ES/ER/TM-96/R2 

Toxicological Benchmarks 

for Screening Potential 

Contaminants of Concern 

for Effects on Aquatic Biota:

1996 Revision

This document has been approved by the

K-25 Site Technical Information Office

for release to the public. Date: 
This report has been reproduced directly from the best available copy.

Available to DOE and DOE contractors from the Office of Scientific an d

Technical Information, P.O. Box 62, Oak Ridge, TN 37831; prices available

from 423-576-8401 (fax 423-576-2865).

Available to the public from the National Technical Information Service, U.S.

Department of Commerce, 5285 Port Royal Rd., Springfield, VA 22161.
ES/ER/TM-96/R2

Toxicological Benchmarks 

for Screening Potential

Contaminants of Concern

for Effects on Aquatic Biota:

1996 Revision

G. W. Suter II

C. L. Tsao

Date Issued—June 1996

Prepared by

Risk Assessment Program

Health Sciences Research Division

Oak Ridge, Tennessee 37831

Prepared for the

U.S. Department of Energy

Office of Environmental Management

under budget and reporting code EW 20

LOCKHEED MARTIN ENERGY SYSTEMS, INC.

managing the

Environmental Management Activities at the

Oak Ridge K-25 Site Paducah Gaseous Diffusion Plant

Oak Ridge Y-12 Plant Portsmouth Gaseous Diffusion Plant

 Oak Ridge National Laboratory

under contract DE-AC05-84OR21400

for the

U.S. DEPARTMENT OF ENERGY
iii

AUTHOR AFFILIATIONS

G. W. Suter II is a member of the Environmental Sciences Division, Oak Ridge Nationa l

Laboratory, Oak Ridge, Tennessee. C. L. Tsao is affiliated with the School of the Environment, Duke

University, Durham, North Carolina.
PREFACE

The purpose of this report is to present and analyze alternate toxicological benchmarks fo r

screening chemicals for aquatic ecological effects. This work was performed under Work Breakdown

Structure 1.4.12.2.3.04.05.04 (Activity Data Sheet 8304, “Technical Integration—Risk Assessment”).

Publication of this document meets a milestone for the Environmental Restoration (ER) Risk Assessment

Program. Since the prior edition of this report (Suter and Mabrey 1994), both the U.S. Environmental

Protection Agency Office of Solid Waste and Emergency Response and EPA Region IV have developed

sets of screening benchmarks for water. This report includes those values and updates the othe r

benchmarks that were presented in the last edition. 
CONTENTS

AUTHOR AFFILIATIONS ........................................................ iii

PREFACE ...................................................................... v

TABLES ....................................................................... ix

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

EXECUTIVE SUMMARY ........................................................ xiii

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

2. METHODS FOR DERIVING BENCHMARKS ...................................... 1

2.1 TYPES OF BENCHMARKS ................................................ 1

2.2 WATER QUALITY CRITERIA ............................................. 2

2.3 TIER II VALUES ........................................................ 13

2.4 LOWEST CHRONIC VALUES ............................................ 14

2.5 ESTIMATED LOWEST CHRONIC VALUES ................................ 14

2.6 TEST EC20s ............................................................ 14

2.7 ESTIMATED TEST EC20s ................................................ 15

2.8 SENSITIVE SPECIES TEST EC20s ......................................... 15

2.9 POPULATION EC25s .................................................... 15

2.10 ECOTOX THRESHOLDS ................................................ 16

2.11 REGION IV SCREENING VALUES ....................................... 16

2.12 BACKGROUND CONCENTRATIONS .................................... 16

3. CHEMICAL-SPECIFIC INFORMATION ......................................... 22

3.1 INORGANICS .......................................................... 23

3.2 ORGANICS ............................................................ 27

4. APPLICATION OF BENCHMARKS ............................................. 34

5. REFERENCES ............................................................... 35

Appendix A DATA USED FOR TIER II CALCULATIONS ............................ A-1

Appendix B METHODS FOR DERIVATION OF TIER II VALUES ..................... B-1

Appendix C TABLE SHOWING CONCENTRATIONS ESTIMATED 

TO CAUSE A 20% REDUCTION IN THE RECRUIT 

ABUNDANCE OF LARGEMOUTH BASS, WITH UPPER 

AND LOWER 95% CONFIDENCE BOUNDS ........................... C-1
TABLES

1 Summary of conventional benchmarks for priority contaminants in fresh water ............ 3

2 Summary of alternative benchmarks for priority contaminants in fresh water based

on levels of chronic effects ...................................................... 9

3 Summary of OSWER threshold values for aquatic life (EPA 1996) 

and Region IV screening values for freshwater surface water .......................... 17

A.1 Data and calculated results for derivation of Tier II values ........................... A-3

B.1 Factors for estimation of the Tier II values ....................................... B-6

C.1 Concentrations estimated to cause a 20% reduction in the recruit abundance 

of largemouth bass, with upper and lower 95% confidence bounds .................... C-3
ACRONYMS

ACRs acute chronic ratios

ARARs applicable or relevant and appropriate requirements

CERCLA Comprehensive Environmental Response, Compensation, and Liability Act

CV Chronic Value

EC50 median effective concentration

EPA U.S. Environmental Protection Agency 

ETs Ecotox Thresholds

FACR Final Acute-Chronic Ratio

FAV Final Acute Value

FCV final chronic value

GLWQI Great Lakes Water Quality Initiative

GMAV genus mean acute value

LC50 median lethal concentration

LOEC Lowest Observed Effect Co

MATC Maximum Acceptable Toxicant Concentration

NAWQC National Ambient Water Quality Criteria

NOEC No Observed Effect Concentration

OSWER Office of Solid Waste and Emergency Response

RI Remedial Investigation

SACR secondary acute chronic ratio

SAV Secondary Acute Values

SCV Secondary Chronic Value

SS sensitive species

SVs screening values
EXECUTIVE SUMMARY

One of the initial stages in ecological risk assessment of hazardous waste sites is the screening of

contaminants to determine which, if any, of them are worthy of further consideration; this process i s

termed contaminant screening. Screening is performed by comparing concentrations in ambient media

to benchmark concentrations that are either indicative of a high likelihood of significant effects (upper

screening benchmarks) or of a very low likelihood of significant effects (lower screening benchmarks).

Exceedance of an upper screening benchmark indicates that the c hemical in question is clearly of concern

and remedial actions are likely to be needed. Exceedance of a lower screening benchmark indicates that

a contaminant is of concern unless other information indicates that the data are unreliable or th e

comparison is inappropriate. Chemicals with concentrations below the lower benchmark are not o f

concern if the ambient data are judged to be adequate.

This report presents potential screening benchmarks for protection of aquatic life fro m

contaminants in water. Because there is no guidance for screening benchmarks, a set of alternativ e

benchmarks is presented herein. The alternative benchmarks are based on different conceptua l

approaches to estimating concentrations causing signifi cant effects. For the upper screening benchmark,

there are the acute National Ambient Water Quality Criteria (NAWQC) and the Secondary Acute Values

(SAV). The SAV concentrations are values estimated with 80% confidence not to exceed the unknown

acute NAWQC for those chemicals with no NAWQC. The alternative chronic benchmarks are th e

chronic NAWQC, the Secondary Chronic Value (SCV), the lowest chronic values for fish and daphnids,

the lowest EC20 for fish and daphnids from chronic toxicity tests, the estimated EC20 for a sensitive

species, and the concentration estimated to cause a 20% reductio n in the recruit abundance of largemouth

bass. It is recommended that ambient chemical concentrations be compared to all of these benchmarks.

If NAWQC are exceeded, the chemicals must be contaminants of concern because the NAWQC ar e

applicable or relevant and appropriate requirements (ARARs). If NAWQC are not exceeded, but other

benchmarks are, contaminants should be selected on the basis of the number of benchmarks exceeded

and the conservatism of the particular benchmark values, as discussed in the text.

To the extent that toxicity data are available, this report presents the alternative benchmarks fo r

chemicals that have been detected on the Oak Ridge Reservation. It also presents the data used t o

calculate the benchmarks and the sources of the data. It compares the benchmarks and discusses their

relative conservatism and utility.

This report supersedes a prior aquatic benchmarks report (Suter and Mabrey 1994). It adds two

new types of benchmarks. It also updates the benchmark values where appropriate, adds some ne w

benchmark values, replaces secondary sources with primary sources, and provides more complet e

documentation of the sources and derivation of all values.
1. INTRODUCTION

An important early step in the assessment of ecological risks posed by a contaminated site is the

screening of contaminants. In many cases, concentrations in water will be reported for more than 100

chemicals, most of which will be reported as undetected at some defined limit of detection. The assessor

must decide which of the detected chemicals constitute an ecological hazard and which of the undetected

chemicals may pose a hazard at concentrations below the reported detection limits. This screening is

done by comparing the reported concentrations to toxicological benchmarks. If concentrations of a

chemical exceed its benchmark for a particular medium, then it is worthy of further measurement and

assessment. If not, it can be ignored (assuming that the analytical data are adequate). 

In practice, a series of benchmarks of differing conservatism may be used. Exceedance of an upper

screening benchmark would suggest a severe hazard and a need for urgent action. Nonexceedance of all

lower screening benchmarks would suggest no hazard. Exceedance of an increasing number o f

benchmarks would constitute increasing evidence of the need for measurement and assessment. I n

addition to providing a better indication of the magnitude of the hazard, the use of multiple benchmarks

provides information about the nature of the hazard which can be used in development of the conceptual

model and in planning the Remedial Investigation (RI). For example, is the chemical at concentrations

that are toxic to only daphnids, to daphnids and fish, to fish and aquatic plants, etc.? Are they a t

concentrations that have been demonstrated to be toxic or do they exceed only benchmarks that include

conservative factors?

The purpose of this report is to present and analyze alternate toxicological benchmarks fo r

screening chemicals for aquatic ecological effects. Since the prior edition of this report (Suter an d

Mabrey 1994), both the U.S. Environmental Protection Agency (EPA) Office of Solid Waste an d

Emergency Response (OSWER) and EPA Region IV have developed sets of screening benchmarks for

water. This report includes those values and updates the other benchmarks that were presented in the

last edition.

This compilation is limited to chemicals that have been detected on the Oak Ridge Reservation and

to benchmarks derived from studies of toxic effects on fresh water organisms. The list of chemical s

detected on the Oak Ridge Reservation includes 45 metals and 105 industrial chemicals. Only fou r

pesticides occur on the list, and those are persistent and wide-spread (chlordane, DDT, heptachlor, and

lindane).

2. METHODS FOR DERIVING BENCHMARKS

2.1 TYPES OF BENCHMARKS

The simplest screening benchmarks are toxicity test endpoints. A test endpoint is a statisticall y

derived numeric summary of the results of a toxicity test. Test endpoints can be calculated in two ways.

First, a level of effect can be estimated by fitting a function such as the probit or logit to th e

concentration-response data to derive a concentration-response model. Then by inverse regression, a

concentration can be estimated that causes a particular level of effect such as the median letha l

concentration (LC50). Second, hypothesis testing statistics can be used to determine whether each of

the tested concentrations caused an effect that was statistically significantly different from the controls.

The lowest concentration causing such an effect is termed the Lowest Observed Effect Concentration
2

(LOEC); the highest concentration for which there were no such effects is termed the No Observed Effect

Concentration (NOEC). The geometric mean of the LOEC and NOEC is te rmed the Chronic Value (CV)

and was formerly termed the Maximum Acceptable Toxicant Concentration (MATC).

Toxicity tests are conventionally divided into acute and chronic tests. Standard acute aquati c

toxicity tests are 48 or 96 hours in duration and use juvenile or adult organisms; the test endpoints are

the median lethal concentration (LC50) or median effective concentration (EC50) for death or som e

equivalent effect (e.g., immobilization). Standard chronic tests include all or most of the lifecycle of the

test organisms, and they include observations of growth, deformities, and reproductive success as well

as lethality. The standard endpoint for chronic tests is the CV.

Another important distinction is between response-specific and integrative endpoints .

Conventionally, NOECs and LOECs are calculated for each response parameter, and the results for the

most statistically sensitive parameter are reported. Because effects on populations and ecosystems are

a result of the integrated effects of the toxicant on all life stages, it is more sensible to integrate th e

responses in the test when calculating the test endpoint. Integrative endpoints may be simple arithmetic

combinations of effects such as the proportional mortality across all tested life stages or populatio n

parameters derived from simple models such as the intrinsic rate of natural increase, r. 

Benchmarks may be combinations of multiple test endpoints. An example is the chronic NAWQC,

which are derived from at least eight LC50s and three CVs.

Finally, benchmarks may be derived by using mathematical models to simulate an assessmen t

endpoint, a specific environmental characteristic that is valued and is at risk due to the contamination

or disturbance that is being assessed (Suter 1989). For example, in this study we present concentrations

estimated to correspond to a 20% reduction in recruit abundance for largemouth bass ( Micropterus

salmoides) because production of fish, particularly game fish, is an assessment endpoint for Oak Ridge

Reservation ecological risk assessments (Suter et al. 1992).

Conventional aquatic benchmarks, which are based on regulatory criteria or standard test endpoints

used to derive criteria, are listed in Table 1. Unconventional aquatic benchmarks, which are based on

levels of effects on integrative endpoints, are listed in Table 2.

2.2 WATER QUALITY CRITERIA

The National Ambient Water Quality Criteria (NAWQC) are appl icable or relevant and appropriate

requirements (ARARs); therefore, they provide the basis for the screening benchmarks for contaminants

in water. The acute NAWQC are calculated by the EPA as half the Final Acute Value (FAV), which is

the fifth percentile of the distribution of 48- to 96-hour LC50 values or equivalent median effectiv e

concentration (EC50) values for each criterion chemical (Stephan et al. 1985). The acute NAWQC are

intended to correspond to concentrations that would cause less than 50% mortality in 5% of expose d

populations in a brief exposure. They may be used as a reasonable upper screening benchmark because

waste site assessments are concerned with sublethal effects and largely with continuous exposures, rather

than the lethal effects and episodic exposures to which the acute NAWQC are applied. The chroni c

NAWQC are the FAVs divided by the Final Acute-Chronic Ratio (FACR), which is the geometric mean

of quotients of at least three LC50/CV 
3

Table 1. Summary of conventional benchmarks for priority contaminants in fresh water (all values in micrograms per liter)

Chemical

NAWQ Criteria Tier II Values Lowest Chronic Value for:

 

Acute Chronic Secondary Secondary Fish Daphnids Non- Aquatic All OrganAcute Chronic Daphnid Plants isms

Value Value Invertebrates

Aluminum 750 87 3,288 1,900 460 460

Ammonia pH and temperature 1.7 630 2,400 1.7

dependent 

Antimony 180 30 1,600 5,400 610 610 i i

Arsenic III 360 190 2,962 914.1 2,320 914.1

Arsenic V 66 3.1 892 *450 48 48

Barium 110 4.0

Beryllium 35 0.66 *57 5.3 100,000 5.3

Boron 30 1.6 8,830 8,830

Cadmium 3.9+ 1.1+ 1.7 0.15 2 0.15

Calcium 116,000 116,000

Chromium III 1,700+ 210+ 68.63 <44 397 <44

Chromium VI 16 11 73.18 6.132 2 2

Cobalt 1500 23 290 5.1 5.1

Copper 18+ 12+ 3.8 0.23 6.066 1 0.23

Cyanide 22 5.2 7.8 18.33 30 7.8

Iron 1,000 1,300 158 158

Lead 82+ 3.2+ 18.88 12.26 25.46 500 12.26

Lithium 260 14

Magnesium 82,000 82,000

Manganese 2,300 120 1780 <1,100 <1,100

Mercury, inorganic or total 2.4 1.30 <0.23 0.96 5 <0.23 a

Mercury, methyl 0.099 0.0028 0.52 <0.04 0.8-4.0 <0.04

Molybdenum 16,000 370 880 880
Table 1. (continued)

Chemical

NAWQ Criteria Tier II Values Lowest Chronic Value for:

 

Acute Chronic Secondary Secondary Fish Daphnids Non- Aquatic All OrganAcute Chronic Daphnid Plants isms

Value Value Invertebrates

45

Nickel 1,400+ 160+ <35 <5 128.4 5 <5

Potassium 53,000 53,000

Selenium 20 5 88.32 91.65 100 88.32

Silver 4.1+ 0.36 0.12 2.6 30 0.12

Sodium 680,000 680,000

Strontium 15,000 1,500 42,000 42,000

Thallium 110 12 57 130 100 57

Tin 2,700 73 350 350

Uranium 46 2.6 *142 *142

Vanadium 280 20 80 1,900 80

Zinc 120+ 110+ 36.41 46.73 >5,243 30 30

Zirconium 310 17 *548 *548

Organics

Acenaphthene 80 23 74 *6,646 227 520 74 e e

Acetone 28,000 1,500 *507,640 1,560 *507,640

Anthracene 13 0.73 *0.09 <2.1 *0.09

Benzene 2,300 130 >98,000 525,000 525,000

Benzidene 70 3.9 *134 *134

Benzo(a)anthracene 0.49 0.027 *0.65 *0.65

Benzo(a)pyrene 0.24 0.014 *0.30 *0.30

Benzoic acid 740 42 *12,976 *12,976

Benzyl alcohol 150 8.6 *589 *589

BHC (lindane) 2 0.08 14.6 14.5 3.3 500 3.3
Table 1. (continued)

Chemical

NAWQ Criteria Tier II Values Lowest Chronic Value for:

 

Acute Chronic Secondary Secondary Fish Daphnids Non- Aquatic All OrganAcute Chronic Daphnid Plants isms

Value Value Invertebrates

6

BHC (other) 39 2.2 *95 *95

Biphenyl 14f

Bis(2-ethylhexyl)phthalate 27 3.0 912 912

4-Bromophenyl phenyl ether 1.5f

Butylbenzyl phthalate 19f

2-Butanone 240,000 14,000 *282,170 *1,394,927 *282,170

Carbon disulfide 17 0.92 *9,538 *244 *244

Carbon tetrachloride 180 9.8 1,970 *5,580 1,970

Chlordane 2.4 0.17 1.6 16 1.09 1.09 a

Chlorobenzene 1,100 64 *1,203 *15,042 224,000 *1203

Chloroform 490 28 1,240 *4,483 1,240

DDD p,p' 0.19 0.011 *1.69 *1.69

DDT 1.1 0.013 0.73 *0.016 0.3 0.3 bf c

Decane 880 49 *7,874 *7,874

Di-n-butyl phthalate 190 35 717 697 697 d

Diazinon 0.17 0.043 g g

Dibenzofuran 66 3.7 *1,003 *1,003

1,2-Dichlorobenzene 260 14 f f

1,3-Dichlorobenzene 630 71 f f

1,4-Dichlorobenzene 180 15 f f

1,1-Dichloroethane 830 47 *14,680 *14,680

1,2-Dichloroethane 8,800 910 41,364 15,200 15,200

1,1-Dichloroethene 450 25 >2,800 *4,720 >798,000 >2,800
Table 1. (continued)

Chemical

NAWQ Criteria Tier II Values Lowest Chronic Value for:

 

Acute Chronic Secondary Secondary Fish Daphnids Non- Aquatic All OrganAcute Chronic Daphnid Plants isms

Value Value Invertebrates

7

1,2-Dichloroethene 1,100 590 *9,538 *9,538

1,3-Dichloropropene 0.99 0.055 244 *805 4,950 244

Dieldrin 0.18 0.062 e e

Diethyl phthalate 1,800 210 85,600 85,600

Di-n-octyl phthalate 3,822 708 708

Endosulfan, all isomers 0.051f

Endrin 0.095 0.061 e e

Ethyl benzene 130 7.3 >440 *12,922 >438,000 >440

Fluoranthene 33.6 6.16 30 15 54400 15 e e

Fluorene 70 3.9 f f

Heptachlor 0.125 0.0069 1.26 *3.18 26.7 1.26 g,h b,g

Hexachloroethane 210 12 e f

Hexane 10 0.58 *65,712 *65,712

2-Hexanone 1,800 99 *32,783 *32,783

Methoxychlor 0.019f

1-Methylnaphthalene 37 2.1 *526 *526

4-Methyl-2-pentanone 2,200 170 77,400 77,400

2-Methylphenol 230 13 *489 *1,316 *489

Methylene chloride 26,000 2,200 108,000 *42,667 *42,667

Naphthalene 190 12 620 *1,163 33,000 620

4-Nitrophenol 1,200 300 *481 7,100 4190 *481

N-Nitrosodiphenylamine 3,800 210 *332 *1,042 *332

2-Octanone 150 8.3
Table 1. (continued)

Chemical

NAWQ Criteria Tier II Values Lowest Chronic Value for:

 

Acute Chronic Secondary Secondary Fish Daphnids Non- Aquatic All OrganAcute Chronic Daphnid Plants isms

Value Value Invertebrates

8

PCBs total 2.0 0.14 0.2 2.1 0.8 0.144 0.1

 Aroclor® 1221 5.0 0.28 *60 *60

b

 Aroclor® 1232 10 0.58 *124 — *124

 Aroclor® 1242 1.2 0.053 9.00 4.9 300 4.9

 Aroclor® 1248 1.4 0.081 —

 Aroclor® 1254 0.60 0.033 2.9 0.1 0.1

 Aroclor® 1260 1,700 94 <1.3 — 2.3

Pentachlorobenzene 8.4 0.47 f f

1-Pentanol 2,000 110 *30,493 *30,493

Phenanthrene 30 6.3 200 200 e e

Phenol 3,600 110 <200 *2,005 20,000 <200 g g

2-Propanol 130 7.5 *590 *590

1,1,2,2 Tetrachloroethane 2,100 610 2,400 9,900 136,000 2,400

Tetrachloroethene 830 98 840 750 >816,000 750

Tetrachloromethane 4,400 240 f f

Toluene 120 9.8 *1,269 *25,229 245,000 *1,269

Tribromomethane 2,300 320 f f

1,2,4-Trichlorobenzene 700 110 f f

1,1,1-Trichloroethane 200 11 *3,493 >669,000 *3,493

1,1,2-Trichloroethane 5,200 1,200 9,400 18,400 9,400

Trichloroethene 440 47 11,100 *7,257 *7,257

Vinyl acetate 280 16 *810 *810

Xylene 230 13 *62,308 *62,308

m-Xylene 32 1.8 f f
Table 1. (continued)

Notes:

+ Hardness dependent criterion normalized to 100 mg/L

* Numbers preceded by * are estimates. Methods of estimation are described in the text.

 The chronic NAWQC for chlordane (0.0043 g/L) and mercury (0.012 μg/L), are based on the final residue values. FCVs are used as benchmarks to protect aquatic life. a

 The chronic NAWQC for DDT (0.001 g/L), total PCBs (0.014 μg/L), and heptachlor (0.0038 μg/l) are is based on the final residue values; for benchmarks to protect aquatic b

life, we use SCVs.

 The CV for DDT in Jarvinen et al. 1977 of 0.9 μg/l is the arithmetic mean of the NOEC and LOEC. We used the geometric mean which is 0.73. c

 For fish di-n-butyl phthalate lowest CV, the geometric mean of the measured concentrations for the NOEC and LOEC rather than the nominal concentrations used by the authors d

(McCarthy and Whitmore 1985) was used herein.

 These numbers are Final Acute Values and Final Chronic Values calculated by the EPA for use in the derivation of sediment quality criteria (EPA 1993b). e

 Values calculated for OSWER (1996). f

 Values calculated by the Great Lakes Water Quality Initiative (EPA 1993d). g

 SAV was calculated by the Great Lakes Water Quality Initiative because some data used to derive FAV were questionable (EPA 1992).

h

 These values are draft FAV and FCV values (EPA 1988b). I
9

Table 2. Summary of alternative benchmarks for priority contaminants in fresh water based

on levels of chronic effects (all values in micrograms per liter)

Chemical Species Test EC

Lowest Test EC for: 20

Sensitive Population 

EC20

20

Fish Daphnids

Aluminum 4,700 540 75

Antimony 2,310 1,900 79

Arsenic III 2,130 633 55 1,995

Arsenic V 1,500 >932 185

Barium

Beryllium *148 3.8 21

Boron 7,000

Cadmium 1.8 0.75 0.013 4.3 a

Calcium

Chromium III 89 8.44 126

Chromium VI 51 0.5 0.266 316

Cobalt 810 <4.4 3.98

Copper 5 0.205 0.26 8.6

Cyanide 5.3 1.17 11

Fluorine *5,336 3,706 1,080

Iron 16

Lead 22 0.35 71

Magnesium

Manganese 1,270 <1,100 112

Mercury, inorganic 0.87 0.87 0.18 0.32

Mercury, methyl <0.03 0.87 0.28

Molybdenum 360

Nickel 62 45 11 215 a

Potassium

Selenium 40 25 2.60

Silver 0.20 <0.56 0.14 0.32 a

Sodium

Strontium

Thallium 81 64 67
Table 2. (continued)

10

Chemical Species Test EC

Lowest Test EC for: 20

Sensitive Population 

EC20

20

Fish Daphnids

Tin

Uranium *455 27

Vanadium 41 430 32

Zinc 47 21 80

Zirconium *2,396 251

Organics

Acenaphthene <197

Acetone *161,867 23,714

Anthracene *0.35 >8.2

Benzene 21 229

Benzidene *158 68

Benzo(a)anthracene

Benzo(a)pyrene >2.99

Benzoic acid *7,409 1,259

Benzyl alcohol *550 375

BHC (lindane) <1.1 11 0.11

BHC (other)

Bis(2-ethylhexyl)phthalate >54 <3 50

2-Butanone *98,772 17,783

Carbon disulfide *5719 1,000

Carbon tetrachloride 65 224

Chlordane <0.25 12.1 0.50 0.71

Chlorobenzene 1,002 165

Chloroethane

Chloroform 8,400 562

DDD p,p' *3.99 0.61

DDT 0.35 0.008

Decane
Table 2. (continued)

11

Chemical Species Test EC

Lowest Test EC for: 20

Sensitive Population 

EC20

20

Fish Daphnids

Di-n-butyl phthalate 270 500 251

Dibenzofuran

1,1-Dichloroethane *8,219 1,585

1,2-Dichloroethane 29,000 <11,000 1,259

1,1-Dichloroethene 447

1,2-Dichloroethenes *5,719

1,3-Dichloropropene *350 40

Diethyl phthalate 1,000

Di-n-octyl phthalate <100 310 1,995

Ethyl benzene 398

Fluoranthene 32

Heptachlor 0.86 0.004 0.1

Hexane *28,995

2-Hexanone *16,155 1,259

1-Methylnaphthalene *500 31.62

4-Methyl-2-pentanone 1,585

2-Methylphenol *470 74

Methylene chloride 410 1,259

Naphthalene 450 >600 1,000

4-Nitrophenols *464 5,000 60

N-Nitrosodiphenylamine *339 40

3-Octanone *3571

PCBs total 0.4 1.2 0.63

 Aroclor® 1221 *80 10

 Aroclor® 1232 *148 16

 Aroclor® 1242 <2.9 1.58

 Aroclor® 1248 0.4 2.5 1.26

 Aroclor® 1254 0.52 1.2 0.63

 Aroclor® 1260 2.1 316

1-Pentanol *15,200 3,548
Table 2. (continued)

12

Chemical Species Test EC

Lowest Test EC for: 20

Sensitive Population 

EC20

20

Fish Daphnids

Phenanthrene 110

Phenol <230 4,467

2-Propanol *35,381 3,162

1,1,2,2-Tetrachloroethane 1,400 <420 1,585

Tetrachloroethene 500 510 50

Toluene <26 200

1,1,1-Trichloroethane *2,457 1,300 251

1,1,2-Trichloroethane 14,800 13,000 15,849

Trichloroethene 5758 232

Vinyl acetate *718 108

Xylene 2680

Notes:

* Numbers preceded by * are estimates. Methods of estimation are described in the text.

 Study LC50's were used rather than species mean LC50s so water hardness would correspond to EC20 values. a

ratios from tests of different families of aquatic organisms (Stephan et al. 1985). It is intended t o

prevent significant toxic effects in chronic exposures and is used in this assessment as one possible lower

screening benchmark. The NAWQC are listed in Table 1.

NAWQC for several metals are functions of water hardness; the criteria are lower for lowe r

hardness levels. The criteria for 100 mg/L hardness as reported by the EPA are presented in this report.

That hardness is near the lower end of the range of hardness values reported for the Oak Ridg e

Reservation, so it is moderately conservative. For sites with different water hardnesses, site-specifi c

criteria should be calculated. The formulas for hardness correction are listed in the discussions o f

individual chemicals.

Many readers will note that the EPA's compilations of NAWQC contain values for many chemicals

that have no NAWQC listed herein (EPA 1986b); the EPA lists lowest CVs for those chemicals fo r

which there is not enough data to calculate a criterion but for which there is at least one CV. Lowes t

CVs are treated as a separate category of benchmarks in this compilation. 

Some chronic NAWQC are based on protection of humans or other piscivorous organisms rather

than protection of aquatic organisms. Those criteria are not included herein because screening for risks

to wildlife or humans is performed by other methods. However, if sufficient data were available t o

calculate a final chronic value (FCV) for those chemicals, then the FCV are presented in place of th e

chronic NAWQC in Table 1, and its derivation is noted.

For particular chemicals, the lower screening benchmark could be lower than the chronic NAWQC

for any one of the following reasons. First, the chronic NAWQC are based on a threshold for statistical

significance rather than biological significance. In some chronic tests, because of highly variable results,

the statistical threshold corresponds to greater than 50% effect on a response 
13

parameter (Stephan and Rogers 1985, Suter et al. 1987). Second, not all important responses ar e

included in the subchronic toxicity tests that are used to calculate many chronic NAWQC. In particular,

effects on fecundity, which is the most sensitive response parameter on average in fish toxicity test s

(Suter et al. 1987), are often not included. Third, the chronic NAWQC are based on the mos t

statistically sensitive of the measured response parameters in each chronic or subchronic test. Therefore,

cumulative effects over the lifecycle of fish and invertebrates are not considered. Fourth, the NAWQC

are set at a level that protects "most species most of the time." Finally, many of the NAWQC have not

been revised since 1980 so they do not incorporate recent data that are included in the calculation o f

other benchmarks. These concerns are supported by the recent finding that nickel concentrations (on the

Oak Ridge Reservation) that are below chronic NAWQC are nonetheless toxic to daphnids (Kszos et

al. 1992).

2.3 TIER II VALUES

If NAWQC were not available for a chemical, the Tier II method described in the EPA's Proposed

Water Quality Guidance for the Great Lakes System was applied (EPA 1993a). Tier II values were

developed so that aquatic benchmarks could be established with fewer data than are required for th e

NAWQC. The Tier II values are concentrations that would be expected to be higher than NAWQC in

no more than 20% of cases. Tier II values calculated by the EPA are listed in Table 1, and the sources

are cited. Other Tier II values are derived as described in the following text.

The Tier II values equivalent to the FAV and FCV are the Secondary Acute Values (SAVs) and

Secondary Chronic Values (SCVs), respectively. The sources of data for the Tier II values are listed in

Appendix A, and the procedure and factors used to calculate the SACs and SCVs are in Appendix B.

The methods described herein differ from EPA's (1993a) in one respect. The Great Lakes SAVs require

an LC50 for a daphnid, but that requirement would severely restrict t he number of benchmarks that could

be calculated. The EPA has provided factors for calculating SAVs when no daphnid LC50s ar e

available, and these factors are used herein (Stephan 1991).

Some of the SAVs and SCVs presented in this report differ from t hose presented in the prior edition

(Suter and Mabrey 1994) for three reasons. First, in the previous report we included all data tha t

occurred in EPA water quality criteria documents. However, much of the data included in criteri a

documents issued prior to 1985 are no longer considered acceptable by the EPA. Second, some dat a

from the EPA’s AQUIRE data set were used by Suter and Mab rey (1994) that appeared to be acceptable

based on the information provided in the data base and the EPA’s rating of the data. It has become clear

that much of that data would not be acceptable to the EPA for calculating criteria. Therefore, w e

obtained all original publications and independently reviewed them against the criteria in Stephan et al.

(1985). Those criteria are summarized in Appendix B. Finally, some new data have been found an d

incorporated.

Only high quality standard data are used in this document if such values are available for a

chemical. That is, if even one test that meets the criteria in Stephan et al (1985) was found, al l

nonconforming tests were excluded. However, when no such values are available, nonstandard or lower

quality test results which were judged by the authors to be reliable were used. Values derived using data

that did not meet the Stephan et al. (1985) criteria are noted.
14

2.4 LOWEST CHRONIC VALUES

The lowest chronic values for fish and invertebrates reported in the literature are potential lower

benchmarks. Chronic values are used to calculate the chronic NAWQC, but the lowest chronic value

may be lower than the chronic NAWQC. Because of the short generation time of algae and the relative

lack of standard chronic tests for aquatic plants, EPA guidelines are followed in using any algal test of

at least 96-hour duration and any biologically meaningful response for the plant values.

2.5 ESTIMATED LOWEST CHRONIC VALUES

Estimated lowest chronic values for fish and invertebrates are another set of potential lowe r

benchmarks. Estimated chronic values were extrapolated from 96-hour LC50s using equations fro m

Suter et al. (1987) and Suter (1993). The equations are as foll ows where LC50 equals the lowest species

mean 96-hour LC50 for fish and 48-hour EC50 for daphnids, and CV equals the estimated chronic value

for that taxon. The 95% prediction interval at the mean is log CV ± the PI value (95% predictio n

intervals contain 95% of observations versus 95% confidence intervals which contain the mean with 95%

confidence).

Fish CV for a metallic contaminant: (1)

log CV = 0.73 log LC50 - 0.70

PI = 1.2

Fish CV for a nonmetallic contaminant: (2)

log CV = 1.07 log LC50 - 1.51

PI = 1.5

Daphnid CV for a metallic contaminant: (3)

log CV = 0.96 log LC50 - 1.08

PI = 1.56

Daphnid CV for a nonmetallic contaminant: (4)

log CV = 1.11 log LC50 - 1.30

PI = 1.35

2.6 TEST EC20s

Another potential lower benchmark is the test EC20 for fish, which is defined as the highest tested

concentration causing less than 20% reduction in (1) the weight of young fish per initial female fish in

a lifecycle or partial life-cycle test or (2) the weight of you ng per egg in an early life-stage test. A similar

potential lower benchmark is the test EC20 for daphnids, which is the highest tested concentratio n

causing less than 20% reduction in the product of growth, fecundity, and survivorship in a chronic test

with a daphnid species. (Daphnids include members of the genera Daphnia, Ceriodaphnia, and

Simocephalus.) These benchmarks are intended to be indices of population production. They ar e

equivalent to chronic values in that they are simply a summary of the results of chronic toxicity tests, and

in most cases the same test supplied the lowest chronic value and the lowest test EC20. However, the

test EC20s are based on a level of biological effect rather than a level of statistical significance, and they

integrate all of the stages of the toxicity test rather than treating each response independently. The 20%

figure was chosen as approximately the mean level of effect on individual response parameters observed
15

at CVs and as a minimum detectable difference in population characteristics in the field (Suter et al .

1987, 1992). These values are listed in Table 2.

2.7 ESTIMATED TEST EC20s

The estimated test EC20 is another potential benchmark. The estimated values were extrapolated

from 96-hour LC50 values using equations from Suter (1992). The equation for the lowest fish tes t

EC20 is as follows where LC50 equals the lowest species mean 96-hour LC50 for fish, and the EC25

for weight of juveniles per egg is used as an estimate of the test EC20 value. (The difference between

20% and 25% effect is trivial given the uncertainties in these estimates and the steepness of th e

concentration-response curves.) The log-scaled 95% prediction interval at the mean is log EC25 ± the

PI value:

log EC25 = 0.90 log LC50 - 0.86 (5)

PI = 1.6

These values are listed in Table 2 for those chemicals that have no empirical test EC20.

2.8 SENSITIVE SPECIES TEST EC20s

The sixth potential benchmark is the EC20, adjusted to approximate the fifth percentile of th e

species sensitivity distribution. It is calculated in the same way as the chronic NAWQC except that the

test EC20s are used in place of CVs, and salt water species were not included. The FAV for each of the

criterion chemicals was divided by the geometric mean of ratios of LC50s to EC20s. These benchmarks

are referred to as sensitive species (SS) test EC20s, and are listed in Table 2.

2.9 POPULATION EC25s

The last potential benchmark is an estimate of the continuous concentration that would cause a 20%

reduction in the recruit abundance of largemouth bass. The method used was described by Barnthouse

et al. (1990) and is briefly summarized herein. The recruit abundance estimates are generated by a

matrix model of a reservoir largemouth bass population (Bart ell 1990). The fecundity, hatching success,

larval survival, and post-larval survival of the model population are each decremented by a valu e

generated from statistical extrapolation models. For each life stage for which a concentration-response

relationship could be calculated, that relationship was adjusted for the relative sensitivity of the tes t

species and the bass. For those life stages with no concentration-response relationship, the relationship

was estimated using life stage to life stage extrapolation models, and the taxonomic adjustment wa s

made. However, if the authors of the study reported that life stage was unaffected, the decrement for that

life stage was set to zero. If no chronic test data were available, extrapolations from LC50s to chronic

responses of each life stage were performed. Uncertainties in a ll of these extrapolations were propagated

through the models to generate estimates of uncertainty. For each chemical, each available freshwater

fish chronic test was used to parameterize a model run. If no chronic test data were available, eac h

available freshwater fish LC50 was used to parameterize a model run. The results are presented i n

Appendix C. The geometric mean of all population EC25 estimates for each chemical is reported i n

Table 2.
16

2.10 ECOTOX THRESHOLDS

The EPA’s OSWER has published Ecotox Thresholds (ETs) which are intended to be used fo r

screening contaminants at Comprehensive Environmental Response, Compensation, and Liability Act

(CERCLA) sites (OSWER 1996); these values are available for 20 meta ls and 47 organics in fresh water

and for 10 metals and 7 organics in marine waters. The fresh water values are presented in Table 3 .

Their derivation is briefly explained in the following text.

In general, chronic NAWQC values are preferred as aqueous ETs. However, as with th e

benchmarks in Table 1, criteria that are based on fish consumption rather than aquatic toxic effect s

(DDT, heptachlor, and toxaphene) are not used. Tier II values are presented in their place. For diazinon,

the FCV calculated by the Great Lakes Water Quality Initiative (GLWQI) was used as a criterion value

(EPA 1992).

OSWER recommends the use of dissolved concentrations of metals. Therefore, the metho d

described in Prothro (1993) is used to correct for dissolved phase concentrations, which causes some of

the metals criteria values used as ETs to differ slightly from the criteria listed in Table 1 or in the Region

IV values.

SCVs are used when NAWQCs are not available. Four of these SCVs are from the GLWQI (EPA

1992), 34 are from the prior edition of this document (Suter and Mabrey 1994), and 18 were calculated

by OSWER (1996). Three chemicals with OSWER-derived SCVs (endosulfan, methoxyclor, an d

malathion) had NAWQCs, but the criteria were judged to be old and unreliable. Tier II values were not

derived if no daphnia acute values were available.

2.11 REGION IV SCREENING VALUES

EPA Region IV has published acute and chronic ecologica l screening values (SVs) for fresh surface

water (Waste Management Division 1995); they are presented in Table 3. The acute SVs consist o f

acute NAWQCs or, for chemicals with no acute NAWQC, of low est acute LC50 or EC50 values divided

by 10. The chronic SVs consist of chronic NAWQCs or, for chemicals with no chronic NAWQC, o f

lowest CVs divided by 10. If there were no CVs, the acute SV is divided by 10 to obtain the chronic SV.

These divisions by 10 serve the same purpose as the models used to calculate Tier II values, but without

the scientific or statistical basis and without using the full available data set. For some chemicals, the

SVs are based on effects on fish eaters or irrigated plants rather than aquatic life. Region I V

acknowledges that other values have greater ecological relevance (Waste Management Division 1995).

As explained previously, there are separate benchmarks to address effects on plants and wildlife and an

entirely separate set of risk assessment methods to protect humans who eat fish. Finally, the hardness

dependent criteria are adjusted to 50 mg/L which is unrealistically low for the Oak Ridge Reservation

and most other sites.

2.12 BACKGROUND CONCENTRATIONS

Background water concentrations should be used as a check for these benchmarks. That is, because

some of these benchmarks are quite conservative and because the measured concentrations in ambient

water may include forms that are not bioavailable, benchmark concentrations may be lower tha n

background water concentrations. If the background concentrations are valid and represent a n

uncontaminated state and if exposed site does not contain forms of the chemicals that are mor e
17

bioavailable or toxic than the forms at background sites, then screening benchmarks lower than th e

background concentration should not be used.

Table 3. Summary of OSWER threshold values for aquatic life (EPA 1996) and Region IV screening

values for freshwater surface water (Region IV 1995) (All values are μg/L)

OSWER Values Region IV Values3

Chemical or FCV Tier II Screening Values 

NAWQC Acute Chronic Screening

`1 2

Values 

Metals

Aluminum 750 87

Antimony 1300 (2s) 160 (2s)

Arsenic III 190 360 190

Arsenic V 8.1 *

Barium 3.9 *

Beryllium 5.1 * 16 (6s) 053 (1s)

Boron -- 7504

Cadmium 1.0 h 1.79 h 0.66 h

Chromium III 180 h 984.32 h 117.32 h

Chromium VI 10 16 11

Cobalt 3.0 *

Copper 11 h 9.22 h 6.54 h

Iron 1000 -- 1000

Lead 2.5 h 33.78 1.32

Manganese 80 *

Mercury 2.40 0.0123

Mercury, inorganic 1.3

Mercury, methyl 0.003 *

Molybdenum 240 *

Nickel 160 h 789.00 h 87.71 h

Selenium 5.0 20.00 5.00

Silver 1.23 h 0.012 (1s)

Thallium 140.00(3s) 4.00 (2s)
Table 3. (continued)

18

OSWER Values Region IV Values3

Chemical or FCV Tier II Screening Values 

NAWQC Acute Chronic Screening

`1 2

Values 

Vanadium 19 *

Zinc 100 h 65.04 h 58.91 h

Organic Compounds

Acenaphthene 23 S 170 (2s) 17

Acrolein 6.8 (3s) 2.1 (1s)

Acrylonitrile 755 (4s) 75.5

Aldrin 3 0.3

Benzene 46 * 530 (7s) 53

Benzidine 250 (4s) 25

Benzo(a)pyrene 0.014 *

a-BHC -- 5006

b-BHC -- 50006

g-BHC (Lindane) 0.08 2 0.08

Biphenyl 14 #

Bis(2-chloroethyl) ether 23800 (1s) 2380

Bis(2-ethylhexyl)phthalate 32 * 1110 (2s) <0.3 (2s)

Bromoform 2930 (2s) 293

4-Bromophenylphenyl ether 1.5 #

4- Bromophenylphenyl phthalate 36 (2s) 12.2 (1s)

Butylbenzyl phthalate 19 # 330 (4s) 22 (2s)

Carbon tetrachloride 3520 (3s) 352

Chlordane 2.4 0.00435

Chlorobenzene 130 * 1950 (5s) 195

2-Chloroethylvinyl ether 35400 (1s) 3540

Chloroform 2890 (3s) 289

2-Chlorophenol 438 (5s) 43.8

Chloropyrifos 0.083 0.041
Table 3. (continued)

19

OSWER Values Region IV Values3

Chemical or FCV Tier II Screening Values 

NAWQC Acute Chronic Screening

`1 2

Values 

4,4'-DDT 0.013 + 1.1 0.001

4,4'-DDE 105 (1s) 10.5

4,4'-DDD 0.064 (8s) 0.0064

Demeton -- 0.1

Diazinon 0.043 F

Dibenzofuran 20 *

1,2-Dichlorobenzene 14 # 158 (4s) 15.8 (3s)

1,3-Dichlorobenzene 71 # 502 (3s) 50.2

1,4-Dichlorobenzene 15 # 112 (5s) 11.2

1,1-Dichloroethane 47 *

1,2-Dichloroethane 11800 (3s) 2000 (1s)

1,1-Dichloroethylene 3030 (3s) 303

2,4-Dichlorophenol 202 (3s) 36.5 (1s)

1,2-Dichloropropane 5250 (3s) 525

Dichloropropylene (cis and 606 (2s) 24.4 (1s)

trans)

Dieldrin 0.062 S 2.5 0.00195

Diethyl phthalate 220 * 5210 (2s) 521

2,4-Dimethylphenol 212 (3s) 21.2

Dimethyl phthalate 3300 (2s) 330

Di-n-butyl phthalate 33 * 94 (6s) 9.4

2,4-Dinitrophenol 62 (3s) 6.2

2,4-Dinitrotoluene 3100 (2s) 310

Dioxin (2,3,7,8-TCDD) 0.1 0.000015

1,2-Diphenylhydrazine 27 (2s) 2.7

Endosulfan, mixed isomers 0.051 #

Endosulfan, alpha 0.051 # 0.22 0.056

Endosulfan, beta 0.051 # 0.22 0.056
Table 3. (continued)

20

OSWER Values Region IV Values3

Chemical or FCV Tier II Screening Values 

NAWQC Acute Chronic Screening

`1 2

Values 

Endrin 0.061 S 0.18 0.00235

Ethylbenzene 290 * 4530 (5s) 453

Fluoranthene 8.1 S 398 (2s) 39.8

Fluorene 3.9 #

Guthion -- 0.01

Heptachlor 0.0069 + 0.52 0.00385

Heptachlor epoxide 0.52 0.00385

Hexachlorobutadiene 9 (5s) 0.93 (1s)

Hexachlorocyclopentadiene 0.7 (4s) 0.07

Hexachloroethane 12 # 98 (5s) 9.8

Isophorone 11700 (2s) 1170

Lindane (see g-BHC)

Malathion 0.097 -- 0.01

Methoxychlor 0.019 # -- 0.03

Methyl bromide 1100 (1s) 110

Methyl chloride 55000 (1s) 5500

3-Methyl-4-chlorophenol 3 (1s) 0.3

(p-Chloro-m-cresol)

2-Methyl-4, 6-dinitrophenol 23 (4s) 2.3

(4,6- Dinitro-o-cresol)

Methylene chloride 19300 (3s) 1930

Mirex -- 0.001

Naphthalene 24 * 230 (4s) 62 (1s)

Nitrobenzene 2700 (2s) 270

2-Nitrophenol -- 3500

4-Nitrophenol 828 (3s) 82.8

n-Nitrosodiphenylamine 585 (2s) 58.5

Parathion 0.065 0.013
Table 3. (continued)

21

OSWER Values Region IV Values3

Chemical or FCV Tier II Screening Values 

NAWQC Acute Chronic Screening

`1 2

Values 

PCB (total polychlorinated 0.19 *

biphenyls)

PCB-1242 0.2 (7s) 0.014

PCB-1254 0.2 (7s) 0.014

PCB-1221 0.2 (7s) 0.014

PCB-1232 0.2 (7s) 0.014

PCB-1248 0.2 (7s) 0.014

PCB-1260 0.2 (7s) 0.014

PCB-1016 0.2 (7s) 0.014

Pentachlorobenzene 0.47 # 250 50

Pentachlorophenol 13 pH 20 pH 13 pH

Phenol 1020 (16s) 256 (1s)

Polynuclear aromatic

hydrocarbons

Phenanthrene 6.3 S

1,2,4,5-Tetrachlorobenzene 250 50

1,1,2,2-Tetrachloroethane 420 * 932 (3s) 240 (1s)

Tetrachloroethylene 120 * 528 (5s) 84 (1s)

Tetrachloromethane 240 #

Toluene 130 * 1750 (5s) 175

Toxaphene 0.011 # 0.73 0.00025

1,2-Trans-Dichloroethylene, 13500 (1s) 1350

Tribromomethane 320 #

Tributyltin -- 0.026

1,2,4-Trichlorobenzene 110 # 150 (4s) 44.9 (1s)

1,1,1-Trichloroethane 62 * 5280 (2s) 528

1,1,2-Trichloroethane 3600 (3s) 940 (1s)

Trichloroethylene 350 *
Table 3. (continued)

22

OSWER Values Region IV Values3

Chemical or FCV Tier II Screening Values 

NAWQC Acute Chronic Screening

`1 2

Values 

 2,4,6-Trichlorophenol 32 (3s) 3.2

m-Xylene 1.8 #

Other

Chloride 860,000 230,000

Chlorine (total residual - TRC) 19 11

Cyanide 5.2 22 5.2

pH -2.5

Oil and Grease -- 0.01 (Low LC ) 50 

Sulfide (S2-, HS-) -- 2

Notes:

EPA derived NAWQC or final chronic values (FCVs). 1

Values calculated using the GLWQI Tier II methodology. 2

Based on EPA Region IV Water Management Division, Water Quality Standards Unit’s Screening List. Those 3

followed by (ns) are derived by Region IV using safety factors.

For long-term irrigation of sensitive crops (minimum standard). 4

Based on the marketability of fish. The use of other values which may have greater ecological 5

significance may be considered.

Lowest plant value reported. 6

(ns) = number of species

h = hardness-dependent ambient water quality criterion (100 mg/L as CaCO3 used for OSWER thresholds and

50 mg/L for Region IV values).

pH = pH-dependent ambient water quality criterion (7.8 pH used for OSWER thresholds and 6.0 for Region IV

values).

S = FCV derived for EPA Sediment Quality Criteria documents.

F = FCV calculated using GLWQI Tier 1 methodology.

t = value is for total of all chemical forms.

* = value as calculated in Suter and Mabrey (1994).

+ = Value with EPA support documents.

# = value calculated by OSWER.

3. CHEMICAL-SPECIFIC INFORMATION

This section describes the sources of information and procedures that are specific to individua l

elements. Except where noted, the sources of data for estimating chronic values and test EC20s for fish

are the same. All data used to calculate Tier II values and estimated chronic values and EC20s ar e

presented in Appendix A.
23

3.1 INORGANICS

Aluminum. There are NAWQC for aluminum. The toxicity of aluminum has been shown to vary

widely with water hardness and pH (Ingersoll et al., 1990a 1990b; Woodward et al., 1989; Sadler and

Lynam, 1988; and Cleveland et al. 1986; and others). The benchmarks were calculated using only tests

in circumneutral water. Lowest chronic and test EC20 values for fish are from 28-day embryo-larval

tests with Pimephales promelas. Kimball (n.d.) presented a CV of 5800 μg/L, however, after further

analysis of Kimball’s data, the EPA (1988a) offered another value of 3288 μg/L as the CV fo r

aluminum. Lowest chronic and test EC20 values for daphnids are from McCauley et al. (1986). The

EPA (1988a) gives a 4-day test EC50 for Selenastrum capricornutum which is used as the plant chronic

value. 

Ammonia. The test EC20 value for fish is from an embryo-larval test with fathead minnow s

(Thurston et al. 1986). The chronic value for fish is from an early life stage test with pink salmon ,

Oncorhynchus gorbuscha (Rice and Bailey 1980). The chronic value for daphnids is from EP A

(1985a). Chronic values were determined using Daphnia magna in life-cycle tests. EPA (1985a)

provided the chronic value for aquatic plants, in which Chlorella vulgaris experienced growth inhibition

(EC50). The NAWQC for ammonia are functions of temperature (T) and pH. The acute NAWQC for

ammonia is 0.52/FT/FPH/2, and the chronic NAWQC for ammonia is 0.80/FT/FPH/Ratio, where:

FT = 10 ; TCAP T 30 0.03(20-TCAP) 

10 ; 0 T TCAP 0.03(20-T)

FPH = 1; 8 pH 9

1 + 10 ; 6.5 pH 8

7.4-pH

1.25

Ratio = 16; 7.7 pH 9

= (24) 10 ; 6.5 pH 7.7 7.7-pH

1 + 10 

7.4-pH

TCAP = 20 C for acute criteria and 15 C for chronic criteria when Salmonids or other sensitive o o

cold water species are present

= 25 C for acute criteria and 20 C for chronic criteria when Salmonids and other sensitive o o

coldwater species are absent

These criteria are presented in greater detail in EPA (1985a and 1986b).

Antimony. Chronic and test EC20 values for antimony are from Kimball (n.d.). The chronic tests

of Pimephales promelas were embryo-larval, and 28-day life-cycle tests were used for Daphnia magna.

The EPA (1978) gives a 4-day EC50 for chlorophyll A inhibition in Selenastrum capricornutum which

is used as the plant value. The SAV and SCV listed in this report are draft FAV and FCV value s

(EPA 1988b).

Arsenic III. NAWQC are listed for arsenic III. The lowest chronic values for fish and daphnids

are given by Call et al. (1983) and Lima et al. (1984). Early life stage tests were used on Pimephales

promelas and life-cycle tests were used on Daphnia magna. Cowell (1965) provides the lowest chronic

value for the algae Spirogyra, Cladophora, and Zygnema which is a concentration that produced a
24

100% kill in 2 weeks. The test EC20 value is derived from Lima et al. (1984) for fish and from Call et

al. (1983) and Lima et al. (1984) for daphnids.

Arsenic V. The chronic and test EC20 values for fish are from an early life stage test wit h

Pimephales promelas (DeFoe 1982), and the test EC20 for daphnids is from Spehar et al. (1980). The

estimated chronic value for daphnids was calculated with a Daphnia magna LC50 from EPA (1985b)

using Equation (3). Vocke (1980) provides the plant value from a 14-day EC50 test with Scenedesmus

obliquus. The SAV and SCV listed in this report are lower than the acute and chronic LOEL value s

listed in the Water Quality Criteria Summary (EPA 1986b).

Barium. The chronic value for daphnids is from a 21-day test on Daphnia magna by Biesinger and

Christensen (1972) which resulted in 16% reproductive impairment.

Beryllium. The chronic and test EC20 values for Daphnia magna are from a life-cycle test in

Kimball (n.d.). Karlander and Krauss (1972) provide the plant value for Chlorella vannieli, a 10 to 20%

reduction in autotrophic growth rates. The estimated chronic and test EC20 values for fish were derived

using data for Pimephales promelas from EPA (1980f) in Equations (1) and (5). The derived SAV and

SCV listed in this report are lower than the lowest CV listed in the Water Quality Criteria Summar y

(EPA 1986b) and the acute and chronic LOEL values listed in the Water Quality Criteria Summary (EPA

1986b).

Boron. The EC20 value for daphnids was based on a 21-day test on Daphnia magna by Gerisch

(1984). A 21-day test of Daphnia magna by Lewis and Valentine (1981) provided the lowest daphnid

chronic value.

Cadmium. The NAWQC for cadmium are functions of water hardness. The equations for these

are e for the chronic value and e for the acute value (EPA 1986b).

(0.7852[ln(hardness)]-3.490 (1.128[ln(hardness)]-3.828)

The lowest chronic value for fish is from Sauter et al. (1976) and Chapman et al. (n.d.) for daphnids.

Early life stage tests were performed on brook trout, and life-cycle tests were performed on Daphnia

magna. The test EC20 value is from Carlson et al. (1982) for fish and Elnabarawy et al. (1986) fo r

daphnids. The value for aquatic plants is from Conway (1977). A relatively low cadmium concentration

reduced the population growth rate of Asterionella formosa by an order of magnitude. 

Calcium. The chronic value for daphnids is a concentration causing a 16% reduction i n

reproduction of Daphnia magna exposed to CaCl2•2H2O (Biesinger and Christensen 1972). Because

the highly conservative secondary values were below commonl y occurring ambient concentrations of this

macronutrient, they were judged to be inappropriate and are not presented.

Chromium III. The NAWQC for chromium III are functions of water hardness. The equations

are e for the chronic value and e for the acute value. The lowest (0.8190[ln(hardness)]+1.5161) (0.8190[ln(hardness)]+3.688)

chronic value for fish is from an early life stage test by Stevens and Chapman (1984) on rainbow trout.

Chapman et al. (n.d.) provide a chronic value from a life-cycle test of Daphnia magna. The plant value

for chromium III is from a 4-day chronic test in which there was a 50% inhibition of growth o f

Selenastrum capricornutum (EPA 1985c). Stevens and Chapman (1984) also provided data for the test

EC20 value for fish.

ChromiumVI. There are NAWQC for chromium VI. The chronic and test EC20 values for fish

are from Sauter et al. (1976). An early life stage test produced the chronic value for rainbow trout. For

daphnids, a life-cycle chronic test was run by Mount (1982) on Daphnia magna, and the test EC20 is

from Elnabarawy et al. (1986). Microcystis aeruginosa, used for the aquatic plant value, showed

incipient inhibition in tests reported by the EPA (1985c).
25

Cobalt. The chronic and test EC20 values for cobalt are from Kimball (n.d.). Daphnia magna

were used in 28-day life-cycle tests, and Pimephales promelas were used in embryo-larval tests.

Copper. The NAWQC for copper are functions of water hardness. The equations ar e

e for the chronic value and e for the acute value. The chronic and (0.8545[ln(hardness)]-1.465) (0.9422[ln(hardness)]-1.464)

test EC20 values for fish are from an early life stage test with brook trout by Sauter et al. (1976). The

daphnid chronic value is from Chapman (n.d.). The test EC20 value for daphnids is derived from Dave

(1984a). A 21-day test LC50 on Daphnia magna provided the chronic value for daphnids. Arthur and

Leonard (1970) provided a chronic value through 6-week tests on the amphipod, Gammarus

pseudolimnaeus. Steeman-Nielsen and Wium-Anderson (1970) provide a plant value based on a lag

in growth of the alga, Chlorella pyrenoidosa.

Cyanide. There are NAWQC for cyanide. The chronic and test EC20 values for fish were both

from a brook trout life-cycle test by Koenst et al. (1977). Oseid and Smith (1979) provide full life-cycle

test on Gammarus pseudolimnaeus, an amphipod. The alga, Scenedesmus quadricauda, showed

incipient inhibition in chronic tests by the EPA (1985e). 

Iron. The NAWQC for iron is based on a field study at a site receiving acid mine drainage and is

not consistent with the current method for deriving criteria. The lowest chronic value for daphnids (158

μg/L) is a threshold for reproductive effects from a 21-day test of FeCl 2 with Daphnia magna (Dave

1984c). It is considerably lower than the 4380 μg/L concentration causing 16% reproductive decrement

in another test of FeCl with D. magna (Biesinger and Christensen 1972). Dave (1984c) argued that his 2

result was more applicable to a situation in which "an acidic iron-containing waste water is discharged

into a lake or a river" where it is neutralized, but Biesinger and Christensen's (1972) result "is probably

more close to the steady-state situation in natural freshwater without any point source of iron." Th e

lowest chronic value for fish is a concentration that caused 100% larval mortality in an embryo-larval

test with rainbow trout exposed to dissolved iron salts (Amelung 1981).

Lead. The NAWQC for lead are functions of water hardness. The equations are e(1.273[ln(hardness)]-4.705)

for the chronic value and e for the acute value. The lowest chronic value for fish was (1.273[ln(hardness)]-1.460)

provided by an early life stage test on rainbow trout by Davi es et al. (1976). Daphnia magna were used

in 21-day tests to determine lowest chronic toxicity by Chapman et al. (manuscript). Borgmann et al.

(1978) provided a chronic value for a life-cycle test on Lymnaea palastris, a snail. Chlorella vulgaris,

Scenedesmus quadricauda, and Selenastrum capricornutum experienced 53%, 35%, and 52% growth

inhibition, respectively, at the plant chronic value (EPA 1985f). The test EC20 value for fish is from

Sauter et al. (1976). The acute-EC20 ratio from which the SS test EC20 was calculated had to b e

obtained using a species mean acute value for Salmo gairdneri (EPA 1985f) since no acute value was

reported by Sauter et al. (1976).

Magnesium. The chronic value for daphnids is a concentration causing a 16% reduction i n

reproduction of Daphnia magna exposed to MgCl2•6H2O (Biesinger and Christensen 1972). Because

the highly conservative secondary values were below commonl y occurring ambient concentrations of this

nutrient element, they were judged to be inappropriate and are not presented.

Manganese. All chronic and test EC20 values for manganese are from Kimball (n.d.). The fish

chronic value is from a 28-day early life-stage test with Pimephales promelas.

Mercury, inorganic, or total. Mercury has NAWQC. However, the chronic criterion for mercury

is based on the final residue value derived from a methyl mercury bioconcentration factor. To protect

aquatic life, the secondary values were derived from the EPA's (1985f) final acute and chronic values.
26

The chronic and test EC20 values for fish are from Call et al. (1983), and those for daphnids are from

Biesinger et al. (1982). The chronic tests for fish were run on Pimephales promeles throughout their

embryo-larval stage. Daphnia magna were used in flow through life-cycle tests. The plant value is for

incipient inhibition of Microcystis aeruginosa in an 8-day test (EPA 1985f). The acute-EC20 ratio used

to calculate the SS test EC20 value had to be derived using a species mean acute value (EPA 1985g) since

no acute value was reported in Biesinger et al. (1982).

Mercury, methyl. The chronic and test EC20 values for fish are from McKim et al. (1976). Brook

trout were used in three generation life-cycle tests. The test EC20 value for daphnids is from Biesinger

et al. (1982). The alga, Chlorella vulgaris, was used in 15-day EC50 (growth) tests by Rai et al. (1981)

to determine chronic toxicity values for aquatic plants.

Molybdenum. The chronic and test EC20 values for daphnids are from Kimball (n.d.). Daphnia

magna were used in a 28-day life-cycle test to determine the chronic value.

Nickel. The NAWQC for nickel are functions of water hardness. The equation for these ar e

e for the chronic value and e for the acute value. However, nickel (0.8460[ln(hardness)]+1.1645) (0.8460[ln(hardness)]+3.3612)

concentrations of 10 μg/L in Oak Ridge Reservation stream water (considerably below the chroni c

NAWQC for nickel but similar to the lowest of the alternate benchmarks) reduced 7-day Ceriodaphnia

dubia survivorship to 60% (Kszos et al. 1992). The chronic and test EC20 values for fish are fro m

Nebeker et al. (1985). The chronic value for fish was determined through an early life stage test o n

rainbow trout. For daphnids, the chronic value was from Lazareva (1985) and the test EC20 was from

Münzinger (1990). Daphnia magna were used in a life-cycle test to determine the chronic value. The

caddisfly, Clistoronia magnifica, was used in life-cycle tests by Nebeker et al. (1984) to determine the

chronic value. The plant chronic toxicity values were provided by the EPA (1986a) for Microcystis

aeruginosa, which showed incipient inhibition.

Potassium. The chronic value for daphnids is a concentration causing a 16% reduction i n

reproduction of Daphnia magna exposed to KCl (Biesinger and Christensen 1972). Because the highly

conservative secondary values were below commonly occurring ambient concentrations of thi s

macronutrient, they were judged to be inappropriate and are not presented.

Selenium. NAWQC are listed for selenium. The chronic and test EC20 values for fish are from

Goettl and Davies (1976). Their tests were during the early life stage of rainbow trout. The chroni c

value for daphnids is from Kimball (n.d.), and the test EC20 is from Johnston (1987). These tests were

run for 28 days on Daphnia magna. The green alga, Scenedesmus obliquus, exhibited reduced growth

in the 14-day chronic toxicity tests (Vocke et al. 1980). The acute-EC20 ratio used in calculation of the

SS EC20 value had to be derived using a species mean acute value for Daphnia magna (EPA 1987a)

because no acute value was reported by Johnston.

Silver. The acute NAWQC for silver, which is a function of water hardness, is given by th e

equation e . The SCV was estimated from the FAV and acute-chronic ratios for thre e

(1.72[ln(hardness)]-6.52)

species. Although questions about two of these ratios prompted the EPA to refrain from calculating a

final chronic value, we judged them to be better than the default value. The lowest chronic value for fish

is based on an early life stage test on rainbow trout by Davies et al. (1978). The lowest chronic value

for daphnids and the test EC20 for fish are from Nebeker et al. (1983). The daphnid CV is from a test

with Daphnia magna. The test EC20 for daphnids is from Elnabarawy et al. (1986). The plant value

is for growth inhibition in Chlorella vulgaris (EPA 1980y).

 
27

Sodium. The chronic value for daphnids is a concentration causing a 16% reduction in reproduction

of Daphnia magna exposed to NaCl (Biesinger and Christensen 1972). Because the highly conservative

secondary values were below commonly occurring ambient concentrations of this macronutrient, they

were judged to be inappropriate and are not presented.

Strontium. The chronic value for daphnids is from 21-day tests on Daphnia magna by Biesinger

and Christensen (1972) which resulted in 16% reproductive impairment.

Thallium. Chronic and test EC20 values are from Kimball (n.d.). Embryo-larval tests were run

on Pimephales promelas, and 28-day chronic tests were run on Daphnia magna. The aquatic plant

value is a 4-day EC50 which reduced the cell numbers of the alga, Selenastrum capricornutum

(EPA 1978).

Tin. The chronic value is from Biesinger and Christensen (1972). It caused 16% reproductiv e

impairment in Daphnia magna in 21 days.

Uranium. The chronic value for fish is an estimate based on a fathead minnow LC50 fro m

Cushman et al. (1977) used in Equation (1). The test EC20 is an estimate based on the same data ;

however, Equation (5) was used. 

Vanadium. The lowest chronic and test EC20 values for fish are from Holdway and Spragu e

(1979) and for daphnids from Kimball (n.d.).

Zinc. The NAWQC for zinc are functions of water hardness. The equations ar e

e for the chronic value and e for the acute value. The chronic and (0.8473[ln(hardness)]+0.7614) (0.8473[ln(hardness)]+0.8604)

test EC20 values for fish are from Spehar (1976), and the chronic value for daphnids is from Chapman

et al. (n.d.). Life-cycle tests were run on Jordanella floridae and Daphnia magna. Nebeker et al.

(1984) provided chronic values from life-cycle tests on the caddisfly, Clistoronia magnifica. Bartlett

et al. (1974) ran 7-day tests on Selenastrum capricornutum. These aquatic plants showed incipient

inhibition of growth.

Zirconium. The chronic and test EC20 values for fish are estimates based on an LC50 fo r

Pimephales promelas from Cushman et al. (1977). These values were calculated using Equations (1)

and (5).

3.2 ORGANICS

Acenaphthene. Although the full data requirements are not met for acenaphthene, the EPA has

presented final acute and chronic values for derivation of sediment quality criteria which are presented

in the criteria columns (EPA 1993b). The fish chronic value is from an early life-stage test wit h

Pimephales promelas, and the non-daphnid chronic value is from a life-cycle test with a midg e

Paratanytarsus sp. (EPA 1993b). The plant value is from EPA (1978). Selenastrum capricornutum

were used in 96-hour EC50 (50% reduction in cell numbers).

Acetone. The test EC20 value for fish is an estimate based on an LC50 for rainbow trout. Th e

chronic value for Daphnia magna is a 28-day life-cycle test from LeBlanc and Surprenant (1983). 
28

Anthracene. The chronic value for daphnids (Daphnia magna) was estimated using an EC50 from

Holst and Giesy (1989). The chronic and test EC20 values for fish are an estimate based on an LC50

for bluegill from Oris and Giesy (1985). Calculations were performed using Equations (2), (4), and (5).

Benzene. The lowest chronic value for daphnids is given by EPA (1978). Daphnia magna were

used in life-cycle tests. The lowest chronic value for aquatic plants is given by Kauss and Hutchinson

(1975), which was a 48-hour test EC50 on Chlorella vulgaris. The chronic value for fish is an estimate

based on data for the rainbow trout from EPA (1980d) and Equation (2). The test EC20 value for fish

is derived from Black and Birge (1982). The reade r should note that Black and Birge conducted a series

of screening tests for a large number of chemicals on several freshwater organisms. Larval fish survival

was recorded to only 4 days post-hatch, and LOECs and NOECs were not determined. These tests, then,

did not generate standard chronic values and are not equivalent to the other chronic tests cited in thi s

report. The test EC20 values based on tests by Black and Birge may be high relative to those fro m

conventional chronic tests. 

Benzidene. The chronic and EC20 value for fish are an estimate based on data for red shiner from

EPA (1980c). Calculations were performed using Equations (2) and (5).

Benzo(a)anthracene. The chronic value for daphnids is an estimate based on data for Daphnia

magna from Trucco et al. (1983) used in Equation (4).

Benzo(a)pyrene. The test EC20 for fish is derived from Hannah et al. (1982). The chronic value

for daphnids is an estimate based on data for Daphnia magna from Trucco et al. (1985) used in

Equation (4).

Benzoic Acid. The chronic value for fish is an estimate based on data for the mosquitofish from

AQUIRE used in Equation (2). The estimated test EC20 for fish is b ased on the same data, but Equation

(5) was used.

Benzyl Alcohol. The chronic and test EC20 values for fish are estimates based on data for bluegill

from Dawson et al. (1977). The calculations were performed using Equations (2) and (5) .

BHC (lindane). There are NAWQC for lindane. The chronic values for daphnids, fish, and nondaphnid invertebrates are all from Macek et al. (1976a). The test EC20 values for daphnids and fish are

also from Macek et al. (1976a). The chronic values were derived from life-cycle tests run on Pimephales

promelas, Daphnia magna, and the midge Chironimus tentans. The chronic value for aquatic plants

is from Krishnakumari (1977); Scenedesmus acutus exhibited 20% growth inhibition in 5 days. The

acute-EC20 ratio from which the SS EC20 was calculated was derived using a species mean acute value

for Salvelinus fontinalis (EPA 1980s) since no acute data were reported by Macek et al. (1976a).

BHC(other). The chronic value for daphnids was estimated using a Daphnia magna EC50 from

AQUIRE in Equation (4).

Bis(2-ethylhexyl)phthalate. The chronic and test EC20 values for fish are from a rainbow trout

early life-stage test (Mehrle and Mayer 1976). A much lower value was reported in the previous edition

of this report, but the results of that study are now believed to be incorrect (Knowles et al. 1987). The

new value is supported by a CV of 912 μg/L from Adams and Heidolph (1985). That study is used in

the derivation of the SCV because, unlike the Knowles et al. (1987) study, it has an accompanying acute

value (48-hr EC50). No test EC20 for daphnids was calculate d because insufficient detail was presented

by Adams and Heidolph (1985) and Knowles et al. (1987).
29

2-Butanone. The chronic values for fish and daphnids are estimates based on data from Veith et

al. (1983) and Randall and Knopp (1980), respectively. Equation (4) was applied to the data fo r

Daphnia magna, and Equation (2) was applied to the data for Pimephales promelas. The test EC20

value for fish is also an estimate using Equation (5) and an LC50 from Veith et al. (1983).

 

Carbon disulfide. The chronic and test EC20 values for fish are estimates based on data fo r

mosquitofish from AQUIRE using equations (2) and (5). The chronic value for daphnids is an estimate

for Daphnia magna using data from Van Leeuwen (1985) in Equation (4).

Carbon tetrachloride. The chronic value for fish is a rainbow trout embryo-larval LC50 (Black

and Birge 1982); therefore, it may be too high. However, it is lower than values presented by Kimball

et al. (n.d.) and EPA (1980h) for fathead minnows. The same test was used to derive the test EC20 for

fish (see the comments on benzene). The chronic value for daphnids is from a 7-day reproduction test

with Daphnia magna (Kimball et al. n.d.). None of the subchronic tests could be used in the calculation

of the SCV.

Chlordane. The chronic NAWQC for chlordane is based on the final residue value. For a criterion

to protect aquatic life rather than its use, the FCV is reported. The lowest chronic and test EC20 values

are derived from Daphnia magna, bluegill, and Chironomus tentans life-cycle tests (Cardwell et al.

1977). 

Chlorobenzene. The chronic values for fish and daphnids are estimates based on data for bluegill

and Daphnia magna from EPA (1980j). The values were calculated using Equations (2) and (4). The

plant value is a 96-hour EC50 for cell number with Selenastrum capricornutum (EPA 1980j).

Chloroform. The test EC20 value for fish is from Black and Birge (1982). (Refer to the section

on benzene). The chronic value is a 27-day LC50 for rainbow trout (embryo-larval) from EPA (1980l).

The EPA (1986b) gives this value as a lowest observed effect value in lieu of a NAWQC. The chronic

value for daphnids is an estimate based on data for Daphnia magna from EPA (1980l) and calculated

from Equation (4).

DDD. The chronic and EC20 values for fish are estimates based on data for largemouth bass from

Mayer and Ellersieck (1986) and are calculated using Equations (2) and (5).

DDT. The acute NAWQC for DDT is used. The chronic NAWQC, however, is not used because

it is based on the final residue value. To protect aquatic life, an SCV is presented. The test EC20 value

for fish is derived from Jarvinen et al. (1977). The fish chronic value is from a Pimephales promelas

life-cycle test (EPA 1980m). The chronic value for daphnids is an estimate based on data for Daphnia

pulex from EPA (1980m) and calculated with Equation (4). The aquatic plant chronic value is fro m

Sodergreen (1968). Chlorella vulgaris was affected in growth and morphology. 

Decane. The chronic value for daphnids is an estimate based on data for Daphnia magna from

LeBlanc (1980) used in Equation (4).

Di-n-butyl phthalate. All chronic and test EC20 values are from McCarthy and Whitmore (1985).

The chronic value for daphnids is based on the geometric means of the observed concentration of fresh

solutions and aged solutions. Daphnia magna were used in life-cycle tests, and Pimephales promelas

were used in early life stage tests. 
30

Dibenzofuran. The chronic value for daphnids is an estimate based on data for Daphnia magna

from LeBlanc (1980) and used in Equation (4).

1,1-Dichloroethane. The chronic and test EC20 values for fish are estimates based on an LC50

for guppy from Koneman (1981) and calculated using Equations (2) and (5).

1,2-Dichloroethane. The chronic value for fish is from Ahmad et al. (1984). Early life stage tests

were conducted on Pimephales promelas. The test EC20 value for fish is from Benoit et al. (1982). The

chronic and test EC20 values for daphnids are from Daphnia magna 28-day life-cycle tests (Richter et

al. 1983).

1,1-Dichloroethene. The chronic values for fish and aquatic plants are from EPA (1978) .

Pimephales promelas were used in embryo-larval tests. The alga, Selenastrum capricornutum, was

used in a 96-hour EC50 where it exhibited loss of chlorophyll A and cell numbers. The chronic value

for daphnids is an estimate based on data for Daphnia magna from EPA (1980n) used in Equation (4).

1,2-Dichloroethene. The chronic and test EC20 values for fish are estimates based on data fo r

bluegill from EPA (1980n). These values were derived using Equations (2) and (5).

1,3-Dichloropropene. The test EC20 for fish was estimated using an LC50 for bluegill from EPA

(1980o) in Equation (5). The chronic values for fish and aquatic plants are from EPA (1978) .

Pimephales promelas were used in an embryo-larval test, and Selenastrum capricornutum were used

in a 96-hour EC50. The alga showed chlorophyll A and cell loss. The chronic value for daphnids was

estimated using an EC50 for Daphnia magna from EPA (1980o) in Equation (4).

Diethyl phthalate. The plant value is a 96-hour EC50 for Selenastrum capricornutum

(EPA 1978). 

Di-n-octyl phthalate. All chronic and test EC20 values are from McCarthy and Whitmore (1985).

Chronic values were based on Pimephales promelas in early life stage tests and Daphnia magna in lifecycle tests. There are no Tier II values for di-n-octyl phthalate because LC50s were not available.

Ethyl benzene. The chronic value for aquatic plants is from EPA (1978). Selenastrum

capricornutum displayed chlorophyll A inhibition in 96-hour EC50. The chronic value for daphnids was

estimated using an EC50 for Daphnia magna from EPA (1980p) in Equation (4).

Fluoranthene. Although the full data requirements are not met for fluoranthene, the EPA (1993c)

has derived an FAV and FCV as a part of the derivation of sediment quality criteria which are presented

in Table 1. The fish CV is from an early life-stage test with Pimephales promelas, and the daphnid CV

is from a life-cycle test with Daphnia magna EPA (1993c).

Heptachlor. The acute NAWQC for heptachlor is used. Because the chronic NAWQC is based

on the final residue value, an SCV is reported herein. The c hronic and test EC20 values for fish are from

Macek et al. (1976b). Pimephales promelas were used in life-cycle tests to determine the chronic value

for fish. The SS test EC20 value was calculated using an acute-EC20 ratio that was derived from a

species mean acute value for Pimephales promelas (EPA 1980r) because no acute data are availabl e

from Macek et al. (1976b). The chronic value for aquatic plants is from EPA (1980r). Growt h

inhibition was exhibited by Selenastrum capricornutum in 96-hour EC50. The chronic value for

daphnids is an estimate based on data for Daphnia pulex from EPA (1980r) using Equation (4).
31

Hexane. The chronic value and test EC20 value for fish are estimates based on LC50s for golden

orfe from AQUIRE and calculated using Equations (2) and (5).

2-Hexanone. The chronic value and test EC20 value are estimates based on an LC50 fo r

Pimephales promelas from Geiger et al. (1986) and calculated using Equations (2) and (5).

1-Methylnaphthalene.The chronic and test EC20 values for fish are estimates based on data for

Pimephales promelas from Mattson (1976). The values were calculated with Equations (2) and (5).

4-Methyl-2-pentanone. The chronic value for fish is from Call et al. (1985). Pimephales

promelas embryos, larva, and juveniles were exposed for 31 to 33 days.

2-Methylphenol. The chronic value for daphnids is an estimate based on data for Daphnia magna

from Adema (1978) and Canton and Adema (1978). The value was calculated using Equation (4). The

chronic and test EC20 values for fish were estimated using an LC50 for rainbow trout from DeGraeve

et al. (1980) in Equations (2) and (5).

Methylene chloride. The chronic value for fish is from Dill et al. (1987). Pimephales promelas

were used in 32-day embryo-larval tests. The chronic value for daphnids is an estimate based on data

for Daphnia magna from LeBlanc (1980) used in Equation (4). The test EC20 value for fish is from

Black and Birge (1982). (Refer to the section on benzene concerning data from this source.)

Naphthalene. The chronic and test EC20 values for fish are from DeGraeve et al. (1982), and the

test EC20 value for daphnids is from Geiger and Buikema (1982). Pimphales promelas were used in

embryo-larval tests to determine chronic toxicity. The chronic value for aquatic plants is from EP A

(1980t). The alga, Chlorella vulgaris, exhibited inhibited cell numbers in 48-hour EC50. The chronic

value for daphnids is an estimate based on data for Daphnia magna from EPA (1980t) used in Equation

(4).

4-Nitrophenol. The chronic and test EC20 values for daphnids are from Francis et al. (1986). The

chronic and test EC20 values for fish are estimates based on data for bluegill from Buccafusco et al .

(1981) and used with Equations (2) and (5). The EPA (1978) is the source for the chronic value fo r

aquatic plants. Selenastrum capricornutum exhibited chlorophyll A reduction in 96-hour EC50. 

N-nitrosodiphenylamine. The source for the estimated fish and daphnid chronic values ar e

Buccafusco et al. (1981) and LeBlanc (1980), respectively. Equation (2) was used to calculate th e

estimated fish (bluegill) value, and Equation (4) was used for the estimated daphnid ( Daphnia magna)

value. The test EC20 value for fish is also an estimate. Buccafusco et al. (1981) provided the LC50 for

bluegill used with Equation (5) to estimate the EC20.

PCBs: Total. There are NAWQC for PCBs, but the chronic criterion is based on the final residue

value. Since that value is intended to protect the use of aquatic life, an SCV is calculated to protect the

aquatic life itself. The fish lowest chronic value and test EC20 are from a full life-cycle test of fathead

minnows by DeFoe (1978). The lowest chronic value and test EC20 for daphnids are from a 2-week

continuous flow test with Daphnia magna (Nebeker and Puglisi 1974). The lowest chronic value for

non-daphnid invertebrates is from a 3-week LC50 for Tanytarsis dissimilis by Nedeker and Puglisi

(1974). The lowest plant value is for reduction in carbon fixation by Scenedesmus quadricaudata in

a 24-hour test (Laird 1973).
32

PCBs: Aroclor 1221. The chronic and test EC20 fish values are estimates based on data fo r

®

cutthroat trout by Stalling and Mayer (1972). Equations (2) and (5) were used to determine the EC20

value for fish. The chronic value for aquatic plants is a 48-hour LC50 for Euglena gracilis (Ewald et

al. 1976).

PCBs: Aroclor 1232. The chronic and test EC20 fish values are estimates based on data fo r

®

cutthroat trout by Stalling and Mayer (1972) and AQUIRE. The geometric mean was derived from these

two values and then placed into Equations (2) and (5).

PCBs: Aroclor 1242. The chronic and test EC20 values for fish are from Nebeker et al. (1974). ®

Pimephales promelas were used in full life-cycle tests. The chronic values for non-daphnid invertebrates

are from Nebeker and Puglisi (1974). Gammarus pseudolimnaeus were exposed to PCBs for 2 months

in a continuous-flow system. The chronic value for aquatic plants is a 24-hour test in whic h

Scenedesmus obtusiusculus showed growth inhibition (Larsson and Tillberg 1975).

PCBs: Aroclor 1248. The chronic and test EC20 values for fish are from DeFoe et al. (1978), ®

and the chronic and test EC20 values for daphnids are from Nebeker and Puglisi (1974). The chronic

values for fish were full life-cycle tests carried out on Pimephales promelas. The chronic value for

daphnids was determined through 3-week exposures that created a 16% reproductive impairment i n

Daphnia magna. The chronic value for a non-daphnid invertebrate is from Nebeker and Puglisi (1974).

Gammarus pseudolimnaeus was exposed for 2 months.

PCBs: Aroclor 1254. The chronic value for fish is from a brook trout life-cycle test (Mauck et ®

al. 1978), and the test EC20 value is from a fathead minnow life-cycle test (Nebeker et al. 1974). The

chronic and test EC20 values for daphnids are from Nebeker and Puglisi (1974). Daphnia magna were

exposed for 2 weeks in a continuous-flow environment. The lowest chronic value for nondaphni d

invertebrates is from a 3-week LC50 for Tanytarsis dissimilis by Nedeker and Puglisi (1974). The

lowest plant value is for reduction in carbon fixation by Scenedesmus quadricaudata in a 24-hour test

(Laird 1973).

PCBs: Aroclor 1260. The chronic and test EC20 values for fish are from DeFoe et al. (1978). ®

The chronic value is ambiguous because significant effects occurred at the lowest concentration tested

in a 30-day fathead minnow larval test at the lowest concentrations t ested (1.3 μg/L) but not in a 240-day

lifecycle at the highest concentration tested (2.1 μg/L).

1-Pentanol. The chronic and test EC20 values for fish are estimates based on data for rainbo w

trout from AQUIRE and calculated using Equations (2) and (5). 

Phenanthrene. The chronic and test EC20 values for daphnids are from Geiger and Buikem a

(1982). The chronic value was determined using Daphnia pulex in full life-cycle tests.

Phenol. The chronic and test EC20 values for fish are from fathead minnow embryo-larval tests

(DeGraeve et al. 1980). The chronic value for daphnids is an estimate based on data for Daphnia

longispina from EPA (1980v) and calculated using Equation (4). The chronic value for aquatic plants

is from Reynolds (1975). Selenastrum capricornutum exhibited 60% reduction in cell numbers and

12% growth inhibition.

2-Propanol. The chronic and test EC20 values for fish are estimates based on data for Pimephales

promelas from AQUIRE and Veith et al. (1983). The geometric mean of these LC50s was used i n

Equations (2) and (4). 
33

1,1,2,2-Tetrachloroethane. The chronic and test EC20 values for fish are from Ahmad et al .

(1984), and the values for daphnids are from Richter et al. (1983). The chronic values for fish wer e

derived from embryo-larval tests on Pimephales promelas. The chronic values for daphnids were

derived from 28-day tests run on Daphnia magna. The chronic value for aquatic plants is from EPA

(1978). Selenastrum capricornutum exhibited chlorophyll A inhibition in 96-hour EC50. 

Tetrachloroethene. The chronic value for fish is an embryo-larval test on fathead minnows (EPA

1980aa). The test EC20 value for fish is from Ahmad et al. (1984). The chronic and test EC20 values

for daphnids are from Richter et al. (1983). These were 28-day tests on Daphnia magna. The plant

value is from EPA (1978). Selenastrum capricornutum decreased in cell number and chlorophyll A

during the 96-hour EC50.

Toluene. The chronic value is an estimate based on data for Daphnia magna from EPA (1980cc)

and calculated using Equation (4). The chronic value from Pimephales promelas is from Devlin

et al. (1982). The test EC20 value for fish is from Black and Birge (1982). (Refer to the section o n

benzene.) Chlorella vulgaris was used in 10-day tests by Kauss and Hutchinson (1975) to determine

the chronic value for aquatic plants. 

1,1,1-Trichloroethane. The chronic value and test EC20 value for daphnids are from Thompson

and Carmichael (1989). Daphnia magna were used in 17-day chronic tests. The chronic value and test

EC20 for fish were estimated based on data for Pimephales promelas from Alexander et al. (1978) and

calculated using Equation (2). The chronic value for aquatic plants is from EPA (1978). Selenastrum

capricornutum decreased in chlorophyll A and cell numbers in the 96-hour EC50.

1,1,2-Trichloroethane. The chronic value and test EC20 values for fish are from Ahmad et al .

(1984) and the chronic and test EC20 values for daphnids are from Richter et al. (1983). The chronic

value for fish is based on 32-day embryo-larval tests on Pimephales promelas, while the chronic value

for daphnids is based on 28-day tests on Daphnia magna.

Trichloroethene. The chronic and test EC20 values for fish are from Smith et al. (1991) .

Jordanella floridae, the flagfish, was used in 28-day embryo-larval tests. The chronic value fo r

daphnids is an estimate based on data for Daphnia pulex from EPA (1980dd) and calculated using

Equation (4).

Vinyl acetate. The chronic and test EC20 values for fish are estimates based on an LC50 fo r

Pimephales promelas from AQUIRE calculated using Equations (2) and (5).

Xylene. The chronic value for fish is an estimate based on an LC50 for common carp fro m

AQUIRE and calculated using Equation (2). The test EC20 value for fish is from Black and Birg e

(1982). (Refer to the section on benzene.)
34

4. APPLICATION OF BENCHMARKS

Use of these aquatic screening benchmarks requires that the assessor choose which benchmarks to

employ and which water concentrations to apply them to. The choice of benchmarks depends on th e

interpretation of the benchmarks, their regulatory standing, and their degree of conservatism. 

Each of the alternative benchmarks has a different interpretation. Exceedances of NAWQC create

a regulatory imperative for action under the Comprehensive Environmental Response, Compensation,

and Liability Act (CERCLA) because they are ARARS. Exceedance of a Tier II value implies a greater

than 20% chance that the NAWQC, if their value wer e known, would be exceeded. Exceedance of a CV

indicates that the field concentration is greater than a concentration dividing statistically insignificant

from significant effects in a chronic toxicity test. Exceedance of a test EC20 indicates that biologically

significant effects levels were exceeded in a chronic toxicity test. Exceedance of the SS test EC2 0

indicates that a biologically significant effect level may be exceeded in a sensitive species. Exceedance

of a population EC20 indicates that a significant reduction in a largemouth bass population could occur.

Therefore, exceedance of either the acute or chronic NAWQC indicates a need for action. Exceedance

of an SCV implies a low risk. Exceedance of any of the other benchmarks indicates a risk of real effects

that should lead to additional data collection and assessment. However, these inferences all depend on

comparison of the benchmarks to appropriate water concentrations.

Contaminant screening is not a regulatory process, but managers at some sites prefer to use only

values that have regulatory standing. The NAWQC are clearly regula tory values in that they are ARARS

and have been adopted by Tennessee and most other states as water quality standards. Lowest chronic

values (the last column in Table 1) have been presented by the EPA in place of NAWQC (EPA 1986b),

but they are not criteria. They merely indicate that the EPA believes toxic effects may occur at tha t

concentration. The Tier II values (SAV and SCV) are proposed by the EPA as values that could be used

for regulatory enforcement in the Great Lakes (EPA 1993a). Th ey are more conceptually consistent with

the NAWQC than lowest chronic values and may come to have the same standing as NAWQC, bu t

currently they are only proposed by the EPA.

OSWER’s Ecotox Thresholds and Region IV’s screening values (or values proposed by othe r

regions) are alternative benchmark sets derived by the EPA. Both are based on NAWQC values ;

however, Region IV uses values adjusted to 50 ppm hardness which is unrealistically conservative for

most sites, while OSWER adjusts to dissolved-phase concentrations which are not available for most

screening assessments. In addition, Region IV uses NAWQCs based on fish marketability which is not

relevant to protecting aquatic life. Therefore, the standard EPA Office of Water NAWQC values and

FCVs in Table 1 will be more useful in most cases. When NAWQCs are not available, the ET s

correspond to SCVs, but some of the SCVs have been superseded by values presented in Table 1 of this

document. When NAWQCs are not available, the SVs are based on divisions of lowest toxic values by

10 or 100 which is equivalent to derivation of SAVs and SCVs but is not as scientifically defensible.

Therefore, for the Oak Ridge Reservation and many other sites, the NAWQCs and Tier II values listed

in Table 1 are generally preferable to either the ETs or SVs.

As discussed in the introduction, the chronic benchmarks are to be used as lower screenin g

benchmarks. The acute NAWQC and SAVs are to be used as upper screening benchmarks. However,

because of their conservatism, exceedance of the SAV cannot be taken to indicate that severe effects are

likely to be occurring. If an SAV is exceeded, the assessor should examine the acute values used t o

generate the Tier II values (Appendix A) and judge whether in fact severe effects are likely.
35

All of these benchmarks are based on toxicity tests conducted in the laboratory. Therefore, the y

should be compared to water concentrations that are as equivalent as possible to concentrations in test

water which is nearly all dissolved. The EPA Office of Water has decided that for metals the appropriate

comparison is to concentrations in 0.1 to 0.45 μm filtered ambient water (HECD 1992, Prothro 1993).

Acid soluble or even total recoverable concentrations, rather than dissolved concentrations, are ofte n

reported because they are required for human health risk assessments. In addition, Region IV and most

other EPA regional offices require use of acid soluble concentrations in ecological risk assessments for

the sake of conservatism. However, acid soluble concentrations of metals typically include 30 to 95%

particle bound material (HECD 1992). Therefore, acid soluble c oncentrations should be used for aquatic

ecological risk assessments to satisfy the regional regulators, but dissolved concentrations should also

be used if possible for a realistic screening of the chemicals and to make realistic estimates of risk.

The NAWQC for hardness dependent metals are based on a hardness of 100 mg/L, which i s

appropriately conservative for ambient waters on the Oak Ridge Reservation. If these benchmarks are

applied to a site with hard or soft water, the NAWQC for those metals should be recalculated a s

recommended by the EPA. 

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39

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40

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Protection Agency, Washington, D.C.

EPA. 1980c. Ambient water quality criteria for benzidene. EPA 440/5-80-023. U.S. Environmental

Protection Agency, Washington, D.C.

EPA. 1980d. Ambient water quality criteria for benzene. EPA 440/5-80-018. U.S. Environmental

Protection Agency, Washington, D.C.

EPA. 1980e. Ambient water quality criteria for benzidene. EPA 440/5-80-023. U.S. Environmental

Protection Agency, Washington, D.C.

EPA. 1980f. Ambient water quality criteria for beryllium. EPA 440/5-80-024. U.S. Environmental

Protection Agency, Washington, D.C.

EPA. 1980g. Ambient water quality criteria for cadmium. EPA 440/5-80-025. U.S. Environmental

Protection Agency, Washington, D.C.

EPA. 1980h. Ambient water quality criteria for carbon tetrachloride. EPA 440/5-80-026.

U.S. Environmental Protection Agency, Washington, D.C.

EPA. 1980i. Ambient water quality criteria for chlordane. EPA 440/5-80-027. U.S. Environmental

Protection Agency, Washington, D.C.

EPA. 1980j. Ambient water quality criteria for chlorinated benzenes. EPA 440/5-80-028.

U.S. Environmental Protection Agency, Washington, D.C.

EPA. 1980k. Ambient water quality criteria for chlorinated ethanes. EPA 440/5-80-029.

U.S. Environmental Protection Agency, Washington, D.C.

EPA. 1980l. Ambient water quality criteria for chloroform. EPA 440/5-80-033. U.S. Environmental

Protection Agency, Washington, D.C.

EPA. 1980m. Ambient water quality criteria for DDT. EPA 440/5-80-038. U.S. Environmental

Protection Agency, Washington, D.C.

EPA. 1980n. Ambient water quality criteria for dichloroethylenes. EPA 440/5-80-041.

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440/5-80-043. U.S. Environmental Protection Agency, Washington, D.C.
41

EPA. 1980p. Ambient water quality criteria for ethylbenzene. EPA 440/5-80-048. U.S. Environmental

Protection Agency, Washington, D.C.

EPA. 1980q. Ambient water quality criteria for fluoranthene. EPA 440/5-80-049.

U.S. Environmental Protection Agency, Washington, D.C.

EPA. 1980r. Ambient water quality criteria for heptachlor. EPA 440/5-80-052. U.S. Environmental

Protection Agency, Washington, D.C.

EPA. 1980s. Ambient water quality criteria for hexachlorocyclohexane. EPA 440/5-80-054.

U.S. Environmental Protection Agency, Washington, D.C.

EPA. 1980t. Ambient water quality criteria for naphthalene. EPA 440/5-80-059. U.S. Environmental

Protection Agency, Washington, D.C.

EPA. 1980u. Ambient water quality criteria for nitrophenols. EPA 440/5-80-063.

U.S. Environmental Protection Agency, Washington, D.C.

EPA. 1980v. Ambient water quality criteria for phenol. EPA 440/5-80-066. U.S. Environmental

Protection Agency, Washington, D.C.

EPA. 1980w. Ambient water quality criteria for phthalate esters. EPA 440/5-80-067.

U.S. Environmental Protection Agency, Washington, D.C.

EPA. 1980x. Ambient water quality criteria for polychlorinated biphenyls. EPA 440/5-80-068.

U.S. Environmental Protection Agency, Washington, D.C.

EPA. 1980y. Ambient water quality criteria for silver. EPA 440/5-80-071. U.S. Environmental

Protection Agency, Washington, D.C.

EPA. 1980z. Ambient water quality criteria for beryllium. NTIS, Springfield, Virginia.

EPA. 1980aa. Ambient water quality criteria for tetrachloroethylene. EPA 440/5-80-073.

U.S. Environmental Protection Agency, Washington, D.C.

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Appendix A

DATA USED FOR TIER II CALCULATIONS
Table A.1. Data and calculated results for derivation of Tier II values (all values in μg/l). Requirements are listed in App. B.2; other terms 

are defined in the text

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference b c

INORGANICS

Arsenic V

Bosmina longirostris 4 EC50 850 850 Passino and Novak, 1984

Daphnia pulex 4 LC50 3,600 3,600 Jurewicz and Buikema, 1980

Gambusia affinis 2,3 LC50 49,000 49,000 Jurewicz and Buikema, 1980

Morone saxatilis 2,3 LC50 40,500 Palawski et al., 1985

Morone saxatilis 2,3 LC50 30,500 35,150 Palawski et al., 1985

Oncorhynchus kisutch 1 LC50 43,600 Buhl and Hamilton, 1990

Oncorhynchus kisutch 1 LC50 58,500 Buhl and Hamilton, 1990

Oncorhynchus mykiss 1 LC50 28,000 Palawski et al., 1985

Oncorhynchus mykiss 1 LC50 67,500 46,860 Buhl and Hamilton, 1990

Pimephales promelas 2,3 LC50 42,000 Palawski et al., 1985

Pimephales promelas 2,3 LC50 25,600 32,790 DeFoe, 1982

Pimephales promelas CV 892 28.7 DeFoe, 1982

Thymallus arcticus 1 LC50 5,020 Buhl and Hamilton, 1990

Thymallus arcticus 1 LC50 5,500 5,255 Buhl and Hamilton, 1990

Tubifex tubifex 7,8 LC50 127,360 127,360 Fargasova, 1994

Tier II Parameters Tier II Values

FAVF 12.9

SAV 65.89

SACR 20.95

SCV 3.1

 The eight acute data requirements. a

 Genus Mean Acute Value. b

 Acute-Chronic Ratio. c
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Barium

Daphnia magna 4 LC50 410,000 410,000 LeBlanc, 1980

Daphnia magna EC16 5,800 70.69 Biesinger and Christensen, 1972 a

Echinogammarus berilloni 5 LC50 122,000 122,000 Vincent et al., 1986

Gammarus pulex 5 LC50 238,000 238,000 Vincent et al., 1986

Potamopyrgus jenkinsi 7,8 LC50 1,700 Vareille-Morel, 1990

Potamopyrgus jenkinsi 7,8 LC50 930 Vareille-Morel, 1990

Potamopyrgus jenkinsi 7,8 LC50 1,800 Vareille-Morel, 1990

Potamopyrgus jenkinsi 7,8 LC50 1,400 Vareille-Morel, 1990

Potamopyrgus jenkinsi 7,8 LC50 1,100 Vareille-Morel, 1990

Potamopyrgus jenkinsi 7,8 LC50 440 Vareille-Morel, 1990

Potamopyrgus jenkinsi 7,8 LC50 330 Vareille-Morel, 1990

Potamopyrgus jenkinsi 7,8 LC50 1,300 976.6 Vareille-Morel, 1990

Tier II Parameters Tier II Values

FAVF 8.6

SAV 113.6

SACR 28.29

SCV 4.0

 In the absence of any experimental value, EC16 is used to calculate an A-C ratio. a
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Beryllium

Asellus intermedius 5 LC50 10,000 10,000 Ewell et al., 1986

Dugesia tigrina 7,8 LC50 10,000 10,000 Ewell et al., 1986

Gammarus fasciatus 5 LC50 700 700 Ewell et al., 1986

Helisoma trivolvis 7,8 LC50 10,000 10,000 Ewell et al., 1986

Lumbriculus variegatus 7,8 LC50 10,000 10,000 Ewell et al., 1986

Pimephales promelas 2,3 LC50 10,000 10,000 Ewell et al., 1986

Ambystoma maculatum 2,3 LC50 3,150 Slonim and Ray, 1975

Ambystoma maculatum 2,3 LC50 18,200 Slonim and Ray, 1975

Ambystoma maculatum 2,3 LC50 8,020 Slonim and Ray, 1975

Ambystoma maculatum 2,3 LC50 8,320 Slonim and Ray, 1975

Ambystoma opacum 2,3 LC50 3,150 4,977 Slonim and Ray, 1975

Caenorhabditis elegans 7,8 LC50 140 140 Williams and Dunsenbery, 1990

Carassius auratus 2,3 LC50 55,900 55,900 Cardwell et al., 1976

Daphnia magna 4 EC50 2,410 Kimball n.d.

Daphnia magna 4 EC50 2,450 2,430 Kimball n.d.

Daphnia magna CV 5.267 461.4 Kimball n.d.

Jordanella floridae 2,3 LC50 46,300 Cardwell et al., 1976

Jordanella floridae 2,3 LC50 41,100 Cardwell et al., 1976

Jordanella floridae 2,3 LC50 41,100 42,760 Cardwell et al., 1976

Pimephales promelas 2,3 LC50 37,900 Cardwell et al., 1976

Pimephales promelas 2,3 LC50 17,900 Kimball n.d.

Pimephales promelas 2,3 LC50 17,500 22,810 Kimball n.d.

Poecilia reticulata 2,3 LC50 1,330 Slonim and Slonim, 1973

Poecilia reticulata 2,3 LC50 160 Slonim and Slonim, 1973

Poecilia reticulata 2,3 LC50 190 Slonim and Slonim, 1973
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Poecilia reticulata 2,3 LC50 1,330 343.2 Slonim and Slonim, 1973

Tubifex tubifex 7,8 EC50 10,250 10,250 Khangarot, 1991

Tier II Parameters Tier II Values

FAVF 4.0

SAV 35

SACR 52.88

SCV 0.66
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Boron

Daphnia magna 4 LC50 133,000 Gersich, 1984

Daphnia magna CV 9,330 Gersich, 1984

Daphnia magna 4 LC50 226,000 173,400 Lewis and Valentine, 1981

Daphnia magna CV 8,832 19.10 Lewis and Valentine, 1981 a

Ptychocheilus lucius 2,3 LC50 279 Hamilton, 1995

Ptychocheilus lucius 2,3 LC50 >100 Hamilton, 1995

Ptychocheilus lucius 2,3 LC50 527 383.4 Hamilton, 1995

Xyrauchen texanus 2,3 LC50 >100 Hamilton, 1995

Xyrauchen texanus 2,3 LC50 233 Hamilton, 1995

Xyrauchen texanus 2,3 LC50 279 255.0 Hamilton, 1995

Gila elegans 2,3 LC50 >100 Hamilton, 1995

Gila elegans 2,3 LC50 280 Hamilton, 1995

Gila elegans 2,3 LC50 552 393.1 Hamilton, 1995

Tier II Parameters Tier II Values

FAVF 8.6

SAV 29.65

SACR 18.29

SCV 1.6

 The A-C Ratio for D. magna is the geometric mean of A-C Ratios from Gersich, 1987 and Lewis and Valentine, 1981. a
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Cobalta

Asellus intermedius 5 LC50 >100,000 Ewell et al., 1986

Carassius auratus 2,3 LC50 66,800 66,800 Ding, 1980

Cyprinus carpio 2,3 LC50 82,700 82,700 Ding, 1980

Daphnia magna 4 EC50 6,830 Kimball, 1978

Daphnia magna 4 EC50 5,150 5,931 Kimball, 1978

Daphnia magna CV 5.103 1,162 Kimball, 1978

Dugesia tigrina 7,8 LC50 25,000 25,000 Ewell et al., 1986

Gammarus fasciatus 5 LC50 >100,000 Ewell et al., 1986

Helisoma trivolvis 7,8 LC50 >100,000 Ewell et al., 1986

Lumbriculus variegatus 7,8 LC50 >100,000 Ewell et al., 1986

Philodina acuticornis 7,8 EC50 59,000 59,000 Buikema et al., 1974

Pimephales promelas 2,3 LC50 22,000 Ewell et al., 1986

Pimephales promelas 2,3 LC50 3,750 Kimball, 1978

Pimephales promelas 2,3 LC50 3,460 6,584 Kimball, 1978

Pimephales promelas CV 286.2 12.59 Kimball, 1978

Rana hexadactyla 3 LC50 17,590 17,590 Khangarot et al., 1985

Tubifex tubifex 7,8 EC50 139,320 139,320 Khangarot, 1991

Tier II Parameters Tier II Values

FAVF 4.0

SAV 1,483

SACR 63.98

SCV 23

 All data are for cobalt II. a
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Lithium

Ptychocheilus lucius 2,3 LC50 28,000 Hamilton, 1995

Ptychocheilus lucius 2,3 LC50 41,000 33,880 Hamilton, 1995

Xyrauchen texanus 2,3 LC50 53,000 Hamilton, 1995

Xyrauchen texanus 2,3 LC50 186,000 99,290 Hamilton, 1995

Gila elegans 2,3 LC50 62,000 Hamilton, 1995

Gila elegans 2,3 LC50 65,000 63,480 Hamilton, 1995

Tubifex tufifex 7,8 EC50 9,340 9,340 Khangarto, 1991

Tier II Parameters Tier II Values

FAVF 36.2

SAV 258.0

SACR 17.9

SCV 14
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Manganesea

Asellus aquaticus 5 EC50 333,000 333,000 Martin and Holdich, 1986

Crangonyx pseudogracilis 5 EC50 694,000 694,000 Martin and Holdich, 1986

Daphnia magna 4 EC50 19,500 Kimball n.d.

Daphnia magna 4 EC50 19,200 19,350 Kimball n.d.

Pimephales promelas 2,3 LC50 30,600 Kimball n.d.

Pimephales promelas 2,3 LC50 36,900 33,600 Kimball n.d.

Pimephales promelas CV 1,775 18.93 Kimball n.d.

Tier II Parameters Tier II Values

FAVF 8.6

SAV 2,250

SACR 18.24

SCV 120

 All data are for manganese II. a
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Mercury, methyl

Oncorhynchus mykiss 1 LC50 24 24 Lock and van Overbeeke, 1981

Salvelinus fontinalis 1 LC50 65 McKim et al., 1976

Salvelinus fontinalis 1 LC50 84 74 McKim et al., 1976

Salvelinus fontinalis CV 0.5193 142.3 McKim et al., 1976

Tier II Parameters Tier II Values

FAVF 242

SAV 0.09917

SACR 35.72

SCV 0.0028
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Molybdenuma

Daphnia magna 4 LC50 203,200 Kimball n.d.

Daphnia magna 4 LC50 210,300 206,700 Kimball n.d.

Daphnia magna CV 877.8 235.5 Kimball n.d.

Pimephales promelas 2,3 LC50 628,000 628,000 Kimball n.d.

Tier II Parameters Tier II Values

FAVF 13.2

SAV 15,660

SACR 42.26

SCV 370

 All tests are for molybdenum VI. a
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Strontium

Daphnia magna 4 LC50 125,000 125,000 Biesinger and Christensen, 1972

Daphnia magna EC16 42,000 2.98 Biesinger and Christensen, 1972 a

Tubifex tubifex 7,8 EC50 240,800 240,800 Khangarot, 1991

Caenorhabditis elegans 7,8 LC50 465,000 465,000 Williams and Dusenbery, 1990 

Tier II Parameters Tier II Values

FAVF 8.6

SAV 14,530

SACR 9.85

SCV 1,500

In the absence of any experimental chronic values, EC16 is used to calculate an A-C Ratio. a 
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Thalliuma

Daphnia magna 4 EC50 880 Kimball, n.d.

Daphnia magna 4 EC50 930 905.0 Kimball, n.d.

Daphnia magna CV 134.5 6.724 Kimball, n.d.

Cyprinodon variegatus LC50 20,900 EPA, 1978 b

Cyprinodon variegatus CV 6,010 3.478 EPA, 1978

Lepomis macrochirus 2,3 LC50 120,000 Buccafusco et al., 1981

Lepomis macrochirus 2,3 LC50 132,000 125,900 Dawson et al., 1977

Pimephales promelas 2,3 LC50 1,810 Kimball, n.d.

Pimephales promelas 2,3 LC50 1,780 1,795 Kimball, n.d.

Pimephales promelas CV 56.92 31.53 Kimball, n.d.

Tier II Parameters Tier II Values

FAVF 8.6

SAV 105.2

SACR 9.034

SCV 12

 All data are for thallium I. a

 Acute value of C. variegatus, a saltwater species, is used for SACR calculation only. b
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Tina

Daphnia magna 4 LC50 55,000 55,000 Biesinger and Christensen, 1972

Daphnia magna EC16 350 157.1 Biesinger and Christensen, 1972 b

Tier II Parameters Tier II Values

FAVF 20.5

SAV 2,683

SACR 36.93

SCV 73

 All data are for tin II. a

 In the absence of any experimental chronic values, EC16 is used to calculate an A-C Ratio. b
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Uranium

Salvelinus fontinalis 1 LC50 5,500 Parkhurst et al., 1984

Salvelinus fontinalis 1 LC50 23,000 11,250 Parkhurst et al., 1984

Tier II Parameters Tier II Values

FAVF 242

SAV 46.48

SACR 17.9

SCV 2.6
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Vanadiuma

Daphnia magna 4 EC50 1,580 Kimball, n.d.

Daphnia magna 4 EC50 1,460 Kimball, n.d.

Daphnia magna 4 EC50 3,800 Bensen &Neven, 1987

Daphnia magna 4 EC50 2,900 Bensen &Neven, 1987

Daphnia magna 4 EC50 3,900 Bensen &Neven, 1987

Daphnia magna 4 EC50 3,600 Bensen &Neven, 1987

Daphnia magna 4 EC50 3,300 2,746 Bensen &Neven, 1987

Daphnia magna CV 1900 2 Bensen &Neven, 1987 b

Gala elegans 2,3 LC50 8,800 Hamilton, 1995

Gala elegans 2,3 LC50 4,000 Hamilton, 1995

Gala elegans 2,3 LC50 3,000 4,727 Hamilton, 1995

Jordanella floridae 2,3 LC50 11,200 11,200 Holdway and Sprague, 1979

Jordanella floridae CV 83.49 134.1 Holdway and Sprague, 1979

Oncorhynchus tshawytscha 1 LC50 16,500 16,500 Hamilton and Buhl, 1990

Pimephales promelas 2,3 LC50 1,800 Kimball, n.d.

Pimephales promelas 2,3 LC50 1,900 1,850 Kimball, n.d.

Pimephales promelas CV 169.7 10.90 Kimball, n.d.

Ptychocheilus lucius 2,3 LC50 7,800 Hamilton, 1995

Ptychocheilus lucius 2,3 LC50 3,800 Hamilton, 1995

Ptychocheilus lucius 2,3 LC50 4,300 5,032 Hamilton, 1995

Salvelinus fontinalis 1 LC50 7,000 Ernst and Garside, 1987

Salvelinus fontinalis 1 LC50 15,000 10,250 Ernst and Garside, 1987

Xyrauchen texanus 2,3 LC50 5,300 Hamilton, 1995
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Xyrauchen texanus 2,3 LC50 2,200 Hamilton, 1995

Xyrauchen texanus 2,3 LC50 4,600 3,770 Hamilton, 1995

Tier II Parameters Tier II Values

FAVF 6.5

SAV 284.6

SACR 14.29

SCV 20

 All data are for vanadium V. a

 Since the experimental A-C Ratio is less than 2, the A-C Ratio of D. magna is et to 2 (Stephan et al., 1985). b
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Zirconium

Oncorhynchus mykiss 1 LC50 20,000 20,000 Couture et al., 1989

Tubifex tubifex 7,8 EC50 221,180 221,180 Khangarot, 1991

Tier II Parameters Tier II Values

FAVF 64.8

SAV 308.6

SACR 17.9

SCV 17
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

ORGANICS

Acetone

Asellus intermedius 5 LC50 >100,000 >100,000 Ewell et al., 1986

Ceriodaphnia dubia 4 LC50 8,098,000 8,098,000 Cowgill and Milazzo, 1991

Chironomus tentans 6 LC50 46,900,000 46,900,000 Ziegenfuss et al., 1986

Corbicula manilensis 7,8 LC50 20,000,000 20,000,000 Chandler and Marking, 1979

Daphnia magna 4 EC50 13,500,000 13,500,000 Randall and Knopp, 1980

Daphnia magna 4 LC50 30,640 LeBlanc and Surprenant, 1983 a

Daphnia magna CV 1,556 19.69 LeBlanc and Surprenant, 1983

Dugesia tigrina 7,8 LC50 >100,000 >100,000 Ewell et al., 1986

Gammarus fasciatus 5 LC50 >100,000 >100,000 Ewell et al., 1986

Helisoma trivolvis 7,8 LC50 >100,000 >100,000 Ewell et al., 1986

Lepomis macrochirus 2,3 LC50 8,300,000 8,300,000 Cairns and Scheier, 1968

Lumbriculus variegatus 7,8 LC50 >100,000 >100,000 Ewell et al., 1986

Oncorhynchus mykiss 1 LC50 5,540,000 5,540,000 Johnson and Finley, 1980

Pimephales promelas 2,3 EC50 7,280,000 Brooke et al., 1984

Pimephales promelas 2,3 EC50 8,120,000 Brooke et al., 1984

Pimephales promelas 2,3 EC50 6,210,000 7,160,000 Brooke et al., 1984

Tier II Parameters Tier II Values

FAVF 3.6

SAV 27,780

SACR 18.48

SCV 1500

Since the acute test was part of the same study as the chronic test, the acute value was used to derive an ACR for D. magna. The LC50 value was not used as part of GMAV because EC50 for immobilization is available. a 
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Anthracene

Daphnia magna 4 EC50 95 Munoz and Tarazona, 1993

Daphnia pulex 4 EC50 754 267.6 Smith et al., 1988

Tier II Parameters Tier II Values

FAVF 20.5

SAV 13.06

SACR 17.9

SCV 0.73
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Benzene

Asellus aquaticus 5 LC50 254,000 254,000 Erben and Pisl, 1993

Carassius auratus 2,3 LC50 34,420 34,420 Pickering and Henderson, 1966

Chironomus thummi 6 LC50 100,000 100,000 Sloff, 1983

Cottus cognatus 2,3 LC50 13,500 13,500 Moles et al., 1979

Daphnia magna 4 LC50 200,000 LeBlanc, 1980

Daphnia magna 4 LC50 400,000 Canton and Adema, 1978

Daphnia magna 4 LC50 620,000 Canton and Adema, 1978

Daphnia magna 4 LC50 412,000 Canton and Adema, 1978

Daphnia magna 4 LC50 356,000 Canton and Adema, 1978

Daphnia magna 4 LC50 412,000 Canton and Adema, 1978

Daphnia magna 4 LC50 356,000 376,200 Canton and Adema, 1978

Daphnia pulex 4 LC50 345,000 Canton and Adema, 1978

Daphnia pulex 4 LC50 265,000 302,400 Canton and Adema, 1978

Gasterosteus aculeatus 2,3 LC50 21,800 21,800 Moles et al., 1979

Ictalurus punctatus 2,3 LC50 425,000 425,000 Johnson and Finley, 1980

Lepomis macrochirus 2,3 LC50 22,490 22,490 Pickering and Henderson, 1966

Oncorhynchus gorbuscha 1 LC50 4,630 Moles et al., 1979

Oncorhynchus kisutch 1 LC50 12,350 Moles et al., 1979

Oncorhynchus mykiss 2,3 LC50 5,300 DeGraeve et al., 1982

Oncorhynchus mykiss 1 LC50 21,600 Hodson et al., 1984

Oncorhynchus nerka 1 LC50 9,430 Moles et al., 1979

Oncorhynchus tshawytscha 1 LC50 10,280 9,008 Moles et al., 1979

Pimephales promelas 2,3 LC50 24,600 Geiger et al, 1990
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Pimephales promelas 2,3 LC50 12,600 17,600 Geiger et al, 1990

Poecilia reticulata 2,3 LC50 36,600 Pickering and Henderson, 1966

Poecilia reticulata 2,3 LC50 28,600 32,350 Galassi et al., 1988

Salvelinus malma 2,3 LC50 10,430 Moles et al., 1979

Salvelinus malma 2,3 LC50 10,480 10,450 Moles et al., 1979

Thymallus arcticus 2,3 LC50 12,890 12,890 Moles et al., 1979

Tier II Parameters Tier II Values

FAVF 4.0

SAV 2,252

SACR 17.9

SCV 130
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Benzidine

Daphnia magna 4 EC50 600 600 Kuhn et al., 1989

Oncorhynchus mykiss 1 LC50 7,400 7,400 EPA, 1980c a

Salmo trutta lacustris 1 LC50 4,350 4,350 EPA, 1980c a

Notropis lutrensis 2,3 LC50 2,500 2,500 EPA, 1980c a

Tier II Parameters Tier II Values

FAVF 8.6

SAV 69.77

SACR 17.9

SCV 3.9

 The EPA criteria document was cited because the data come from an EPA internal investigation, which was not available. a
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Benzo(a)anthracene

Daphnia pulex 4 LC50 MOR 10 10 Trucco et al., 1983 a

Tier II Parameters Tier II Values

FAVF 20.5

SAV 0.4878

SACR 17.9

SCV 0.027

 The test was based on a non-standard, but conservative, exposure of 96 hours. The standard exposure is 48 hr for daphnids. a

The length of the Daphnid is 1.9-2.1 mm; the age of the Daphnid species is not available.
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Benzo(a)pyrene

Daphnia pulex 4 LC50 MOR 5 5 Trucco et al., 1983 a

Tier II Parameters Tier II Values

FAVF 20.5

SAV 0.2439

SACR 17.9

SCV 0.014

The test was based on a non-standard, but conservative, exposure of 96 hours. The standard exposure is 48 hr for daphnids. a

The length of the Daphnid is 1.9-2.1 mm; the age of the Daphnid species is not available.
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Benzoic acid

Gambusia affinis 2,3 LC50 180,000 180,000 Wallen et al., 1957 a

Tier II Parameters Tier II Values

FAVF 242

SAV 743.8

SACR 17.9

SCV 42

 Done in turbid water. a
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Benzyl alcohol

Lepomis macrochirus 2,3 LC50 10,000 10,000 Dawson et al., 1977

Pimephales promelas 2,3 LC50 460,000 460,000 Mattson et al., 1976

Tier II Parameters Tier II Values

FAVF 64.8

SAV 154.3

SACR 17.9

SCV 8.6
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

BHC (other than Lindane)

Daphnia magna 4 EC50 800 800 Canton et al., 1975

Tier II Parameters Tier II Values

FAVF 20.5

SAV 39.02

SACR 17.9

SCV 2.2
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Bis(2-ethylhexyl) phthalate

Chironomus plumosus 6 EC50 >18,000 Streufert et al., 1980

Daphnia pulex 4 EC50 133 133 LeBlanc, 1980

Daphnia magna 4 LC50 2,000 Adams & Heidolph, 1985 a

Daphnia magna CV 912 2.193 Adams & Heidolph, 1985

Gammarus pseudolimnaeus 4 LC50 >32,000 Sanders et al., 1973

Gasterosteus aculeatus 2,3 LC50 >300 van den Dikkenberg et al., 1989

Ictalurus punctatus 2,3 LC50 >100,000 Johnson and Finley, 1980

Jordanella floridae 2,3 LC50 >320 Adema et al., 1981

Lepomis macrochirus 2,3 LC50 >770,000 Buccafusco et al., 1981

Lepomis macrochirus 2,3 LC50 >100,000 Johnson and Finley, 1980

Oncorhynchus kisutch 1 LC50 >100,000 Johnson and Finley, 1980

Oncorhynchus mykiss 1 LC50 > 320 Adams et al., 1995

Pimephales promelas 2,3 LC50 >670 Adams et al., 1995

Pimephales promelas 2,3 LC50 >160 Adams et al., 1995

Rana pipiens 3 LC50 4,440 4,440 Birge et al., 1978

Tier II Parameters Tier II Values

FAVF 5.0

SAV 26.60

SACR 8.890

SCV 3.0

 This LC50 was used to calculate the A-C ratio, but not the GMAV because an EC50 was available. a
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

2-Butanone

Daphnia magna 4 EC50 5,091,000 5,091,000 Randall and Knopp, 1980

Pimephales promelas 2,3 LC50 3,200,000 3,200,000 Veith et al, 1983

Tier II Parameters Tier II Values

FAVF 13.2

SAV 242,400

SACR 17.9

SCV 14,000
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Carbon disfulfidea

Poecilia reticulata 2,3 LC50 MOR 4,000 4,000 Van Leeuwen et al., 1985

Tier II Parameters Tier II Values

FAVF 242

SAV 16.53

SACR 17.9

SCV 0.92

Although carbon disfulide is a volatile compound, static test was used because flow-through, measured tests are not available. a 
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Carbon tetrachloridea

Pimephales promelas 2,3 LC50 41,400 Geiger et al., 1990

Pimephales promelas 2,3 LC50 43,300 Kimball, n.d.

Pimephales promelas 2,3 LC50 42,900 42,530 Kimball, n.d.

Tier II Parameters Tier II Values

FAVF 242

SAV 175.7

SACR 17.9

SCV 9.8

 Because carbon tetrachloride is a volatile compound, only flow-through, measured tests were used. a
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C ratio Reference

Chlorobenzene

Carassius auratus 2,3 LC50 51,620 51,620 Pickering and Henderson, 1966

Ceriodaphnia dubia 4 LC50 7,900 Cowgill et al., 1985 a

Ceriodaphnia dubia 4 LC50 7,900 Cowgill et al., 1985 a

Ceriodaphnia dubia 4 LC50 11,400 8,927 Cowgill et al., 1985 a

Daphnia magna 4 LC50 86,000 LeBlanc, 1980

Daphnia magna 4 LC50 13,000 Cowgill et al., 1985 a

Daphnia magna 4 LC50 10,700 Cowgill et al., 1985 a

Daphnia magna 4 LC50 15,400 116,500 Cowgill et al., 1985 a

Lepomis macrochirus 2,3 LC50 7,400 7,400 Bailey et al., 1985

Oncorhynchus mykiss 1 LC50 7,460 7,460 Hodson et al., 1984

Pimephales promelas 2,3 LC50 16,900 16,900 Geiger et al., 1990

Poecilia reticulata 2,3 LC50 45,530 45,530 Pickering and Henderson, 1966

Tier II Parameters Tier II Values

FAVF 6.5

SAV 1,138

SACR 17.9

SCV 64

 Author indicated both D. magna and C. dubia/affinis are less sensitive to chlorobenzene at 24 C than at 20 C; thus, tests with 20 C were used to established a conservative a o o o

 estimate of the effect of chlorobenzene.
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Chloroforma

Ictalurus punctatus 2,3 LC50 75,000 75,000 Anderson and Lusty, 1980

Lepomis macrochirus 2,3 LC50 16,200 Anderson and Lusty, 1980

Lepomis macrochirus 2,3 LC50 22,300 Anderson and Lusty, 1980

Lepomis macrochirus 2,3 LC50 13,300 Anderson and Lusty, 1980

Lepomis macrochirus 2,3 LC50 18,300 Anderson and Lusty, 1980

Lepomis macrochirus 2,3 LC50 20,800 17,880 Anderson and Lusty, 1980

Micropterus salmoides 2,3 LC50 55,800 Anderson and Lusty, 1980

Micropterus salmoides 2,3 LC50 52,500 Anderson and Lusty, 1980

Micropterus salmoides 2,3 LC50 45,400 51,040 Anderson and Lusty, 1980

Oncorhynchus mykiss 1 LC50 18,200 Anderson and Lusty, 1980

Oncorhynchus mykiss 1 LC50 18,400 Anderson and Lusty, 1980

Oncorhynchus mykiss 1 LC50 22,100 Anderson and Lusty, 1980

Oncorhynchus mykiss 1 LC50 15,100 Anderson and Lusty, 1980

Oncorhynchus mykiss 1 LC50 17,100 18,040 Anderson and Lusty, 1980

Pimephales promelas 2,3 EC50 70,700 70,700 Geiger et al., 1990

Tier II Parameters Tier II Values

FAVF 36.2

SAV 493.9

SACR 17.9

SCV 28

 Because chloroform is a volatile compound, only flow-through, measured tests were used. a
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

p,p'DDD

Asellus brevicaudus 5 LC50 10 Sanders, 1972

Asellus brevicaudus 5 LC50 16 12.65 Mayer and Ellersieck, 1986

Bufo woodhousei 3 LC50 140 140 Sanders, 1970

Cypridopsis vidua 5 EC50 45 45 Mayer and Ellersieck, 1986

Daphnia pulex 4 EC50 3.2 3.2 Mayer and Ellersieck, 1986

Gammarus fasciatus 5 LC50 0.6 Sanders, 1972

Gammarus fasciatus 5 LC50 0.86 Sanders, 1972

Gammarus lacustris 5 LC50 0.64 0.68 Sanders, 1969

Ictalurus punctatus 2,3 LC50 1,500 15,000 Mayer and Ellersieck, 1986

Ischnura verticalis 6 LC50 34 34 Mayer and Ellersieck, 1986

Micropterus salmoides 2,3 LC50 42 42 Mayer and Ellersieck, 1986

Oncorhynchus mykiss 1 LC50 70 72 Mayer and Ellersieck, 1986

Palaemonetes kadiakensis 5 LC50 0.68 Sanders, 1972

Palaemonetes kadiakensis 5 LC50 2.4 1.3 Mayer and Ellersieck, 1986

Pimephales promelas 2,3 LC50 4,400 4,400 Mayer and Ellersieck, 1986

Polycelis felina 7,8 LC50 740 740 Kouyoumjian and Uglow, 1974

Pseudacris triseriata 3 LC50 400 400 Sanders, 1970

Pteronarcys californica 6 LC50 380 380 Sanders and Cope, 1968

Simocephalus serrulatus 4 EC50 4.5 4.5 Mayer and Ellersieck, 1986

Stizostedion vitreum 2,3 LC50 14 14 Mayer and Ellersieck, 1986

Tier II Parameters Tier II Values

FAVF 3.6

SAV 0.1889

SACR 17.9

SCV 0.011
Table A.1. (continued)
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Decanea

Daphnia magna 4 LC50 18,000 18,000 LeBlanc, 1980

Tier II Parameters Tier II Values

FAVF 20.5

SAV 878.0

SACR 17.9

SCV 49

 Although decane is a volatile compound, static test was used because flow-through tests were not available. a
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C ratio Reference

Di-n-butyl phthalate

Chironomus plumosus 6 EC50 760 760 Streufert et al., 1980

Daphnia magna 4 EC50 5200 5200 McCarthy and Whitmore, 1985

Daphnia magna CV 1004 5.179 McCarthy and Whitmore, 1985

Gammarus pseudolimnaeus 5 LC50 2100 2100 Johnson and Finley, 1980

Ictalurus punctatus 2,3 LC50 2900 2900 Johnson and Finley, 1980

Lepomis macrochirus 2,3 LC50 1200 Buccafusco et al., 1981

Lepomis macrochirus 2,3 LC50 700 916.5 Johnson and Finley, 1980

Oncorhynchus mykiss 1 LC50 1600 1600 Adams et al., 1995

Oncorhynchus mykiss CV 137.8 11.61 Rodes et al., 1995 a

Orconectes nais 5 LC50 10000 10000 Johnson and Finley, 1980 b

Pimephales promelas 2,3 LC50 1100 Geiger et al., 1985

Pimephales promelas 2,3 LC50 850 Geiger et al., 1985

Pimephales promelas 2,3 LC50 2020 McCarthy and Whitmore, 1985 c,d

Pimephales promelas 2,3 LC50 920 1148 Adams et al., 1995

Pimephales promelas CV 748.3 2.699 McCarthy and Whitmore, 1985

Tier II Parameters Tier II Values

FAVF 4.0

SAV 190.0

SACR 5.455

SCV 35

 Length of the test is 60 d post-hatch (99 d exposure); the National Guidelines recommend 90 d post-hatch for salmonids. a
Table A.1. (continued)

 Authors note toxicity is hardness(44-272 ppm) and pH(6.5-9.0) independent; no further data are available. b

 Derived from range-finding test. c

 ACR derived from acute test of larval fathead minnows is the only test available as part of the same study as the chronic test. The National Guidelines d

recommend using juvenile fish for deriving ACR. 

 Because of an accident during the experiment, length of the test is 20 d post-hatch; the National Guidelines recommend 28-32 d post-hatch for fish other than salmonids. However, the authors note since a larger number e

of fish died at 1.0 mg/L, "no evidence that additional exposure time would have produced any meaningful result".
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Dibenzofuran

Daphnia magna 4 LC50 1,700 1,700 LeBlanc, 1980

Pimephales promelas 2,3 EC50 780 Geiger et al., 1988

Pimephales promelas 2,3 EC50 980 874.3 Geiger et al., 1988

Tier II Parameters Tier II Values

FAVF 13.2

SAV 66.23

SACR 17.9

SCV 3.7
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

1,1-Dichloroethanea

Poecilia reticulata 2,3 LC50 202,000 202,000 Köneman, 1981

Tier II Parameters Tier II Values

FAVF 242

SAV 834.7

SACR 17.9

SCV 47

 Although 1,1-dichloroethane is a volatile compound, static test was used because flow-through test is not available. a
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C ratio Reference

1,2-Dichloroethanea

Daphnia magna 4 EC50 160,000 160,000 Richter et al., 1983

Pimephales promelas 2,3 LC50 116,000 116,000 Walbridge et al., 1983

Pimephales promelas CV 41,360 2.804 Benoit et al, 1985

Tier II Parameters Tier II Values

FAVF 13.2

SAV 8,788

SACR 9.649

SCV 910

 Because 1,2-Dichloroethane is a volatile compound, only flow-through, measured tests were used (static, measured tests for Daphnids). a
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

1,1-Dichlorolethenea

Pimephales promelas 2,3 LC50 MOR 108,000 108,000 Dill et al., 1980

Tier II Parameters Tier II Values

FAVF 242

SAV 446.3

SACR 17.9

SCV 25

 Although 1,1-dichloroethene is a volatile compound, static test is used because flow-through, measured tests are not available. a
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

1,2-Dichloroethenea

Lepomis macrochirus 2,3 LC50 140,000 140,000 Buccafusco, 1981

Daphnia magna 4 LC50 220,000 220,000 LeBlanc, 1980

Tier II Parameters Tier II Values

FAVF 13.2

SAV 10,610

SACR 17.9

SCV 590

 Although 1,2-dichloroethene is a volatile compound, static tests were used because flow-through, measured tests are not available. a
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

1,3-Dichloropropenea

Pimephales promelas 2,3 EC50 239 239 Geiger et al., 1990

Tier II Parameters Tier II Values

FAVF 242

SAV 0.9876

SACR 17.9

SCV 0.055

a Because 1,3-dichloropropene is a volatile compound, only flow-through measured test was used.
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Diethyl phthalate

Daphnia magna 4 EC50 86,000 86,000 Adams et al., 1995

Daphnia magna CV 38,410 2.239 Rhodes et al., 1995

Lepomis macrochirus 2,3 LC50 16,700 16,700 Adams et al., 1995

Pimephales promelas 2,3 LC50 31,800 Geiger et al., 1985

Pimephales promelas 2,3 LC50 17,000 23,250 Adams et al., 1995

Oncorhynchus mykiss 1 LC50 12,000 12,000 Adams et al., 1995

Tier II Parameters Tier II Values

FAVF 6.5

SAV 1,846

SACR 8.952

SCV 210
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Ethyl benzenea

Pimephales promelas 2,3 EC50 8,450 8,450 Geiger et al., 1990

Poecilia reticulata 2,3 LC50 9,600 9,600 Galassi et al., 1988

Tier II Parameters Tier II Values

FAVF 64.8

SAV 130.4

SACR 17.9

SCV 7.3

 Because ethyl benzene is a volatile compound, only flow-through, measured tests were used. a
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Hexane

Pimephales promelas 2,3 EC50 2,500 2,500 Geiger et al., 1990

Tier II Parameters Tier II Values

FAVF 242

SAV 10.33

SACR 17.9

SCV 0.58
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

2-Hexanone

Pimephales promelas 2,3 LC50 428,000 428,000 Geiger et al., 1986

Tier II Parameters Tier II Values

FAVF 242

SAV 1,769

SACR 17.9

SCV 99
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

1-Methylnaphthalene

Pimephales promelas 2,3 EC50 9,000 9,000 Mattson et al., 1976 

Tier II Parameters Tier II Values

FAVF 242

SAV 37.19

SACR 17.9

SCV 2.1
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

4-Methyl-2-pentanone

Pimephales promelas 2,3 LC50 540,000 Brooke et al., 1984

Pimephales promelas 2,3 LC50 505,000 522,200 Veith et al., 1983a

Pimephales promelas CV 77,360 6.750 Call et al., 1985

Tier II Parameters Tier II Values

FAVF 242

SAV 2,158

SACR 12.93

SCV 170
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

2-Methylphenol

Carassius auratus 2,3 LC50 MOR 23,250 23,250 Pickering and Henderson, 1966

Lepomis macrochirus 2,3 LC50 MOR 20,780 20,780 Pickering and Henderson, 1966

Oncorhynchus mykiss 1 LC50 MOR 8,400 8,400 DeGraeve et al., 1980

Pimephales promelas 2,3 LC50 14,000 Geiger et al., 1990

Pimephales promelas 2,3 LC50 18,200 15,960 DeGraeve et al., 1980

Poecilia reticulata 2,3 LC50 18,850 18,850 Pickering and Henderson, 1966

Tier II Parameters Tier II Values

FAVF 36.2

SAV 232.0

SACR 17.9

SCV 13
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Methylene chloride

Daphnia magna 4 LC50 MOR 220,000 220,000 LeBlanc, 1980

Lepomis macrochirus 2,3 LC50 MOR 220,000 220,000 Buccafusco et al., 1981

Pimephales promelas 2,3 EC50 330,000 330,000 Geiger, 1986

Pimephales promelas LC50 MOR 502,000 Dill et al., 1987 a

Pimephales promelas CV 108,540 4.625 Dill et al., 1987

Tier II Parameters Tier II Values

FAVF 8.6

SAV 25,580

SACR 11.40

SCV 2,200

 The LC50 value is used to calculate the ACR because it is part of the same study as the chronic test; but it is not used to determine the GMAV of Pimephales sp. a

because an EC50 is available.
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C ratio Reference

Napthalene

Daphnia magna 4 EC50 2,194 Munoz and Tarazona, 1993

Daphnia pulex 4 EC50 4,663 3,199 Smith et al., 1988

Oncorhynchus mykiss 1 LC50 1,600 1,600 DeGraeve et al., 1982

Pimephales promelas 2,3 LC50 6,140 Geiger et al., 1985

Pimephales promelas 2,3 LC50 7,900 6,965 DeGraeve et al., 1982

Pimephales promelas CV 619 12.77 DeGraeve et al., 1982

Tier II Parameters Tier II Values

FAVF 8.6

SAV 186.0

SACR 15.96

SCV 12
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

4-Nitrophenol

Daphnia magna 4 EC50 7,680 Keen and Baillod, 1985

Daphnia magna 4 EC50 4,700 6,008 Kuhn et al., 1989

Daphnia magna CV 7,071 2 Kuhn et al., 1989 a

Gammarus pseudolimnaeus 5 LC50 6,550 6,550 Howe et al., 1994

Ictalurus punctatus 2,3 LC50 15,000 15,000 Holcombe et al., 1984

Lepomis macrochirus 2,3 LC50 8,300 8,300 Buccafusco et al., 1981

Oncorhynchus mykiss 1 LC50 7,900 7,900 Hodson et al., 1984

Oncorhynchus mykiss CV 989.1 7.987 Hodson et al., 1991

Pimephales promelas 2,3 LC50 59,000 Phipps et al., 1981

Pimephales promelas 2,3 LC50 62,000 Phipps et al., 1981

Pimephales promelas 2,3 LC50 41,000 Holcombe et al., 1984

Pimephales promelas 2,3 LC50 37,300 Geiger et al., 1985

Pimephales promelas 2,3 LC50 41,000 Geiger et al., 1985

Pimephales promelas 2,3 LC50 58,600 48,760 Geiger et al., 1985

Tier II Parameters Tier II Values

FAVF 5.0

SAV 1,202

SACR 3.997

SCV 300

 Since the experimental A-C Ratio was less than 2, the A-C Ratio of D. magna is set to 2 (Stephan et al, 1985). a
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

N-Nitrosodiphenylamine

Daphnia magna 4 LC50 7,800 7,800 LeBlanc, 1980

Tier II Parameters Tier II Values

FAVF 20.5

SAV 3,805

SACR 17.9

SCV 210
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

2-Octanonea

Pimephales promelas 2,3 EC50 36,000 36,000 Brooke, 1984

Tier II Parameters Tier II Values

FAVF 242

SAV 148.8

SACR 17.9

SCV 8.3

Because 3-Octanone tests do not have standardard exposure, 2-Octanone tests, which have the standard exposure, were used. a
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

PCBs: total

Pimephales promelas 9.443 Nebeker et al., 1974

Tier I Parameters Tier I Values

FAV 2.0 EPA, 1980x

Tier II Parameters Tier II Values

SACR 14.64

SCV 0.14
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

PCBs: Aroclor 1221 ®

Oncorhynchus clarki 1 LC50 1,200 Mayer et al., 1977

Tier II Parameters Tier II Values

FAVF 242

SAV 4.959

SACR 17.9

SCV 0.28
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

PCBs: Aroclor 1232 ®

Oncorhynchus clarki 1 LC50 2,500 Johnson and Finley, 1980

Tier II Parameters Tier II Values

FAVF 242

SAV 10.33

SACR 17.9

SCV 0.58
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

PCBs: Aroclor 1242 ®

Gammarus pseudolimnaeus 5 LC50 72 Nebeker and Puglisi, 1974

Gammarus pseudolimnaeus 5 LC50 74 72.99 Nebeker and Puglisi, 1974

Ictalurus punctatus 2,3 LC50 >100 Johnson and Finley, 1980

Ischnura verticalis 7,8 LC50 400 400 Mayer et al., 1977

Oncorhynchus clarki 1 LC50 5,400 5,400 Mayer et al., 1977

Perca flavescens 2,3 LC50 >150 Johnson and Finley, 1980

Pimephales promelas 2,3 LC50 15 15 Nebeker et al., 1974

Pimephales promelas LC50 300 Nebeker et al., 1974 a

Pimephales promelas CV 9.000 33.33 Nebeker et al., 1974

Tier II Parameters Tier II Values

FAVF 12.9

SAV 1.163

SACR 22.02

SCV 0.053

a Because this value is more than ten times of another life stage, it is not used in the GMAV calculation. However, since the preferred life stage in deriving the A-C Ratio is juvenile, it is used in A-C Ratio derivation. 
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

PCBs: Aroclor 1248 ®

Gammarus pseudolimnaeus 5 LC50 MOR 29 29 Nebeker and Puglisi, 1974

Ictalurus punctatus 2,3 LC50 MOR >100 Johnson and Finley, 1980

Lepomis macrochirus 2,3 LC50 MOR 278 Stalling and Mayer, 1972

Lepomis macrochirus 2,3 LC50 690 438.0 Johnson and Finley, 1980

Oncorhynchus clarki 1 LC50 5,750 5,750 Johnson and Finley, 1980

Perca flavescens 2,3 LC50 >100 Johnson and Finley, 1980

Tier II Parameters Tier II Values

FAVF 20.1

SAV 1.443

SACR 17.9

SCV 0.081
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

PCBs: Aroclor 1254 ®

Coregonus hoyi 1 LC50 >10,000 Passino and Kramer, 1980

Gammarus fasciatus 5 LC50 2,400 2,400 Johnson and Finley, 1980

Ictalurus punctatus 2,3 LC50 >200 Johnson and Finley, 1980

Ischnura verticalis 6 LC50 200 200 Mayer et al., 1977

Lepomis macrochirus 2,3 LC50 2,740 2,740 Johnson and Finley, 1980

Oncorhynchus clarki 1 LC50 42,500 42,500 Johnson and Finley, 1980

Orconectes nais 5 LC50 100 100 Johnson and Finley, 1980

Perca flavescens 2,3 LC50 >150 Johnson and Finley, 1980

Pimephales promelas 2,3 LC50 7.7 7.7 Nebeker et al., 1974

Pimephales promelas CV 2.878 2.676 Nebeker et al., 1974

Tier II Parameters Tier II Values

FAVF 12.9

SAV 0.5969

SACR 17.9

SCV 0.033
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

PCBs: Aroclor 1260 ®

Ictalurus punctatus 2,3 LC50 >400 Johnson and Finley, 1980

Lepomis macrochirus 2,3 LC50 >400 Johnson and Finley, 1980

Oncorhynchus clarki 1 LC50 61,000 61,000 Mayer et al., 1977

Perca flavescens 2,3 LC50 >200 Johnson and Finley, 1980

Tier II Parameters Tier II Values

FAVF 36.2

SAV 1,685

SACR 17.9

SCV 94
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C ratio Reference

1-Pentanola

Pimephales promelas 2,3 LC50 472,000 472,000 Geiger et al., 1986

Tier II Parameters Tier II Values

FAVF 242

SAV 1950

SACR 17.9

SCV 110

Because 1-pentanol is a volatile compound, only flow-through, measured test was used. a
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

2-Propanol

Chironomus riparius 7 LC50 12,500,000 12,500,000 Roghair et al., 1994

Pimephales promelas 2,3 LC50 10,400 Veith et al., 1983

Pimephales promelas 2,3 LC50 9,640 Veith et al., 1983

Pimephales promelas 2,3 LC50 6,550 8,692 Brooke et al., 1984

Tier II Parameters Tier II Values

FAVF 64.8

SAV 134.1

SACR 17.9

SCV 7.5
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

1,1,2,2-Tetrachloroethanea

Daphnia magna 4 EC50 23,000 23,000 Richter et al., 1983

Daphnia magna CV 9,829 2.34 Richter et al., 1983

Jordanella floridae 2,3 LC50 18,480 18,480 Smith et al., 1991

Jordanella floridae CV 8,467 2.183 Smith et al., 1991

Pimephales promelas 2,3 LC50 20,400 Walbridge et al., 1983

Pimephales promelas 2,3 LC50 20,300 20,350 Geiger et al., 1985

Pimephales promelas CV 2,366 8.601 Ahmad et al., 1984

Tier II Parameters Tier II Values

FAVF 8.6

SAV 2,149

SACR 3.529

SCV 610

 Because 1,1,2,2-tetrachloroethane is a volatile compound, only flow-through, measured tests were used. a
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Tetrachloroethenea

Daphnia magna 4 EC50 8,500 8,500 Richter et al., 1983

Daphnia magna CV 750.0 11.33 Richter et al., 1983

Jordanella floridae 2,3 LC50 8,430 8,430 Smith et al., 1991

Jordanella floridae CV 3,107 2.714 Smith et al., 1991

Oncorhynchus mykiss 1 LC50 5,840 Shubat et al., 1982

Oncorhynchus mykiss 1 LC50 4,990 5,398 Shubat et al., 1982

Pimephales promelas 2,3 LC50 13,400 Walbridge et al., 1983

Pimephales promelas 2,3 LC50 20,300 16,490 Geiger et al., 1985

Pimephales promelas CV 836.7 19.71 Geiger et al., 1985

Tier II Parameters Tier II Values

FAVF 6.5

SAV 830.5

SACR 8.463

SCV 98

Because tetrachloroethene is a volatile compound, only flow-through, measured tests were used. a 
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Toluenea

Pimephales promelas 23 LC50 31,700 Geiger et al., 1990

Pimephales promelas 2,3 LC50 36,200 Geiger et al., 1986

Pimephales promelas 2,3 LC50 30,000 Devlin et al., 1982

Pimephales promelas 2,3 LC50 31,000 Devlin et al., 1982

Pimephales promelas 2,3 LC50 26,000 Devlin et al., 1982

Pimephales promelas 2,3 LC50 18,000 28,170 Devlin et al., 1982

Pimephales promelas CV 4,899 5.243 Devlin et al., 1982

Tier II Parameters Tier II Values

FAVF 242

SAV 116.4

SACR 11.89

SCV 9.8

 Because toluene is a volatile compound, only flow-through, measured tests were used. a
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

1,1,1-Trichloroethanea

Pimephales promelas 2,3 LC50 52,900 Geiger et al., 1986

Pimephales promelas 2,3 LC50 42,300 47,300 Geiger et al., 1986

Tier II Parameters Tier II Values

FAVF 242

SAV 195.5

SACR 17.9

SCV 11

 Because 1,1,1-trichloroethane is a volatile compound, only flow-through, measured tests were used. a
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

1,1,2-Trichloroethanea

Daphnia magna 4 EC50 81,000 81,000 Richter et al., 1983

Daphnia magna CV 18,385 4.406 Richter et al., 1983

Jordanella floridae 2,3 LC50 45,117 45,117 Smith et al., 1991

Jordanella floridae CV 46,609 2 Smith et al., 1991 b

Pimephales promelas 2,3 LC50 81,600 81,600 Ahmad et al., 1984

Pimephales promelas CV 9,423 8.659 Ahmad et al., 1984

Tier II Parameters Tier II Values

FAVF 8.6

SAV 5,246

SACR 4.241

SCV 1200

Because 1,1,2-trichloroethane is a volatile compound, only flow-through, measured tests were used. a 

 Since the experimental A-C Ratio is less than 2, the A-C Ratio of J. floridae is set to 2 (Stephan et al., 1985). b
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Trichloroethenea

Jordanella floridae 2,3 LC50 28,280 28,280 Smith et al., 1991

Jordanella floridae CV 11,057 2.558 Smith et al., 1991

Pimephales promelas 2,3 LC50 40,700 Alexander et al., 1978

Pimephales promelas 2,3 LC50 45,000 Walbridge et al., 1983

Pimephales promelas 2,3 LC50 44,100 43,230 Geiger et al., 1985

Tier II Parameters Tier II Values

FAVF 64.8

SAV 436.4

SACR 9.358

SCV 47

 Because trichloroethene is a volatile compound, only flow-through, measured tests were used. a
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C Ratio Reference

Vinyl acetatea

Carassius auratus 2,3 LC50 42,330 42,330 Pickering and Henderson, 1966

Lepomis macrochirus 2,3 LC50 18,000 18,000 Pickering and Henderson, 1966

Pimephales promelas 2,3 LC50 14,000 Pickering and Henderson, 1966

Pimephales promelas 2,3 LC50 15,000 Pickering and Henderson, 1966

Pimephales promelas 2,3 LC50 14,000 Pickering and Henderson, 1966

Pimephales promelas 2,3 LC50 15,000 Pickering and Henderson, 1966

Pimephales promelas 2,3 LC50 15,000 Pickering and Henderson, 1966

Pimephales promelas 2,3 LC50 23,000 Pickering and Henderson, 1966

Pimephales promelas 2,3 LC50 26,000 Pickering and Henderson, 1966

Pimephales promelas 2,3 LC50 20,000 Pickering and Henderson, 1966

Pimephales promelas 2,3 LC50 24,000 Pickering and Henderson, 1966 b

Pimephales promelas 2,3 LC50 19,730 18,090 Pickering and Henderson, 1966 b

Poecilia reticulata 2,3 LC50 31,080 31,080 Pickering and Henderson, 1966

Tier II Parameters Tier II Values

FAVF 64.8

SAV 277.8

SACR 17.9

SCV 16

 Although vinyl acetate is a volatile compound, static tests were used because flow-through, measured tests are not available. a

 Auther notes hardness influences toxicity; vinyl acetate is more toxic in soft water than hard water. b
Table A.1. (continued)

Compound Genus/species Requirement Endpoint Concentration GMAV A-C ratio Reference

Xylenea

Lepomis macrochirus 2,3 LC50 15,700 15,700 Bailey et al., 1985

Pimephales promelas 2,3 EC50 15,300 Geiger et al., 1990 b,d

Pimephales promelas 2,3 EC50 14,800 15,050 Geiger et al., 1990 c,d

Tier II Parameters Tier II Values

FAVF 64.8

SAV 232.3

SACR 17.9

SCV 13

 Because xylene is a volatile compound, only flow-through, measured tests were used. a

o-xylene (99+% purity) was used. b 

 m-xylene (99% purity) was used. c

 Because analytical procedures used at waste sites do not discriminate isomers, toxicity tests on individual and mixture of isomers are considered equivalent. d
Appendix B

METHODS FOR DERIVATION OF TIER II VALUES
B-3

METHODS FOR DERIVATION OF TIER II VALUES

B.1 Method for data selection

The procedure used to select and aggregate test data was adopted from the guidelines for deriving

National Ambient Water Quality Criteria (NAWQC) (Stephan et al. 1985). The selection criteria are

summarized in the following text.

B.1.1 Chemical Considerations

Not all forms of inorganic chemicals require unique Tier II values. Metal salts with the sam e

oxidation state at ambient conditions (e.g., BeCl 2 and BeSO4) are expected to exhibit similar toxicity and

are given a common Tier II value. Nonionizable, covalently bonded compounds of metals or metals of

different oxidation states were considered different chemicals, for which separate Tier II values wer e

derived. 

For volatile compounds, only results of flow-through tests with measured chemical concentrations

were used, if available. However, if flow-through measured tests were not available, the genus mea n

acute value (GMAV) was based on static and flow-through unmeasured tests. 

Pesticides were screened for commercial formulations; wettable powder, emulsifiable concentrates,

and formulated mixtures were eliminated. Only pesticides of technical grades or better were considered.

B.1.2 Dilution water considerations

Test results were rejected if unusual dilution water was used (e.g., TOC > 5 ppm, lack o f

appropriate salts, low dissolved oxygen), unless toxicity has been demonstrated to be independent o f

these factors. Tests in which dissolved oxygen fell below 40% saturation for static or 60% saturation

for flow-through were eliminated. 

B.1.3 Biological parameters

Tests of certain organisms were excluded from the Tier II value derivation. Single-celled organisms

and brine shrimp (Artemia sp.) were not used. Fish were generally limited to species with wild North

American populations. However, if none of the tests with North American fish were acceptable an d

values for other organisms were not available, non-resident fish were used. 

Tests which did not refer to a standard procedure or indicate use of a control group were excluded.

Acute tests in which organisms were fed were eliminated, unless feeding was demonstrated to b e

independent of toxicity.

For the acute tests, only daphnids and midges (Chironomus sp.) have a specified starting age.

Daphnids must be less than 24 hours of age at the start of the test. Midges in second or third insta r

larvae were preferred, but midge tests starting at fourth instar were accepted. Although the starting age

for all other organisms has not been specified, juvenile stages were preferred whenever they wer e

available (unless another life stage is more sensitive to the chemical). All organisms should receive a

96-hour exposure period, except daphnids and midges, where 48 hours is the standard exposure period.

The endpoint for daphnids and midges is the EC50 for immobilization. If this is not available, LC50
B-4

is used. For fish, the preferred endpoint is the EC50 for loss of equilibrium, immobilization, and/o r

mortality. If those are not available, LC50 is used. 

In chronic tests, the starting age, exposure duration, and endpoints may be different for daphnids

and fish and for salmonids and non-salmonids. Daphnids must be less than 24 hours old at the start of

the test, and the test should last at least 21 days . Endpoints are based on mortality and number of young

per female.

For a given fish species, preference is given to the following types of chronic tests in the order as

follows: full life cycle, partial life cycle, and early life stage. The less desirable chronic test is no t

included in the calculation if a more desirable type is available. 

B.1.4 Variation of Acute Values within the same genus

If the acute values within a species or among species in a genus differ by a factor of 10 or more,

the higher values were excluded, and those that are within the factor of 10 range were used to attain a

conservative estimate. If the acute concentrations of a given species differ by a factor of two or more

among different life stages, the more sensitive life stage is used to protect the organisms in all life stages.

B.1.5 ACR Considerations

If the acute chronic ratios (ACRs) for a chemical differ by more than a factor of 10, the tests were

carefully examined to determine whether outliers should be rejected. ACRs from saltwater specie s

should be used along with the freshwater ACRs when less than three ACRs from freshwater species are

available. If the lowest GMAV is from larvae of barnacles, bivalves, lobsters, crabs, shrimp, o r

abalones, the secondary acute chronic ratio (SACR) is assumed to be 2. If an ACR is less than 2 ,

acclimation may have occurred. The ACR is then set to 2. 

Preference was given to acute and chronic tests done in the same study. If these are not available,

an acute value with water characteristics similar to the chronic value was used. If values from similar

water are not available, the GMAV of the species is used with the chronic value to derive an ACR. If

multiple chronic values for a species are available but none are part of the same study as an acute test,

the geometric mean of the chronic values was calculated and used with the GMAV to derive an ACR for

that species.

B.1.6 Acceptable exposure types and life stage used to derive ACR

For daphnids, renewal is required for chronic tests; while for acute tests, static exposure i s

acceptable. All chronic test concentrations should be measured. The life stage of daphnids has to be 24

hours or younger at the start of both acute and chronic tests.

For fish, both acute and chronic tests require flow-through measured tests. For acute fish tests, the

life stage of the organism should be juvenile.

B.1.7 Other considerations

Concentrations above the solubility of chemicals and “greater than” values were used only when

at least one definitive concentration was available. 
B-5

B.2 Calculation method

Tier II values are derived if fewer than eight of the acute data requirements or three chronic data

requirements presented in EPA (1993a) are met. The eight acute data requirements include:

1. The family Salmonidae in the class Osteichthyes

2. One other family (preferably a commercially, or recreationally important, warmwater species)

in the class Osteichthyes (e.g., bluegill, channel catfish, etc.)

3. A third family in the phylum Chordata (e.g., fish, amphibian, etc.)

4. A planktonic crustacean (e.g., a cladocceran, copepod, etc.)

5. A benthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)

6. An insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.)

7. A family in a phylum other than Arthropoda or Chordata (e.g., Rotifera, Annelida, Mollusca,

etc.)

8. A family in any order of insect or any phylum not already represented

If all of these data requirements are not met, then an FAV is calculated. The FAV is a Tier I

criterion, and its derivation is documented in Stephan et al. (1985) and in Appendix A of EPA (1993a).

The FAV, however, is used in the derivation of the SCV if the chronic data requirements are not met.

Tier II values, as mentioned previously, are calculated when the data requirements are not met. The

first calculation of the Tier II criteria is the SAV. The SAV is derived by taking the lowest genus mean

acute value (GMAV) for any of the genera present and dividing it by a Final Acute Value Facto r

(FAVF). The FAVF is selected from Table B.1 where n is the number of the eight acute dat a

requirements that are satisfied. FAVFs are selected from the tw o columns depending on whether an acute

value (LC50 or EC50) for a daphnid is included in the data set.

Once the SAV is calculated, the Secondary Acute-Chronic Ratio (SACR) is derived. If three o r

more Acute-Chronic Ratios (ACRs) are present, then the SACR is determined by finding the geometric

mean of the ACRs. There must be at least three ACRs. If there are not three chronic values from the

literature, then a default value of 17.9 (EPA 1991) is used until the total number of ACRs is three. If

multiple ACRs are given for the same genus, then the geometric me an of those ACRs must be calculated.

This genus mean ACR can then be used in the derivation of the SACR. Therefore, several members of

the same genus can only present one value towards the mandatory three. If no ACRs are given, then the

SACR is 17.9.

 

The final calculation for Tier II values is the derivation of an SCV. The SCV is calculated b y

dividing the FAV or SAV by the SACR.

 
B-6

Table B.1. Factors for estimation of the Tier II values (EPA 1993 and Stephan 1991)

Number of GMAVs Factor for data sets that Factors for data sets that do a

include an acute value for a not include an acute value

daphnid for a daphnid b b

1 20.5 242

2 13.2 64.8

3 8.6 36.2

4 6.5 20.1

5 5.0 12.9

6 4.0 9.2

7 3.6 7.2

 GMAV is Genus Mean Acute Value a

 Daphnids includes members of the genera Daphnia, Ceriodaphnia, and Simocephalus.

b
Appendix C

TABLE SHOWING CONCENTRATIONS ESTIMATED TO CAUSE

A 20% REDUCTION IN THE RECRUIT ABUNDANCE OF

LARGEMOUTH BASS, WITH UPPER AND LOWER 95%

CONFIDENCE BOUNDS
Table C.1. Concentrations estimated to cause a 20% reduction in the recruit abundance of largemouth bass, with upper and lower 

95% confidence bounds. All units are ug/L

Chemical Test Species Test Lower Median Upper Source

Type 95% CL 95%CL

Ammonia Fathead minnow Chronic 3.98 100 1585 Mayes et al. 1986

Fathead minnow Chronic 3.98 32 200 Thurston et al. 

1986

Antimony Fathead minnow Acute 5.01 79 501 EPA 1980b

Arsenic III Fathead minnow Chronic 100 1995 31623 Call et al. 1983

Arsenic V Fathead minnow Acute 20 159 1000 EPA 1985a

Rainbow trout Acute 10 100 501 EPA 1985a

Mosquitofish Acute 32 398 2512 EPA 1985a

Beryllium Fathead minnow Acute 0.35 7.08 40 EPA 1980f

Bluegill Acute 2.00 32 126 EPA 1980f

Flagfish Acute 2.00 32 126 EPA 1980f

Guppy Acute 1.58 25 126 EPA 1980f

Cadmium Fathead minnow Chronic 1 10 79 Pickeringand Gast 1972

Bluegill Chronic 1.99 13 50 Eaton 1974

Brook trout Chronic 0.13 1.26 6.31 Benoit et al. 1976

Brook trout Chronic 0.32 3.16 25 Sauter et al. 1976

Flagfish Chronic 0.63 3.98 50 Carlson et al. 1982

Flagfish Chronic 0.79 3.16 7.94 Spehar 1976

Chromium III Rainbow trout Chronic 13 126 1000 Stevens and Chapman

1984

Chromium VI Fathead minnow Chronic 25 158 1260 Pickering 1980

Rainbow trout Chronic 100 631 5010 Sauter et al. 1976

Cobalt Fathead minnow Acute 0.16 3.98 32 Lind et al. 1978

Copper Fathead minnow Chronic 0.40 3.98 40 Mount 1968

Fathead minnow Chronic 0.32 3.16 16 Mount and Stephan 1969

Bluegill Chronic 1.995 13 50 Benoit 1975

Brook trout Chronic 1 3.98 16 McKim and Benoit

1971

Brook trout Chronic 1 5.01 40 Sauter et al. 1976

Coho salmon Chronic 3.16 32 316 Hazel and Meith 1970
Table C.1. (continued)

Chemical Test Species Test Lower Median Upper Source

Type 95% CL 95%CL

Rainbow trout Chronic 3.98 32 200 Seim et al. 1984

Cyanide Fathead minnow Chronic 0.20 2.51 16 Smith et al. 1979

Atlantic Salmon Chronic 1.99 16 200 Leduc 1978

Bluegill Chronic 5.01 25 158 Smith et al. 1979

Brook trout Chronic 1.58 13 79 Smith et al. 1979

Lead Brook trout Chronic 13 50 316 Holcombe et al.

1976

Rainbow trout Chronic 13 100 631 Sauter et al. 1976

Manganese Fathead minnow Acute 11 112 794 Kimball n.d.

Mercury, inorganic Fathead minnow Chronic 0.04 0.79 13 Call et al. 1983

Fathead minnow Chronic 0.01 0.13 3.16 Snarski and Olson 1982

Mercury, methyl Rainbow trout Acute 0.004 0.16 1.26 EPA 1985e

Brook trout Acute 0.02 0.50 3.98 EPA 1985e

Nickel Fathead minnow Chronic 32 126 501 Pickering 1974

Rainbow trout Chronic 13 63 398 Nebeker et al. 1985

Rainbow trout Chronic 126 1260 15800 Nebeker et al. 1985

Silver Fathead minnow Chronic 0.01 0.1 1 Holcombe et al. 1983

Rainbow trout Chronic 0.1 1 7.94 Nebeker et al. 1983

Thallium Fathead minnow Acute 0.25 4.47 40 EPA 1980bb

Bluegill Acute 73 1000 6310 EPA 1980bb

Uranium Fathead minnow Acute 0.398 10 50 Cushman et al. 1977

Fathead minnow Acute 0.501 10 50 Cushman et al. 1977

Fathead minnow Acute 0.631 13 79 Cushman et al. 1977

Fathead minnow Acute 32 398 3980 Cushman et al. 1977

Vanadium Fathead minnow Acute 0.28 5.01 40 Kimball n.d.

Brook trout Acute 5.01 63 398 Ernst and Garside 1987

Flagfish Acute 10 100 501 Holdway and Sprague

1979

Zinc Fathead minnow Chronic 3.98 40 316 Benoit and Holcombe

1978
Table C.1. (continued)

Chemical Test Species Test Lower Median Upper Source

Type 95% CL 95%CL

Fathead minnow Chronic 3.16 40 316 Brungs 1969

Coho salmon Chronic 16 126 794 Finlayson and Verrue

1980

Flagfish Chronic 6.31 32 126 Spehar 1976

Rainbow trout Chronic 40 501 5010 Sinley et al. 1974

Zirconium Fathead minnow Acute 3.16 50 316 Cushman et al. 1977

Fathead minnow Acute 3.16 50 398 Cushman et al. 1977

Fathead minnow Acute 32 398 3160 Cushman et al. 1977

Fathead minnow Acute 63 794 6310 Cushman et al. 1977

Bluegill Acute 10 126 501 Cushman et al. 1977

Bluegill Acute 200 2510 15800 Cushman et al. 1977

Organics

AC 222,705 Fathead minnow Chronic 0.0006 0.01 0.063 Spehar et al. 1983

Acetone Fathead minnow Acute 1780 19900 25100 AQUIREa

Bluegill Acute 3160 50100 501000 AQUIREa

Rainbow trout Acute 1260 31600 316000 AQUIREa

Mosquitofish Acute 631 10000 100000 AQUIREa

AG thiosulfate complex Fathead minnow Chronic 1000 10000 79400 LeBlanc et al. 1984 

Aldicarb Fathead minnow Chronic 3.16 50 631 Pickering and Giliam

1982

Atrazine Brook trout Chronic 100 1000 12600 Macek et al. 1976b

Benzene Fathead minnow Acute 10 100 794 EPA 1980d

Bluegill Acute 13 158 1000 EPA 1980d

Rainbow trout Acute 3.16 40 316 EPA 1980d

Mosquitofish Acute 200 3160 25100 EPA 1980d

Guppy Acute 32 316 1580 EPA 1980d

Benzidene Rainbow trout Acute 5.01 63 398 EPA 1980c

Lake trout Acute 3.16 40 251 EPA 1980c

Flagfish Acute 10 126 794 EPA 1980c

Benzoic acid Mosquitofish Acute 126 1260 10000 AQUIREa

Benzyl alcohol Fathead minnow Acute 16 1780 12600 AQUIREa

Bluegill Acute 6.31 79 398 AQUIREa

Bis(2-ethylhexyl)phthalate Rainbow trout Acute 100 1000 7940 AQUIREa

Largemouth bass Acute 25 316 1580 AQUIREa
Table C.1. (continued)

Chemical Test Species Test Lower Median Upper Source

Type 95% CL 95%CL

Channel catfish Acute 0.006 0.40 6.31 AQUIREa

2-Butanone Fathead minnow Acute 501 10000 100000 AQUIREa

Mosquitofish Acute 1990 31600 398000 AQUIREa

Captan Fathead minnow Chronic 0.32 3.16 20 Hermanutz et al. 1973

Carbaryl Fathead minnow Chronic 3.16 32 1000 Carlson 1971

Carbon disulfide Mosquitofish Acute 100 1000 7940 AQUIREa

Carbon tetrachloride Fathead minnow Acute 11 126 1260 EPA 1980h

Bluegill Acute 40 398 3160 EPA 1980h

Chloramine Fathead minnow Chronic 0.32 3.16 13 Arthur and Eaton 1971

Chlordane Bluegill Chronic 0.13 0.40 2.51 Cardwell et al. 1977

Brook trout Chronic 0.20 1.26 7.94 Cardwell et al. 1977

Chlorobenzene Fathead minnow Acute 11 112 794 EPA 1980j

Bluegill Acute 10 126 1000 EPA 1980j

Guppy Acute 32 316 2510 EPA 1980j

Chloroform Bluegill Acute 79 794 5010 EPA 1980l

Rainbow trout Acute 40 398 3160 EPA 1980l

p,p'DDD Fathead minnow Acute 0.79 13 100 AQUIREa

Bluegill Acute 0.002 0.1 1 AQUIREa

Rainbow trout Acute 0.02 0.40 3.16 AQUIREa

Largemouth bass Acute 0.003 0.13 1 AQUIREa

Channel catfish Acute 0.025 1.26 16 AQUIREa

2,4-D Butoxyethanol ester Coho salmon Chronic 10 100 1260 Finlayson and Verrue

1985

Diazinon Fathead minnow Chronic 0.32 3.16 25 Allison and Hermanutz

1977

Flagfish Chronic 10 50 316 Allison and Hermanutz

1977

Di-n-butyl phthalate Fathead minnow Chronic 13 251 3980 McCarthy and Whitmore

1985

2,6-Dichlorobenzamide Rainbow trout Chronic 1260 12600 50100 Van Leeuwen and Maas

1985

1,3-Dichlorobenzene Fathead minnow Chronic 316 1585 15849 Ahmad et al. 1984
Table C.1. (continued)

Chemical Test Species Test Lower Median Upper Source

Type 95% CL 95%CL

1,4-Dichlorobenzene Fathead minnow Chronic 32 398 6310 Ahmad et al. 1984

1,1-Dichloroethane Guppy Acute 158 1580 12600 AQUIREa

1,2-Dichloroethane Fathead minnow Acute 40 398 3160 EPA 1980k

Bluegill Acute 316 3980 31600 EPA 1980k

1,1-Dichloroethene Fathead minnow Acute 40 398 3160 EPA 1980n

Bluegill Acute 50 501 3980 EPA 1980n

2,4-Dichlorophenol Fathead minnow Chronic 32 200 1580 Holcombe et al. 1982

1,2-Dichloropropane Fathead minnow Chronic 398 3980 39800 Benoit et al. 1982

1,3-Dichloropropane Fathead minnow Chronic 501 5010 50100 Benoit et al. 1982

1,3-Dichloropropene Bluegill Acute 3.16 40 251 EPA 1980o

Diethyl phthalate Bluegill Acute 79 1000 6310 AQUIREa

2,4-Dimethylphenol Fathead minnow Chronic 100 1260 19900 Holcombe et al. 1982

Dimethyl phthalate Rainbow trout Chronic 0.004 0.04 0.40 Ward and Boeri 1991b

1,3-Dinitrobenzene Rainbow trout Chronic 100 1000 7940 Van Der Schalie 1983

Rainbow trout Chronic 63 794 6310 Van Der Schalie 1983

Dinoseb Fathead minnow Chronic 0.13 3.16 40 Call et al. 1983

Di-n-octyl phthalate Fathead minnow Chronic 200 1990 39800 McCarthy and Whitmore

1985

Diuron Fathead minnow Chronic 1 16 158 Call et al. 1983

Dursban Fathead minnow Chronic 0.002 0.032 0.20 Jarvinen et al. 1983

DNBP Rainbow trout Chronic 0.00004 0.0004 0.005 Ward and Boeri 1991a

Endrin Fathead minnow Chronic 0.005 0.13 1.58 Carlson et al. 1982

Endosulfan Fathead minnow Chronic 0.002 0.016 0.13 Macek et al. 1976b

Ethyl benzene Fathead minnow Acute 10 158 1000 EPA 1980p

Bluegill Acute 50 501 3980 EPA 1980p

Guppy Acute 79 794 5010 EPA 1980p

Fenitrothion Fathead minnow Chronic 0.1 126 1990 Kleiner et al. 1984
Table C.1. (continued)

Chemical Test Species Test Lower Median Upper Source

Type 95% CL 95%CL

Fluoranthene Bluegill Acute 2.00 32 126 EPA 1980q

Fluridone Fathead minnow Chronic 32 398 10000 Hamelink et al. 1986

Fonofos Fathead minnow Chronic 3.16 20 158 Pickering and Giliam

1982

Guthion Fathead minnow Chronic 0.013 0.13 3.98 Adelman et al. 1976

Heptachlor Fathead minnow Chronic 0.01 0.1 0.63 Macek et al. 1976b

Hexachlorobutadiene Fathead minnow Chronic 0.32 3.98 63 Benoit et al. 1982

Hexachlorocyclohexane (lindane) Bluegill Chronic 0.16 1 6.31

Macek et al. 1976a

Hexachloroethane Fathead minnow Chronic 3.98 100 1580 Ahmad et al. 1984

2-Hexanone Fathead minnow Acute 100 1260 12600 AQUIREa

Kelthane Fathead minnow Chronic 0.32 7.94 100 Spehar et al. 1982

LAS 11.2 Fathead minnow Chronic 126 1580 25100 Holman et al. 1980

LAS 11.7 Fathead minnow Chronic 13 200 2510 Holman et al. 1980

LAS Mixture Fathead minnow Chronic 20 316 1580 Pickering and Thatcher

1970

Malathion Flagfish Chronic 3.162 20 126 Hermanutz 1978

1-Methylnaphthalene Fathead minnow Acute 1.78 31.62 200 AQUIREa

4-Methyl-2-pentanone Fathead minnow Acute 141 1580 15800 AQUIREa

2-Methylphenol Fathead minnow Acute 3.98 40 398 AQUIREa

Bluegill Acute 13 126 1000 AQUIREa

Rainbow trout Acute 6.31 79 398 AQUIREa

Methylene chloride Fathead minnow Acute 63.10 1000 10000 AQUIREa

Bluegill Acute 158 1580 12600 AQUIREa

Naphthalene Fathead minnow Chronic 73 1000 12600 DeGraeve et al. 1982

4-Nitrophenol Fathead minnow Acute 13 159 1260 AQUIREa

Bluegill Acute 3.98 50 316 AQUIREa

Rainbow trout Acute 6.31 79 398 AQUIREa
Table C.1. (continued)

Chemical Test Species Test Lower Median Upper Source

Type 95% CL 95%CL

Channel catfish Acute 0.79 20 200 AQUIREa

N-nitrosodiphenylamine Bluegill Acute 3.16 40 251 AQUIREa

PCBs: Aroclor 1221 Cutthroat trout Acute 0.63 10 50 AQUIREa

PCBs: Aroclor 1232 Cutthroat trout Acute 1.26 16 126 AQUIREa

PCBs: Aroclor 1242 Fathead minnow Chronic 0.13 1.58 40 Nebeker et al. 1974

PCBs: Aroclor 1248 Flagfish Chronic 0.13 1.26 7.94 Nebeker et al. 1974

PCBs: Aroclor 1254 Fathead minnow Chronic 0.1 0.63 7.94 Nebeker et al. 1974

PCBs: Aroclor 1260 Cutthroat trout Acute 32 316 2510 AQUIREa

Pentachloroethane Fathead minnow Chronic 100 1260 19900 Ahmad et al. 1984

Pentachlorophenol Fathead minnow Chronic 1.58 32 501 Holcombe et al. 1982

Fathead minnow Chronic 0.32 1.99 20 Spehar et al. 1985

Fathead minnow Chronic 0.63 6.31 63 Spehar et al. 1985

Fathead minnow Chronic 1.26 13 126 Spehar et al. 1985

Fathead minnow Chronic 1.99 16 158 Spehar et al. 1985

Rainbow trout Chronic 1.58 10 50 Dominguezand Chapman

1984

1-Pentanol Bluegill Acute 398 5010 39800 AQUIREa

Rainbow trout Acute 200 2510 19900 AQUIREa

Permethrin Fathead minnow Chronic 0.02 0.40 5.01 Spehar et al. 1983

Phenol Fathead minnow Chronic 1000 12600 199000 Degraeve et al. 1980

Rainbow trout Chronic 126 1580 15800 Degraeve et al. 1980

Propanil Fathead minnow Chronic 0.01 0.1 0.63 Call et al. 1983

2-Propanol Fathead minnow Acute 200 3160 31600 AQUIREa

Pydrin Fathead minnow Chronic 0.006 0.13 1.58 Spehar et al. 1982

1,1,2,2-Tetrachloroethane Fathead minnow Chronic 251 1580 50100 Ahmad et al. 1984

Tetrachloroethene Fathead minnow Acute 3.16 50 398 EPA 1980aa

Bluegill Acute 10 100 501 EPA 1980aa

Rainbow trout Acute 3.16 40 316 EPA 1980aa
Table C.1. (continued)

Chemical Test Species Test Lower Median Upper Source

Type 95% CL 95%CL

Tetrachloroethylene Fathead minnow Chronic 40 1000 12600 Ahmad et al. 1984

Toluene Fathead minnow Acute 10 126 1000 EPA 1980cc

Bluegill Acute 13 126 1000 EPA 1980cc

Guppy Acute 50 501 3160 EPA 1980cc

Toxaphene Brook trout Chronic 0.01 0.063 0.40 Mayer et al. 1975

1,1,1-Trichloroethane Fathead minnow Acute 18 200 1580 AQUIREa

Bluegill Acute 32 316 1580 AQUIREa

1,1,2-Trichloroethane Fathead minnow Chronic 1000 15800 251000 Ahmad et al. 1984

Trichloroethene Fathead minnow Acute 13 158 1260 EPA 1980dd

Flagfish Acute 20 251 1260 Smith et al. 1991

Bluegill Acute 32 316 1990 EPA 1980dd

2-Trifluoromethyl-4-phenol Brook trout Chronic 100 501 3160 Dwyer et al. 1978

Trifluralin Fathead minnow Chronic 0.063 0.63 7.94 Macek et al. 1976b

1,3,5-Trinitrobenzene Fathead minnow Chronic 3.16 50 631 Van der Schalie 1983

Rainbow trout Chronic 13 158 1580 Van der Schalie 1983

Rainbow trout Chronic 13 158 1580 Van der Schalie 1983

Vinyl acetate Fathead minnow Acute 3.16 40 398 AQUIREa

Bluegill Acute 10 126 794 AQUIREa

Guppy Acute 25 251 1580 AQUIREa

 EPA (n.d.) a