '
43.94
19.78 ,
33.27
27.70
24.11
10.30
10.96
10.50
6.620
14.38
5.100
7.320
247.1
Solubility Limited
Nominal Water
Concentration
(«e/U
33.12
43.94
19.78
25.30
12.28
5.110
3.640
8.280
8.350
6.620
2.880
3.110
1.460
173.9
"Predicted by SPARC in distilled water at 25°C.
Predicted from Di Toro et al. (1991).
cNominal concentration predicted by KQC, regardless of solubility limits; highest concentration only.
dTarget sediment concentration//^.
-------
Table 6-1. Relative Distribution of SESGTUFCV.TOT to EESGTUFCV „ and ^ESGTU^^ for the
Combined EMAP Dataset (N=488).
Percentile
50
80
90
95
99
SESGTUpcv.TOj/SESGTUrev.,3
2.75
6.78
8.45
11.5
16.9
EESGTUFCV.TOT /EESGTUFCV 3
1.64
2.80*
3.37
4.14
6.57
-------
Table 6-2. PAH measured in various sediment monitoring programs. See Di Tcro and McGrath
(2000) for data sources.
Parameter NOAA
Acenaphthene x
Acenaphthylene x
Anthracene x
Chrysene x
Fluoranthene ~ x
Fluorene x
naphthalene x
phenanthrene x
pyrene x
Benzo(k)fluoranthene x
Benzo(b)fluoranthene x
Benzo(a)pyrene x
Benzo(a)anthracene x
Benzo(e)pyrene x
Benzo(g,h,0perylene x
Dibenz(a,h)anthracene x
2,6-dimethylnaphthalene x
Indeno(l,2,3-cd)pyrcne x
1-methylnaphthalene x
2-methylnaphdialene x
perylene x
1-methylphenanthrene x
2,3,5-trimethylnaphthalene x
2-methylanthracene
2-methylpbenanthrene
3 ,6-dimethy Iphenanthrene
9-methylanthracene
9, 10-dimethylanthracene
Cl-benzo(a)anthracenes /chrysenes
C2-benzo(a)andTracenes /chrysenes
C3-benzo(a)anthracenes /chrysenes
C4-benzo(a)anthracenes /chrysenes
Cl-fluoranthenes/pyrenes
C2-fluoranthenes/pyrenes
Cl-fluorenes
C2-fluorenes
C3-fluorenes
Cl-naphthalenes
C2-naphthalenes
C3-naphthalenes
C4-naphthalenes
Cl-phenanthrenes/anthracenes
C2-phenanthrenes/ anthracenes
C3-phenanthrenes/anthracenes
C4-phenanthrenes/anthracenes
Total Number of PAHs* 23
plumber of data points 640
SFEI
x
x
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
25
137
San
Diego
x
x
x
x
x
x
x
x
x
X
X
X
X
X
X
X
X
X
X
X
X
X
X
23
182
Southern
California
x
x
x
x
x
x
x
x
x
x
x
X
X
X
X
X
X
X
X
X
X
X
X
23
40
NY/NJ
REMAP*
X
x
x
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
23
153
Virginian
EMAP8
x
x
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
23
318
Elliott
Bay
x
x
x
x
x
x
x
x
x
x
x
x
x
x
x
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
33c
30
Carolinian
EMAP
x
X
X
X
X
X
X
X
X
X
X
X
X
X
X •
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
34
280
Louisian
EMAP
* x
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
34
229^
A Benzo(b)fluoranthene and benzo(k)flouranthene were measured together.
B A specific Cl-PAH was not .included in the total if the Cl alkylated PAH series was measured.
For example, 1-methylnaphthalene was not included in the total if the Cl-naphthalenes were measured.
c For this dataset, the Cl-Naphthalenes were not measured. As a result, the 1-methy (naphthalene and 2-methylnaphthaIene
were considered when determining the total number of PAHs.
-------
'able 6-3. Teratogenic and carcinogenic effects of benzo(a)pyrene (BaP) and anthracene on freshwater and saltwater fishes. Measured concentrations of
exposure are converted to sediment concentrations (Coc) likely to result in the equivalent effect using EqP and SAR methodology.
Organism Chemical Log,0 tfow
FRESHWATER
Fathead minnow eggs Anthracene 4.53
Topminnows BaP 6.11
Rainbow trout eggs BaP • 6.11
SALTWATER
English sole eggs BaP . 6.11
Sand sole eggs BaP 6.11
Calif, grunion eggs BaP 6.11
Calif, grunion eggs BaP 6.11
Calif, grunion eggs BaP 6.11
FRESHWATER
Japanese medaka BaP 6.11
guppy BaP 6.11
LogKoc
4.46
6.00
6.00
6.00
6.00
6.00
6.00
6.00
6.00
6.00
Measured Q-derived Measured
/"« /" /" b (i b
'-d . "-0C '-ORG ^L
(Mg/L) (A'g/goc) 6«g/g) /upu 0/g/g Lipid)
TERATOGENIC EFFECTS
8.8 0.06 147
>3.81C >3810 9 0.06 150
(1,000)
0.21 210 1.9 0.05 38;6
157 0.03 5233d
0.10 100 2.1 0.03 70
>3.81 >3810 1 0.03 33.3
(5)
>3.81 >3810 10.5 0.03 350
(24)
>3.81" >3810 20.0 0.03 666
(869)
CARCINOGENIC EFFECTS
4
>3.81C >3840
(261)
>3.8r >3840
(209)
CL-derived
Coc
(Mg/goc) References
219 Hall and Oris, 1991
256 Goddard et ah, 1987
66 Hannah etal., 1982
Hoseetal., 1984
8,937" Hose et al., 1981
120 Hoseetal., 1982
57 Winkleretal., 1983
598 Winkleretal., 1983
1,137 Winkler et al., 1983
' Hawkins etal., 1988, 1990
Hawkins etal., 1988, 1990
jiW
If thu concentration of BaP exceeded its solubility of 3.81 ^g/L, the published concentration in water is listed in parenthesis with the solubility of 3.81 /.ig/L listed above as the concentration of
ixposure. Therefore the maximum Cx value for these exposures is 3840A
-------
Table 6-2. PAH measured in various sediment monitoring programs. See Di Tcro and McGrath
(2000) for data sources.
Parameter NOAA
Acenaphthene x
Acenaphthylene x
Anthracene x
Chrysene x
Fluoranthene ~ x
Fluorene x
naphthalene x
phenanthrene x
pyrene x
Benzo(k)fluoranthene x
Benzo(b)fluoranthene x
Benzo{a)pyrene x
Benzo(a)anfljracene x
Benzo(e)pyrene x
Benzo(g,h,i)perylene x
Dibenz(ath)andiracene x
2,6-dimethylnaphthalene x
Indeno(l,2,3-cd)pyrene x
1-methylnaphthalene x
2-methylnaphthalene x
perylene x
1-methylphenanthrene x
2,3,5-trimethylnaphthalene x
2-methylanthracene
2-methylphenanthrene
3 ,6-dimethylphenanthrene
9-methylanthracene
9, 10-dimethylanthracene
Cl-benzo(a)anthraeenes /chiysenes
C2-benzo(a)andiracenes /chiysenes
C3-benzo(a)anthracenes /chiysenes
C4-benzo(a)anthracenes /chiysenes
Cl-fluoranthenes/pyrenes
C2-fluoranthenes/pyrenes
Cl-fluorenes
C2-fluorenes
C3-fluorenes
Cl-naphthalenes
C2-naphthalenes
C3 -naphthalenes
C4-naphthalenes
Cl -phenajnthrenes/anthracenes
C2-phenanthrenes/anthracenes
C3-phenanthrenes/anthracenes
C4-phenanthrenes/anthracenes
Total Number of PAHs8 23
Number of data points 640
SFEI
x
x
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
25
137
San
Diego
x
x
x
x
x
x
x
x
x
x
x
x
x
X
X
X
X
X
X
X
X
X
X
23
182
Southern
California
x
x
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
23
40
NY/NJ
REMAP*
x
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
23
153
Virginian
EMAP8
x
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
23
318
Eiliou
Bay
x
x
x
x
x
x
x
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
33C
30
Carolinian
EMAP
x
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
34
280
Louisian
EMAP
"< X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
34
229
1 Benzo(b)fluoranthene and benzo(k)flourandiene were measured together.
B A specific Cl-PAH was not .included in the total if the Cl alkylated PAH series was measured.
For example, 1-methylnaphthalene was not included in the total if the Cl-naphthalenes were measured.
c For this dataset, the Cl-Naphthalenes were not measured. As a result, the 1-mediy[naphthalene and 2-methylnaphthalene
were considered when determining die total number of PAHs.
-------
'able 6-3. Teratogenic and carcinogenic effects of benzo(a)pyrene (BaP) and anthracene on freshwater and saltwater fishes. Measured concentrations of
exposure are converted to sediment concentrations (Coc) likely to result in the equivalent effect using EqP and SAR methodology.
Organism Chemical Log10 Kow
Measured
/"«
**i .
LogKoc (Mg/L)
Cd-derived Measured
r r b
<-OC t"ORQ
(Mg/goc) fcg'g) /LipH
CL-derived
C b C
(pg/g Lipid) (Mg/goc) References .
TERATOGENIC EFFECTS
FRESHWATER
Fathead minnow eggs Anthracene 4.53
Topminnows BaP 6.11
Rainbow trout eggs BaP • 6.11
SALTWATER
English sole eggs BaP . 6.11
Sand sole eggs BaP 6. 1 1
Calif, grunion eggs BaP 6.11
Calif, grunion eggs BaP 6.11
Calif, grunion eggs BaP 6.11
4.46
6.00 >3.81'
(1,000)
6.00 0.21
6.00
6.00 0.10
6.00 >3.81
(5)
6.00 >3.81
(24)
6.00 >3,81C
. (869)
8.8 0.06
>3810 9 0.06
210 1.9 0.05
157 0.03
100 2.1 0.03
>3810 1 0.03
>3810 10.5 0.03
>3810 20.0 0.03
147 219 Hall and Oris, 1991
150 256 Goddard et ah, 1987
38;6 66 Hannah ctal., 1982
Hoseetal., 1984
5233d 8,937" Hose et al., 1981
70 120 Hoseetal., 1982
33.3 57 Winkleretai., 1983
350 598 Winkleretal., 1983
666 1,137 Winkleretal., 1983
CARCINOGENIC EFFECTS
FRESHWATER
Japanese medaka BaP 6.11
guppy BaP 6.11
6.00 >3.81C
(261)
6AA ^ ^ QIC
»W >j.ol
(209)
'
>3840
>3840
' Hawkins et al., 1988, 1990
Hawkins et al., 1988, 1990
If ihu concentration of BaP exceeded its solubility of 3.81 /ng/L, the published concentration in water is listed in parenthesis with the solubility of 3.81 ^
-------
Appendix A. Individual datasets which comprise the acute lethality data base. Table from Di Toro et al. (2000).
Common Name,
Scientific Name
Freshwater
Paramecjum,
Tetrahymena elliotti
Hydra,
Hydra oligactis
Snail,
Lymnae stagnalis
Cladocerah,
Daphnia cucullata
Cladoceran,
Daphnia magna
Ciadoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia pulex
Cladoceran,
Daphnia pulex
Test Duration (hr)
24
48
48
48
24
48
48
48
• 48
48
Test Conditions
Method* Concentration*1
S U
S U
S U
S U
S U
S U
S U
FT.R M
S M
S U
No. of Data
Points'
10(12)
5
5
5
21(28)
72(78)
19
1(2)
(1)
6
References
i
Rogerson et al., 1983
Slooffetal., 1983
Slooffetal., 1983
Canton and Adema, 1978
LeBlanc, 1980a
Abernethy et al., 1988; U.S. EPA, 1978; Canton
and Adema, 1978 Rogerson et al., 1983; Bringman
and Kuhn, 1959; Eastman et al., 1984; Dill, 1980
EG&G Bionomics, 1982; Thurston et al., 1985;
Adema, 1978; Oris et al., 1991; Brooke, 1991;
Millemann et al., 1984; Munkrittrick et al., 1991
EG&G Bionomics, 1982; Brooke, 1994
Trucco et al., 1983
Canton and Adema, 1978; Passino and Smith, 1987
A-l
-------
Test Conditions
Common Name,
Scientific Name
Brine shrimp,
Artemia salina
Crayfish,
Orconectes immunis
Mosquito,
Aeries aegypti
Mosquito,
Culex pipiens
Midge,
Tanytarsus dissimitis
Rainbow trout,
Oncorltynchus mykiss
Rainbow trout,
Oncorhynchus mykiss
Rainbow trout,
Oncorhynchus mykiss
Rainbow trout,
Oncorhynchus mykiss
Rainbow trout,
Oncorhynchus mykiss
Rainbow trout,
Oncorhynchus mykiss
Rainbow trout,
Test Duration (hr)
24
96
48
48
. 48
48
24
24
48
96
96
96
Method'
S
FT
S
S
S
FT.
FT
S
S
FT
S
S
Concentration11
N
M
U
U
M
M
M
U
U
M
M
U
No. of Data
Points'
32(34)
6
5
5
9
7
6
1(2)
6
22
1
1
References
Abernethy et al., 1988; Abernethy et ah, 1986
i
Thurston et al., 1985; Holcombe et al., 1987
Slooffeta!., 1983
SJooffetal., 1983
Thurston et al., 1985; Call et al., 1983
Holcombe et al., 19.87; Call et al., 1983
Calletal., 1983
Bentlyetal., 1975
Slooff et al., 1983; Bently et al., 1975
Thurston et al., 1985; Call et al., 1983; Holcombe et
al., 1987; Call et al., 1986; DeGraeve et al., 1982;
Hodsonetal., 1988
Home et al., 1983
Bently eta!., 1975
Oncorhynchus mykiss
A-2
-------
Appendix A. Individual datasets which comprise the acute lethality data base. Table from Di Toro et al. (2000).
Test Conditions
Common Name,
Scientific Name
Freshwater
Paramecium,
Tetrahymena eltiotti
Hydra,
Hydra oligactis
Snail,
Lymnae stagnalis
Cladoceran,
Daphnia cucullata
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia pulex
Cladoceran,
Daphnia pulex
Test Duration (hr)
24
48
48
48
24
48
48
48
• 48
48
Method"
S
S
S
S
S
S
S
FT.R
S
S
No. of Data
Concentration' Points0
U 10(12)
U 5
U 5
U 5
U 21(28)
U 72(78)
U 19
M 1(2)
M (1)
U 6
References
i
Rogersonetal., 1983
Slooffetal., 1983
Slooffetal., 1983
Canton and Adema, 1978
LeBlanc, 1980a
Abernethy et al., 1988; U.S. EPA, 1978; Canton
and Adema, 1978 Rogerson et al., 1983; Bringman
and Kuhn, 1959; Eastman et al., 1984; Dill, 1980
EG&G Bionomics, 1982; Thurston et al., 1985;
Adema, 1978; Oris et al., 1991; Brooke. 1991;
Millemann et a!., 1984; Munkrittrick et al., 1991
EO&G Bionomics, 1982; Brooke, 1994
Trucco et al., 1983
Canton and Adema, 1978; Passino and Smith, 1987
A-l
-------
Test Conditions
Common Name,
Scientific Name
Brine shrimp,
Anemia salina
Crayfish,
Orconectes immunis
Mosquito,
Aedes aegypli
Mosquito,
Culex pipiens
Midge,
Tanytarsus dissimilis
Rainbow trout,
Oncoritynchus mykiss
Rainbow trout,
Oncorhynchus mykiss
Rainbow trout,
Oncorhynchus mykiss
Rainbow trout,
Oncorhynchus niykiss
Rainbow trout,
Oncorhynchus mykiss
Rainbow trout,
Oncorhynchus mykiss
Rainbow trout,
Test Duration (hr)
24
96
48
48
. 48
48
"24
24
48
96
96
96
Method"
S
FT
S
S
S
FT.
FT
S
S
FT
S
S
Concentration11
N
M
U
U
M
M
M
U
U
M
M
U
No. of Data
Points0
32(34)
6
5
5
9
7
6
1(2)
6
22
1
1
References
Abernethy et al., 1988; Abernethy et al., 1986
i
Thurston et al., 1985; Holcombe et al., 1987
Slooffetal., 1983
Slooffetal., 1983
Thurston et al., 1985; Call et al., 1983
Holcombe et al., 19.87; Call et al., 1983
Call et al., 1983
Bently et al., 1975
Stooff etal., 1983; Bently etal., 1975
Thurston et al., 1985; Call et al., 1983; Holcombe et
al., 1987; Call et al., 1986; DeGraeve et al., 1982;
Hodsonctal., 1988
Home et al., 1983
Bently etal., 1975
Oncorhynchus mykiss
A-2
-------
Test Conditions
Common Name,
Scientific Name
Bleak,
Alburnus albumus
Goldfish,
Carasius auratus
Goldfish,
Carasius auratus
Goldfish,
Carasius auratus
Goldfish,
Carasius auratus
Goldfish,
Carasius auratus
Goldfish,
Carasius auratus
Goldfish,
Carasius auratus
Golden orfe,
Leuciscus idus melanotus
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow.
Test Duration (hr)
96
24
24
24
96
96
48
48
24
24
24
48
Method'
S
S
S
FT
S
FT
S
FT
S
S
FT
S
Concentration11
I
M
U
M
U
M
U
M
KM)
U
M
U
No. of Data
Points'
7
26(28)
5(6)
1(2)
4
1(2)
5(6)
1(2)
26 '
6
8
11
References
Bengtssonetal., 1984
Bridie etal., 1979 '
Pickering and Henderson, 1966
Brennimanetal., 1976
Pickering and Henderson, 1966
Brennimanetal., 1976
Pickering and Henderson, 1966
Brenniman et al., 1976
Juhnke and Ludemann, 1978
Pickering and Henderson, 1966
Ahmad et al., 1984
Pickering and Henderson, 1966
Pimephales promelas
A-3
-------
Test Conditions
Common Name,
Scientific Name
Fathead minnow,
Pimephales promelas
Fathead minnow.
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Channel catfish,
Ictaluna punctatus
Medaka,
Oryzias latipes
American flagfish,
Jordanella floridae
American flagfish,
Jordanella floridae
American flagfish,
Test Duration (hr)
48
96
96
96
96
„
96
48
24
48
96
Method*
FT
FT
S
R
S
FT.S
S
FT
FT
FT
Concentration1"
M
M
M
U
U
M
U
M
M
M
No. of Data
Points'
8
141(146)
3(4)
1
4
7
4(5)
6
6
6
References
Ahmad et at., 19"84
i.
Veith et al., 1983; Thurston et al., 1985; Holcombe
et al., 1987; Ahmad et al., 1984; Dill, 1980;
DeGraeve et al., 1982; Alexander etal., 1978;
Broderius and Kahl, 1985; Cairns and Nebeker,
1982; Hall et al., 1989; Hall et al., 1984; Call et al.,
1985; CLSES, 1984; CLSES, 1985; CLSES, 1986;
CLSES, 1988; CLSES, 1990; Kimball, 1978
Bridie et al., 1979; EG&G Bionomics, 1982;
Gendussa, 1990; Hornectal., 1983
Academy Natural Sci., 1981
Pickering and Henderson, 1966
Thurston et al., 1985; Holcombe et al., 1983;
Gendussa, 1990
Slooff etal., 1983
Smith et al., 1991
t
Smith et al., 1991
Smith etal., 1991
Jordanella floridae
A-4
-------
Test Conditions
Common Name,
Scientific Name
Mosquitofish,
Gambusia affinis
Mosquitofish,
Gambusia affinis
Mosquitofish,
Gambusia affinis
Mosquitofish,
Gambusia affinis
Guppy,
Poecilia reticulata
Guppy,
Poecilia reticulata
Guppy,
Poecilia reticulata
Bluegill,
Lepomis macrochirus
Bluegill,
Lepomis macrochirus
Bluegill,
Lepomis macrochirus
Bluegill,
Lepomis macrochirus
Bluegill,
Test Duration (hr)
24
48
96
96
24
48
96
24
24
48
48
96
Method'
S
S
FT
S
S
S
s
s
FT
FT
S
FT
Concentration11
U
U
M
U
U
'
U
U
U
M
M
U
M
No. of Data
Points'
(3)
(3)
5(6)
3
0)
10(11)
4
18(19)
1
1
6(7)
8
References
Thurstonetal., 1985
i
Thurston ct al., 1985
Thurstonetal., 1985;
Wallenetal.. 1957
Wallenetal., 1957
Pickering and Henderson, 1966
Slooff et al., 1983; Pickering and Henderson, 1966
Slooffetal., 1983
Pickering and Henderson, 1966; Buccaftisco et at.,
1981; Bently etal., 1975
Call et al., 1983
Call et al., 1983
Pickering and Henderson, 1966; Bently et al., 1975
Thurston et al., .1985; Bently et al., 1975; Call et
Lepomis macrochirus
al., 1983; Holcombe et al., 1987
A-5
-------
Test Conditions
Common Name,
Scientific Name
Bluegill,
Lepomis macrochlrus
Tadpole,
Rana catesbeiana
Clawed toad,
Xenopus laevls
Mexican axolotl,
Ambystom mexicanum
Salt water
Annelid worm,
Neanthes arenaceodentata
Annelid worm,
Neanthes arenaceodentata
Copepod,
Nitocra spinipes
Artiphipod,
Leptocheirus plumulosus
Mysid,
Americamysis baliia
Mysid,
Americamysis bahia
Mysid,
Test Duration (hr)
96
96
48
48
96
96
96
96
96
96
96
Method*
S
FT
S
S
S
R
S
FT
S
S
R
Concentration11
U
M
U
U
U
U
I
M
U
M
U
No. of Data
Points'
36(40)
5
5
S
4(5)
(1)
6
4
20(23)
1
1
References
Pickering and Henderson, 1966; U.S. EPA, 1978;
LeBlanc, 1980b; ; Buccafusco et al., 1981; Bently et
al., 1975; Dawson et al., 1977. i
Thurston et al., 1985
SlooffandBaerselman, 1980
SlooffandBaerselman, 1980
Home et al., 1983; Rossi and Neff, 1978
Thursby et al., 1989a
Bengtsson et al., 1984
Swartz, 1991a; Champlin and Poucher, 1992a;
Boeseetal., 1997
U.S. EPA, 1978; Champlin and Poucher, 1992a;
Zaroogianetal., 1985
EG&G Bionomics, 1982
Thursby et al., 1989b
Americamysis bahia
8(9)
A-6
-------
Test Conditions
Common Name,
Scientific Name
Mysid,
Americamysis bahia
Grass shrimp,
Palaemonetes pugio
Grass shrimp,
Palaemonetes pugio
Grass shrimp,
Palaemonetes pugio
Grass shrimp,
Palaemonetes pugio
Crab,
Ponunus pelagicus
Inland silverside,
. Menidia berylUna
Inland silverside,
Menidia berylUna
Sheepshead minnow,
Cyprinodon variegatus
Sheepshead minnow,
Cyprinodon variegatus
Sheepshead minnow,
./"* ' (..._ _. • *_._
Test Duration (hr)
96
96
96
96
96
96
96
96
24
48
96
Method'
FT
R
S
FT
S
S
R
S
S
S
S
' Concentration11
M
u-
U
M
M
M
U
U
U
U
U
No. of Data
Points6
8(9)
2
4
1
1
4
1
7(8)
7(8)
11(12)
13(15)
References
Battelle, 1987; Champlin and Poucher, 1992a;
Home et al., 1983; EG&G Bionomics, 1978; U.S.
EPA, 1978; Kuhn and Lussier, 1087; Thursby,
1991b
Battelle, 1987; Thursby et al., 1989a
Champlin and Poucher, 1992a; Home et al., 1983;
Thursby, 1991b; Tatem etal., 1978
Battelle, 1987
Tatem, 1977
Mortimer and Cornell, 1994
Thursby etal., 1989a
Champlin and Poucher, 1992a; Dawson et al., 1977;
Home et al., 1983
Heitmuller et al., 1981
Heitmulleretal., 1981
Hcitmulteretal., 1981:
Cyprinodon variegatus
U.S. EPA, 1978
A-7
-------
Common Name,
Scientific Name
Sheepshead minnow, .
Cypnnodon variegatus
Total Data Points
Test Conditions
No. of Data
Test Duration (hr) Method" Concentration* Points'
96 ' FT M 2
736 (796)
References.
Ward et ah, 1981 ; Battelle, 1987
'Method: S=static, FT « flow-through, R=renewal
bConcentration: U-unmcasured (nominal), M»clwmical measured, I«=initial
'Number of data points used; ()=number of data before screening for concentration > solubility and outliers.
A-8
-------
Appendix B. Chemicals which comprise the acute toxicity database for narcosis chemicals in Section 2 of this
document. Table from Di Toro et al. ( 2000).
Chemical
triethylene glycol
methanol
2,4-pentanedione*
ethanol
acetone
2-chloroethanol*
2-(2-ethoxyethoxy)ethaiioI
1 -chloro-2-propanol*
1 ,3-dichloro-2-propanol*
2-methyl-2,4-pentanediol
2-butanone
2-propaiwl
3-chloro-l-propanol*
1-propanol
cyclopcntanone
2-methyl-2-propanol
methyl chloride
2-butanol
methyl bromide*
3-methyl-2-butanone
2,3-dibromopropanol*
cyclohexanone
cyclopentanol
2-raethyl-l-propanol
4-methyl-3-peme-2-one
2-pentanone
l-butanol
3-pentanone
CASA
112276
67561
123546
64175
67641
107073
111900
127004
96231
107415
78933
67630
627305
71238
120923
75650
74873
78922
74839
563804
96139
108941
96413
78831
141797
107879
71363
96220
Class8
ao
ao
k
ao
k
ao
ao
ao
ao
ao
k
ao
ao
ao
k
ao
al.ha
ao
al.ha
k
ao
k
ao
ao
k
k
ao
k ,
"ow
-1.48
-0.715
-0.509
-0.234
-0.157
-0.048
0.011
0.156
0.165
0.246
0.316
0.341
0.363
0.399
0.453
0.663
0.677
0.717
0.791
0.792
0.819
0.827
0.849
0.858
0.867
0.877
0.946
0.954
MWD
150.17
32.04
100.12
46.07
58.08
80.51
134.17
94.54
128.99
118.17
72.11
60.10
94.54
60.10
84.12
74.12
50.49
74.12
94.94
86.13
217.90
98.14
86.13
74.12
98.14
86.13
74.12
86.13
MVE
131
41.0
100
59.0
74.0
65.0
111
84.0
91.0
120
90.0
77.0
82.0
75.0
89.0
95.0
56.0
93.0
57.0
108
96.0
103
89.0
93.0
118
107
92.0
108
— r •
SF
-
13.5
7.87
11.9
13.71
9.09
-
44.8
6.30
43.0
2.81
13.6
2.00
11.2
1.11
16.5
0.0666
14.9
0.154
1.32
5.97
0.445
5.19
10.6
2.68
1.03
3.03
0.849
B-l
-------
Chemical
2-methyl-2-butanol
2-n-butoxyethanol
diethyleneglycolmoiro-n-butylether
3,3-dimethyl-2-butanone
diethyl ether
4-methoxy-4-methyI-2-pentane
4-methyl-2-pentanone
dichloromethane
t-butylmethyl ether
cyclohexanol
2-hexanone
1 ,2-dichloroethane
1-pentanol
3-methyl-3-pentanol
2-phenoxyethanol
,
2(2.2nrichloroethanol
4-methyl-2-pentanol
3-hexanol
2-hepcanone
5-methyl-2-hexanone
2,4-dimethyl-3-pentanol
6-methyl-5-heptene-2-one
2-hexanol
1 ,3-dichIoropropane
1 ,2-dichloropropane
diisopropyl ether
chloroform
1 , 1 ,2-trichloroethane
1 ,4-dimethoxybenzene
2,6-dimethoxytoIunehe
CASA
75854
111762
112345
75978
60297
107700
108101
75092
1634044
108930
591786
107062
71410
77747
122996
115208
108112
623370
110430
110123
600362
110930
626937
142289
78875
108203
67663
79005
150787
' 5673074
Class8
ao
ao
et
k
et
k
k
al,ha
et
ao
k
al.ha
ao
ao
ao
ao
ao
ao
ke
ke
ao
ke
ao
al.ha
al.ha
et
al.ha
al.ha
ar
ar
if c
Aow
1.03
1.05
1.09
1.09
1.15
1.17
1.17
1.18
1.20
1.29
1.29
1.40
1.49
1.49
1.50
1.61
1.66
1.66
1.67
1.68
1.78
1.82
1.83
1.84
1.86
1.87
1.91
1.91
1.95
1.99
MWD
88.15
118.17
162.23
100.16
74.122
130.19
100.16
84.93
88.149
100.16
100.16
98.96
88.15
102.18
138.17
149.4
102.18
102.18
114.19
114.19
116.2
126.2
102.18
112.99
112.99
102.18
119.38
133.4
138.165
152.19
—' ' —
MVE
' '
110
131
170
125
105
143
124
65.0
122
103
124
79.0
109
125
122
93.0
126
125
141
141
140
151
126
97.0
99.0
138 -
81.0
94.0
132
147
— — _
SF
•
1 1.62
8.78
40.0
0.954
1.16
41.5
0.862
0.211
9.04
1.61
0.598
0.114
0.581
3.79
0.173
48.4
2.25
2.18
0.312
0.271
3.05
0.487
1.13
0.0363
0.0342
0.0918
0.0319
0.0369
0.0250
0.0283
B-2
-------
Chemical
benzene
l-hexanol
2-octanone
l-chloro-3-bromopropane
5-methyl-3-heptanone
anisole
2,6-dimethyl-2,5-heptadiene
t-1 ,2-dichloroethylene
1 ,2,3-trichloroepropane
1,1-dichloroethylene
1 ,3-dibromopropane*
bromofonn
1,1,2,2-tetrachloroethane
1 ,4-dichlorobutane
1,1-dichloropropane
2-nonanone
1.1,1-trichloroethane
1 , 1 . 1 ,2-tetrachloroethane
5-nonanone
1-heptanol
chlorobenzene
2-ethyl-l-hexanol
bicyclo{2,2, l)hepta-2,5-diene
toluene
styrene
tetrachloromethane
2-decanone
bromobenzene
cyclopentane
1,5-dichloropentane
CASA
71432
111273
111137
109706
541855
100663
504201
156605
96184
75354
109648
75252
79345
110565
78999
821556
71556
630206
502567
111706
108907
104767
121460
108883
100425
56235
693549
108861
278923
628762
Class6
ar
ao
ke
al.ha
ke
ar
fce
al.ha
al.ha
al.ha
al.ha
al.ha
al.ha
al.ha
al.ha
ke
al.ha
al.ha
ke
ao
ar.ha
ao
al
ar
ar
al.ha
ke
ar.ha
al
al.ha
^ow
2.00
2.02
2.02
2.04
2.05
2.06
2.07
240
2.13
2.19
2.24
2.25
2.31
2.33
2.36
2.38
2.38
2.43
2.44
2.57
2.58
2.58
2.60
2.62
2.72
2.73
2.73
2.75
2.76
2.76
MWD
78.11
102.18
128.21
157.44
128.21
108.14
138.21
96.94
147.43
96.94
201.9
252.73
167.85
127.01
112.99
142.24
133.4
167.85
142.24
116.2
112.56
130.23
92.14
92.14
104.15
153.82
156.27
157.01
70.134
141.04
MVE
89.0
125
157
100
156
111
164
81.0
107
81.0
103
88.0
106
113
101
174
101
110
174
142
102
155
102
107
116
97.0
190
106
95.0
130
SF
0.0260
0.159
0.111
0.0184 .
0.111
0.0148
0.0171
0.0202
0.0177
0.0141
0.00930
0.00650
0.0181
0.00990
0.00790
0.0801
0.00662
0.0050
0.0740
0.0487
0.00320
0.132
0.00490
0.00600
0.00550
0.00248
0.0599
0.00196
0.00260
0.00286
B-3
-------
Chemical
1 ,3 ,5-cycloheptatriene
trichloroethylene .
di-n-butyl ether
t-1 ,2-dichlorocyclohexane
pentachloroethane
2,4-hexadiene
butylphenyl ether
benzophenone
ethylbenzene
2,3-dimethyl-l ,3-butadiene
2-undecanone
l-octanol
3-chlorotoluene
4-chlorotoluene
o-xylcne
m-xylene
p-xylene
1 ,4-dichlorobenzene
3 ,5,5-trimethyl-l-hexanol
1 ,2-dichlorobenzene
1 ,3-dichlorobenzene
napthalene
cyclohexane
CASA
544252
79016
142961
822866
76017
592461
1126790
119619
100414
513815
112129
118875
108418
106434
95476
108383
106423
106467
3452979
95501
541731
91203
110827
Class8
, al
al.ha
et
al.ha
al.ha
al
et
ke
ar
al
ke
ao
ar.ha
ar,ha
ar
ar
ar
ar.ha
ao
ar.ha
ar.ha
pah
al
^ow
2.77
2.81
2.89
2.90
2.95
2.98
3.00
3.05
3.06
3.06
3.08
3.10
3.12
3.13
3.13
3.19
3.21
3.24
3.29
3.31
3.31
3.36
3.38
MWD
92.14
131.39
130.23
153.05
202.29
82.145
150.22
182.22
106.17
82.145
170.29
130.23
126.59
126.59
106.17
106.17
106.17
147.00
144.26
147.00
147.00
128.17
84.16
MVE
104
90.0
170
128
121
115
160
163
123
121
207
158
118
118
121
124
124
113
172
113
115
125
109
SF
* 0.00377
0.00360
0.00614
0.00162
0.00111
0.00237
0.000790
0.000480
0.00219
0.00162
0.0459
0.0161
0.000834
0.000817
0.00191
0.00154
0.00146
0.000581
0.0117
0.000507
0.000524
0.00110
0.000919
tetrachloroethylene
127184 al.ha 3.38 165.83 99.0 0.000710
B-4
-------
Chemical
2-dodecanone
cumene
pentane
1 ,2-dibromobenzene
1,5-cyclooctadiene
1-nonanol
1 ,2,4-trimethylbenzene
n-propylbenzene
dipentyl ether
1 ,3,5-trimethylbenzene
hexachloroethane
2,4-dichlorotoluene
1-methylnaphthalene
2-methylnaphthalene
2-chloronaphthalene
1 -chloronaphthalene
1 4-Hirhlnrotoluene
CASA
6175491
98828
109660 .
585539
111784
143088
95636
103651
693652
108678
67721
95738
90120
91576
91587
90131
95750
Class"
ke
ar
al
ar,ha
al
ao
ar
ar
et
ar
al,ha
ar.ha
pah
pah
pah.ha
pah.ha
ar.ha
r c
•"•OW
3.43
3.49
3.50
3.56
3.61
3.63
3.65
3.67
3.69
3,69
3.73
3.79
3.84
3.86
3.88
3.88
3.88
MWD
184.32
120.19
72.15
235.92
108.18
144.26
120.19
120.19
158.28
120.19
236.74
161.03
142.20
142.20
.162.62
162.62
161.03
MVE
223
140
116
119
130
175
138
140
202
140
132
129
140
141
136
136
129
SF
0.0357
*
0.000762
0.000592
0.0001%
0.000386
0.00552
0.000487
0.000467
0.000757
0.000414
0.0000936
0.000457
0.000280
0.000270
0.000100
0.000100
0.000120
biphenyl
92524
ar
3.91 154.21 150 0.000216
1,3,5-trichlorobenzene
108703 ar.ha 3.97 181.45 125 0.0000933
1,2,3-trichlorobenzene
87616 ar.ha 3.98 181.45 124 0.0000870
1,2,4-trichlorobenzene
120821 ar.ha 4.00 181.45 126 0.0000886
B-5
-------
Chemical
CAS*
Class6
MWD
MVE
acenaphthene
2,5-dimethyl-2,4-hexadiene
methyl cyclohexane
1 ,2,4,5-tetramethylbenzene
hexane
1,3-diethylbenzene
1-decanol
p-tert-butyltoluene
diphenylether
amylbenzene
phenanthrene
*
1 ,2.4,5-tetrachlorobenzene
1 ,2 ,3 ,4-tetrachlorobenzene
1 ,2,3,5-tetrachlorobenzene
1-undecanol
pyrene
9-methylanthracene
fluoranthene
1-dodecanol
83329
764136
108872
95932
110543
141935
112301
98511
101848
538681
85018
95943
634662
634902
112425
129000
779022
206440
112538
pah
al
al
ar
al
ar
ao
ar
et
ar
pah
ar.ha
ar.ha
ar.ha
ao
pah
pah
pah
ao
4.01
4.10
4.10
4.11
4.12
4.17
4.19
4.26
4.36
4.52
4.57
4.64
4.64
4.64
4.70
4.92
5.01
5.08
5.20
154.21
110.20
98.19
134.22
86.18
134.22
158.28
148.25
170.21
148.25
178.23
215.89
215.89
215.89
172.31
202.26
192.26
202.26
186.34
140
146
128
152
132
156
192
173
152
173
161
136
136
136
207
182
175
197
223
* 0.000100
0.000133
0.000155
0.000159
0.000131
0.000135
0.00181
0.0000995
0.0000595
0.0000502
0.0000340
0.0000151
0.0000145
0.0000148
0.000640
0.0000120
0.00000980
0.0000102
0.000238 '
pentachlorobenzene
608935 ar.ha 5.32 250.34 147 0.00000218
octane*
111659
ai
5.34 114.23 . 164 0.00000625
B-6
-------
Chemical CASA Class6 *owc MWD MVE Sr
1-tridecanol* 112709 ao 5.75 200.36 224 0.0000793
*
decane* 124185 al 6.56 142.28 229 0.000000300
*
Chemical is not included: LC50>S.
ACAS=Chemical abstract number
"Class: ao=alcohol, ar=aromatic. ha=halogenated, et=ether, al=aliphatic, ke=ketone, pah=PAH
cKov,=log,0(Kow);
DMW=molecular weight (gm/mol);
EV=molar volume (cmVmol);
FS=aqueous solubility(mol/L)
B-7
-------
-------
Appendix C. Summary of data on the acute toxicity of PAHs to freshwater and saltwater species and the derivation of genus mean acute values.
COMMON/SCIENTIFI
CNAME
FRESHWATER
Hydra,
Ifytfra amcricana
Hydra,
Hydra sp.
Annelid,
Lumbricutus variegaius
Annelid,
Lumbriculus variegatus
Snail,
Mudalia potosensis
Snail,
Aplexa hypnorum
Snail,
Physa heierostropha
Snail,
Physella virgata
Cladoceran,
Daplmia magna
Cladoceran,
Daplmia magna
Cladoceran,
Daplmia magna
Cladoceran,
Daplmia magna
PAH
LIFE- TESTED LOG
STAGE* HABITAT" (CAS #) K™c
J W,E fluoranthene 5.08
(206-44-0)
X W,E phenanthrene 4.57
(85-01-8)
X I phenanthrene 4.57
(85-01-8)
A I fluoranthene 5.08
(206-44-0)
X E fluorene 4.21
(86-73-7)
X E acenaphthene 4.01
(83-32-9)
X E fluoranthene 5.08
(206-44-0)
A E fluorantliene 5.08
(206-44-0)
X W naphthalene 3.36
(91-20-3)
J W naphthalene 3.36
(91-20-3)
X W naphthalene 3.36
(91-20-3)
J W 1-methyl 3.84
naphthalene
(90-12-0)
PAH NORMALIZED
SPECIFIC PAH SPECIFIC SPECIES
CONCEN- . LC50/EC50" LC50/EC50" SMAV" SMAV1 SMAV'
METHOD0 TRATION" (u2/L) (wmol/L) (umol/L) («mol/iu-) (wmol/tw.)
FT M 70 0.346 0.346 22.1 22.1
FT M 96 0.539 0.539 11.2 11.2
FT M >419 >2.35 >2,35 >49.0
FT M >178 >0,880 >0.880. >56 >52.4
S U >1900° >11.4 >11.4 >108 ' >108
(5600)
FT M >2040 >13.2 >13.2 >81.8 >81.8
S U 137 0.677 0.677 43.2 43.2
FT M >178 >0.880 >0.880 >56 >56
S U 8570 66.9
S U 4723 36.9
S M 2160 16.9 34.6 51.0
S U 1420 9.99 • 9,99 42.2
GMAV"
(wmol/fu-) REFERENCES
Speharetal., 1999
i
15.5 Call et a!., 1986
Call etal., 1986
>52.4 Speharetal., 1999
>108 Finger etal., 1985
>81,8 Holco'mbe etal., 1983
43.2 Home and Oblad, 1983
>56 Speharetal., 1999
U.S. EPA, 1978
AberneOiy etal., 1980
Millemannetal., 1984
Abernelhy etal., 198G
C-1
-------
COMMON/SC1ENTIFI
CNAME
Cladoceran,
Daphnia magna
Cladoceran,
Duphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Dailuiia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
LIFE-
STAGEA
J
X
X
X
X
X
X
J
X
, Neonate
Neonate
Neonate
X
HABITAT8
W
W
W
W
W
W
W
W
W
W
W
W
W
PAH
TESTED LOG
(CAS fl K™c
2-metliyl 3.86
naphthalene
(91-57-6)
acenaphihene 4.01
(83-32-9)
acenaphthene 4.01
(83-32-9)
acenaphthene 4.01
(83-32-9)
acenaphthene 4.01
(83-32-9)
acenaphthene 4.01
(83-32-9)
fluorene 4.21
(86-73-7)
phenanthrene 4.57
(85-01-8)
phenanthrene 4.57
(85-01-8)
phenanthrene 4.57
(85-01-8)
phenanthrene 4.57
(85-01-8)
phenanthrene 4.57
• (85-01-8)
phenamhrene 4.57
(85.-01-8)
CONCEN- LC50/EC5011
METHOD" TRATION8 (uv.ll]
S U 1491
S U 3450
S U .>3800
(41000)
S M 320
S M 1300
FT • M 120
S U 430
S U 207
S U 843
S M 700
S.R M 212
FT M • 230
FT M 117
Kow
PAH NORMALIZED
SPECIFIC PAH SPECIFIC SPECIES
LC50/EC50" SMAV" SMAV1 SMAV'
(umol/L) (wmol/L) («mol/&v) fomol/Br*.)
10.5 10.5 46.3
22.4
>24.6
2.08
8.43
0.778 0.778 4.80
2.59 2.59 24.5
1.16
4.73
3.93
1.19 _ _
1.29
0.656 0.920 19.2
GMAV"
(umol/E^.) REFERENCES
Aberncthy etal., 1986
Randall and Knopp, 1980
LcBlanc, 1980a
EG&G Bionomics, 1982
EG&G Bionomics, 1982
EG&G Bionomics, 1982
Finger etal., 1985
Abernethy etal., 1986
Eastmond etal., 1984
Millcmannetal., 1984
Brooke, 1994
Brooke, 1993
Call eta!,, 1986
C-2
-------
COMMON/SCIENTIFI LIFE-
CNAME STAGE* HABITAT*
Cladoceran, J W
Daphnia magna
Cladoceran, J W
Dai'hnta magna
Cladoceran, J W
Daphnia tnagna
Cladoceran, J W
Daphnia magna
Cladoceran, J W
Daphnia magna
Cladoceran, X W
Daphnia magna
Cladoceran, X W
Daphnia pulex
Cladoceran, X W
Daplmia pulex
Cladoceran, X W
Daphnia pulex
Cladoceran, X W
Daphnia pulex
Cladoceran, X W
Daphnia pulex
Cladoceran, Neonate W
Daphnia pulex
PAH
TESTED LOG
//"" A C tf\ f" C
(v-Aiff) rwvi/
pyrene 4.92
(129-00-0)
9-methyl 5.01
anthracene
(779-02-2)
fluoranthene 5.08
(206-44-0)
fluoranthene 5.08
(206-44-0)
fluoranthene 5.08
(206-44-0)
fluoranthene 5.08
(206-44-0)
naphthalene 3.36
(91-20-3)
fluorene 4.21
(86-73-7)
1,3-dimethyl 4.37
naphthalene
(575-41-7)
2,6-dimethyl 4.37
naphthalene
(581-42-0)
anthracene 4.53
(120-12-7)
phenanthrene 4.57
(85-01-8)
V
PAH NORMALIZED
SPECIFIC PAH SPECIFIC SPECIES
CONCEN- LCSOreCSO' LC50/EC5r/ SMAV" SMAV1 SMAV1
METHOD0 TRATION8 («E/L) (wniol/L) (umol/c™-)
S U 90.9 0.45 0.45 20.1
S U 124,8 0.65 O.G5 34.9
S U >260 >1.29
(320000)
S M 45 0.222
R M 117 0.578
S M 105.7 0.523 0.407 25.9 25.2
S U 4663 36.4 36.4 54.0
s U 212 1.27 1,27 12.1
S U 767 4.92 4,92 66
s U 193 1.24 1.24 16.8
s U >45 >0.25 >0.25 >4.9L
(754)
S U 734 4.12 '
GMAVK
(urnol/K,*.) REFERENCES
Abernethy etal., 1986
Abernethy etal., 1986
i
LeBlanc, 1980a
Oris etal., 1991
Spehar et al., 1999
Suedel ad Rodgers, 1996
Smitli et al., 1988
Smith etal., 1988
Smitli etal., 1988
Smith etal., 1988
Smith etal., 1988
Passino and Smith, 1987
C-3
-------
COMMON/SC1ENTIPI LIFE-
CNAME STAGEA HABITAT"
Cladoceran, X W
Daphnia pulex
Cladoceran, X W
Daphnia pulex
Cladoceran, X W
Daphnia pulex
Chdoceran, X W
Daphnia pulex
Amphipod, X E
Gammarus minus
Amphjpod, A E
Gammarus minus
Amphipod, X E
Gammarus
pseudolimnaeia
Amphipod, X E
Gammarus
pseudotimnaeus
Amphipod, A E
Gammarus
pseudoiimnaeus
Amphipod, J E
Hyalelh aaeca
Dragonfly, N E
Ophiogomphus sp.
Stonefly, X E
Peltoperla maria
PAH
TESTED LOO
(CAS /n K™,c
plienantlirene 4.57
(85-01-8)
plienantlirene 4.57
(85-01-8)
phenanthrene 4.57
(85-01-8)
2-methyl 4.99
anthracene
(613-12-7)
acenaphthene 4.01
(83-32-9)
fluoranthene 5.08
(206-44-0)
fluorene 4.21
(86-73-7)
plienantlirene 4.57
(85-01-8)
fluorantliene 5.08
(206-44-0)
fluoranthene 5.08
(206-44-0)
fluoranthene 5.08
(206-44-0)
acenaphthene 4.01
(83-32-9)
K
PAH NORMALIZED
SPECIFIC PAH SPECIFIC SPECIES
CONCEN- LC50/EC5011 LC50/EC501" SMAV" SMAV1 SMAV1
METHOD0 TRATION" Oyt/LV _ fyimoVL) (umoUL) (wmol/iw.) (nmol/E^)
S U >HOO >6.17
S U 350 1.96
S M 100 0.56 1.66 34.6
S U >30 >0.156 >0.156 >8.1I- 30.2
(96)
S U 460 '3.0 3.0 18.4
S U 32 0.16 0.16 10.1 13.6
S U 600 3.61 3,61 34.2
FT M 126 0.707 0.707 14.8
FT M 43 0.213 0.213 13.5 19.0
171 M 44 0.218 0.218 13.9 13.9
FT M >178 >0.880 >0.880 >56 >56
s U 240 1.6 1.6 9.6
GMAV*
(wmol/p,,-1) REFERENCES
Gciger and Buikcma, 1981, 1982
Smith etal., 1988
i
Trucco etal., 1983
27.6 Smith et al., 1988
Home etal., 1983
Hdrnc and Oblad, 1983
Finger etal., 1985
Call et at., 1986
16.1 Spehar et al., 1999
13.9 Spehar etal., 1999
•ft*
>56 Spehar et al., 1999
Home etal., 1983
C-4
-------
COMMON/SCHiNTlin
C NAME
Stoncfly,
Peltoperla maria
Miige,
Cli ronomus teutons
Midge, '
Cliironomus teutons
Mids.e,
Quronomus tentans
Midge,
Clttronomus rlpariiis
Midge,
Paratanytarsus sp.
Midge,
ParatoJiytarsus sp.
Midge
Tanytarsus dissimilis
Midge
Tanytarsus dissimilis
Coho salmon
Oncorhyncltus kisutdt
Coho salmon
Oncorhynchus kisutdi
Rainbow trout
Oncorhynchus mykiss
Rainbow trout
Oncorliyitdiiis mykiss
LIFE-
STAGE* HABITAT"
X E
L I
L I
L 1
L 1
X E
X E
L I
L I
E I
F W
pre SU I
pre SU I
PAH
TESTED LOO
(CAS iC) Ko«,c
fluoranthene 5.08
(206-44-0)
naphthalene 3.36
(91-20-3)
phenanthrene 4.57
(85-01-8)
fluoranthene 5.08
(206-44-0)
fluorene 4.21
(86-73-7)
acenaphthene 4.01
(83-32-9)
acenaphthene 4,01
(83-32-9)
naphthalene 3.36
(91-20-3)
naphthalene 3.36
(91-20-3)
naphthalene 3.36
(91-20-3)
naphthalene 3.36
(91-20-3)
naphthalene 3.36
(91-20-3)
naphthalene 3.36
(91-20-3)
PAH NORMALIZED
SPECIFIC PAH SPECIFIC SPECIES
CONCBN- LC50/EC501' LC50/EC50r SMAV" SMAV1 SMAV'
METHOD" TRATION" («e/U Omiol/L) (wnol/L) (umoVe*} . (wmol/c,,,.)
S U 135 0.667 0.667 42.5 20.2
S M 2810 21.9 21.9 32.5
S M . ' 490 2.75 2.75 57.0
S M >250 >1.24 >1.24 >79L 43.0
S U >1900 > 11.42 > 11.42 >108 >108
(2350)
S M 2000 13.0
S M 2090 13.6 13.3 82 82
S U 20700 162
S U 12600 98.31 126 187 187
R M > 11800 >92.1
R M 5600 43.7 43.7 65.0 65.0
S • U 1800 14.0
S U 6100 47.6
GMAV*
(iimoV&f) REFERENCES
20.2 Home and Oblad, 1983
i _ Millemannetal., 1984
Millemann et at., 1984
Suedel ad Rodgers, 1996
>68.2 Finger etal., 1985
Northwestern Aquatic Science
Inc., 1982
82 Northwestern Aquatic Science
Inc., 1982
Darville and Wilhm, 1984
187 Darville and Wilhm, 1984
Korn and Rice, 1981
Korn and Rice, 1981
Edsall, C.C., 1991
Edsall, C.C., 1991
C-5
-------
COMMON/SCIENTIFI
C NAME
Rainbow trout
Oncorhynchus mykiss
Rainbow trout
0, corhynchus mykiss
Rainbow trout
Oncorhynchus mykiss
Rainbow trout
On<-,}rhynchus mykiss
Rainbow trout
Oncorhynchus mykiss
Rainbow trout
Oncorhynchus mykiss
Rainbow trout
Oncorhynchus mykiss
Rainbow trout
Oncorhynchus mykiss
Rainbow trout
Oncorhynchus mykiss
Rainbow trout
Oncorhynchus mykiss
Rainbow trout
Oncorhynchus mykiss
Rainbow trout
Oncorhynchus mykiss
Brown trout,
Salnvj trutla
LIFE-
STAGE*
preSU
preSU
preSU
J
X
J
J
preSU
L
J
X
J
J
HABITAT"
I
1
I
W
W
W
W
I
W
W
W
W
W
PAH
TESTED
naphthalene
(91-20-3)
naphthalene
(91-20-3)
naphthalene
(91-20-3)
naphthalene
(91-20-3)
naphthalene
(91-20-3)
acenaphthene
(83-32-9)
fluorene
(86-73-7)
1,3-dimethyl
naphthalene
(575-41-7)
phenanthrene
(85-01-8)
phenanthrene
(85-01-8)
fluoranthene
(206-44-0)
fluoranthene
(206-44-0)
acenaphthene
(83-32-9)
LOG
3.36
3.3C
3.36
3.36
3.36
4.01
4.21
4.37
4.57
4.57
5.08
5.08
4.01
CONCEN-
METHOD0 TRATION"
S U
S U
S ' U
FT M
FT M
FT M
S U
S U
S U
FT M
S M
FT M
Ft M
PAU NORMALIZED
SPECIFIC PAH SPECIFIC
LC50/EC501' LC50/EC50" SMAV" SMAV1
(ue/U (umol/U (uttvol/U (umolfE/v)
2600 20.3
4400 ' 34.3
- 5500 42.9
1600 12.5
2300 17.9 15.0 22.2
670 4.34 4.34 26.9 .
820 4.93 4.93 46.7
1700 10.9 14.0 188L
>UOO >6.2
(3200)
375 2.10 2.10 43.9
187 0.925
2<5-0 0.129 0.129 8.19
580 3.76 3.76 23.3'
SPECIES
SMAV1 GMAV*
(umol/jw) (wmol/iw) REFERENCES
Edsall, C.C., 1991
t _ Edsall. C.C., 1991
Edsall. C.C., 1991
DcGraeve et al., 1982
DeGraeve e( al., 1980
Holcombe et al., 1983
Finger et al., 1985
Edsall, C.C., 1991
Edsall, C.C., 1991
Call etal., 1986
Home and Oblad, 1983
25.1 40.4 Spehar etal., 1999
23.3 23.3 Holcombe etal., 1983
C-6
-------
COMMON/SC1ENTIFI LIFE-
C NAME STAOEA HABITAT"
Fathead minnow, J W
Ptmephales promelas
Fathead minriow, J W
P'mephales promelas
Fathead minnow, X W
Pimepltales promelas
Fathead minnow, J W
Pimephales promelas
Fathead minnow, J W
Pimephales promelas
Fathead minnow, J W
Pimephales promelas
Fathead minnow, J w
Pimephales promelas
Fathead minnow, J W
Pimephales promelas
Fathead minnow, J W
Pimephales promelas
Fathead minnow, A W
Pimephales promelas
Fathead minnow, / W
Pimephales promelas
Fadiead minnow, J W
Pimephales promelas
Fathead minnow, J W
PAH
TESTED LOQ
(CAS « K™c
naphthalene 3.36
(91-20-3)
naphthalene 3.36
(91-20-3)
naphthalene 3.36
(91-20-3)
naphthalene 3.36
(91-20-3)
naphthalene 3.36
(91-20-3)
naphthalene 3.36
(91-20-3)
1-methyl 3.84
naphthalene
(90-12-0)
acenaphthene 4.01
(83-32-9)
acenaphthene 4.01
(83-32-9)
acenaphthene 4.01
(83-32-9)
acenaphthene 4.01
(83-32-9)
acenaphthene 4.01
(83-32-9)
acenaphthene 4.01
PAH NORMALIZED
SPECIFIC PAH SPECIFIC
CONCEN- LC50/EC50" LC50/EC50r SMAV". SMAV1
METHOD" TUATION* («H/L) fumol/L) (wmol/L^ (umol/E~->
S M 1990 15.5
IT M 7900 61.6
FT M 4900 38.2
FT M 6140 47.9
FT M 8900 69.4
FT M 6080 47.4 51.8 76.8
S U '• 9000 63.4 63.4 268
.S M 3100 20
S M 1500 9.7
R U 3700 24
FT M 1730 11.2
FT M 608 3.94'
FT M >1400 >9,1
C-7
Sl'ECIES
SMAV' GMAV*
(Mmol/fcv) (wmol/a/,1 REFERENCES
Millemannetal., 1984
DeGraeveetal., 1982
i
DeGraeveetal., 1980
Geigeretal., 1985
DeGraeveetal., 1980
Holcombeetal., 1984
Mattson et al., 1976
Marine Bioassay Lab., 1981
EG&G Bionomics, 1982
Academy of Natural Sci., 1981
Gcigereta!., 1985
Cairns and Nebekcr, 1982
EG&G Bionomics, 1982
-------
COMMON/SCIENTIFI
C NAME
Pimephales promelas
Fathead minnow,
Pimephales promelas
Cathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Channel catfish,
laalurus punaatus
Channel catfish.
Ictalurus punaatus
Bluegill,
Lepomis macrodurus
Bluegill,
Lepomis macrochirus
Bluegill,
Lepomis macrochirus
PAH
LIFE- TESTED LOO
STAGE*' HABITAT8 (CAS #1 K™5
(83-32-9)
J W acenaphthene 4.01
(83-32-9)
X W fluorene 4.21
(86-73-7)
J W pbenanthrene 4.57
(85-01-8)
J W fluoranthene 5.08
(206-44-0)
J W fluoranthene 5.08
(206-44-0)
A W fluoranthene 5.08
(206-44-0)
J W fluoranthene 5.08
(206-44-0)
J E acenaphthene 4.01
(83-32-9)
J E fluoranthene 5.08
(206-44-0)
J W acenaphthene 4.01
(83-32-9)
X W fluorene 4.21
(86-73-1)
J W phenanthrene 4.57
(85-01-8)
PAH NORMALIZED
SPECIFIC PAH SPECIFIC
CONCEN- LC50/EC501' LC50/EC50' SMAV11 SMAV1
METHOD0 TRATION" (ue/L) (wmol/L) («mol/L) (umol/jw-)
FT, M 1600 10 7.71 48.0
S U >1900 >11.4 >H,4 >108t
(100000)
S • M >HOO >6.17 >6.17 >129L
S M 95 0.470
S M 7.71 0.0381
FT U >21.29
(>1000)
FT M 69 0.34 0.34 22.0
FT M 1720 11.2 11.2 69.0
S M 37.40 0.185 0.185 12.0
S U 1700 11.0 11.0 68
s U 910 5.47 5.47 51.8
Fr M 234 1.31 ' 1.31 27.4
SPECIES
SMAV1 GMAVK
(wmol/E,v) (wmol/e/t) REFERENCES
Holcombe etal., 1983
i
Finger etal., 1985
U.S. EPA, 1978
Home and Oblad, 1983
Gendusa, 1990
Birge etal., 1982
68.3 68.3 Spehar etal., 1999
Holcombe etal., 1983
28.8 28.8 Gendusa, 1990
Buccafuscoetal.. 1981
Finger etal., 1985
Call etal., 1980
C-8
-------
COMMON/SC1ENT1F1 L1FE-
CNAME STAGE* HABITAT"
Bluegill, J \V
Lepontis macrocltirus
Bluegill, J W
Lcpomis macrocliirtu
South african clawed frog L W
Xenopus laevis
South african clawed frog L W
Xenopus laevis
SALTWATER
Annelid worm, J I
Nennthes
arenaceodentata
Annelid worm, X I
Neanthes
arenaceodentata
Annelid worm. J I
Neanthes
arenaceodentata
Annelid worm,
Neanthes A I
arenaceodentata
Annelid worm, J I
Neanthes
arenaceodentata
Annelid worm, J I
Neanthes
arenaceodentata
Archiannelid, J 1
DinopMlus gyroclliatus
Mud snail, A I,E
Nauarius obsolem
PAH
TESTED LOO CONCEN-
(CAS« K™c METHOD" TRATION"
fluoranlhene 5.08 S U
(206-44-0)
fluoranthene 5.08 FT M
naphthalene 3.36 FT M
(91-20-3)
naphthalene 3.36 FT M
(91-20-3)
naphthalene 3.36 S U
(91-20-3)
acenaphthcne 4.01 S U
(83-32-9)
acenaphthene 4.01 R U
(83-32-9)
phenanthrene S U
(85-01-8) 4.57
fluoranthene 5.08 S U
(206-44-0)
fluorantliene 5.08. S U
(206-44-0)
phenanthrene 4.57 R U
(85-01-8)
phenanthrene 4.57 R M
(85-01-8)
Kow
PAH NORMALIZED
SPECIFIC PAH SPECIFIC SPECIES
LC50/EC50r LC50/EC50P SMAV" SMAV1 SMAV'
(»g/L) (nmol/D (umo\/L) (umol/E/vO (umol/a/^
>260 >1.3
(4000)
44 0.218 0.218 13.9 34.0
2100 16.38
2100 16.38 16.38 24.3 24.3
3800 29.6 29.6 44.0
3600 23.3
>3800 >24.6 23.3 144
(16440)
600 3.37 3.37 70.0
>260 >1.29
(500)
>260 >1.29 >1.29 >82L 76.3
(20000)
185.40 1.04 1.04 21.7 21.7
>245 >1,37 >1.37 >28.7 >28.7
OMAVK
(umol/e«.) REFERENCES
Buccafusco el a)., 1981; EPA,
1978
34.0 Speharetal., 1999
Edmisten and Bands, 1982
24.3 Edmisten and Bantle, 1982
Rossi and Neff, 1978
Home etal., 1983
Thursby etal., I989a
Rossi and Neff, 1978
Rossi and Neff, 1978
76.3 Speharetal.. 1999
21.7 Battelle Ocean Sciences, 198"
>28.7 Dattelle Ocean Sciences, 198'
C-9
-------
COMMON/SCIENTIFI
C NAME
Blue mussel,
Mytilus edulis
Pacific oyster, *
( 'rassostrea gigas
Coot clam,
MuU/iia lateralis
Cost dam,
Mulinia lateralis
Soft-shell clam,
Mya arenaria
Calanoid copepod
Eurytemora qffinis
Calanokl copepod
Eurytemora qffinis
Calanoid copepod
Eurytemora qffinis
Calanoid copepod
Eurytemora qffinis
Mysid,
Amcricamysis baliia
Mysid,
• Amcricamysis bahia
Mysid,
. Atncricamysis bitMa
PAH
L1PE- TESTED LOG ' CONCEN-
STAGE* HABITAT" (CAS ft IC™C METHOD0 TRATION*
A E,W phenanthrene 4.57 R M
(85-01-8)
E/L W naphthalene 3.36 S U
(91-20-3)
J E pyrene 4.92 FT M
(129-00-0)
J E fluoranthene 5.08 S U
(206-44-0)
A 1 phenanthrene 4.57 R M
(85-01-8)
A X naphthalene 3.36 S U
(91-20-3)
A X 2-methyl 3.86 S U
naphthalene
(91-57-6)
A X 2,6-dimethyl 4.37 S M
naphthalene
(581-42-0)
A X 2.3.5- 4.86 S M
trimethyl
naphthalene
(2245-38-7)
J E acenaphthene 4.01 S U
(83-32-9)
] E acenaphthene 4.01 S M
(83-32-9)
j E acenaphthene 4.01 R U .
(83-32-9)
KOW
PAH NORMALIZED
SPECIFIC PAH SPECIFIC SPECIES
LC50/EC5011 LC50/EC50r SMAV" SMAV1 SMAV'
GJC/L) tomol/L) (ymol/L) fomol/enr) (/jmol/c/^-)
>245 >1.37 >1.37 >28.7 >28.7
>31000 >242 >242 >359 >359
(199000) ,
>132 > 0.653 > 0.653 >29.2
(>240)
>260 >l-29 >1.29 >82.0 >48.9
(10710)
>245 >1.37 >1.37 >28.7 >28.7
3798 22.6 22.6 33.5
1499 7.74 7.74 34.2
852 3.9 3.9 52.0
316 1.3 1.3 50.0 41.5
970 6.29 _
160 1.04 _
1190 7.72 .
GMAVK
(wnot/iw) REFERENCES
>28.7 Battelle Ocean Sciences, 1987
, >359 U.S. EPA, 1980
Champlin and Poucher, 1992c
>48.9 Spehar etal.. 1999
>28.7 Battelle Ocean Sciences, 1987
Ott, etal., 1978
Ott, etal., 1978
Ott, eta!., 1978
41.5 Ottt el al.. 1978
U.S. EPA. 1978;Wardctal..
1981
EG&G Bionomics, 1982
Thursbyetal., !989a
C-10
-------
COMMON/SC1ENTIFI
CNAME
Mysid,
Americamysis baliia "
Mysvd,
A •nericamysis bahia
Mysid,
Americamysis bahia
MyVid,
Americamysis bahia
Mysid,
Americamysis bahia
Mysid,
Americamysis baliia
Mysid,
Americamysis bahia
Mysid,
Americamysis bahia
Mysid,
Americamysis bahia
Mysid,
Americamysis bahia
Mysid,
Americamysis bahia
Mysid,
Neomysis americana
Mysid,
Neomysis americana
LIFE-
STAGE* HABITAT"
J E
J E
J E
J E
J E
J E
J E
J E
J E
J E
J E
X E
X E
PAH NORMALIZED
PAH SPECIFIC PAH SPECIFIC SPECIES
TESTED LOG CONCEN- LC50/EC50" LC50/EC50' SMAV" SMAV' SMAVJ
(CASdO K^c METHOD0 TRAT10N" (wc/L) (wmol/L) («mol/L) (ymol/av) Omiol/jwO
acenaphthene 4.01 FT M 460 2.98
(83-32-9) "
acenaphthene 4.01 FT M 190 1.23
(83-32-9) ~ "
acenaphthene 4.01 FT M 466.1 3.02
(83-32-9) "
acenaphthene 4.01 FT M 271.9 1.76 2.10 13.0
(83-32-9)
phenanthrene 4.57 FT M 27.1 0.152
(85-01-8)
phenanthrene 4.57 FT M *7.7 0.099 0.123 2.60
(85-01-8)
pyrene 4.92 FT M 28.28 0.140 0.140 6.30
(129-00-0)
fluoranthene 5.08 S U 31 0.153
(206-44-0)
fluoranthene 5.08 S U 40 0.198
(206-44-0)
fluoranthene 5.08 FT M 30.53 0.151
(206-44-0)
fluoranthene 5.08 FT M 87 0.430 0.255 16.2 7.66
(206-14-0)
naphthalene 3.36 S M 1250 9.75 _
(91-20-3)
naphthalene 3,36 S M 1420 11.1 10.4 15.4 15.4
(91-20-3)
GMAV*
fwmol/Bne) REFERENCES
Thursby el al., 1989b
EG&G Bionomics, 1982
i
Horneetal., 1983;Thursby,
1991a
Horneetal., 1983;Thursby,
1991a
Kuhnand Lussier, 1987
Battelle Ocean Sciences, 1987
Champlin and Poucher, I992c
Speharetal., 1999
U.S. EPA, 1978
Champlin and Poucher, 19921
Speharctal., 1999
7.66 EG&G Bionomics, 1978
Hargreaveseta!., 1982
15.4 Hargreaves etal., 1982
C-ll
-------
COMMON/SC1ENTIFI LIFE-
CNAME STAGE* HABITAT"
Isopod J I.E
Excirolana
vancouverensis
\mphipod, J t
. \nipelisca abdita
Amphipod, J I
Ampelisca abdita
Amphipod, ' A E,I
Leptocheints plumutosus
Amphipod, A E,I
Leptocheirus pluinulosus
Amphipod, 3 E,I
Leptocheirus plumulosus
Amphipod, X E,I
Leptocheirus plumulosus
Amphipod, J I
Rhepoxynius abronius
Amphipod, . J I
Eohaustorius estuarius
Amphipod, J I
Grandidierella japonica
Amphipod, J I
CoropMum insidiosum
Amphipod, J I.E
Emeriia analogs
Vfpln shrimn X "
PAH
TESTED LOO CONCBN- LC50/EC50"
(CAS#> K™c METHOD0 TRATION" (utJU
fluoranthene 5.08 . R M >70
(206-44-0)
acehaphthene 4.01 R U 1125
(83-32-9)
fluoranthene 5.08 S U 67
(206-44-0)
acenaphthene 4.01 FT M 589.4
(83-32-9)
phenanthrene 4.57 FT M 198,4
(85-01-8)
pyrene 4.92 FF M 66.49
(129-00-0)
fluoranthene 5.08 R M 51
(206-44-0)
fluoranthene 5.08 R M 63
(206-44-0)
fluorattthene 5,08 R M >70
(206-44-0)
fluoranlhene 5.08 R M 27
(206-44-0)
fluoranthene 5.08 R M 54
(206-44-0)
fluoranthene 5.08 R M 74
(206-44-0)
naphthalene 3,36 FT M 1390
LC50/EC50"
tumol/L)
>0.346
7.30
0.33
3.82
1.11
0.329
0.252
0.311
> 0.346
0.133
0.267
0.366 .
10.8
PAH
SPECIFIC
SMAV11
tomol/L)
> 0.346
7.30
0.33
3.82
1.11
0.329
0.252
0.311
>0.346
. 0.133
0.267
0.366
10.8
NORMALIZED
PAH SPECIFIC
SMAV1
>22.1
45.1
21.1
23.6
23.2
14.7
16.1
19.9
>22.1
8.5
17.0
23.3
16.1
SPECIES'
SMAV' GMAV*
(umo\/e*r) 22.1 >22.1 Boese etal.. 1997
i
Thursby elal., 1989a
30.8 30.8 Spehar etal., 1999
Swartz, 1991 a
Swartz, 199 la
Champlinand Poucher , 199^
19.0 19.0 Boese etal., 1997
19.9 19.9 Boese et al.. 1997
>22.1 >22.1 Boese etal.. 1997
8.5 8.5 Boese etal., 1997
17.0 17.0 Boese etal., 1997
23.3 23.3 Boese etal., 1997
16.1 16.1 Rice and Thomas, 1989
C-I2
-------
COMMON/SC1ENT1FI LIFE-
C NAME STAGE"
Eutilis sucklcyi
Grass shrimp, * X
Palaemonetes pugio
Gt iss shrimp, X
Pattiemonetes pugio
Grass shrimp. L
Palaemonetes pugio
Grass shrimp, A
Palaemonetes pugio
Grass shrimp, A
Palaemonetes pugio
Grass shrimp, J
Palaemonetes pugio
Sand shrimp, X
Crangon septcmspinosus
American Lobster, L
Homarus americanus
Hermit crab, A
Paqurus longicarpus
Slipper limpet, L
Crepidula fornicata
Sea urchin, E
Arbacia punaalata
Sea urchin, E
Arbacia punaalata
HABITAT"
E,W
E,W
E,W
E.W
E,W
E,W
E
-
E
W
W
W
PAH
TESTED LOG CONCEN-
. (CAS #) K™c METHOD0 TRATION"
(91-20-3)
naphthalene 3.36 S M
(91-20-3)
acenaphtliene 4.01 S U
(83-32-9)
acenaphtliene 4.01 R U
(83-32-9)
phenanthrene 4.57 R U
(85-01-8)
phenanthrene 4.57 FT M
(85-01-8)
fluoranthene 5.08 S U
(206-444)
acenaphthene 4.01 S U
(83-32-9)
fluoranthene 5.08 R U
(206-44-0)
phenanthrene 4.57 FT M
(85-01-8)
acenaphthene 4.01 R U
(83-32-9)
acenaphthene 4.01 S U
(83-32-9)
fluoranthene 5.08 S U
(206-44-0)
PAH NORMALIZED
SPECIFIC PAH SPECIFIC
LC50/EC50" LC50/EC50" SMAV" SMAV1
2350 18.3 18.3 27.2
676.8 4.39
1697 11.0 6.95 43.0
200.8 1.127
145.4 0.816 0.816 17.0
142 0.702 0.702 44.7
245 1,59 1.59 4.80
>2<50 1-29 1.29 81.9
(317)
163.7 0.918 0.918 19.2
3436 22.3 22.3 138
>3800 >24.6 >24.6 > 152
(8163)
>260 >l-3 >t-3 >82
(20000)
SPECJHS
SMAV1 GMAV"
(wiTiol/tv.) (Mnol/kv) REPERENCES
Tatem etal.,. 1978
1 Home etal., 1983;Thursby,
1991b
Thursby et al., I989a
Battelle Ocean Sciences,
Batielle Ocean Sciences,
30.7 30.7 Spehar etal., 1999
1987
1987
9.80 9.80 Horneetal., 1983;Thursby,
1991b
81.9 81.9 Spehar etal., 1999
19.2 19.2 Battelle Ocean Sciences,
138 138 Thursby et al. , 1989a
Thursby etal., 1989a
>117 >117 Spehar etal., 1999
1987
C-13
-------
COMMON/SCIENTIFI
CNAME
Pink salmon,
Oncorhynchus gorbuscha
Pink salmon,
Oncorhynd\us gorbuscha
I ink salmon,
Oncorhynchus gorbuscha
Pink salmon,
Ovcorhynchiis gorbuscha
Pink salmon,
Oncorhynchus gorbuscha
Sheepshead minnow,
Cyprinodon variegatus
Sheepshead minnow,
Cyprinodon variegaius
Sheepshead minnow,
Cyprinodon variegatus
Sheepshead minnow,
Cyprinodon variegatus
Sheepshead minnow,
C)>prinodon variegatus
Sheepshead minnow,
Cyprinodon variegatus
Sheepshead minnow,
Cyprinodon variegaius
LIFE-
STAGE*
Fry
Fry
Fry
Fry
Fry
J
J
A
I
J
j
J
HABITAT"
W
W
W
W
W
E.W
E,W
E,W
E,W
E.W
E.W
E.W
PAH
TESTED LOG CONCEN-
_JCAS#) IC^0 METHOD0 TRATJON*
naphthalene 3.36 FT M
(91-20-3)
naphthalene 3.36 FT M
(91-20-3)
naphthalene 3.36 FT M
(91-20-3)
naphthalene 3.36 FT M
(91-20-3)
naphthalene 3.36 FT M
(91-20-3)
acenaphlhene 4.01 S U
(83-32-9)
acenaphthene 4.01 R U
(83-32-9)
acenaphthene 4.01 FT M
(83-32-9)
phenanthrene 4.57 R U
(85-01-8)
phenanthrcne 4.57 FT M
(85-01-8)
pyrene 4.92 FT M
(129-00-0)
fluoranthene 5.08 S U
(206-44-0)
Kow
PAH NORMALIZED
SPECIFIC PAH SPECIFIC
LC50/EC5011 LC50/EC50P SMAV" SMAV1
(unfL) d.imol/1) (umoVD («mol/e~.)
960 7.49
900 7.02
990 7.72
1010 7.88
890 6.94 7.40 11.0
2200 14.3
>3800 >25 _ _
(50000)
3100 20.1 20.1 124
>245 >1.37
429.4 2.41 2.41 50.0
>132 >0,653 >0.653 >29.2
(>640)
>2dO >l-29
(>20000) . . •
SPECIES
SMAV' GMAV*
(wmol/E~.) (wmol/e^-1 REFERENCES
Rice and Thomas, 1989
Rice and Thomas, 1989
i
Rice and Thomas, 1989
Rice and Thomas, 1989
1 1 .0 1 1 .0 Rice and Thomas, 1 989
Heitmuller etal., 1981
Thursby etal., 1989a
Ward etal., 1981
Battelle Ocean Sciences, 1987
ttattellc Ocean Sciences, 1987
Champlin and Poucher, 1992b
Champlin and" Poucher, 1992a;
Spehar el al., 1999
Sheepshead minnow,
Cyprinodon variegatus
E.W fluorantliene 5.08 S
(206-44-0)
>1.29 >82L
(> 560000)
78.7 78.7 Helunuller etal., 1981 ;U.S
EPA, 1978
C-14
-------
PAH NORMALIZED
PAH • SPECIFIC PAH SPECIFIC SPECIES
COMMON/SCIENT1FI L1PE- TESTED LOO CONCEN- LC50/EC501' LC50/EC5011 SMAV11 SMAV1 SMAV'
GMAV*
CNAME
Inland silverside,
Menidia beryllina
*»
Inland silverside,
Menidia beryllina
Inland silverside,
Menidia beryllina
Inland silverside,
Menidia beryllina
Atlantic silverside,
Menidia menidia
Winter flounder,
STAGE* HABITAT"
X W
J W
J W
J W
A W
J
(CAS « K,,,,c
acenaphthenc 4.01
(83-32-9)
acenaphthene 4.01
(83-32-9)
pyrene 4.92
(192-00-0)
fluoranthene 5.08
(206-44-0)
phenanthrene 4.57
(85-01-8)
fluoranthene 5.08
(206^4-0)
• METHOD0
S
R
FT
S
FT
S
TRAT10NB
U
U
M •
U
M
M
(uzIL)
2300
>3800
(5564)
>132
(>188.17)
>260
108
>188
(wmol/U (Mmol/U)
14.9
>24.6 >19.2
> 0.653 > 0.653
>1.29 >1.29
0.606 0,606
>0.929 >0.929
(wmol/e/r)
>150
>29.2
>82.0
12.6
>59.2
(umol/E^ (wmo!/E«-) REFERENCES
Home ct al., 1983
Thursby et al., 1989a
i
Champlin and Poucher,
>65.8 _ Spehar etal., 1999
12.6 28.8 Battelie Ocean Sciences,
> 59 .2 > 59 .2 Spehar et al . , 1 999
1992
198'
ALife-stage: A = adult, J = juvenile, L = larvae, E = embryo. U = life-stage and habitat unknown, X = life-stage unknown but habitat known.
BHabitat: I = infauna, E = epibenthic, W « water column.
clog tfow: Predicted using SPARC (Karickoff et al, 1991).
DMethod: S= static, R = renewal, FT= flow-through.
E Concentration: U = unmeasured (nominal), M » chemical measured.
F Acute Values: 96 hour LC50 or EC50, except for Daphnia and Tanytarsus which are 48 hours duration.
GBolded acute values are the water solubilities of the PAH (Mackay et al., 1992). For these tests the acute values exceeded solubility. Therefore, solubilities are used instead
of the acute value for further calculations.
" PAH-specific SMAV: Geometric mean of the acute values by PAH and species.
1 PAH-specific SMAVs at a log Kw =1.0; calculated as antilog (log)0LC50 + 0.945log10Kow)/1000 (see Equation 2-33).
J Species SMAV: Geometric mean of ^Tow-normalized SMAVs for a species across PAHs.
K GMAV: Geometric mean of SMAVs for all species within a genus.
L Not used in calculations.
C-15
-------
-------
APPENDIX D. Comparison of PAH-specific equilibrium partitioning sediment guidelines (ESGs) derived from narcosis theory and the median response concentration of
benthic species for individual PAHs in spiked-sediment toxicily tests,
Common Name,
Scientific Name
Oligochaete,
Lwtibriculus variegatns
01 gochaete,
Lumbriculus variegatits
Oligochaete,
Umnodrilus hoffmeisteri
Oligochaete,
Umnodrilus hoffmeisteri
Oligochaete,
Umnodrilus hoffmeisteri
Cladoceran,
Daphnia niagna
Cladoceran,
Daphnia niagna
Cladoceran,
Daphnia magna
Amphipod,
Hyalella azteca
Amphipod,
Hyalella azteca
Amphipod,
Hyalella azteca
Amphipod,
Hyalella azteca
Amphipod,
Hyalella azteca
Chemical
pyrene
pyrene
phenanthrene
phenanthrene
pyrene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
Response
7 d LC50
7 d EC50-SA
10 d LC50
28 d EC25-R
28 d EC25-R
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
Median
Response
Cone/
fwa/sbc)
>9090
(61100)
>9090
(51400)
> 34300
(42500)
5790
8440
2380
955
3260
> 23900
(37649)
1250
1480
500
22000
(M2/20C)
694
694
593
593
694
704
704
704
704
704
704
704
704
Test-
Specific PAH-
ESGUrcv,B Specific
fUnitless) SMAVC GMAV" References11
>13.1 - - Kukkonen and Landrum, 1994
>13.1 - - Kukkonen and Landrum, 1994
>57.8 >S7.8 >57.8 Lotufo and Fleeger, 1 996
9.80 - - Lotufo and Fleeger, 1996
12.2 - - Lotufo and Fleeger, 1996
Suedeletal., 1993
Suedeletal., 1993
Suedeletal., 1993
Driscotl et al., 1997a
Suedeletal., 1993
Suedeletal., 1993
Suedeletal., 1993
31.3 . - - Harkey etal., 1997
D-l
-------
Common Name,
Scientific Name
Amphtpod,
Hyalella azteca
Amphipod,
Corophium spinicome
Amphipod,
Cumphium spinicome
Amphipod,
Leptocheirus plumulosus
Amphipod,
Leptocheirus plumulosus
Amphipod,
Leptocheints plumulosus
Amphipod,
Leptocheints plumulosus
Amphipod,
Leptocheirus plumulosus
Amphipod,
Leptocheirus plumulosus
Amphipod,
Rliepoxynius abronius
Amphipod.
RJiepoxynius abronius
Amphipod,
Rliepoxynius abronius
Amphipod,
Rliepoxynius abronius
Amphipod,
Chemical
fluoranthene
fluoranthene
fluoranthene •
acenapthene
acenapthene
acenapthene
phenanthrene
phenanthrene
phenanthrene
acenapthene
acenapthene
phenanthrene
phenanthrene
pyrene
Response
10 d LC50
. lOdLCSO
10 d LC50
lOdLCSO
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
lOdLCSO
10 d LC50
10 d LC50
Median
Response
Conc.A
(WE/HOC)
• -5130
2830
4390
10900
23500
8450
6870
8080
8180
2310
2110
3080
2220
1220
(we/coc)
704
704
704
489
489
489
593
593
593
489
489
593
593
694
Test-
Specific
ESOUr.cvlu
(Unitlcss)
7.29
4.02
6.23
22.3
48.1
17.3
11.59
13.63
13.8
4.72
4.31
5.19
3.74
1.76
PAH-
Specific
SMAV(: GMAV" References1"1
15.1 15.1 DeWttttal.,
Swartz et al.,
5.01 5.01 Swartz etal.,
Swartz etal.,
Swartz etal.,
26.4 - Swartz el al.,
Swartz et al.,
Swartz et al.,
13.0 18.5 Swartz etal.,
Swartz etal.,
4.51 • Swartz etal.,
Swartz et al.,
4.41 - Swartz et al.,
Swartz etal.,
19&9
1990
1990
1991a
1991a
1991a
1991a
199 la
1991a
1997
1997
1997
1997
, 1997
Riiepoxynius abronius
D-2
-------
Common Name,
Scientific Name
Amphipod,
Rhepoxynius abrotuus
Amphipod,
Rhepoxynius abrotu'Ss
Amphipod,
R tepoxynius abronius
Amphipod,
Rhepoxynius abronius
Amphipod,
Rhepoxynius abronius
Amphipod,
Rhepoxynius abronius
Amphipod,
Rhepoxynius abronius
Amphipod,
Rhepoxynius abronius
Amphipod,
Rhepoxynius abronius
Amphipod,
Rhepoxynius abronius
Amphipod,
Rhepoxynius abronius
Amphipod,
Rhepoxynius abronius
Amphipod,
Rhepoxynius abronius
Amphipod,
Eoliaustorius estuarius
Amphipod,
Chemical
pyrene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
acenapthene
acenapthene
Resoonse
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10dLC50
10 d LC50
10 d LC50
10 d LC50
Median
Response
Cone.*
2810
>4360
4410
3080
2230
3150
1890
2790
2320
1700
1030
2100
3310
1630
4180
COCMM.KM
694
704
704
704
704
704
704
704
704
704
704
704
704
489
489
D-3
Test-
Specific
ESGUpcv,*
(Unitless)
4.05
>6.19
6.26
4.38
3.17
4,50
2.68
3.96
3.30
2.41
1.47
2.98
4.70
. 3.33
8.55
PAH-
Specific
SMAVC GMAVIJ References6
2.67 - Swartzetal., 1997
DeWittetal.,
DeWittctal.,
DeWittetal.,
Swartzetal.,
DeWittetal.,
Swartzetal.,
DeWittetal.
Swartz et al.,
DeWittetal,,
Swartz et al.,
Swartzetal.,
3,56 3:67 Swartzetal.,
Swartzetal.,
Swartzetal.,
1992
1992
1992
1990
1992
1990
, 1992
1997
1989
1988
1990
1997
1991a
1991a
-------
Common Name, .
Srifiitlfic Name
Eoliaiistorius estuarius
Amphipod,
Eohaustorius estuarius
Amphipod, *
Eoliaustorius estuarius
Amphipod,
Eohaustorius estuarius
Amphipod,
Eoliaustorius estuarius
Amphipod,
Eoliaustorius estuarius
Amphipod,
Eoliaustorius estuarius
Amphipod,
Eoliaustorius estuarius
Midge,
Chironomus teutons
Midge,
Chironomus teutons
Midge,
Chironomus tentatis
Amphipod,
Diporeia sp.
Amphipod,
Dworeia so.
Chemical
acenapthene
phenanthrene
phenanlhrene
phenanthrene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
fluoranthene
pyrene
fluoranthene
ResDOiisc
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
10 d LC50
31dLC50
10 d LC50
Median
Response
Conc.A
(wc/uoc)
1920
4210
3760
4060
3100
3930
3570
1590
1740
(582
>9090
(147000)
> 23900
(29300}
^•OC/MHI.FCVI
fog/eoc)
489
593
593
593
704
704
704
704
704
704
694
704
Test-
Specific
ESGUrcviD
(Unitless)
3.93
7.10
6.34
6.85
4.40
5.59
5.07
-
'-
-
>13.1
>34.0
PAH-
Specific
SMAVC GMAV" References'5
4.82 - Swartzetal.,
Swartzctal.,
i
Swartzetal.,
6.75 - Swartzetal.,
DeWittetal.,
DeWittetal..
5.00 5.46 DeWittetal.,
Suedel et al.,
Suede! etal.,
Suedel eta!,.
Landrum et al
>34.0 >34.0 Driscoll et al.
1991a
1991a
1991a
1991a
1989
1989
1989
1993
1993
1993
., 1994
, 1997a
A Bolded median response concentration (acute) values are the COCiPAHl-M,I, based on the water solubilities of the PAH (Mackay et al., 1992). For these tests the interstitial water concentration at
the median response concentration exceeded solubility. Therefore,' solubilities are used instead of (he acute value for further calculations.
B Test-specific ESGUs: Quotient of the median response concentration G"g/goc) and COCiPAH|iPCVi (from Table 3-4),
c PAH-specific SMAV: Geometric mean of the test-specific ESGTUFCV, values from 10-d LC50 tests by species and PAH. Test-specific ESGTUFCVI values greater that solubility included only if
they are the sole 10-d LC50 for the species.
D GMAV: Geometric mean of the PAH-specific SMAVs for all species within a genus.
D-4
-------
E Spiked sediments from Suedel et al. (1993) were unlikely at equilibrium; i.e., organisms were tested lifter only 18 to 24 hours after spiking,
D-5
-------
-------
Appendix E. Teratogenic effects from laboratory exposure to PAHs.
Species
fathead minnow
(embryos),
Pimephales
promelas
freshwater
topminnows,
Poeciliopsis
monacha
Poeciliopsis
lucida
English sole
(embryos),
Parophrys
velulus
Rainbow trout
(embryos),
Oiicorhynchus
mykiss
Mode
of
Exposure
maternal
via water
water;
acetone carrier
maternal
via oral
aqueous from
BaP spiked to
sediment
Method PAH
lab; Anthracen
flow- e
through
lab; BaP
static
renewal
lab; BaP
wild-
caught
lab; BaP
Static
renewal
(7-10d)
Exposure
Cone
Associated
with Effect
6.66 ^ig/L
11.6MS/L
l,OOO^g/L
nominal;
1,250 ^g/L
was acutely
lethal
8,000 ^g/L
(8 mg/kg
force-fed)
0.21 Mg/L
measured
Exposure
Time
6 wks
3 wks
24 h
followed by
6 mo. of
monitoring
.
through to
36 d
post-hatch
Toxic Effects):
-yolk-sac malformations
-edema
-eye deformities
-increased AHH and
EROD activities
-malformation of tail
regions
-insufficient yolk-sac
-reduced fin-fold size
-reduced hatching
success
-nuclear pycnosis
-lack of body pigment
-insufficient yolk-sac
-abnormalities of eyes
-increased mortality (at
2.40 fig/L in aqueous)
-muscle necrosis
-abnormal mitosis in
eyes and brains
Tissue Cone
8.8a //g/g (eggs)
9.0 ,ug/g
converted from
35,7 nmol/g
wet wt.
5 1.2 and 263
Mg/g (eggs) -
avg, = 157;
Tissue cone, from 80
mg/kg i.p. maternal
injection
1.93^g/g(eggs),
12.34 jtg/g (alevins),
from exposure to 2.40
Mg/LBaP
Comments: Reference
i
Effects on embryos Hall and Oris,
incubated with solar 1991
ultraviolet light
radiation
Implied effect - Goddard et al . ,
increased AHH and 1987
EROD activity
indicative of
carcinogenic and
teratogenic metabolites
formed during
metabolism of BaP by
MFO-system
-Eggs maintained 1 1 Hose et al., 1981
days until yolk-sac
absorbed; static.
-Incidence of effect 4
times greater than
controls (Chai-square
df«3.81)
Poor control survival Hannah et al,,
(52% mortality) 1982;
Hose etal., 1984
E-l
-------
Species
Sand sole
(embryos),
Psettit htltys
melanostichus
Flathead sole
(embryos),
Hippoglossoide
s elassodon
English sole
(embryos),
Parophrys
vetulus
gizzard shad,
Dorosoma
cepedianum
Mode
of
Exposure
water;
static
water;
static
water
water via
treated
sediment
Exposure
Cone
Associated
Method PAH with Effect
lab BaP O.l^g/L
measured;
range
(0.08-0.12)
lab BaP 4.2 ^g/L
bound to decreasing to
bovine <0.05 f^g/L
serum (DL)
albumin
lab BaP 2.1 pgfL
measured
lab; BaP US^g/g
static sediment
(initial);
0.74 uglg
sediment
(mean of
days 4,8 and
15)
Exposure .
Time
through to
yolk-sac
absorption
(7-10d)
through to
yolk-sac
absorption
(7 -10 d)
through to
yolk-sa.c
absorption
(7 -10 d)
22 d
Toxic Effects):
-overgrowth of tissues
-arrested development
-twinning;
Effects only after 48 h,
i.e., during
organogenesis
-hatching success sig.
decrease
-nuclear pycnosis and
general disruption of-
neural and ocular
tissues
none-
none
Tissue Cone Comments:
•2. 1 pig/g effects only exhibited
wet weight in 5 % of animals;
average hatching
success of controls only
57% versus 28% BaP-
treated
very low hatching
success in controls and
experlmentals; 5.5 and
11.5%, respectively
-
BDL in all but 2 fish -40 ligated shad in 250
on day 4- . LH,0 with 4. 15 kg
(0.001 and 0.0002 sediment
Mg/g wet weight) -no sig. decline in
sediment cone.
after day 4.
Reference
Hoseeui., 1982
Hose et al., 1982
Hoseetal., 1982
Koloketal., 1996
E-2
-------
Species
gizzard shad,
Doroscwia
cepedlauun
estuarine
clams,
Rangia cuneata
estuarine
clams,
Rangia cuneata
coho salmon
(24 h Post
fertilization),
Oncorhynchus
kisutch
coho salmon,
(32 d post
fertilization),
Oncorliynctms
kisutclt
Mode
of
Exposure
water and/or
sediment
ingestion
water; acetone
carrier
water; acetone
carrier
water; 0.5%
DMSO
water; 0.5%
DMSO
Method
lab;
static
lab;
static
lab;
static
lab;
static
exposur
e then
flow-
through
lab;
static
exposur
e then
flow-
through
Exposure
Cone
Associated Exposure
PAH with Effect Time Toxic EffccUs):
BaP 1 .02 /Kg/g 22 days none
sediment
(initial);
0.63 ,ug/g
sediment
(mean of
days 4,8, and
15)
BaP 30.5 f^g/L 24 h none
BaP 30.5A
-------
Species
coho salmon,
(24 h Post
fertili '.ation),
Oncorhynchus
• kisutch
coho salmon,
(32 d post
fertilization),
Oncorhynchus
kisutch
Calif, grunion
(embryos),
Leuresthes
tennis
Mode
of
Exposure Method
water; 0.5% lab;
DMSO static
exposur
e then
flow-
through
water; 0.5% lab;
DMSO static
exposur
e then
flow-
through
water lab;
static
Exposure
Cone
Associated Exposure
PAH with Effect Time Toxic Effectfs):
BaP 25,000 Mg/L 24 h None
'
BaP 25,000 ,ug/L 24 h None
BaP measured: 15 days -reduction in % hatch
5 ng/L -lateral folding of tail
(steady- -absence of caudal fin
state): folds
Tissue Cone
0.54 decreasing to
0. 15 nmol/mg protien
from 2 to 68 d post
fertilization
4.47 decreasing to
0.33 nmol/mg protien
from 2 to 68 d post
fertilization
day 15: 0.992 ppm
(wet weight); 6.872
ppm (dry weight)
Comments: Reference
Cone, of BaP in tissue Ostrander et al .,
are not converted 1989
because wet weights
were not given; only
the mg protein/animal.
Can possibly borrow
weights from earlier
paper.
Cone, of BaP in tissue Ostrander et al . ,
are not converted 1989
because wet weights
were not given; only
the mg protein/animal.
Can possibly borrow, ...
weights from earlier
paper.
-steady slate
concentration Winkler et al.,
readied in 4 to 10 days 1983
(initial)
-hemorrhagic lesion or
congested vasculature in
caudal region
E-4
-------
Species
Calif, grunion
(embryos),
LeureSi hes
tennis
Calif, grunion
(embryos),
Leuresthes
tennis
Pacific herring
(embryos),
Ciupca pallasi
Mode
of
Exposure Method PAH
water lab; BaP
static
water lab; BaP
static
seawater lab; Field
contaminated static MixtureA
by contact
with oiled
gravel •
experiment 1;
less weathered
Exposure
Cone
Associated Exposure
with Effect Time
measured: 15 days
5-24 Mg/L
(steady
state); 24-
361 Mg/L
(initial)
measured: 15 days
869 ppb
(initial);
steady-state
not reached
9.1/x/L 16 days
Toxic Effcct(s):
-retarded growth (14d)
-sporadic heart beat
-displaced head relative
to yolk-sac
-absence of
melanophores near
lateral lines
-absence of lens
formation
-lesions as larvae
(above)
-retarded growth (14d)
-lateral curvature mid-
body
-absent melanophores
-unused yolk sac
-lesions as larvae
(above)
-yolk sac edema
Tissue Cone
day 15:
0.92 to 10.48 Mg/g
wet weight; 6.87 to
62.80 Mg/g (dry
weight)
day 15 - 19.98 ug/g
wet weight; 112.03
Mg/g dry weight
13.7 Mg/g wet weight
Comments: Reference
-steady state Winkler et al.,
concentration 1983
reached in 4 to 10 days
steady-state
concentration never Winkler etal.,
reached 1933
Crude Oil characterized Carls et al., 1999
for PAHs only;
concentrations of
individual PAHs not
given
E-5
-------
Species
Pacific herring
(embryos),
Clupt i pallasi
Mode
of
Exposure Method
seawater lab;
contaminated state
by contact
with oiled
gravel -
experiment 2;
more
weathered
Exposure
Cone
Associated
PAH with Effect
Field 0.41 ju/L to
Mixture* 0.72 ulL
Exposure
Time Toxic EffectbV: Tissue Cone
16 days - yolk sac edema 0.022 ^g/g wet
•pericardial edema weight
- skeletal, spinal, and
craniofacial
abnormalities
• anaphase aberration
Comments: Reference
Crude Oil characterized
for PAHs Only;
concentrations of
individual PAHs not
given
Artificially weathered Alaska North Slope crude oil.
E-6
-------
Appendix F. Carcinogenic effects from laboratory and field exposure to PAHs and PAH mixtures.
Species
Japaness Medaka,
Oryzia . atipes
(6- 10 d old)
Mode
of
Exposure Method
Water; Lab; static
dimethyl-
formamide
carrier.
Exposure Cone
Associated
PAH with Effect
BaP 261 Mg/L
Exposure
Time
2 x 6h, 1
week apart
Toxic Effcct(s):
Neoplastic lesions in
livers and other
tissues after 36 weeks
• 36%vsl%
(controls); 20 fish
with adenoma, 6 with
bepatocellular
carcinoma
Tissue
Cone Comments:
Exposures carried out
at26°Cinthedark;
concentration exceeds
saturation solubility of
BaP
Reference
Hawkins ei al,
1988;
Hawkins et al.,
1990
guppy.
Poedlia reticulata
(6-10 d old)
Water;
dimethyl-
formamide
carrier.
Lab; static
BaP
2 x 6h, 1
week apart
Rainbow trout
(fmgerlings),
Oncorhynchus iriyldss
Rainbow trout
(juvenile),
Oncorhynchus tnykiss
(10 mo)
oral
Lab
BaP
l.OOOppmper
feeding
12 and 18
months
ip injection
Lab
BaP
1 mg B(a)P in
0.4 ml PG
(I/month for 12
months)
18 months
(6 months
after final
injection)
Neoplastic lesions in
livers and other
tissues after 52 weeks
23%vsO%
(controls); 1 altered
foci, 5 adenoma, 4
with hepatoccllular
carcinoma
Incidence of
neoplasms on liver
15%(1.0/liver)atl2
months
25%(7.7/liver)atl8
months
Incidence of
neoplasms in various
organs"= 46% (x =>
7.7 tumors/organ)
Studies carried out
longer because
tumorigenic response in
guppy is slower than in
medaka
MFO info also
available
0% at 6 months
0% on other organs
Organs examined =
gonads, swim bladder,
liver, spleen, head and
trunk kidneys,
pancreas, intestines,
and stomach
Hawkins et al,
1988;
Hawkins et al.,
1990
Hendricks ct
al., 1985
Hendricks et
a!., 1985
F-l
-------
'•n'ji..iii!i!i . i.i1 1 1 'i.Try^ "^
Species
PoeciUopsis ludda and
Pocdliopsis monaclia
(1-7 months old)
PoeciUopsis ludda and
Poedliopsis monacha
(1-6 weeks old)
Bullheads
Japanese Medaka,
Poecilia retlculata
(6-10 d old)
Rainbow trout
(embryos),
Oncorhynchus tnykiss
Mode
of
Exposure
water;
acetone
carrier
water;
acetone
carrier
Direct skin
(river
sediment
extract)
Water via
Sediment
extract re-
dissolved in
acetone
injection of
sediment
extract into
yolk sac
Method
Lab: (multiple
exposures) 3
to 4 exposure
periods of S-
20 hours each
week
Lab: (multiple
exposures) 5
exposures
periods of 6
hours each
week
Lab
Lab
Lab
Exposure Gone
Associated
PAH with Effect
•7,12- 5 ppm (per
dimethylbehz(a)- exposure)
anthracene
*
7, 12- 5 ppm (per
dimethylbenz(a)- exposure)
anthracene
Field MixtureA 5 % RSE painted
once per week
Field Mixture0 1 82 ppb TPAH
Black River, OH
extract;
254 ppb TPAH
Fox River, WI
extract
Field Mixture0 Doses":
(Expl) 0.006 g
(Exp II) 0.012 g
0.006 g
n om p
Exposure
Time
7-8
months
(from
initial
exposure)
6-7
months
18 months
24 .h
1 year
Tissue
Toxic Effects): Cone
incidence of hepatic
tumors «• 48%
Incidence of hepatic
tumors » 41,8%
23% of survivors
hyperplastic
9% with multiple
paplllomas
hepatocellular
carcinoma - Black
River Ex. (2/15 fish);
Pancreatic-duct cell
adenoma • Fox River
Ex. (1/15 fish)
Hepatic carcinomas
(I) 8.9% (11/123)
(II) 8.1% (12/148)
4.0% (5/148)
1 ^ 9, nifi^]
Comments: Reference
only survivors Schukz and
examined » Schultz 1982
(55% mortality in 5
ppm treatment)
(13% mortality in
control)
22% mortality in Schultz and
treatment Schukz 1982
16% mortality in
control
Tumor-bearing livers
enlarged, yellow-white
to greenish and
granular.
Survival of control and Black, 1983
experimental fish was
31%.
No incidence of
carcinomas in controls Fabacher el al . ,
up to 270 days post- 1 99 1
exposure; one incidence
of lymphoma after 360
days of exposure.
Note; PCBs also Metcalfe et al
present sediment from 1988
Hamilton Harbour
3uffalo River, NY; total no. PAHs measured = 13, total no. of carcinogenic PAHs = 6.
Black River, OH. And Fox River, WI; full compliment of measured PAHs.
-lamilton Harbor, ON, Canada; total no. PAHs measured = 13, total no. of carcinogenic PAHs = 6.
Doses are calculated as gram equivalent wet weight of sediment represented by the volume of extract micro-injected into each trout sac-fry.
F-2
-------
FIGURES
*
Figure 2-1. Schematic diagram of the log10LC50 versus Iog10KoW relationship. At logJOArow = 0,
KQW — 1, the concentration in water equals the concentration in octanol.
Figure 2-2. Comparisons of (A) logJOKoW predicted by SPARC versus measured logloKow using
slow stir method and (B) reported log10LC50 values versus the aqueous solubility
estimated by SPARC. The diagonal line represents equality.
Figure 2-3. Ratios of (A) 48- to 96-hour LC50 values and (B) 24- to 96-hour LC50 values versus
togio^ow- The line in (B) is the regression used to correct the 24-hour LC50 to 96-
hour LC50.
Figure 2-4. Log10LC50 versus logloKOVf for the indicated species. The line has a constant slope of
-0.945. The y-intercepts vary for each species. Outliers are denoted by a plus symbol
Figure 2-5. Statistical comparison of slopes fitted to individual species to the universal slope of
-0.945 showing (A) the probability that the difference occurred by chance (filled bars)
and number of data points in the comparison (hatched bars) for each species in the
database, and (B) the deviations of the individual estimates from the universal slope.
Abbreviations are based on the first letter of the genus and either the first or second
letters of the species names given in Appendix A (e.g., Aae —Aedes aegypti and Am
=Ambystoma mexicanurri).
-------
Figure 2-6. Chemical class comparisons. (A) Residuals from the regression grouped by class with
mean ± 2 standard errors. (B) Residuals grouped by class with chemical Glass
corrections included in the regression.
Figure 2-7. The coefficient of variation of the estimated species-specific body burdens versus the
number of data points for that species (A), the log probability plot of the residuals (B),
and the residuals versus log1(XKi>w (C).
Figure 2-8. Log,0LC50 versus Iog10£ow for (A) L. macrochirus, (B) D. pulex, and (C) G. affinis.
The line connects the individual estimates of the LC50 values, including the chemical
class correction.
Figure 2-9. Comparison of target lipid model, line-of-fit and observed LC50 data for individual
PAHs, by species. The PAHs included are: naphthalene (3.36), 1-methylnaphthalene
(3.84), 2- methylnaphthalene (3.86), 2-chloronaphthalene (3.88), 1-chloronaphthalene
(3.88), acenaphthene (4.01), phenanthrene (4.57), pyrene (4.92), 9-methylanthracene
(5.01), fluoranthene (5.08). Number in parentheses = logloKOVf. Solid line and filled
symbols are for non-halogenated PAHs. Dotted lines and unfilled symbols are for the
halogenated (Le., chlorinated) PAHs. Plus symbols (+) denote outliers. Data axe
from Di Toro et al. (2000) and were used for toxicity test screening criteria.
Figure 2-10. Predicted and observed body burdens for five species.
Figure 2-11. Additivity of type I narcosis toxicity. Comparison of the observed TU concentrations
calculated from four studies to the predicted TU of 1.0. The number of chemicals in
-------
the tested mixtures are as indicated (adopted from Hermens et al., 1984).
*
Figure 3-1. GMAVs at a logjotf^ of 1.0 from water-only acute toxicity tests using freshwater and
saltwater genera versus percentage rank of their sensitivity. Freshwater genera are
indicated by open symbols and saltwater genera are indicated by closed symbols.
Figure 3-2. Probability distributions of FAY difference statistics to compare water-only toxicity
data from (A) freshwater versus saltwater genera and (B) benthic versus WQC.
Figure 4-1. Probability distribution of the 2ESGTUFCV for PAH mixtures in sediments from
coastal and estuarine locations in the United States (NOAA, 1991; Adams et al., 1996;
Anderson et al., 1996; Fairey et al., 19%; U.S. FJ>A, 1996a, b, 1998; Hunt et al.,
1998). Horizontal line indicates a toxic unit of 1.0.
Figure 4-2. Probability distribution of the 2ESGTUFCV for PAH mixtures in sediments from all the
j.
coastal and estuarine locations in the United States from Figure 4-1 (NOAA, 1991;
Adams et al., 1996; Anderson et al., 1996; Fairey et al., 1996; U.S. EPA, 1996a, b,
1998; Hunt et al., 1998). Horizontal line indicates a toxic unit of 1.0.
Figure 5-1. Percent mortality versus predicted interstitial water toxic units for six chemicals and
three sediments per chemical. Sediment types are indicated by open symbols (lowest
organic carbon content), doubled symbols (intermediate organic carbon content) and
filled symbols (highest organic carbon content),
Figure 5-2. Percent mortality versus predicted interstitial water toxic units for seven chemicals and
-------
three sediments per chemical. Sediment types are indicated by open symbols (lowest
organic carbon content), doubled symbols (intermediate organic carbon content) and
filled symbols (highest organic carbon content). Uncertainty error bars are represented
by~solid vertical lines (see U.S. EPA, 1999a for source of KQC values).
Figure 5-3. Percent mortality of Khepoxynius abronius in sediments spiked with acenaphthene,
phenanthrene, fluoranthene, or pyrene (see Appendix D for data).
Figure 5-4. Percentage rank, based on ESGTUFCV-,, of the sensitivities of genera of benthic
organisms from spiked sediment toxicity tests with individual PAHs.
Figure 5-5. Mortality of the amphipod, Rhepoxynius abronius, from tests 10-day sediment toxicity
tests with four parent PAHs separately (triangles) and in combination (circles) from
(Swartz et al., 1997) versus predicted sediment toxic units (PSTUs). PSTUs are the
sediment concentrations in each treatment divided by the predicted PAH-specific
*•
sediment LC50 values. The predicted PAH-specific sediment LC50 values are derived
from the interstitial water 10-day LC50 values from spiked sediment toxicity tests and
the universal narcosis slope to derive the PAH-specific critical tissue concentrations.
The geometric mean of the critical tissue concentrations, the universal narcosis slope
and the PAH-specific £QW and KQC were used to derive PAH-specific sediment LC50
values. For the mixture experiment the toxic units are the sum of the sediment
concentrations for each of the four PAHs divided by their respective PAH-specific
sediment LC50 values.
Figure 5-6. Response of H. azteca exposed for 10 days under flow-through conditions to sediment
-------
spiked with a mixture of high KQW PAH. Acute TUs were calculated based on
measured sediment PAH concentrations and the GMAV from Appendix C. Asterisks
%
indicate significant reduction compared to the control (a=0.05).
Figure 5-7. Response of H. azteca exposed for 28 days under flow-through conditions to sediment
spiked with a mixture of high KQW PAH. Acute TUs were calculated based on
measured sediment PAH concentrations and the GMAV from Appendix C. Asterisks
indicate significant reduction compared to the control (a=0.05).
Figure 5-8. Survival (after 28 days) and growth (after 10 days) of H. azteca expressed on .the basis
of measured PAH concentrations in tissues (lipid normalized). Effect concentrations
were calculated from acute water-only effect data for fluoranthene, methanol, ethanol,
and 2-propanone using the narcosis modeL Acute TUs were calculated by dividing the
lipid-normalized concentration of PAH in tissue by the GMAV, assuming lipid ~
octanol. The chronic threshold is represented by the GMAV divided by the ACR.
Data are from Di Toro et al. (1999).
Figure 5-9. Response of H. azteca exposed for 10 days (3 renewals) to sediment spiked with a
mixture of high KQW PAH. Acute TUs were calculated based on measured sediment
PAH concentrations and the GMAV from Appendix C. Asterisks indicate significant
reduction compared to the control (a=0.05).
Figure 5-10. Response of L. plumulosus exposed for 10 days under static conditions to sediment
spiked with a mixture of high K<,w PAH. Acute TUs were calculated based on
measured sediment PAH concentrations and the GMAV from Appendix C. Asterisks
-------
are treatments with effects significantly different from controls.
*
Figure 5-11. Amphipod (Ampelisca abdita) abundance versus SESGTUFCV. Vertical line is the ESG
of hO SESGTUpcv. Data are from the Virginian and Louisianian province EMAP
(U.S. EPA, 1996a,b) and the New York/New Jersey Harbor REMAP (Adams et al.,
1996).
Figure 6-1. Comparison of observed EESGTUFCV(TOT to observed SESGTUpcv.ia from 13 PAHs
(A) and SESGTUFCX23 from 23 PAHs (B) for the combined dataset including U.S.
EPA EMAP Louisian and Carolinian Provinces (N=490). The line shows the
resulting log-log linear regression equation.
Figure 6-2. Probability distribution of the (A) EESGTUFCVrJ3 and (B) SESGTUFCVJ3 values for
each sediment from the entire database. Symbols are as described in text.
Figure 6-3. BaP concentration of 539 sediment samples from the EMAP and Elliot Bay datasets
versus the £ESGUs of 34 PAHs (A) and a probability plot of these BaP concentrations
at an £ESGU = 1 (B). The solid line in both plots is the BaP critical sediment
concentration for teratogenic and carcinogenic effects
Figure 6-4. Anthracene concentration of 539 sediment samples from the EMAP and Elliot Bay
datasets versus the £ESGUs of 34 PAHs (A) and a probability plot of these
Anthracene concentrations at an £ESGU = 1 (B). The solid line in both plots is the
Anthracene critical sediment concentration for teratogenic effects (219 A*g/goc)-
-------
Figure 6-5. Computed solubilities of nine PAHs relative to their 25°C solubilities as a function of
temperature. The solid line is the least-squares regression line (Equation 6-1Q).
-------
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E
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o
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Log Aqueous Solubility (tnoI/L)
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Log ,0LC50 (mmol/L) Log ,0LC50 (mmol/L) Log 18LC50 (mmoI/L) Log JLC50 (mmoI/L)
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Log 1(LC50 (mmol/L) Log)0 LC50 (mmol/L) Log 10LC50 (mmol/L) Log IOLC50 (mraoI/L)
I
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t 1 1 1 1 1 1 1 1 1 1 1 1 1 1 1 t 1 1 t 1 1 1 1
-------
14-day LC50
Guppy
4-day LC50
Fathead Minnow
2-day LC50
D. magna
16-day NOEC
y//////////\ 50
71 mnonn I -' -* S •' •' •' f *' •' •' S •' •' •' / •' •' •' s .'•'•' S t ^_
v. magna ?// //// s/s / ///// s/// ////\ 25
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0.1
10
100
Toxic Units
No. of Chemicals Tested
-------
400
T
O Water column life stages
A Benthic life stages
Crassosfreal
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r o i
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r 1
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r .tfff*****^ i
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0.0001
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0.01 0.1 1 10 20 50 80 90 99 99.9 99.99
% Less Than or Equal To
-------
o
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100
80
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40
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—i 1—i—i—i i i i |
• Kepone
ffl Phenanthrene
+ Endrin .
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T Acenaphthene
A DDT
0.01
0.1
10
100
Predicted Interstitial Water Toxic Units
-------
i I I r i i
o
100
80
60
40
20
* Dicldrin
• Kepone
• Phenanthrene
• Endrin
• Fluoranthene
T Acenaphthene
A DDT
0.01
0.1
10
100
Predicted Sediment Toxic Units
-------
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100
80
60
40
20
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Leptocheirus
Eohaustorius
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Rhepoxynius
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10 20 30 40 50 60 70 80 90 100
Percentage Rank of Genera
-------
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-------
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