UnitedStater OfficeofWater EnvironmentalProtection Regulatmrand Standards Agency Warhmgton. DC20460 May 1, 1986 

# e,Ep', Water EPA 440/5-86-001 

# QUALlTY CRITERIA 

# for WAm 

# 1986

## - TO INTERESTED PARTIES Section 304(a)(l) of the Clean Water Act (33 U.S.C. 1314(a) (1) requires the Environmental Protection Agency (EPA) to pub1ish and periodically update ambient water qua1ity criteria. These criteria are to accurately reflect the latest scientific knowledge (a) on the kind and extent of all identifiable effects
on health and welfare including, but not limited to, plankton, fish shellfish, wildlife, plant life, shorelines, beaches, aesthetics, and recreation which may be expected from the presence of pollutants 

### in any body of water including ground water; (b) on the concentration and dispersal of pollutants,or their byproducts, through biological, physical, and chemical processes; and (c) on the effects of pollutants on biological community diversity, productivity, and stability, including information on the factors affecting rates of eutrophication and organic and inorganic sedimentation for varying types of receivingwaters. These criteria are not rules and they do not have regulatory impact. Rather, these criteria present scientific data and guidance of the environmental effects of pollutants which can be useful to derive regulatory requirements based on considerations of water quality impacts. When additional data has become available, these summaries have been updated to reflect the latest Agency recommendations on acceptable limits for aquatic life and human health protection. Periodically EPA and its predecessor agencies has issued ambient water quality criteria, beginning in 1968 with the "Green Book" followed by the 1973 publication of the "Blue Book" (Water Quality Criteria 1972). In 1976, the "Red Book" (Quality

ForaalcbytheSvpmlendsntofDocuments,USMwmmsntRlnUngORW Waahpton.DC M02Criteria forWater) was published. On November 28, 1980 (45 FR 79318), and February 15, 1984 (49 FR 5831), EPA announced through Federal - Register notices, the publication of 65 individual ambient water quality criteria documents 

### €or pollutants listed as toxic under section 307(a)(l) of the Clean Water Act. on July 29, 1985 (50FR 30784), EPA published additional water quality criteria documents. The development and publication of ambient water quality criteria has been pursued over the past 10 years and is an ongoing process. EPA expects to publish about 10 final criteria documents each year. Some of these will update and revise existing criteria recommendations and others will be issued for the first time. In a continuing effort to provide thosewho use EPA’Swater quality and human health criteria with up-to-date criteria values and associated information, this document 

# - - QualmCriteria

__ €or Water 

# - 1986 was assembled. This document includes summaries of all the contaminants for which EPA has developed criteria recommendations (Appendix A-C)

# . The appropriate appendix is identified 

### at the end of each summary. 

### A more detailed description of these procedures can be found 

### in the appropriate Appendix. Copies of this document can be obtained by contacting the U.S. Government Printing Office at: U.S. Government Printing Office Superintendent of Documents N. Capitol and H Street N.W. Washington, D.C. 20401 A fee is charged for this document. Copies of the complete background ambient water qualitycriteria documents containing all the data used to develop the 

### criteria recommendations summarized herein and the “Red Bookt8, including completebibliographies are available only from: 

# 0

National Technical Information Service 5285 Port Royal Road Springfield,VA 22161 Telephone: (703) 487-4650 The NTIS order numbers for the criteria documents can be found in the Index. A fee is charged for copies of these documents. 

### As new criteria are developed and existing criteria revised, updated criteria summaries will be made available once a year 

### to those who purchase this document through the U.S, Government Printing office. You will automatically be placed on the mailing list to receive annual updates. The cost for receiving annual updates 

### is included in the purchase price of the document.



## - - Quality Criteria 

## - for Water, 1986 is designed to be easily updated to reflect EPA‘s continuing work 

### to present the latest scientific information and practices, Our planned schedule €or future criteria development in the next fewyears is attached for your information. 

# a

The Agency 

### is current1 y developing Acceptable Daily Intake (ADI) 

### or Verified Reference Dose (RfD) values on a number of chemicals for Agency

-wide use. Based upon this new analysis the values have changed significantly for 5 chemicals from those used in the original human health criteria calculation done in 1980. The chemicals affected are as follows: 

# 0chemical 

# . 1980 WQC 1. cyanide 200 ug/L 2. Ethylbenzene 1.4 mg/L 4. Phenol 3.5 mg/L 3. Nitrobenzene 19.8 mg/L 5. Toluene 14.3 mg/L Draft 

## RfD .02 mg/kg/day .Q1mg/kg/day .Q005 mg/kg/day 0.1 mg/kg/day 0.3 mg/kg/day
FOR FORTHER INFORMATION CONTACT: 

### Dr. Frank Gostomski at the above address 

### or by phoning (202) 245- 3030. 

### It is EPA's goal 

### to continue to develop and make available ambient water quality criteria reflecting the latest scientific practices and information. In this way we can continue to improve and protect the quality of the Nation's waters. James 

### M. Conlon 

# i/ and Standards

### DRAFT CRITERIA DOCUMENTS TO 

### BE PROPOSED
LATE FY 86/EARLY 

## -- FY 87 

## -- 

# 0

Diethyhexylphthalate 1,2,4, 

### Trichlorobenzene Silver Phenanthrene 2,4,5, 

### Trichlorophenol Organotins Tributyltin Selenium (no saltwater criteria) Hexachlorobenzene Antimony 111 

### Acrolein (no saltwater criteria)



## - - LATE 

### FY 87/EARLY Thallium (no saltwater criteria) Tetrachloroethylene 

### (no saltwater criteria) Phenol Toluene Chloroform (no saltwater criteria) 'imaline Acrvlontrile 

# w Hexachlorocyclopentadiene 

### (no saltwater criteria) Dimethylphenol Hexachlorobutadiene (no saltwater criteria) 

# - Both lists will incorporate aquatic and human health values. 

# - All above are toxic pollutants except for 

### organotins and analine which are non-conventionals.INDEX INTRODUCTION SUMMARY CHART

.,' Acenaphthene Acrolein Acrylonitrile Aesthetics Alkalinity Aldrin/Dieldrin 

### Ammonia Antimony Arsenic Asbestos Bacteria Barium Benzene Benzidine Beryllium Boron Cadmium Carbon Tetrachloride Chlordane Chlorinated Benzenes Chlorinated Ethanes Chlorinated Naphthalenes Chlorine Chlorinated Phenols Chloroalkyl Ethers Chlorof om Chlorophenoxy Herbicides Chromium 2-Chlorophenol Color Copper Cyanide DDT and Metabolites 

### Demeton Dichlorobenzenes Dichlorobenzidine Dichloroethylenes 2,4, 

# - Dichlorophenol Dichloropropanes/Dichloropropenes 2,4, 

# - Dimethylphenol Dinitrotoluene Diphenylhydrazine Endosulfan Endrin Ethylbenzene Fluoranthene Gasses, Total Dissolved Guthion PB-263943 PB 81-117293 

### PB 81-117343 PB 81-117350 PB-263943 PB 85-227031 PB 81-117376 PB 81-117384 PB 81-117392 PB 81-117400 

### PB 81-117426 PB 85-227429 PB 81-117434 PB 81-117418 PB 81-117442 PB-263943 PB 85-227478 PB 81-117459 PB-263943 PB 85-227023 PB 85-227460 PB 81-117491 PB-263943 PB 81-117509 PB 81-117517 PB 81-117525 PB 81-117533 PB 81-117541 PB 81-117558 PB 81-117566 PB 81-117731 PB 81-117582 PB 81-117590 PB 81-117608 PB-263943 PJ3-263943 PB 81-117574 NTIS No. -- PB 81-117269 PB 81-117277 PB 81-117285 FB-263943 PB-263943 PB 81-117301 PB 85-227114 PB 81-117319 PB 85-227445 PB 81-117335 PB 86-158-045 h PB-263943Haloethers Halomethanes Hardness Heptachlor Hexachlorobutadiene Hexachlorocyclohexane Hexachlorocyclopentadiene Iron Isophorone Lead Malathion Manganese Mercury Methoxychlor Mirex Naphthalene Nickel Nitrates, Nitrites Nitrobenzene Nitrophenols Nitrosamines Oil and Grease Oxygen, Dissolved Parathion Pentachlorophenol Ph Phenol Phosphorus Phthalate Esters Polychlorinated Biphenyls Polynuclear Aromatic Hydrocarbons Selenium Silver Solids (Dissolved) h Salinity Solids (Suspended) & Turbidity Sulfides, Hydrogen Sulfide Taintina Substances PB 81-117616 PB 81-117624 PB-263943 PB 81-117632 PE 81-117640 PB 81-117657 PB 81-117665 PB-263943 PB 81-117673 PB 85-227437 PB-263943 PB-263943 PB 85-227452 PB-2 63943 PB-263943 PB 81-117707 

### PB 81-117715 PB-263943 PB 81-117723 PB 81-117749 PB 81-117756 PB-263943 

### PB 86-208253 PB-263943 PB 81-117764 PB-263943 PB 81-117772 PB-263943 PB 81-117780 PB 81-117798 PB 81-117806 

### PB 81-117814 PB 81-117822 PB-263943 PB-263943 PB-263943 PB-263943 Temperagure PB-263943 Tetrachloroethylene PB 81-117830 Thallium PB 81-117848 Toluene PB 81-117855 Toxaphene PB 81-117863 Trichloroethylene PB 81-117871 Vinyl Chloride PB 81-117889 Zinc PB 81-117897 2,3,7,8-Tetrachlorodibenzo-p-dioxin EPA # 440/5-84-007



### APPENDIX A APPENDIX B APPENDIX C BIBLIOGRAPHY Methodology for Developing Criteria Methodology for Developing Criteria Methodology for Developing Criteria

# I SUMMARY CHART

# 1

# 0 CRITERIA: ACENAPHTHENE
Aquatic Life
The available data for acenaphthene indicate that acute toxicity to freshwater aquatic life occurs at concentrations as low as 1,700 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No data are available concerning the chronic toxicity of acenaphthene to sensitive freshwater aquatic animals but toxicity to freshwater algae occur at concentrations as low as 520 ug/L. The available data for acenaphthene indicate that acute and chronic toxicity to saltwater aquatic life occurs at concentrations as low as 970 and 710 ug/L, respectively, and would occur at lower concentrations among species that are more sensitive than those tested. Toxicity to algae occurs at concentrations 

### as low as 500 ug/L.
Human Health Sufficient data are not available for acenaphthene to derive
a level which would protect against the potential toxicity of this compound. Using available organoleptic data, to control undesirable taste and odor quality of ambient water the estimated level is 0.02 mg/L. It should be recognized that organoleptic data, have limitations as a basis for establishing water quality criteria, and have no demonstrated relationship to potential adverse human health effects. 

# 0 (45 F.R. 79318, November 28, 1980)
, SEE APPENDIX B FOR METHODOLOGYACROLEIN
Aquatic Life The available data for acrolein indicate that acute and chronic toxicity to freshwater aquatic life occurs at concentrations as low as 68 and 21 ug/L, respectively, and would
occur at lower concentrations among species that 

### are more sensitive than those tested. The available data for acrolein indicate that acute toxicity to saltwater aquatic life occurs at concentrations as low as 55 ug/L and would occur at lower concentrations among species that
are more sensitive than those tested. No data are available concerning the chronic toxicity of acrolein to sensitive saltwater aquatic life. 

# 0

Human Health For the protection of human health from the toxic properties of acrolein ingested through contamins'ed aquatic organisms, the ambient water criterion is determined o be 320 ug/L. For the protection of human health from the toxic properties of acrolein ingested through contaminated aquatic organisms alone, the ambient water criterion is determined to be 780 ug/L*

(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGY 

# 0

,CRITERIA: ACRYMNITRILE
Aquatic Life The available,data for acrylonitrile indicate that acute toxicity to freshwater aquatic life occurs at concentrations as low as 7,550 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No definitive data are available concerning the chronic toxicity of acrylonitrile to sensitive freshwater aquatic life but mortality
occurs at concentrations as low as 2,600 ug/L with a fish species exposed for 30 days. Only one saltwater species has been tested with acrylonitrile and no statement can be made concerning acute or chronic

Human Health For the maximum protection of human health from the potential carcinogenic effects resulting from exposure to acrylonitrile through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentrations should be zero, based
on the nonthreshold assumption for this chemical. However, zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer risk
over the lifetime are estimated at and lo-’. The corresponding recommended criteria are 0.58 ug/L, 0.058 ug/L, and 0.006 ug/L, respectively. If these estimates are made for consumption of aquatic organisms only, excluding consumption 

# 0

,of water, the levels are 6.5 ug/L, 0.65 ug/L, and 0.065 ug/L, respectively.

(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYAESTHETIC QUALITIES
CRITERIA:



# a All waters free from substances attributable to wastewater or other discharges that:
settle to form objectionable deposits;
float as debris, scum, oil, 

### or other matter to form nuisances; produce objectionable color, odor, taste,
or turbidity; injure 

### or are toxic or produce adverse

physiological responses in humans, animals or plants: and, produce undesirable or nuisance aquatic life.
RATIONALE: Aesthetic qualities of water address the general principles laid down 

### in common law. They embody the beauty and quality of water and their concepts may vary within the minds of individuals encountering the waterway. A rationale for these qualities cannot be developed with quantifying definitions; however, decisions concerning such quality factors can portray the best in the public interest.

_.,Aesthetic qualities provide the general rules toprotect water against environmental insults: they provide minimal freedom requirements from pollution; they are essential properties to protect the Nation's waterways.

(QUALITY CRITERIA FOR WATER, JULY 1976) PB-263943 SEE APPENDIX C FOR METHODOLOGYALKALINITY CRITERION: 20 

### mg/L or more as CaC03 freshwater aquatic life except where natural concentrations are less.
INTRODUCTION: 

### Alkalinity is the sum total of components in the water that tend to elevate the pH of the water above a value of about 4.5. It 

### is measured by titration with standardized acid to a pH value of about 4.5 

### and it 

### is expressed commonly as milligrams per liter of 

### calcium carbonate. Alkalinity, therefore, is a measure of the buffering capacity of the water, and since pH 

### has a direct effect
on organisms as well as an indirect effect on the 

### toxicity of certain other pollutants in the water, the buffering capacity is important to water quality. Examples of 

### commonly occurring materials in natural waters that increase the alkalinity are carbonates, bicarbonates, phosphates and hydroxides.
RATIONALE: 

### The alkalinity of water used for municipal water supplies is important because it affects the amounts of chemicals that need to be added to accomplish calculation, softening and control of corrosion in distribution systems. The alkalinity of water assists in the neutralization of excess acid produced during the addition of such materials as aluminum sulfate during chemical coagulation. Waters having sufficient alkalinity do not have to be supplemented with artificially added materials to increase the

i 

### alkalinity. Alkalinity resulting from naturally occurring

# a materials such as carbonate and bicarbonate is not considered a health hazard in drinking water supplies, per se, and naturally occurring maximum levels up to approximately 400 mg/L 

### as calcium carbonate 

### are not considered 

### a problem 

### to human health (NAS, 1974). Alkalinity is important for fish and other aquatic lifein freshwater systems because it buffers pH changes that occur

-naturally as a result of photosynthetic activity of the

chlorophyll

-bearingvegetation. Components of alkalinity such as carbonate and biocarbonate will complex some toxic heavy metals and reduce their toxicity markedly. For these reasons, the National Technical Advisory Committee (NATC, 1968) recommended a minimum alkalinity of 20 mg/L 'and the subsequent NAS Report

(1974) recommended that natural alkalinity not be reduced by more than 25 percent but did not place an absolute minimal value for it. The use of the 25 present reduction avoids theproblem of establishing standards on waters where natural alkalinity is at 

### or below 20 mg/L. For such waters, alkalinity should not be further reduced.
The NAS Report recommends that adequate amounts of alkalinity be maintained tobuffer the pH within tolerable limitsformarine waters. It has been noted as a correlation that productive waterfowl habitats are above 25 mg/L withhigher alkalinities resulting in better waterfowl habitats (NATC, 1968).Excessive alkalinity can cause problems for swimmers by altering the pH of the lacrimal fluid around the eye, causing irritation. 

# 0

For industrial water supplies, high alkalinity can be damaging to industries involved in food production, especially those in which acidity accounts for flavor and stability, such as the carbonated beverages. In other instances, alkalinity is desirable because water with a high alkalinity is much less corrosive.

A brief summary of maximum alkalinities accepted as a source of raw water by industry 

### is included in Table 1. The concentrations listed in the table are for water prior to treatment and thus are only desirable ranges and not critical ranges for industrial use. 

# 0

The effect 

### of alkalinity in water used for irrigation may be important in some instancesbecause it may indirectly increase the relative proportion of sodium in soilwater. As an example, when bicarbonate concentrations are high, calcium and magnesium ions that are in solution precipitate as carbonates in the soil water gs the water becomes more concentrated through evaporation and transpiration. As the calcium and magnesium ions decrease in concentration, the percentage of sodium increases and results in soil and plant damage. Alkalinity may also lead to chlorosis in plants because it causes the iron toprecipitate as a hydroxide (NAS, 1974). Hydroxyl ions react with available iron in the soilTABLE 

### I* Maximum Alkalinity 

### In Waters Used As A Source Of Supply Prior To Treatment
Industry Alkalinity mg/L as CaC03 

## - Steam generation boiler makeup....... 

# ..... 350 Steam generation cooling

# .................. 500 Textile mill products

# ..................... 50-200 Paper and allied products

# ................. 75-150 Chemical and Allied Products.............. 500 Petroleum refining

# ........................ ' 500 Primary metals industries................. 200 Food canning industries......... 

# .......... 300 1 Bottled and canned soft drinks............ 

## * NAS, 1974water and make the iron unavailable to.plants. Such deficiencies induce chlorosis and further plant damage. Usually alkalinity must exceed 6 mg/L before such effects are noticed, however.

(QUALITY CRITERIA FOR WATER, JULY 1976) PB-263943 SEE APPENDIX C FOR METHODOLOGY*ALDRIN-DIELDRIN
Aquatic 

### Life Dieldrin For dieldrin the criterion to protect freshwater aquatic life
as derived using the Guidelines is 0.0019 ug/L as a 24

-hour average, and the concentration should not exceed 1.0 ug/L at any time.


### For dieldrin the criterion to protect saltwater aquatic life
as derived using the Guidelines is 0.0019 ug/L as a 24

-hour average, and the concentration should not exceed 0.71 ug/L at any time

# - Aldrin
For freshwater aquatic life the concentration of aldrin should not exceed 4.0 ug/L at any time. No data are available concerning the chronic toxicity of aldrin to sensitive freshwater aquatic life. For saltwater aquatic life the concentration of aldrin should not exceed 1.3 ug/L at any time. No data are available concerning the chronic toxicity of aldrin to sensitive saltwater aquatic life. Human Health For the maximum protection of human health from the potential carcinogenic effects of exposure to aldrin through ingestion of contaminated water and contaminated aquatic organisms, the

I *Indicates suspended, canceled or restricted by U.S. EPA Office 

### of Pesticides and Toxic Substances 

# .

# a ambient water concentration should be zero,based on the nonthreshold assumption for this chemical. However, zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer risk over the lifetime are estimated at and The corresponding recommended criteria are 0.74 ng/L, 0.074 ng/L, and 0.0074 ng/L, respectively. If these estimates are made for consumption of aquatic organisms only, excluding consumption of water, the levels are 0.79 ng/L, 0.079 ng/L, and 0.0079 ng/L, respectively. 

### FOP the maximum protection of human health from the potential carcinogenic effects of exposure to dieldrin through ingestion of contaminated water and Contaminated aquatic organisms, the ambient water concentration should be zero, based on the nonthreshold assumption for this chemical. However, zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer risk over the ,lifetime are estimated at and The corresponding recommended criteria are 0.71 ng/L, 0.071 ng/L, and 0.0071 ng/L, respectively. If these above estimates are made for consumption of aquatic organisms only, excluding consumption of water, the levels are 0.76 ng/L, 0.076 ng/L, and 0.0076 ng/L, respectively. 

# 0

(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYAMMONIA SUMMARY :
All concentrations used herein are expressed as un-ionized ammonia (NH3), because NH3, not the ammonium ion (NH4+) has been demonstrated 

### to be the principal toxic form of ammonia. The data used in deriving criteria are predominantly from flow through tests in which ammonia concentrations were measured. Ammonia was reported 

### to be acutely toxic 

### to freshwater organisms at concentrations (uncorrected 

### €or pH) ranging from 0.53 to 22.8 mg/L NH3 for 19 invertebrate species representing 14 families and 16 genera and from 0.083 

### to 4.60 mg/L NH3 

### €or 29 fish species from 9 families and 18 genera. Among fish species, reported 96- hour LC50 ranged from 0.083 to 1.09 mg/L for salmonids and from 0.14 

### to 4.60 mg/L NH3 

### for nonsalmonids. Reported data from chronic tests 

### on ammonia with two freshwater invertebrate species, both daphnids, showed effects at concentrations (uncorrected for pH) ranging from 0.304 

### to 1.2 mg/L NH3, and with nine freshwater fish species, from five families and seven genera, ranging from 0.0017 

### to 0.612 mg/L NH3. I

Concentrations of ammonia acutely toxic to fishes may cause loss of equilibrium, hyperexcitability, increased breathing, cardiac output and oxygen uptake, and, in extreme cases, convulsions, coma, and death. At lower concentrations ammonia has many effects on fishes, including a reduction in hatching success, reduction in growth rate and morphological development, and pathologic changes in tissues of gills, livers, and kidneys.Several factors have been shown to modify acute NH3 toxicity in fresh water. Some factors alter the concentration of unionized ammonia in the water by affecting the aqueous ammonia equilibrium, and some factors affect the toxicity of un-ionized ammonia itself, either ameliorating or exacerbating the effects of ammonia. Factors that have been shown to affect ammonia toxicity include dissolved oxygen concentration, temperature, pH, previous acclimation to ammonia, fluctuating or intermittent exposures, carbon dioxide concentration, salinity, and the presence of other toxicants. The most well

-studied of these is pH: the acute toxicity of NH3 has been shown to increase as pH decreases. Sufficient data exist from toxicity tests conducted at different pH values to formulate a mathematical expression to describe pH

-dependent acute NH3 toxicity. The very limited amount of data regarding effects 

### of pH 

### on chronic NH3 toxicity also indicates increasing NH3 toxicity with decreasingpH,but the data are insufficient to derive a broadly applicable toxicity/pH relationship. Data on temperature effects on acute NH3 toxicity are limited and somewhat variable, but indications are that NH3 toxicity to fish 

### is greater as temperature decreases. There is no information available regarding temperature effects on chronic NH3 toxicity. Examination of pH and temperature

-corrected acute NH3 toxicity values among species and genera of freshwater organisms showed that invertebrates are generally more tolerant than fishes, a notable exception being the fingernail clam. There is
no clear trend among groups of fish; the several most sensitive

# atested species and genera include representatives from diverse families (Salmonidae, Cyprinidae, Percidae, and Centrarchidae). Available chronic toxicity data for freshwater organisms also indicate invertebrates (cladocerans, one insect species) tobe
more tolerant than fishes, again with the exception of the fingernail clam. When corrected for the presumed effects of temperatureandpH, there isalsono cleartrend among groups of fish for chronic toxicity values, the most sensitive species including representatives from five families (Salmonidae, Cyprinidae, Ictaluridae, Centrarchidae, and Catostomidae) and having chronicvalues rangingby not much more than a factoror two. The range of acute

- chronic ratios for 10 species from 6 

# 0

families was 3 to 43, and acute-khronic ratioswere higher for the species having chronic tolerance below the median. Available data indicate that differences in sensitivitiesbetween
warm and coldwater families of aquatic organisms are inadequate towarrant discrimination in the national ammonia criterion between bodies of water with I'warm1' and 'lcoldwaterll fishes; rather, effects of organism sensitivities on thecriterion are most appropriately handled by site

- specific criteria derivation procedures. Data for concentrations of NH3 toxic to freshwater phytoplankton and vascular plants, although limited, indicate that freshwater plant species are appreciablymore tolerant to NH3 than are invertebrates or fishes. The ammonia criterion appropriate for the protection of aquatic animals will therefore in all likelihood be sufficiently protective of plant life. 

# 0

,,Available acute and chronic data for ammonia with saltwater organisms are very limited, and insufficient to derive a saltwater criterion. A few saltwater invertebrate species have been tested, and the prawn Macrobrachiurn rosenberqil was the most sensitive. The few saltwater fishes tested suggest greater sensitivity than freshwater fishes. Acute toxicity of NH3 appears to be greater at low pH values, similar to findings in freshwater. Data for saltwater plant species are limited to diatoms, which appear to be more sensitive than the saltwater invertebrates for which data are available. More quantitative information needs to be published on the toxicity of ammonia to aquatic life. Several key research needs must be addressed to provide 

### a more complete assessment of ammonia toxicity. These are: (1)acute tests with additional saltwater fish species and saltwater invertebrate species: (2) life

-cycle and early life

-stage tests with representative freshwater and saltwater organisms from different families, with particular attention to trends of acute

-chronic ratios; (3) fluctuating and intermittent exposure tests with a variety of species and exposure patterns: (4) more complete tests of the individual and combined effects of pH and temperature, especially for chronic toxicity: (5) more histopathological and histochemical research with fishes, which would provide a rapid
means of identifying and quantifying sublethal ammonia effects; and (6) studies on effects of dissolved and suspended solids on acute and chronic toxicity.NATIONAL CRITERIA: The procedures described 

### in the Guidelines for Deriving Numerical National Water Quality Criteria for the Protection of Aquatic Organisms and Their Uses indicate that, except possibly where 

### a locally important species is very sensitive, freshwater aquatic organisms and their uses should not be affected unacceptably if: (1) the 1

-hour* average concentration of un

-ionized ammonia (in mg/L NH3) does not exceed, more often than once every 3 years on the average, the numerical value given by 0.52/FT/FPH/2, where:

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

## - < T - < 30 10-0.03(20-T) ; 0 - < T - < TCAP FPH = 1 :a<p~<g 1+10-7.4-PH 1.25 ; 6.5 TCAP = 20 C: Salmonids or other coldwater species present

= 25 C; Salmonids and other coldwater species absent <pH<8 sensitive
sensitive
(*An averaging period of 1 hour may not be appropriate if excursions of concentrations to greater than 1.5 times the average occur during the hour; in such cases, a shorter averaging period may be needed.) (2) the 4

-day average concentration of u n- ionizedammonia (in mg/L NH3) does not exceed, more
on the average, the average* 0.80/FT/FPH/RATIO, where FT and FPH
, often than once every 3 years numerical value given by
are as above and:RATIO = 16 ; 7.7 - < pH - <9

= 24 10

-7.7

-ph 1+10-7.4ph ;6.5< - ph - < 7.7
TCAP = 15 C; Salmonids or other sensitive coldwater species present

coldwater species absent = 20 C: Salmonids and other sensitive (*Because these formulas are nonlinear in pH and temperature, the criterion should be the average of separate evaluations of the formulas reflective of the fluctuations of flow, pH, and temperature within the averaging period; it is not appropriate in general to simply apply the formula to average pH, temperature, and flow.) The extremes for temperature (0, 30) and pH (6.5, 9) given in the above formulas are absolute. It is not permissible with current data to conduct any extrapolations beyond these limits. In particular, there is reason to believe that appropriate criteria at pH > 9 will be lower than the plateau between pH 8 and 9 given above. Criteria concentrations for the pH range 6.5 to 9.0 and the temperature range 0 C to 30 C are provided in the following tables. Total ammonia concentrations equivalent to each unionized ammonia concentration are also provided in these tables. There are limited data on the effect of temperature on chronic toxicity. EPA will be conducting additional research on the effects of temperature on ammonia toxicity in order to fill perceived data gaps. Because of this uncertainty, additional site

-specific information should be developed before thesecriteria are used in wasteload allocation modeling. For example, the chronic criteria tabulated for sites lacking salmonids are less certain at temperatures much below 20 C than those tabulated at temperatures near 20 C. Where the treatment levels needed to meet these criteria below 20 C may be substantial,use of sitespecific criteria is strongly suggested. Development of such criteria should be based upon site

-specific toxicity tests. Data available for saltwater species are insufficient to derive a criterion for saltwater. The recommended exceedence frequency of 3 years is the Agency's best scientific judgment of the average amount of time it will take an unstressed system to recover from a pollution event in which exposure to ammonia exceeds the criterion. A stressed system, for example, one in which several outfalls occur in a limited area, would be expected to require more time for 

# e

recovery. The resilience of ecosystems and their ability to
recover differ greatly, however, and site

-specific criteria may be established if adequate justification is provided. The use 

### of criteria 

### in designing waste treatment facilities requires the selection of an appropriate wasteload allocation model. Dynamic models are preferred for the application of these criteria. Limited data or other factors may make their use impractical, in which case one should rely on a steady

-state model. The Agency recommends the interim use of 145 or lQlO for Criterion Maximum Concentration design flow and 745 or 7410 for the Criterion Continuous Concentration design flow in steadystatemodels forunstressed and stressed systemsrespectively. 1(I) Onchow avuagm ancmntratlonr for mmonla.* ,r\ PH 

### oc 5c 10

### c [IS

### c MC 25 

### c MC
A

. Salmmldr or omr Smnrltlvm Coldwatr Speclos Present Un-1onIz.d Amnia (mqllltorNH,) 6.54 0.0091 0.0129 0.0182 0.026 O.OS6 0.OY 0.036 6.75 0.0149 0.02 I 0.030 0.042 0.059 0.059 O.OS9 7

### .oo 0.025 0.033 0.Mb 0.066 0.09) 0.093 0.093 0.054 0.048 0.068 0.095 0.135 0.135 0.135 730 0.045 0.w 0.091 0.128 0.181 0.181 0.181 735 

### n93 0.056 0.080 0.113 0.159 0.22 0.22 0.22 8.00 0.065 0092 0.130 0.184 0.26 0.26 036 0.065 0.092 0.130 0.184 0.26 0.26 0.26 0.065 0.092 0.130 0.184 0-26 036 0.26 835 8.54 8.15 0.065 0.092 0.130 0.184 0.26 0.26 0.26 9

### .oo 0.065 0.092 0.130 0.184 026 036 026 Total Amonla (mg/Iltu NH3) 35 32 28 25 17.4 12.2 8.0 4 .I 2.6 I.47 0

### .a 33 _- w) 26 22 163 11.4 7-5 43 2.4 1.w 0.83 31 28 25 20 15.5 10.9 7.1 4.1 2.3 1.37 0A3 30 

### n -. 24 19.7 14.9 103 69 4;o 2.3 I 

### .s 0.86 29 27 -. 23 19.2 14.6 10.3 6-0

. _. 3.9 2.3 1.42 0.91 20 14.31 18.6 133 16.4 11.6 13.4 9.5 10.1 7.3 4.8 3.5 2.8 2.1 1.71 I .28 I-07 0.83 0.72 038 7.2md 5.2

8. Sallnonlds and OthU S.nrltlv* Coldratw Speclor Absmt UWl0nlz.d AnnuxlIa (mg/Iltr NH,) 0.0091 0.0129 0.0182 0.026 0.036 0.051 o.os1 0.0149 0.02 1 0.030 0.042 O.OS9 0.084 0.084 0.023 0.033 0.046 0.066 0.093 0.131 0.131 0.034 0.048 0.068 0.095 0.135 0.190 0.190 0.045 0.064 0.091 0.128 0.181 0.26 0.26 0.056 0.000 0.1 13 0.159 0.22 0.32 0.32 0.065 0.092 0.130 0.184 0.26 057 057 0.065 0.092 0.1SO 0.184 0.26 0.37 0.37

6-54 6.75 7.oo 725 7.50 

## - 7.75 8.00 8.25 830 8.75 9 .00 _-. 0;065 0;092 Oil30 Oil84 0.26 0;37 0;37 0.065 0.092 0.130 0.184 0.26 0.37 0.37 0.06s 0492 0.130 0.184 036 0.37 0.37 Total Amnia (mg/llter NWg) 35 32 28 23 17.4 12.2 8.o 4.s 2.6 1.47 0.86 33 30 26 22 16.3 11.4 7.5 4.2 2-4 I.40 0.83 31 28 25 20 15.5 10.9 7.1 4.1 2.3 1.31 0.83 30 27 24 19.7 14.9 10.5 6.9 4.0 2.3 1.JB 0.86 29 27 23 19.2 14.6 105 6.8 3.9 2.3 1.42 0.91 29 26 23 19.0 !4 

### .s 10.2 6.8 4.O 2.4 1.52 1.01 20 18.6 16.4 13.5-

4. 2.9 1.el 1.18 0.82(2) 4-day average cmcentratlons for annonIa.*
PH oc 5c 10 c 15 C 20 c is c MC
A. Salmldsor Other Sensltlve ColdMater SDecles Present Un-Ionized Amonla (rng/lltr NH3)

x 630 0.0007 6.75 0.0012 7.00 0.0021 7.25 0.0037 7.so 0.0066 7.75 0.0109 8.oo 0.0126 8.25 0.0126 830 0.0126 8.75 0.0126 9-00 0.0126 0.0009 0.0017 0.0029 0.0052 0.0093 0.01 53 0.0177 0.0177 0.0177 0.0171 0.0177 0.0013 0.0023 0.0042 0.0074 0.0132 0.022 0.025 0.025 0.025 0.025 0.025 0.0019 0.0033 0.0059 0.0105 0.0186 0.03 1 0.035 0.035 0.035 0.035 0.035 0.0019 0.0033 0.0059 0.0105 0.01% 0.031 0.035 0.035 0.035 0.035 0.Of5 0.0019 0.0019 0.0033 0.0033 O.CO59 0.0059 0.0105 0.0105 0.0186 0.0186 0.031 0.031 0.035 0.035 0.035 0.035 0.035 0.035 0.03s 0.035 0.035 0.035

630 23 2.4 2.2 23 1.49 1.04 0.73 6.73 2.5 2.4 2.2 2.2 1.49 I.04 0.73 7.00 2.5 2.4 23 23 1-49 1.w 0.74 7.25 2.5 2.4 2.2 2.2 1.M 1.04 0.74 7.50 2.5 2.4 22 23 1.M 1.05' 0.74 7.75 2.3 2.2 2.1 2.0 1.40 0.99 0.71 0.47 8.a0 1.53 1.44 1.37 1.33 0.93 8.25 0.87 0.82 0.78 0.76 0.54 8.50 0.49 0.47 0.45 0.44 022 023 0.17 8.75 0.28 0.27 0.26 0.27 0.19 OS15 0.11 9 .W 0.16 0.16 0.16 0.16 0.13 0.10 0.08 

# 00:s 0.28

8. Salmonlds'and Other Sensltlve Coldwater Species Absent? Un-lonired'A~la (mg/lltr NH3) 6.50 0.0007 0.0009 0.0013 0.0019 0.0026 0.0026 0.0026 6.75 0.0012 0.0017 0.0023 0.0033 O.oQ47 0.0047 0-0047 7 .00 0.0021 0.0029 0.0042 0.0059 0.0083 0.0083 0.0083 7.25 0.0037 0.0052 0.0074 0.0105 0.0148 0.0148 0.0148 730 0.0066 0.0093 0.0132 0.0186 0.026 0.026 0.026 7.75 0.0109 0.01% 0.022 0.031 0.043 0.043 0.043 8.00 0.0126 0.0177 0.025 0.035 0.050 0.050 0.050 8.25 0.0126 0.0177 0.025 0.035 0.050 0.050 0.050 8.50 0.0126 0.0177 0.025 0.035 0.ow 0.0% 0.0% 8.75 0.0126 0.0177 0.025 0.035 0.050 0.0% 0.oso 9.W 0.0126 0.0177 0.025 0.035 0.0% 0.0% 0.0%

6.50 6.7s 7.00 72s 730 7.75 8.oo 8.25 8.50 8.75 9.oo 2.5 2.5 2.4 2.5 25 2.3 1.53 037 0.49 0.28 0.16 2.4 2-4 2-4 2-4 2.4 2-2 1-44 0.82 0.47 037 0.16 2.2 23 23 2.2 2.2 2.1 1.37. 0.78 0-45 0.26 0.16 23 23 23 2-2 23 2.0 1.33 0.76 0.44 0.27 0.16 2.1 2.1 2.1 2. I 2.1 1.98 1.31 0.76 0.45 037 0.17 Bs

## d 1.46 l,ZD 1.03 0 8c 1.47 1.z: 1.04 D.@g 1.47 , tl 1.04 0,BC 1.48 l>2P1.05 0 0(P 1.491.22. I.WO,@? I.39 /,/U1.00 0.82. 0.93 0.7@ 061Oa<s' 034 0.40 0*33 035 0.21 0.16 0.14 0.1 I

+ To convert ihw values to mg/llter N. multlply by 0.822. t Sltcspocltlc erltala dwelopmeni Is shongly suggested attqm*Yrosabove 20 C

because of ihe llmltddata aveilable to gwuate the crltrla rac-tlan, and attanporatures b.lW 20 C boCauSe Of tha llnltsd data and brause WO aangn In the crltwla mqhave algnltlcant Impact on the level of trmtunt rqulrd In meeting the recamended crltorie.The Agency acknowledges that the Criterion Continuous Concentration stream flow averaging period used for steady

-state wasteload allocation modeling may be as long as 30 days in situations involving POTWs designed to remove ammonia where limited variability of effluent pollutant concentration and resultant concentrations in receiving waters can be demonstrated. In cases where low variability can be demonstrated, longer averaging periods for the ammonia Criterion Continuous Concentration (e.g., 30

-day averaging periods) would be acceptable because the magnitude and duration of exceedences above the Criterion Continuous Concentration would be sufficiently limited. These matters are discussed in more detail in the Technical Support Document for Water Quality

-Based Toxics Control (U.S. EPA, 1985a).

(50 F.R. 30784, July 29, 1985) SEE APPENDIX A FOR METHODOLOGYANTIMONY CRITERIA: 

### Aquatic Life
The available data for antimony indicate that acute and 

### chronic toxicity 

### to freshwater aquatic life occur at concentrations as low as 9,000 

### and 1,600 

### ug/L, respectively, and would occur at lower concentrations among species that are more sensitive than those tested. Toxicity to algae occurs at concentrations as low as 610 

### ug/L. 

### No saltwater organisms have been adequately tested with antimony, and no statement can be made concerning acute 

### or chronic toxicity. Human Health For 

### the protection of human health from the toxic properties of antimony ingested through water and contaminated aquatic organisms, the ambientwater criterion is determined to be 146 

### UWL. 

### For the protection of human health from the toxic properties of antimony ingested through contaminated aquatic organisms alone, the ambient water criterion is determined to be 45 mg/L.

(45 F.R. 79318, 

### November 28, 1980) SEE 

### APPENDIX B FOR 

### METHODOLOGY

JARSENIC AQUATIC 

### LIFE SUMMARY: 

# 0

The chemistry of arsenic in water is complex and the form present in solution is dependent on such environmental conditions
as Eh, pH, organic content, suspended solids, and sediment. The relative toxicities of the various forms of apsenic apparently vary from species to species. For inorganic arsenic(II1) acute values for 16 freshwater animal species ranged from 812 ug/L for
a cladoceran to 97,000 ug/L for a midge, but the three acutechronic ratios only ranged from 4.660 to 4.862. The five acute values for inorganic arsenic(V) covered about the same range, but the single acute

-chronic ratio was 28.71. The 

### six acute values for MSMA ranged from 3,243 to 1',403,000 ug/L. The freshwater residue data indicated that arsenic is not bioconcentrated to a high degree but that lower forms of aquatic life may accumulate higher arsenic residues than fish. The low bioconcentration factor and short half

-life of arsenic in fish tissue suggest that residues should not be a problem to predators of aquatic life. 

# a

The available data indicate that freshwater plants differ a great deal as to their sensitivity to arsenic(II1) and arsenic(V). In comparable tests, the alga, 

### -----___--- Selenastrum capricornutum, was 45 times more sensitive to arsenic(V) than to arsenic(III), although other data present conflicting information on the sensitivity of this alga to arsenic(V). Many plant values for inorganic arsenic(II1) were in the same range as the available chronic values for freshwater animals; several 

# 0 -plant values for arsenic(V) were lower than the one available chronic value. The other toxicological data revealed a wide range of toxicity based on tests with a variety of freshwater species and endpoints. Tests with early life stages appeared to be the most sensitive indicator of arsenic toxicity. Values obtained from this type of test with inorganic arsenic(II1) were lower than chronic values contained in Table 2. For example, an effect concentration of 40 ug/L was obtained in a test on inorganic arsenic(II1) with embryos and larvae of a toad. Twelve species of saltwater animals have acute values for inorganic arsenic(II1) from 232 to 16,030 ug/L and the single acute

-chronic ratio is 1.945. The only values available for inorganic arsenic(V) are for two invertebrate and are between 2,000 and 3,000ug/L. Arsenic(II1) and arsenic(V) are equally toxic to various species of saltwater algae, but the sensitivities of the species range from 19 ug/L to more than 1,000ug/L. In a test with an oyster, a BCF of 350 was obtained for inorganic arsenic(II1).
NATIONAL CRITERIA: The procedures described in the Guidelines for Deriving Numerical National Water Quality Criteria for the Protection of Aquatic Organisms and Their Uses indicate that, except possibly where a locally important species is very sensitive, freshwater aquatic organisms and their uses should not be affected unacceptably if the 4

-day average concentration of arsenic(II1) does not exceed 190 ug/L more than once every 3 years on theaverage and if the 1

-hour average concentration does not exceed 360 ug/L more than once every 3 years on the average. The procedures described in the Guidelines indicate that, except possibly where a locally important species is very sensitive, saltwater aquatic organisms and their uses should not be affected unacceptably if the 4

-day average concentration of arsenic(II1) does not exceed 36 ug/L more than once every 3 years
on the average and if the 1

-hour average concentration does not exceed 69 ug/L more than once every 3 years on the average. This criterion might be too high wherever Skeletonema cosrarum or Thalassiosira aestivalis 

### --- are ecologically important. Not enough data are available to allow derivation of numerical national water quality criteria for freshwater aquatic life for inorganic arsenic(V) or any organic arsenic compound. Inorganic arsenic(V) is acutely toxic to freshwater aquatic animals at concentrations as low as 850 ug/L and an acute

-chronic ratio of 28 

### was obtained with the fathead minnow. Arsenic(V) affected freshwater aquatic plants at concentrations as low as 48 ug/L. Monosodium methanearsenace (MSMA) is acutely toxic to aquatic animals at concentrations as low as 1,900 ug/L, but no data are available concerning chronic toxicity to animals or toxicity to plants. Very few data are available concerning the toxicity of any form of arsenic other than inorganic arsenic(II1) to saltwater aquatic life. The available data do show that inorganic arsenic(v) is acutely toxic to saltwater animals at concentrations as low as 2,319 ug/L and affected some saltwaterplants at 13 

### to 56 ug/L. chronic toxicity of any arsenic(II1) to saltwater No data are availableconcerning the form of arsenic other than inorganic aquatic life. EPA believes that a measurement such as tlacid-solublettwould provide a more scientifically correct basis upon which to establish criteria formetals. The criteriawere developed on this basis. However, atthistime, no EPA approved methods for such a measurement are available to implement the criteria through the regulatory programs of the Agency and the States. The Agency is considering development and approval of methods for
a measurement such as acid

-soluble. Until available, however, EPA recommends applying the criteria using the total recoverable method. This has two impacts: (1)certain species of some metals cannot be analyzed directly because the total recoverable method does not distinguish between individual oxidation states, and (2) these criteria may be overly protective when based on the total recoverable method. The recommended exceedence frequency of 3 years is the Agency's best scientificjudgment of theaverage amount of time it willtake an unstressed system torecover from a pollution event in which exposure to arsenic(II1) exceeds the criterion. a stressed system, for example, one inwhich several outfalls occur in a limited area, would be expected torequire more time for recovery. The resilience of ecosystems and their ability to
recover differ greatly, however, and site

- specific criteria may be established if adequate justification is provided. 

# 0 The use of criteria in designing waste treatment facilities , requires the selection of an appropriate wasteload a1 locationmodel. Dynamic models are preferred for the application of these criteria. Limited data or other factors may make their use impractical, in which case one should rely on a steady

-state model, The Agency recommends the interim use of 145 or lQlO for Criterion Maximum Concentration design flow and 745 

### or 7Q10 for the Criterion Continuous Concentration design flow in steadystatemodels forunstressed and stressed systems respective1 y. These matters are discussed in more detail in the Technical Support Document fox Water Quality

-Based Toxics Control (U.S. 

### EPA, 1985). HUMAN HEALTH CRITERIA: For the maximum protection of human health from the potential carcinogenic effects due to expos,ureof arsenic through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentration should be zero based on the nonthreshold assumption for this chemical. However, zero level may not be attainable at the present time. Therefore, the levels which may result 

### in incremental increase of cancer risk over the lifetime are estimated at and The corresponding 

### criteria are 22 ng/L, 2.2 ng/L, and .22 ng/L, respectively. If the above estimates are made for consumption of aquatic organisms only, excluding consumption of water, the levels are 175 ng/L, 17.5 ng/L, and 1.75 ng/L, respectively. Other concentrations representing different risk levels may be 

# e

calculated by use of the Guidelines. The risk estimate range is presented for information purpoes and does not represent an

,, Agency judgment on an 81acceptable8t risk level.(45 SEE F.R. 79318 APPENDIX A Nov. 28,1980) (50 FOR METHODOLOGY F.R. 30784, July



# aASBESTOS CRITERIA: Aquatic Life No freshwater organisms have been tested with any asbestifom mineral and no statement can be made concerning acute or chronic toxicity No saltwater organisms have been tested with any asbestiform mineral and no statement can be made concerning acute or chronic toxicity. Human Health For the maximum protection of human health from the potential carcinogenic effects of exposure to asbestos through ingestion of water and contaminated aquatic organisms, the ambient water concentration should be zero. The estimated levels which would result in increased lifetime cancer risks of and are 300,000 fibers/L, 30,000 fibers/L, and 3,000 fibers/L, respectively. Estimates for consumption of aquatic organisms only, excluding the consumption of water cannot be made.

(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR MmnoDomeYBACTERIA

Freshwater Bathinq Based on a statistically sufficient number of samples (generally not less than 5 samples equally spaced over 

### a 30

-day period), the geometric mean of the indicated bacterial densities should not exceed one or the other of the following:(') E. coli 126 per 100 ml; or enterococci 33 per 100 ml;
no sample should exceed a one sided confidence limit (C.L.) calculated using the following as guidance: designated bathing beach 75%C.L. moderate use for bathing 82% C.L. light use for bathing 90%C.L. infrequent use for bathing 95%C.L. based on a site

-specific log standard deviation, 

### or if site data
are insufficient to establish a log standard deviation, then using 0.4 as the log standard deviation for both indicators. Marine Water Bathinq Based on 

### a statistically sufficient number of samples (generally not less than 5 samples equally spaced over a 30

-day period), the geometric mean of the enterococci densities should not exceed 35 per 100 ml; no sample should exceed 

### a one sided confidence limit using the following as guidance: designated bathing beach 75%C.L. moderate use for bathing 82% C.L. light use for bathing 90%C.L. infrequent use for bathing 95%C.L.based on a site

-specific log standard deviation, or if site data
are insufficient to establish a log standard deviation, then using 0.7 as the log standard deviation.

Note (1) 

## - Only one indicator should be used. The Regulatory agency should select the appropriate indicator for 

### its conditions. Shellfish Harvesting Waters The median fecal coliform bacterial concentration should not exceed 14 MPN per 100ml with notmore than 10percent of samples exceeding 43MPNperlOOml forthetakingofshellfish. RATIONALE Bathing Waters A recreational water quality criterion can be defined as a "quantifiable relationship between the density of an indicator 

### in the water and the potential human health risks involved in the water's recreational use." From such a definition, a criterion can be adopted which establishes upper limits for densities of indicator bacteria in waters that are associated with acceptable health risks for swimmers. The Environmental ProtectionAgency, in 1972, initiated a series of studies at marine and fresh water bathing beaches which
were designed to determine if swimming in sewage-contaminated marine and fresh water carries a health risk for bathers; and, if so, to what type of illness. Additionally, the Agency wanted to determine which bacterial indicator is best correlated to swimming

-associatedhealth effects and if the relationship 

### is strong enough to provide a criterion. (l)

### The quantitative relationships between the rates of swimmingassociated health effects and bacterial indicator densities were determined using regression analysis. Linear relationships were estimated from data grouped on the basis of 

### summers 

### or trials with similar indicator densities. The data for each summer were analyzed by pairing the geometric mean indicator density for a summer bathing season at each beach with the corresponding swimming

-associated gastrointestinal illness rate for the same
summer. The swimming

-associated illness rate was determined by subtracting the gastrointestinal illness rate in nonswimmers from that for swimmers. Ihese two variables from multiple beach sites
were used 

### to calculate a regression coefficient, y

-intercept and 95%

### confidence intervals for the paired data. In the marine studies the total number of points for use in regression analysis
was increased by collecting trial days with similar indicator densities from each study location and placing them into groups. The swimming

-associated illness rate was determined as before, by suk&racting the nonswimmer illness rate 

### of all the individuals included in the grouped trial days from the swimmer illness rate during these safe grouped trial days. The grouping by trial days with similar indicator densities approach was not possible with the freshwater data because the variation of bacterial indicator densities in freshwater samples was not larqe enouqh to 

### allow such an adjustment to be made. For the saltwater studies the results of the regression analyses of illness rates against indicator density data was very similar using the "by summer" 

### or Itby grouped trial days" approaches. 

# 0

1The methods used to enumerate the bacterial indicator densities which showed the best relationship to swimmingassociated gastroenteritis rates were specifically developed €or the recreational water quality studies.' These membrane filtermethods have successfully undergone precision and bias testingby the EPA Environmental Monitoring and Support Laboratory. (2) Several monitoring situations to assess bacterial quality are encountered by regulatory agencies. The situationneeding the most rigorous monitoring is the designated swimming beach. Such
areas are frequently lifeguard protected, provideparking and other public access and are heavily used by the public. Public beaches of this type were used by EPA in developing the relationship described in this document. Other recreational activities may involvebodies of water which are regulated by individual State water quality standards. These recreational resources may be natural wading ponds used by children or waters where incidential fullbody contact occurs because of water skiing or other similar activities. EPA's evaluation of the bacteriological data indicated that using the fecal coliform indicator group at the maximum geometric
mean of 200perlOOm1, recommended inQualiwCriteria



## ___- forwater would cause an estimated 8 illnessper 1,000 swimmers at fresh water beaches and 19 illness per 1,000 swimmers at marine beaches. These relationships are only approximate and are based
on applying ratios of the geometric means of the various indicators from the EPA studies to the 200 per 100 ml fecalcoliform criterion. However,these are EPA's best estimates of the accepted illness rates for areaswhich apply the EPA fecal coliform criterion. The E. coli and enterococci criteria presented in Table 1 were developed using these currently accepted illness rates. The equations developed by D~four(~) and Cabelli(*) were used to calculate the geometric mean indicator densities corresponding to the accepted gastrointestinal illness rates. These densities are for steady state dry weather conditions. The beach is in noncompliance with the criteria if the geometric mean of several bacterial density samples exceeds the value listed in Table 1. Noncompliance is also signaled by an unacceptably high value for any single bacterial sample. The maximum acceptable bacterial density for a single sample is set higher than that for the geometric mean, in order to avoid necessary beach closings based on single samples. Indeciding whether a beach shouldbe left open, 

### it is the long term geometric mean bacterial density that is of interest. Because of day

-to

-day fluctuations around this mean, 

### a decision based on a single sample (or even several samples) may be erroneous, i.e., the sample may exceed the recommended mean criteria 

### even though the long

-term geometric
mean 

### is protective,ormay fall below the maximum even if this
mean 

### is 

### in the nonprotective range. To set the single sample maximum, it is necessary to specify the desired chance that the beach will be left open when the protection is adequate. This chance, 

### or confidence level,was based on Agency judgment. For the simple decision rule considered here, a smaller confidence level corresponds to a more /stringent (i.e. lower) single sample maximum. Conversely, a greater confidence level corresponds to less stringent (i.e. higher) maximum values. This technique reduces the chances of single samples inappropriately indicating violations of the recommended criteria. By using a control chart analogy (5) and the actual log standard deviations from the EPA studies, single sample maximum densities for various confidence levelswere calculated. EPA then assigned qualitative use intensities to those confidence levels. A low confidence level (75%)was assigned to designated beach areas because a high degree of caution should be used to evaluate water quality for heavily used areas. Less intensively used areas would allow less restrictive single sample limits. Thus, 95% confidence might be appropriate for swimmable water in remote areas. Table 1 summarizes the results of these calculations. These single sample maximum levels should be recalculated for individual areas if significant differences in log standard deviations occur. The levels displayed in Table 1 depend not only on the assumed standard deviation of log densities, but also on the chosen level of acceptable risk. While this level was based 

### on the historically accepted risk, it is still arbitrary insofar as the historical risk was itself arbitrary. Currently EPA is not recommending a change in the stringency of its bacterial criteria for recreational waters. Such a change does not appear warranted until more information based on greater experience with the new indicators canbe accrued. EPA and theState Agencies can then evaluate the impacts of change in 

### terms of beach closures and other restricted 

### uses.
Shellfish Harvesting Waters The microbiological criterion for shellfishwater quality has been accepted by international agreement tobe 70 total coliforms per 100 

### ml, using a median MPN, with no more than 10percent 

### of the 

### values exceeding 230 total coliforms. No evidence of disease outbreak from consumption 

### of 

### raw shellfishwhich were grown in waters meeting this bacteriological criterion has been demonstrated. This standard has proven to be a practical limit when supported by sanitary surveys of the growing waters, acceptable quality in she1 lfish meats, and good epidemiological evidence. However, evidence from field investigations suggests that not alltotal coliform occurrences can be associated with fecal pollution. Thus, attentionhasbeen directed toward the adoption of the fecal coliform test tomeasure more accurately the occurrence and magnitude of fecal pollution in shellfishgrowing waters. 

### A series of studies was initiated by the National Shellfish Sanitation Program and data relating the occurrence of total coliforms to numbers 

### of fecal coliforms were compiled. The data showthata 70 coliformMPNperlOOmlatthe5Othpercentilewas equivalent toa fecal coliform MPN of 14 per 1JOml. The data, therefore, indicate that a median value for a fecal coliform standard is 15 and the9Othpercentileshouldnotexceed 43 fora 

# 0 5-tubeI 3

-dilution method. EPA is currently (1986) co- sponsoring, with the National

### Oceanic and Atmospheric Administration, research into the application of the enterococci and E. 

### coli indicators for assessing the quality of shellfish harvesting waters. The Food and Drug Administration is also reviewing the results of these studies. A 

### change 

### to the new indicatorsmay be forthcoming if the studies show a correlation between gastrointestinal disease and the consumption of raw shellfish from waters with defined densities of the new indicators. However, these studies have not sufficiently progressed 

### to justify any change 

### at this time. Thus, evaluation of the microbiological suitability of waters for recreational taking of 

### shellfish should be based upon the fecal colifonn bacterial levels. 

## c6)CIIITERIA FOR INDICAllR FOR BrnIOrnCALIEWITIES shlesanpleMaximun Allowable Oensity (41, (5) Acceptable Srhh Steady State Designated Msderate Full Lightly Used Infrequmtly Used enteritis Fate per Indicator (upper 75%C.L.) Recreation Contact Rxreation 1000 swimners Density (upper 82%CL.) Rereation (upper 95%CL.) Assaiated Qstro- Geawtric Mean madlArea my contact Full my 

### m11 myONltact (upr90%C. L. Freshwater

enterococci 8 33(1)



## - - E. coli 8 126P) Marine Bter 61 235 89 108 151 298 406 576

enterococci 19 35(3) 104 124 276 NOtest (1) Calculated to nearest mlenunber using quation:
Calculated to nearest whole nunber using equation:
Calculated to nearest wblenunber using equation: (mean entemxccidensity) = i"tilogl0 (mean

## -- E. coli density) = antFloglO (mean enterococcidensity) = antiloglo illness rate/lOOO people

### + 6.28 9.40 (2) illness rate/l000 pqi le+ 11.74 9.40 (3) illness rate/lOOO people

# - 0.20 12.17 500

(4) sirgle sanple lhit=mtilql0(laglo indicator geamtric

### + Factor determined frm x (lq110stand, mean density/100 ml) areas rnder the Wnnal deviation) prcbability cuwe for tb ass- level of pmbability The appmpdata factors for tb indicated one sided confidence levels are: 75%C.L. 

## - -675 82% C.L. 

## - -935 90%C.L. 

## - 1.28 95%C.L. 

## - 1.65 (5) Based on the observed log standard deviations dwhq tk EPA studies: and enterccccci; and 0.7 formq*e mter: enterococci. standard dwiation for itscoditions &ich muld then vary t& sig(ie mple m t. 0.4 forfreshwater E . 

### & Each 'uridi tion sbupfstablish-its om1.

2.

3.

4.

5.

6. References Ambient Water Quality Criteria for Bacteria 

# - 1986, EPA 440/5-84-002, U.S. Environmental Protection Agency, Office of Water Regulations and Standards, Washington, DC. (NTIS
access #: PB 86

-158

-045) Test Methods for Escherichia coli and Enterococii in Water By The Membrane Filter procedure, EPA 600/4-85-076, U.S. Environmental Protection Agency, Cincinnati, OH. (NTIS
access #: PB 86

-158

-052) Dufour, A. P. 1983. Health Effects Criteria for Fresh Recreationa1 Waters. EPA-60 O/ 1

-84

-004

## , U.S. Environmenta1 Protection Agency, Cincinnati, OH. Cabelli, V. J. 1981. Health Effects Criteria for Marine Recreational Waters. EPA-600/1-80-031, U.S. Environxental Protection Agency, Cincinnati, OH. 

### ASTM. 1951. Manual on Quality Control of Materials. Special Technical Publication 15

-C, American Society for Testing and Materials, Philadelphia, PA. U.S. Environmental Protection Agency. 1976. Quality Criteria forWater. U.S. Environmental ProtectionAgency, Washington, DC.BARIUM

1mg/L for domestic water supply (health).

INTRODUCTION: Barium is a yellowish

-white metal of the alkaline earth group. It occurs in nature chiefly as barite, BaS04 and witherite, BaC03, both of which are highly insoluble salts. The metal is stable 

### in dry air, but readily oxidized by humid air or water. Many of the salts of barium are soluble inboth water and acid, and soluble barium salts are reported to be poisonous (Lange, 1965: NAS, 1974). However, barium ions generally are thought tobe rapidly precipitated orremoved from solutionby absorption and sedimentation (McKee and Wolf, 1963 NAS, 1974). I

While barium is a malleable, ductile metal, its major commercial value is in its compounds. Barium compounds are used 

### in a variety of industrial applications including the metallurgic, paint, glass and electronics industries, as well as for medicinal purposes.
RATIONALE: Concentrations of barium drinking water supplies generally range from less than 0.6 ug/L to approximately 10 ug/L with upper limitsinafewmidwesternandwesternStates ranging from100to 3,000 ug/L (PHS, 1962/1963; Katz, 1970; Little, 1971). Barium enters the body primarily through 

### air and water, since appreciable amounts are not contained in foods (NAS, 1974). 

# 0The fatal dose ofbarium forman 

### is reported 

### tobe 550 

### to 600 mg. Ingestion of soluble barium compounds may also result 

### in effects on the gastrointestinal tract, causing vomiting and diarrhea, and 

### on the central nervous system, causing violent tonic and clonic spasms followed in some cases by paralysis

(Browning, 1961; Patty, 1962, cited in Preliminary Air Pollution Survey of Barium and Its Compounds, 1969). Barium salts are considered to be muscle stimulants, especially for the heart muscle (Sollman, 1957). By constrictingblood vessels, barium may cause an increase 

### in blood pressure. On the otherhand, 

### it 

### is not likely that barium accumulates in the bone, muscle, kidney


### or other tissues because 

### it is readily excreted (Browning, 1961; McKee and Wolf, 1963). Stokinger and Woodward (1958) developed a safe concentration for barium in drinking water based on the limiting values for industrial atmospheres, an estimate of the amount absorbed into the blood stream, and daily consumption of 2 liters of water. From other factors they arrived at a limiting concentration of 2 mg/L for a healthy adult human population, to which a safety factor was applied to allow for any possible accumulation in the body. Since barium 

### is not removed by conventional water treatment processes and because of the toxic effect on the heart andbloodvessels,a limitoflmg/L isrecommended forbarium in domestic water supplies. Experimental data indicate that the soluble barium concentration in fresh and marine water generally would have 

### to exceed 50 mg/L before toxicity to aquatic life would be expected. 

### In most natural waters, there is sufficient sulfate or carbonate

### to precipitate the barium present in the water as a virtually insoluble, non-toxic compound. Recognizing that the physical and chemical properties 

### of barium generally wil

### P preclude the existence of the toxic soluble form under usual marine and fresh water conditions, a restrictive criterion for aquatic life appears unwarranted. 

# 0

(QUALITY CRITERIA FOR WATER, JULY 1976) PB-263943 SEE APPENDIX C FOR METHODOLOGYCRITERIA: Aquatic Life
The available data for benzene indicate that acute toxicity to freshwater aquatic life occurs at concentrations as low as 5,300 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No data are available concerning the chronic toxicity of benzene to sensitive freshwater aquatic life. The available data for benzene indicate that acute toxicity to saltwater aquatic life occurs at concentrations as low as 5,100 ug/L and would occur at lower concentrations among species that aremore sensitive than those tested. No definitive data
are available concerning the chronic toxicity of benzene to sensitive saltwater aquatic life,but adverse effects occur at concentrationsas lowas700ug/Lwitha fish speciesexposed for 168 days. Human Health For the maximum protection of human health from the potential carcinogenic effects of exposure to benzene through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentrations should be zero, based on the non threshold assumption Tor this chemical. However, zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer risk over the lifetime are estimated at and The corresponding recommended criteria are 6.6 ug/L, 0.66 ug/L, and0.066 ug/L, respectively. If these estimates are made for consumption of aquatic organisms only, excluding consumption of

### i water, the levels are 400 ug/L, 40.0 ug/L, and 4.0 ug/L, respectively.

(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYBENZIDINE
Aquatic Life The available data for beniidine indicate that acute toxicity to freshwater aquatic life occurs at concentrations as low as 2,500 ug/L and would occur at lower concentrations among species that are more sensitive than those tested NO data are available concerning the chronic toxicity of benzidine to sensitive freshwater aquatic life. No saltwater organisms have been tested with benzidine and no statement can be made concerning acute and chronic toxicity.
Human Health For the maximum protection of human health from the potential carcinogenic effects of exposure to benzidine through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentrations should be zero,based on the nonthreshold assumption for this chemical. However, zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer risk over the lifetime are estimated at loq5, The corresponding recommended criteria are 1.2 ng/L, 0.12 ng/L, and 0.01 ng/L, respectively. If these estimates are made for consumption of aquatic organisms only, excluding consumption of water, the levels are 5.3 ng/L, 0.53 and

ng/L, and 0.05 ng/L, respectively.
145 F.R. 79318, November 28. 1980) 

# 0

_# SEE APPENDIX B 'FOR METHODOLOGYBERYLLIUM
CRITERIA: Aquatic Life
The available data for beryllium indicate that acute and chronic toxicity to freshwater aquatic life occur at concentrations as low as 130 and 5.3 ug/L, respectively, and would occur at lower concentrations among species that are more sensitive than those tested. Hardness has a substantial effect


### on acute toxicity. The limited saltwater data base available for beryllium does not permit any statement concerning acute or chronic toxicity.

Human


### For the maximum protection of carcinogenic effects of exposure Health
human health from the potential to beryllium through ingestion 

### of contaminated water and contaminated aquatic organisms, the ambient water concentration should be zero, based on the non threshold assumption for this chemical. However, zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer risk over the lifetime are estimated at 10'-6t and 10-70 The corresponding recommended criteria are 37 ng/L, 3.7 ng/L, and 0.37 ng/L, respectively. If these estimates are made 

### forconsumption of aquatic organisms only, excluding consumption of water, the levels are 641 ng/L, 64.1 ng/L, and 6.41 ng/L, respectively.

(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYCRITERION:
750 mg/L for long-term irrigation on sensitive crops.
INTRODUCTION: Boron 

### is not found in its elemental form 

### in nature: it is usually found as a sodium 

### or calcium borate salt. Boron salts
are used 

### in fire retardants, the production of glass, leather tanning and finishing industries, cosmetics, photographic materials, metallurgy and for high energy rocket fuels. Elemental boron also can be used 

### in nuclear reactors for neutron absorption. Borates are used as "burnable" poisons.
RATIONALE : Boron is an essential element- for growth of plants but there is no evidence that it is required by animals, The maximum concentration found in 1,546 samples of river and lake waters 

### from various parts of the United States was 5.0 mg/L; the mean Value was 0.1 mg/L (Kopp and Kroner, 1967). Ground waters could contain substantially higher concentrations at certain places. The concentration in seawater is reported as 4.5 mg/L in the form of borate (NAS, 1974). Naturally occurring concentrations of boron should have no effects on aquatic life. The minimum lethal dose for minnows exposed to boric acid at 20 OC for 6 hours was reported to be 18,000 to 19,000 mg/L 

### in distilled water and 19,000 to 19,500 mg/L in hard water (Le clerc and Devlaminck, 1955: Le Clerc, 1960).

### In the dairy cow, 16 to 20 g/day of boric acid for 40 days produced no ill effects (McKee and Wolf, 1963). Sensitive crops have shown toxic effects at 1000 ug/L or less of boron (Richards, 1954). Bradford (1966), ina 

### review of boron deficiencies and toxicities, stated that when the boron concentration in irrigation waters was greater than 0.75 ug/L,
some sensitive plants such as citrus began to show injury. Biggar and Fireman (1960) showed that with neutral and alkaline soils of high absorption capacities, water containing 2 ug/L boron might be used for some timewithout injury to sensitive plants. The criterion of 750 ug/L is thought to protect sensitive crops during long

-term irrigation.

(QUALITY CRITERIA FOR WATER, JULY 1976) PB

-263943 SEE APPENDIX C FOR METHODOLOGYCADMIUM AQUATIC LIFE SUMMARY: 

# - Freshwater acute values for cadmium are available for species in 44 genera and range from 1.0 ug/L for rainbow trout to 28,000 ug/L for a mayfly. The antagonistic effect of hardness on acute toxicity has been demonstrated with five species. Chronic tests have been conducted 

### on cadmium with 12 freshwater fish species and 4 invertebrate species with chronic values ranging from 0.15 ug/L for

## _- Daphnia 

## -- mas5 - to 156 ug/L for the Atlantic salmon. Acute

-chronic ratios are available for eight speciesand range from 0.9021 for the chinook salmon to 433.8 for the flagfish. Freshwater aquatic plants are affected by cadmium at concentrations ranging from 2 to 7,400 ug/L. These values are in the same range as the acute toxicity values for fish and invertebrate species, and are considerably above the chronic values. Bioconcentration factors (BCFs) for cadmium in fresh water range from 164 to 4,190 for invertebrates and from 3 to 2,213 for fishes. Saltwater acute values for cadmium and five species of fishes range from 577 ug/L for larval Atlantic silverside to 114,000 ug/L for juvenile mummichog. Acute values for 30 species of invertebrates range from 15.5 ug/L for a mysid to 135,000 ug/L for an oligochaete worm. The acute toxicity of cadmium generally increases as salinity decreases. The effect of temperature seems to be species

-specific. Two life

-cycle tests with 

## - Mysidopsis bahia under different test conditions resulted in similar chronic values of 8.2 and 7.1 ug/L, but the acute

-chronic ratios were 1.9 and 15, respectively. The acute values appear to 

# 0reflect effects of salinity and temperature, whereas the few available chronic values apparently do not. A life-cycle test with Mysidopsis bigelowi also resulted 

### in a chronic value of 7.1 ug/L and an acute-chronic ratio of 15. and macroalgae revealed effects at 22.8 to 860 ug/L. Studies with microalgae

BCFs determined with a variety of saltwater invertebrates ranged from 5 to 3,160. BCFs for bivalve molluscs were above 1,000 

### in long exposures, with no indication that steady-state had been reached. Cadmium mortality is cumulative for exposure periods beyond 4 days. Chronic cadmium exposure resulted 

### in significant effects on the growth of bay scallops at 78 ug/L and
on reproduction of a copepod at 44 ug/L.
NATIONAL CRITERIA: 1 The procedures described in the Guidelines for Deriving Numerical National Water Quality Criteria for the Protection of Aquatic Organisms and Their Uses indicate that, except possibly where a locally important species is very sensitive, freshwater aquatic organisms and their uses should not be affected unacceptably if the 4-day average concentration (in ug/L) of cadmium does not exceed the numerical value given by .(0.7852 [ln(hardness)1-3.490) more than once every 3 years on the average and if the one-hour average concentration (in ug/L) does not exceed the numerical value given by .(1.128[ ln(hardness)]- 3.828) more than once every 3 years on the average. For example, at hardnesses of 50, 100, and 200mg/L as CaC03 the 4- day average concentrations of cadmium are 0.66, 1.1, and 2.0 ug/L, respectively, and the 1-hour average concentrations are1.8, 3.9 and 8.6 ug/L. If brook trout, brown trout, and striped bass are as sensitive as some data indicate, they might not be protected by this criterion. The procedures described in the Guidelines indicate that, except possibly where a locally important species is very sensitive, saltwater aquatic organisms and their uses should not be affected unacceptably if the 4

-day average concentration of cadmium does not exceed 9.3 ug/L more than once every 3 years on the average and if the 1

-hour average concentration does not exceed 43 ug/L more than once every 3 years on the average. The little information that is available concerning the sensitivity of the American lobster to cadmium indicates that this important species might not be protected by thiscriterion. Inaddition, data suggest that the acute toxicity of cadmium is salinity dependent: therefore, the 1

-hour average concentration might be underprotective at low salinities and overprotective athigh salinities. EPA believes that a measurement such as t'acid-solublell would provide a more scientifically correct basis upon which to establish criteria formetals. The criteriaweredeveloped on this basis. However, at this time, no EPA

-approved methods for such a measurement are available to implement the criteria through the regulatory programs of the Agency and the States. The Agency is considering development and approval of methods for
a measurement such as acid

-soluble. Until available, however, EPA recommends applying the criteria using the total recoverable method. This has two impacts: (1)certain species of some metals 

# 0cannot be analyzed directly because the total recoverable method does not distinguish between individual oxidation states, and (2) these criteria may be overly protective when based on the total recoverable method. The recommended exceedence frequency of 3 years is the Agency's best scientific judgment of the average amount of time 

### it will take an unstressed system to recover from a pollution event in which exposure to cadmium exceeds the criterion. 

### A stressed system, for example, one in which several outfalls occur in a limited area, would be expected to require more time for recovery. The resilience of ecosystems and their ability to
recover differ greatly, however, and site

-specific criteria may be established if adequate justification is provided. I The use of criteria in designing waste treatment facilities requires the selection of an appropriatewasteload allocation model. Dynamic models are preferred for the application of these criteria. Limited data or other factors may make their use impractical, in which case one should rely on a steady

-state model. The Agency recommends the interim use of 145 or lQlO for Criterion Maximum Concentration design flow and 745 or 7410 for the Criterion Continuous Concentration design flow in steadystate models for unstressed and stressed systems, respectively. These matters are discussed 

### in more detail in the Technical Support Document for Water Quality

-Based Toxics Control (U.S. EPA, 1985). HUMAN HEALTH CRITERIA: The ambient water quality criterion for cadmium is recommended to be identical to the existing drinking waterstandard which is 10ug/L. Analysis of the toxic effects data resulted in a calculated level which is protective of human 

# 0

health against the ingestion of contaminated water and contaminated aquatic organisms. The calculated value is comparable to the present standard. For this reason a selective criterion based on exposure solely from consumption of 6.5 grams of aquatic organisms was not derived.

(45 F.R. 79318 Nov. 28,1980) (50 F.R. 30784, July 29, 1985) SEE APPENDIX A FOR METHODOLOGYCARBON TETRACHLORIDE CRITERIA: Aquatic Life The available data for carbon tetrachloride indicate that acute toxicity to freshwater aquatic life occurs at concentrations as low as 35,200 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. 

### No data are available concerning the chronic toxicity of carbon tetrachloride to sensitive freshwater aquatic life. The available data for carbon tetrachloride indicate that acute toxicity to saltwater aquatic life occurs at concentrations
as low as 50,000 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No data
are available concerning the chronic toxicity of carbontetrachloride to sensitive saltwater aquatic life.

Human Health For the maximum protection of human health from the potential carcinogenic effects of exposure to carbon tetrachloride through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentrations should be zero, based on the nonthreshold assumption for this chemical. However, zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer risk over the lifetime are estimated at and lo-’. The corresponding recommended criteria are 4.0 ug/L, 0.40ug/L, and 0.04 ug/L, respectively. If these estimates are made forconsumption of aquatic organisms only, excluding consumption of

I water, the levels are 69.4 ug/L, 6.94 ug/L, and 0.69 ug/L respectively. 

# 0

(45F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYCRITERIA: 

# 0 CHLORDANE Aquatic 

### Life

For chlordane the criterion to protect freshwat tic life
as derived using the Guidelines is 0.0043 ug/L as a 24-hOUr average, and the concentration should not exceed 2.4 ug/L at any time. For chlordane the criterion to protect saltwater aquatic life as derived using the Guidelines 

### is 0.0040 ug/L as a 24

-hour average, and the concentration should not exceed 0.09 ug/L at any time.

Human Health 

### r aqu

For the maximum protection of human health from the potential carcinogenic effects of exposure to chlordane through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentration should be zero based on the nonthreshold assumption for this chemical. However, zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer risk over the lifetime are estimated at loq5, lom6, and lo-’. The corresponding recommended criteria are 4.6 ng/L, 0.46 ng/L, and 0.046 ng/L, respectively. If these estimates are made for consumption of aquatic organisms only, excluding consumption of water, the levels are 4.8 ng/L, 0.48 ng/L, and 0.048 ng/L, respectively.

(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYCHLORINATED BENZENES CRITERIA: Aquatic 

# - Life The available data for chlorinated benzenes indicate that acute toxicity to freshwater aquatic life occurs at concentrations as low as 250 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No data are available concerning the chronic toxicity of the more toxic of the chlorinated benzenes to sensitive freshwater aquatic life, but toxicity occurs at concentrations as low as 50 ug/L for a fish species exposed for 7.5 days. The available data for chlorinated benzenes indicate that acute and chronic toxicity to saltwater aquatic life occur at concentrationsas low as 160 and 129 ug/L, respectively,and would occur at lower concentrations among species that are more sensitive than those tested.Human Health Xonochlorobenzene For comparison purposes, two approaches were used to derive criterion levels for monochlorobenzene. Based on available toxicity data, for the protection of public health the derived level is 488 ug/L. Using available organoleptic data, to control undesirable taste and odor quality of ambient water the estimated level is 20 ug/L. It should be recognized that organoleptic data have limitations as a basis for establishing water quality criteria, and have no demonstrated relationship to potential adverse human health effects. 

# a
(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGY

# 0 CRITERIA: CHLQRINATED ETHANES
Aquatic 

# - Life The available freshwater data for chlorinated ethanes indicate that toxicity increases greatly with increasing chlorination, and that acute toxicity occurs at concentrations as low as 118,000ug/L for l,Z-dichloroethane,18,000ug/L for two trichloroethanes, 9,320ug/L for two tetrachloroethanes, 7,240 ug/L for pentachloroethane, and 980ug/L for hexachloroethane. Chronic toxicity occurs 

### at concentrations as low as 20,000 ug/L for 1,2-dichloroethane, 9,400 ug/L for l,l,Z-trichloroethane, 2,400 ug/L for 1,1,2,2-tetrachloroethane, 1,100 ug/L for pentachloroethane, and 540 ug/L for hexachloroethane. Acute and chronic toxicity would occur at lower concentrations among species that are more sensitive than those tested. 

# 0

The available saltwater data for chlorinated ethanes indicate that toxicity increases greatly with increasing chlorination and that acute toxicity to fish and invertebrate species occurs at concentrations 

### as low as 113,000 ug/L for lI2-dichloroethane, 31,200 ug/L for l,l,l-trichloroethane, 9,020 ug/L for 1,1,2,2-tetrachloroethane, 390 ug/L for pentachloroethane, and 940 ug/L for hexachloroethane. Chronic toxicity occurs at concentrations as low as 281 ug/L for pentachloroethane. Acute and chronic toxicity would occur at lower concentrations among species that are more sensitive than those tested.Human Health For the maximum protection of human health from the potential carcinogenic effects of exposure to 1,2-dichloroethane through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentration should be zero, based
on the nonthreshold assumption for this chemical. However, zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer risk
over the lifetime are estimated at and The corresponding recommended criteria are 9.4 ug/L, 0.94 ug/L, and 0.094 ug/L, respectively. If these estimates are made for consumption of aquatic organisms only, excluding consumption of water,' the levels are 2,430 ug/L, 243 ug/L, and 24.3 ug/L, respectively. For the maximum protection of human health from the potential carcinogenic effects of exposure to l,l, 2

-trichloroethane through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentration should be zero, based
on the nonthreshold assumption for this chemical. However,
zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer risk over the lifetime are estimated at and lo-'. The corresponding recommended criteria are 6.0 ug/L, 0.6 ug/L, and 0.06 ug/L, respectively. If these estimates are made for consumption of aquatic organisms only, excluding consumption of water, the levels are 418 ug/L, 41.8 ug/L, and 4.18 ug/L, respectively.For the maximum protection of human health from the potential carcinogenic effects 

### of exposure to 1,1,2,2-tetrachloroethane through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentration should be zero, based
on the nonthreshold assumption for this chemical. However, 

### zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer risk over the lifetime are estimated at and The corresponding recommended criteria are 1.7 ug/L, 0.17 ug/L, and 0.017 ug/L, respectively. If these estimates are made for consumption of aquatic organisms only, excluding consumption of water, the levels are 107 ug/L, 10.7 ug/L, and 1.07 ug/L, respectively. I For the maximum protection of human health from the potential carcinogenic effects of exposure to hexachloroethane through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentration should be zero, based
on the nonthreshold assumption for this chemical. However, zero level may not be attainable at the present time. Therefore, the levelswhich may result in incremental increase of cancer risk
over the lifetime are estimated at and loe7. The corresponding recommended criteria are 19 ug/L, 1.9 ug/L, and 0.19 ug/L, respectively. If these estimates are made for consumption 

### of aquatic organisms only, excluding consumption of water, the levels are 87.4 ug/E, 8.74 ug/L, and 0.87 ug/L, respectively. 

# 0

JFor the protection of human health from the toxic properties of l,l,l-trichloroethane ingested through water and contaminated aquatic organisms, the ambient water criterion is determined to be 18.4 mg/L. For the protection of human health from the toxic properties of l,l,l-trichloroethane ingested through contaminated aquatic organisms alone, the ambient water criterion 

### is determined to be 1.03 ug/l. Because of insufficient available data €or monochloroethane, 1,l-dichloroethane, 1,1,l12-tetrachloroethane, and pentachloroethane, satisfactory criteria cannot be derived at this time, using the present guidelines.
(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYCRITERIA: CHLORINATED NAPHTHALENES
Aquatic Life The available data for chlorinated naphthalenes indicate that acute toxicity to freshwater aquatic life occurs at concentrations as low as 1,600 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No data are available concerning the chronic toxicity of chlorinated naphthalenes to sensitive freshwater aquatic life. The available data for chlorinated naphthalenes, indicate that acute toxicity 

### to saltwater aquatic life occurs at concentrations
as low as 7.5 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No data are available concerning the chronic toxicity of chlorinated naphthalenes to sensitive saltwater aquatic life. 

# 0

Human Health Using the present guidelines, a satisfactory criterion cannot be derived at this time because of insufficient available data for chlorinated naphthalenes.

(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGY 

# 0

2CHLORINE

SUMMARY: Thirty

- three freshwater species in 28 genera have been exposed to TRC and the acute values range from 28 ug/L for


## - Daenia 

## - - magna to710 Ug/L forthethreespine stickleback. Fish and invertebrate species had similar ranges of sensitivity. Freshwater chronic tests have been conducted with two invertebrate and one fish species and the chronic values for these three species ranged from less than 3.4 to 26 ug/L, with acute

-chronic ratios from 3.7 to greater than 78. The 

### acute sensitivities of 24 species of saltwater animals 

### in 21genera have been determined for CPO, and theLC50 range from 26 ug/L for the eastern oyster to 1,418 ug/L for a mixture of two shore crab species. This range is very similar tOthat observed with freshwater species, and fish and invertebrate species had similar sensitivities. Only one chronic test has been conducted with a saltwater species, Menidia Eeninsulae
--I-__ I and in thistest the acute chronic ratio was 1.162. The available data indicate that aquatic plants are more resistant to chlorine than fish and invertebrate species.
NATIONAL CRITERIA: The procedures described in the Guidelines for Deriving Numerical National Water Quality Criteria for the Protection of Aquatic Organisms and Their Uses indicate that, except possibly where a locally important species is very sensitive, freshwater aquatic organisms and their 

### uses should not be affectedunacceptably if the 4

-day average concentration of total residual chlorine does not exceed 11 ug/L more than once every 3 years on J-- the average and if the 1

-hour average concentration does not exceed 19 ug/L more than once every 3 years on the average. The procedures described in the Guidelines indicate that, except possibly where a locally important species is very sensitive, saltwater aquatic organisms and their 

### uses should not be affectedunacceptably if the 4

-day average concentration of chlorine

-produced oxidants does not exceed 7.5 ug/L more than
once every 3 years on the average and if the one-hour average concentration does not exceed 13 ug/L more than once every 3 years on the average. The recommended exceedence frequency of 3 years is the Agency's best scientificjudgment of the average amount of time 

## , it willtake an unstressed system torecover from a pollution event 

### inwhich exposure to chlorine exceeds the criterion. A stressed system, for example, one inwhich several outfalls occur in a limited area, would be expected torequire more time for recovery. The resilience of ecosystems and their ability to
recover differ greatly, however, and site

- specific criteria may be established if adequate justification is provided. The use of criteria in designing waste treatment facilities requires the selection of an appropriate wasteload a1 location model. Dynamic models are preferred for the application of these criteria. Limited data or other factors may make their use

# a impractical, in which case one should rely on a steady

- state model. The Agency recommends the interim use of 145 or lQlO for Criterion Maximum Concentration design flow and 745 or 7Q10 forthe Criterion Continuous Concentration design flow in steadystate models for unstressed and stressed systems, respectively. These matters are discussed 

### in more detail in the Technical Support Document for Water Quality-Based Toxics Control (U.S. EPA, 1985).

(50 F.R. 30784, July 29, 1985) SEE APPENDIX A FOR METHODOLOGYCHLORINATED PHENOLS Aquatic 

# - Life The available freshwater data for chlorinated phenols indicate that toxicity generally increases with increasing 

### chlorination, and that 

### acute toxicity occurs 

### at concentrations as low as 30 ug/L for 4

-chloro

-3

-methylphenol to greater than 500,000 ug/L for other compounds. Chronic toxicity occurs at concentrations as low as 970 ug/L for 2,4,6-trichlorophenol. Acute and chronic toxicity would occur 

### at lower concentrations among species that are more sensitive than those tested. The available saltwater data for chlorinatedphenols indicate that toxicity generally increases with increasing chlorination and that acute toxicity occurs at concentrationsas low as 440 ug/L 

### for 2,3,5,6-tetrachlorophenol and 29,700 ug/L for 4- chlorophenol. Acute toxicity would occur at lower concentrations among species that are more sensitive than those tested. No data
are available concerning the chronic toxicity of chlorinated phenols to sensitive saltwater aquatic life.
Human Health Sufficient data are 

### not available for 3

-chlorophenol to derive a level which would protect against the potential toxicity of this compound. Using available organoleptic data, to control undesirable taste and odor qualities of ambientwater, the estimated level is 0,1 ug/L. It should be recognized that organoleptic data have limitations as a basis for establishing a water quality criterion, and have no demonstrated 

# a

/relationship to potential adverse human health effects. Sufficient data are not available for 4

-chlorophenol to derive a level which would protect against the potential toxicity of this compound. Using available organoleptic data, to control undesirable taste and odor qualities 

### of ambient water the estimated level 

### is 0.1 ug/L. It should be recognized that organoleptic data have limitations as a basis for establishing a water quality criterion, and have no demonstrated relationship 

### to potential adverse human health effects. Sufficient data are not available for 2,3-dichlorophenol to derive a level which would protect against the potential toxicity of this compound. Using available organoleptic data, to control undesirable taste and odor qualities of ambient water the estimated level is 0.04 ug/L. It should be recognized that organoleptic data have limitations as a basis for establishing a water quality criterion, and have no demonstrated relationship to potential adverse human health effects. Sufficient data are not available for 2,5-dichlorophenol to derive a level which would protect against the potential toxicity of this compound. Using available organoleptic data, to control undesirable taste and odor qualities of ambient water the estimated level is 0.5 ug/L. It should be recognized that organoleptic data have limitations as a basis for establishing a water quality criterion, and have no demonstrated relationship to potential adverse human health effects. Sufficient data are not available for 2,6-dichlorophenol to derive a level which would protect against the potential toxicity of this compound. Using available organoleptic data, to controlundesirable taste and odor qualities of ambient water the estimated level is 0.2 ug/L. It should be recognized that organoleptic data have limitations as a basis for establishing a water quality criterion, and have no demonstrated relationship to potential adverse human health effects. Sufficient data are not available for 3,4-dichlorophenol to derive a level which would protect against the potential toxicity of this compound. Using available organoleptic data, to control undesirable taste and odor qualities of ambient water the estimated level is 0.3 ug/L. It should be recognized that organoleptic data have limitations as a basis 

### for establishing a water quality criterion, and have no demonstrated relationship to potential adverse human health ef'fects. For comparison purposes, 

### two approaches were used to derive criterion levels for 2,4,5-trichlorophenol. Based on available toxicity data, to protect public health the derived level 

### is 2.6 mg/L. Using available organoleptic data, to control undesirable taste and odor quality of ambient water the estimated level is 1.0 ug/L. It should be recognized that organoleptic data have limitations as a basis for establishing a water quality criterion, and have 

### no demonstrated relationship to potential adverse human health effects. For the maximum protection of human health from the potential carcinogenic effects of exposure to 2,4,6-trichlorophenoI through the ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentration should be zero, based on the nonthreshold assumption for thischemical. However, zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer risk over the lifetime are estimated at 10-5, 10-6, and 10-7. The corresponding recommended criteria are 12 ug/L, 1.2 ug/L, and 0.12 ug/L, respectively. If these estimates are made for consumption 

### of aquatic organisms only, excluding consumption 

### of water, the levels are 36 ug/L, 3.6 ug/L, and 0.36 ug/L, respectively. Using available organoleptic data, to control undesirable taste and odor qualities of ambient water the estimated level 

### is 2 ug/L. It should be recognized that organoleptic data have limitations
as a basis for establishing. 

### a water quality criterion, and have no demonstrated relationship to potential adverse human health effects. Sufficient data are not available for 2,3,4,6- tetrachlorophenol to derive a level which would protect against the potential toxicity of this compound. Using available organoleptic data, 

### to control undesirable taste and odor qualities of ambientwater the estimated level is 1.0 ug/L. It should be recognized that organoleptic data have limitations 

### as a basis for establishing a water quality criterion, and have demonstrated relationship to potential adverse human health effects. Sufficient data are not available for 2

-methyl

-4

-chlorophenol to derive a criterion level which would protect against any potential toxicity of this compound. Using available organoleptic data, to control undesirable taste and odor qualities of ambient water the estimated level is 1,800ug/L. Itshould be recognized that organoleptic data have limitations as a basis for establishing a water quality criterion and have no demonstrated relationship to potential adverse human health effects

# . Sufficientdata are not available for 3

-methyl

-4

-chlorophenol to derive 

### a criterion level which would protect against any potential toxicity of this compound. Using available organoleptic data, to control undesirable taste and odor qualities of ambient water the estimated level is 3,000 ug/L. It should be recognized that organoleptic data have limitations as a basis for establishing a water q u a l i t y c r i t e r i o n , and have no demonstrated relationship to potential adverse human health effects 

## , Sufficient data arenot available for 3

-methyl

-6

-chlorophenol to derive a criterion level which would protect against any potential toxicity of this compound. Using available organoleptic data, to control undesirable taste and odor qualities of ambient water the estimated level is 20 ug/L. It should be recognized that organoleptic data have limitations as a basis for establishing a water quality criterion, and have no demonstrated relationship to potential adverse human health effects

# .

(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYCRITERIA:



# a CHLOROALKYL ETHERS Aquatic 

# - Life
The available data for chloroalkyl ethers indicate that acute toxicity to freshwater aquatic life occurs at concentrations as low as 238,000ug/L and would occur at lower concentrations among species that are more sensitive than those tested. NO definitive data are chloroalkyl ethers to sensitive freshwater aquatic life. available concerning the chronic toxicity 

### of

No saltwater organism has been tested with any chloroalkyl ether and therefore, no statement can be made concerning acute or chronic toxicity.
Human Health
For the protection of human health from the toxic properties of bis(2-chloroisopropy1) ether ingested through water and contaminated aquatic organisms, the ambient water criterion is determined to be 34.7 ug/L. For the protection of human health from the toxic properties of bis(2-chloroisopropy1) ether ingested through contaminated aquatic organisms alone, the ambient water criterion is determined to be 4.36 mg/L. 

### For the maximum protection of human health from the potential carcinogenic effects of exposure to bis(chloromethy1) ether through ingestion 

### of contaminated water and contaminated aquatic organisms, the ambient water concentrations should be zero, based on the nonthreshold assumption for this chemical. However, zerolevel may 

### not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer risk
over the lifetime are estimated at 10-5, and The corresponding recommended criteria are 37.6 

### x ug/L, 3.76 

### x ug/L, and 0.376 

### x ug/L, respectively. If these estimates are made for consumption 

### of aquatic organisms only, excluding consumption 

### of water, the levels are 18.4 

### x ug/L, 1.84 

### x ug/L, and 0.184 x 10-3 ug/L, respectively.
For the maximum protection of human health from the potential carcinogenic effects of exposure 

### to bis(2-chloroethyl) ether through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentrations should be zero based
on the nonthreshold assumption for this chemical. However, zero level may not be attainable at thepresent time. Therefore, the levels which may result in incremental increase of cancer risk over the lifetime are estimated at and 10-7. The corresponding recommended criteria are 0.30 ug/L, 0.030 ug/L, and 0.003 ug/L, respectively. If these estimates are made for consumption of aquatic organisms only, excluding consumption of water, the levels are 13.6 ug/L, 1.36 ug/L, and 0.136 ug/L, respectively.
(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYCRITERIA: CHLOROFORM


### Aquatic 

### Life
The available data for chloroform indicate that acute toxicity to 

### freshwater aquatic life occurs at concentrations as low as 28,900 

### ug/L, and would occur at lower concentrations among species that are more sensitive than the three tested species Twenty

-seven-day LC50 

### values indicate that chronic toxicity occurs at concentrations as low as 1,240 

### ug/L, and could occur at lower concentrations among species or other life stages that are
more sensitive than the earliest life cycle stages of the rainbow trout. The data base for saltwater species is limited to one test and therefore, no statement can be made concerning acute or 1 

### chronic toxicity.

Human 

### Health
For the maximum protection of human health from the potential carcinogenic effects of exposure to chloroform through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentrations should be zero, based on the nonthreshold assumption for this chemical. However, zero level may not be attainable at thepresent time. Therefore, the levels which may result in incremental increase 

### of cancer risk over the lifetime are estimated at loe5, 

### The correspondingrecommended criteria are



### . 1.90 

### ug/L, 0.19 

### ug/L, and 0.019 

### ug/L, respectively. If these andestimates are made for consumption of aquatic organisms only, excluding consumption of water, the levels are 157 ug/L, 15.7 ug/L, and 1.57 ug/L, respectively.

(45 F.R. 79318, November 28, 1980) SEE APPENDIX 

### B FOR METHODOLOGYCHMROPHENOXY HERBICIDES 2,4-D; 2,4,5-TP CRITERIA:

2,4-D 100 ug/L for domestic water supply (health) 2,4,5-TP 10 ug/L for domestic water supply (health)
RATIONALE:
Two widely used herbicides are 2,4-D (2, 4- dichlorophenoxyacetic acid) and 2,4,5-TP (silvex) [2-(2’4, 5- trichlorophenoxy) propionic acid. Each of these compounds is formulated 

### in a variety of salts and esters that may have a marked difference in herbicidal properties, but all are hydrolyzed rapidly to the corresponding acid in the body. The subacute oral toxicity of chlorophenoxy herbicides has been investigated in a number of species of experimental animals (Palmer and Radeleff, 1964; Lehman, 1965). The dog was found to be sensitive and often displayed mildinjury in response to doses of 10 mg/kg/day for 90 days, and serious effects from a dose of 20 mg/kg/day for 90 days. Lehman (1965) reported that the noeffect level of 2,4-D is 0.5 mg/kg/day in the rat, and 8.0 mg/kg/day in the dog. Data are available on the toxicity of 2,4-D to man. A daily dosage of 500 mg (about 7 mg/kg) produced no apparent ill effects in a volunteer over a 21

-day period (Kraus, 1946). When 2,4-D
was investigated as a possible treatment €or disseminated coccidioidomycosis, the patient had no side effects from 18 intravenous doses during 33 days; each of the last 12 doses in 

# athe series was 800 mg (about 15 mg/kg) or more, the last being 2000 mg (about 37 mg/kg) (Seabury, 1963). A 19thand final dose of 3600 mg (67 mg/kg) produced mild symptoms. The long

-termno- effects levels (mg/kg/day) are listed for the rat and the dog. Those values are adjusted by a factor of 1/500 for 2,4-D and 2,4,5-TP. The safe levels are then readjusted to reflect total allowable intake per person. Since little 2,4-D or 2,4,5-TP is expected to occur in foods, 20 

### percent of the safe 

### exposure level can reasonably be allocated 

### to 

### water without jeopardizing the health of the 

### consumer.

(QUALITY CRITERIA FOR WATER, JULY 1976) PB

-263943 SEE APPENDIX C FOR METHODOLOGYCHROMIUM 

### rvI) AQUATIC

## LIFE SUMMARY: 

# 0

Acute toxicity values for chromium(V1) are available for freshwater animal species in 27 genera and range from 23.07 ug/L for 

### a cladoceran 

### to 1,870,000 ug/L for 

### a stonefly. These species include 

### a wide variety of animals that perform 

### a wide spectrum of ecological functions. All five tested species of daphnids are especially sensitive. The few data that are available indicate that the acute toxicity of chromium(V1) decreases as hardness and pH increase. The chronic value for both rainbow trout and brook 

### trout is 264.6 uq/L, which is much lower than the chronic value of 1,987 ug/L for the fathead minnow. The acute

-chronic ratios for these three fishes range from 18.55 to 260.8. In all three chronic tests a temporary reduction 

### in growth occurred at low concentrations. Six chronic tests with five species of daphnids gave chronic values 

### that range 

### from <2.5 

### to 40 ug/L and the acute

-chronic ratios range from 1.130 to >9.680. Except for the fathead minnow, all the chronic tests were conducted in soft water. Green algae are quite sensitive to chromium(V1). The bioconcentration factor obtained with rainbow trout is less than 3. Growth of chinook salmon was reduced at a measured concentration 

### of 16 ug/L. 

# 0

The acute toxicity of chromium (VI) to 23 saltwater vertebrate and invertebrate species ranges from 2,000 ug/L €or a polychaete
worm and a mysid to 105,000 ug/L for themud Snail. The chronic values 

### €or a polychaete range from <13 

### to 36.74 ug/L, whereasthat for a mysid is 132 ug/L. The acute

-chronic ratios range from 15.38 to >238.5. Toxicity to macroalgae was reported at 1,000 and 5,000 ug/L. Bioconcentration factors for chromium(V1) range from 125 to 236 for bivalve molluscs and polychaetes.
CHROMIUM 1111) Acute values for chromium(II1) are available for 20 freshwater animal species in la genera ranging from 2,221 ug/L for a mayfly to 71,060 ug/L for caddisfly. Hardness has a significant influence on toxicity, with chromium(II1) being more toxic in soft water. A life

-cycle test with 

## __ Daphnia 

## ____ maqna 

## __ __ in soft water gave a chronicvalue of 66 ug/L. Ina comparable test inhard water the lowest test concentration of 44 ug/L inhibited reproduction of



## - Dap&nia 

## - -- mgE,but this effect may have resulted from ingested precipitated chromium. In a life

-cycle test with the fathead minnow in hard water the chronic value was 1,025 ug/L. Toxicity data are available for only two freshwater plant species. A concentration of 9,900 ug/L inhibited growth of roots of Eurasian watermilfoil. A freshwater green alga was affected by a concentration of 397 ug/L in soft water. No bioconcentration factor has been measured for chromium(II1) with freshwater organisms. Only two acute values are available for chromium (111) in saltwater 10,300 ug/L for the eastern oyster and 31,500 ug/L for the mummichog. In a chronic test effects were not observed on a polychaete worm at 50,400 ug/L at pH = 7.9, but acute lethality occurred when pH = 4.5. Bioconcentration factors for saltwaterorganisms and chromium(II1) range from 86 to 153, similar to the bioconcentration factors for chromium(V1) and saltwater species.
NATIONAL CRITERIA: CHROMIUM(VI) The procedures described in the Guidelines for Deriving Numerical National Water Quality Criteria for the Protection of Aquatic Organisms and Their Uses indicate that, except possibly where a locally important species is very sensitive, freshwater aquatic organisms and their uses should not be affected unacceptably if the 4

-day average concentration of chromium(V1) does not exceed 11 ug/L more than once every 3 years on the average and if the 1

-hour avera e concentration does not exceed 

## 7 16 ug/L more than once every 3 years 

### on the average. The procedures described in the Guidelines indicate that, except possibly where a locally important species is very sensitive, saltwater aquatic organisms, and their uses should not be affected unacceptably if the 4

-day average concentration of chromium(V1) does not exceed 50 ug/L more than once every 3 years
on the average and if the 1

-hour average concentration does not exceed 1,100 ug/L more than once every 3 years on the average. Data suggest that the acute toxicity of chromium (VI) is salinity dependent; therefore, the 1

-hour average concentration might be underprotective at low salinities. CHROMIUM(1111 The procedures described in the Guidelines indicate that,

.I except possibly where a locally important species is very sensitive, freshwater aquatic organisms and their uses should notbe affected unacceptably if the 4

-day average concentration (in ug/L) of chromium(II1) does not exceed the numerical value given by e(0.8190[ln(hardness)]+l.561) more than once every 3 years on the average and if the 1

-hour average concentration (inug/L) does not exceed the numerical value given by (0.8190[ln(hardness) ]+3.688) more than once every 3 years on the e average. For example, at hardnesses of 50, 100, and 200 mg/L as CaC03 the &day average concentrations of chromium(II1) are 120, 210, and 370 ug/L, respectively, and the 1

-hour average concentrations are 980, 1,700, and 3,100 ug/L. No saltwater criterion can be derived for chromium(III), but 10,300 ug/L is the EC50 for eastern oyster embryos, whereas 50,400 ug/L did test. EPA believes provide a more not affect a polychaete worm in a life

-cycle 

# a that a measurement such as 18acid-soluble1' would scientifically correct basis upon which to establish criteria for minerals. The criteria were developed on this basis. However, at this time,no EPA

-approved methods for such a measurement are available to implement the criteria through the regulatory programs of the Agency and the States. The Agency is considering development and approval of methods for a measurement such as acid

-soluble. Until available, however, EPA recommends applying the criteria using the total recoverable method. This has two impacts: (1) certain species of some metals recoverable cannot be analyzed directly method does not distinguish because the total 

# a between individualoxidation states, and (2) these criteria may



# 0 when based on the total recoverablemethod. The recommended exceedence frequency be overly protective

of 3 years is the 'Agency'sbest scientific judgment of the average amount of time



### it will take an unstressed system to recover from a pollution event in which exposure to chromium exceeds the criterion. A stressed system, for example, one in which several outfalls occur in a limited area, would be expected or require more time for recovery. The resilience of ecosystems and their ability to
recover differ greatly, however, and site

-specific criteria may be established if adequate justification is providedThe use of criteria in designing waste treatment facilities requires the selection of an appropriate wasteload a1location model. Dynamic models are preferred for the application of these criteria. Limited data or other factors may make their use impractical, 

### in which case one should rely on a steady

-state model. The Agency recommends the interim use of 1Q5 or lQlO for Criterion Maximum Concentration design flow and 745 or 7410 or the Criterion Continuous Concentration design flow in steadystate models for unstressed and stressed systems, respectively. These matters are discussed 

### in more detail in the Technical Support Document for water Quality

-Based Toxics Control (U.S. 

### EPA, 1985). HUMAN HEALTH CRITERIA: 

# 0

For the protection of human health of Chromium I11 ingested through water 

# 0 from the toxic properties and contaminated aquaticorganisms, the ambient water criterion is determined to be 170 mg/LJ.
For the protection of human health from the toxic properties of Chromium I11 ingested through contaminated aquatic organisms alone, the ambient water criterion is determined to be 3433 mg/L. The ambient water quality criterion for total Chromium VI is recommended to be identical to the existing drinking water standard which is 50 ug/L. Analysis of the toxic effects data resulted 

### in a calculated level which is protective of human health against the ingestion of contaminated water and contaminated aquatic organisms. The calculated value is comparable to the present standard. For this reason a selective criterion based on exposure solely from consumption of 6.5 grams of aquatic organisms was not derived.

(45 F.R. 79318 Nov. 28,1980) (50 F.R. 30784, July 29, 1985) SEE APPENDIX A FOR 

### METHODOLOGY2-CHLOROPHENOL
Aquatic Life
The available data for 2

-chlorophenol indicate that acute toxicity to freshwater aquatic life occurs at concentrations as low as 4,380 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No definitive data are available concerning the chronic toxicity of 2- chlorophenol to sensitive freshwater aquatic life,but flavor impairment occurs in one species of fish at concentrations as low
as 2,000 ug/L. No saltwater organisms have been tested with 2- I chlorophenol and therefore, no statement can be made concerning acute or chronic toxicity. Human Health Sufficient data are not available for 2

-chlorophenol to derive a level which would protect against the potential toxicity of this compound. Using avai1able organoleptic data, to control undesirable taste and odor qualities of ambient water the estimated level is 0.1 ug/L. 

### It should be recognized that organoleptic data have limitations as a basis for establishing a water quality criterion, and have no demonstrated relationship to potential adverse human health effects.

(45 F.R. 79318, November 28, 1980) SEE APPENDIX 

### B FOR METHODOLOGYCOLOR

Waters shall be virtually free from substances producing objectionable color for aesthetic purposes; the source of supply should not exceed 75 color units on the platinum

-cobalt scale for domestic water supplies; and
not reduce the depth of the compensation point for photosynthetic activity by more than 10 percent from the seasonally established norm for aquatic life. increased color (in combination with turbidity) should

INTRODUCTION:
Color in 

### water principally results from degradation processes 

### in the natural environment. Although colloidal forms of iron and manganese occasionally are the cause of color in water, the most
common causes are complex organic compounds originating from the decomposition of naturally occurring organic matter (AWWA, 1971). Sources of organic material include human materials from the soil such as tannins, human acid and humates: decaying plankton: and other decaying aquatic plants. Industrial discharges may contribute similar compounds: for example, those from the pulp and paper and tanning industries. Other industrial discharges may contain brightly colored substances such as those from certain processes in textile and chemical industries. Surface waters may appear colored because of suspended matter which comprises turbidity. Such color is referred to as apparent color and is differentiated from true color caused by colloidal human materials (Sawyer, 1960). Natural color 

### is reported in

,color 9mits" which generally are determined by use of the platinum

-cobalt method (Standard Methods, 1971). There is no general agreement as to the chemical composition of natural color, and in fact the composition may vary chemically from place to place (AWWA, 1971). Black and Christman (1963a) characterized color

-causing colloids examined as aromatic, polyhydroxy, methoxy carboxylic acids. Shapiro (1964) characterized color

-causing constituents as being dialyzable and composed of aliphatic, polyhydroxyl carboxylic acids with molecular weights varying from less than 200 to approximately 400. The colloidal fraction of color exists in the 3.5 to 10 mu diameter range (Black and Christman, 1963b). These same authors summarized other characteristics of color observed in laboratory studies of natural waters: color is caused by light scattering and fluorescence rather than absorption of light energy, and pH affects both particle size of the color

-causing colloids and the intensity of color itself.
RATIONALE: Color in water is an important constituent in terms of aesthetic considerations. To be aesthetically pleasing, water should be virtually free from substances introduced by man's activitieswhich produce objectionable color. "Objectionable color18is defined to be a significant increase over natural background levels. Non

-natural colors such as dyes should not be perceptible by the human eye as such colors are especially objectionable to those who receive pleasure by viewing water in its natural state. Because of the extreme variations in thenatural background amount of color, it 

### is meaningless to attempt numerical limits. The aesthetic attributes of water depend on one’s appreciation of the water setting. 

# 0

The effects of col’or on public water supplies also are principally aesthetic. The 1962 Drinking Water Standards (PHS, 1962) recommended that color in finished waters should not exceed 15 units on the platinum

-cobalt scale. Water consistently can be treated using standard coagulation, sedimentation and filtration processes to reduce color to substantially less than 15 color units when the source water does not exceed 75 color units AWWA, 1971; NAS, 1974). The effects of color inwater on aquatic life principally are to reduce light penetration and thereby generally reduce photosynthesis by phytoplankton and to restrict the zone for aquatic vascular plant growth. 

# a

The light supply necessary to support plant life is dependent
on both intensity and effectivewave lengths (Welch,1952). In general, the rate of photosynthesis increases with the intensity of the incident light. Photosynthetic rates are most affected in the red region and least affected in the blue

-violet region of incident light (Welch, 1952). It has been found that in colored waters the red spectrum is not a region of high absorption so that the effective penetration, and therefore the intensity for photosynthesis, is not as restricted as are other wave lengths. It should be emphasized that transmission of all parts of the spectrum is affected by color, but the greatest effect is on the 

# 0 standard 

### or blue end of the spectrum (Birge and Juday, 1930). InTABLE 2. Maximum color of surface waters that have been used as sources for industrial water supplies. Industry

## or Industrial 

### Use Color units Boiler make up 1,200 cooling water 1,200 Pulp and paper Chemical and allied products Petroleum 360 500

25highly colored waters (45 to 132 color units) Birge and Juday (1930) measured the light transmission as a percentage of the incident level and found very little blue, 50 percent or less yellow, and 100 to 120 percent red. 

# 0

The light intensity required for some aquatic vascular plants to photosynthetically balance the oxygen used in respiration may be 5 percent of full sunlight during maximum
summer illuminationperiods (NTAC,1968). Asmuch as 10 percent of the incident light may be required for plankton to likewise photosynthetically produce sufficient oxygen to balance their respiration requirements (NTAC, 1968). The depth at which such a compensation point 

### is reached, calledthe compensation depth, delineates the zone of effe,ctive photosynthetic oxygen production. To maintain satisfactory biological conditions, this depth cannot be substantially reduced. 

# 0
Industrial requirements as related to water color have been standardized (NAS,1974). Table 2 lists themaximum value used


### as a source of water for various industries and industrial uses. Through treatment, such waters can be made to meet almost any industrial requirement.

(QUALITY CRITERIA FOR WATER, JULY 1976) PB

-263943 SEE APPENDIX C FOR METHODOLOGY

# 0 AQUATIC 

### LIFE SUMMARY: *COPPER

Acute toxicity data freshwater animals. At are available for species in 41 genera of


### a hardness of 50 mg/L the genera range in sensitivity from 16.74 ug/L for Ptychocheilus 

## - to 10,240 ug/L for Acroneuria. Data for eight species indicate that acute toxicity decreases as hardness increases. Additional data for several species indicate that toxicity also decreases 

### with increases 

### in alkalinity and total organic carbon. Chronic values are available €or 15 freshwater species and range from 3.873 ug/L €orbrook trout to 60.36 ug/+ for northern pike. Fish and invertebrate species seem to be about equally sensitive to the chronic toxicity of copper. Toxicity tests have been conducted on copper with a wide range of freshwater plants and the sensitivities are similar to those of animals. Complexing effects of the test media and a lack of good analytical data make interpretation and application of these results difficult. Protection 

### of animal species, however, appears to offer adequate protection of plants. Copper does not appear to bioconcentrate very much in the edible portion of freshwater aquatic species. The acute sensitivities of saltwater animals to copper range from 5.8 ug/L for the blue mussel to 600 ug/L for the green crab. A chronic life

-cycle test has been conducted with a mysid, and adverse effects were observed at 77 ug/L but not at 38 ug/L, which resulted in an acute

-chronic ratio of 3.346. Several *Indicates susDended. canceled or restricted bv U.S.EPA Office of Pesticides ahd Toxic Substances 

# -saltwater algal species have been tested, and effects were observed between 5 and 100 ug/L. Oysters can bioaccumulate copper up to 28,200 times, and become bluish

-green, apparently without significant mortality. In long

-term exposures, the bay scallop was killed at 5 ug/L.
NATIONAL CRITERIA: The procedures described in the Guidelines for Deriving Numerical National Water Quality Criteria for the Protection of Aquatic Organisms and Uses indicate that, except possibly where a locally important species 

### is very sensitive, freshwater aquatic organisms and their uses should not be affected unacceptably if the 4

-day average concentration (in ug/L) of copper does not exceed the numerical value given, by .(0.8545[ ln(hardness)

### 3

-1.465) more than once every 3 years on the average and if the 1

-hour average concentration (in ug/L) does not exceed the numerical value given by ,(0.9422 [ln(hardness)1-1.464) more than once every 3 years on the average. For example, at hardnesses of 50, 100, and 200 mg/L as CaC03 the 4

-day average concentrations of copper
are 6.5, 12, and 21 ug/L, respectively, and the 1

-hour average concentrations are 9.2, 18, and 34 ug/L. The procedures described in the Guidelines indicate that, except possibly where a locally important species is very sensitive, saltwater aquatic organisms and their uses should not be affected unacceptably if the 1

-hour average concentration 

### of copper does not exceed 2.9 ug/L more than once every 3 years on the average. EPA believes that a measurement such as tsacid-solublets wouldprovide a more scientifically correct basis upon which to establish criteria formetals. The criteriawere developed on this

### basis. However, atthistime, no EPA approved methods for such a measurement are available to implement the criteria through the regulatory programs of the Agency and the States. The Agency is considering development and approval of methods for a measurement such as acid

- soluble. Until available, however, EPA recommends applying the criteria using the total recoverable method. This has two impacts: (1)certain species of
some metals cannot be analyzed directly because the total recoverable method does not distinguish between individual oxidation states, and (2) these criteria may be overly protective when based on the total recoverable method. The recommended exceedence frequency of 3 years is the Agency's best scientificjudgment of theaverage amount of time it 

### will take an unstressed system to recover from a pollution event in which exposure to copper exceeds the criterion. A stressed system, for example, one inwhich several outfalls occur in a limited area, would be expected torequire more time for recovery. The resilience of ecosystems and their ability to
recover differ greatly, however, and site

- specific criteria may be established if adequate justification is provided. The use of criteria in developing waste treatment facilities requires the selection of an appropriate wasteload allocation model. Dynamic models are preferred for the application of these criteria. Limited data or other factors may make their use impractical, in which case one should rely on a steady

- state model. The Agency recommends the interim use of 1Q5or lQlO for 

# 0Criterion Maximum Concentration design flow and 745 or 7410 for the Criterion Continuous Concentration (CCC) design flow in steady

-state models for unstressed and stressed systems respectively. These matters are discussed in more detail in the Technical Support Document for Water Quality

-Based Toxics Control (U.S. EPA, 1985). HUMAN HEALTH CRITERIA: Sufficient data is not available for copper to derive a level which would protect against the potential toxicity of this compound. Using available organoleptic data, for controlling undesirable taste and odor quality of ambient water, the estimated level is 1 mg/L. It should be recognized that organoleptic data as a basis for establishing a water quality criteria have 1imitations and have no demonstrated relationship to potential adverse human health effects. I

(45 F.R. 79318 Nov. 28,1980) (50 F.R. 30784, July 29, 1985) SEE APPENDIX A FOR METHODOLOGYCYANIDE AQUATIC 

# - LIFE SUMMARY: Data on the acute toxicity of free cyanide (the 

### sum of cyanide present as HCN and CN

-, expressed as CN) are available for a wide variety of freshwater species that are involved in diverse community functions. The acute sensitivities ranged from 44.73 ug/L to 2,490 ug/L, but all of the species with acute sensitivitiesabove 400 ug/L were invertebrates. A long

-term survival, and 

### a partial and life

- cycle test with fish gave chronic values of 13.57, 7.849, and 16.39 ug/L, respectively. Chronic values for two freshwater invertebrate species were 18.33 and 34.06 ug/L. Freshwater plants were affected at cyanide concentrations ranging from 30 ug/L to 26,000 ug/L. The acute toxicity of free cyanide to saltwater species ranged from 4.893 ug/L to>10,000ug/L and invertebrateswereboth the most and least sensitive species. Long

-term survival 

### in an early life

- stage test with the sheepshead minnow gave a chronic value of 36.12 ug/L. Long

-term survival in a mysid life

- cycletest resulted 

### in a chronic value of 69.71 ug/L. Testswith thered macroalga, Champia parvula --I showed cyanide toxicity at 11 to 25 ug/L, but other species were affected at concentrations up to 3,000 ug/L. NATIONAL CRITERIA: The procedures described in the Guidelines for Deriving Numerical National Water Quality Criteria for the Protection of Aquatic Organisms and Their Uses indicate that, except possibly where 

### a locally important species is very sensitive, freshwater aquatic organisms and their uses should not be affectedunacceptably if the 4

-day average concentration of cyanide does not exceed 5.2 ug/L more than once every 3 years on the average and if the 1

-hour average concentration does not exceed 22 ug/L
more than once every 3 years on the average. The procedures described in the Guidelines indicate that, except possibly where a locally important species 

### is very sensitive, saltwater aquatic organisms and their uses should not be affected unacceptably if the 1

-hour average concentration of cyanide does not exceed 1.0 ug/L more than once every 3 years on the average. EPA believes that a measurement such as "acid soluble" would provide a more scientifically correct basis upon which to establish criteria for cyanide. The criteria were developed on this basis. However,at this time,no EPA

-approvedmethods for such a measurement are available to implement the criteria through the regulatory programs of the Agency and the States. The Agency is considering development and approval of methods for a measurement such as acid soluble. Until available, however, EPA recommends applying the criteria using the total recoverablemethod. These criteria may be overly protective when based on the total recoverablemethod. The recommended exceedence frequency of 3 years is the Agency's best scientific judgment of the average amount of time it will take 

### an unstressed system to recover from a pollution event in which exposure to cyanide exceeds the criterion. A stressed system, for example, one in which several outfalls occur in a limited area, would be expected to require more time for recovery. The resilience of ecosystems and their ability torecover differ greatly, however, and site

-specific criteria may be established if adequate justification is provided. The use of criteria in designing waste treatment facilities requires the selection of an appropriate wasteload a1location model. Dynamic models are preferred for the application of these criteria. Limited data or other factors may make their use impractical, in which case one should rely on a steady

-state model. The Agency recommends the interim use of 1Q5 or lQlO for Criterion Maximum Concentration design flow and 745 or 7410 for the Criterion Continuous Concentration design flow in steady

### state models for unstressed and stressed systems respectively. These matters are discussed in more detail in the Technical Support Document for Water Quality

-Based Toxics Control (U.S. EPA, 1985). H" HEALTH CRITERIA The ambient water quality criterion for cyanide is recommended to be identical to the existing drinking water standard which is 200 ug/L. Analysis of the toxic effects data resulted in a calculated level which is protective of human health against the ingestion of contaminated water and contaminated aquatic organisms. The calculated value is comparable to the present standard. For this reason 

### a selective criterion based on exposure solely from consumption of 6.5 grams of aquatic organisms was not derived. NOTE: The U.S. EPA is currently developing Acceptable Daily Intake (ADI) or Verified Reference Dose (RfD)values for Agency

-wide use for this chemical. The new value should be substitutedwhen it becomes available. The January, 1986, draft Verified Reference Dose document cites an RfD of .02 mg/kg/day for free cyanide. -, 

# 0CRITERIA:
DDT

_. 

# - - DDT AND METABOLITES
Aquatic 

## Life

For DDT and its metabolites the criterion to protect freshwater aquatic life as derived using the Guidelines is 0.0010 ug/L as a 24

-hour average and the concentration should not exceed 1.1 ug/L at any time. For DDT and its metabolites the criterion to protect' saltwater aquatic life as derived using the Guidelines is 0.0010 ug/L as a 24

-hour average and the concentration should not exceed 0.13 ug/L 

### at any time. TDE 

## -The available data for TDE indicate that acute toxicity to freswater aquatic life occurs at concentrations as low as 0.6 ug/L and would occur at lower concentrations among species that
are more sensitive than those tested. No data are available concerning the chronic toxicity of TDE to sensitive freshwater aquatic life. The available data for TDE indicate that acute toxicity to saltwater aquatic life occurs at concentrations as low 

### as 3.6 ug/L and would occur at lower concentrations among species that
are more sensitive than those tested. No data are available concerning the chronic toxicity of TDE to sensitive saltwater aquatic life. DDE 

## -The available data for DDE indicate that acute toxicity './ to freshwater aquatic life occurs at concentrations as low as1,050 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No data are available concerning the chronic toxicity of DDE to sensitive freshwater aquatic life. The available data for DDE indicate that acute toxicity to saltwater aquatic life occurs in concentrations as low as 14 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No data are available concerning the chronic toxicity of DDE to sensitive saltwater aquatic life. Human Health For the maximum protection of human health from the potential carcinogenic effects of exposure to DDT through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentration should be zero, based on the nonthreshold assumption for this chemical. However, zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer 

### risk
over the lifetime are estimated at and The corresponding recommended criteria are 0.24 nq/L, 0.024 ng/L, and 0.0024 ng/L, respectively. If these estimates are made for consumption of aquatic organisms only, excluding consumption of water, the levels are 0.24 ng/L, 0.024 ng/L, and 0.0024 ng/L, respectively.

(45F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGY

# a CRITERION: DEMETON

0.1 ug/L for freshwater and marine aquatic life RATIONALE: Static LC50 bioassays yielded toxicity values for the organophosphorus pesticide demeton for carp, goldfish, fathead minnow, channel catfish, guppy, rainbow, trout and bluegill, ranging from 70 ug/L to 15,000 ug/L (Hendersonand Pickering, 1958; Ludemann and Neumann, 1982; Macek and McAllister, 1970; McCann and Jasper, 1972; Pickering et al. 1962). Results of these tests demonstrate


### an apparent sharp division 

### in species sensitivity, with bluegill (Lepomis macrochirusr, rainbow 

### trout (Salmo gairdneri) and guppy, (Poecilia 

# --- --------- reticulatg,' being susceptible to lower concentrations while the remaining species were comparatively resistant. In the 96-hOUr exposures toxicity did not increase significantly with time, indicating that concentrations close to nominal may not have been maintained for more than a few hours, Bluegills with a 24-hour LC50 of 70 ug/L were the most sensitive fish (Mccann and Jasper, 1972). When fish were exposed to acutely toxic levels of demeton €or 12 hours by Weiss (1959, 1961) themaximum inhibition of brain acetiylcholinesterase (AChE) was not reached. The lowest levels of AChE occurred after 24 to 48 hOUrS. It was demonstrated that maximum inhibition could last as long as two weeks after exposure, and subsequent recovery to levels approaching normal took many more weeks. Weiss (1958) reported a significant increase 

### in mortality of fathead minnows exposed for a secondtime to the organophosphate, Sarin, before the fish had recovered normal brain AChE levels. The resistance of fully recovered fish was equal to that of previously unexposed controls. Weiss and Gakstatter (1964a)reported no significant inhibition of brain AChE in bluegills, goldfish and shiners (Notemigonus



## __ crysoleucasl, 

## __-

### ----- following 15

-day exposures to demeton at continuously replenished, nominal concentrations of 1 ug/L. Acute toxicity values reported for invertebrates range from 10 to 100,000ug/L (Ludemann and Neumann, 1962; Sanders,1972). In general,molluscs and tubifex worms were very resistant while the smaller crustaceans and insect larvae were susceptible. Ludemann and Neumann (1962) reported that Chironomus plumosus larvae were the most sensitive species they tested. A 24

-hour exposure at 10 ug/L produced undefined effects while 100 percent
were killed at 1000 ug/L. Calculated LC50 data for invertebrates apparently are limited to a single, nominal concentration static exposure of Gammarus


### ______ fasciatus (Sanders,1972). These 24- and 96

-hourLC50valuesarereportedas 500and27ug/L, indicatinga time

-related effect not observed in the bioassays with fishes. As only a fewofthesensitivespecieshavebeentestedandgreat variance in response can result with different test methods, caution must be exercised in estimating the sub

-acute concentration for aquatic fauna in general. It appears that no study has been made of possible residual effects other than AChE inhibition, which might result from short exposures to subacute concentrations of organophosphates. There are few data on the toxicity of demeton to marine organisms. Butler (1964) reported a 48

-hour EC50 of 63 ug/L forthe pink shrimp, Peneaus duorarum, and a 24

-hour LC50 of 550 ug/L for the spot, Leiostomus xanthurus. Chronic demeton toxicity data for freshwater organism are not currently available. Since no data are available at this time to indicate long

-term no-effect levels for aquatic organisms, 

### a criterion must be derived based partly on the fact that all organophosphates inhibit the production of the AChE enzyme. Demeton 

### is unique, however, in that the persistence of its AChEinhibiting ability is greater than that of 10 other common organophosphates, even though its acute toxicity is apparently 

### less. The effective "half-life" of AChE inhibition for demeton 

### is greater than one year (Weiss and Gakstatter, 1964b). Because such inhibition may be additive with repeated exposures and may be compounded by any of the organophosphates, it is recommended that a criterion for demeton be based primarily on its enzymeinhibiting potential. A criterion of 0.1 ug/L demeton for freshwater and marine aquatic life 

### is recommended since it will not be expected to significantly inhibit AChE over a prolonged period of time. In addition, the criteria recommendation is in close agreement with the criteria for the other organophosphates.

(QUALITY CRITERIA FOR WATER, JULY 1976) PB

-263943 SEE APPENDIX C FOR METHODOLOGYDICHLOROBENZENES
Aquatic 

# - Life The available data for dichlorobenzenes indicate that acute and chronic toxicity to freshwater aquatic life occur at concentrations as low as 1,120 and 763 ug/L, respectively, and would occur at lower concentrations among species that are more sensitive than those tested. The available data for dichlorobenzenes indicate that acute toxicity to saltwater aquatic life occurs at concentrationsas low as 1,970 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. 

### No data are available concerning the chronic'toxicity of dichlorobenzenes to sensitive saltwater aquatic life. 

# 0

Human Health For the protection of human health from the toxic properties of dichlorobenzene ingested through water and contaminated aquatic organisms, the ambient water criterion is determined to be 400 ug/L. For the protection of human health from the toxic properties of dichlorobenzenes ingested through contaminated aquatic organisms alone, the ambient water criterion is determined to be 2.6 mg/L. (45 F.R. 79318, November 28, 1980) SEE APPENDIX B.FOR METHODOLOGY 

# 0

.,DICHLOROBENZIDINE CRITERIA: Aquatic 

### Life The data base available for dichlorobenzidines and freshwater organisms is limited to one test on bioconcentration of 3,3- dichlorobenzidine, and therefore, no statement can be made concerning acute or chronic toxicity. No saltwater organisms have been tested with any dichlorobenzidine, and therefore, 

### no statement can be made concerning acute or chronic toxicity.
Human Health For the maximum protection of human health from the potential carcinogenic effects of exposure to dichlorobenzidine through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentrations should be zero, based
on the nonthreshold assumption for this chemical. However, zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer risk
over the lifetime are estimated at and lo-'. The corresponding recommended criteria are 0.103 ug/L, 0.010 ug/L, and 0.001 ug/L, respectively. If these estimates are made for consumption'of aquatic organisms only, excluding consumption of water, the levels are 0.204 ug/L, 0.020 ug/L, and 0.002 ug/L, respectively. 

# 0

(45 F.R. 79318, November 28, 1980) _.* SEE APPENDIX B FOR METHODOLOGYDICHLOROETHYLENES
Aquatic Life The available data for dichloroethylenes indicate that acute toxicity 

### to freshwater aquatic life occurs at concentrations 

### as low as 11,600 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No definitive data are available concerning 

### the chronic toxicity 

### of dichloroethylenes to sensitive freshwater aquatic life. The available data for dichloroethylenes indicate that acute and chronic toxicity to saltwater aquatic life occurs at concentrations as low as 224,000 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No data are available concerning the chronic toxicity 

### of dichloroethylenes to sensitive saltwater aquatic life.
Human Health 1,1

-Dichloroethylene 

### For the maximum protection of human health from the potential carcinogenic effects of exposure to 1,l dichloroethylene through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentrations should be zero, based on the non threshold assumption for 

### this chemical. However, zero level may not be attainable at the present time. Therefore, the levelswhich may result in incremental increase 

### of
cancer risk over the lifetime are estimated at 10-5e 10- 

# 0

.- 6, and The corresponding recommended criteria are 0.33 ug/L, 0.033 ug/L, and 0.003 ug/L, respectively. Ifthese estimates are made for consumption of aquatic organisms only,excluding consumption of water, the levels are 18.5 ug/L, 1.85 ug/L, and 0.185 ug/L, respectively. 1,2-Dichloroethylene Using the present guidelines, a satisfactory criterion cannot be derived at this tine because of insufficient available data for 1,2-dichloroethylene.

(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGY2,4-DICHLOROPHENOL CRITERIA: Aquatic Life
The available data for 2,4-dichlorophenol indicate that acute and chronic toxicity to freshwater aquatic life occurs at concentrations as low as 2,020 and 365 ug/L, respectively, and would occur at lower concentrations among species that are more sensitive than those tested. Mortality to early life stages of one species of fish occurs 

### at concentrations as low as 70 ug/L. Only one test has 

### been conducted with saltwater organisms and 2,4-dichlorophenol and therefore, no statement can be made concerning acute or chronic toxicity.
Human Health For comparison purposes, two approaches were used to derive criterion levels for 2,4-dichlorophenol. Based on available toxicity data, to protect public health the derived level is 3.09 mg/L. Using available organoleptic data, to control undesirable taste and odor qualities of ambient water the estimated level is 0.3 ug/L. It should be recognized that organoleptic data have limitations as a basis for establishing a water quality criterion, and have no demonstrated relationship to potential adverse human health effects.

(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYDICHLOROPROPANES/DICHLOROPROPROPENES CRITERIA: Aquatic 

## Life The available data for dichloropropanes indicate that acute and chronic toxicity to freshwater aquatic life occurs at concentrations as low as 23,000 and 5,700ug/L, respectively, and would occur at lower concentrations among species that are more sensitive than those tested. The available data for dichloropropene indicate that acute and chronic toxicity to freshwater aquatic life occurs 

### at concentrations as low as 6,060 and 244 ug/L, respeptively, and would occur at lower concentrations among species that are more sensitive than those tested.
The available data for dichloropropane indicate that acute and chronic toxicity to saltwater aquatic life occur at concentrations as low as 10,300 and 3,040 ug/L, respectively, and would occur at lower concentrations among species that are more sensitive than those tested. The available data for dichloropropene indicate that acute toxicity to saltwater aquatic life occurs at concentrationsas low as 790 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No data
are available concerning the chronic toxicity of dichloropropene to sensitive saltwater aquatic life.Human Health Using the present guidelines, a satisfactory criterion cannot be derived at this time because of insufficient available data for dichloropropanes.

(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYAquatic Life The available data for 2,4-dimethylphenol indicate that acute toxicity to freshwater aquatic life occurs at concentrations as low as 2,120 ug/L and would occur at lower concentrations among species that are more sensitivethan those tested. No data are available concerning the chronic toxicity of dimethylphenol to sensitive freshwater aquatic life. No saltwater organisms have been tested with 2,4- dimethyl

-phenol and therefore, no statement can be made concerning acute or chronic toxicity. Human Health Sufficient data are not available for 2,4-dimethylphenol to derive a level which would protect against the potential toxicity of this compound. Using available organoleptic data, to control undesirable taste and odor quality of ambient water the estimated level is 400 ug/L. It should be recognized that organoleptic data have limitations as a basis for establishing a water quality criterion, and have no demonstrated relationship to potential adverse human health effects.

(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYCRITERIA: DINITROTOLUENE
Aquatic Life The available data for dinitrotoluenes indicate that acute and chronic toxicity to freshwater aquatic life occurs at concentrations as low as 330 and 230 ug/L, respectively, and would occur at lower concentrations among species that are more sensitive than those tested. The available data for dinitrotoluenes indicate that acute toxicity to saltwater aquatic life occurs at concentrations as low as 590 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. 

### No data are available concerning the chronic toxicity of dinitrotoluenes to sensitive saltwater aquatic life but a decrease in algal cell numbers occurs at concentrations as low as 370 ug/L.
Human Health 

### For the maximum protection of human health from the potential carcinogenic effects of exposure to 2,4-dinitrotoluenethrough ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentration should be zero, based
on the nonthreshold assumption for this chemical. However,
zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer risk over the lifetime are estimated at and The corresponding recommended criteria are 1.1 ug/L, 0.11 ug/L, and 0.011 ug/L, respectively. If these estimates are made for consumption of aquatic organ

-isms only, excluding consumptionof water, 

### the levels are 91 ug/L, 9.1 ug/L, and 0.91 ug/L, respectively.

(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYDIPHENYLHYDRAZINE
Aquatic Life The available data for 1,2-diphenylhydrazine indicate that acute toxicity to freshwater aquatic life occurs at concentrations as low as 270 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No data are available concerning the chronic toxicity of 1,2-diphenylhydrazine to sensitive freshwater aquatic life. NO saltwater organisms have been tested with 1,2- diphenylhydrazine and therefore, no statement .can be made concerning acute or chronic toxicity. Human Health For the maximum protection of human health from the potential carcinogenic effects of exposure to diphenylhydrazine through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentrations shopld be zero, based
on the nonthreshold assumption for this chemical. However, zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer risk
over the lifetime are estimated at and The corresponding recommended criteria are 422 ng/L, 42 ng/L, and 4 ng/L, respectively. If these estimates are made for consumption of aquatic organisms only, excluding consumption of water, the levels are 5.6 ug/L, 0.56 ug/L, and 0.056 ug/L, 

# 0

respectively. 

# 0
(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYENDOSULFAN
Aquatic Life For endosulfan the criterion to protect freshwater aquatic life as derived using the Guidelines is 0.056 ug/L as a 24

-hour average and the concentration should not exceed 0.22 ug/L at any time. For endosulfan the criterion to protect saltwater aquatic life as derived using the Guidelines is 0.0087 ug/L as a 24

-hour average and the concentration should not exceed 0.034 ug/L 

### at any time. Human Health For the protection of human 'healthfrom the toxic properties of endosulfan ingested through water and contaminated aquatic organisms, the ambient water criterion is determined to be 74 ug/L. For the protection 

### of human health from the toxic properties 

### of endosulfan ingested through contaminated aquatic organisms alone, the ambient water criterion is determined to be 159 ug/L.

(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYCRITERIA: *ENDRIN
Aquatic 

## Life For endrin the criterion to protect freshwater aquatic life as derived using the Guidelines is 0.0023 ug/L as 

### a 24

-hour average, and the concentration should not exceed 0.18 ug/L at any time. For endrin the criterion to protect saltwater aquatic life as derived using the Guidelines is 0.0023 ug/L 

### as a 24

-hour average, and the concentration should not exceed 0.037 ug/L at any time.
Human Health The ambient water quality criterion for endrin is recommended to be identical to the existing water standard which is 1.0 ug/L. Analysis of the toxic effects data resulted in 

### a calculated level which is protective of human health against the ingestion of contaminated water and contaminated aquatic organisms. The calculated value is comparable to the present standard. For this reason a selective criterion based on exposure solely from assumption of 6.5 g of aquatic organisms was not derived.

*Indicates suspended, canceled or restricted by W.S. EPA Office 

### of Pesticides and Toxic Substances
(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGY

# 0 CRITERIA:

The avai 3 B da ETHYLBENZENE
Aquatic

## Life

3 for ethylbenzene idicate t at acute toxicity to freshwater aquatic life occurs at concentrations as low as 32,000 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No definitive data are available concerning the chronic toxicity of ethylbenzene to sensitive freshwater aquatic life. The available data for ethylbenzene indicate that acute toxicity to saltwater aquatic life occurs at concentrations 

### as low as 430 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No data are available concerning the chronic toxicity of ethylbenzene to sensitive saltwater aquatic life. Human Health For the protection of human health from the toxic properties of ethylbenzene ingested through water and contaminated aquatic organisms, the ambient water criterion 

### is determined to be 1.4 W/L. For the protection of human health from the toxic properties 

### of ethylbenzene ingested through contaminated aquatic organisms alone, the ambient water criterion 

### is determined to 

### be 3.28 mg/L. (45 F.R. 79318, November 28, 1980) SEE APPENDIX 

### B FOR METHODOLOGY N

O

T

E: The U.S. EPA is currently developing Acceptable Daily Intake (ADI) or Verified Reference Dose (RfD)values for Agency

-wide use for this chemical. The 

### new value should be substituted when it becomes available. The January, 1986, draft Verified Reference Dose document cites an RfD of 0.1 mg/kg/day for ethylbenzene.FLUORANTHENE
Aquatic Life The available data for fluoranthene indicate that acute toxicity to freshwater aquatic life occurs at concentrations as low as 3,980 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No data are available concerning the chronic toxicity of fluoranthene to sensitive

-freshwater aquatic life. The available data €or fluoranthene indicate that acute and chronic toxicity to saltwater aquatic life occur at concentrations as low as 40 and 16 ug/L, respectively, and would
occur at lower concentrations' among species that are more sensitive than those tested. 

# a

Human Health For the protection of human health from the toxic properties of fluoranthene ingested through water and contaminated aquatic organisms, the ambient water criterion is determined to be 42 ug/L. For the protection of human health from the toxic properties of fluoranthene ingested through contaminated aquatic organisms alone, the ambient water criterion is determined to be 54 ug/L.
(45 F.R. 79318, Novembe-r28, 1980) SEE APPENDIX B FOR METHODOLOGYGASES, TOTAL DISSOLVED
CRITERION:
To protect freshwater and marine aquatic life, the total dissolved gas concentrations in water should not exceed 110 

### percent of the saturation value for gases at the existing atmospheric and hydrostatic pressures.
RATIONALE: Fish in water containing excessive dissolved gas pressure 

### or tension are killed when dissolved gases in their circulatory system come out of solution to form bubbles (emboli) which block the flow of blood through the capillary vessels. In aquatic organisms this 

### is commonly referred to as "gas bubble diseasett. External bubbles (emphysema) also appear in the fins, on the opercula, in the skin and in other body tissues. Aquatic invertebrates are also affected by gas bubble disease, but usua1l.y at supersaturation levels higher than those lethal to fish. 

# 0

The standard method of analyzing for gases in solutions has been the Van Slyke method (Van Slyke et al. 1934); now, gas chromatography also is used for determination of individual and total gases. For determination of total gas pressure, Weiss has developed the saturometer, a device based upon a thin

-wall silicone rubber tube that is permeable to gases but impermeable to water. Gases pass from the water through the tube, thus 

# 0 raising the internal gas pressure which is measured by amanometer or pressure gauge connected to the tube (NAS, 1974). This method alone does not separate the total gas pressure into the separate components, but Winkler oxygen determinations can be
run simultaneously, and gas concentrations can be calculated. Total dissolved gas concentrationsmust be determined because analysis of individual gases may not determine with certainty that gas supersaturation exists. For example, water could be highly supersaturated with oxygen, but if nitrogen were at less than saturation, the saturation as measured by total gas pressure might not exceed 100 percent. Also, if the water was highly supersaturated with dissolved oxygen, the oxygen alone might be sufficient to create gas pressures or tensions greater than the Criterion limits, but one would not know the total gas pressure or tension, or by how much the criterion was exceeded. The rare and inert gases such as argon, neon and helium are not usually involved in causing gas bubble disease as their contribution to total gas pressures is very low. Dissolved nitrogen (NZ),which comprises roughly 80 percent of the earth's atmosphere, is nearly inert biologically and is the most significant cause of gas bubble disease in aquatic animals. Dissolved oxygen, which is extremely bioactive, is consumed by the metabolic processes of the organism and is less important in causing serious gas bubble disease though it may be involved in initiating emboli formation in the blood (Nebeker et al. 1976a).
Percent saturation of water containing a given amount of gas varies with the absolute temperature and with the pressure. Because of the pressure changes, percent saturation with a givenamount of gas changes with depth of the water. Gas supersaturation decreases by 10 percent per meter of increase in water depth because of hydrostatic pressure; a gas that is at 130 percent saturation at the surface would be at 100 percent saturation at 3 meters' depth. Compensation €or altitude may be needed because a reduction in atmospheric pressure changes the water/gas equilibria, resulting in changes in solubility of dissolved gases. There are several ways that total dissolved gas supersaturation can occur: 1. Excessive biological activity

--dissolved oxygen concentrations often reach supersaturation because 

### of excessive algal photosynthesis. Renfro (1963) reported gas bubble disease in fishes resulting, in part, from algal blooms. Algal blooms often accompany an increase in water temperature and this higher temperature further contributes 

### to supersaturation. I

2. Lindroff (1957) reported that water spillage at hydropower dams caused supersaturation. When excess water is spilled over the face of a dam 

### it entrains air as it plunges to the stilling

### orplunge pool atthebaseofthedam. Themomentum 

### of the fall carries the water and entrained gases to great depths in the pool; and, under increased hydrostatic pressure, the entrained gases are driven into solution, causing supersaturation of dissolved gases. 3. Gas bubble disease may be induced by discharges from power-generating and other thermal sources (Marcello et al. ./ 1975). Cool, gas-saturated water is heated as 

### it passes through the condenser 

### or heat exchanger. As the temperature of the waterrises, percent saturation increases because of the reduced solubility of gases at higher temperatures. Thus, the discharged water becomes supersaturated with gases and fish or other organisms living in the heated water may exhibit gas bubble disease (DeMont and Miller, 1972: Malouf et al. 1972; Keup, 1975). 

### ! In recent years, gas bubble disease has been identified as a major problem affecting valuable stocks of salmon and trout in the Columbia River system (Rulifson and Abel, 1971). The disease is caused by high concentrations of dissolved atmospheric gas which enter the river's water during heavy spillinq at hydroelectric dams. A report by Ebel et al. (1975)presents results from field and laboratory studies on the lethal, sublethal and physiological effects of gas on fish, depth distribution of fish in the river (fishcan compensate for some high concentrations of gas by moving deeper into the water column), detection and avoidance of gas concentrations by fish, intermittent exposure of fish to gas concentrations, and bioassays of many species of fish exposed to different concentrations of gas. Several conclusions resulting from these studies are: 1. When either juvenile or adult salmonids are confined to shallowwater (1

### m), substantial mortality occurs at and above 115 percent total dissolved gas saturation. 2. When either juvenile or adult salmonids are free to sound and obtain hydrostatic compensation either in the laboratory or in the field, substantial mortality still occurs when saturation ,levels 

### (of total dissolved gases) exceed 120 percent saturation. 3. On the basis of survival estimates made 

### in the Snake River from 1966 to 1975, 

### it is concluded that juvenile fish lossesranging from 40to 95percentdooccurandamajorportion 

### of this mortality can be attributed to fish exposure to supersaturation by atmospheric gases during years of high flow. 4. Juvenile salmonids subjected to sublethal periods of exposure to supersaturation can recoverwhen returned to normally saturated water, but adults do not recover and generally die from direct and indirect effects of the exposure. 5. Some species of salmon and trout can detect and avoid supersaturated water; others may not. 6. Higher survival was 'observed during periods of intermittent exposure than during continuous exposure. 7. 

### In general, 

### in acute bioassays, salmon and trout were less tolerant than the nonsalmonids. Dawley and Ebel (1975) found that exposure of juvenile spring chinook salmon,Oncorhynchus tshawytscha, 

## - - and steelhead trout, Salmo qairdneri, 

### to 120 percent saturation for 1.5 days resulted in over 50 percent mortality; 100 percent mortality occurred in less than 3 days. They also determined that the threshold level where significant mortalities begin occurring is at 115 percent nitrogen saturation (111percent total gas saturation in this test). Rucker (1974), using juvenile coho salmon, Oncorhynchus kisutch, determined the effect of individual ratios of oxygen and nitrogen and established that a decrease in lethal effect -., occurred when the nitrogen content fell below 109 percentsaturation even though total gas saturation remained at 119 percent saturation, indicating the importance of determining the concentration of the individual components (02and N2) of the atmospheric supersaturation. Nebeker et al. (1976a), using juvenile sockeye salmon, Oncorhynchus nerka, also showed that there was a significant increase in fish mortality when the nitrogen concentration was increased while holding the total percent saturation constant. They also showed that there was no significant difference 

### in fish mortality at different C02 concentrations. Research collected by Bouck et al. (1975) showed that gas supersaturated water at and above 115 percent total gas saturation is acutely lethal to most species of salmonids, with 120 percent saturation and above rapidly lethal to all salmonids tested. Levels as low as 110 percent will produce emphysema in most species. Steelhead trout were most sensitive to gassupersaturateawater followed by sockeye salmon, Oncorhyncnus nerka. Chinook salmon, 

## ______ Oncorhynchus 

## _____ -_--_ tshawytscha -----I were intermediate in sensitivity. Coho salmon, Oncorhyncnus kisutch,
were significantly the more tolerant of the salmonids though 

## -----

still much more susceptible than non

-salmonids like bass or carp.

- DaFnia 

### -- rmqna 

## __ exhibited a sensitivity to supersaturation similar to that of the salmonids (Nebeker et al. 1975), with 115 percent saturation lethal within a few days. Stoneflies exhibited
an intermediate sensitivity similar to bass with mortality at 130 percent saturation. Crayfish were very tolerant, with levels
near 140 percent total gas saturation resulting in mortality.No differences are proposed inthe criteria €or freshwater and marine aquatic life as the data available indicate that there probably is little difference 

### in overall tolerances between marine and freshwater species. The development of gas bubble disease inmenhaden, Soortia sp., and their 

### tolerance to gas saturation in laboratory bioassays and 

### in the field (Pilgrim Nuclear Power Station Discharge Canal) are discussed by Clay et al. (1975) and Marcello et al. (1975). At 100 percent and 105 percent nitrogen saturation, no gas bubbles developed externally or in any of the internal organs of menhaden. At 105 percent nitrogen saturation, however, certain behavioral changes became apparent. Fish sloughed of€mucus, swamerratically, were more excitable, and became darker in color. Menhaden behavioral changes observed at 110percent nitrogen saturationwere similartothose noted at 3.05 percent. Inaddition, 

### at110percent gas emboli

### were found in the intestines, the pyloric caeca, and occasionally the operculum. The behavioral changes described were also observed at 115percent, and clearlydefined subcutaneous emphysema was observed inthe

### finsand occasionallyintheeye. At120percent and 130 percent nitrogen saturation, menhaden developed within a fewhours classic symptoms of gasbubble disease. Externally, emboli 

### were evident 

### in all 

### fins, the operculum and within the oral cavity. Exophthalmia also occurred and emboli developed in internal The bulbous arteriosis and swimbladderwere severely

J distended, and emboli were found along the length of the gill arterioles, resulting in hemostasis. Atwater temperatures of 30 organs. 

# 0OC, menhaden did not survive, regardless of gas saturation level. At water temperatures of 15 

## , 22 

## , and 25 OC 100 percent of the menhaden died within 24 hours at 120 percent and 130 percent gas saturation. Fifty percent died after 96 hours at 115 percent (22 OC) Menhaden survival after 96 hours at 110 percent nitrogen saturation ranged from 92 percent at 22O and 25' to 83 percent at 15 OC. Observations on the relationship between the mortality rate of menhaden and gas saturation levels at Pilgrim Station during the April 1975, incident suggest that the fish may tolerate somewhat higher gas saturation levels in nature. It has been shown by Bouck et al. (1975)and Dawley et al. (1975) that survival of salmon and steelhead smolts in seawater is not affected by prior exposure to gas supersaturation while in fresh water. No significant mortality of juvenile coho and sockeye salmon occurred when they were exposed to sublethal concentrations of supersaturated water and then transferred to seawater (Nebeker et al. 197633).

(QUALITY CRITERIA FOR WATER, JULY 1976) PB

-263943 SEE APPENDIX C FOR METHODOLLIGYGUTHION
CR

### ITE RIO N: .01 ug/L for freshwater and marine aquatic life.

RATIONALE: Ninety

-six

-hour LC50 values for fish exposed to the organophosphorus pesticide guthion range from 4 to 4270 ug/L (Katz, 1961: Pickering et al. 1962; Lahav and Sarig, 1969; Macek et al. 1969; Macek and McAllister, 1970). The only long

-term fish exposure data available are those obtained recently by Adelman and Smith (unpublished data) Decreased spawning (eggs produced per female) was observed in fathead minnows, PimephalE 

### prrelas ---I exposed during a complete life cycle. An estimated "safe" long

-term exposure concentration for fathead minnows lies between 0.3 and 0.5 ug/L. survival of larvae was reduced at approximately 0.7 ug/L. 

# 0

An investigation of the persistence of guthion in fish revealed that 50percent of the chemical was lost in less than one week (Meyer, 1965). Analysis of plankton and pond water in the same study indicated a 50percent lossof guthioninabout48 hours. Flint et al. (1970)determined the half

-life of guthion at 30C in pond water and in a phosphate buffer protected from light in the laboratory. The half

-life in pond water was 1.2 days whereas that in the laboratory solution was 10 days. The
more rapid degradation in pond water was attributed to the effect of sunlight and microorganisms. Organophosphate pesticides are toxic because they inhibit theenzyme acetylcholinesterase (AChE) which is essential to nerve impulse conduction and transmission (Holland et al. 1967). Weiss (1958, 1959, 1961) demonstrated that a 40 to 70 percent inhibition of fish brain AChE usually is lethal. Centrarchids generally are considered one of the more sensitive groups of fish to guthion (Pickering et al. 1962; Weiss and Gakstatter, 1964; Meyer, 1965). Weiss and Gakskatter (1964) found that over a 15- day period bluegills, 

## -_ Lepomis 

## __ macrochirus1 exhibited AChE inhibition at 1.0 ug/L guthion but not at 0.1 ug/L. Exposure at 0.05 ug/L for 30days also failed toproduce inhibitionbelow the range of normal variation, but the authors stated that it appeared there was a downward trend in brain enzyme activity and that if exposure was continued a definite reduction might develop. Weiss (1961) found that about 30 days were required for fathead minnow and bluegill brain AChE levels to recover after 8 to 24 hours exposure to 10 ug/L guthion. Benke and Murphy (1974) showed that repetitive injection of fish with guthion caused cumulative inhibition of brain AChE and mortality. After substantial inhibition by guthion exposure, it takes several weeks for brain AChE of fishes to return to normal
even though exposure is discontinued (Weiss, 1959, 1960; Carter, 1971). Inhibition of brain AChE of fishes by 46 percent or more has been associated with harmful effects in exposures to there organophosphate pesticides for a life cycle (Eaton, 1970) and for shorter periods (Carter, 1971; Coppage and Duke, 1971; Coppage, 1972; Coppage and Matthews, 1974: Post and Leasure, 1974; Coppage et al. in press). In static tests, similar inhibition of AChE and mortality were caused in the sheepsheadminnow, Cyprinodonvariegatus, in 2, 24, 48 and 72 hours at concentrations of 50, 7, 3.5 and 3 ug/L, respectively (Coppage, 1972). These data indicate that reduction of brain AChE activity of marine fishes by 70 to 80 percent or more in short

-term exposures to guthion may be associated with some deaths. There 

### is no evidence to indicate that guthion would cause adverse effects through the food chain. Tissue residue accumulation for whole fish calculated from the data of Meyer (1965) indicate no more than a twentyfold accumulation. LC50 toxicity values for birds are relatively high and range from 70 to 2,000 mg/kg (Tucker and Crabtree, 1970). Ninety

-six

-hour LC50 values for aquatic invertebrates range from 0.10 to 22.0 ug/L (Nebeker and Gaufin, 1964; Gaufin et al. 1965: Jensen and Gaufin, 1966: Sanders and Cope, 1968: Sanders, 1969, 1972). Sanders (1972) exposed the grass shrimp, Paleomonetes kadiakensis 

# --_-__ r 

### to guthion in a continuous flow bioassay for up to 20 days and found that the 5- and 20

-day LC50 values were 1.2 and 0.16 ug/L, respectively. He found that the amphipod, 

### ---- Gammarus -I--_- fasciatus1 was the most sensitive aquatic organism tested, with a 96

-hour LC50 of 0.10 ug/L. Jensen and Gaufin (1966), also using a continuous flow system, exposed two species of stonefly naiads in 4- and 30

-day studies. They observed 96

-hour and 30

-day LC50 values for Acroneuria pacifica of 2.0 and 0.24 ug/L, respectively, whereas for Pteronarcys 

## -
- californica the values were 4.6 and 1.3 ug/L, respectively. Results of other toxicity studies on marine organisms have

1.3 been reported. The 24

-hour LC50 for the white mullet, 

## _- MUG1 

## _ 

# 0curema, was found to be 5.5 ug/L guthion (Butler, 1963). The 96- hour LC50 for the striped mullet, Mugil cephalus, was determined by Lahav and Sarig (1969)to be 8 ug/L guthion. Portman (1972) reported the 48

-hour LC50 for the fish, 

## - Pleuronectes - limanda, 

### to be 10 to 30 ug/L. The 48

-hour LC50 for the European shrimp, Cranqon crangon, was found to be 0.33 ug/L guthion (Portman, 1972). Butler (1963) found that the 24

-hour EC50 €or blue crab,


## ------- Callinectes 

## - sapidus,was 550 ug/L and the 48

-hourEC50 €orpink shrimp, Penaeus duorarum, was 4.4 ug/L guthion. The 48

-hour TLm 

### was estimated 

### to be 620 ug/L 

### €or fertilized oyster eggs, Crassostrea 

## -- vixinica ---I and 860 ug/L for fertilized clam eggs, Mercenaria 

## - mercenaria (Davis and Hidu, 1969).
A criterion level of .01 ug/L for guthion is based upon use of an 0.1 application factor applied to the 96

-hour LC50 of 0.1 ug/L for 

## ---- - Gammarus and a similar value of 0.3 ug/L for the European shrimp.

(QUALITY CRITERIA FOR WATER, JULY 1976) PB

-263943 SEE APPENDIX C FOR METHODOLOGYHALOETHERS CRITERIA: Aquatic Life The available data for haloethers indicate that acute and chronic toxicity to freshwater aquatic life occurs at concentrations as low as 360 and 122 ug/L, respectively, and would occur at lower concentrations among species that are more sensitive than those tested. No saltwater organisms have been tested with any haloether and therefore, no statement can be made concerning acute or chronic toxicity. Human Health Using the present guidelines, a satisfactory criterion cannot be derived at this time because of insufficient available data for ha1oethers. 

# 0

(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYHALOMETHANES
CRITERIA: Aquatic 

## Life The available data for halomethanes indicate that acute toxicity to freshwater aquatic life occurs at concentrations as low a 11,000 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No data are available concerning the chroni-ctoxicity of halomethanes to sensitive freshwater aquatic life. The available data for halomethanes indicate that acute 

### and chronic toxicity to saltwater aquatic life occurs at concentrations as low as 12,000 and 6,400ug/L, respectively, and would occur at lower concentrations among species that are more sensitive than those tested. A decrease in algal cell numbers
occurs at concentrations as low as 11,500 ug/L. 

# 0

Human Health For the maximum protection 

### of human health from the potential carcinogenic effects of exposure to chloromethane, bromomethane, dichloromethane, bromodichloromethane, tribromomethane, 

### dichlorodifluoromethane, trichlorofluoromethane,
or combinations of these chemicals through ingestion of contaminated water and aquatic organisms, the ambient water concentration should be zero, based on the nonthreshold assumption for this chemical, However, zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer 

### risk 

### over the lifetime 

# 0

-are estimated at loe6 and The corresponding recommended criteria are 1.9 ug/L, 0.19 ug/L, and 0.019 uq/L, respectively. If these estimates are made for consumption of aquatic organisms only, excluding consumption of water, the levels are 157 ug/L, 15.7 ug/L, and 1.57 ug/L, respectively.

(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYHARDNESS
I"RODUC"ION: Water hardness is caused by the polyvalent metallic ions disolved in water. In fresh water these are primarily calcium and magnesium although other metals such as iron, strontium and manganese contribute to 

### the extent that appreciable concentrations are present. Hardness commonly is reported as an equivalent concentration of calcium carborate (CaC03). The concept of hardness comes from water supply practice. 

### It is measured by soap requirements for adequate lather formation and as an indicator of the rate of scale formation in hot water heaters and low pressure boilers. A commonly used classification is given in the following table (Sawyer, 1960). TABLE 3. Classification of Water by Hardness Content Conc. mg/L CaC03 Description 0 

# - 75 75 

# - 150 150

# - 300 300 and up soft moderately hard hard very hard
Natural sources of hardness principally are limestones which
are dissolved by percolating rainwatermade acid by dissolved carbon dioxide. Industrial and industrially related sources include the inorganic chemical industry and discharges from operating and abandoned mines. Hardness in fresh water frequently is distinguished in carbonate and non-carbonate fractions. The carbonate fraction is chemically equivalent to the bicarbonates present in water. ISince bicarbonates generally are measured as alkalinity, the carbonate hardness usually 

### is considered equal to the alkalinity. RATIONALE: The determination of hardness in raw waters subsequently treated and used for domestic water supplies is useful as a parameter to characterize the total dissolved solids present and for calculating dosages where lime

-soda softening is practiced. Because hardness concentrations in water have not been proven health related, the final level achieved principally 

### is 

### a function of economics. Since hardness in water can be removed with treatment by such processes as lime

-soda softening and zeolite or ion exchange systems, a criterion for raw waters used for public water supply is not practical.
The effects of hardness on freshwater fish and other aquatic life appear to be related to the ions causing the hardness rather than hardness. Both the NTAC (1968)and NAS (1974)panels have recommended against the use of the term hardness but suggest the inclusion of the concentrations of the specific ions. This procedure should avoid confusion in future studies but is not helpful in evaluating previous studies. For most existing data, it is difficult to determine whether toxicity ofvariousmetal 

### ions is reduced because of the formation of metallic hydroxides and carbonates caused by the associated increases in alkalinity, or because of an antagonistic effect of one of the principal cations contributing to hardness, e.g., calcium, or a combination of both effects. Stiff (1971)presented a theory (without proof)that if cupric ions were the toxic form of copper whereas copper carbonate complexes were relatively non-toxic, then the observed difference in toxicity of copper between hard and soft waters can be explained by the difference in alkalinity rather than hardness. Doudoroff and Katz (1953), in their review of the literature on toxicity, presented data showing that increasing calcium in particular reduced the toxicity of other heavy metals. Under usual conditions in fresh water and assuming that other bivalent metals behave similarly to copper, it is reasonable to
assume that both effects occur simultaneously and explain the observed reduction of toxicity of metals inwaters containing carbonatehardness. The amount of reduced toxicity related to hardness, as measured by a 40

-hour LC50 for rainbow trout, has been estimated tobe about four times for copper and zincwhen the hardness was increased from 10 to 100 mg/L as CaC03 (NAS, 1974)

# - Limits on hardness for industrial uses arequite variable. Table 4 lists maximum values that have been accepted by various industries as a source of raw water (NAS, 1974). Subsequent treatment generally can reduce hardness to tolerable limits although costs of such treatment are an important factor in determining its desirability €or a particular water source. Hardness is not a determination of concern for irrigation use of water. The concentrations of the cations calcium and magnesium, which comprise hardness, are important in determining the exchangeable sodium in a given water. This particular calculationwillbe discussed under total dissolved solids ratherTABLE 4. Maximum Hardness Levels Accepted

By Industry as a Raw Water Source* Industry Electric utilities Maximum Concentration m&L as CaC03 

## - 5,000 Textile 120 Pulp and paper 475 Chemical 1,000 Petroleum 900 Primary metals 1,000 

## * Requirements for final use within a process may be essential11 zero, which requires treatment for concentration reductions.than hardness. 

# a

(QUALITY CRITERIA FOR WATER, JULY 1976) PB-263943 SEE APPENDIX C FOR METHODOLOGYHEFTACHLOR CRITERIA: Aquatic Life For heptachlor the criterion to protect freshwater aquatic life as derived using the Guidelines is 0.0038 ug/L as a 24

-hour average, and the concentration should not exceed 0.52 ug/L at any time. For heptachlor the criterion to protect saltwater aquatic life as derived using the Guidelines is 0.0036 ug/L as a 24

-hour average, and the concentration should not exceed 0.053 ug/L at any time.
Human Health For the maximum protection of human health from the potential carcinogenic effects of exposure to heptachlor through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentration should be zero, based on the non threshold assumption for this chemical. However, zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer risk over the lifetime are estimated at and The corresponding recommended criteria are 2.00 ng/L, 0.20 ng/L, and 0.020 ng/L, respectively. If these estimates are made for consumption of aquatic organisms only, excluding consumption of water, the levels are 2.04 ng/L, 0.20 ng/L, and 0.020. ng/L, 

# 0

respectively. 

# 0 (45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYHEXACHLOROBUTADIENE CRITERIA: Aquatic Life The available data for hexachlorobutadiene indicate that acute and chronic toxicity to freshwater aquatic life
occur at concentrations as low as 90 and 9.3 ug/L, respectively, and would occur at lower concentrations among species that are
more sensitive than those tested. The available data for hexachlorobutadiene indicate that acute toxicity to saltwater aquatic life occurs at concentrations
as low as ?2ug/L and would occur at lower concentrationsamong species that are more sensitive than those tested. No data are I available concerning the chronic toxicity of hexachlorobutadiene to sensitive saltwater aquatic life. 

# 0

Human Health 

### For the maximum protection of human health from the potential carcinogenic effects 

### of exposure to hexachlorobutadiene through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentrations should be zero, based on the nonthreshold assumption for this chemical. However, zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer risk over the lifetime 

### 'are estimated at and The corresponding recommended criteria are 4.47 ug/L, 0.45 ug/L, and 0.045 ug/L, respectively. If these estimates are 

# 0
i

-. made for consumption of aquatic organisms only, excludingconsumption of water, the levelsare 500 ug/L, 50 ug/L, and 5.0 ug/L, respectively.

(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYHEXACHUIROCYCLOHEXANE CRITERIA: Aquatic Life Lindane For lindane the criterion to protect freshwater aquatic life
as derived using the Guidelines is 0.080 ug/L as a 24

-hour average and the concentration should not exceed 2.0 ug/L at any time. For saltwater aquatic life the concentration of lindane should not exceed 0.16 ug/L at any time. No data are available concerning the chronic toxicity of lindane to sensitive saltwater aquatic life. BHC 

# -The available data for a mixture of isomers of BHC indicate that acute toxicity to freshwater aquatic life occurs at concentrations as low as 100 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No data are available concerning the chronic toxicity of
a mixture of isomers of BHC to sensitive freshwater aquatic life. The available data for a mixture of isomers of BHC indicate that acute toxicity to saltwater aquatic life occurs at concentrations as low as 0.34 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No data are available concerning the chronic toxicity of
a mixture 

### of isomers of BHC to sensitive saltwater aquatic life. 

# 0

i.Human Health For the maximum protection of human health from the potential carcinogenic effects of exposure to hexachlorocyclohexane through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentrations should be zero, based
on the nonthreshold assumption for this chemical. However, zero level may not be attainable at the present time. Therefore, the levelswhich may result in incremental increase of cancer risk



## , and 10- over the lifetime are estimated at loq5, The corresponding recommended criteria are 22 ng/L, 2.2 7 ng/L, and .22 ng/L, respectively. If these estimates are made for consumption of aquatic organisms only, excluding consumption of water, the levels are 74 ng/L, 7.4 ng/L, and .74 ng/L, respectively. 10-6

For the maximum protection of human health from the potential carcinogenic effects of exposure to hexachlorocyclohexane through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentrations should be zero, based
on the nonthreshold assumption for this chemical. However, zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer risk
over the lifetime are estimated at and The corresponding recommended criteria are 134 ng/L, 13.4 ng/L, and 1.34 ng/L, respectively. If these estimates are made for consumption of aquatic organisms only, excluding consumption of water, the levels are 450 ng/L, 45.0 ng/L, and 4.50 ng/L, respectively.For the maximum protection of human health from the potential carcinogenic effects due to exposure of rhexachlorocyclohexane through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentrations should be zero, based on the nonthreshold assumption for this chemical. However, zero level may not be attainable 

### at the present time. Therefore, the levels which may result 

### in incremental increase of cancer risk over the lifetime are estimated at and The corresponding recommended criteria are 186 ng/L, 18.6 ng/L, and 1.86 ng/L, respectively. If these estimates are made for consumption of aquatic organisms only, excluding consumption of water, the levels are 625 ng/L, 62.5 ng/L, and 6.25 ng/L, respectively. For the maximum protection of human health from the potential carcinogenic effects of exposure to technicalhexachlorocyclohexane through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentrations should be zero, based on the nonthreshold assumption for this chemical. However, 

### zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer 

### risk over the lifetime are estimated at 10-5, loe6, and The corresponding recommended criteria are 52 ng/L, 5.2 ng/L, and -52 ng/L, respectively. If these estimates are made for consumption of aquatic organisms only, excluding consumption of water, the levels are 174 ng/L, 17.4 ng/L, and 1.74 ng/L, respectively.

, / .* ,Using the present guidelines, satisfactory criteria cannot be derived at this time for d- and e- hexachlorocyclohexane because of insufficient available data.

(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYHEXACHLOROCYCLOPENTADIENE CRITERIA: Aquatic Life The available data forhexachlorocyclopentadiene indicate that acute and chronic toxicity to freshwater aquatic life occurs at concentrations as low as 7.0 and 5.2 ug/L, respectively, and would occur at lower concentrations among species that are more sensitive than those tested. The available data for 

### hexachlorocyclopentadiene indicate that acute toxicity to saltwater aquatic life occurs at concentrations as low as 7.0 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. NO data are available concerning the chronic toxicity of hexachlorocyclopentadiene to sensitive saltwater aquatic life. 

# 0

Human Health For comparison purposes, two approaches were used to derive criterion levels for hexachlorocyclopentadiene. Based on available toxicity data, to protect public health the derived level 

### is 206 ug/L. Using available organoleptic data, to control undersirable taste and odor quality of ambient water the estimated level 

### is 1 ug/L. It should be recognized that organoleptic data have limitations as a basis for establishing water quality criteria, and have no demonstrated relationship to potential adverse human health effects.

-.

, (45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGY0.3 mg/L for domestic water supplies (welfare). 1.0 mg/L for freshwater aquatic life. INTRODUCTION: Iron is the fourth most abundant, by weight, of the elements that make 

### up the earth's crust. Common inmany rocks, it is an important component of many soils, especially the clay soils where usually it is 

### a major constituent. Iron inwater may be present in varying quantities dependent upon the geology of the


### area and other chemical components of the waterway. Iron 

### is an essential 

### trace element required by both plants and animals. In some waters it may be 

### a limiting factor for the growth of algae 

### and otherplants; this is true especially 

### in some 

### marl lakes where it 

### is precipitated by the highly alkaline conditions. It is a vital oxygen transport mechanism in the blood of all vertebrate and some invertebrate animals. The ferrous, orbivalent (Fe++), and the ferric, or trivalent (Fe+++) irons, are the primary forms of concern in the aquatic environment, although other forms may be in organic and inorganic wastewater 

### streams. The ferrous (Fe++) form can persist in waters void of dissolved oxygen and originates usually from groundwaters 

### or mines 

### when these are pumped or drained. For practical purposes the ferric (Fe 

### +++) form is insoluble. Iron 

### can 

### exist in natural organometallic or humic compounds and colloidal forms. Black or brown swamp watersmay contain iron concentrations of several mg/L in the presence or absence of

..

### ..,_. ,~.,.,. .,

~~ dissolved oxygen, but this iron form has little effect on aquaticlife.

(QUALITY CRITERIA FOR WATER, JULY 1976) PB-263943 SEE APPENDIX C FOR METHODOLOGY



# a

.. .i

. :/ISOPHORONE
Aquatic Life The available data for isophorone indicate that acute toxicity to freshwater aquatic life occurs at concentrations as low as 117,000 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No data are available concerning the chronic toxicity of isophorone to sensitive freshwater aquatic life. The available data for isophorone indicate that acute toxicity to saltwater aquatic life occurs at concentrations as low as 12,900 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No data are available concerning the chronic toxicity of isophorone to sensitive saltwater aquatic life. I



### Human Health For the protection of human health from the toxic properties of isophorone ingested through water and contaminated aquatic organisms, the ambient water criterion is determined to be 5.2 

### W/L. For the protection of human health from the toxic properties of isophorone ingested through contaminated aquatic organisms alone, the ambient water criterion is determined to be 520mg/L.

(45 F.R. 79318, November 28, 1980) 

# 0
;;. : SEE APPENDIX B FOR METHODOLOGY

.. -...*.LEAD AQUATIC 

## LIFE SUMMARY: The acute toxicity of lead to several species of freshwater animals has been shown to decrease as the hardness of water increases. At a hardness of 50 mg/L the acute sensitivities of 10 species range from 142.5 ug/L for an amphipod to 235,900 ug/L for a midge. Data on the chronic effects of lead on freshwater animals are available for two fish and two invertebrate species. The chronic toxicity of lead also decreases as hardness increases and the lowest and highest available chronic values (12.26 and 128.1 ug/L) are both for a cladoceran, but in soft and hard water, respectively. Acute

-chronic ratios are available for three species and range from 18 to 62. Freshwater algae are affected by concentrations of lead above 500 ug/L, based on data for four species. Bioconcentration factors are available for four invertebrateand two fish species and range from 42 to 1,700. 

# 0

Acute values are available for 13 saltwater animal species and range from 315 ug/L for the mummichog to 27,000 ug/L for the soft shell clam. A chronic toxicity test was conducted with amysid; unacceptable effects were observed at 37 ug/L but not at 17 ug/L and the acute

-chronic ratio for this species is 124.8. A species of macroalgae was affected at 20 ug/L. Available bioconcentration factors range from 17.5 to 2,570.
NATIONAL CRITERIA: The procedures described 

### in the Guidelines for Deriving 

# 0

-2 Numerical National Water Quality Criteria for the Protection ofAquatic Organisms and Their Uses indicate that, except possibly where a locally important species is very sensitive, freshwater aquatic organisms and their uses should not be affected unacceptably if the 4

-day average concentration (in ug/L) of lead does not exceed the numerical value given by (1.273[ln(hardness)

### 3

-4.705) more than once every 3 years on the e average and if the 1

-hour average concentration (in ug/L) does not exceed the numerical value given.by .(1.273 [ln(hardness) 

### 3- 1.460) more than once every 3 years on the average. For example, at hardnesses of 50, 100, and 200 mg/L as CaC03 the 4

-day average concentrations of lead are 1.3, 3.2, and 7.7 ug/L, respectively, and the 1

-hour average concentrations are 34, 82, and 200 ug/L. The procedures described in, the Guidelines indicate that, except possibly where a locally important species is very sensitive, saltwater aquatic organisms and their uses should not be affected unacceptably if the 4

-day average concentration 

### of lead does not exceed 5.6 ug/L more than once every 3 years 

### on the average and if the 1

-hour average concentration does not exceed 140 ug/L more than once every three years on the average. EPA believes that a measurement such as tfacid-solubletl would provide a more scientifically correct basis upon which to establish criteria formetals. The criteria were developed 

### on this basis. However, at this time,no EPA

-approved methods for such a measurement are available to implement the criteria through the regulatory programs of the Agency and the States.

# a The Agency is considering development and approval of methods for
a measurement such as acid

-soluble. Until available, however, EPA recommends applying the criteria using the total recoverablemethod. This has two impacts: (1) Certain species of some 

### metals 

### cannot be analyzed directly because the total recoverable method does not distinguish between individual oxidation states, and (2) these criteria may be overly protective when based on the total recoverable method. The recommended exceedence frequency of 3 years is the Agency's best scientificjudgment of theaverage amount of 

### time it willtake an unstressed system to recover from a pollution event in which exposure to lead exceeds the criterion. A stressed system, for example, one inwhich several outfalls occur 

### in a limited area, would be expected to require more time for recovery. The resilience of ecosystems and their ability to
recover differ greatly, however,

## ' and site

- specific criteria may be established if adequate justification is provided. The use of criteria in designing waste treatment facilities requires the selection of an appropriatewasteload allocation model. Dynamic models are preferred for the application of these criteria. Limited data or other factors may make their use impractical, 

### in which case one should rely on a steady

- state model. The Agency recommends the interim use of lQ5 or lQl0 for Criterion Maximum Concentration design flow and 745 or 7Q1Q for the Criterion Continuous Concentration design flow in steadystate models for unstressed and stressed systems, respectively. These matters are discussed in more detail in the Technical Support Document for Water Quality

-Based Toxics Control (U.S. 

# 0HUMAN HEALTH CRITERIA: The ambient water quality criterion for lead is recommended to be identical to the existing drinking water standard which is 50 ug/L. Analysis of the toxic effects data resulted in a calculated level whic is protective to human health against the ingestion of contaminated water and contaminated aquatic organisms. The calculated value is comparable to the present standard. For this reason a selective criterion based 

### on expoeure Soley from consumption of 6.5 grams of aquatic organisms
was not derived.

(45 F.R. 79318 Nov. 28,1980) (50 F.R. 30784, July 29, 1985) SEE APPENDIX A FOR METHODOLOGY

# e CRITERION: MALATHION

0.1 ug/L for freshwater and marine aquatic life. RATIONALE: The freshwater fish most sensitive to malathion, an organophosphorus pesticide, appear to be the salmonids and centrarchids. Post 

### and Schroeder (1971) report a 96

-hour LC50 between 120 and 265 ug/L for 4 species of salmonids. Macek and McAllister (1970) found a 96

-hour LC50 range between 101 and 285 ug/L for 3 species of centrarchids and 3 species of salmonids. Other 96

-hour LCSO's are: rainbow trout, 

## -- Salmo gairdrleri, 68 ug/L (Cope, 1965)i largemouth bass, MicroEerus -------I salmoides 50 ug/L (Pickering et al. 1962); and chinook salmon, Oncorhynchus
I-- tshawytscha ---I 23 ug/L (Katz, 1961). All of the above testswere in static systems. Eaton (1970) determined a 96

-hour LC50 for bluegill, 

## - LeEmis --------I macrochirus in a flow

-through system at110 ug/L. Macek and McAllister (1970)reported a similar 96-hOUr LC50 for the bluegill in a static exposure. Static 96

-hour LC50s of 120 and 160 ug/L were reported by Post and Schroeder (1971) for brook trout, Salvelinus fontha&. Bender (1969) indicated that the acute toxicity to fathead minnows, Pimephales 

## -- promelas, 

## - is slightly greater (about 2.0 times) in a static system than in
a flow

-through system. The f low

-through acute toxicity to fathead minnows reported by Mount and Stephan (1967) approximated the static acute toxicity reported by Henderson and Pickering 

# 0

(1958)and Bender (1969).



# 0

xiMany aquatic invertebrates appear to be more sensitive than fish to malathion. The 96

-hour LC50 for Gammarus lacustris was 1.0 ug/L (Sanders, 1969); for Pteronarcella badia 1 1.1 ug/L (Sanders and Cope, 1968); and for 

## ---- Gammarus 

### ----- fasciatus1 0.76 ug/L (Sanders, 1972). The 48-hOUr LC50 for Simocephalus
-----I- serrulatus
was 3.5 ug/L and for

## - Daphnia 

## -pulex, 1.8 ug/L (Sanders and Cope, 1966). 

### -- Daphnia 

## ---- were immobilized in 50 hours in 0.9 ug/L (Anderson, 1960). The 24

-hour LC50s for two species of midge larvae were 2.1 ug/L (Mulla and Xhasawinah, 1969) and 2.0 ug/L (Karnak and Collins, 1974). Safe life cycle exposure concentrations for the more sensitive invertebrates are not known. The most sensitive aquatic organisms probably have not yet been tested; safe concentrations for the most s'ensitive invertebrates exposed through a complete life cycle have not been determined; and effects of low concentrations on invertebrate behavior are unknown. The stability of malathion in water is dependent on the chemical and biological conditions of the water (Paris et al. 1975). Weiss and Gakstatter (1964) have shown that the half

- life of malathion was reduced from about 5 

### months atpH 6 to 1to 2 weeks atpH 8. Eichelberger and Lichtenberg (1971) found that only 10percent remained inthe LittleMiamiRiver (pH 7.3

-8.0) after 2 weeks. Bender (1969) states that one of the malathion breakdown products may be more toxic than the parent compound. It has been shown that a measured concentration of 575 ug/L malathion 

### in flowing seawater kills 40 to 60 percent of themarine fish, Lagodon rhomboides, in 3.5 hours and causes about 75 percent 

### brain acetylcholinesterase (AChE) inhibition (Coppage 

### et al. 1975). Similar inhibition of AChE and mortality were caused in pinfish in 24, 48, and 72 hours'at measured concentrations of 142, 92 and 58 ug/L, respectively. A concentration of 31ug/L caused 34 percent AChE inhibition in pinfish but no deaths in 72 hours. Coppage and Matthews (1974) demonstrated that deathmay be associated with reductions of brain AChE activity of four marine fishes by 70 to 80 percent 

### or more 

### in short

-term exposures to malathion. Coppage and Duke (1971) found that moribund mullet, Mugil cephalus, in an estuary sprayed with malathion (3 oz./acre) during a large

- scale mosquito control operation had about 98 percent inhibition of brain AChE. This is in agreement with 70 to 80 percent or more inhibition of brain AChE levels at and below which some deaths are likely to occur in short

- term exposure. Spot, Leiostomus xanthurus, and Atlantic croaker, Micropogon 

## - undule, also had substantial inhibition of brain during the spray operation (70 percent or more inhibition). 

# 0

Toxicity studies have been made on a number of marine animals. Eisler (1970) studied the 96

-hour LC50 for several marine fishes at 20 OC in static, aerated seawater. The 96

-hour LC50 values 

### (in ug/L) were: Menidia menidia, 125: 

## - Mugil cephalus, 550; Fundulus 

## rnnialis 

## _--- 1 250; Fundulus heteroclitus, 240;


## - sphaeroides 

# --_-__--- ---_-----I maculatus 3250: Anquilla 

## __ 

# _-___ --___-__I rostrata 82: and Thalassoma bifasciatum, 27. Katz (1961) reported the static 24- hour LC50 for Gasterosteus aculeatus in 25 o/oo saltwater as 76.9 ug/L active ingredient. The 96

-hour LC50 for striped bass,Morone 

## _--_ --.-------I saxatilis in intermittent flowing seawater has been reported as 14ug/L (U.S. BSFW, 1970). Reporting on studies of the toxicityof malathion on marine invertebrates, Eisler (1969) found the 96-hour LC50 (static, 24 o/oo salinity aerated) to be 33 ug/L for sand shrimp, Crangon septemspinosa; 82 ug/L for grass shrimp, Saemonetes vulgaris; 

## -- and 83 ug/L for hermit crab, Pagurus longicarpus. Growth of oyster, Crassostrea virginica, was reduced 32 percent by 96

-hour exposure to 1 mg/L (Butler, 1963). The 48

-hour LC50 for fertilized eggs of oysters was estimated by Davis and Hidu (1969) to be 9.07 mg/L and the 14

-day LC50 for larvae, 2.66 mg/L. Malathion enters the aquatic environment primarily as a result of its application as an insecticide. Because it degrades quite rapidly in most waters, depending on pH, its occurrence is sporadic rather than continuous. Because the toxicity is exerted through inhibition of AChE and because such inhibition may be additive with repeated exposures and may be caused by any of the organophosphorus insecticides, inhibition of AChE by more than 35 percent may be expected to result in damage to aquatic organisms. An application factor of 0.1 is applied tothe 96-hOUr LC50 data for Gammarus lacustris, - G. fasciatis and Daphnia, which are all approximately 1.0 ug/L, yielding a criterion of 0.1 ug/L.

(QUALITY CRITERIA FOR WATER, JULY 1976) PB

-263943 SEE APPENDIX C FOR METHODOLOGYMANGANESE

50 ug/L for domestic water supplies (welfare): 100 ug/L for protection of consumers of marine molluscs. INTRODUCTION: Manganese does not occur naturally as a metal but is found in various salts and minerals, frequently 

### in association with iron compounds. The principal manganese

-containing substances are manganese dioxide (MnOZ) 

## , pyrolusite, manganese carbonate (rhodocrosite)and manganese silicate (rhodonite)

~ The oxides are the only important minerals mined. Manganese is not mined in the United States except when manganese is contained in iron ores that are deliberately used to fohferro

-manganese alloys. The primary uses of manganese are in metal alloys, dry cell batteries, micro

-nutrient fertilizer additives, organic compounds used in paint driers and as chemical reagents. Permanganates are very strong oxidizing agents of organic materials. Manganese is a vital micro

-nutrient for both plants and animals. When manganese is not present in sufficient quantities, plants exhibit chlorosis (a yellowing of the leaves) 

### or failure of the leaves to develop properly. Inadequate quantities of manganese in domestic animal food results in reduced reproductive capabilities and deformed or poorly maturing young. Livestock feeds usually high corn diet have sufficient manganese, but beef cattle on a may require a supplement.RATIONALE: Although inhaled manganese dusts have been reported to be toxic 

### to humans, manganese normally 

### is ingested as a trace nutrient 

### in food. The average human intake 

### is approximately 10 mg/day (Sollman, 1957). Very large doses of ingested manganese can cause some disease and liver damage but these are not known to occur 

### in the United States. Only a few manganese toxicity problems have been found throughout the world and these have occurred under unique circumstances, i.e., a well in Japan near a deposit 

### of buried batteries (McKee and Wolf, 1963). 

### It is possible to partially sequester manganese with special treatment but manganese is not removed in the conventional treatment of domestic waters (Riddick et al. 1958: Illig, 1960). Consumer complaints arise when manganese exceeds a concentration 

### of 150 ug/L 

### in water supplies (Griffin, 1960). These complaints are concerned primarily with the brownish staining of laundry and objectionable tastes in beverages. It is possible that the presence of low concentrations of iron may intensify the adverse effects 

### of manganese. Manganese at concentrations of about 10 to 20 ug/L is acceptable to most consumers. A criterion for domestic water supplies of 50 ug/L should minimize the objectionable qua1ities. McKee and Wolf (1963) summarized data on toxicity of manganese to freshwater aquatic life. Ions of manganese are found rarely at concentrations above 1 mg/L. The tolerance values reported range from 1.5 mg/L to over 1000 mg/L. Thus, manganese is not considered to be a problem in fresh waters. Permanganateshavebeen reportedtokill fish in 8to18hours atconcentrations of 2.2 to 4.1 mg/L, but permanganates are not persistent because they rapidly oxidize organic materials and are thereby reduced and rendered nontoxic. Few data are available 

### on the toxicity of manganese to marine organisms. The ambient concentration of manganese 

### is about 2 ug/L (Fairbridge, 1966). The material is rapidly assimilated and bioconcentrated into nodules that are deposited on the sea floor. The major problem with manganese may be concentration in the edible portions of molluscs, as bioaccumulation factors as high


### as 12,000 have been reported (NAS, 1974). In order to protect against a possible health hazard to humans by manganese accumulation in shellfish, a criterion of 100 ug/L 

### is recommended for marine water. Manganese 

### is not known 

### to be a problem iq water consumed by livestock. At concentrations of slightly less than 1 mg/L 

### to 

### a few milligrams per liter, manganese nay be toxic to plants 

### from irrigation water applied to soils with pH values lower than 6.0. The problem may be rectified by liming soils to 

### increase the pH. Problems may develop with long

-term (20 year) continuous irrigation on other soils with water containing about 10 mg/L of manganese (NAS, 1974). But, as stated above, manganese is rarely found in surface waters at concentrations greater than 1mg/L. Thus, no specific criterion for manganese in agricultural 

### waters is proposed. In select areas, and where acidophilic crops ate cultivated and irrigated, a criterion of 200 ug/L is suggested 

# 0 for consideration. i 

### \+./Most industrial users of water can operate successfully where the criterion proposed for public water supplies is observed. Examples of industrial tolerance of manganese in water are summarized for industries such as dyeing, milk processing, paper, textiles, photography and plastics (McKeeand Wolf, 1963). A more restrictive criterion may be needed to protect or ensure product quality.

(QUALITY CRITERIA FOR WATER, JULY 1976) P B- 263943 SEE APPENDIX C FOR METHODOLOGY*MERCURY
AQUATIC 

### LIFE Data are SUMMARY: available on the acute toxicity of mercury(I1) ,to 28 genera of freshwater animals. Acute values for invertebrate species range from 2.2 ug/L for Daphnia pulex to 2,000 ug/L for three insects. Acute values for fishes range from 30 ug/L for the guppy to 1,000 ug/L for the - Mozambique tilapia. Few data are available for various organomercury compounds and mercurous nitrate, and they all appear to be 4 to 31timesmore acutely toxic than mercury(I1). Available chronic data indicate that methylmercury is the most chronically toxic of the tested mercury compounds. Tests on methylmercury with Daphnia magna and brook trout produced chronic values less than 0.07 ug/L. For mercury(I1) the chronic value obtained with 

## - Daania

__- msna - was about 1.1 ug/L and the acute- chronic ratiowas 4.5. In both a life

- cycletest and an early life

- stage test on mercuric chloride with the fathead minnow, the chronic value was less than 0.26 ug/L and the acute

-chronic ratio
was over 600. 

# 0

Freshwater plants show a wide range of sensitivities to mercury, but the most sensitive plants appear to be less sensitive than the most sensitive freshwater animals to both mercury(I1) and methylmercury. A bioconcentration factor of 4,994 is available for mercury(II), but the bioconcentration factors for methylmercury range from 4,000 to 85,000. 

# 0 \., *Indicates suspended, canceled or restricted by U.S. EPA Office of Pesticides and Toxic SubstancesData on the acute toxicity of mercuric chloride are available for 29 genera of saltwater animals, including annelids, molluscs, crustaceans, echinoderms,and fishes. Acute values range from 3.5 ug/L for a mysid to 1,678ug/L for winter flounder. Fishes tend to be more resistant and molluscs and crustaceans tend to be more sensitive to the acute toxic effects of mercury(I1). Results of a life

-cycle test with the mysid show that mercury(I1) at a concentration of 1.6 ug/L significantly affected time of first spawn and productivity; the resulting acute

-chronic ratio
was 3.1. Concentrations of mercury that affected growth and photosynthetic activity of one saltwater diatom and six species of brown algae range from 10 to 160 ug/L. Bioconcentration factors of 10,000 and 40,000 have been obtained for mercuric chloride and methylmercury with an oyster.
NATIONAL CRITERIA: Derivation of 

### a water quality criterion for mercury is more complex than for most metals because of methylation of mercury in sediment, in fish, and in the food chain of fish. Apparently almost all mercury currently being discharged is mercury(I1). Thus mercury(I1) should be the only important possible cause of acute toxicity and the Criterion Maximum Concentrationscan be based on the acute values for mercury(I1). The best available data concerning long

-term exposure of fish to mercury(I1) indicates that concentrations above 0.23 ug/L caused statistically significant effects on the fathead minnow and caused the concentration of total mercury in the whole bodyto exceed 1.0 mg/kg. Although it is not known what percent of themercury in the fishwasmethylmercury, it is also

### not known whether uptake from food would increase the concentration in the fish in natural situations. Species such as rainbow trout, coho salmon, and especially thebluegill, might suffer chronic effects and accumulate high residues of mercury about the same as the fathead minnow. With regard to long

-term exposure tomethylmercury, McKim et al. (1976) found that brook trout can exceed the FDA action level without suffering statistically significant adverse effects on survival, growth, orreproduction. Thus formethylmercury the Final Residue Value would be substantially lower than the Final Chronic Value. Basing a freshwater criterion on the Final Residue Value of 0.012 ug/L derived from the bioconcentration factor of 81,700 for methylmercury with the fathead minnow (Olson et al. 1975) essentially assumes that all discharged mercury is methylmercury. On the other hand, there is the possibility that in field situationsuptake from food might add totheuptake from water. Similar considerations apply to the derivation of the saltwater criterion of 0.025 ug/L using the BCF of 40,000 obtained for methylmercury with the Eastern oyster (Kopfler, 1974). Because the Final Residue Values formethylmercury are substantially below theFinal Chronic Values formercury(II), it is probably not too important that many fishes, including the rainbow trout, coho salmon, bluegill, and haddock might not be adequately protected by the freshwater and saltwater Final Chronic Values for mercury(I1).In contrast to all the complexities of deriving numerical criteria for mercury, monitoring for unacceptable environmental effects should be relatively straightforward. The most sensitive adverse effect will probably be exceedence of the FDA action level. Therefore, existing discharges should be acceptable if the concentration of methylmercury in the edible portion of exposed consumed species does not exceed the FDA action level. The procedures described in the Guidelines for Deriving Numerical National Water Quality Criteria for the Protection of Aquatic Organisms and Their Uses indicate that, except possibly where a locally important species is very sensitive, freshwater aquatic organisms and their uses should not be affected unacceptably if the 4

-day average concentration of mercury does I not exceed 0.012 ug/L more than once every 3 years on the average and if the 1

-hour average concentration does not exceed 2.4 ug/L
more than once every 3 years on the average. If the 4

-day average concentration exceeds 0.012 ug/L more than once in a 3- year period, the edible portion of consumed species should be analyzed to determine whether the concentration of methylmercury exceeds the FDA action level. The procedures described in the Guidelines indicate that, except possibly where a localy important species is very sensitive, saltwater aquatic organisms and their uses should not be affected unacceptably if the 4

-day average concentration of mercury does not exceed 0.025 ug/L more than once every 3 years on the average and if the 1

-hour average concentration does not exceed 2.1 ug/L more than once every 3 years on the average. If the 4

-day average concentration exceeds 0.025 ug/L more than oncein a 3

-year period, the edible protion of consumed species should be analyzed to determine whether the concentration of mathylmercury exceeds the FDA action level. 

# 0

EPA believes that a measurement such as "acid-soluble" would provide a more scientifically correct basis upon which to establish criteria formetals. The criteria weredeveloped on thisbasis. However, atthistime, no EPA approved

-methods for such a measurement are available to implement the criteria through the regulatory programs of the Agency and the States. The Agency is considering development and approval of methods for
a measurement such as acid

-soluble. Until available, however, EPA recommends applying the criteria using the total recoverable method. This has two impacts: (1) certain species of some metals cannot be analyzed directly because the total recoverable method does not distinguish between individual oxidation states, and (2) these criteria may be overly protective when based on the total recoverable method. 

# 0

The recommended exceedence frequency of 3 years is the Agency's best scientificjudgment of the averageamount of time it willtake an unstressed system torecover from a pollution event in which exposure to mercury exceeds the criterion. A stressed system, for example, one in which several outfalls occur in a limited area, would be expected to require more time for recovery. The resilience of ecosystems and their ability to
recover differ greatly, however, and site

- specific criteria may be established if adequate justification is provided. 

# 0

..,

,'The use of criteria in designing waste treatment facilities requires the selection of an appropriate wasteload a1location model. Dynamic models are preferred for the application of these criteria. Limited data or other factors may make their use impractical, in which case one should rely on a steady

-state model. The Agency recommends the interim use of 1Q5 or lQl0 for Criterion Maximum Concentration design flow 

### and 745 

### or 7410 for the Criterion Continuous Concentration design flow in steadystatemodels for unstressed and stressed systems respectively. These matters are discussed in more detail in the Technical Support Document for Water Quality

-Based Toxics Control (U.S EPA, 1985). HUMAN HEALTH CRITERIA I For the protection of human health from the toxic properties of mercury ingested through water and contaminated aquatic organisms, the ambientwater criterion 

### is determined to be 144 

### nWL. For the protection of human health from the toxic properties of mercury ingested through contaminated aquatic organisms alone, the ambient water criterion is determined to be 146 ng/L.
NOTE: These values include the consumption of freshwater, estuarine, and marine species.

(45 F.R. 79318 Nov. 28,1980) (50 F.R. 30784, July 29, 1985) SEE APPENDIX A FOR METHODOLOGY

# 0 CRITERIA: METHOXYCHMR
100 ug/L for domestic water supply (health); 0.03 ug/L for freshwater and marine aquatic life.
RATIONALE : The highest level of methoxychlor found tohave minimal orno long

-term effects in man is 2.0 mg/kg of body weight/day (Lehman, 1965). Where adequate human data are available for corroboration of the animal results, the 

### total tfsafe't drinking water intake level is assumed to be l/lOO of the no-effect or minimal effect level reported for the most sensitive animal tested, in this case, man. Applying the available data and based upon the assumptions that 20 percent of the total intake of methoxychlor is from drinking water, and that the average person weighs 70 kg and
consumes 2 liters of water per day, the formula for calculating a criterion is 2.0 mg/kg 

### x 0.2 x 70 kg 

### x 1/100 

### x 1/2 = 0.14 mg/L. A criterion 

### level for domestic 

### water supply of 100 ug/L is recommended. Few data: 

### are available on acute and chronic effects of methoxychlor on freshwater fish. Merna and Eisele (1973) observed reduced hatchability of fathead minnow pimzhales 

## - prcelas) 

### -- embryos 

### at 0.125 ug/L and lack of spawning at 2.0 ug/L. Yellow perch, Perca 

### -- flavescens, exposed to 0.6 ug/L for 8 months exhibited reduced growth. The 36

-hour LC50 concentration
was 7.5 and 22 ug/L for the fathead minnow and yellow perch,



### .- respectively. Korn and Earnest (1374) obtained a 96

-hour LC50of 3.3 ug/L with juvenile stripped bass, Morone -----_I saxatilis exposed to methoxychlor in a flowing

-water bioassay. Sanders (1972)determined a 96

-hour LC50 value of 0.5 ug/L for the crayfish, Orconectes nais. Merna and Eisele (1973) obtained a 96

-hour LC50 value of 0.61 ug/L for the scud, Gammarus pseudolimnaeus and 96

-hour LC5O's ranging from 1.59 to 7.05 ug/L for the crayfish, Orconectes --I nais and three aquatic insect larvae. 

### In 28

-day exposuresI reduction in emergence of mayflies,



### ----- Stenonema sp. and 

### in pupation of caddisflies, Cheumatospsyche 

# _- sp., were observed at 0.5 and 0.25 ug/L concentrations, respectively. They also found methoxychlor to be degraded in a few weeks or less in natural waters. Eisele (1974) conducted a study in which a section of a natural stream was dosed at 0.2 ug/L methoxychlor for 1 year. The near extinction of one species of scud, wllella 

### ---- azteca, and reductions in populations of other sensitive species, as well as biomass, were observed. Residue accumulation of up to 1,000 times the level 

### in the stream was observed in first

-year crayfish, Orconectes

# __ nais. Metcalf et al. (1971) traced the rapid conversion of methoxychlor to water soluble compounds and elimination from the tissues of snails, mosquito larvae and mosquitofish. Thus, methoxychlor appears to be considerably less bioaccumlative in aquatic organisms than some of the other chlorinated pesticides. Methoxyhlor has a very low accumulation rate in birds and mammals (Stickel, 1973), and relatively low avian (Heath et al. 1972) and mammalian (Hodge et al. 1950) toxicities. No administrative guidelines for acceptable levels in edible fishtissues have been established by the U.S. Food and Drug Administration. The above data indicate that 0.1 ug/L methoxychlor would be just below chronic effect level for the fathead minnow and onefifth the acute toxicity level in a crayfish species. Therefore, a criterion level of 0.03 ug/L is recommended. This criterion should protect fish as sensitive as striped bass and is 10 times lower than the level causing effects on some invertebrate populations in a 1

-year dosing of a natural stream. Bahner and Nimmo (1974) found the 96

-hour LC50 of methoxychlor for the pink shrimp, Penaeus ----I duorarum to be 3.5 ug/L and the 30

-day LC50 to be 1.3 ug/L. Using an application factor of 0.01 with the pink shrimp's acute toxicity of 3.5 ug/L, the recommended criterion for the marine environment is 0.03 ug/L. Butler (1971) found accumulation factors of 470 and 1,500 for the molluscs, Mercenaria 

## _-_____-_- 

## ______-___ mercenaria and 

### gyg arenaria, respectively, when exposed to 1 ug/L methoxychlor for 5 days. Using the 1,500 accumulation factor 

### as a basis, a water concentration of 0.2 ug/L would be required to meet the U.S. Food and Drug Administration's guideline for methoxychlor in meat products. Thus, the recommended marine criterion of 0.03 ug/L is an order of magnitude lower than this concentration.

(QUALITY CRITERIA FOR WATER, JULY 1976) PB

-263943 SEE APPENDIX C FOR METHODOLOGY -

# .,MIREX CRITERION: 0.001 ug/L for freshwater and marine aquatic life. RATIONAL??.: Mirex is used to control the imported fire ant Solenzsis 

# - saevissima richteri in the southeastern United States. Its use is essentially limited to the control of this insect and it is always presented in bait. In the most common formulation, technical grade mirex is dissolved in soybean oil and sprayed on corncob grits. The bait produced in this manner consists of 0.3 percent

### mirex, 14.1 percent soybean oil and 85 percent corncob grits. bait often is applied ata rate of 1.4 kg/ha, The mirex
I equivalent to 4.2 grams of toxicant per hectare. Relatively few studies have been made of the effects of 

### mirex
on freshwater invertebrates og yhrdr, only Dudke et al. (1971) report chemical analyses of mirex in the water. Their study reported effects on two crayfish species exposed to

### mirex by three techniques. First, field

-collected crayfish were exposed to several sublethal concentrations of technical grade 

### mirex solutions €or various periods of time; second, crayfish were exposed to 

### mirex leached from bait (0.3 percent active ingredient) ; and third, the crayfish were fed mirex bait. Procambarus uandingi juveniles were exposed to 1 or 5 ug/L for 6 

### to 144 hours, transferred tocleanwater and observed for 10 days. After 5 days in clean water, 95 percent of the animals exposed to 1 ug/L for 14 hours were dead. Exposure to 5 ug/L for 6, 24, and 58 hours resulted in 26, 50, and 98percent mortality 10 days after transfer toclean water. Crayfish, Procambarus 

# 0’..



# - hayi, were exposed to 0.1 and 0.5 ug/L for 48 hours. Four days after transfer 

### to clean water, 65 percent of the animals exposed to 0.1 ug/L were dead. At the 0.5 ug/L concentration, 71 percent of the animals were dead after 4 days in clean water. Tissue residue accumulations (wetweight basis) ranged from 940- 

### to 27,210

-fold above water concentrations. In leached bait experiments, 10 bait particles were placed in 2 liters of water but isolated 

### from 20 juvenile crayfish. Thirty percent 

### of the crayfish were dead in 4 days and 95percent were dead in 7 days. Water analysis indicated mirex concentrations of 0.86 ug/~.In feeding Qxperiments, 108 crayfish each were fed one bait particle. Mortality was noticed on the first day after feeding,

j8 and by the sixth day 77 percent were dead. In another experiment, all crayfish were dead 4 days after having been fed 2 bait particles each. From this report it is obvious that mirex is extremely toxic to these species of crayfish. Mortality and accumulation increases with time of exposure 

### to the insecticide. Concentrations as low as 0.1 ug/L 

### or the ingestion of one particle resulted in death. $

Research 

### to determine effects of mirex on fish has been concentrated on species which have economic and sport fishery importance. Hyde et al. (1974) applied mirex bait (0.3 percent mirex) at the standard rate (1.4 kg/ha) in four ponds containing channel catfish, Ictalurus punctatus. Three applications were made over an 8~011th period with the first application 8 days after fingerling (averageweight 18.4 g) catfishwere placed in the ponds. Fish were collected at each subsequent application(approximately 4

-month intervals). Two and one half months after the final application, the ponds 

### were drained, 

### all fish 

### were measured and weighed, and thepercent survivalwas calculated. Mirex residues 

### in the fish at termination of the experiment ranged from 0.015 ug/g (ppm) in the filletto0.255 uq/g 

### inthe fat. 

# 0

In another study, Van Valin et al. (1988) exposed bluegills,


## - Lepomis macrochirus, and the goldfish, Carassius auratus, to 

### mirex by feedinga mirex

-treated diet (1, 3, and 5 mg 

### mirex per kg body weight) or by treating holding ponds with

### mirex bait (1.3, 100, and 1000 ug/L computed water concentration). They reported no mortality 

### or tissue pathology forthe bluegills; however, after 58 days of exposure, gillbreakdown 

### ingoldfish
was found in the 100 and 1000 ug/L contact exposure ponds, and kidney breakdown 

### was occurring in the 1000 ug/L ponds. Mortality in the feeding experiments was not related to the 

### level of exposure, although growth of the bluegills fed 5 ug/L 

### mirex was reduced. In laboratory and field test systems, reported concentrations of 

### mirex usually arebetween 0.5 and 1.0 ug/L (Van Valin et al. 1968: Ludke et al. 1971). Although mirex seldom 

### is found above 1 ug/L in the aquatic environment, several field studies have shown that the insecticide is accumulated through the food chain. Borthwick et al. (1973) reported the accumulation of mirex in South Carolina estuaries. Their datarevealedthat

### mirex was transported from treated land and marsh to the estuary animals and that accumulation, especially in predators, occurred. In the test area, water supplies consistently were less than 0.01 ug/L.Residues infishvaried from non- detectable percent of the samples containing 

### and the percent of samples containing 

### mirex residues. to 0.8 ug/g with 15 The amount of 

### mirex increased 

### at higher trophic levels. Fifty

- four percent of the raccoons sampled contained mirex residues up to 4.4 ug/g and 78 percent of the birds contained residues up to 17 ug/g. Navgi and de laCruz (1973) reported average residues formolluscs (0.15 ug/g), fish (0.26 ug/g), insects (0.29 ug/g), crustaceans (0.44 ug/g) and annelids (0.63 ug/g. They also reported that mirex was found in


### areas 

### not treated with 

### mirex which suggests movement of the pesticide in the environment. Wolfe and Norment (1973) sampled
an area for one year following an aerial application of mirex bait (2.1 g mirex/ha). Crayfish residues ranged from 0.04 to 0.16 ug/g. Fish residues were about 2 to20 timesgreaterthan the

### controls and averaged from 0.01 to0.78 ug/g. Kaiser (1974), reported the presence of rnirex 

### in fish from the Bay of Quinte, Lake Ontario, Canada. Concentrations range from 0.02 ug/g in the gonads of the northern long nose gar, Lepistosteus osseus, to 0.05 ug/g 

### in the areal fin of the northern pike, 

## ___- Esox lucius. Mirex has never been registered for use in Canada. 

### Mirex does not appear to be greatly toxic to birds, with LCSO’s 

### for the young of four species ranging from 547 to greater than 1667 ug/g (Heath et al. 1972). Long

-term dietary dosages caused no adverseeffect at3 ug/gwithmallards and13ug/gwith pheasants (Heath and Spann, 1973). However, it has been reported (Stoke et al. 1978) that the persistence of mirex in bird tissue exceeds that of 

### allorganochlorine compounds tested except forDDE. Delayed mortality occurred among birds subjected 

### to doses above expected environmental concentration. A summary examination of the data available at this 

### time shows a mosaic of effects. Crayfish and channel catfish survival 

### is affected by mirex in the water or by ingestion of the bait particles. Bioaccumulation 

### is well established for a wide variety of organisms but the effect of this bioaccumulation on the aquatic ecosystem is unknown. There is evidence that mirex is very persistent in bird tissue. Considering the extreme toxicity and potential for bioaccumulation, every effort should be made to keep mirex bait particles out of water containing aquatic organisms and water concentrations should not exceed 0.001 ug/L mirex. This value is based upon an application factor of 0.01 applied to the lowest levels at which effects on crayfish have been observed. Data upon which to base a marine criterion involve several estuarine and marine crustaceans. A concentration of 0.1 ug/L technical grade mirex 

### in flowing seawater was lethal to juvenile pink shrimp, Penaeus durorarum, in a 3

-week exposure (Lowe et al. 1971). In static tests with larval stages (megalopal) of the mud crab, Rhithropanopeus harrisii, reduced survival was observed in 0.1 ug/L mirex (Bookhout et al. 1972). 

### In three of four 28

-day seasonal f low

-through experiments, Tagatz et al. (1975) found reduced survival of



### __- Callinectes sapidus, Penaeus durorarum, and grass shrimp, 

## -_-_--_--_ Palaemonetes 

# ~us&, at levels of 0.12 ug/L in summer, 0.06 ug/L in fall and 0.09 ug/L in winter. Since two reports, Lowe et al. (1971) and Bookhout et al. - (1972), stated that effects of mirex on estuarine and marinecrustaceans were observed only after considerable time had elapsed, it seems reasonable that length of exposure is an important consideration 

### €or this chemical. This may not be the
case in fresh water since the crayfishwere affectedwithin 48 hours. Therefore, a 3- to 4

- week exposure might be considered 88acute81 and by applying an application factor of 0.01 to a reasonable average of toxic

-effect levels as summarized above, a recommended marine criterion of 0.001 ug/L results.

(QUALITY CRITERIA FOR WATER, JULY 1976) PB-263943 SEE APPENDIX C FOR METHODOLOGYN?QrnLENE


### Aquatic Life
The 

### available data for naphthalene indicate that acute and chronic toxicity to 

### freshwater aquatic life occurs at concentrations as low as 2,300 

### and 620

### ug/L, respectively,and would occur at lower concentrations among species that are more sensitive than those tested. The available data for naphthalene indicate that acute toxicity to saltwater aquatic 1 ife occurs at concentrationsas 

### low as 2,350 

### ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No data are available concerning the chronic toxicity of naphthalene to sensitive saltwater aquatic life. I



### Human Health Using the present guidelines, a satisfactory criterion cannot be derived at this time because of insufficient available data for naphthalene.
(45 F.R. 79318, 

### November 28, 1980) 

### SEE APPENDIX B FOR 

### METHODOLOGYNICKEL
Aquatic Life FOI total recoverable nickel the criterion (in ug/L) to protect freshwater aquatic life as derived using the Guidelines is the numerical value given by e(0.76[1n(hardness)]+l.06) as a 24

-hour average, and the concentration (in ug/L) should not exceed the numerical value given by .(0.76[ln (hardness)]+4.02) at any time. For example, at hardnesses of 50, 100, and 200 mg/L
as CaC03 the criteria are 56, 96, and 160 ug/L, respectively, as 24

-hour averages, and the concentrations should not,exceed1,100, 1,800, and 3,100 ug/L, respectively, at any time. For total recoverable nickel the criterion to protect saltwater aquatic life as derived using the Guidelines is 7.1 ug/L as a 24

-hour average, and the concentration should not exceed 140 ug/L at any time. 

# 0

Human Health For the protection of human health from the toxic properties of nickel ingested through water and contaminated aquatic organisms, the ambient water criterion is determined to be 632 wl/L. For the protection of human health from the toxic properties of nickel ingested through contaminated aquatic organisms alone, the ambient water criterion is determined to be 4.77 W/L.

(45 F.R. 79318, November 28, 1980) 

# 0
SEE A PPEN 

### DIX B FOR METHODOLOGY

# 0 CRITERION: NITF?ATES/NITRITES

10 mg/L nitrate nitrogen (N) for

domestic water supply (health). INTRODUCTION: Two gases (molecular nitrogen and nitrous oxide) and five forms of nongaseous, combined nitrogen (amino and amide groups, ammonium, 

### nitrite, and nitrate) are important in the nitrogen cycle. The amino and amide groups are found in soil organic 

### matter and as constituents of plant and animal protein. The ammonium ion either 

### is released 

### from proteinaceous organic matter and 

### urea, or 

### is synthesized inindustrial processes involving atmospheric nitrogen fixation. The nitrite ion is formed from the nitrate 

### or the ammonium ions by certain microorganisms found in soil, water, sewage, and the digestive tract. The nitrate ion is formed by thecomplete oxidation of ammonium ionsby soilor 

### water microorganisms; 

### nitrite is 

### an intermediate product 

### of this 

### nitrification process. In oxygenated natural water systems 

### nitrite is rapidly oxidized to 

### nitrate. Growing plants 

### assimilate 

### nitrate or ammonium ions and convert them to protein. A process known as denitrification takes place when nitratecontaining soils become anaerobic and the conversion to 

### nitrite, molecular nitrogen, or nitrous oxide occurs. Ammonium ions may also be produced in 

### some circumstances. 

# 0

Among the major point sources of nitrogen entry intowater bodies are municipal and industrial wastewaters, septictanks, and feed lotdischarges. Diffuse sources of nitrogen include farm

-site fertilizer and animal wastes, lawn fertilizer, leachate 

# a

### from waste disposal in dumps 

### or sanitary landfills, atmospheric fallout, nitric oxide and nitrite discharges from automobile exhausts and other combustion processes, and losses from natural sources such as mineralization of soil organic matter (NAS, 1972). 

### Water reuse systems in some fish hatcheries employ a nitrification process for ammonia reduction; this may result in exposure of the hatchery fish to 

### elevated levels of nitrite (Russo et al. 1974). RATIONALE: 

### In quantities normally found in food 

### or feed, nitrates become toxic only under conditions in which they are, 

### or may be, reduced 

### to nitrites. Otherwise, at "reasonable" concentration nitrates are rapidly excreted in the urine. High intake of nitrates constitutes a hazard primarily 

### to warmblooded animals under conditions that are favorable to reduction 

### to nitrite. Under certain circumstances, nitrate canbe reduced 

### to nitrite in the gastrointestinal tract which then reaches the bloodstream and reacts directly with hemoglobin to produce methemoglobin, consequently impairing transport. I



### The reaction of nitrite with hemoglobin can be hazardous in infants under 3 

### months of age. Serious and occasionally fatal poisonings in infants have occurred following ingestion of untreated well waters shown to 

### contain nitrate at concentrations greater than 10 

### mg/L nitrate nitrogen (N) (NAS, 1974). 

### High nitrate concentrations frequently are found in shallow farm and rural community wells, often as the result of 

### inadequate protection from barnyard drainage 

### or from septic tanks (USPHS,1961; Stewart et al. 1967). Increased concentrations of nitrates also have been found 

### in streams from farm tile drainage in areas of intense fertilization and farm crop production (Harmesonet al. 1971). Approximately 2,000 cases of infant methemoglobinemia have been reported 

### in Europe and North America since 1945; 7 to 8 percent of the affected infants died (Walton, 1951; Sattelmacher, 1962). Many infants have drunk water in which the nitrate nitrogen content was greater than 10 mg/L without developing methemoglobinemia. Many pub1ic water supplies in the United States contain levels that routinely exceed this amount, but only one U.S. case of infant methemoglobinemia associated with 

### a public water supply has ever been reported (Virgil et al. 1965). The differences in susceptibility tomethemoglobinemia are not yet understood but appear to be related to a combination of factors including nitrate concentration, enteric bacteria, and the lower acidity characteristic of the digestive systems of baby mammals. Methemoglobinemia systems and other toxic effects were observed when high nitrate well waters containing pathogenic bacteria were fed 

### to laboratory mammals (Wolff et al. 1972). Conventional water treatment has no significant effect on nitrate removal 

### from water (NAS, 1974). Because of the potential risk of methemoglobinemia to bottlefed infants, and in view of the absence of substantiated physiological effects at nitrate concentrationsbelow 10mg/L nitrate nitrogen, this level is the criterion for domestic water supplies. Waters with nitrite nitrogen concentrations over 1 

# 0

~mg/L should not be used for infant feeding. Waters with a significant nitrite concentration usually would be heavily polluted and probably bacteriologically unacceptable. Westin (1974) determined that the respective 96-hOUr and 7- day LC50 values for chinook salmon, Oncorhynchus tshawytscha,


### were 1,310 and 1,080 mg/L nitrate nitrogen in fresh water and 990 and 900mg/L nitrate nitrogen 

### in 15 o/oo salinewater. For fingerling rainbow trout, Salmo qairdneri, the respective 96-hour and 7

-day LC50 values were 1,360 and 1,060 mg/L nitrate nitrogen in fresh water, and 1,050 and 900 mg/L nitrate nitrogen 

### in 15 o/oo saline water. Trama (1954)reported that the 96-hOUr LC50 for bluegills, Asomis 

## -- macrochirus ------I at 20°C was 2,000 mg/L nitrate nitrogen (sodium nitrate) and 420 mg/L nitrate nitrogen

(potassium nitrate). Knepp and Arkin (1973) observed that largemouth bass, Micropterus salmoides, and channel catfish, Ictalurus punctatus, could be maintained at concentrations up 

### to 400 mg/L nitrate (90 mg/L nitrate nitrogen) without significant effect upon their growth and feeding activities. The 96

-hour and 7

-day LC50 values for chinook salmon,

-___ Qncorhynchus tshawytscha, were found to be 0.9 and 0.7 mg/L nitrite nitrogen in fresh water (Westin, 1974). Smith and Williams (1974) tested the effects of nitrite nitrogen and observed that yearling rainbow trout, Salmo gairdneri, suffered a 55 percent mortality after 24 hours at 0.55 mg/L; fingerling rainbow trout suffered a 50percent mortality after 24 hours of exposure at 1.6 mg/L; and chinook salmon, Oncorhynchus tshawytscha, suffered a 40 percent mortality within 24 hours at0.5 mg/L. There were no mortalities among rainbow trout exposed to 0.15 mg/L 

### nitrite nitrogen for 48 hours. These data indicate that salmonids are more sensitivetonitritetoxicitythan are other fish species, e.g., minnows, 

# -_-- Phoxinus laevis that suffered a 50 percent mortality within 1.5 hours of exposure to 2,030 mg/L 

### nitrite nitrogen, but required 14days of exposure €or mortality to occur at 10mg/L (Klingler, 1957), and carp, Cyprinus 

### -- care,when raised 

### ina 

### water reuse 

### system, tolerated up 

### to 1.8 mg/L 

### nitrite nitrogen (Saeki, 1965). Gilbette, et al. (1952) observed that the critical range for creek chub, Semotilus 

# -atromaculatus, was 80 to 400 mg/L nitrite nitrogen. 

### Wallen et 

### al. (1957) reported a 24-hour LC50 of 1.6 mg/L nitrite nitrogen, 

### and 48- and 96

-hour LC50 values of 1.5 mg/L 

### nitrite nitrogen for mosquitofish, Gambusia affinis. McCoy (1972) tested the 

### nitrite susceptibility of 13 fish species and found that logperch, Percina 

# -- caprodes -_I were themost sensitive speciestested (mortalityat5 mg/L nitrite nitrogen 

### inless than 3 hours of exposure) whereas carp, 9prinus carpio, and black bullheads, 

### ---- Ictalurus

# ---- melas8 survived 40 mg/L nitrite nitrogen €or 

### a 48

-hour exposure period; the common white sucker, Catostomus --..-------I commersoni and the quillback, Carpiodes cyprinus, survived 100mg/L for 48 and 36 hours, respectively. 

# e

Russo et al. (1974) performed flow

-through nitrite bioassays inhard water (hardness= 199mg/L CaC03; alkalinity= 176 mg/L CaCQ3; pH = 7.9) on rainbow trout, Salmo gairdneri, of four different 

### sizes, and obtained 96-hOUr LC50 

### values ranging from 0.19 to 0.39 mg/L nitritenitrogen. Duplicate bioassays on 12- gram rainbow trout were continued long enough for their toxicitycurves to level off, and asymptotic LC50 concentrations of 0.14 and 0.15 mg/L were reached in8 days; on day 19, additional mortalities occurred. For 2

-gram rainbow trout, the minimum tested level of 

### nitritenitrogen atwhich no mortalities were observed after 10 days was 0.14 mg/L; for the 235

-gram trout, the minimum level with no mortality after 10 days was 0.06 mg/L. It is concluded that (1)levels of nitrate nitrogen at or below 90 mg/L would have no adverse effects on warmwater fish (Knepp and Arkin, 1973); (2) nitritenitrogen atorbelow 5 mg/L should be protective of most warmwater fish (McCoy, 1972); and (3) 

### nitrite nitrogen at or below 0.06 mg/L should be protective of salmonid fishes (Russo et al. 1974; Russo and Thurston, 1975). These levels either are not known tooccur orwould be unlikely to occur in natural surface waters. I Recognizing that concentrations of nitrate ornitritethat would exhibit toxic effects on warm- or coldwater fish could rarely occur in nature, restrictive criteria are not recommended.

(QUALITY CRITERIA FOR WATER, JULY 1976) PB

-263943 SEE APPENDIX C FOR METHODOLOGYNITROBENZENE CRITERIA: Aquatic Life The available data for nitrobenzene indicate that acute toxicity to freshwater aquatic life occurs at concentrations as low as 27,000 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No definitive data are available concerning the chronic toxicity of nitrobenzene to sensitive freshwater aquatic life. The available data for nitrobenzene indicate that acute toxicity 

### to saltwater aquatic life occurs at concentrations as low as 6,680 ug/L and would occur at lower concentrations among species thaf;are more sensitive than those tested. No definitive data are available concerning the chronic toxicity 

### of nitrobenzene to sensitive saltwater aquatic life. Human Health For comparison purposes, two approaches were used to derive criterion levels for nitrobenzene. Based on available toxicity data, to protect public health the derived level is 19.8 mg/L. using available organoleptic data, to control undesirable taste and odor qualities of ambient water the estimated level is 30 ug/L. It should be recognized that organoleptic data have limitations as a basis for establishing a water quality criterion, and have no demonstrated relationship to potential adverse human health effects. (45 F.R. 79318, November 28, 1980)
NOTE: The U.S. EPA is currently developing Acceptable Daily Intake (ADI) or Verified Reference Dose (RID)values for Agency

-wide use for this chemical. The new value should SEE APPENDIX B FOR METHODOLOGYbe substituted when it becomes available. The January, 1986, draft Verified Reference Dose document cites an RfD of .0005 mg/kg/day for nitrobenzene.NITROPHENOLS CRITERIA: Aquatic Life The available data for nitrophenols indicate that acute toxicity to freshwater aquatic life occurs at concentrations as low as 230 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No data are available concerning the chronic toxicity of nitrophenols to sensitive freshwater aquatic life but toxicity to one species of algae occurs at concentrations as low as 150 ug/L. The available data for nitrophenols indicate that acute toxicity to saltwater aquatic life occurs at concentrationsas low 

### as 4,850 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No data are available concerning the chronic toxicity of nitrophenols to sensitive saltwater aquatic life. 1



### Human Health Because 

### of insufficient available data for mono- and trinitrophenols, satisfactory criteria cannot be derived at this time, using the present guidelines. For the protection of human health from the toxic properties of dinitrophenols and 2,4-dinitro-o-cresol ingested through water and contaminated aquatic organisms, the ambient water criteria are determined to be 70 ug/L and 13.4 ug/L, respectively. For the protection of human health from the toxic properties of dinitrophenols and 2,4-dinitro-o-cresol ingested through contaminated aquatic organisms alone, the ambient water criteria 

## -are determined to be 14.3 mg/L and 765 ug/L, respectively.

(45 

### F.R. 79318, November 28, 1980) SEE APPENDIX 

### B FOR METHODOLOGYNITROSAMINES


### Aquatic Life The available data for nitrosamines indicate that acute toxicity to freshwater aquatic life occurs at concentrations as low as 5,850 

### ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No data are available concerning the chronic toxicity of nitrosamines to sensitive freshwater aquatic life. The available data for nitrosamines indicate that acute toxicity to saltwater aquatic life occurs at concentrationsas low as 3,300,000 

### ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No 

### data
are available concerning the chronic toxicity of nitrosamines to sensitive saltwater aquatic life.
Human Health 

### For the maximum protection of human health from the potential carcinogenic effects of exposure to N

-nitrosodiethylamine and all other nitrosamines except those listed below, through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentrations should be zero, based 

### on the non threshold assumption for this chemical. However, zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer risk over the lifetime are estimated at lo"*, 

### and 1OpcPs 

### The corresponding recommended criteria are 8.0 

### ng/L, 0.8 

### ng/L, and 0.08 

### ng/L, respectively. 

### If these estimates are made for L 

# 0consumption of aquatic organisms only, excluding consumption of water, the levels are 12,400 ng/L, 1,240 ng/L, and 124 ng/L, respectively. For the maximum protection of human health from the potential carcinoqenic effects of exposure to N

-nitrosodimethylamine through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentrations should be zero, based on the nonthreshold assumption for this chemical. However, zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of
cancer risk over the lifetime are estimated at 10- 6, and The corresponding recommended criteria are 14 ng/L, 1.4 ng/L, and 0.14 ng/L, respectively. If these estimates
are made for consumption of aquatic organisms only, excluding consumption 

### of water, the levels are 160,000ng/L, 16,000ng/L, and 1,600 ng/L, respectively. For the maximum protection of human health from the potential carcinogenic effects of exposure to N

-nitrosodibutylamine through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentrations should be zero, based on the nonthreshold assumption for this chemical. However, zero level may not be attainable at the present time. Therefore, the levelswhich may result in incremental increase of cancer risk over the lifetime are estimated at 10- 6, and The corresponding recommended criteria are 64 ng/L, 6.4 ng/L, and 0.64 ng/L, respectively. If these estimates are made for consumption of aquatic organisms only, excluding consumption of water, the levels are 5,868 ng/L, 587ng/L, and 58.7 ng/L, respectively.



# 0 For the maximum protection o'f human health from the potential carcinogenic effects of exposure to N

-nitrosopyrrolidine through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentrations should be zero based
on the nonthreshold assumption for this chemical. However, zero level may not be attainable at the present time. Therefore, the levelswhich may result in incremental increase of cancer risk



### . over the lifetime are estimated at and The corresponding recommended criteria are 160 ng/L, 16 ng/L, and 1.6 ng/L, respectively. If these estimates are made for consumption of aquatic organisms only, excluding consumption of water, the levels are 919,000 ng/L, 91,900 ng/L, and 9,190 ng/L, respectively. For the maximum protection of human health from the potential carcinogenic effects of exposure to N

-nitrosodiphenylamine through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentrations should be zero, based 

### on the non threshold assumption for this chemical. However, zero level

### may not be attainable 

### at the present time. Therefore, the levels which may result 

### in incremental increase of cancer 

### risk over the lifetime are estimated at 10-5, The corresponding recommended criteria are 49,000 ng/L, 4,900 ng/L, and 490 ngfL, respectively. If these estimates are made for consumption of aquatic organisms only, excluding consumption of water, the levels are 161,000 ng/L, 16,100 ng/L, and 1,610 ng/L, respectively. and

L,(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYOIL AND GREASE

- -

For domestic water supply: Virtually free from oil and grease, particularly from the tastes and odors that emanate from petroleum products. For aquatic life: (1) 0.01 of the lowest continuous flow 96

-hour LC50 to several important freshwater and marine species, each having a demonstrated high susceptibility to oils and petrochemicals. (2) Levels of oils or petrochemicals in the sediment which cause deleterious effects to the biota should not be allowed. (3) Surface waters shall be virtually free from floating nonpetroleum oils of vegetable or animal origin, aswell as petroleum

-derived oils. 1 INTRODUCTION: It has been estimated that between 5 and 10 million metric tons 

### of oil enter the marine environment annually (Blumer, 1970). A major difficulty encountered in the setting of criteria for 

### oil and grease is that these are not definitive chemical categories, but include thousands of organic compounds with varying physical, chemical, and toxicological properties. They may be volatile or nonvolatile, soluble or insoluble,persistent
or easily degraded. RATIONALE: Field and laboratory evidence have demonstrated both acute lethal toxicity and long

-term sublethal toxicity of oils to aquatic organisms. Events such as the Tampico Maru wreck of 1957 in Baja, California, (Diaz

-Piferrer,1962),and the No. 2 fuel oil spill in West Falmouth, Massachusetts, in 1969 ..I(Hampson and Sanders, 1969), both of which caused immediate death to

### a wide variety of organisms, are illustrativeof the lethal toxicity that may be attributed to oil pollution. Similarly, a gasoline spill in South Dakota in November 1969 (Bugbee and Walter, 1973) 

### was reported to have caused immediate death to the majority of freshwater invertebrates and 2,500 fish, 30 percent of which were native species of trout. Because of the wide range of compounds included in the category of oil, it is impossible to establish meaningful 96

-hour LC50 values for oil and grease without specifying the product involved. However, as the data in Table 6 show, the most susceptible category of organisms, the marine larvae, appear 

### tobe intolerant of petroleum pollutants, particularly the water soluble compounds, at concentrations as low as 0.1 mg/L. The long

-term sublethal effects of oilpollution refer to interferences with cellular and physiological processes such as feeding and reproduction and do not lead toimmediatedeath of the organism. Disruption of such behavior apparently can result from petroleum product concentrations as low as 10to 100ug/L (see Table 7). Table 7 summarizes some of the sublethal toxicities for various petroleum pollutants and aquatic species. In addition to sublethal effects reported at the 10 to 100 ug/L level, it has been shown that petroleum products can harm aquatic life at concentrations as low as 1ug/L (Jacobson and Boylan, 1973). Bioaccumulation of petroleum products presents two especially important public health problems: (1)the tainting of edible,aquatic species, and (2) the possibility of edible marine organisms incorporating the high boiling, carcinogenic polycyclic aromatics in their tissues. Nelson

-Smith (1971) reported that 0.01 mg/L of crude oil caused tainting in oysters. Moore et al. (1973) reported that concentrations as low as 1 to 10 ug/L could lead to tainting within very short periods of time. It has been shown that chemicals responsible for cancer in animals and man (such as 3,4-benzopyrene)occur in crude oil (Blumer,1970). It also has been shown that marine organisms are capable of incorporating potentially carcinogenic compounds into their body fat where the compounds remain unchanged (Blumer, 1970). Oil pollutants may also be incorporated into sediments. There is evidence that once this occurs in the sediments below the aerobic surface layer, petroleum oil can remain unchanged and toxic for long periods, since its rate of bacterial degradation is slow. For example,Blumer (1970)reported that 

### No. 2 fuel oil incorporated into the sediments after the West Falmouth spill persisted for over a year, and even began spreading in the form of oil

-laden sediments to more distant areas that had remained unpolluted immediately after the spill. The persistence of unweathered oil within the sediment could have a long

-term effect
on the structure of the benthic community or cause the demise of specific sensitive important species. Moore et al. (1973) reported concentrations of 5 mg/L for the carcinogen 3, 4- benzopyrene in marine sediments. Mironov (1967) reported that 0-01mg/L oil produced deformed and inactive flatfish larvae. Mironov (1970) also reported inhibition or delay of cellular division in algae by oil -,concentrations of to 10-1 mg/L. Jacobson and Boylan (1973) reported a reduction in the chemotactic perception of food by the snail, Nassarius -- obsoletus at kerosene concentrations of 0.001 to 0.004 mg/L. Bellen et al. (1972) reported decreased survival and fecundity in worms at concentrations of 0.01 to 10 mg/L of detergent. Because of the great variability 

### in the toxic properties of oil, it is difficult to establish a numerical criterionwhich would be applicable to all t-jpes of oil. Thus, an application factor of 0.01 of the 96

-hour LC50 as determined by using continuous flow with a sensitive resident species should be employed for individual petrochemical components. There is a paucity of toxicological data on the ingestion of the components of refinery wastewaters by humans or by test animals. It is apparent that any tolerable health concentrations for petroleum

-derived substances far exceed the limits of taste and odor. Since petroleum derivatives become organoleptically objectionable at concentrations far below the human chronic toxicity, 

### it appears that hazards to humans will not arise from drinking oil

-polluted waters (Johns Hopkins Univ., 1956; Mckee and Wolf, 1963). Oils of animal or vegetable origin generally are nontoxic to humans and aquatic life. In view of the problem of petroleum oil incorporation in sediments, its persistence and chronic toxic potential, and the present lack of sufficient toxicity data to support specific criteria, concentrations of oils in sediments should not approach levels that cause deleterious effects to important species or thebottom community as a whole. Petroleum and nonpetroleum oils share some similar physical and chemical properties. Because they share common properties, they may cause similar harmful effects in the aquatic environment by forming a sheen, film, ordiscoloration on the surface of the water. Likepetroleum oils, nonpetroleum oils may occur at four levels of the aquatic environment: (a) floating
on the surface, (b) emulsified in the water column, (c) solubilized, and (d) settled on the bottom as a sludge. Analogous tothe greaseballs from vegetable oil and animal fatsare the tarballs of petroleum origin which have been found in the marine environment or washed ashore on beaches. Oils of any kind can cause (a) drowning of waterfowl because of loss of buoyancy, exposure because of loss of insulating capacity of feathers, and starvation and vulnerability to 

# 0
predators because of lack of mobility; (b) lethal effects on fish by coating epithelial surfaces of gills, thus preventing respiration; 

### (c) potential fishkills resulting from biochemical oxygen demand: (d) asphyxiation of benthic life forms when floating masses become engaged with surface debris and settle on the bottom: and (e) adverse aesthetic effects of fouled shorelines and beaches. These and other effects have been documented in the U.S. Department of Health, Education and Welfare report on Oil Spills Affecting the Minnesota and Mississippi Rivers and the 1975 Proceedings of the Joint Conference on Prevention and Control of Oil Spills. 

# e Oils of animal or vegetable origin generally are chemically

_, nontoxic to humans or aquatic life; however, floating sheens ofsuch oils result in deleterious environmental effects described in this criterion. Thus, it 

### is recommended that surface waters shall be virtually free from floating nonpetroleum oils of vegetable or animal origin. This same recommendation applies to floating oils of petroleum origin since they too may produce similar effects.

(QUALITY CRITERIA FOR WATER, JULY 1976) PB-263943 SEE APPENDIX C FOR METHODOLOGYDISSOLVED OXYGEN 

# 0 NATIONAL CRITERIA: The national criteria for ambient dissolved oxygen concentrations for the protection of freshwater aquatic life are presented in Table 1. The criteria are derived from the production impairment estimates which are based primarily upon growth data and information on temperature, disease, and pollutant stresses. The average dissolved oxygen concentrations selected are values 0.5 mg/L above the slight production impairment values and represent values between no production impairment and slight production impairment. Each criterionmay thusbe viewed as an estimate of the threshold concentration below which detrimental effects are expected. Criteria for coldwater fish are intended 

### to apply to waters containing a population of one or more species in the family Salmonidae {Bailey et al., 1970) or to waters containing other coldwater or coolwater fish deemed by the user to be closer to salmonids in sensitivity than to most warmwater species. Although the acute lethal limit €or salmonids is at orbelow 3 mg/L, the coldwater minimum has been established at 4 mg/L because 

### a significant proportion of the insect species common to salmonid habitats are less tolerant of acute exposures to low dissolved oxygen than are salmonids. Some coolwater species may require more protection than that afforded by the other life stage criteria for warmwater fish and it may be desirable to protect sensitive coolwater species with the coldwater criteria. Many states have more stringent dissolved oxygen standards for cooler waters, waters that contain either ._ 

# asalmonids, nonsalmonid coolwater fish, or the sensitive centrachid, the smallmouth bas5 The warmwater criteria are necessary to protect early life stages of warmwater fish as sensitive as
as channel catfish and 

### to protect other life stages of fish as sensitive as largemouth bass. Criteria for early life stages are intended to apply only where and when these stages occur. These criteria represent dissolved oxygen concentrations which 

### EPA believes provide a reasonable and adequate degree of protection for freshwater aquatic life. The criteria do not represent assured no

-effect levels. However, because the criteria represent worst case conditions

(i.e. for wasteload allocation and waste treatment plant design)

~ conditions will be better than the criteria nearly all of the time at most sites. In situations where criteria conditions are just maintained for considerableperiods the proposed criteria represent some risk of production impairment. This impairment would depend on innumerable other factors. If slight production impairment 

### or a small but undefinable risk of moderate impairment is unacceptable, than one should use the "no production impairment" values given in the document as means and the "slight production impairment') values as minima. The tablewhich presents these concentrations is reproduced here as table 2. The criteria do representdissolved oxygen concentrations believed to protect the more sensitive populations of organisms against potentially damaging production impairment. The dissolved oxygen concentrations in the criteria are intended to be protective at typically high seasonal environmental temperatures for the appropriate taxonomic and life stage classi-Table 1. Water quality criteria for ambient dissolved oxygen 

# 0 concentration.

Coldwater Criteria Warmwater Criteria

Stages

# Ue Stages Stages Stages Other Life Early kife Other Life

30 Day Mean NA3 6.5 NA 5.5

7 Day Mean 9.5 (6.5) NA 6.0 NA 7 Day Mean NA Minimum 5.0 NA 4.0
1 Day 8.0 (5.0) 4.0 5.0 3.0 Minimum 415

These are water column concentrations recommended to achieve the required intergravel dissolved oxygen concentrations shown in parentheses. The 3 mg/L differential is discussed in the criteria document. For species that have early life stages exposed directly to the water column, the figures in parentheses apply. Includes all embryonic and larval stages and all juvenile forms to 30

-days following hatching. 

# 0

3 NA (not applicable). For highly manipulatable discharges, further restrictions apply (see page 37) All minima should be considered as instantaneous concentrations to be achieved at all times. fications, temperatures which are often higher than those used in the research from which the criteria were generated, especially for other than early life stages. Where natural conditions alone create dissolved oxygen concentrations less than 110 percent of the applicable criteria
means or minima or both, the minimum acceptable concentration is90 percent of the natural concentration. These values are similar to those presented graphically by Doudoroff and Shumway (1970) and those calculated from Water Quality Criteria 1972 (NAS/NAE, 1973). Absolutely no anthropogenic dissolved oxygen depression in the potentially lethal area below the 1

-day minima should be allowed unless special care is taken to ascertain the tolerance of resident species to low dissolved oxygen. .If daily cycles of dissolved oxygen are essentially sinusoidal, a reasonable daily average is calculated from the day's high and low dissolved oxygen values. A time

-weighted average may be required if the dissolved oxygen cycles are decidedly non-sinusoidal. Determining the magnitude of daily dissolved oxygen cycles requires at least two appropriately timed measurements daily, and characterizing the shape of the cycle requires several more appropriately spaced measurements. Once a series of daily mean dissolved oxygen concentrations
are calculated, an average of these daily means can be calculated (Table 3). For embryonic, larval, and early life stages, the averagingperiod should not exceed 7 days. This short time is needed to adequately protect these often short duration, most sensitive life stages. Other life stages can probably be adequately protected by 30

-day averages. Regardless of the averaging period, the average should be considered a moving average rather than a calendar

-week or calendar

-month average.Table 2. Dissolved Oxygen Concentrations (mg/L) Versus



# 0 Quantitative Level of Effect.

1. Salmonid Waters
a. Embryo and Larval Stages No Production Impairment = 11* (8) Slight Production Impairment = 9* (6) Moderate Production Impairment = 8* (5) Severe Production Impairment = 7* (4) Limit to Avoid Acute Mortality = 6* (3) (*Note: These are water column concentrations recommended to achieve the required intergravel dissolved oxygen concentrations shown 

### in parentheses. The 3 mg/L difference is discussed in the criteria document.) b. Other Life Stages No Production Impairment =8 light Production Impairment =6 Moderate Production Impairment = 5 Severe Production Impairment = 4 Limit to Avoid Acute Mortality = 3 2. Nonsalmonid Waters 

### a. Early Life Stages No Production Impairment = 6.5 Slight Production Impairment = 5.5 Moderate Production Impairment = 5 Severe Production Impairment = 4,5 Limit to Avoid Acute Mortality = 4 b. Other Life Stages No Production Impairment =6 Slight Production Impairment = 5 Moderate Production Impairment = 4 Severe Production Impairment = 3.5 Limit to Avoid Acute Mortality = 3 3. Invertebrates No Production Impairment =8 Some Production Impairment =5 Acute Mortality Limit =4Table 3. Sample calculations for determining daily means and 7-day mean dissolved oxygen concentrations (30-day averages are calculated in a similar fashion using 30 days data). Dissolved Oxygen (mg/L)

Day Daily 

### Max. Daily Min. Daily Mean 9.0 7.0 10.0 7.0 11.0 8.0 12.

## oa 8.0 10.0 8.0 11.0 90 12.03 10.0 8.0 8.5 9.5 9.0 10.0 1Q.5c

9.5b

57.0 65.0 1

-day Minimum 7.0 ?-day Mean Minimum 8.1 ?-day Mean 9.3

a Above air saturation concentration (assumed to be 11.0 mg/L for this example). b (11.0 -b 8.0)2.
c (11 0 +10.0)2.
The criteria have been established on the basis that the maximum dissolved oxygen value actually used in calculating any daily mean should not exceed the air saturation value. This consideration is based primarily on analysis of studies of cycling dissolved oxygen and the growth of largemouth bass

(Stewart et al., 1967), which indicated that high dissolved oxygen levels (> 6 mg/L) had no beneficial effect on growth. During periodic cycles of dissolved oxygen concentrations, minima lower than acceptable constant exposure levels are tolerable 

### so long as:1. the average concentration attained meets or exceeds the
2. the average dissolved oxygen concentration is calculated as
3. criterion;
recommended in Table 3; and the minima are not unduly stressful and clearly are not lethal. A daily minimum has been included to make certain that no acute mortality of sensitive species occurs as a result of lack of oxygen. Because repeated exposure to dissolved oxygen concentrations at or near the acute lethal thresholdwill be stressful and because stress can indirectly produce mortality or other adverse effects (e-g., through disease), the criteria are designed to prevent significant episodes of continuous or regularly recurring exposures 

### to dissolved oxygen concentrations at or near the lethal threshold. This protection has been achieved by setting the daily minimum for early life stages at the subacute lethality threshold, by the use 

### of a 7

-day averaging period for early life stages, by stipulating 

### a 7

-day mean minimum value for other life stages, and by recommending additional limits for manipulatable discharges. The previous EPA criterion for dissolved oxygen published in Quality Criteria for Water (USEPA, 1976) 

### was a minimum of 5 mg/L (usually applied as a 7410) which 

### is similar to the current criterion minimum except for other life stages of warmwater fish which now allows a criteria 

### are similar 

### of the Federal Water 7

-day mean minimum of 4 mg/L. The new to those contained in the 1968 "Green Book" Pollution Control Federation (FWPCA, 1968).A. The Criteria 

### and Monitoring and Design Conditions The acceptable mean concentrations should be attained most of the time,but some deviation below these values would probably not cause significant harm. Deviations below the mean will probably be serially correlated and hence apt to occur on consecutive days. The significance of deviations below the mean will depend on whether they occur continuously or in daily cycles, the former being more adverse than the latter. Current knowledge regarding such deviations is limited primarily to laboratory growth experiments and by extrapolation to other activityrelated phenomena. Under conditions where large daily cycles of dissolved oxygen occur, it is possible to meet the criteria mean values and consistently violate the mean minimum criteria. Under these conditions the mean minimum criteria will clearly be the limiting regulation unless alternatives such as nutrient control can dampen the daily cycles. The significance of conditions which fail to meet the recommended dissolved oxygen criteria depend largely upon five factors: (1) the duration of the event; (2) the magnitude of the dissolved oxygen depression; (3) the frequency of recurrence; (4) theproportional area of the site failing 

### to meet the criteria, and (5) the biological significanceof the site where the event
occurs. Evaluation of an event's significance must be largely
case- and site

-specific. Common sense would dictate that the magnitude of the depression would be the singlemost important factor in general, especially if the acute value is violated. Alogical extension of these considerations is that the event must be considered in the context of the level of resolution of the monitoring or modeling effort. Evaluating the extent, duration, and magnitude of an event must be a function 

### of the spatial and temporal frequency of the data. Thus, a single deviation below the criterion takes on considerably less significance where continuous monitoring occurs than where sampling 

### is comprised 

### of once-a-week grab samples. This is 

### so because based on continuous monitoring the event 

### is provably small, but with the much less frequent sampling the event is not provably small and 

### can be considerably worse than indicated by the sample. The frequency of recurrence 

### is of considerable interest to those modeling dissolved oxygen concentrations because the return period, or period between recurrences, is a primary modeling consideration contingent upon probabilities of receiving water volumes, waste loads, temperatures, etc. It should be apparent that return period cannot be isolated from the other four factors discussed above. Ultimately, the question 

### of return period may be decided on a site

-specific basis taking into account the other factors (duration, magnitude, areal extent, and biological significance) mentioned above. Future studies of temporal patterns of dissolved oxygen concentrations, both within and between years, must be conducted to provide a better basis for selection of the appropriate return period. In conducting wasteload a1location and treatment plant design computations, the choice of temperature 

### in the models will be important. Probably the best option would be to use temperatures consistent with those expected in the receiving water over thecritical dissolved oxygen period for the biota. B. The Criteria and Manipulatable Discharges If daily minimum DOs are perfectly serially correlated, i.e, if the annual lowest daily minimum dissolved oxygen concentration is adjacent in timeto the next lower daily

### minimum dissolved oxygen concentration and one of these two minima is adjacent to the third lowest daily minimum dissolved oxygen concentration, etc., then in order to meet the 7

-day mean minimum criterion it is unlikely that there willbe more than three or four consecutive daily minimum values below the acceptable 7

-day mean minimum. Unless the dissolved oxygen pattern is extremely erratic, it is also unlikely that the lowest dissolved oxygen concentration will be appreciably below the acceptable 7

-day mean minimum orthatdailyminimum values below the 7

-day mean minimum willoccur inmore than one ortwo weeks each year. For some discharges, the distribution of dissolved oxygen concentrations can be manipulated tovarying degrees. Applying the daily minimum to manipulatable discharges would allow repeated weekly cycles of minimum acutely acceptable dissolved oxygen values, a condition of unacceptable stress and possible adverse biological effect. For this reason, the application of the one day minimum criteriontomanipulatable discharges must limit either the frequency of occurrence of values below the acceptable 7

-day mean minimum ormust impose further limits on the extent of excursions below the 7

-day mean minimum. For such controlled discharges, it is recommended that the occurrence of dailyminima below the acceptable 7

-daymean Iminimum be limited to 3 weeks per year or that the acceptable
one-day minimum be increased to4.5 mg/L forcoldwater fishand 3.5 mg/L for warmwater fish, Such decisions could be sitespecific based upon the extent of control and serial correlation. 

# ePARATHION CRITERION: 0.04 ug/L for freshwater and marine aquatic life. RATIONALE: Acute static LC50 values of the organophosphorus pesticide, parathion, for freshwater fish have ranged generally from about 50 ug/L for 

### more sensiitive species such as bluegills, Lepomis macrochi=, toabout 2.5 mg/L for the more resistant species such as minnows (U.S. Environ. Prot. Agency, 1975). In flowing water exposures, Spacie (1975) obtained 96-hour LC50 values of 0.5 mg/L, 1.6 mg/L, and 1.76 mg/L f o r b l u e g i l l s , 

## _- Lepomis 

## ____ macrochirus, fathead minnows, 

## -- Pimep&ales promelas, and brook trout, Salvelinus _______I fontinalis respectively. Korn and Earnest (1974) found a 96-hOUr LC50 of 18 ug/L forjuvenile freshwater and estuarine striped bass, Morone saxatilis, in a flowing water system, I

Few chronic exposure data are available for aquatic organisms. Brown bullheads, fctalurus nebulosus, exposed to 30 ug/L parathion for 30 days exhibited tremors; at 60 ug/L they convulsed and were found to have developed a deformed vertebral column (Mount and Boyle, 1969). In a 23-mOnth exposure of bluegills, Spacie (1975) observed deformities (scoliosisand a characteristic protrusion in the throat region) 

### at 0.34 ug/L, but not at 0.16 ug/L. Tremors, convulsions, hypersensitivity, and hemorrhages also were evident at higher concentrations. Reproductive impairment and deformities were observed in fathead minnows exposed to 4.0 ug/L for 8 1/2 months.Development of brook trout, 

### S, fontinalis 

## -- embryos exposed to 32 ug/L was abnormal and mortalities associated with premature hatching were observed. Embryos at 10 ug/L appeared normal. No adverse effects on juveniles and adults was evident during 9 months' exposure to 7 ug/L. Inhibition of cholinesterase enzymes is the well

-established mode of physiological action of parathion and other organic phosphorus pesticides (Weiss, 1958). The degree of inhibition of brain acetylcholinesterase (AChE) activity has been the most frequently used measure of effect of these pesticides. Various studies (Weiss, 1958, 1959, 1961;Murphy et al., 1968; Gibson et al. 1969) have shown the degree of inhibition to be dependent upon toxicant concentration, length of exposure, and species sensitivity. The results of these studies have also indicated AChE inhibition ranging from 25 to 90

(1959) also showed that susceptibility of recovery of AChE activity following that death results from percent of normal. Weiss depended upon the extent prior exposure and that the recovery period for fish exposed to parathion was relatively long. In bluegills, AChE activity was only 50 percent recovered 30 days after exposure 

### to 1 mg/L for 6 to 7 hours (Weiss, 1961). Some of the other physiological effects observed to result from exposure of fish to parathion have been inhibition of spermatogenesis in guppies, 

### _______- Poecilia reticulata at 10 ug/L (Billard and deKinkelin, 1970), alternation of oxygen consumption rate in bluegills, Lepomis macrochirus, at 100 ug/L (Dowden, 1966), and liver enlargement associated with increased pesticide

-hydrolizing capability in mosquitofish, Gambusiaaffinis (Ludke, 1970). 

# 0 Parathion has been found acutely toxic to aquatic invertebrates at under 1 ug/L e.g., a 50

-hour LC50 of 0.8 ug/L for 

## - Daphnia maqgg; 48

-hour LC50 of 0.6 ug/L for 

### -- Daphnia 

## -- pulex; 

### --- 48

-hour LC50 of 0.37 for Simocephalus 

## ---_ 

## _____-_ serrulatus (a daphnid) (Sanders and Cope, 1966); a 5

-day LC50 of 0.93 ug/L for the larval stonefly, Acroneuria pacifica (Jensen and Gaufin, 1964); and a 96

-hour LC50 of 0.43 ug/L for the larval caddisfly

- HydroEsychc 

### --- 

## - -- californica 

## --------- (Gaufin et al. 1965). Mulla and Khasawinah (1969) obtained 

### a 24

-hour LC50 of 0.5 ug/L for 4th instar larvae of the midge 

## -- Tanypus 

## - qrodhausi. Spacie (1975) obtained 96

-hour LC5O's in flow

-through bioassays of 0.62 ug/L for Daphnia magna, 0.40 ug/L for the scud, Gammarus fasciatus and 31.0 ug/L for 4th instar of Chironomous tentans, a midge. Other invertebrates have been found acutely sensitive to parathion in concentrations of from 1 to 30 ug/L in water (U.S. Environ. Prot. Agency, 1975). Few longer exposures have been conducted. Jensen and Gaufin (1964) obtained 30

-day LC50's for Pteronarcys 

## - ----I-- californica and Acroneuria 

## ----_ pacifica 

## ---- of 2.2 and 0.44 ug/L, respectively. Spacie (1975) found the 3

-week LC50 for Daphnia mxna 

## - to be 0.14 ug/L. Statistically significant reproductive impairment occurred at concentrations above 0.08 ug/L. A 43

-day LC50 of 0.07 ug/L was reported for Gammarus fasciatus and a concentration of 0.04 ug/L produced significantly greater mortality than among controls. Limited information is available on persistence of parathion

~ in water. Eichelberger and Lichtenberg (1971)determined thehalf

-life in river water (pH 7.3 

## - 8.0) to be 1 week. Using AChE inhibitory capacity as the indicator, Weiss and Gakstatter (1964) found the half

-life of parathion or 

### its active breakdown products to be 40, 35, and 20 days 

### in ‘lnaturalllwaters having a pH of 5.1. 7.0, and 8.4, respectively. The possibility of breakdown resulting in compoundsmore toxic thanparathion was suggested by Burke and Ferguson (1969)who determined that the toxicity of this pesticide to mosquitofish 1 Gambusia ---_I affinis
was greater in static than in flowing water test systems. Sanders (1972), in 96

-hour bioassays with the scud, Gammarus 

## _-

-------I fasciatus and glass shrimp, Palaemonetes -_-I_- kadiakensis I also observed greater toxicity under static than in flow

-through conditions. 

# a Tissue accumulations of parathion by exposed aquatic organisms are not great and do not appear to be very persistent. Mount and Boyle (1969) observed concentrations in the blood of bullhead, 

## --------- Ictalurus melas -----I up to about 50 times water concentrations. Spacie (1975) found muscle concentrations in chronically exposed brook trout, 

## - S. ___--_I fontinalis to be several hundred times water concentrations; bluegills, 

### -- Lepomis 

## ---- macrochirus, had about 25 times water concentrations in their bodies. Leland (1968) demonstrated a biological half

-life of parathion in rainbow trout, Salmo Eirdneri1 exposed and then placed 

### in fresh water to be only 30 

### to 40 hours. It 

### is not expected that parathion residues in aquatic organisms exposed to the recommended criterion concentrations will be a hazard to
consumer organisms. 

# aWeiss and Gakstatter (1964)have shown that 15

-day continuous exposure to parathion (1.0 ug/L) can produce progressively greater 

### (i.e-, cumulative) 

### brain AChE inhibition in a fish species. After substantial inhibition by parathion exposure, it takes several weeks for brain AChE of exposed fishes to return to normal even though exposure is discontinued (Weiss, 1959, 1961). fishes by 46 percent or more has been associated with harmful effects in exposures to organophosphate pesticides for one life cycle (Eaton, 1970) and for short periods (Carter, 1971; Coppage and Duke, 1971; Coppage, 1972; Coppage and Matthews, 1974; Post and Leasure, 1974; Coppage et al. 1975). It has been shown that a concentration of 10 ug Inhibition of brain AChE of

parathion/L of flowing seawater kills 40 

### to 60 percent of the marine fishes &agodon 

## ---- ---------- rhomboides (pinfish) and Leostomus 

### -- xanthurus

__ (spot) in 24 hours and causes about 87 to 92 percent brain AChE inhibition (Coppage and Matthews, 1974.) Similar inhibition of AChE and mortality were caused in sheepshead minnows, Cyprinodon variegatus, in 2, 24, 48, and 72 hours at concentrations 

### of 5,000, 2,000, 100, and 10 ug/L, respectively 

### in static tests (Coppage, 1972). These data indicate that reductions of brain AChE activity of marine fishes

### by 70 to 80 percent or more in short

-term exposures to parathion may be associated with some deaths.

# 0 Other estimates 

### of parathion toxicity to marine organisms follow. The 48-hour EC50 for parathion to Penaeus duorarum 

### was found to be 0.2 ug/L (Lowe et al. 1970). Lahav and Sarig (1969) reported the 96-hour LC50 for mullet, Mugil cephalus to be 125 ug/L. The shell growth of the oyster, Crassostrea virginica, was found by Lowe et al. (1970)to be decreased by 22 percent after 96 hours in 1.0 mg/L. An application factor 

### of 0.1 is applied to the 96-hourLC50 data for invertebrates which range upward from 0.4 ug/L. A criteria of 0.04 ug/L is recommended formarine and freshwater aquatic life.

(QUALITY CRITERIA FOR WATER, JULY 1976) PB-263943 SEE APPENDIX C FOR METHODOLOGYCRITERIA: 

# 0 PENTACHLOROPHENOL
Aquatic Life
The available data for pentachlorophenol indicate that acute and chronic toxicity to freshwater aquatic life occurs at concentrations as low as 55 and 3.2 ug/L, respectively, and would
occur at lower concentrations among species that are more sensitive than those tested. The available data for pentachlorophenol indicate that acute and chronic toxicity to saltwater aquatic life occur at concentrations as low as 53 and 34 ug/L, respectively, and would
occur at lower concentrations among species that are more sensitive than those tested.
Human Health For comparison purposes, two approaches were used to derive criterion levels for pentachlorophenol. Based on available toxicity data, to protect public health the derived level is 1.01 W/L. Using available organoleptic data, to control undesirable taste and odor qualities of ambient water the estimated level is 30 ug/L. It should be recognized that organoleptic data have limitations as a basis for establishing a water quality criterion, and have 

### no demonstrated relationship to potential adverse human health effects.

(45F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYCRITERIA: Range 5

- 9 Domestic water supplies (welfare) 6.5 

# - 9.0 Freshwater aquatic life 6.5 

# - 8.5 Marine aquatic life (but not more than 0.2 units outside of normallyoccurring range.) INTRODUCTION : I8pH" is a measure of the hydrogen ion activity in a water sample. It is mathematically related tohydrogen ion activity according to the expression: pH = -log 10 (H'), where (H') is the hydrogen ion activity. The pH of natural waters is a measure of acid

-base equilibrium achieved by the various dissolved compounds, salts, and gases. The principal system regulating pH 

### in natural waters is the carbonate system which is composed of carbon dioxide (C02), carbonic acid, (HzC03), bicarbonate ion (HC03) and carbonate ions (Cog). The interactions and kinetics of this system have been described by Stumm and Morgan (1970). pH is an important factor in the chemical and biological systems of natural waters. The degree of dissociationof weak acids or bases is affected by changes in pH. This effect is important because the toxicity of many compounds is affected by the degree of dissociation. One such example 

### is hydrogen cyanide (HCN). Cyanide toxicity to fish increases as the pH is lowered - because the chemical equlibrium is shifted toward an increased concentration of HCN. Similar results have been shown for hydrogen sulfide (Has) (Jones, 1964).The solubility of metal compounds contained in bottom sediments or as suspended material,also is affected by pH. For example, laboratory equilibrium studies under anaerobic conditions indicated that pH was an important parameter involved in releasingmanganese from bottom sediments (Delfinoand Lee, 1971). The pH of a water does not indicate ability to neutralize additions of acids or bases without appreciable change. This characteristic, termed "buffering capacity," is controlled by the amounts of alkalinity and acidity present. RATIONALE: Knowledge of pH in the raw water used €or public water supplies is important because without adjustment to a suitable level, such waters may be corrosive and adversely affect treatment processes including coagulation and chlorination. Coagulation for removal of colloidal color by use of aluminum
or iron 

### salts generally has an optimum pH range of 5.0 to 6-5 (Sawyer, 1960). Such optima are predicated upon the availability of sufficient alkalinity to complete the chemical reactions. The effect of pH on chlorine inwater principally is on the equilibrium between hypochlorous acid (HOC1) and the hypochlorite ion (OC1-) according to the reaction: HOCl = H+ + OC1- Butterfield (1984) has shown that chlorine disinfection is more effective at values less than pH 7. Another study (Reid and Carlson, 1974) has indicated, however, that in natural waters no significant difference in the kill rate for Escherichia -- coli was 

# cobserved between pH 6 and pH 8. corrosion of plant equipment and piping in the distribution system can lead to expensive replacement as well as the introduction of metal ions such as copper, lead, zinc, and cadmium. Langelier (1936) developed a method to calculate and control water corrosive activity that employs calcium carbonate saturation theory and predicts whether the water would tend to dissolve or deposit calcium carbonate. By maintaining the pH at the proper level, the distribution system can be provided with
a protective calcium carbonate lining which prevents metal pipe corrosion. Generally, this level is above pH 7 and frequently approaches pH 8.3, the point of maximum bicarbonate/carbonate buffering. Since pH is relatively easily adjusted prior to and during water treatment, a rather wide range 

### is acceptable for waters serving as a source of public water supply. A range of p~ from 5.0 to 9.0 would provide a water treatable by typical (coagulation, sedimentation, filtration, and chlorination) treatment plant processes. As the range is extended, the 

### cost of neutralizing chemicals increases. A review of the effects of pH on fresh water fish has been published by the European Inland Fisheries Advisory Commission (1969). The commission concluded: There is no definite pH range within which a fishery is unharmed and outside which it is damaged, but rather, there is a gradual deterioration as the pH values are further removed from the normal range. The pH range which is not directly lethal to fish is 5

# - 9;however, the toxicity of several common pollutants is markedly affected by pH changes within this range, and increasing acidity or alkalinity may make these poisons more toxic. Also, an acid discharge may liberate sufficient C02 from bicarbonate in the water either

### to be directly toxic, or to cause the pH range 5 

# - 6 to become lethal. Mount (1973) performed bioassays on the fathead minnow, Pimephal- promelas, for a 13-mQnth, one generation time period to determine chronic pH effects. Tests were run at pH levels of 4.5, 5.2. PH Range Effect on Fish* 5.0 

# - 6.0 Unlikely to be harmful to any species unless either the concentration of free C02 is greater than 20 ppm, or the water contains iron salts which are precipitated as ferric hydroxide, the toxicity of which is not known. is present in excess of 100 ppm. 6.0 

# - 6.5 Unlikely to be harmful to fish unless free carbon dioxide

6.5 

# - 9.0 Harmless to fish, although the toxicity of other poisons may be affected by changes within this range.
EIFAC, 19695.9, 6.6, and a control of 7.5. Atthe two lowest pH values (4.5 and 5.2) behavior was abnormal and the fish were deformed. At pH values less than 6.6, egg production and hatchability were reduced when compared with the control. It was concluded that a pH of 6.6 was marginal for vital life functions. Bell (1971) performed bioassays withnymphs of caddisflies (two species) stoneflies (four species), dragonflies (two species), and mayflies (one species). All are important fish food organisms. The 30

-day TL50 values ranged from 2.45 to 5.38 withthe caddisflies being the most tolerant and themayflies being the least tolerant. The pH values at which 50 percent of the organisms emerged ranged from 4.0 to 6.6 with increasing percentage emergence occurring withthe increasing pH values. Based on present evidence, a pH range of 6.5 to9.0 appears to provide adequate protection for the life of freshwater fish and bottom dwelling invertebrates fish food organisms. Outside of this range, fish suffer adverse physiological effects increasing in severity as the degree of deviation increases until lethal levels are reached. Conversely, rapid increases inpH can cause increased NH3 concentrations that are also toxic. Ammonia has been shown to be 10timesas toxic atpH 8.0 as atpH 7.0 (EIFAC, 1969). The chemistry of marine waters differs fromthat of fresh water because of the largeconcentration of saltspresent. In addition toalkalinity based on the carbonate system, there is also alkalinity from other weak acid salts such as borate. Because of the buffering system present in seawater, thenaturally occurring variability of pH is less than in fresh water. Some marine communities are more sensitivetopH change than others (NAS, 1974). Normal pH values in seawater are 8.0 to 8.2 at the surface, decreasing to 7.7 to 7.8 with increasing depth (Capurro, 1970). The NAS Committee's review (NAS, 1974) indicated that plankton and benthic invertebrates are probably
more sensitivethan fishtochanges 

### inpH andthatmature forms and larvae of oysters are adversely affected at the extremes of the pH range of 6.5 to 9.0. However, in the shallow, biologically active waters intropical 

### or subtropical areas, large diurnal pH changes occur naturally because of photosynthesis. pH values may range from 9.5 inthe daytime to 7.3 

### in the early morning before dawn. Apparently, these communities are adapted to such variations or intolerant species


### areabletoavoid

### extremes bymovingout ofthearea. For open ocean waters where the depth is substantially greater than the euphotic zone, the pH should not be changed more than 0.2 units outside of the naturally occurring variation or in any case outside the range of 6.5 to 8.5. For shallow, highly productive coastal and estuarine areas where naturally occurring variations approach the lethal limits for some species, changes inpH should be avoided, but in any case not exceed the limits established for fresh water, i.e., pH of 6.5 to 9.0. As with freshwater criteria, rapid pH fluctuations that are caused by waste discharges should be avoided. Additional support 

### for these limits is provided by Zirino and Yamamoto (1972). These investigators developed a model which illustrates the effects of 

# 0

%. variable pH on copper, zinc, cadmium, and lead; small changes inp~ cause large shifts in these metallic complexes. Such changes may affect toxicity of these metals. For the industrial classifications considered, the NAS report (NAs, 1974) tabulated the range of pH values used by industry for various process and cooling purposes. In general, process waters used varied from pH 3.0 to 11.7, while cooling waters used varied from 5.0 to 8.9. Desirable pH values are undoubtedly closer to neutral to avoid corrosion and other deleterious chemical reactions. Waters with pH values outside these ranges are considered unusable for industrial purposes. The pH of water applied for irrigation purposes is not normally a critical parameter. Compared with the large buffering capacity of the soil matrix, the pH of applied water is rapidly changed to approximately that of the soil. The greatest danger 

### in acid soils is that metallic ions such as iron, manganese, or aluminum may be dissolved in concentrations which are subsequently directly toxic to plants. Under alkaline conditions, the danger to plants is the toxicity of sodium carbonates and bicarbonates either directly or indirectly (NAS, 1974). To avoid undesirable effects 

### in irrigation waters, the pH should not exceed a range of 4.5 to 9.0.

(QUALITY CRITERIA FOR WATER, JULY 1976) PB-263943 SEE APPENDIX C FOR METHODOLOGYCRITERIA: 

# 0 PHENOL Aquatic Life The available data for phenol indicate that acute and chronic toxicity to freshwater aquatic life occurs at concentrations as lowas 10,200 and 2,560 ug/L, respectively, and would occur at lower concentrations among species that are more sensitive than those tested. The available data for phenol indicate that toxicity to saltwater aquatic life occurs at concentrations as low as 5,800 ug/L and would occur at lower concentrations among species that
are more sensitive than those tested. NO data are available concerning the chronic toxicity of phenol to sensitive saltwater aquatic life. 

# 0 Human Health For comparison purposes, two approaches were used to derive criterion levels for phenol. Based on available toxicity data, to protect public health the derived level is 3.5 mg/L. Using available organoleptic data, to control undesirable taste and odor qualities of ambient water the estimated level 

### is 0.3 mg/L. It should be recognized that organoleptic data have limitations 

### as a basis for establishing a water quality criterion, and have no demonstrated relationship to potential adverse human health effects. NOTE: The U.S. EPA is currently developing Acceptable Daily Intake (ADI) or Verified Reference Dose (RfD)values for Agency

-wide use for this chemical. The new value should be substitutedwhen it becomes available. The January, 1986, draft Verified Reference Dose document cites an RfD of 0.1 mg/kg/day for phenol. 

# .'/ (45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGY 

# 0PHOSPHORUS
CRITERION:: 0.10 ug/L yellow (elemental) phosphorus for marine or estuarine water. INTRODUCTION: Phosphorus in the elemental form is particularly toxic and is subject to bioaccumulation in much the same way as mercury. Phosphorus asphosphate is one bf themajor nutrients required forplant nutrition and is essential for life. 

### Inexcess of a critica1 concentrat ion, phosphates stirnulate p 1 ant growths. During the past 30 years, a formidable case has developed for the belief that increasing standing crops of aquaticplants, which often interfere with water uses and are nuisances to man, frequently are caused by increasing supplies of phosphorus. Such phenomena are associated with a condition of accelerated eutrophication or aging 

### of waters. Generally, it is recognized that phosphorus is not the sole cause of eutrophication but there is substantiating evidence that frequently it is the key element of 

### all of the elements required by freshwater plants, and generally, it is present in the least amount relative toneed. Therefore, 

### an increase 

### in phosphorus allows use of other already present nutrients for plant growth. Further, of 

### all of the elements required for plant growth in the water environment, phosphorus is the most easily controlled by man. Large deposits of phosphate rock are found nearthewestern shore of Central Florida, aswellasina number of otherStates. Deposits inFlorida are found inthe form of pebbleswhich vary 

# 0

..,in size from fine sand to about the size of 

### a human foot. These pebbles are embedded in 

### a matrix of clay and sand. The phosphate rock beds lie within 

### a few feet of the surface and mining 

### is accomplished by using hydraulic water jets and 

### a washing operation that separates the phosphates from waste materials. The process is similar to that of strip

-mining. Florida, Idaho, Montana, North Carolina, South Carolina, Tennessee, Utah, Virginia, and Wyoming share phosphate mining activities. Phosphates enter waterways from several different sources. The human body excretes about one pound per year of phosphorus expressed as I1Pt1.The use of phosphate detergents and other domestic phosphates increases the per capita contribution to about 3.5 pounds per year of phosphorus as P. Some industries, such as potato processing, have wastewaters high in phosphates. Crop, forest, idle, and urban land contribute varying amounts of phosphorus

-diffused sources in drainage to watercourses. This drainagemay be surface runoff of rainfall, effluent from tile lines, 

### or return flow from irrigation. Cattle feedlots, concentrations of domestic duck or wild duck populations, tree leaves, and fallout from the atmosphere all are contributing
sources. Evidence indicates that: (1) high phosphorus concentrations are associated with accelerated eutrophication of waters, when other growth

-promoting factors are present: (2) aquatic plant problems develop in reservoirs and other standing waters at phosphorus values lower than those critical in flowing streams: (3) reservoirs and lakes collect phosphates from influent streamsand store 

### a portion of them within consolidated sediments, thus serving as a phosphate sink; and (4) phosphorus concentrations critical tonoxious plant growth vary and nuisance growths may result from 

### a particular concentration of phosphate in one geographical area but not inanother. The amount orpercentage of inflowing nutrients that may be retained by a lake or reservoir is variable and will depend upon: (1)the nutrient loading to the lake or resevoir; (2) the volume of the euphotic zone; (3) the extent of biological activities; (4) the detention 

### time within a lake basin or the timeavailable forbiological 

### activities; the penstock from the reservoir. and (5)the level of discharge from the lake orof

Once nutrients are combined within the aquatic ecosystem, their removal is tedious and expensive. Phosphates are used by algae and higher aquaticplants and may be stored inexcess of
use within the plant cell. With decomposition of the plant cell,
some phosphorus may be released immediately through bacterial action €or recycling within the biotic community, while the remainder may be deposited with sediments. Much of the material that combines with the consolidated sediments within the lake bottom is bound permanently and will not be recycled into the
sys tern. 

# 0

RATIONAm: Elemental Phosphorus
Isom (1960) reported an LC50 of 0.105 mg/L at 48 hours and 0.025 mg/L at 160 hours for bluegill sunfish, 

## __ Lepomis 

### _---
y.

~ macrochirus, exposed to ye1low phosphorus in distilled water at~ ~ -

~~ __

- 26 OC and pH 7. The 125

-and 195

-hour LC50's of yellow phosphorus to Atlantic cod, Gadus morhua, and Atlantic salmon, Salmo salar, smolts in continuous

-exposure experiments were 1.89 and 0.79 ug/L, respectively (Fletcher and Hoyle, 1972). No evidence of an incipient lethal level was observed since the lowest concentration of p4 tested was 0.79 ug/L. Salmon that were exposed to elemental phosphorus concentrations of 40 ug/L or less developed a distinct external red color and showed signs of extensive hemolysis. The predominant features of p4 poisoning in salmon were external redness, hemolysis, and reduced hematocrits. Following the opening of an elemental phosphorus production plant in Long Harbour, Placentia Bay, Newfoundland, divers observed dead fish upon the bottom throughout the Harbour (Peer, 1972). Mortalities were confined to 

### a water depth of less than 18 meters. There was visual evidence of selective mortality among benthos. Live mussels were found within 300 meters of the effluent pipe, while all scallops within this area were dead. Fish will concentrate elemental phosphorus from water containing as little as 1 ug/L (Idler, 1969). In one set of experiments, a cod swimming in water containing 1 ug/L elemental phosphorus for 18 hours concentrated phosphorus to 50 ug/kg in muscle, 150 ug/kg 

### in fatty tissue, and 25,000 ug/kg in the liver

(Idler, 1969; Jangaard, 1970). The experimental findings showed that phosphorus is quite stable in the fish tissues.The criterion of 0.10 ug/L elemental phosphorus for marine or estuarine waters is .1 of demonstrated lethal levels to important marine organisms and of levels that have been found to result in significant bioaccumulation. 

# 0Phosphate Phosphorus Although 

### a total phosphorus criterion tocontrol nuisance aquatic growths is not presented, it is believed that the following rationale to support such a criterion, which currently 

### is evolving, should be considered. Total phosphate phosphorus concentrations 

### inexcess of 100 ug/L P may interfere with coagulation in water treatment plants. When such concentrations exceed 25 ug/L atthe time of the spring turnover on a volume

-weighted basis in lakes or reservoirs, they may occasionally stimulate excessive or nuisance growths of algae and other aquatic plants. Algal growths inpart'undesirable tastes and odors to

### water, interfere with water treatment, become aestheticallyunpleasant, and alterthechemistry of the water supply. They contribute to the phenomenon of cultural 

# 0 eutrophication. To prevent the development of biological nuisances and to control accelerated or cultural eutrophication, total phosphates
as phosphorus (P) should not exceed 50 ug/L in any stream at the point where it entersany lake orreservoir, nor 25ug/L within the lake or reservoir. A desired goal for the prevention of plant nuisances in streams or other flowing waters not discharging directly to lakes or impoundments is 100ug/L total P (Mackenthun, 1973) Most relatively uncontaminated lake districts 

### axe known tohave surfacewatersthat contain from 10 to 30 ug/L total phosphorus as P (Hutchinson, 1957). The majority of the Nation's eutrophication problems are associated with lakes or reservoirs and currently there are more 

# 0

, 

### ..

..data to support the establishment of a limiting phosphorus level in those waters than in streams or riversthat do not directly impact such water. There are natural conditions, also, that would dictate the consideration of either 

### a more or less stringentphosphorus level. Eutrophication problems may occur in waters where the phosphorus concentration is less than that indicated above and, obviously, such waters would need more stringent nutrient limits. Likewise, there are those waters within the Nation where phosphorus is not now a limiting nutrient and where the need for phosphorus limits is substantially diminished. Such conditions are described 

### in the last paragraph of this rationale. There are two basic needs in establishing a phosphorus criterion for flowing waters: ode is to control the development of plant nuisances within the flowing water and, in turn, to control and prevent animal pests that may become associated with such plants; the other is toprotect the downstream receiving waterway, regardless of its proximity in linear distance. It is evidentthataportionofthatphosphorus that

### entersa streamor other flowing waterway eventually will reach a receiving lake or estuary either as a component of the fluid mass, as bed load sediments that are carried downstream, oras floating organic materials that may drift just above the stream's bed or float on its water's surface. Superimposed on the loading from the inflowing waterway, a lake or estuary may receive additional phosphorus as fallout from the air shed or as a direct introduction from shoreline areas.Another method to control the inflow of nutrients, particularly phosphates, into a lake is that of prescribing 

### an annual loading to the receiving water. Vollenweider (1973) suggests total phosphorus (P) loadings in grams per square meter of surface area per year that will be a critical level for eutrophic conditions within the receiving waterway for a particular water volume where the mean depth of the lake in meters is divided by the hydraulic detention time in years. Vollenweider's data suggest a range of loading values that should result inoligotrophic lakewater quality. 

# 0

Eutrophic or Critical Oligotrophic or Mean Depth/Hydraulic Permissible

Detention Time Loading Loading

(meters/year)(grams/meter2/year) (grams/meter2/year)
0.5 1.0 2.5 5.0 7.5 10.0 25.0 50.0 75.0 100.0 0.07 0.10 0.16 0.22 0.27 0.32 0.50 0.71 0.87 1-00 0-14 0.20 0.32 0.45 0.55 0.63 1.00 1.41 1.73 2.00
There may be waterways wherein higher concentrations or loadings of total phosphorus do not produce eutrophy, as well as those waterways wherein lower concentrations or loadings of total 

# 0

L-7phosphorus may be associated with populations of nuisance organisms. Waters now containing less than the specified amounts of phosphorus should not be degraded by the introduction of additional phosphates. It should be recognized that a number of specific exceptions
can occur to reduce the threat of phosphorus as a contributor to lake eutrophy: 1. Naturally occurring phenomena may limit the development of plant nuisances. 2. Technological or costeffective limitationsmay help control introduced pollutants. 3. Waters may be highly laden with natural silts or colorswhich reduce the penetration of sunlight needed €or plant photosynthesis. 4. Some waters morphometric features of steep banks, great depth, and substantial flows contribute to a history of no plant problems. Wateks may be managed primarily for waterfowl or other wildlife. 7. In some waters nutrient other than phosphorus is limiting to plant growth: the level and nature of such limiting nutrient would. not be expected to increase to an extent that would influence eutrophication. 6. In some waters phosphorus control cannot be sufficiently effective under present technology to make phosphorus the limiting nutrient. 5.



### No national criterion is presented for phosphate phosphorus for the control of eutrophication.

(QUALITY CRITERIA FOR WATER, JULY 1976) PB

-263943 SEE APPENDIX C FOR METHODOLOGYPHTHALATE ESTERS CRITERIA: Aquatic 

### Life The available data for phthalate esters indicate that acute and chronic toxicity 

### to freshwater aquatic life occurs at concentrations as low as 940 and 3 ug/L, respectively, and would
occur at lower concentrations among species that are more sensitive than those tested. The available data for phthalate esters indicate that acute toxicity to saltwater aquatic life occurs at concentrations as low as 2,944 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No data are available concerning the chronic toxicity of phthalate esters to sensitive saltwater aquatic life but toxicity to one species of algae occurs at concentrations as low as 3.4 ug/L. 

## , 

# 0

Human Health For the protection of human health from the toxic properties of dimethyl phthalate ingested through water and contaminated aquatic organisms, the ambient water criterion 

### is determined to be 313 mg/L. For the protection of human health from the toxic properties of dimethyl phthalate ingested through contaminated aquatic organisms alone, the ambient water criterion is determined to be 2.9 g/l.For the protection of human health from the toxic properties of diethyl phthalate ingested through water and contaminated aquatic organisms, the ambient water criterion is determined to be 350mg/L. For the protection of human health from the toxic properties of diethyl phthalate ingested through contaminated aquatic organisms alone, the ambient water criterion is determined to be 1.8 g/l. For the protection of human health from the toxic properties of dibutyl phthalate ingested through water and contaminated aquatic organisms, the ambient water criterion is determined to be 34 mg/L. For the protection of human health from the toxic properties of dibutyl phthalate ingested through contaminated aquatic organisms alone, the ambient water criterion is determined to be 154 mg/L. For the protection of human health from the toxic properties of di-2-ethylhexyl phthalate ingested through water and contaminated aquatic organisms, the ambient water criterion is determined to be 15 mg/L. For the protection of human health from the toxic properties of di

-2-ethylhexyl phthalate ingested through contaminated aquatic organisms alone, the ambient water criterion is determined to be 50 mg/L.

(45 F

### .

### R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYPOLYCHLORINATED BIPHENYLS Aquatic Life For polychlorinated biphenyls the criterion to protect freshwater aquatic life as derived using the Guidelines is 0.014 ug/L 

### as a 24

-hour average. The concentration of 0.014 ug/L is probably too high because it is based on bioconcentration factors measured in laboratory studies, but field studies apparently produce factors at least 10 times higher for fishes. The available data indicate that acute toxicity to freshwater aquatic life probably will occur only at concentrations above 2.0 ug/L and that the 24

-hour average should provide adequate protection against acute toxicity. For polychlorinated biphenyls the criterion to protect 

# 0 saltwater aquatic life as derived using the Guidelines is 0.030 ug/L as a 24

-hour average. The concentration of 0.030 ug/L is probably too high because it is based on bioconcentration factors measured in laboratory studies, but field studies apparently produce factors at least 10 times higher for fishes. The available data indicate that acute toxicity to saltwater aquatic life probably will only occur at concentrations above 10 ug/L and that the 24

-hour average criterion should provide adequate protection against acute toxicity.
Human Health For the maximum protection of human health from the potential carcinogenic effects of exposure to polychlorinated biphenyls through ingestion of contaminated water and contaminated aquatic 

# 0

.i”iorganisms, the ambient water concentration should be zero, based
on the nonthreshold assumption for this chemical. However,
zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer risk over the lifetime are estimated at and The corresponding recommended criteria are 0.79 ng/L, 0.079 ng/L, and 0.0079 ng/L, respectively. If these estimates aremade for consumption of aquatic organisms only, excluding consumption of water, the levels are 0.79 ng/L, 0.079 ng/L, and 0.0079 ng/L, respectively.

(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYPOLYNUCLEAR AROMATIC HYDROCARBONS
CRITERIA: Aquatic 

## Life The limited freshwater data base available for polynuclear aromatic hydrocarbons, mostly from short

-termbioconcentration studies with two compounds, does not permit a statement concerning acute or chronic toxicity. The available data for polynuclear aromatic hydrocarbons indicate that acute toxicity 

### to saltwater aquatic life occurs at concentrations as low as 300 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. 

### No data are available concerning the chronic toxicity of polynuclear aromatic hydrocarbons to sensitive saltwater aquatic life.
Human Health For the maximum protection of human health from the potential carcinogenic effects of exposure to polynuclear aromatic hydrocarbons through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentration should be zero,based on the nonthreshold assumption for this chemical. However, zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer risk over the lifetime are estimated at 

### lom6, and The corresponding recommended criteria are 28.0 ng/L, 2.8 ng/L, and 0.28 ng/L, respectively. If these estimates are made for consumption of aquatic organisms only, excludinq consumption of water, the levels are 311.0 nq/L.31.1 ng/L, and 3.11 ng/L, respectively.

(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYSELENIUM CRITERIA: Aquatic Life For total recoverable inorganic selenite the criterion to protect freshwater aquatic life as derived using the Guidelines 

### is 35 ug/L as 

### a 24

-hour average, and the concentration should not exceed 260 ug/L at any time. For total recoverable inorganic selenite the criterion to protect saltwater aquatic life as derived using the Guidelines is 54 ug/L 

### as a 24

-hour average, and the concentration should not exceed 410 ug/L at any time. The available data for inorganic selenate indicate that acute toxicity to freshwater aquatic life occurs at concentrations as low as 760 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No data are available concerning the chronic toxicity of inorganic selenate to sensitive freshwater aquatic life. No data are available concerning the toxicity of inorganic selenate to saltwater aquatic life.

Human Health The ambient water quality criterion for selenium is recommended to be identical to the existing water standard which is 10 ug/L. Analysis of the toxic effects data resulted in 

### a calculated level which is protective of human health against the ingestion of contaminated water and contaminated aquatic

(- organisms. The calculated value is comparable to the present 

# 0standard. For this reason 

### a selective criterion based on 

### exposure solely from consumption of 6.5 grams of aquatic organisms was not derived.

(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYSILVER
Aquatic 

# - Life For freshwater aquatic life the concentration (in ug/L) of total recoverable silver should not exceed the numerical value given by e(l.72 [ln(hardness)

### 3

- 6.52) atany time. For example, athardnesses of 50, 100, and 200 mg/L as CaC03, the concentration of total recoverable silver should not exceed 1.2, 4.1, and 13 ug/L, respectively, at any time. The available data indicate that chronic toxicity to freshwater aquatic life may occur at concentrations as low as 0.12 ug/L. For saltwater aquatic life the concentration of total recoverable silver should not exceed 2.3 ug/L atany time. No data are available concerning the chronic toxicity of silver to sensitive saltwater aquatic life.

Human Health The ambient water quality criterion for silver is recommended to be identical to the existing water standard, which is 50 ug/L. Analysis of the toxic effects data resulted in
a calculated level which is protective of human health against the ingestion of contaminated water and contaminated aquatic organisms. The calculated value is comparable tothe present standard. For this reason a selective criterion based on exposure solely from consumption of 6.5 grams of aquatic organisms was not derived. 

# a

- '. ' (45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYSOLIDS (DISSOLVED)AND 

## -SALINlTY

CRITERION: 250 mg/L for chlorides and sulfates in domestic water supplies (welfare).

INTRODUCTION: Dissolved solids and total dissolved solids are terms generally associated with freshwater systems and 

### consist of inorganic salts, small amounts of organic matter, and dissolved materials (Sawyer, 1960). The equivalent terminology in Standard Methods is filtrable residue (Standard Methods, 1971). Salinity is an oceanographic term, and although not precisely equivalent tothe total dissolved salt content it is related toit (Capurro, 1970). For most purposes, the terms total dissolved salt content and salinity are equivalent. The principal inorganic anions dissolved in water include the carbonates, chlorides, sulfates, and nitrates (principally in ground waters) ; the principal cations are sodium, potassium, calcium, and magnesium. RATIONALE: Excess dissolved solids are objectionable in drinking water because of possible physiological effects, unpalatable mineral tastes, and higher costs because of corrosion 

### or the necessity for additional treatment. The physiological effects directly related to dissolved solids include laxative effects principally from sodium sulfate and magnesium sulfate and the adverse effect of sodium on certain patients afflictedwithcardiac disease and women withtoxemia associated with pregnancy. One study was made using data 

### ,. ~ 

# ecollected from wells in North Dakota. Results from a questionnaire showed that with wells in which sulfates ranged from 1,000 to 1,500 mg/L, 62 percent of the respondents indicated laxative effects associated with consumption of the water. However, nearly one-quarter of the respondents to the questionnaire reported difficulties when concentrations ranged from 200 to 500mg/L (Moore,1952). To protect transients to an area, a sulfate level of 250 mg/L should afford reasonable protection from laxative effects. As indicated, sodium frequently is the principal component of dissolved solids. Persons on restricted sodium diets may have an intake restricted from 500 to 1,000 mg/day (Nat. Res. Coun., 1954). That portion ingested in water must be compensated by reduced levels in food ingested so that the total does not exceed the allowable intake. Using certain assumptions of water intake 

### (e.g., 2 liters of water consumed per day) and sodium content 

### of food, it has been calculated that for very restricted sodium diets, 20 mg/L in water would be the maximum, while for moderately restricted diets, 270 mg/L would be maximum. Specific sodium levels for entire water supplies have not been recommended but various restricted sodium intakes are recommended because:

(1) the general population is not adversely affected by sodium, but various restricted sodium intakes are recommended by physicians for a significantportion of the population, and (2) 270 mg/L of sodium is representative of mineralized waters that may be aesthetically unacceptable, but many domestic water supplies exceed this level. Treatment for removal bf sodium inwater supplies 

### is costly (NAS, 1974). A study based on consumer surveys in 29 California water systems was made to measure the taste threshold of dissolved salts 

### in water (Bruvold et al., 1969). Systems were selected to eliminate possible interferences from other taste

-causing substances than dissolved salts. The study revealed that
consumers rated waters with 319 to 397 mg/L dissolved solids as llexcellentlt while those 

### with 1,283 to 1,333 mg/L dissolved solids
were "unacceptable" depending 

### on the rating system used. A *lgoodll rating 

### was registered for dissolved solids less than 658 to 755 mg/L. 

### The 1962 PHS Drinking Water Standards recommended a maximum dissolved solids concentration 

### of 500 mg/L unless more suitable supplies were unavailable. Specific constituents included in the dissolved solids 

### in water may cause mineral tastes at lower concentrations than other constituents. Chloride ions have frequently been cited as having
a low taste threshold in water. Data from Ricter and MacLean (1939)

### on a tastepanel of 53 adults indicated that 61mg/L NaCl
was themedian level for detecting a difference 

### from distilled water. At a median concentration of 395 mg/L chloride a salty taste was distinguishable, although the range was from 120 to 1,215 mg/L. Lockhart, 

### @t al. 1955) evaluated the effect of chlorides on water used forbrewing coffee indicated threshold concentrations for chloride ranging from 210 mg/L to 310 mg/L depending on the associated cation. These data indicate that a level of 250 mg/L chlorides is a reasonable maximum level to 

# 0 \.p protect consumers of drinking water.The causation of corrosion and encrustation of metallic surfaces by water containing dissolved solids 

### is well known. 

### In water distribution systems corrosion is controlled by insulating dissimilar metal connections by nonmetallic materials, using pH control and corrosion inhibitors, or some form of galvanic or impressed electrical current systems (Lehmann, 1964). 

### In household systems water piping, wastewater piping, water heaters, faucets,toilet flushing mechanisms, garbage grinders and both clothes and dishwashing machines incure damage. By using water with 1,150 mg/L dissolved solids as compared with 250 mg/L, service life was reduced from 70 percent for toilet flushing mechanisms to 30 percent for washing equipment. Such increased corrosion was calculated in 1968 to cost the consumer an additional $0.50 per 1,000 gallons used. All species of fish and other aquatic life must tolerate a range of dissolved solids concentrations 

### in order to survive under natural conditions. Based on studies 

### in Saskatchewan it has been indicated that several common freshwater species survived 10,000 mg/L dissolved solids, that whitefish and pikeperch survived 15,000 mg/L, but only the stickleback survived 20,000 mg/L dissolved solids. It was concluded that lakes with dissolved solids in excess of 15,000mg/L were unsuitable for most freshwater fishes (Rawson and Moore, 1944). The 1968 NTAC Report also recommended less than that caused chloride. maintaining osmotic pressure levels of by a 15,000 mg/L solution of sodium

### Marine fishes alsoexhibitvariance inabilitytotolerate salinity changes. However, fishkillsin Laguna Madre off the Texas coast have occurred with salinities

### inthe range of 75 to 100o/oo. Such concentrated seawater 

### is caused by evaporation and lack of exchange with the Gulf of Mexico (Rounsafell and Everhart, 1953). Estuarine speciesof fish are

### tolerant of salinitychanges ranging from fresh to brackish to seawater. Anadromous species likewise are tolerant although evidence indicates that the young cannot tolerate the change until the normal time of migration (Rounsefell and Everhart, 1953). Other aquatic species are more dependent on salinity forprotection from predators orrequire certain 

### minimal salinities for successful hatching of eggs. The oyster drill cannot tolerate salinities less than 12.5 o/oo, Therefore, estuarine segments containing salinities below about 12.5 o/oo produce most of the seed oysters for planting (Rounsefell and Everhart, 1953). Based on similar examples, the 1968 NTAC Report recommended that to protect fish and other marine 

### animals no changes inhydrography or stream flow should be allowed that permanently change isohaline patterns inthe estuary by more than 10 percent from natural variation. Many of the recommended game bird levels fordissolved solids concentrations in drinking water have been extrapolated from data collected on domestic species such as chickens. However, young ducklings were reported poisoned in Suisan Marsh by salt when maximum summer salinities varied from 0.55 to 1.74 o/oo with

~ means as high as 1.26 o/oo (Griffith, 1963).Indirect effects of excess dissolved solids are primarily the elimination of desirable food plants and other habitat

-forming plants. Rapid salinity changes cause plasmolysis of tender leaves and stems because of changes in osmotic pressure. The 1968 NTAC Report recommended the following limits in salinity variation from natural toprotect wildlifehabitats:
Natural Salinity Variation Permitted (O/OO) 

### (o/oo) 0 

### to 3.5 1 3.5 to 13.5 2 13.5 to 35 4 Agricultural uses of water are also limited by excessive dissolved solids concentrations. Studies have indicated that chickens, 

### swine, cattle, and sheep can survive on saline waters up to 15,000 mg/L of salts of sodium and calcium combined with bicarbonates, chlorides, and sulfates but only 10,000 mg/L of corresponding salts of potassium and magnesium. The approximate limit for highly alkaline waters containing sodium and calcium carbonates is 5,000 mg/L (NTAC, 1968). Irrigation use of water depends not only upon the osmotic effect of dissolved solids, but also on the ratio of the various cations present. In arid and semiarid areas 

### general classification of salinity hazards has been prepared (NTAC, 1968) (seeTable 9). Table 9.-Dissolved Solids Hazard for Irrigation Water (mg/L). water from which no detrimental effects willusually be noticed

--------------------- 500 -
.. .. ,,water which can have detrimental effects on sensi500

-1,000 tive crops--------------------- water that may have adverse effects on many crops and requires careful managemerit practices----------------- 1,000

-2,000 water that can be used for tolerant plants on perme- able soilswith careful management practices

----------- 2,000

- 5,000 The amount of sodium and the percentage of sodium in relation to other cations are often important. In addition to contributing to osmotic pressure, sodium is toxic to certain plants, especially fruits, and frequently causes problems 

### insoil structure, infiltration, and permeability rates (Agriculture Handbook #60, 1954). A high percentage of exchangeable sodium in soils containing clays that swell when wet can cause a soil condition adverse to water movement and plant growth. The exchangeable

-sodium percentage (ESP)

## * is an index of the sodium status of soils. An ESP of 10 to 15 percent is considered excessive if a high percentage of swelling clay minerals is present (Agricultural Handbook #60, 1954). 

# 0

For sensitive fruits, the tolerance for sodium for irrigation water is for a sodium adsorption ratio (SAR)** of about 4, whereas for general crops and forages a range of 8 to 18 is generally considered usable (NTAC, 1968). It is emphasized that application of these factors must be interpreted in relation to specific soil conditions existing in a given locale and therefore frequently requires field investigation. Industrial requirements regarding the dissolved solids 

# .

,- content of raw waters is quite variable. Table 10 indicatesTable 10.-Total Dissolved Solids Concentrations of Surface Waters That Have Been Used as Sources for Industrial Water Supplies Industry/Use Maximum Concentration (mgm Textile 150 Pulp and Paper 1,080 Chemical 2,500 Petroleum 3,500 Primary Metals 

## . 1,500 Boiler Make-up 35,000maximum values accepted by various industries for process requirements (NAS, 1974). Since water of almost any dissolved 

# 0

solids concentration can be de

-ionized to meet the most stringent requirements, the economics of such treatment are the 1imiting factor for industry. *ESP = 100 [a 

### + b(SAR)] 1 [a 

### + b(SAR)] where: a = intercept respresenting experimental error

(ranges from -0.06 to 0.01) from 0.014 

### to 0.016) b =slope 

### of regression line (ranges
**SAR = sodium adsorption ratio = Na 

# - [0.5(Ca 

## + Mg)]"" SAR is expressed as milliequivalents

(QUALITY CRITERIA FOR WATER, JULY 1976) PB

-263943 SEE APPENDIX C FOR METHODOLOGY 

# 0SOLIDS (SUSPENDED, SETTLEABLE) 

## - AND TURBIDITY
CRITERIA Freshwater fish and other aquatic life: Settleable and suspended solids should not reduce the depth of the compensation point for photosynthetic activityby more than 10 percent from the seasonally established norm for aquatic life. INTRODUCTION: The term lkuspended and settleable solidst1is descriptive of the organic and inorganic particulate 

### matter 

### in water. The equivalent terminology used for solids in Standard Methods (APHA, 1971) is total suspended matter for suspended solids, settleable matter for settleable solids, volatile suspended matter for volatile solids and fixed suspended matter for fixed suspended solids. The term ltsolidstlis used in this discussion because of its more common use in the water pollution control literature. 

# 0

RAT1ONALE : Suspended solids and turbidity are importantparameters in b o t h m u n i c i p a l and industrial water supplypractices. Finished drinking waters have a maximum limitof 1turbidityunit where the water enters the distribution system. This limit is based on health considerations as it relates to effective chlorine disinfection. Suspended matter provides areas where microorganisms do not come into contact with the chlorine disinfectant (NAS,1974). The ability of common water treatment processes (i.e.,coagulation, sedimentation, filtration, and chlorination) to remove suspended matter to achieve acceptable final turbidities is a function of the composition of the material 

### as well as its concentration. Because of the variability 

# 0of such removal efficiency, it is not possible to delineate a general raw water criterion for these uses. Turbid water interferes with recreational use and aesthetic enjoyment of water. Turbid waters can be dangerous for swimming, especially if diving facilities are provided, because ofthe possibility of unseen submerged hazards and the difficulty in locating swimmers 

### in danger of drowning (NAS, 1974). The less turbid the water the more desirable it becomes for swimming and other water contact sports. Other recreational pursuits such as boating and fishing will be adequately protected by suspended solids criteria developed for protection of fish and other aquatic life. Fish and other aquatic life requirements concerning suspended solids can be divided into those whose effect occurs in the water column and those whose effect occurs following sedimentation to the bottom of the water body. Noted effects are similar for both fresh and marine waters. The effects of suspended solids on fish have been reviewed by the European Inland Fisheries Advisory Commission (EIFAC, 1965). This review in 1965 identified four effects on the fish and fish food populations, namely:
(1) by acting directly on the fish swimming in water in which solids are suspended, and either killing them or reducing their growth rate, resistance to disease, etc.; (2) by preventing the successful development of fish eggs and larvae; (3) by modifying natural movements and migrations of fish;(4) by reducing the abundance of food available to the fish;.

# . . Settleablematerials which blanket the bottom of water bodies damage the invertebrate populations, block gravel spawning beds, and if organic, remove dissolved oxygen from overlyingwaters (ElFAC, 1965; Edberg and Hofsten, 1973). In a study downstream from the discharge of a rock quarry where inert suspended solids
were increased to 80 mg/L, the density of macroinvertebrates decreased by 60 percent while in areas of sediment accumulation benthic invertebratepopulations alsodecreased by 60percent regardless of the suspended solid concantrations (Gammon, 1970). similar effects have been reported downstream from an area which
was intensively logged. Major increases in stream suspended solids (25 ppm turbidity upstream versus 390 ppm downstream) caused smothering of bottom invertebrates, reducing organism density toonly 7.3 per square foot versus 25.5 per square foot upstraam (Tebo, 1955). When settleable solids block gravel spawning beds which contain eggs, high mortalities result although there is evidence that some species of salmonids will not spawn in such areas (EIFAC, 1965). It has been postulated that silt attached to the eggs prevents sufficient exchange of oxygen and carbon dioxide between the egg and the overlying water. The important variables are particle size, stream velocity, and degree of turbulence (EIFAC, 1965).Deposition of organic materials to the bottom sediments can
cause imbalances in stream biota by increasing bottom animal density principally worm populations, and diversity is reduced as pol lution

-sensitive forms disappear (Mackenthun, 1973). Algae 

### 1ikewise flourish in such nutrient

-rich areas although forms may become less desirable (Tarzwell and Gaufin, 1953). Plankton and inorganic suspended materials reduce light penetration into the water body, reducing the depth of thephotic
zone. This reduces primary production and decreases fish food. The NAS commitee in 1974 recommended that the depth of light penetration not be reduced by more than 10 percent (NAS, 1974). Additionally, the near surface waters are heated because of the greater heat absorbency of the particulate material which tends to stabilize the water column and prevents vertical mixing (NAS, 1974). Such mixing reductions decrease the dispersion of dissolved oxygen and nutrients to lower portions of the water body. One partially offsetting benefit of suspended inorganic material in water is the sorption of organic materials such as pesticides. Following this sorption process subsequent sedimentationmay remove thesematerials from the water column into the sediments (NAS, 1974). Identifiable effects of suspended solids on irrigation use of water include the formation of crusts on top of the soil which inhibits water infiltration and plant emergence, and impedes soil aeration; the formation of films on plant leaves which blocks sunlight and impedes photosynthesis and which may reduce themarketability of some leafy crops like lettuce, and finally the adverse effect on irrigation reservoir capacity, delivery canals, and other distribution equipment (NAS, 1974). 

# 0

The criterion for freshwater fish and other aquatic lifeare essentially that proposed by the National Academy of Sciences and the Great Lakes Water Quality Board.

(QUALITY CRITERIA FOR WATER, JULY 1976) PB-263943 SEE APPENDIX C FOR METHODOLOGYCRITERION: SULFIDE

# = HYDROGEN SULFIDE

2 ug/L'undissociated HZS for fish and other aquatic life, fresh and marine water. INTRODUCTION: Hydrogen sulfide is a soluble, highly poisonous, gaseous compound havinq t h e c h a r a c t e r i s t i codor of rotten eggs. It is detectable 

### in air by humans at a dilution of 0.002 ppm. It will dissolve in water at 4,000 mg/L at 20' C and one atmosphere of pressure. Hydrogen sulfide biologically is an active compound that is found primarily as an anaerobic degradation product of both organic sulfur compounds and inorganic sulfates. Sulfides
are constituents of many industrial wastes such as those from tanneries, paper mills, chemical plants, and gas works. The anaerobic decomposition of sewage, sludge beds, algae, and other naturally deposited organic material is a major source of hydrogen sulfide. 

# 0

When soluble sulfides are added towater they react with hydrogen ions to form HS or HZS, the proportion of each depending
on thepH. The toxicityof sulfides derivesprimarily from H2S rather than from the hydrosulfide (HS-) or sulfide (S=) ions' When hydrogen sulfide dissolves inwater it dissociates according to the reactions: H2S HS- 

### + H+ and HS- S= 

### + H+ AtpH 9 about 99 percent of the sulfideis inthe form of HS-



## , atpH 7 thesulfideisequallydividedbetween HS- and.H2S: and at pH 5 about 99 percent of the sulfide is present as H2S (NAS 

# 0

-_- 

# a 1974). The fact that H2S is oxidized in well

- aerated water by natural biological systems to sulfates or is biologically oxidized 

### to elemental sulfur has caused investigators tominimize the toxic effects of H2S on fish and other aquatic life. RATIONALE: The degree of hazard exhibited by sulfide to aquatic animal life is dependent on thetemperature, pH, and dissolvedoxygen. At lower pH values a greater proportion is inthe form of the toxic undissociated H2S. In winter when the pH is neutral or below or when dissolved oxygen levels are low but not lethal to fish, the hazard from sulfides is exacerbated. Fish exhibit a strong avoidance reaction to sulfide. Based on data from experiments with the stickleback, Jones (1964) hypothesized that if fish encounter a lethal concentration of sulfidethere is a reasonable chance they willbe repelled by it before they 

### are harmed. This, of course, assumes that an escape route is open. Many past data on the toxicity of hydrogen sulfidetofish and other aquatic life have been based on extremely short exposure periods. Consequently, these early data have indicated that concentrations between 0.3 and 0.4 mg/L permit fish to survive (Van Horn 1958, Boon and Follis 1967, Theede et al., 1969). Recent :ong-term data, both in field situations and under controlled 1aborator.y conditions, demonstrate hydrogen sulfide toxicity at lower concentrations. Colby and Smiti

-i (1967)found thatconcentrations ashigh as 0.7 mg/L have been found within 20 mm of the bottom of sludge beds, and the levels of 0.1 to 0.02 mg/L were common within thefirst 20 mm of water above this layer. Walleye (Stizostedion vitreum) eggs held in trays in this zone did not hatch. Adelman and Smith (1970) reported that the hatchability of northern pike 

### (Esox 

### lucius) eggs was substantially reduced at 25 ug/L H2S: at 41 ug/L mortality was almost complete. Northern pike fryhad 96- hour LC50 values that varied from 17 to 32 ug/L at normal oxygen levels of 6.0 mg/L. The highest concentration of hydrogen sulfide that had no observable effect on eggs and fry was 14 and 4 ug/L, respectively. Smith and Oseid (1972), working on eggs, fry and juveniles of walleyes and white suckers (Catostomus commersoni) and Smith (1971), Safe levels in working on walleyes 

### and fathead minnows, Pimephales promelas, were found tovary from 2.9 ug/L to 12 ug/L with eggs being the least sensitive and juveniles being the most sensitive in short

-term tests. In 96- hour bioassays, fathead minnows and goldfish, Carassius auratus, varied greatly in tolerance to hydrogen sulfide with changes in temperature. They were more tolerant atlow temperatures (6 to 10, C). Holland, et al. (1960) reported that 1.0 mg/L sulfide caused 100 percent mortality in 72 hours with Pacific salmon. 

# 0

On the basis of chronic tests evaluating growth and survival, the safe H2S level for bluegill (Lepomis macrochirus) juveniles and adults was 2 ug/L. Egg deposition in bluegills was reduced after 46 days in 1.4 ug/L H2S (Smith and Oseid, 1974). White sucker eggs were hatched at 15 ug/L, but juveniles showed growth reductions at 1 ug/L. Safe level for fathead minnows were between 2 and 3 ug/L. Studies showed that safe levels for Gammarus Pseudolimnaeus and Hexagenia - limbata were 2 and 15 ug/L, respectively (Oseid and Smith, 1974a, 197413). Some species 

# 0

ctypical of normally stressed habitats,Asellus spp., were much more resistant (Oseid and Smith, 1974~). Sulfide criteria for domestic or livestock use have not been established because the unpleasant odor and taste would preclude such use at hazardous concentrations. It is recognized that the hazard from hydrogen sulfide to aquatic life is often localized and transient. Available data indicate that water containing concentrations 

### of 2.0 ug/L undissociated H2Swould not be hazardous tomost fish and other aquatic wildlife, but concentrations in excess of 2.0 ug/L would constitute a long

-term hazard.

I

(QUALITY CRITERIA FOR WATER, JULY 1976) PB-263943 SEE APPENDIX C FOR METHODOLOGYTAINTING SUBSTANCES

Materials should not be present in concentrations that individually or in combination produce undesirable flavors which are detectable by organoleptic tests performed on the edible portions of aquatic organisms. RATIONALE : Fish or shellfish with abnormal flavors, colors, tastes or odors are either not marketable or will result in consumer complaints and possible rejection of the food source even though subsequent lots of organisms may be acceptable. Poor product quality can and has seriously affected or eliminated the commercial fishing industry in some areas. Recreational fishing also can be affected adversely by off

-flavored fish. For the majority of sport fishermen, the consumption of their catch is part of their recreation and off

-flavored catches can result in diversion of the sportsmen to other water bodies. This can have serious economic impact on the established recreation industries such 

### astackleand bait sales and boat and cottagerental. 

# 0

Water Quality Criteria, 1972 (NAS, 1974) lists a number of wastewaters and chemical compounds that have been found to lower the palatability of fish flesh. Implicated wastewaters included those from 2,4-D manufacturing plants, kraft and neutral sulfite pulping processes, municipal wastewater treatment plants, oily wastes, refinery wastes, phenolic wastes, and wastes from slaughterhouses. The 9ist of imp1icated chemical compounds is long: it includes cresol and phenol compounds, kerosene, naphthol, styrene, toluene, and exhaust outboard motor fuel. As little as 0.1 ug/L o-chlorophenol was reported to cause tainting 

### .. 

# aof fish flesh. Shumway and 

# a Palensky 1973) determined estimated threshold concentrations for 22 organic compounds. The values ranged from 0.4 ug/L (2

## , 4

-dichlorophenol) to 95,000 ug/L (formaldehyde) 

# . An additional 12 compoundswere tested, 7 of which were not found to impair flavor at or near lethal levels. Thomas (1973) reviewed the literature review on tainting substances revealed serious problems that have occurred. Detailed studies and methodology used to evaluate the palatability of fishes in the Ohio River as affected by various waste discharges showed that the susceptibility of fishes to the accumulation of tainting substances is variable and dependent upon the species, length of exposure, and the polJutant. As little as 5 ug/L of gasoline can impart off

-flavors to fish (Boyle, 1967).

(QUALITY CRITERIA FOR WATER, JULY 1976) PB

-263943 SEE APPENDIX C FOR METHODOLOGYTEMPERATURE
Freshwater Aquatic 

### Life For any time of year, there are two upper limiting temperatures for a location (based on the important sensitive species found there at that time): 1. One limit consists 

### of a maximum temperature for short exposures that is time dependent and is given by the speciesspecific equation: Temperature =(l/b) (log [time 

### 3

-a) 

# - 2, C (C,) 10 (min) where: loglo = logarithm to base 10 (common logarithm)
a = intercept on the "y" or logarithmic axis of the l'ine fitted to experimental data and which is available for some species from Appendix 11

-C, National Academy of Sciences 1974 document. b = slope of the line fitted to experimental data and available for some species from Appendix 11-C, of the National Academy of Sciences document. and 2. 

### The second value 

### is a limit on the weekly average temperature that:
a. In the cooler months (mid

-October to mid

-April in the north and December 

### to February in the south) will protect against mortality of importr to mid

-April in the north and December to February in the south) will protect against mortality of important species if the elevated plume temperature is suddenly dropped to the ambient temperature, with the limit being theb. acclimation temperature minus apt0 when the 

### lower lethal threshold temperature equals the ambientwater temperature (in some regions this limitation may also be applicable in summer).
or 

### In the warmer months (April through October in the north and March through November in the south) 

### is determined by adding to the physiological optimum temperature

(usually for growth) a factor calculated as one-third of the difference between the ultimate upper incipient lethal temperature and the optimum temperature 

### €or the most sensitive important species (and appropriate life state) that normally is found at that location and time.
or

c. During reproductive seasons (generallyApril through June and September through October 

### in the north and March through May and October through November in the south) the limit is that temperature that meets sitespecific requirements for successful migration, spawning, egg incubation, fry rearing, and other reproductive functions of important species. These local requirements should supersede all other requirements when they are applicable.
or d. There is a site

-specific limit that 

### is found necessary to preserve normal species diversity or prevent appearance of nuisance organisms.Marine Aquatic 

# - Life 

### In order to assure protection 

### of the characteristic indigenous marine community of a water body segment from adverse thermal effects:
a. the maximum acceptable increase 

### in the weekly average temperature resulting from artificial
sources is1' C (1.8 F) during all seasonsofthe year, providtng the summer maxima are not exceeded; and b. daily temperature cycles characteristic of the water body segment should not be altered in either amplitude or frequency. Summer thermal maxima, which define the upper thermal limits for the communities 

### of the discharge area, should be established


### on a site

-specific basis. Existing studies suggest the following regional limits: 

# 0Short

-term Maximum Maximum True Daily Mean* Sub tropical regions (southof Cape Canaveral and Tampa Bay, Florida, and Hawaii 32.2' C (90° F) 29.4O C (85' F)

Cape Hatteras, N.C., to Cape Canaveral, Fla. Long Island (south shore) 30.6O C (87O F) 27.8O C (82O F) 32.2' C (90' F) 29.4O C (85O'F)

to Cape Hatteras, N.C. (* True Daily Mean = average of 24 hourly temperature readings.) Baseline thermal conditions should be measured at a site where there is no unnatural thermal addition from any source, which is 

### in reasonable proximity to the thermal discharge (within 5 miles) and which has similar hydrography to that of .the receiving waters at the discharge. INTRODUCTION: The uses of water by man 

### in and out of its natural situs in the environment are affected by its temperature. Offstream domestic uses and instream recreation are both partially temperature dependent. Likewise, the 

### 1ife associated with the aquatic environment in any location has its species composition and activity regulated by water temperature. Since essentially all of these organisms are so-called "cold blooded" or poikilotherms, the temperature of the water regulates their metabolism and ability to survive and reproduce effectively. Industrial uses for process water and for coolingare likewise regulated by the water's temperature. Temperature, therefore, is an important physical parameter which to some extent regulates many of the beneficial uses of water. The Federal Water Pollution Control Administration in 1967 called temperature acatalyst, 

### a depressant, an activator, a restrictor, a stimulator,
a controller, a killer, one of the most important and most influential water quality characteristics to life in water." 

# 0

RATIONALE: The suitability of water for total body immersion is greatly affected by temperature. 

### In temperate climates, dangers from exposure to low temperatures is more prevalent than exposure to elevated water temperatures. Depending on the amount of activity by the swimmer, comfortable temperatures range from 20° C to 30° 

### e. Short durations of lower and higher temperatures can be tolerated by most individuals. For example, for a 30

-minute period, temperatures of 10' C or 35O C can be tolerated without harm by most individuals (NAS, 1974). Temperature also affects the self-purification phenomenon in water bodies and therefore the aesthetic and sanitary qualities that exist. Increased temperatures accelerate the biodegradation of organic material both 

### in the overlying water and in bottom deposits which makes increased demands on the dissolved oxygen resources of a given system. The typical situation is exacerbated by the fact that oxygen becomes less soluble as water temperature increases. Thus, greater demands are exerted on an increasingly
scarce resource which may lead to total oxygen depletion and obnoxious septic conditions. These effects have been described by Phelps (1944) 

## , Carp (1963), and Velz (1970). Indicator enteric bacteria, and presumably enteric pathogens,
are likewise affected by temperature. It has been shown that 

# - both total and fecal coliform bacteria die away more rapidly in the environment with increasing temperatures (Ballentine andKittrell, 1968). Temperature effects have been shown for water treatment processes. Lower temperatures reduce the effectiveness of coagulation with alum and subsequent rapid sand filtration. In
one study, difficulty was especially pronounced below 5O C (Hannah, et al., 1967). Decreased temperature also decreases the effectiveness 

### of chlorination. Based on studies relating chlorine dosage 

### to temperature, 

### and with a 30

-minute contact time, dosages required for equivalent disinfective effect increased by as much as a factor of 3 when temperatures were decreased from 20° C to loo C (Reid and Carlson, 1974). Increased temperature may increase the odor of water because of the increased volatility of odor

-causing compounds (Bumson, 1938). Odor problems associated with plankton may also be aggravated. The effects of temperature on aquatic organisms have been the subject of comprehensive literature reviews (Brett,1956; Fry, 1967; FWPCA, 1967; Kine, 1970) and annual literature reviews published by the Water Pollution Control Federaticn (Coutant, 1968, 1969, 1970, 1971; Coutant and Goodyear, 1972; Coutant and Pfuderer, 1973, 1974). Only highlights from the thermal effects
on aquatic life are presented here. Temperature changes in water bodies can alter the existing aquatic community. The dominance of various phytoplankton groups in specific temperature ranges has been shown. For example, from 20° C to 25' C, diatoms predominated; green algae predominated from 30' C: to 35O C and blue

-greens predominated above 3.5' C

### airns, 1956). Likewise, changes from a coldwater fishery to a warm-water fishery can occur because temperature may be directly lethal toadults or fry cause a reduction of activityor limit 

# 0 (c

reproduction (Brett, 1960) Upper and lower limits for temperature have been established for many aquatic organisms. Considerably more data 

### exist for upper as opposed to lower limits. Tabulations of lethal temperatures for fish and other organisms are available (Jones, 1964: FWPCA, 1967 NAS, 1974). Factors such as diet, activity, age, general health, osmotic stress, and even weather contribute tothe lethality

### of temperature. The aquatic species, thermal accumulation state and exposure time are considered the critical factors (Parker and Xrenkel, 1969). The effects of sublethal temperatures on metabolism, respiration,behavior, distribution and migration, feeding rate, growth, and reproduction have been summarized by Be Sylva (1969). Another study has i l l u s t r a t e d t h a t inside the tolerance zone there is encompassed a more restrictive temperature range in which normal activity and growth occur and yet an even more restrictive zone inside that in which normal reproduction will
occur (Brett, 1960). De Sylva (1969) has summarized available data on the combined effects of increased temperature and toxic materials on fish indicate that toxicity generally increases with increased temperature and that organisms subjected to stress from toxic materials are less tolerant of temperature extremes. The tolerance of organisms toextremes of temperature is a function of their genetic ability to adapt tothermal changes 

# 0

~within their characteristic temperature range, the acclimation temperature prior to exposure, and the time of exposure to the elevated temperature (Coutant, 1972). The upper incipient lethal temperature or the highest temperature that 50 percent of a sample of organisms can survive is determined on the organism at the highest sustainable acclimation temperature. The lowest temperature that 50 percent of the warm acclimated organisms can survive in 

### is the ultimate lower incipient lethal temperature. True acclimation to changing temperatures requires several days

(Brett, 1941). The lower end of the temperature accommodation range for aquatic life is 0' C in freshwater and somewhat less for saline waters. However, organisms acclimated 

### to relatively
warm water, when subjected to reduced temperatures that 

### under other conditions of acclimation would not be detrimental, may suffer a significant mortality caused by thermal shock (Coutant, 1972). Through the natural changes in climatic conditions, the temperatures of water bodies fluctuate daily, as well as seasonally. These changes do not eliminate indigenous aquatic populations, but affect the existing community structure and the geographic distribution of species. Such temperature changes are necessary to induce the reproductive cycles of aquatic organisms and to regulate other life factors (Mount, 1969). Artificially induced changes such as the return 

### of cooling water or the release of cool hypolimnetic waters from impoundmentsmay alter indigenous aquatic ecosystems (Coutant, 1972). Entrained organisms may be damaged by temperatureincreases across cooling water condensers if the increase is sufficiently great or the exposure period sufficiently long. Impingement upon condenser screens, chlorination for slime control, 

### or other physical insults damage aquatic life (Raney, 1969: Patrick, 1969 (b)). However, Patrick (1969(a)) has shown that algae passing through condensers are 

### not injured if the temperature 

### of the outflowing water does not exceed 345O C. In open waters elevated temperatures nay affect periphyton, benthic invertebrates, and fish, in addition to causing shifts in algal dominance. Trembley (1960) studies of the Delaware River downstream from a power plant concluded that the periphyton population was considerably altered by the discharge. The number and distribution of bottom organisms decrease as water temperatures increase. The upper tolerance limit for a balanced benthic population structure is approximately 32O C, A 

# 0

large number of these invertebrate species are able to tolerate higher temperatures than those required for reproduction (FWPCA, 1967). 

### In order to define criteria for fresh waters, Coutant (1972) cited the following was cited as currently definable requirements: 1. Maximum sustained temperatures that are consistent with maintaining desirable levels of productivity, 2. maximum levels of metabolic acclimation to warm temperatures that will permit return to ambient winter temperatures should artificial sources of heat cease, 3. Time

-dependent temperature 1imitations for survival of brief exposures to temperature extremes, both upper and lower,4. Restricted temperature ranges for various states of reproduction, including (for fish) gametogenesis, spawning migration, release of gametes, development of the embryo, commencement of independent feeding (and other activities) by 

### j



### uveni

### 1es

## , and temperatures required for metamorphosis, emergence, 

### or other activities of lower forms, 5. Thermal limits for diverse species compositions of aquatic communities, particularly where reduction in diversity creates nuisance growths of certain organisms, or where important food sources (food chains) are altered, 6. Thermal requirements of downstream aquatic life (in rivers) where upstream diminution of a coldwater resource will adversely affect downstream temperature requirements. The major portion of such information that is available, however, is for freshwater fish species rather than lower forms of marine aquatic life. The temperature

-time duration for short

-term exposures such that 50 percent of a given population will survive an extreme temperature frequently is expressed mathematically by fitting experimental data with a staright line on a semi

-logarithmicplot with time on the logarithmic scale and temperature on the linear scale (see fig. 1). In equation form this 50percent mortality relationship 

### is: loglo (time 

### (minutes)) = a 

### + b (Temperature (O C)) where: loglo= logarithm to base 10 (common logarithm)
a = intercept on the "y" or logarithmic axis of the line fitted to experimental data and which is available for some species from Appendix 11-C, of the National Academy of Sciences document. b = slope of the line fitted to experimental data and which is available for some species from Appendix 11-C, of the National Academy of Sciences document. To provide a safety factor so that none or only a few organisms will perish, it has been found experimentally that a

### criterion of 2O C 

### below maximum temperature is usually sufficient (Black, 1953). To 

### provide safety for all the organisms, the temperature causing a median mortality for 50 

### percent of the population would be calculated and 

### reduced by2' C 

### in the case of an elevated temperature. Available scientific information includes upper and lower incipient lethal temperatures, coefficients I1at1 and llbll 

### for the thermal resistance equation, 

### and information of size, life stage, and geographic source of the particular test species (Appendix 11-C, NAS, 1974). 

### Maximum temperatures 

### for an extensive exposure (e.g., more than 1 

### week) must be divided into those forwarmer periods and winter. Other than for reproduction, the most temperaturesensitive life function appears to 

### be growth (Coutant, 1972). 

### Coutant (1972) 

### has suggested that a satisfactory estimate of a 

### limiting maximum weekly mean temperature may be an average of the optimum temperature for growth and the temperature 

### €or zero net growth. Because of the difficulty 

### in determining the temperature of
zero net growth, essentially the same temperature can be derived by adding to the optimum essentially 

### to temperature (for growth 

### or other physiological functions) 

### a factor calculated 

### as onethird of 

### the difference between the ultimate upper incipient lethal temperature and the optimum temperature (NAS, 1974). 

### In equation form: Maximum weekly (ultimateupper optimum) average = 

### optimum 

## + 1/3 

### (incipient lethal

# - temperature) temperature temperature (temperature) Since temperature tolerance varies with various states of development of a particular species, the criterion for 

### a -particular location would be calculated for the most important lifeform likely tobe present during a particularmonth. One caveat in using the maximum weekly mean temperature is that the limit for short

- term exposure must not be exceeded. Example calculations for predicting the summer maximum temperatures for short

-term survival and for extensive exposure for 

### various fish species are presented inTable 11. These calculations use the above equations and data from EPA's Environmental Research Laboxatory in Duluth. The winter maximum temperature must not exceed the ambient water temperature by more than the amount of change a specimen acclimated to the plume temperature can tolerate. Such a change could occur by a cessation of the source of heat or by the specimen being driven from an area by addition of biocides or other factors. However, there are inadequate data to estimate a safety factor for the Isno stress" level from cold shocks (NAS, 1974). Figure 2 was developed from available data 

### in the literature (ERL

-Duluth, 1976) and can be used for estimating allowable winter temperature increases. Coutant (1972) has reviewed the effects of temperature on aquatic life reproduction and development. Reproductive events
are noted as perhaps themost thermallyrestricted of all life phases assuming other factors are at or near optimum levels. Natural short

- term temperature fluctuations appear to cause reduced reproduction of fish and invertebrates.TABLE 11.

-Example Calculated Values for Maxima for Survival for Juveniles and Adults During the Summer (Centigrade and Fahrenheit). Species Growtha Maxima Maximum Weekly Average Temperatures for Growth and Short

-Term

b Atlantic salmon Bigmouth buffalo Black crappie Bluegill Brook trout Carp Channel catfish Coho salmon Emerald shiner Freshwater drum Lake herring (Cisco) Largemouth bass Northern pike Rainbow trout Sauger Smallmouth bass Smallmouth buffalo Sockeye salmon Striped bass Threadfin shad White bass White crappie White sucker Yellow perch 20 (68) 27 (81) 32 (90) 19 (66) 32 (90) 18 (64) 30 (86) 17 (63) 32 (90) 28 (82) 19 (66) 25 (77) 29 (84) 18 (64)

28 (82) 28 (82) 29 (84) 23 (73)

35 (95) 24 (75) 35 (95) 24 (75)

25 (77) 30 (86) 24 (75) 34 (93)

22 (72)

a 

# - Calculated according to the equation (using optimum temperature for growth) maximum weekly average temperature for growth = optimum temperature 

## + 1/3 (ultimate incipient lethal temperatureoptimum temperature. b 

# - Based on temperature (OC) = l/b (log” time(min.)

-a) 2O C, acclimation at the maximum weekly average temperature €or summer growth, and data in Appendix 11-C of Water Quality Criteria, published by National Academy of Sciences.
c

# - Based on data for larvae (ERL

-Duluth, 1976). 

# 0

-.,There are indadequate data available quantitating the most temperature

-sensitive life stages among various aquatic species. Uniform elevation of temperature 

### a few degrees but still within the spawning range may lead to advanced spawning for spring spawning species and delays for fall spawners. Such changes may not be detrimental unless asynchrony occurs between newly hatched juveniles and their normal food source. Such asynchrony may be most pronounced among anadromous species 

### or other migrants who pass from the warmed area to a normally chilled, unproductive
area. Reported temperature data 

### on maximum temperatures for spawning and embryo survival have been summarized 

### in Table 12 (from ERL

-Duluth 1976). Although the limiting effects of thermal addition 

### to estuarine and marine waters are not as conspicuous in the fall, winter, and spring as during the summer season of maximum heat stress, nonetheless crucial thermal limitations do exist. Hence, 

### it is important that the thermal additions to the receiving waters be minimized during all seasons of the year. Size of harvestable stocks of commercial fish and shellfish, particularly
near geographic limits of the fishery, appear to be markedly influenced by slight changes 

### in the long

-term temperature regime (Dow, 1973). Jefferies and Johnson (1974) studied the relationship between temperature and annual variation 

### in 7

-year catch data for winter flounder,Pseudopleuronectes _-__-_--_-I americanus in Narragansett Bay, Rhode Island, revealed that a 78 percent decrease in annual catch correlated closely with a 0.5OC increase in the averagetemperature over the 30-month period between spawning and recruitment into the fishery. Sissenwine's 1974 model predicts a 68 percent reduction of recruitment in ye1Powtail flounder, Limanda 

### --- ferrugiia, with a l0C long-term elevation in southern New England waters.TABLE 12. Summary of Reported Values for Maxima for Embryo Survival During the Spawning Season (Centigrade and Fahrenheit) Maximum Weekly Average Temperature for Spawning 

### and Short

-Term

Species
Atlantic Salmon Bigmouth Buffalo Black Crappie Bluegill Brook Trout carp Channel Catfish Coho Salmon Emerald Shiner Freshwater Drum Lake Herring (Cisco) Largemouth Bass Northern Pike Rainbow Trout Sauger Smallmouth Bass Smallmouth Buffalo Sockeye Salmon Striped Bass Threadfin Shad White Bass White Crappie White Sucker Yellow Perch Spawning, Embryo Survivalb 5 17 25

9 21 27 10 24 21

3 21 11

9 17 17 10 18 18 17 18 10 12 I 10 (41) 7

77

### 1 34 70) 33 (63) 27

48) 13 81) 29 50) 13 75) 28 70) 26 37) 8 70) 27 52) 19 48) 13 50) 21 63

### 1 21 13 63) 50) 64

### 1 24 64

### 1 34 63) 26 23 20 64) 20 50) 54) 

### a 

# - the optimum or mean of the range of spawning temperatures reported for the species (ERL

-Duluth, 1976). b 

# - the upper temperature for successful incubation and hatching reported for the species (ERL

-Duluth, 1976)

# -
c 

# - upper temperature for spawning.Community balance can be influenced strongly by such temperature

-dependent factors as rates of reproduction, recruitment, and growth of each component population. A few degrees elevation in average monthly temperature can appreciably alter a community through changes in interspecies relationships. A 50 percent reduction 

### in the softshell clam fishery in Maine by the green crab, Carcinus maenus, illustrates how an increase in winter temperatures can establish new predator

-prey relationships. Over a period of 4 years, there was a natural amelioration of temperature and the monthly mean for the coldest month of each year did not fall below 2OC. This apparently precluded appreciable ice formation and winter cold kill of the green crab and permitted a major expansion of its population, with increased predation of the softshell clam resulting (Glude, 1954: Welch, 1968). Temperature 

### is 

### a primary factor controlling reproduction and
can influence many events of the reproductive cycle from gametogenesis to spawning. Among marine invertebrates, initiation 

### of reproduction (gametogenesis) 

### is often triggered during late winter by attainment of a minimum environmental threshold temperature. 

### In some species, availability of adequate food is also a requisite (Pearse, 1970; Sastry, 1975: devlaming, 1971). Elevated temperature can limit gametogenesis by preventing accumulation of nutrients in the gonads. This problem could be acute during the winter if food availability and feeding activity is reduced. Most marine organisms spawn during the spring and summer; gametogenesis is usually initiated during the 

# 0previous fall. It should also be noted that some species spawn only during the fall (herrinhg) ,while others during the winter and very early spring. At the higher latitudes, winter breeders include such estuarine community dominants as acorn barnacles, Balanus balanus and B. balanoides, the edible blue mussel Mytilus 

## _ -- -

--- - I edulis sea urchin, Strongylocentrotus drobachiensis, sculpin, and the winter flounder, Pseudopleuronectes - americanus. The two boreal barnacles require temperatures below 10°C before egg production will be initiated (Crisp, 1957). It is clear that adaptations for reproduction exist which are dependent on temperature conditions close to the natural cycle. Juvenile and adult fish usually thermoregulate behaviorally by moving to water having temperatures closest to their thermal preference. This provides a thermal environment which approximates the optimal temperature for many physiological functions, including growth (Neil1 and Magnuson. 1974). As a consequence, fishes usually are attracted to heated water during the fall,winter, and spring. Avoidance will occur as warmer temperature exceeds the preferendum by 1 to 3OC (Coutant, 1975). This response precludes problems of heat stress for juvenile 

### and adult fishes during the summer, but several potential problems exist during the other seasons. The possibility of cold shock and death of plume

-entrained fish resulting from winter plant shutdown is well recognized. Also, increased incidence of disease and a deterioration of physiological condition has been observed among plume

-entrained fishes, perhaps because of insufficient food (Massengill, 1973). A weight loss of approximately 10 percent for each lo C rise in water temperaturehas been observed in fish when food is absent. (Phillips et al., 1960) There may also be indirect adverse effects on the indigenous community because of increased predation pressure if thermal addition leads to 

### a concentration of fish which are dependent on this community for their food. Fish migration 

### is often linked to natural environmental temperature cycles. In early spring, fish employ temperature 

### as their environmental cue to migrate northward (e.g., menhaden, bluefish) or to move inshore (winter flounder). Likewise, water temperature strongly influences timing of spawning runs ofanadromous fish into rivers (Leggett and Whitney, 1972). 

### In the autumn, a number of juvenile marine fishes and shrimp are dependent on a drop in temperature to trigger their migration from estuarine nursery grounds for oceanic dispersal or southward migration (Lund and Maltezos, 1970; Talbot, 1966). Thermal discharges should not alter diurnal and tidal temperature variations normally experienced by marine communities. Laboratory studies show thermal tolerance to be enhanced when animals are maintained under a diurnally fluctuating temperature regime rather than at a constant temperature (Costlow and Bookhout, 1971; Furch, 1972; Hoss, et al.,). A daily cyclic regime can be protective additionally as it reduces duration of exposure to extreme temperatures (Pearce, 1969; Gonzalez, 1972). 

# 0

Summer thermal maxima should be established to protect the various marine communities within each biogeographic region. During the summer, naturally elevated temperatures may be of

-1sufficent magnitude to cause death or emigration (Glynn, 1968; Vaughn, 1961). This more commonly occurs in tropical and warm temperate zone waters, but has been reported for enclosed bays and shallow waters in other regions as well (Nichols, 1918). Summer heat stress also can contribute to increased incidence of disease or parasitism (Sinderman, 1965)

### : reduce or block sexual maturation (Thorhaug, et al., 1971: deVlaming, 1972); inhibit or block embryonic cleavage of larval development (Calabrese, 1969); reduce feeding and growth of juveniles and adults (011a and Studholme, 1971): result in increased predation (Gonzalez, 1972); and reduce productivity of macroalgae and seagrasses (South and Hill, 1970; Zieman, 1970). The general ceilings set forth here
are derived from studies delineating limiting temperatures for the more thermally sensitive species or communities of a biogeographic region. Thermal effects data are presently insufficient to set general temperature limits for all coastal biogeographic regions. The data enumerated in the Appendix, plus any additional data subsequently generated, should be used to develop thermal limits which specifically consider communities relevant to given water bodies.

(QUALITY CRITERIA FOR WATER, JULY 1976) PB-263943 SEE APPENDIX C FOR METHODOLOGY2,3,7,8-TETRACHMRODIBENZO-P-DIOXIN CRITERIA: Aquatic Life Not enough data are available concerning the effects of 2,3,7,8-TCDD 

### on aquatic life and its uses to allow derivation of national criteria. The available information indicates that acute values for some freshwater animal species are >1.0 ug/L;
some chronic values are <0.01 ug/L; and the chronic value for rainbow trout is <0.001 ug/L. Because exposures of
some species of fishes 

### to 0.01 ug/L for <6 days resulted in substantial mortality several weeks later, derivation of aquatic life criteria for 2,3,7,8-TCDD may require special consideration. Predicted bioconcentration factors (BCFs) for 2,3,7,8-TCDD range from 3,000 

### to 900,000, but the available measured BCFs range from 390 to 13,000. If the BCF is 5,000, 

# 0

concentrations >0.00001 ug/L should result in concentrations in edible freshwater and saltwater fish and shellfish that exceed levels identified in a U.S. FDA health advisory. If the BCF is >5,000 or if uptake in a field situation is greater than that in laboratory tests, the value of 0.00001 ug/L will be too high.
Human Health For the maximum protection of human health from the potential carcinogenic effects of 2,3,7,8-TCDD exposure through ingestion of contaminated water and contaminated aquatic orqanisms, the -
. ambient water concentration should be zero. This criterion isbased on the nonthreshold assumption for 2,3,7,8-TCDD. However,
zero may notbean attainable level atthistime.

(49 F.R. 5831, February 15, 1984) SEE APPENDIX B FOR METHODOLOGYTETRACHLOROETHYLENE
Aquatic Life The available data for tetrachloroethylene indicate that acute and chronic toxicity to freshwater aquatic life
occurs at concentrations as low as 5,280 and 840 ug/L, respectively, and would occur at lower concentrations among species that are more sensitive than those tested. The available data for tetrachloroethylene indicate that acute and chronic toxicity to saltwater aquatic life
occurs at concentrations as low as 10,200 and 450 ug/L, respectively, and would occur at lower concentrations among species that are more sensitive than those tested.
Human Health For the maximum protection of human health from the potential carcinogenic effects of exposure to tetrachloroethylene through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentrations should be zero, based
on the nonthreshold assumption for this chemical. However, zero level may not be attainable at the present time. Therefore, the levelswhich may result in incremental increase of cancer risk over the lifetime are estimated at and The corresponding recommended criteria are 8.0 ug/L, 0.80 ug/L, and 0.08 ug/L, respectively. If these estimates are made forconsumption of aquatic organisms only, excluding consumption of water, the levels are 88.5 ug/L, 8.85 ug/L, and 0.88 ug/L, respectively.

(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYCRITERIA: THALLIUM
Aquatic Life The available data for thallium indicate that acute and chronic toxicity to freshwater aquatic life occurs at concentrations as low as 1,400 and 40 ug/L, respectively, and would occur at lower concentrations among species that are more sensitive than those tested. Toxicity to one species of fish
occurs at concentrations as low as 20ug/L after 2,600hours of exposure. The available data for thallium indicate that acute toxicity 

### to saltwater aquatic life occurs at concentrations as low as 2,130 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No data are available concerning the chronic toxicity of thallium to 

# 0

sensitive saltwater aquatic life.

Human Health For the protection of human health from the toxic properties of thallium ingested through water and contaminated aquatic organisms, the ambient water criterion is determined to be 13 U9/L. For the protection of human health from the toxic properties of thallium ingested through contaminated aquatic organisms alone, the ambient water criterion 

### is determined to be 48 ug/L.
(45 F.R. 79318, November 28, 1980) 

# 0 SEE APPENDIX B FOR METHODOLOGY

# m CRITERIA: TOLUENE
Aquatic Life The availab-2 data for toluene indicate t at acute toxicity to freshwater aquatic life occurs at concentrations as low as 17,500 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No data are available concerning the chronic toxicity of toluene to sensitive freshwater aquatic life. The available data for toluene indicate that acute and chronic toxicity to saltwater aquatic life occurs at concentrations as low as 6,300 and 5,000ug/L, respectively, and would occur 

### at lower concentrations among species that are more sensitive than those tested. 

# 0 Human Health For the protection of human health from the toxic properties 

### of toluene ingested through water and contaminated aquatic organisms, the ambient water criterion is determined to be 14.3 w/L. For the protection of human health from the toxic properties of toluene ingested through contaminated aquatic organisms alone, the ambient water criterion is determined to be 424 

### W/L-

(45 F.R. 79318, November 28, 1980)
NOTE: The U.S. EPA is currently developing Acceptable Daily Intake (ADI)or Verified Reference Dose (RfD)values €or Agency

-wide use for this chemical. The new value should be substituted when it becomes available. The January,

* - 1986, draft Verified Reference Dose document cites an RfD of 0.3 mg/kg/day for toluene. SEE APPENDIX B FOR METHODOLOGY 

# 0TOXAPHENE
CRITERIA: Aquatic 

# - Life For toxaphene the criterion to protect freshwater aquatic life as derived using the Guidelines is 0.013 ug/L as a 24

-hour average, and the concentration should not exceed 1.6 ug/L at any time. For saltwater aquatic life the concentration of toxaphene should not exceed 0.070 ug/L at any time. No data are available concerning the chronic toxicity of toxaphene to sensitive saltwater aquatic life.

Human Health For the maximum protection of human health from the potential carcinogenic effects of exposure to toxaphene through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentration should be zero, based on the non threshold assumption for this chemical. However, zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer risk over the lifetime are estimated at and The corresponding recommended criteria are 7.1 ng/L, 0.71 ng/L, and 0.07 ng/L, respectively. If these estimates are made for consumption of aquatic organisms only, excluding consumption of water, the levels are 7.3 ng/L, 0.73 ng/L, and 0.01 ng/L, respectively. 

# 0

-. \ - (45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYCRITERIA: TRICHLOROETHYLENE
Aquatic Life The available data for trichloroethylene indicate that acute toxicity to freshwater aquatic life occurs at concentrations as low 

### as 45,000 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. 

### No data are available concerning the chronic toxicity of trichloroethylene to sensitive freshwater aquatic life but the behavior of one species is adversely affected at concentrations as low as 21,900 ug/L. The available data for trichloroethylene indicate that acute toxicity to saltwater aquatic life occurs at concentrations as low as 2,000 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No data are available concerning the chronic toxicity of trichloroethylene to sensitive saltwater aquatic life. 

# 0

Human Health For the maximum protection of human health from the potential carcinogenic effects of exposure to trichloroethylene through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentration should be zero, based
on the nonthreshold assumption for this chemical. However,
zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer risk over the lifetime are estimated at lom5, loe6, and lo-’* The corresponding recommended criteria are 27 ug/L, 2.7 ug/L, and 

# 0

I_ 0.27 ug/L, respectively. If these estimates are made forconsumption of aquatic organisms only, excluding consumption of water, the levels are 807 ug/L, 80.7 ug/L, and 8.07 ug/L, respectively.

(45 F.R. 79318, November 28, 1980) SEE APPENDIX 

### B FOR METHODOLOGYCRITERIA: VINYL CHLORIDE

Aquatic Life No freshwater organisms have been tested with vinyl chloride and no statement can be made concerning acute or chronic toxicity. No saltwater organisms have been tested with vinyl chloride and no statement can be made concerning acute or chronic toxicity.
Human Health For the maximum protection of human health from the potential carcinogenic effects of exposure to vinyl chloride through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentrations should be zero, based
on the nonthreshold assumption for this chemical. However,
zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of
cancer risk over the lifetime are estimated at 10-5r and The corresponding recommended criteria are 20 ug/L, 2.0 ug/L, and 0.2 ug/L, respectively. If these estimates are made for consumption of aquatic organisms only, excluding consumption of water, the levels are 5,246 ug/L, 525 ug/L, and 52.5 ug/L, respectively.

(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYZINC CRITERIA: Aquatic 

# - Life For total recoverable zinc the crit rion toprotect fre hwater aquatic life as derived using the Guidelines is 47 ug/L as a 24- hour average and the concentration (in ug/L) should not exceed the numerica1 value given by 0.83 [ln(hardness)]+1.95) at any time. For example, at e( hardnesses of 50, 100, and 200 mg/L as CaC03 the concentration of total recoverable zinc should

### not exceed 180, 320, and 570 ug/L at

### any time. For total recoverable 

### zinc the criterion toprotect saltwater aquatic life as derived using the Guidelines is 58 ug/L as a 24- hour average and the concentration should not exceed 190 ug/L at any time.

Human Health Sufficient data are not available for zinc to derive a level which would protect against the potential toxicity of this compound. Using available organoleptic data, to control undesirable taste and odor quality of ambient water the estimated level is 5 mg/L. It should be recognized that organoleptic data have limitations as a basis for establishing a water quality criteria, and have no demonstrated relationship to potential adverse human health effects.

(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYI

~ 

# APPENDIX A

### DERIVATION OF THE 1985 

### CRITERION 

## - - - Derivation of numerical national water quality criteria for the protection of aquatic organisms and their uses is a complex process that uses information from many areas of aquatic toxicology. After a decision is made that a national criterion is needed for a particular material, all available information concerning toxicity to, and bioaccumulation by, aquatic organisms is collected, reviewed for acceptability, and sorted. If enough acceptable data on acute toxicity to aquatic animals are available, they are used to estimate the highest 1

-hour average concentration that should not result in unacceptable effects on aquatic organisms and their uses. If justified, this concentration is made a function of a water quality characteristic such as pH, salinity, or hardness. Similarly, data on the chronic toxicity of the material to aquatic animals
are used to estimate the highest 4

-day average concentration that should not cause unacceptable toxicity during a long

-term exposure. If appropriate, this concentration is also related to
a water quality characteristic. Data on toxicity to aquatic plants are examined to determine whether plants are likely to be unacceptably affected by concentrations that should not cause unacceptable effects on animals. Data on bioaccumulation by aquatic organisms are used to determine if residues might subject edible species to restrictions by the U.S. 

### Food and Drug Administration or if such residues might harm some wildlife consumers of aquatic life. All other available data are examined €or adverse effects that might

### be biologically important. If a thorough review of the pertinent information indicates that enough acceptable data are available,numerical national water quality criteria are derived for fresh water or saltwater
or both to protect aquatic organisms and their uses from unacceptable effects due to exposures to high concentrations for short periods of time, lower concentrations for longer periods of time, and combinations 

### of the two.
I. 

### Collection of 

### Data 

# - -- A. 

### Collect all available data on the material concerning (a) toxicity to, and biqaccumulation by, aquatic animals and plants, (b) FDA action levels [12], and (c) chronic feeding studies and long

-term field studies with wildlife species that regularly consume aquatic organisms. 

### B. All data that are used should be available in typed, dated, and signed hard copy (pub1ication, manuscript, letter, memorandum, etc.) with enough supporting information to indicate that acceptable test procedures were used and that the results are probably reliable. 

### In some cases it may be appropriate to 

### obtain additional written information from the investigator, if possible. Information that is confidential or privileged or otherwise not available for distribution should not be used. C. 

### Questionable data, whether published or

### unpublished, should not be used. For example, data should usually be rejected if they are from tests that did not contain a control treatment, tests in which too many organisms in the control treatment died or showed signs of stress or disease, and tests in which distilled or deionized water was used as the dilution water without addition of appropriate salts. D. Data on technical grade materials may be used if 

### appropriate, but data on formulated mixtures and emulsifiable concentrates of the material of 

### concern should not be used. 

### E. For some highly volatile, hydrolyzable, or degradable materials it is probably appropriate to
use only results of flow

-through tests in which the concentrations of 

### test material in the test solutions were measured often enough using acceptable analytical methods. F. 

### Data should be rejected if they were obtained using: 1. Brine shrimp, because they usually occur naturally only in water with salinity greater than 35 

### g/kg. 2. 

### Species that do not have reproducing wild populations in North America (SeeAppendix 1). 3. 

### Organisms that were previously exposed to substantial concentrations of 

### the test 

# 0 t. 

### material or other contaminants.G. Questionable data, data on formulated mixtures and emulsifiable concentrates, and data obtained with nonresident species 

### or previously exposed organisms may be used to provide auxiliary information but should not be used 

### in the derivation of criteria. 11. Required 

# - Data 

## - A. Certain data should be available tohelp ensure that each of the four major kinds of possible adverse effects receives adequate consideration. Results 

### of acute and chronic toxicity testswith representative species of aquatic animals are necessary so that data available for tested species can be considered a useful indication of the sensitivities of appropriate untested species. Fewer data concerning toxicity to aquatic plants
are required because procedures for conducting tests with plants and interpreting the results of such tests are not as well developed. Data concerning bioaccumulation by aquatic organisms
are required 

### only if relevant data are available concerning the significance of residues in aquatic organisms. I



### B. To derive a criterion for freshwater aquatic organisms and their uses, the following should be available: 1. Results of acceptable acute tests (see Section

### IV) with at least one species of freshwater animal in at least eight different families such that all of the following are included:
a.

b.

C.

d.



### e.

f.

g.



### h. the family Salmonidae in the class Osteichthyes
a 

### second family 

### in the class Osteichthyes, preferably a commercially 

### or recreationally important warmwater species (e.g., bluegill, channel catfish, etc.)


### a third family in the phylum Chordata (may be in the class Osteichthyes 

### or may be an amphibian, etc.) a planktonic crustacean (e.g., cladoceran, copepod, etc.)


### a benthic crustacean (e.g., ostracod, isopod, amphipod, crayfish, etc.)
an insect (e.g., mayfly, dragonfly, damselfly, stonefly, caddisfly, mosquito, midge, etc.) 

### a family 

### in a phylum other than Arthropoda 

### or Chordata (e.g., Rotifera, Annelida, Mollusca, etc.)
a family in any order of insect or any phylum not already represented. 2. 

### Acute-chronic ratios (see Section TI) with species of aquatic animals in at least three different families provided that of the three species:a. at least one is a fish b. at least one is an invertebrate
c. 

### at least one is an acutely sensitive freshwater species (the other two may be saltwater species). 3. Results of at least one acceptable test with a freshwater alga or vascular plant (see Section VIII). If plants are among the aquatic organisms that are most sensitive to the material, results of a test with 

### a plant in another phylum (division) should also be available. 4. At least one acceptable bioconcentration factor dete'rmined with an appropriate freshwater species, if a maximum permissible tissue concentration is available (see Section IX)

# . C. To derive a criterion for saltwater aquatic organisms and their uses, the following should be available: 1. Results of acceptable acute tests (see Section IV) with at least one species of saltwater animal in at least eight different families such that all of the following are included:


### a. two families in the phylum Chordata b. a family in 

### a phylum other than Arthropoda
or Chordata

### c. either the Mysidae or Penaeidae family d. three other families not in the phylum Chordata (may include Mysidae 

### or Penaeidae,whichever was not used above)
e. any other family. 2. 

### Acute

-chronic ratios (see section VI) 

### with species of aquatic animals in at least three different families provided that of the three species:
a. at least one 

### is a fish b. at least one is an invertebrate
c. at least one is an acutely sensitive saltwater species (the other one may be a 

### freshwater species). 3. 

### Results of 

### at least one acceptable test with a 

### saltwater alga or vascular plant (see Section 

### VIII. If plants are among the aquatic organisms most sensitive to the material, results of a test with a plant in another phylum (division) should also be available. 4. 

### At least one acceptable bioconcentration factor determined with an appropriate saltwater species, if a maximum permissible tissue concentration is available (see Section IX)* D. If 

### all the required data are available, a numerical criterion can usually be derived, except in special 

# 0

%. 

### cases. For example, derivation of a criterionmight not be possible if the available acutechronic ratios vary by more than a factor of 10 with no apparent pattern. Also, if a criterion is to be relatedtoa water qualitycharacteristic T (see Sections V and VII)

## , more data will be necessary. Similarly, if all required data are not available, 

### a numerical criterion should not be derived except 

### in special cases. For example, even if not enough acute and chronic data 

### are available, 

### it might be possible to

### derive a criterion if the available data clearly indicate that the Final Residue Value should be much lower than either the Final Chronic Value 

### or the Final Plant Value. 

### E. Confidence in a criterion usually increases as the amount of available pertinent data increases. Thus, additional data areusually desirable.

111. Final Acute Value A. Appropriate measures of the acute (short

-term) toxicityofthematerialtoavarietyofspeciesof aquatic animals are used to calculate the Final Acute Value. The Final Acute Value is an estimate

' of the concentration of the material corresponding to a cumulative probability of 0.05 inthe acute toxicity values for the genera with which acceptable acutetests have been conducted on the material. However, insome cases, if the SpeciesMean Acute Value of 

### a commercially or recreational1 y important species is lower than the calculated Final Acute Value, then that Species 

### Mean Acute Value replaces the calculated Final Acute Value in order toprovide protection for that important species. 

### B. Acute toxicity tests should have been conducted using acceptable procedures [13]. C. Except for tests with saltwater annelids and mysids, results of acute tests during which the test organisms were fed should not be used, unless data indicate that the food did not affect the toxicity of the test material. D. Results of acute tests conducted in unusual dilution water, e.g., dilution water in which total 

# 0
organic carbon or particulate matter exceeded 5 mg/L, should not be used, unless a relationship is developed between acute toxicity and organic carbon
or particulate matter or unless data show that organic carbon, particulate matter, 

### etc., do not affect toxicity. 

### E. Acute values should be based on endpoints which reflect the total severe acute adverse impact of the test material on the organisms used in the test. Therefore, only the following kinds of data
on acute toxicity to aquatic animals should be used:1. Tests with daphnids and other cladocerans should be started with organisms less than 24 hours old and tests with midges should be stressed with second- or third

- instar larvae. The result should be the 48

-hr EC50 based on percentage of organisms immobilized plus percentage of organisms killed. If such an EC50 

### is not available from a test, the 48

-hr LC50 should be used in place of the desired 48

-hr EC50. An EC50 or LC50 of longer than 48 hours 

### can be used as long as the animals
were not fed and the control animals were acceptable at the end of the 

### test. 

# a 2. The result 

### of a test with embryos and larvae of barnacles, bivalve molluscs (clams, mussels, oysters, and scallops)

## , sea urchins, lobsters, crabs, shrimp, and abalones should be the 96

-hr EC50 based on thepercentage of organisms with incompletely developed shells plus the percentage of organisms killed. If such an EC50 isnot availablefroma test, the lower of the 9 6

- hr EC50 based on the percentage of organisms with incompletely developed shells and the 96

-hr LC50 should be used 

### inplace of the desired 96

-hr EC50. If the duration of the test was between 48 and 96 hours, the EC50 or LC50 at the end of the test should be used.3. The 

### acute values from tests with 

### all other freshwater and saltwater animal species and older life stages of barnacles, bivalve molluscs, sea urchins, lobsters, crabs, shrimps, and abalones should be the 96-hr EC50 based on the percentage of organisms exhibiting loss of equilibrium plus the percentage of organisms immobilized plus the percentage OF organisms killed. If such 

### an EC50 is not available from a test, the 96

-hr LC50 should be used 

### in place of the desired 96

-hr EC50. 4. Tests with single

- celledorganisms arenot considered acute testa, even if the duration
was 96 hours or less. 

# 0

5. If the tests were conductedproperly, acute 

### values reported 

### as "greaterthan" values and those which are 

### above the solubility of the test material should be used, because rejection 

### of such acute values would unnecessarily lower the Final Acute Value by eliminating 

### acute values for resistant species. F. If the acute toxicity of the material to aquatic animals apparently has been shown to be related to
a water quality characteristic such as hardness 

### or particulate matter for freshwater 

### animals orsalinity or particulate matter for saltwater animals, a Final Acute Equation should be derived based on thatwater qualitycharacteristic. Goto Section V. G. If the available data indicatethatone 

### or more life stages are at least 

### a factor of 2 more resistantthan one ormoreother lifestagesofthe
same species, the data for the more resistant life stages should not be used inthe calculation of the Species Mean Acute Value (SMAV) because a species
can only be considered protected from acute toxicity if all life stages 

### are protected. H. The agreement of the data within and between species should be considered. Acute values that appear to be questionable in comparison with other acute and chronic data for the same species and for other species in the 

### same genus probably should not be used in calculation of a Species Mean Acute Value. For example, if the acute values available For a species or genus differ by more than a factor of 10, some 

### or allof the 

### values probably should not be used in calculations. I. For each species for which at least one acute value 

### is available, the Species Mean Acute Value should be calculated asthegeometricmean of the results of all flow

-through tests in which the concentrations of test material were measured. For a species for which no such result 

### isavailable,the Species Mean Acute Value should be calculated


### as the geometric 

### mean of 

### all available acute values, i.e., 

### results of flow

-through tests in which the concentrations were not measured and results of static and renewal tests based on initial concentrations of test material (nominal concentrations 

### are acceptable for most test materials if measured concentrations are not available).
NOTE: Data reported by original investigators should not be rounded off. Results of 

### all intermediate calculations should be rounded [14] to four significant digits.
The geometric mean of N numbers is the Nth root of 

# 0 NOTE: the product of the N numbers. Alternatively, the geometric mean 

### can be calculated by adding the logarithms of the N numbers, dividing the sum by 

### N, and taking the antilog of the quotient. The geometric 

### mean of twonumbers is the square root of the product of the two numbers, and the geometric mean of one number is that number. Either natural (base 0) or common (base 10) logarithms can be used to calculate geometric
means as long as they areused consistently 

### within each set of data, i.e., the antilog used must match the logarithm Used.NOTE: Geometric means, rather than arithmetic means, are used here because the distributions of sensitivities of individual organisms 

### in toxicity tests on most materials and the distributions of sensitivities of species within a genus aremore likely to be lognormal than normal. Similarly, geometric means are used for acute-chronic ratios and bioconcentration factors because quotients are likely to be closer to lognormal than normal distributions. In addition, division of the geometric mean of a set of numerators by the geometric mean of the set of corresponding denominators will result in the geometric mean of the set of corresponding quotients. J. For each genus 

### €or which one 

### or more Species Mean Acute Values are available, the Genus Mean Acute Value should be calculated as the geometric mean of the Species Mean Acute Values available 

### for the genus. 

### K. Order theGenusMeanAcuteValue fromhigh to low. 

### L. Assign ranks, 

### R, to the Genus Mean Acute Value from vvlvv for the lowest to *'N" €or the highest. If two or more Genus Mean Acute Values are identical, arbitrarily assign them successive ranks. M. Calculate the cumulative probability, P, €or each Genus Mean Acute Value as 

### R/ (N+l).

### N. Select the four Genus 

### Mean Acute Value which have cumulative probabilities closest to 0.05 (if there
are less than 59 Genus Mean Acute Value, these will always be the four lowest Genus Mean Acute Values). Using the selected Genus Mean Acute Values and Fs, 

### calculate: S2= E(ln GMAV)2)- ((Eln GMAV))2/4) (PI

# - ((E /"~))2/4) 0.

L = (E(1n GMAV) 

# - S(E(/Ap)))/4 A = S(/"O.OS) +L FAV = eA (See [113 for development of the calculation procedure and Appendix 2 for example calculation and computer program.) NOTE: Natural logarithms (logarithmstobase el denoted
as 

### In) are used herein merely because they are easier to 

### use on some hand calculators and computers than common (base 10) logarithms. Consistent use of either 

### will produce the same 

### result. P

. If for a commercially orrecreationally important species the geometric mean of the acute values from flow

- through tests in which the concentrations 

### of test material were measured is lower than the calculated 

### Final Acute Value, then that geometric mean should be used as the Final Acute Value instead of the calculated Final Acute

### Value. Q. GO to 

### section VI.

## - IV. Final Acute Equation 

# 0
A. When enough data are available to show that acute toxicity to two or more species is similarly related to 

### a water quality characteristic, the relationship should be taken into account as described in Sections B

-G below or using analysis 

### of covariance [15,16]. The two methods 

### are equivalent and produce identical results. The manual method described below provides an unuerstanding of this application of covariance analysis, but computerized versions of covariance analysis are much more convenient for analyzing large data tests. 

### If two or more factors affect toxicity, multiple regression analysis should be used. B. 

### For each species for which comparable acute toxicity values are available at two or more different values of the water quality characteristic,perform a least squares regression 

### of the acute toxicity values on the corresponding values of the water quality characteristic to obtain the slope and its 95 percent confidence limits €or each species.
NOTE: Because the best documented relationship fitting these data is that between hardness and acute toxicity of metals in fresh water and a log

-log

### relationship, geometric means and natural logarithms of both toxicity and water quality are used in the rest of this section. 

### For relationships based on other water quality characteristics such as pH, temperature, or 

### salinity, no transformation 

### or a 

### different transformation might fit the data better, and appropriate changes will be necessary throughout this section. C. 

### Decide whether the data for eachspecies are useful, taking into account the range and number of the tested values of the water quality characteristic and the degree of agreement within and between species. 

### For example, a slope based
on six datapointsmight be of limitedvalue if it is based only on data for a very narrow range of values of the water quality characteristic. A 

### slope based on only two data points, however, might be useful if it is consistent with other information and if the two points cover a broad enough range of the water quality characteristic. In addition, acute values that appear 

### to be questionable in comparison with other acute and chronic data available for the same species and for other species in the same genus probably should not be used. 

### For example, if after adjustment for the water quality characteristic, the acute values available for a species 

### or genusdifferby more than a factorof 10, probably some or all of the values should be rejected. If useful slopes are not available for at least one fish and one invertebrate or if the available slopes aretoo dissimilar or if too fewdata are availabletoadequatelydefine therelationship between acute toxicity and the water quality characteristic, return to Section IV.G, using the results of tests conducted under conditions and in waters similar tothose commonly used for toxicity tests with the species. D. Individually for each species calculate the geometric mean of the available acute values and then divide each of the acutevalues for species by the mean for the species. This normalizes the values so that the geometric mean of the normalized values for each species individual1 y and for any combination of species is 1.0. 

### E. Similarly normalize the values of thewater quality characteristic for each species individually. F. Individually foreach speciesperform a least squares regression of the normalized acute toxicity values on the corresponding normalized values of the water quality characteristic. The resulting slopes and 95 percent confidence limits


## ~. willbe identical tothose obtained in Section B.NOW, however, if the data are actually plotted, the line of best fit for each individual species 

### will go through the point 1,l in the 

### center of the graph. G. Treat all the normalized data as if they were all for the same species and perform a least squares regression of all the normalized acute values on the corresponding normalized values of the water quality characteristic to obtain the pooled acute slope, V, and its 95 percent confidence limits. If all the normalized data are actually plotted, the lineof best fitwillgo through thepoint 1,l 

### in the 

### center of the graph. H. For each species aalculate the geometric mean, W, of the acute toxicity values and the geometric 

### mean, XI of the values of the 

### water quality characteristic. (These were calculated in steps D and 

### E.) I. For each species calculate the logarithm, Y, of the Species 

### Mean Acute Value at 

### a selected value, 2, of the water q u a l i t y c h a r a c t e r i s t i cusing the equation:

Y = In W

# - v(ln X 

# - In 2). J. For each species calculate the SMAV at Z using the equation: SMAV = eY.
NOTE: Alternatively, the Species Mean Acute Values 

### at Z


### can be obtained by skipping step H using theequations in steps I and J to adjust each acute value individually to 2, and then calculating the geometric mean of the adjusted values €or each species individually. This alternative procedure allows an examination of the range of the adjusted acute values for each species. 

### K. Obtain the Final Acute Value at 

### Z by using the procedure described in Section 1V.J-0. 

### L. If the Species Mean Acute Value at Z of a commercially or recreationally important species is lower than the calculated Final Acute Value at 

### Z, then that Species Mean Acute Value should be 

### used as the Final Acute Value at 

### Z instead of the calculated Final Acute Value. M. The Final Acute Equation is written as: Final Acute 

### Value = .(V[ln(water quality characteristic)] 

## + In A 

# - V[ln 

### Z]), where V = pooled acute slopeandA=FinalAcutevalueat 2. Because V, A, and 2 

### are known, the Final Acute Value can be calculated for any selected value of the 

### water quality characteristic.

V. 

# - Final Chronic Value A. Depending on the data that are available concerning chronic toxicity toaquatic animals, the Final Chronic Value might be calculated inthe
same manner as the Final Acute Value or by dividing the Final Acute Value by the Final Acute-NOTE :



### B. Chronic Ratio. 

### In some cases it may not be possible 

### to calculate 

### a Final Chronic Value.
As the name implies, the acute

-chronic ratio is 

### a way of relating acute and chronic toxicities. The acute

-chronic ratio is basically the inverse of the application factor, but this new name is better 

### because 

### it is more descriptiveand should help prevent confusion between 'application factors" and "safety factors." Acute

-chronic ratios and application factors are ways of relating the acute and chronic toxicities of a material 

### to aquatic organisms. Safety factors are used to provide 

### an 

### extra margin of safetybeyond the known or estimated sensitivities of aquatic organisms. Another advantage of the acute

-chronic ratio is that it willusually be greaterthan 1; this should avoid the confusion 

### as to whether 

### a largeapplication factor is 

### one that is close to unity or one that has a denominator that is much greater than the numerator. Chronic values should be based on results of flowthrough (except renewal is acceptable for daphnids) 

### chronic tests in which the concentrations of test material in the test solutions wereproperly measured atappropriate I

times during the test. 

### .* C. Results of chronic tests 

### in which survival,growth, 

### orreproduction 

### inthe control treatment
was unacceptably low should not be used. The limits of acceptability will depend on the species. D. Results of chronic tests conducted in unusual dilution water, e.g., dilution water in which total organic carbon or particulate matter exceeded 5 mg/L, should not be used, unless a relationship is developed between chronic toxicity and organic carbon or particulate matter or unless data show that organic carbon, particulate matter, etc., do not affect toxicity. E. Chronic values should be based on endpoints and lengths of exposure appropriate tothe species. Therefore, only 

### results of the following kinds of chronic toxicity tests should be used: 1. Life

- cycle toxicity tests consisting of exposures of each of two or more groups of individuals of a species to a different concentration of the test material throughout
a lifecycle. To ensure that all lifestages and life processes are exposed, tests with fish should begin with embryos or newly hatched young less than 48 hours old, continue through 

### maturation and reproduction, and should end not less than 24 days (90 days for salmonids) after the hatching of the next generation. Tests with daphnids should beginwithyoung lessthan24hoursoldandlastfor not less than 21 days. Tests with mysids should begin withyoung less than 24 hours old and continueuntil 7 dayspastthemediantime of first brood release inthe controls. For fish, data should be obtained and analyzed on survival 

### and growth of adults and young, maturation of males and females, eggs spawned per female, embryo viability (salmonids only)

## , and hatchability. For daphnids, data should be obtained 

### and analyzed on survival and young per female. For mysids, data should be obtained and analyzed on survival, growth, and young per female. 2. Partial life

- cycle toxicity tests consisting of exposures of each of two or more groups of individuals of a species of fish to a concentration of the test material through most portions of a life cycle. Partial lifecycle 

### tests are allowed with fish species that require more than a year to reach sexual maturity, so that allmajor life stages can be exposed tothe test material inless than 15 months. Exposure to the test material should begin with immature juveniles at least 2 months prior to active gonad development, continue through maturation and reproduction,

### and end not less than 24 

### days (90 

### days for salmonids) after the hatching of the next generation. Data should be obtained and analyzed on survival and growth 

### of adults and 

### young,maturation of males and females,eggs spawned per female, embryo viability (salmonids only), and hatchability. 3. 

### Early life

-stage toxicity tests consisting of 28- 

### to 32

-day (60 

### days.post hatch for salmonids) exposures of the early life stages of a species of fish from shortly a,fter fertilization through embryonic, larval, and early juvenile development. Data should be obtained and analyzed on survival and growth.
NOTE: 

### Results of 

### an early life

-stage test areused as predictions of results of life

-cycle and partial life

-cycle tests with the same species. Therefore,when results of a life

-cycle or partial life

-cycletest are available, results of an early life

-stage test with the same species should not be used. Also, results of early life

-stage tests in which the incidence of mortalities or abnormalities increased substantiallynear the end of the test should not be used because results of such tests are 

### possibly not good predictions of 

### the results of comparable life

-cycle orpartial 

### 1ife-cycle tests.

# 0 F. A chronic value may be obtained by calculating the geometric mean of the lower and upper chronic limits from a chronic test or by analyzing chronic data using regression analysis. A lower chronic limitis the highest tested concentration (a) in
an acceptable chronic test, (b) which did not
cause an unacceptable amount of adverse effect on any of the specified biological measurements, and (c) below which no tested concentration caused an unacceptable effect. An upper chronic limitis the lowest tested concentration (a) in an acceptable chronic test, (b) which did cause an unacceptable amount of adverse effect on one 

### or more of the specified biological measurements, and 

### (c) above which all tested concentrations also caused such 

### an effect.
NOTE: Because various authors have used 

### a varietyof terms and definitions to interpret and report results of chronic tests, reported results should be reviewed carefully. The amount of effect that 

### is considered unacceptable is often based on a statistical hypothesis test, but might also be defined in terms of a specified percent reduction from the controls. 

### A small percent reduction (e.g., 3 percent) might be considered acceptable
even if it is statistically significantly different 

### from the control, whereas a largepercent reduction (e.g., 30 percent) might be considered unacceptable even if it is not statistically significant. G. If the chronic toxicity of the material toaquatic animals apparently has been shown tobe related to
a water quality characteristic such ashardness or particulate matter for freshwater animals or salinity or particulate matter for saltwater animals, a Final Chronic Equation should be derived based 

### on that water quality characteristic. Go to Section VII. H. If chronic values are available for species in eight families 

### as described 

### in Sections III.B.1 or III.C.1, a Species 

### Mean Chronic Value (SMCV) should be calculated for each species for which at least one chronic 

### value is available by calculating the geometric mean of all chronic values available for the species, and appropriate Genus 

### Mean Chronic Values should be calculated. The Final Chronic Value should

### then be obtained using theprocedure described inSection 1V.J

- 0. Then go to Section V1.M. I. For each chronic value for which at least one corresponding appropriate acute value is available, calculate

### an acute

-chronicratio, using for the numerator the geometric mean of the results of all acceptable flow

-through (except 

# 0
static is acceptable for daphnids) acute tests inthe same dilution water and in which the concentrations were measured. For fish, the acute test(s) should have been conducted with juveniles. The acute test(s) should have been part of the
same study as the chronic test. If acute tests
were 

### not conducted as part of the same study, acute tests conducted in the same laboratory and dilution water, but in a different study, may be used. If no such acute tests are available, results of acute tests conducted 

### in the same dilution water 

### in a different laboratory may be used. If no such acute tests are available, an acute-chronic ratio should not be calculated. J. For each species, calculate the species mean acute-chronic ratio as the geometric mean of all acute-chronic ratios available for that species. K. For some materials the acute-chronic ratio seems to be the same for all species, but for other materials the ratio seems to increase 

### or decrease
as the Species Mean Acute Value (SMAV) increases. Thus the Final Acute-Chronic Ratio can be obtained 

### in four ways, depending on the data available: 1. If the Species Mean Acute-Chronic ratio Seems to increase or decrease as the Species Mean Acute Value increases, the Final Acute-Chronic Ratio should be calculated as the geometric
mean of the acute-chronic ratios for specieswhose Species Mean Acute Values are closeto the Final Acute Value. 2. If no major trend is apparent and the acutechronic ratios for a number of species are within a factor of 10, the Final AcuteChronic Ratio should be calculated as the geometric mean of all the Species Mean AcuteChronic Ratios available for both freshwater and saltwater species. 3. 

### For acute 

### tests conducted on 

### metals and possibly other substances with embryos and larvae of barnacles, 

### bivalve molluscs, sea urchins, lobsters, crabs, shrimp, and abalones (see Section IV.E.2), it is probably appropriate to assume thatthe acute

-chronic 

# 0

ratio is 2. Chronic tests are very difficult 

### toconduct with most such species, but it is likely that the sensitivities of embryos and larvaewould determine the 

### results of lifecycle tests. Thus, if the lowest available Species Mean Acute Values 

### were determined with embryos and larvae of such species, the Final Acute

-Chronic Ratio should probably be assumed to be 2, so that the Final Chronic Value is equal 

### to the Criterion Maximum Concentration 

### (see Section X1.B) 

# a

*.,~

..?a.

...,..4. 

### If the most appropriate Species Mean AcuteChronic Ratios are less than 2.0, 

### and especially if they are less than 1.0, 

### acclimation has probably occurred during the chronic test. Because continuous exposure and acclimation cannot be assured to provide adequate protection in field situations, the Final Acute

-Chronic Ratio should be assumed to be 2, 

### so thattheFinal ChronicValue isequal to the Criterion Maximum Concentration (see Section X1.B). If the available Species Mean Acute

-Chronic Ratios do not fit one of these cases, a Final Acute

-Chronic Ratio probably cannot be obtained, and a Final Chronic Value probably cannot be calculated. L. 

### Calculate the Final Chronic Value by dividing the Final Acute Value by the Final Acute

-Chronic Ratio. If there was a Final Acute Equation rather than a Final Acute Value, see also Section VI1.A. M. 

### If the Species Mean Chronic Value of a commercially or 

### recreationally important species is lower than the calculated Final Chronic Value, then that species Mean Chronic Value should be used as 

### the Final Chronic Value instead of the calculated Final Chronic Value. N. Go 

### to Section VIII.

### VI. Final Chronic Equation



# 0- A. A 

### Final Chronic Equation can be derived in two ways. Theprocedure described here in Section A 

### will result in the chronic slope being the same as the acute slope. The procedure described in Sections

### B

-N usually will result in the chronic slope being different from the acute slope. 1. 

### If acute

-chronic ratios are available €or 

### enough species at enough values of thewater quality characteristic to indicate that the acute

-chronic ratio is probably the same 

### for all species and is probably independent of the water quality characteristic, calculate the Final Acute

-Chronic Ratio as 

### the geometric
mean of the available Species Mean AcuteChronic Ratios. ’

2. 

### Calculate the Final Chronic Value at the selected value Z 

### of the water quality characteristic by dividing the Final Acute Value at Z 

### (see Section V.M) by the Final Acute

-Chronic Ratio. 3. 

### Use V = 

### pooled acute slope (see section V.M)
as 

### L = 

### pooled chronic slope. 4. Go 

### to Section VI1.M. B. 

### When enough data are available to show that chronic toxicity to at least 

### one species is related to a water quality characteristic, the

### relationship should be taken into account as described in Sections B-G or using analysis of covariance [15,16]. The two methods are equivalent and produce identical results. The manual method described below provides an understanding of this application of covariance analysis, but computerized versions of covariance analysis are much more convenient for analyzing large data sets. 

### If two or more factors affect toxicity, multiple regression analysis should be used.


### For each species for which comparable chronic toxicity values are available at two or more different values of the water quality characteristic, perform a least squares regression of the chronic toxicity values on the corresponding values of the water quality characteristic 

### to obtain the slope and its 95 

### percent confidence limits for each species.
NOTE: 

### Because the best documented relationship fitting these data is that between hardness and acute toxicity of metals in freshwater and a log-log relationship, geometric means and natural logarithms of both toxicity and water quality are used in the rest of this section. 

### For relationships based on other water quality characteristics such as pH, 

### temperature, orsalinity, no transformation or a different transformation might fit the data better, and appropriate changes will be necessary throughout this section. ftis probably preferable, but not necessary, to use the same transformation that was usedwiththeacutevaluesinsectionv. 

### D. Decide whether the data for each speciesare useful, taking into account therange and number of the tested values of the water quality characteristic and the degree of agreement within and between species. For example, a slope based
on sixdatapointsmightbeof limitedvalueif it is based only on data 

### €or a very narrow range of values of the water quality characteristic, A slope based on only 

### two data points, however, might be useful if 

### it is consistent with other information and if the two points cover a broad enough range of the 

### water quality characteristic. In addition, chronic values that appear to be questionable incomparison with other acute and chronic data available 

### €or the same species and for other species 

### in the same genus probably should not be used. For example, if after adjustment for the water qua1ity characteristic, the chronic values available for 

### a species or genus differ by more than a factor of 10, probably
some or all of the values should be rejected. If

### a useful chronic slope is not available for at least one species 

### or if the available slopes are too dissimilar or if too few data are available to adequately define the relationship between chronic toxicity and the water quality characteristic, it might be appropriate to assume that the chronic slope is the same as the acute slope, which is equivalent to assuming that the acute

-chronic ratio is independent of the water quality characteristic. Alternatively, return to Section VI.H, 

### using the results of tests conducted under conditions and 

### in waters similar to those commonly used for toxicity tests with the species. 

### E. Individually for each species calculate the geometricmean of 

### the available chronic values and then divide each chronic value for a species by the mean for the species. This normalizes the chronic values so that the geometric mean of the normalized values for each species individually and for any combination of species is 1.0. F. 

### Similarly normalize the values of the water quality characteristic for each species individually. G. 

### Individually for each species perform a least squares regression of the normalized chronic toxicity values on the corresponding normalized values of the water quality characteristic. The resulting slopes and the 95 

### percent confidence

### limits will be identical to those obtained in Section 

### B. 

### Now, however, if the data are actually plotted, the line of best fit for each individual species will go through the point 1,1 

### in the center of the graph. K. 

### Treat all the normalized data as if they were all for the same species and perform a least squares regression of all the normalized chronic values on the corresponding normalized values of 

### the water quality characteristic 

### to obtain the pooled chronic slope, 

### L, and its 95 

### percent confidence limits, If all the normalized data are actually plotted, the line of 

### best fit will go through the point 1,l 

### in the center of the graph. 

### I. For each species calculate the geometric mean, MI 

# 0

of the toxicity values and the geometric mean, PI 

### of the values of the water quality characteristic. (These were calculated in steps 

### E and F.)J.

NOTE :



### K.

NOTE :



### L.

M. For each species 

### calculate the logarithm, Q, of the Species Mean Chronic Value at 

### a selected value, 

### Z, of the water quality characteristic using the equation: Q = In

### M 

# - L(ln P

# - In 

### Z). Although it 

### isnot necessary, it 

### willusually be best touse the same value of the water quality characteristic here as was used in section V.I. For each species calculate 

### a Species 

### Mean Chronic Value at

## z usingtheequation: SMCV =

### eQ. Alternatively, the Species Mean Chronic Values at Z can be obtained by skipping step J, using the equations in steps J and 

### K to adjust each acute value individually to 2, and then calculating the geometric means of the adjusted values for each species individually. This alternative procedure allows an examination of the range of the adjusted chronic values 

### for each species. Obtain the Final Chronic Value at 2 by using the procedure described in Section 1V.J-0. If the Species Mean Chronic Value at Z of a commercially or recreationally important species is lower than the calculated Final Chronic Value at 

### Z, then that Species Mean Chronic Value should beused astheFinal ChronicValueatZinsteadof the calculated Final Chronic Value.N. The Final Chronic Equation iSwritten as: Final ChronicValue = 

### e(L[ln(water quality characteristic)] 

## + In S 

# - L[ln Z]), where L = pooled chronic slope and S = Final Chronic Value at 2. Because L, S and Z are known, the Final Chronic Value can be calculated for any selected value of the water quality characteristic.
Final Plant Value A. Appropriate measures of the toxicity of the material to aquatic plants areused to compare the relative sensitivities of aquatic plants and animals. Although procedures for conducting and interpreting the results of toxicity tests with plants 

### are not 

### welldeveloped, results of tests with plants usually indicate that criteria which adequately protect aquatic animals and their uses will probably also protect aquatic plants and their uses. B. A plant value is the result of a 96

-hr test conducted with 

### an alga or a chronic test conducted with an aquatic vascular plant. NOTE: A test of the toxicity of a 

### metal to a plant usually should not be used if the medium contained
an excessive amount of 

### a complexing agent, such as EDTA, that might affect the toxicity of the 

### metal. Concentrations of EDTA above about 200 ug/L should probably be considered excessive.C. The Final Plant Value should be obtained by selectingthe lowest result from 

### a test with an important aquatic plant species in which the concentrations of test material were measured and the endpoint was biologically important.
VIII. Final Residue Value A. The Final Residue Value is intended to (a) prevent concentrations in commercially 

### or recreationally important aquatic species from affecting marketability because of exceedence of applicable FDA action levels and (b) protect wildlife, including fishesand birds, that consume aquatic organisms from demonstrated unacceptable effects. The Final Residue Value is the lowest of the residue values that are obtained by dividing maximum permissible tissue concentrations by appropriatebioconcantration or bioaccumulation factors. A maximum permissible tissue concentration is either 

### (a) an FDA action level [12] for fish oil or for the edible portion of fish or shellfish, or (b) a maximum acceptable dietary intake based on observations on survival, growth, 

### or reproduction in a chronic wildlife feeding study or 

### a long

-term wildlife field study. If no maximum permissible tissue concentration is available, go to Section X because no Final Residue Value can be derived.

### B. ~ioconcentration 

### actors (BCFS) and bioaccumulation factors (BAFs) are quotients of the concentration of a material in one or more tissues of an aquatic organism divided by the average concentration in the solution inwhich the organism had been living. A BCF is intended to account Only fornetuptake directlyfrom water, andthusalmosthastobemeasured inalaboratory test. Some uptake during the bioconcentration test might notbedirectlyfromwater ifthefood sorbs
some of the 

### test material before it is eaten by thetest organisms. A BAF is intended to account fornetuptake fromboth food and

### water ina realworld situation. A BAF almost has to be measured in a field situation 

### inwhich predators accumulate the material directly from water and by consuming prey that itself could have accumulated the material from both food and water. The BCF and BAF areprobably 

### similar for a material with a low BCF, but the BAF isprobably higher than the BCF formaterials with high BCFs. Although BCFs are not too difficult to determine, very few BAFs have been measured acceptably because it is necessary to make enoughmeasurements of theconcentration of the material in water to show that it was reasonably constant for a long enough period of time over the range of territory inhabited by the

### organisms. Because so 

### few acceptable BAFs 

### are available, only BCFs 

### will be discussed further. However, if an acceptable BAF 

### is available for a material, it should be used instead of any available BCFs. C. 

### If a maximum permissible tissue concentration is available for a substance (e.g., parent material, parent material plus metabolites, etc.)

## , the tissue concentration used in the calculation of the BCF 

### should be for the same substance. otherwise the tissue concentration used in the calculation of the BCF 

### should be'that of the material and its metabolites which are structurally similar and are not much more soluble in water than the parent material. D. 1. A BCF 

### should be used only if the test was flow

-through, the BCF 

### was calculated based on measured concentrations of 

### the test material in tissue and in the test solution, and the exposure continued at least until either apparent steady

-state or 28 

### days was reached. Steady

-state is reached when the BCF 

### does not change significantly over a period of time, such a 2 

### days or 16 

### percent of the length of 

### the exposure, whichever is longer. The BCF 

### used from a test should be the highest of (a) the apparent steady

-state BCF, 

### if apparent steady

-state was reached, (b) the highest BCF

### obtained, if apparent steady

-state was not reached, and (c) the projected steady

-state BCF, if calculated. 2. 

### Whenever a BCF is determined 

### for a lipophilic material, the percent lipids should also be 

### determined 

### in the tissue(s) for which the BCF
was calculated. 3. A 

### BCF obtained from an exposure that adversely affected the 

### test organismsmay be used only if it is similar to a BCF obtained with unaffected organisms of the same species at lower concentrations that did not cause adverse effects. 4. 

### Because maximum permissible tissue concentrations are almost never based on dry weights, a BCF calculated using dry tissue weights must be converted 

### to a wet tissue weight basis. If no conversion factor is reported with the BCF, multiply the dry weight BCF by 0.1 

### for plankton and by 0.2 

### for individual species of fishes and invertebrates ~171. 5. 

### If more than one acceptable BCF is available for a species, the geometric mean of the available values should be used, except that 

### if the BCFs are from different lengths of 

### exposure and the BCF increases with length ofexposure, the BCF for the longest exposure should be used. E. If enough pertinent data 

### exist, several residue values can be calculated by dividing 

### maximum permissible tissue concentrations by appropriate BCFs: 1. For each available maximum acceptable dietary intake derived from a chronic feeding study or 

### a long

- term field study with wildlife, including birds and aquatic organisms, the appropriate BCF is based on the whole body of aquatic species which constitute' or represent a major portion of the diet of the tested wildlife species. 2. For an FDA action level for fish or shellfish, the appropriate BCF is the highest geometric
mean species BCF for the edible portion 

### (muscle for decapods, 

### muscle with 

### orwithout skin for fishes, adductor 

### muscle for scallops, and total soft 

### tissue for other bivalve 

### molluscs) of 

### a consumed species. The highest species BCF is used because FDA action levels
are applied on a species

-by

-species basis. F. For lipophilic materials, it might be possible to calculate additional residue values. Because the steady

-state BCF for a lipophilic material Seems to be proportional to percent lipids from one tissue 

### to another and from one species to another[18-20], extrapolations can be made from tested tissues or species to untested tissues or species
an the basis 

### of percent lipids. 1. For each BCF for which the percent lipids is known for the same tissue for which the BCF 

### was measured, normalize the BCF to a 1 percent lipid basis by dividing the BCF by the percent lipids. This adjustment to a 1 percent lipid basis is intended to make all the measured BCFs far a material comparable regardless of the species or tissue'withwhich the BCF 

### was measured. 2. calculate the geometric mean normalized BCF. Data for both saltwater 

### and freshwater species should be used to determine the mean normalized BCF, unless the data show that the normalized BCFs are probably not similar, 3. Calculate all possible residue values by dividing the available maximum permissible tissue concentrations by the mean normalized BCF and by the percent lipids values appropriate 

### to the maximum permissible tissue concentrations, i.e., (maximum permissible tissue concentration) Residue value = (mean normalized BCF)(appropriate percent lipids) tissue concentration) Residue value = (mean normalized BCF) (appropriatepercent lipids)


### a. For an FDA action level for fish oil, the

### appropriate percent lipids value is 100. 

### b. For an FDA action level for fish, the appropriate percent lipids value 

### is 11 

### for freshwater criteria and 10 

### for saltwater criteria because FDA action levels are applied on a species-byspecies basis to commonly consumed species. The highest lipid contents in the edible portions of important consumed species are about 11 

### percent for both the freshwater chinook salmon and lake trout and about 10 

### percent for the saltwater Atlantic herring [21].


### c. 

### For a 

### maximum acceptable dietary intake derived fromachronic feeding studyora long

-term field study with wildlife, the appropriate percent lipids is that 

### of an aquatic species or 

### group of aquatic species which constitute a major portion of the diet of the wildlife species. G. 

### The Final Residue Value is obtained by selecting the lowest of the available residue values.

### NOTE: In some cases the Final Residue Value will not be low 

### enough. For example, a residue value calculated from an FDA 

### action level will probably result in an average concentration in the edible portion of a fatty species that is at the action level. Some individual organisms, and possibly
some species, will have residue concentrations higher than the mean value but no mechanism has been devised to provide appropriate additional protection. Also, some chronic feeding studies and long

-term field studies with wildlife identify concentrations that cause adverse effects but do not identify concentrations which do not cause adverse effects; again, no mechanism has been devised to provide appropriate additional protection. These are some of the species and
uses that are not protected at all times in all places.



## - x. other 

### Data Pertinent information that could not be used in earlier sectionsmight be available concerning adverse effects on aquatic organisms and their uses. The most important of these are data on cumulative and delayed toxicity, flavor impairment, reduction in survival, growth, or reproduction, or any other adverse effect that has been shown to be biologically important. Especially important are data for species for which no

~~

### other data are available. Data from behavioral, biochemical, physiological, microcosm, and field studies might also be available. Data might be available from tests conducted in unusual dilution water (see 1V.D and VI.D), from chronic tests in which the concentrations were not measured (see VI.B), from tests with previously exposed organisms (see 1I.F)

## , and from tests on formulated mixtures 

### or emulsifiable concentrates (see 1I.D). Such data might affect a criterion if the data were obtained with an important species, the test concentrations were measured, and the endpoint was biologically important. '


### XI. Criterion

_. A. A 

### criterion consists of two concentrations: the Criterion Maximum Concentration and the Criterion Continuous Concentration. B. 

### The Criterion Maximum Concentration (CMC) is equal to one-half the Final Acute Value. C. 

### The Criterion Continuous Concentration (CCC) is equal to the lowest of 

### the Final Chronic Value, the Final Plant Value, and the Final Residue Value, unless other data (see Section X) 

### show that 

### a lower value should be used. If toxicity is related to a water quality characteristic, the Criterion continuous concentration is obtained from the Final Chronic Equation, the Final Plant Value, and the Final Residue Value by selectingthe one, or the combination, that results in the lowest concentrations 

### in the usual range of the water quality characteristic, unless other data

(see Section X) show that 

### a lower value should be used. 

### D. Round [14] both the Criterion Maximum Concentration and the Criterion Continuous Concentration to two significant digits. 

### E. The criterion is stated as: The procedures described in the Guidelines for Deriving Numerical National Water Quality Criteria for the Protection of Aquatic Organisms and Their Uses indicate that, except possibly where a locally important species is very sensitive, (1) aquatic organisms and their uses should not be 

# 0

affected unacceptably 

### if the 4-day average concentration of (2) does not exceed (3) ug/L more than once every 3 years on the average and if the 1-hour average concentration does not exceed (4) ug/L more than once every 3 years on the average. where (1) = insert nlfreshwaternl 

### or nrsaltwaternl (2) = insert name of material (3) = insert the Criterion Continuous Concentration (4) = insert the Criterion Maximum Concentration.Final Reviev A. The derivation of the criterion should be carefully reviewed by rechecking each step of the Guidelines. Items that should be especially checked are: 1. If unpublished data are used, arethey

### well documented? Are allrequired data available? 2. 3. Is the range of acute values for any species greater 

### than 

### a factor of 

### lo? 4. Is the range of Species Mean Acute Values for any genus greater than a factor of lo? 5. 

### Is there more than a factor of 10 difference between the 'four lowest 

### Genus Mean Acute Values? 6. Are any of the four lowest Genus Mean Acute Valuesquestionable? 7. 

### Is the 

### Final Acute Value reasonable in comparison with the Species Mean Acute Values and Genus Mean Acute Values? 8. 

### For any commercially or recreationally important species, is the geometric mean of the acute values from flow

-through tests in which the concentrations of test material were measured lower than the Final Acute Value? 9. Are any of the chronic values questionable? 

# 010.

11.

12

13.

14* 15. 16. 

### Are chronic values available for acutely sensitive species? Is 

### the range of 

### acute

-chronic ratiosgreater than a factor of 10? Is 

### the Final Chronic Value reasonable in comparison with the available acute and chronic data? 

### Is the measured or predicted chronic value for any commercially or recreationally important species below the Final Chronic Value? Are any of the other data important? 

### Do any data look like they might be outliers? Are there any deviations from 

### the Guidelines? Are they acceptable? B. 

### On the basis of all

### availablepertinent laboratory and field information, determine if the criterion is consistent with sound scientific evidence. If it 

### is not, another criterion, either higher or lower, should be derived using appropriate modifications of these Guidelines.

# APPENDIX BSUMHARY OF THE 1980 AQUATIC 

### LIFE GUIDELINES
The Guidelines forDeriving 

### Water Quality Criteria forthe Protection of Aquatic Life and its Uses were developed to describe an objective, internally consistent, and appropriate way of ensuring thatwater qualitycriteria foraquatic lifewould provide, 

### on the average, a reasonable amount of protection. The resulting criteria 

### are not intended to provide 100 percent protection of all species and 

### alluses of aquatic life allof the time, but they are intended to protect most species in a balanced, healthy aquatic community. Minimum data requirements are identified in four areas; acute toxicity 

### to animals (eight data points), chronic toxicity 

### to animals (three data points), toxicity toplants, and residues. Data on acute toxicity are needed 

### for a variety of fish and invertebrate species and are 

### used to derive a Final Acute Value. By taking into account the number and relative sensitivities of the tested species, the Final Acute Value 

### is designed toprotect most, but not necessarily 

### all, of the tested and untested species. Data on chronic toxicity 

### to animals can be used 

### to derive a Final Chronic Valueby 

### two differentmeans. If chronicvalues are available for a specified number and array of species, a Final Chronic Value can be calculated directly. If not, an acute

-chronic ratio is derived and then used with the Final Acute Value to obtain the Final Chronic Value. The Final Plant Value is obtained by selectingthe lowest plant toxicity value based on measured concentrations.The Final Residue Value is intended toprotect wildlifewhich
consume aquatic organisms and the marketability of aquatic organisms. Protection of the marketability of aquatic organisms 

### is, in actuality, protection of a use of that water body (commercial fishery). Two kinds of data are necessary 

### to calculate the Final Residue Value: a bioconcentration factor (BCF) and 

### a maximum permissible tissue concentration, which can be anFDAaction level

### or canbetheresultof achronicwildlife feeding study. For lipid

- soluble pollutants, the BCF is normalized forpercent lipids and then the Final Residue Value is calculated by dividing the maximum permissible tissue concentration by the normalized BCF and by an appropriate percent lipidvalue. BCFs are normalized forpercent lipidssincethe BCF measured for any individual aquatic species is generally proportional tothe percent lipids in that species. 

# a

If sufficient data 

### are available to demonstrate that one or more of the final values should be related to a water quality characteristic, such as salinity, hardness, or suspended sol ids, the final value(s) are expressed as a function of that characteristic. Afterthe four final values (Final Acute Value, Final Chronic Value, Final Plant Value, and Final Residue Value) have been obtained, the criterion is established withthe Final Acute value becoming the maximum value and the lowest of the other three values becoming the 24

-hour average value. All of the data used to calculate the four final values and any additional pertinent information 

### are then reviewed to determine if the criterion is reasonable. If sound scientific evidence indicates that thecriterion should be raised or lowered,appropriate changes are made as necessary. The November 28, 1980, Guidelines have been revised from the earlier published versions (43 FR 21506, May 18, 1978; 43 FR 29028, July 5, 1978;44 

### FR 15926, March 15, 1979). Detailshave been added in many places and the concept of a minimum data base has been incorporated. 

### In addition, three adjustment factors and the species sensitivity factor have been deleted. These modifications were the result of the Agency's analysis of public comments and comments received from the Science Advisory Board on earlier versions of the Guidelines. These comments and the Resultant modifications are addressed fully 

### in Appendix D 

### to this notice.
Criteria 

### for the Protection

## of Human Health Interpretation of the Human Health Criteria 

# 0

The human health criteria issued today are summarized in Appendix A of this Federal Register notice. Criteria for the protection of human health are based on their carcinogenic, toxic, or organoleptic (taste and odor) properties. The meanings and practical uses of the criteria values are distinctly different depending on the properties on which they are based. The objective 

### of the health assessment portions 

### of the criteria documents 

### is to estimate ambient water concentrations which, in the case of noncarcinogens, prevent adverse health effects in humans, and in the case of suspect 

### or proven carcinogens, represent various levels of incremental cancer risk.

### Health assessments typically contain discussions of four elements: exposure, pharmacokinetics, toxic effects, and criterion formulation. The 

### exposure section summarizes information on exposure routes: ingestion directly from water, indirectly from consumption of aquatic organisms found in ambient water, other dietary sources, inhalation, and dermal contact. Exposure assumptions are used to 

### derive human health criteria. Most 

### criteria are based solely on exposure from consumption of water containing a specified concentration of a toxic pollutant and through consumption of aquatic organisms which are assumed to 

### have bioconcentrated pollutants from the water in which they live. Other multimedia routes of exposure such as air, nonaquatic diet, or dermal are not factored into the criterion formulation for the vast majority of pollutants because of 

### lack of data. The criteria are calculated using the combined aquatic exposure pathway and also using the aquatic organism ingestion exposure route alone. In criteria reflecting both the water consumption and aquatic organism ingestion routes of exposure, the relative exposure contribution varies with the propensity 

### of a pollutant 

### to bioconcentrate,with the consumption of aquatic organisms becoming more important as the bioconcentration factor (BCF) 

### increases. As 

### additional information on total exposure is assembled for pollutants for which criteria reflect only the two specified aquatic exposure routes, adjustments in water concentration values may be 

### made. The demonstration of significantly different exposure patterns will become an element

### of a process 

### to adapt/modify human health

-based criteria to local conditions, somewhat analogous to 

### the aquatic life criteria modification process discussed previously. It 

### is anticipated that States at their discretion will be able 

### to set appropriate human health criteria based on this process. 

# 0

Specific health

-based criteria are developed only if a weight of evidence supports the occurrence of the toxic effect and if dose/response data exist from which criteria can be estimated. The pharmacokinteics section reviews data on absorption, distribution,metabolism, and excretion 

### to assess the biochemical fate of the compounds in the human and animal system. The toxic effects section reviews data on acute, subacute, and chronic toxicity, synergistic and antagonistic effects, and specific information on mutagenicity, teratogenicity, and carcinogenicity. From this review, the toxic effect 

### to be protected against is identified taking into account the quality, quantity, and weight of 

### evidence characteristic of the data. The criterion formulation section reviews the highlights of the text and specifies a rationale for criterion development and the mathematical derivation of the criterion number. Within the limitations of time and resources, current published information of significance was incorporated into the human health assessments. Review articles nad reports were used for data evaluation and synthesis. Scientific judgment was exercised in reviewing and evaluating the data in each criteria document and in identifying the adverse effects for which protective criteria were published. 

# 0 >.Criteria for suspect or proven carcinogens are presented as concentrations in water associated with a range of incremental cancer risks to man. Criteria for noncarcinogens represent levels at which exposure 

### to a single chemical is not anticipated to produce adverse effects in man. In a few cases, organoleptic

(taste and odor) data form the basis for the criterion. While this type of criterion does not represent a value which directly affects human health, it is presented as an estimate of the level of a pollutant that will not produce unpleasant taste or odor either directly from water consumption or indirectly by consumption of aquatic organisms found in ambient waters. A criterion developed 

### in this manner 

### is judged to be as useful as other types of criteria in protecting designated water uses. 

### In addition, where data are available, toxicity

-based criteria are also presented for pollutants with derived organoleptic criteria. The choice of criteria used 

### in water quality standards for these pcllutants will depend upon the designated use to be protected. 

### In the case of 

### a multiple use water body, the criterion protecting the most sensitive use will be applied. Finally, for several pollutants no criteria are recommended because insufficient information is available for quantitative criterion formulation. 

### Risk Extrapolation Because methods do not exist to establish the presence of a threshold for carcinogenic effects, EPAIs policy is that there is
no scientific basis for estimating "safe" levels 

### for carcinogens. The criteria for carcinogens, therefore, state that therecommended concentration for maximum protection of human health is zero. In addition, the Agency has presented a range of concentrations corresponding to incremental cancer risks of to (one additional case of cancer in populations ranging from 10 million to 100,000, respectively). Other concentrations representingdifferent risk levelsmay be calculated by use of the Guidelines. The risk estimate range is presented for information purposes and does not represent an Agency judgment on 

### a "acceptable" risk level. Summary of the Human Health Guidelines The health assessments and corresponding criteria were derived based on Guidelines and Methodology Used in the Preparation of Health Effect Assessment Chapters of the Consent Decree Water Criteria Documents (theGuidelines ) developed by EPA'S Office of Research and Development. The estimation of 

# 0

health risk associated with human exposure to environmental pollutants requires predicting the effect of low doses for up to
a lifetime 

### in duration. A combination 

### of epidemiological and animal dose/response data 

### is considered the preferred basis for quantitative criterion derivation. No

-effect (noncarcinogen) or specified risk (carcinogen) concentrations were estimated by extrapolation from animal toxicity or human epidemiology studies using the following basic exposure assumptions: a 70

-kilogram male person (Report of the Task Group on Reference Man, International Commission for Radiation Protection, November 23, 1957) as the exposed individual; the average daily consumption of freshwater and 

# 0

### estuarine fish and shellfish products equal 

### to 6.5 

### grams/day; and the average ingestion of 2 

### liters/day of water (Drinking Water and Health, National Academy of Sciences, National Research Council, 1977). 

### Criteria based 

### on these assumptions are estimated to be protective of an adult male who experiences average exposure conditions. Two basic methods were used to formulate health criteria, depending on whether the prominent adverse effect was cancer or other toxic manifestations. The €01

### lowing sections detail these methods. Carcinogens Extrapolation of cancer responses from high 

### to low doses and subsequent risk estimation from animal data are performed using a linearized multi

-stage model. This procedure is 

### flexible enough to fit all monotonically

-increasing dose response data, since it incorporates several adjustable parameters. The multi

-stage model is a linear nonthreshold model as was the "one-hit" model original1 

### y used in the proposed criteria documents. The 1

### inear nonthreshold concept has been endorsed by the four agencies in the Interagency Regulatory Liaison Group and is 

### less likely to underestimate risk at the low doses typical of environmental exposure than other models that could be used. Because of the uncertainties associated with dose response, animal

-to

-human extrapolation, and other unknown factors; because of the use of average consumptions; and because of 

### the serious public health consequences that could result if risks were underestimated, EPA 

### believes that it is prudent to use conservative methods toestimate risk 

### in the 

### water quality criteria program. 

### The linearized multistage model 

### is more systematic and invokes fewer arbitrary assumptions than the “one-hit”procedure previously used. 

# 0

It should be noted that extrapolation models provide estimates 

### of risk since 

### a variety of assumptions are built into any model. Models using widely different assumptions may produce estimates ranging over several orders of magnitude. Since there is at present no way to demonstrate the scientific validity of any model, the use of risk extrapolation models 

### is a subject of debate in the scientific community. However, risk extrapolation is generally recognized 

### as the only tool available at this time 

### €or estimating the magnitude of health hazards associated with nonthreshold toxicants and has been endorsed by numerous Federal agencies and scientific organizations, including EPA‘s Carcinogen Assessment Group, the National Academy of Sciences, and the Interagency Regulatory Liaison Group, as a useful means of assessing the risks of exposure to various carcinogenic pollutants. Noncarcinogens
Health criteria based on toxic effects of pollutants other than carcinogenicity are estimates of concentrationswhich are not expected to produce adverse effects 

### in humans. They are based upon Acceptable Daily Intake (ADI) levels and are generally derived using no-observed

-adverse

-effect

-level data from animal studies although human data are used wherever available. The AD1 is calculated using safety factors to account for uncertainties 

# 0inherent in extrapolation from animal to man. In accordance With the National Research Council recommendations (DrinkingWater 

### and Health, National Academy of Sciences, National Research Council, 1977), safety factors of 10, 100, or 1,000 are used, depending 

### on the quality and quantity of data. 

### In some instances extrapolations are made from inhalation studies or limits to approximate a human response from ingestion using the StokingerWoodward model (Journal of American Water Works Association, 1958). Calculations of criteria from ADIS are made using the standard exposure assumptions (2 liters of water, 6.5 grams of edible aquatic products, and an average body weight of 70 kg).

# APPENDIX C



# .

### THE PHILOSOPHY OF TRE 1976 WATER QUALITY CRITERIA 

# - --- Water quality criteria specify concentrations of water constituentswhich, if 

### not exceeded, are expected to support an organic ecosystem suitable for the higher uses of water. Such criteria are derived from scientific facts obtained from experimental or

# L~J g&gg observations that depict organic responses to a defined stimulus or material under identifiable or regulated environmental conditions for a specified time period. Water quality criteria are 

### not intended to offer the same degree of strategy for survival and propagation at all times to all organisms within a 

### given ecosystem. They are intended not only to protect essential and significant life in water and the directusersofwater,butalsotoprotect 

### lifethat isdependent on life in water 

### for its existence, or that may consume intentionally 

### or unintentionally any edible portion of such life. The criteria levels for domestic water supply incorporate available data for human health protection. Such values are different from the criteria levelsnecessary forprotection of aquatic life. The Agency's interim primary drinking water regulations (40 

### Federal Register 59566 

### December 24, 1975), 

### as required by the Safe Drinking Water Act (42 U.S.C. 

### 300f, et seq.) 

## , incorporate applicable domestic water supply criteria. Where pollutants are identified in both the quality criteria for domestic water supply and the Drinking Water Standards, the concentration levels are identical. Water treatment may not significantly affect the removal of certain pollutants.

### What is essential and significant life in water? Do Daphnia


### or stonefly nymphs qualify as such life? Why does 1/100th of a concentration that is lethal 

### to 50 

### percent of the test organisms (LC50)

### constitute a criterion in some instances,whereas 1/2 

### or l/lOth of some effect levels constitutes a criterion in other instances? These are questions that often are asked of those who undertake the task of criteria formulation. The universe of organisms composing life in water is great in both kinds and numbers. As in the human population, physiological variability exists among individuals of the same species in response to a given stimulus. A 

### much greater response variation exists among species of 

### aquatic organisms. Thus, aquatic organisms do not exhibit the same degree of harm, individually 

### or by species, from a given concentration of a toxicant 

### or potential toxicant within the environment. In establishing a level 

### or concentration of a quality constituent as a criterion it is necessary to ensure a reasonable degree of safety for those more sensitive species that are important to the functioning of the aquatic ecosystem even though data on the response of such species 

### to the quality constituent under considerationmay not be available. The aquatic foodweb is an intricate relationship of predator and prey organisms. A water constituent that may in some way destroy 

### or eliminate an important segment of that food web would, in all likelihood, destroy or 

### seriously impair other organisms associated with it. 1



# 0 Although experimentation relating to the effects of particular substances under controlled conditions began in the

### early 19OO's, 

### the effects of any substance on more than a few of the vast number of aquatic organisms have not been investigated. Certain test animals have been selected by investigators for intensive investigation because of their importance to man, their availability to the researcher, and their physiological responses to the laboratory environment. As 

### general indicators of organism responses such test organisms are representative of the expected results for other associated organisms. In this context Daphnia
or stoneflies or other associated organisms indicate the general levels of toxicity to be expected among untested species. In addition, test organisms are themselves vital 1inks within the food web that results in the fish population in a particular waterway. The ideal data base for criteria development would consist of 

### information on a large percentage of aquatic species and would show the community response to a range of concentrations for a 

### tested constituent during a long time period. This information is not available but investigators are beginning to derive such information for a few water constituents. Where only 96

-hour bioassay data are available, judgmental prudence dictates that a substantial safety factor be employed to protect all life stages of the test organism in waters of 

### varying quality, as well as associated organisms within the aquatic environment that have not been tested and that may be more sensitive to the test constituent. Application factors have been used to provide the degree of 

### protection required. Safe levels for certain chlorinated hydrocarbons and certain heavy metals were estimated by applying an 0.01 

### application factor to the 96

-hour LC50 

### value 

# afor sensitive aquatic organisms. Flow

-through bioassays have been conducted 

### for some test indicator organisms over 

### a substantial period of their life history. In 

### a few other cases, information is available for the organism's natural life or for
more than one generation of the species. Such data may indicate


### a minimal effect level, aswell as 

### a no-effect level. The word '*criterion*I should not be used interchangeably with


### or as 

### a synonym for the word '*standard.**The word '*criterion" represents a constituent concentration 

### or level associated with 

### a degree of environmental effect upon which scientific judgment may be based. As it is currently associated with the water environment it has come to mean a designated concentration of 

### a constituent that, when not exceeded, will protect an organism,
an organism community, 

### or a prescribed water use 

### or quality with
an adequate degree of safety. A criterion, in some cases, may be


### a narrative statement instead of a constituent concentration. 

### on the other hand, a standard connotes a legal entity for a particular reach of waterway 

### or €or an effluent. A water quality standard may use 

### a water quality criterion as 

### a basis for regulation or enforcement, but the standard may differ from 

### a criterion because of prevailing local natural conditions, such as naturally occurring organic acids, 

### or because of the importance of a particular waterway, economic considerations, 

### or the degree of safety 

### to 

### a particular ecosystem that may be desired. Toxicity 

### to aquatic life generally is expressed in terms of acute (short 

### term) or chronic (long

-term) effects. Acute toxicity refers to effects occurring in a short time period:

### often death is the end point. Acute toxicity can be expressed as the lethal concentration for a stated percentage of 

### organisms tested, 

### or the reciprocal, which is the tolerance limit of a percentage of surviving organisms, Acute toxicity for aquatic organisms generally has been expressed for 24 

### to 96-hOur exposures. chronic toxicity refers to 

### effects through an extended time period. Chronic toxicity may be expressed in terms of an observation period equal 

### to the lifetime of 

### an organism or 

### to 

### the time span of more than one generation. Some chronic effects may be reversible, but most are not. Chronic effects often occur in the species population rather than in the individual. or 

### the sperm does not remain viable, the species would be eliminated from an ecosystem because of reproductive failure. Physiological stress may make a species less competitive with others and may result in a gradual population decline or 

### absence from an area. The elimination of a microcrustacean that serves as 

### a vital food during the larval period of a fish's life could result ultimately in the elimination of the fish from an area. The 

### phenomenon of bioaccumulation of certain materials may result in chronic toxicity to 

### the ultimate consumer in a rood chain. Thus, fish may mobilize lethal toxicants from their fatty tissues during periods of 

### physiological stress. Egg shells of predatory birds may be weakened to a 

### point of destruction in the nest. Bird chick embryos may have increased mortality rates. There may be a hazard to 

### the health of man if aquatic organisms with toxic residues are consumed. If eggs fail 

### to developThe fact that living systems, i.e., individuals, populations, species, and ecosystems, can take up, accumulate, and bioconcentrate manmade and natural toxicants is well documented. In aquatic systems biota are exposed directly to pollutant toxicants through submersion in a relatively efficient solvent (water) and are exposed indirectly through food webs and other biological, chemical, and physical interactions. Initial toxicant levels, if not immediately toxic and damaging, may accumulate in the biota 

### or sediment over time and increase to levels that are lethal 

### or sublethally damaging to aquatic organisms 

### or to consumers of these organisms. Water quality criteria reflect a knowledge of the capacity for environmental accumulation, persistence, and effects of specific toxicants in specific aquatic systems. Ions of toxic materials frequently cause adverse effects because they pass through the semipermeable membranes of an organism. Molecular diffusion through membranesmay occur for
some compounds such as pesticides, polychlorinated biphenyls, and other toxicants. Some materials may not pass through membranes in their natural 

### or waste

-discharged state, but in water they may be converted 

### to states that have increased ability 

### to affect organisms. 

### For example, certain microorganisms can methylate mercury, thus producing a material thatmore readily enters physiological systems. Some materials may have multiple effects: for example, an iron salt may not be toxic; 

### an iron floc 

### or gel may be an irritant 

### or clog fish gills 

### to effect asphyxiation; iron at low concentrations can be a trace nutrientbut at high concentrations 

### it can be a toxicant. Materials also can affect organisms 

### if their metabolic byproducts cannot be excreted. Unless otherwise stated, criteria are based on the total concentration of the substance because an ecosystem can produce chemical,physical, and biological changes that may be detrimental to organisms living in or using the water. Inprescribing water quality criteria, certain fundamental principles dominate the reasoning process. In establishing a level or concentration as a criterion for a given constituent it was assumed that other factors within the aquatic environment
are acceptable to maintain the integrity of the water. Interrelationshipsand interactions among organisms and their environment, as well as the interrelationships of sediments and the constituents they contain to the water above, are recognized 

# 0 as fact. Antagonistic and synergistic reactions among many quality constituents 

### inwater also are recognized as fact. The precise definition of such reactions and their relative effects on particular segments of aquatic life have not been identified with scientific precision. Historically much of the data to support criteria development was of an ambient concentration

-organism response nature. Recently, data are becoming available on longterm chronic effects on particular species. Studies now determine carcinogenic, teratogenic, and other insidious effects of toxic materials. Some unpolluted waters in the Nation may exceed designated criteria for particular constituents. There is variability in the natural quality of water and certain organisms become adapted

### to that quality, which may be considered extreme in other areas. Likewise, it is recognized that a single criterion cannot identify minimal quality for the protection of 

### the integrity of water for every aquatic ecosystem in the Nation. 

### To provide an adequate degree 

### of safety 

### to protect against long

-term effects may result in a criterion that cannot be detected 

### with present analytical tools. In some cases, a mass balance calculation can provide a means of assurance that the integrity of the waterway is not being degraded. Water quality criteria do not have direct regulatory impact, but they form the basis for judgment in several Environmental Protection Agency programs that are derived from water quality considerations. For 

### example, water quality standards developed by the States under section 303 

### of the Act and approved by EPA


### are 

### to be based on the water quality criteria, appropriately modified 

### to take account of local conditions. The local conditions 

### to be considered include actual and projected uses of 

### the water, natural background levels of particular constituents, the presence 

### or absence 

### of sensitive important species, characteristics 

### of the local biological community, temperature and weather, flow characteristics, and synergistic 

### or antagonistic effects of combinations of pollutants. Similarly, by providing a judgment on desirable levels of ambient water quality,water quality criteria are the starting point in deriving toxic pollutant effluent standards pursuant to section 307(a) of the Act. Other EPA 

### programs that use water quality criteria involve drinking water standards, the ocean

### dumping program, designation of hazardous substances, dredge spoil criteria development, removal of in

-place toxic materials, thermal pollution, and pesticide registration. To provide the water resourceprotection forwhich they are designed, quality criteria should apply to virtually all of the Nation's navigable waters with modifications for local conditions
as needed. 

### To violate quality criteria for any substantial length of time or in any substantial portion of awaterway may result 

### in an adverse affect on aquatic life and perhaps a hazard to man or 

### other consumers of aquatic life. Quality criteria have been designed -toprovide long

-term protection. Thus, they may provide a basis for effluent standards, but it is not intended that criteria values become effluent standards. It is recognized that certain substances may 

# a be applied to the aquatic environment with the concurrence of a governmental agency for the precise purpose of controlling or managing a portion of the aquatic ecosystem: aquatic herbicides and piscicides are examples 

### of such substances. For such occurrences, criteria obviously do not apply. It is recognized further that pesticides applied according to official label instructions to agricultural and forest lands may be washed to a receiving waterway by a torrential rainstorm. Under such conditions it is believed that such diffuse source inflows should receive consideration similar to that of a discrete effluent discharge and that in such instances the criteria should be applied to the principal portion of the waterway rather than to that peripheral portion receiving the diffuse inflow. 

# e

-.

,

### The format for 

### presenting water quality criteria includes a 

### concise statement of the dominant criterion or 

### criteria for a particular constituent followed by a narrative introduction, a rationale that includes justification for the designated criterion or criteria, and 

### a listing of the references cited within the rationale. An effort has been made 

### to restrict supporting data to those which either have been published or 

### are in press awaiting publication. 

### A particular constituent may have
more than one criterion to 

### ensure more than one water use 

### or condition, i.e., hard 

### or soft water where applicable, suitability
as 

### a drinking water supply source, protection of 

### human health when edible portions of selectedbiota are consumed,provision for recreational bathing or 

### waterskiing, and permitting an appropriate factor of safety to ensure protection for essential
warm-or coldwater associated biota. Criteria are presented 

### €or those substances that may occur in water where data indicate the potential for harm to aquatic life,


### or to water users, 

### or to the consumers of the water or 

### aquatic life. Presented criteria do not represent an all

-inclusive list of constituent contaminants. omissions from criteria should not be construed to mean that an omitted quality constituent is either unimportant or 

### non-hazardous.

### BIBLIOGRAPHY Adelman, I.R. and L.L. 

### Smith, 1970. 

### Effect of hydrogen sulfide on northern pike eggs and sac fry. 99:501. Trans. Amer. Fish. SOC., 

### Agriculture Handbook No. 60, 

### 1954. Diagnosis and improvement of 

### saline and alkali soils. L.A. 

### Richards, editor, U.S. Govern- ment Printing Office, Washington, D.C. Anderson, B.G., 1960. 

### The toxicity of organic insecticides to 

### Daphnia. Second Seminar on Biol. Problems in Water Pollution. Robert A. 

### Taft Sanitary Engineering Center Technical Report W60

-3, Cincinnati, Ohio. Bahner, L.H. and 

### D.R. Nimmo, 1974. Methods to assess effects of 

### combinations of toxicants, salinity, and temperature on estumarine animals. Proc. 9th Am. 

### Conf. on Trace Substances in Env. Health, Univ. Miss.?olumbia, Mo. Ballentine, R.X. and F.W. Kittrell, 1968. Observations of fecal colifonns in several recent streampollution studies. ings of the Symposium on Fecal Coliform Bacteria in Water and Wastewater, May 21

-22, 1968, Bureau of Sanitary Engineering, California State Department of Public Health. Bell, H.L., 1971. 

### Effect of low pH on the survival and emergence of aquatic insects. Water Res., 5:313. 

### Bellan, et al., 1972. The sublethal effects of a detergent on the reproduction, development, and settlement in the polychaetous annelid Capitella capitata. Marine Biology, 14:183. ProceedBender, M.E., 1969. The toxicity of the hydrolysis and breakdown products of malathion to the fathead minnow (PimephalE promelas, Rafinesque). Water Res., 3:571. methyl parathion, parathion and azinphosmethyl in mice and fish: Onset and recovery of inhibition. Bull. Environ. Contam. Toxicol., 12:117. Berg, G., 1974. 

### Reassessment of the virus problem in sewage and in surface and renovated waters. Sixth International Water poll. Res. California. Pergamon Press. 

### Bigqar, J.W. and M. 

### Fireman, 1960. 

### Boron abosrption and release by soils. Billard, R. and dekinkelin, 1970. Sterilization of the testicles of guppies by means of non-lethal doses of parathion. D Hydrobiologie, 9(1):91. 

### Benke, G.M. 

### and S.D. 

### Murphy, 1974. 

### Anticholinesterase action of

Soil Sci. SOC.

### Amer. Proc., 24:115 

### AnnalesBlack, E.C., 1953. Upper lethal temperatures of some British Columbia freshwater fishes. Jour. Fish. Res. Bd. Can., 10:196 Blumer, M., 1970. Oil contamination and the living resources of the sea. F.A.O. Tech. Conf. Rome. FIR:MP/7O/R-lIllP. Bollard, E.G. and G.W. Butler, 1966. Mineral nutrition of plants. Ann. Rev. Plant Physiol., 17:77. Bonde, G.J., 1966. Bacteriological methods for the estimation of water pollution. Hlth. Lab. Sci. 3:124. Bonde, G.J., 1974. Bacterial indicators of sewage pollution. International Symposium on Discharge of Sewage from Sea Out- falls. Pergamon Press. Bookhout, C.G. 

# - et -.I a1 1973. Effects of mirex on the larval development of two crabs. Water, Air, and Soil Pollution, 1:165.
channel catfish. Trans. Amer. Fish. SOC., 96:31.
mirex 

### in selected estuaries of South Carolina, 1969-71. Pesti- cides Monit. Jour., 7:6.

an reproduction of fish exposed to gas supersaturated water. Unpublished report. U.S. Environmental Protection Agency, Western Fish Toxicology Station, Corvallis, Oregon. Boyd, C.E. and D.E. Ferguson, 1964. Susceptibility and resistance of mosquitofish to several insecticides. Econ. Entomo1.

## , 57:430. Boyle, H.W., 1967. Taste/odor contamination of fish from the Ohio River. Fed. Water Poll. Cont. Admin., Cincinnati, Ohio. Bradford, G.R., 1966. Boron [toxicity, indicator plants]

## , in diagnostic criteria for plants and soils. H.D. Chapman, Ed., University of California, Division of Agricultural Science, Berkeley, p. 33. development and weight of sockeye salmon embryos and alevins. International Pacific Salmon Fisheries Commission, Progress Report 

### No. 12, pp. 1-26, mimeo.


### of speckled trout. Trans. Amer. Fish. SOC., 70:397.
of fishes. Quarterly Rev. Biol., 31:75. Boon, C.W. and 

### B.J. Follis, 1967. Effects of hydrogen sulfide on Borthwick, P.W., et al., 1973. Accumulation and movement of

Bouck, G.R., et al., 1975. Mortality, saltwater adaption

Brannon, E.L., 1965. The influence of physical factors on the

Brett, J.R., 1941. Tempering versurs acclimation 

### in the planting
Brett, J.R., 1956. Some principals 

### in the thermal requirementsBrett, J.R., 1960. Thermal requirementsof fish--three decades of study, 1940-1970. In: Biological problems in water pollution. C.M. Tarzwell (ed.) Dept. of Health, Education and Welfare, Public Health Service. Brinley, F.J. 

## , 1944. Biological Studies. House Document 266, 78th Congress, 1st session: Part 11, Supplement F. pp. 1275- 1353. 

# 0

Brungs, W.A., 1971. Chronic effects of low dissolved oxygen concentrations on fathead minnow (Pimephalespromelas). - J. Fish. Res. Bd. Canada. 28:1119-1123.

taste in domestic water. Jour. Amer. Water Works Assn., 61:575. Bugbee, S.L. and C.M. Walter, 1973. The response of macroinvertebrates to gasoline pollution in a mountain stream. In: Prevention and control of oil spills, proceedings of symposium March 13-17, Washington, D.C., p. 725.
insecticides 

### to resistant and susceptible mosquitofish in static and flowing solutions. 

### , Mosquito News, 29(1):96. Burson, B., 1938. Seasonal temperature variations 

### in relation to water treatment. Jour. Amer. Water Works Assn., 30:793. Butler, P.A., 1963. Commercial fisheries investigations. In: pesticide wildlife Studies during 1961 and 1962. U.S. Fish. Wildl. Serv. Circ. 167, Washington, D.C. organisms. 

### In: A Guide to Marine Pollution, E.D. Goldberg, ed. Gordon and Beach, NY. Calabrese, A., 1969. Individual and combined effects of salinity and temperature on embryos and larvae of the coot clam, Mulinia 

## - lateralis (say), Biol. Bull. 137, 3:417. embryos of the american oyster, Crassotrea virginica. Marine Biol.

## , 18:162. Camp, T.R., 1963. Water and 

### its impurities. Reinhold Publishing Corp, New York, New York. Capurro, L.R.A., 1970. Oceanography for practicing engineers. Barnes and Noble Inc., New York. Carlson, A.R., et al., 1974. Effects of lowered dissolved oxygen concentrations on channel catfish (Ictalurus embryos and larve. Trans. Amer. Fish. SOC. 103:623-626. Bruvold, W.H., et ,al., 1969. Consumer assessment of mineral

Burke, W.D. and D.E. Ferguson, 1969. Toxicities of four 

# 0

Butler, 

### P., et al., 1972. Test, monitoring and indicator

Calabrese, A., et al., 1973. The toxicity of heavy metals toChin, E., 1961. 

### A trawl study of an estuarine nursery area 

### in Galveston Bay with particular reference to penaeid shrimp. 

### P~.D.Dissertation, University of Washington. significance of lead isotopes 

### in pelagic sediments. Cosmochim. Acta., 26:263. Clay, 

### A., et a1

# ., 1975. Experimental induction of gas bubble disease in menhaden. Presented a the American Fisheries Society, September, 1975, Las Vegas, Nevada. New England Aquarium, Boston, Mass. Coble, D.W., 1961. Influence of water exchange and dissolved oxygen 

### in redds on survival of steelhead trout embryos, Trans. Amer. Fish. SOC. 90~469-474. Cooper, A.C., 1965. The effect of transported stream sediments on the survival of sockeye and pink salmon eggs and alevin. International Pacific Salmon Fisheries Commission, Bulletin Chow, T.J., and C.C. Patterson, 1962. The occurrences and Geochim.

18 : 1-71. Coppage, D.L., 1972. Organophosphate pesticides: specific level of brain ACHE inhibition related to death in sheepshead minnows. Trans. Amer. Fish. SOC., 101:534. Coppage, D.L. and T.W. Duke, 1971. Effects of pesticides in estuaries along the Gulf and Southeast Atlantic Coasts. In: Proceedings of the 2nd Gulf Coast Conference on Mosquito Suppression and Wildlife Management (C.H. Schmidt, ed.) National Mosquito Control-Fish and Wildlife Management Coordinating Committee, Washington, D.C. Coppage, D.L. and E. Matthews, 1974. Short-term effects of organophosphate pesticides on cholinesterases of estuarine fishes and pink shrimp. Bull. Environ. Contam. Toxicol., 11:483.
inhibition 

### in fish as 

### a diagnosis of environmental poisoning by malathion, 0, 0-dimethyl S-(1,l-dicarbethoxy-ethyl) phosphorodithioate. Pesticide Biochemistry and Physiology (in press).
temperatures on larval development in the mud crab, Rhitropanopeus harrisii. In: Fourth European Marine Biology Symposium. D.I. Crisp (ed.)

## , Cambridge University Press, London.
review of the lterature of 1967. Jour. Water Poll. Cont. Fed., 40:1047. Coutant, C.C., 1969. Thermal pollution effects: A review of the Coppage, D.L. .et al., 1975. Brain acteylcholinesterase

Costlow, Jr., J.D. and C.G. Bookhout, 1971. The effect of cyclic

Coutant, C.C., 1968. Thermal pollution--biologicaly effects: A

literature of 1968. Jour. Water Poll. Cont. Fed., 41:1036.Coutant, C.C., 1970. Thermal pollution effects: A review of the literature of 1970. Thermal pollution effects: A review of the literature of 1969. Jour. Water Poll. Cont. Fed., 42:1025. Coutant, C.C., 1971. Thermal pollution effects: A review of the literature of 1970. Jour. Water Poll. Cont. Fed., 43:1292. Coutant, C.C., 1972. Biological aspects of thermal pollution, 11. Scientific basis for water temperature standards at power plants. CRC Critical Rev. 

### in Environ. Cont., 3:1. Coutant, C.C., 1975. Temperature selection by fish

--a factor in power plant impact assessments. In: Symposium on the physical and biological effects on the environment of cooling systems and thermal discharges at nuclear power stations. Int'l Atomic Energy Agency 

### (Inpress). Coutant, C.C., and C.P. Goodyear, 1972. Water pollution

-thermal pollution: 

### A 

### review of the literature of 1971. Jour. Water Poll. Cont. Fed., 45:1250. Coutant, C.C., and H.A. Pfuderer, 1973. Water pollution

-thermal effects: 

### A review of the literature of 1973. Jour. Water Poll. Cont. Fed., 45:1331.
effects: A review of the literature of 1974. 

### Jour. Water Poll. Cont. Fed., 45:1476.
marine animals. Nature, 179:1138. Coutant, C.C., and H.A. Pfuderer, 1974. Water pollution

-thermal
Crisp, D.J., 1957. Effect of low temperature 

### on the breeding of
Datta, N. and J. Olearte, 1974. R

-Factors 

### in strains of Salmonella typhi and Shigella dysenteri I isolated during efi7emic.s in Mexico:

## - Classification by comrJabilitv. Antimicrobial Agents and Chemotherapy 5:310. embryonic development of clams and oysters and on survival and grouwth of the larvae. U.S. Fish and Wildlife Service, Fishery Bulletin, 67:393. - 

## - 

# - Davis, H.C. and 

### H. Hindu, 1969. Effects of pesticides on

Dawlev, E.M. and W.J. Ebel. 1975. Effectw of various

~~ concentrations of dissolved atmospheric gas on juvenile chinook salmon, Oncorhynchus tsawytscha, and steelhead trout. Fish. Bull., U.S. (In press) Dawley, E., et al., 1975. Bioassays of total dissolved gas pressure. (Unpublished report. National Marine Fisheries Services, Seattle, Washington. Delfino, J.J. and G.F. 

### Lee, 1971. Variation 

### of manganese, dissolved oxygen and related chemical parameters in the bottom waters of Lake Mendota, Wisconsin. Water Res., 5:1207.DeMont, W.J., et al., 1975. Effect of atmospheric gas supersaturation caused by dams on salmon and steelhead trout to the Snake and Columbia Rivers. Final Report. Northwest Fisheries Center, NMFS, Seattle, Washington. De Sylva, D.P., 1969. Theoretical considerations of the effects of heated effluents on marine fisher. 

### In: Biological aspects of thermal pollution. P.A. Krenkel and F.C. Parker (eds.), Vanderbilt University Press. photoperiod on reproductive cycling of the estuarine gobiid fish, Gillichthys mirabilk. Fishery Bull. 70, 4:1137. deVlaming, V.L., 1971. The effects of food deprivation and salinity changes on reproductive function 

### in the estuarine gobiid fish, Gillichtys mirabilis. 

# - Biol. Bull., 141:450. Diaz-Piferrer, 1962. The effects on an oil spill on the shore of Guanica, Puerto Rico (abstract)Ass. Isl. Mar. Labs, 4th Mtg. Curaco, 12-13. Doudoroff, 

### P. and Katz, M.. 1953. Critical review of literature deVIaming, V.L., 1972. The effects of temperature and 

# * -

on the toxicity of industrial wastes and their components to fish. 11. The metals and salts. Sew. and Ind. Wastes, 25, p. 002. Doudoroff, P. and D.L. Shumway, 1970. Dissolved oxygen requirements of fresh water fishes. FA0 Fish. Tech. Paper No. 06. Dow, R.L., 1973. Fluctuations 

### in marine species abundance dur climatic cycles. Mar. Tech. SOC. Jour., 7,4:30. Dowden, B.F., 1966. Effects of five insecticides on the oxygen consumption of the bluegill sunfish, Le omis macrochirus. Ph.D. Thesis, Louisiana State Universfiton Rouge, 

### LA. Eaton, J.G., 1970. Chronic malathion toxicity to the bluegill (Lepomis macrochirus Rafinesque)

# . Water Research, 4: 673. Ebel, W.J., et al., 1975. Effect of atmospheric gas supersaturation caused by dams on salmon and steelhead trout of the Snake and Columbia Rivers. Final Report. Northwest Fisheries Center, NMFS, Seattle, Washington.
sediment studied in-situ and 

### in the laboratory. Water Research, 7: 1285. Edberg, 

### N. and Hofstan, B.V., 1973. Oxygen uptake 

### of bottom
Eddy, R.M., 1972. The influence of dissolved oxygen 

# . concentration and temperature on the survival and growth of chinook salmon embryos and fry. M.S. Thesis, Oregon State Univ., June, 1972.

### Eichelberger, J.W. and J.J. Lichtenberg, 1971. Persistence of pesticides in river water. Environ. Sci. & 

### Technol., 5:541. Eisler, R., 1969. 

### Acute toxicities of insecticides to marine decapod crustaceans. Crustaceana, 16:302. 

### Eisler, ‘R., 1970. Acute toxicities of organochlorine and organophosphorus insecticides to estuarine fishes. U.S. 

### Bureau of Sport Fisheries and Wildlife, Technical Paper 46. 

### Ellis, M.M., 1937. 

### Detection and measurement of stream pollution. Bull. US. 

### Buraue of Sport Fisheries, and Wildlife. 48(22): 

### 365-437. Environmental ProtectionAgency, 1973. The control of pollution irom hydrographic modifications. EPA 430/9-73-017,.U.S. 

### Government Printing Office, Washington, D.C. Environmental Protection Agency, 1985a. Technical Support Document for Water Quality

-Based Toxics Control. Office of Water, Washington, D.C. Everett, G.V., 1973. Rainbow trout, Salmon gairdneri (Rich.)

## , fishery of Lake Titicaca. J. Fish. Biol., 5:429-440. European Inland Fisheries Advisory Commission, 1969. 

### Water quality criteria for Eurpoean freshwater fish

--extremepH values and inland fisheries, prepared by EIFAC Working Party on Water Quality Criteria for European Freshwater Fish. Water Research, 3:593. 

### ERL

-Duluth, Environmental Reseach Laboratory, 1976, 

### Procedures for developing temperature criteria for freshwater fish. Ecological Research Series, Report in Preparation. Fairbridge, R.W. (ed.)

## , 1966. 

### The encyclopedia of oceanography. Reinhold, New York, New York. Federal Water Pollution Control Administration, 1967. Temperature and aquatic life. Laboratory Investigations

-No.6, Technical Advisory and Investigations Branch, Cincinnati, Ohio. Fetterolf

## , C.M. Jr., 1973. Mixing zone concepts: Biological Methods for the Assesment of Water Quality, ASTM STP

-528, American Society for Testing and Materials, pp. 31

-45. 

### Food and Drug Administration, 1974. 

### Poisonous or deleterious substances in peanuts, evaporated milk, fish and shellfish. Proposed Rules. Federal Register, December 6, 1974, 

### Washington

## , D.C. temperature, In: Thermobiology. A.H. Rose (ed.) 

## , Academic Press, New York. Fry, F.E.J., 1967. Responses of vertebrate poikilotherms to
Furch, X., 1972. 

### Der Einfluss einer Vorbehandlung mit konstantenund wechselnden temperaturen auf die hitzerestistenz von Gammarus 

## -- salinus und Idotea 

# - balthica. 

### Mar. Biol., 15:12. Gallagher, T.P., et 

### al., 1969. Pollution affecting shellfish harvesting in Mobile Bay, Alabama, Tech. Servs. F.W.P.C.A. Southeast Water Lab., Athens, GA. Gammon, J.R., 1970. The effect of inorganic sediment on stream biota. Environmental Protection Agency. Water Poll. Cont. Res. Series, 18050 DWC 12/70, USGPO, Washington, D.C. Garside, E.T., 1966. Effect of oxygen in relation to temperature on the development of embryos of brook trout and rainbow trout. J. Fish. Res. Bd. Canada. 23:1121-1134.
insecticides to various aquatic invertebrates. Water and Sew, Works, 112:276. Geldreich, E.E. and Kenner, 1969. Concepts of fecal streptococci in stream pollution. Jour. Water Poll. Contr. Fed. 41:R336. Geldreich, E.E., 1972. Buffalo Laboratory recreational water quality: A study 

### in bacteriological data interpretation. Water Ree. 6:912. Geldreich, E.E., 1974. Microbiological criteria concepts for coastal bathing waters. Ocean Mgt. (In press). Geldreich, E.E. 

## , 1974. Monitoring marine waters for microbiological quality. WHO Conference

# - Scientific Aspect of Marine Pollution. Geneva Switzerland. Gibson, J.R., 

# - et --.I a1 1969. Sources of error in the use of fish- brain acetylcholinesterase activity as a monitor for pollution. Bull. Environ. Contam. Toxicol., 4:17. Gillette, L.A., et al.! 1952. Appraisal of a chemical waste problem by fish toxicity tests. Sewage Ind. Wastes, 24:1397. Glude, J.B., 1954. The effects of temperature and predators on the abundance of the soft-shell clam, arenaria, in New England. Trans. Amer. Fish. SOC., 04:13. Radioactivity 

### in the marine enviroment. Sciences, Washington, D.C., p. 137. Gonzalez J.G., 1972. Seasonal variation in the responses of estuarine populations to heated water in the vicinity of a steam generating plant. Ph.D. Dissertation, Uinv. Rhode Island, p. 142. Gaufin, A.R., et al., 1965. The toxicity of ten organic

Goldgerg, 

### E.D., et al., 1971. Marine chemistry. In: National Academy of

Griffin, A.E., 1960. Significance and removal of manganese 

### in

### water supplies. Jour. Amer. Water Works Assn., 52:1326. Griffith, E.W., 1963. 

### Salt as a possible limiting factor to the Suisan Marsh pheasant population. Wildlife Protection Study, Cooperative Study of California. Guarraia, 

### L. J., 1972. Brief literature review of gebsiellg as pathogens. In seminar on the significance of 

### Fecal coliform in 

### Industrial Waste, E.P.A., T.R.3, 

### National Field Investigations Center, Denver,CO, p. 94.



## - lucius L.) 

### when incubated under different oxygen conditions. Probs. of Ichthyol., 9:841-851. Haas, A.R.C., 1932. Nurtirional aspects in mottleleaf and other physiological diseases 

### of citrus. Hilgardia, 6:483. 

### Hamdorf, K., 

### 1961. Die Beeinflussung der Embryonal 

# - und Larvalentqicklung der Regenbogenforelle (Salmo iridues Gibb.) durch die Umwelgfactoren 02-Partialdruck and Temperatur. verg1. 

### Physiol

# . 44: 

### 451

-462.


### 15:8. techniques for coagulation

-filtration. jour. Amer. Water Works Assn., 59:1149. Harmeson, R.H., et al., 1971. The nitrate situation in Illinois. Jour. Amer. Water Works Assn., 63:303. 

### Heath, R.G., et al., 1972. Comparative dietary toxicities of pesticides to birds. Wildlife Report No. 

### 152, U.S. 

### Dept. of the Interior, Washington, D.C., p. 51. 

### environment; 

### A continuing controversy. Intercont. Med. Book Corp., N.Y., pp. 421

-435. concentrations on the growth of junenile coho salmon. Trans. Amer. Fish. SOC. 91:155-167. inorganic pollutants on young salmon and trout. Department Fish. Res., Bull. No. 5,

### p. 264. 

### Annual Report Belta Fish 

### and 

# 0

Gulidov, M.V., 1969. Embryonic develoopment of the pike (=

2. 

### Hampson, G.R., 

### and H.L. Sanders, 1969. 

### Local oil spill. Oceanus, Hannah, S.A., J.M. 

### Cohen, and G.G. 

### Robeok, 1967. 

### Control

Bureau of Sport Fisheries and Wildlife,
Heath, R.G., 

### and J.W. Spann, 1973. 

### Pesticides in the

Hermann, R.B., et al., 1962. Influence of dissolved oxygen
Holland, G.A., 

### et al., 1960. 

### Toxic effects 

### of organic and Washington, Holland, HeT.,, 

## a&., 1967. Use of 

### fish brain 

# .L acetylocholinesterase to monitor pollution by 

### organophosphorus - 

# w pesticides. Bull. Environ. Contsm. Toxicol., 2:?~56.- 

### HOSS, D.I., et al., 1975. 

### Effects of temperature, copper andchlorine on fish during simulated entrainment 

### in power plant condenser cooling systems. Symp. Physical and Biological Effects on the Environment of Cooling Systems and Thermal Discharges at Nuclear Power Plants. Intll Atomic Energy Agency

(Inpress). comparison of total coliform and fecal coliform values 

### in shellfish growing areas and a proposed fecal coliform growing area standard. Presented at 8th National Shellfihs Sanitation Workshop. (FDA, Washington, 

### D.C.) Hunt, D.A. and J. Springer, 1974. Preliminary repdrt on tlA1t

Hutchinson, G.E., 1957. A treatise on limnology. John Wiley & Hyde, X.M., et 

# e., 1974. The effect of mirex on channel catfish Idler, D.R., 1969. Coexistence of a fishery and a major industry Illig, G.L. Jr., 1960. Significance and removal of manganese in
Itazawa, Y. 1971. An estimation 

### of the minimum level of Sons,New York. production,
in Placentia Bay. Chemistry in Canada, 21(11):16.
water supplies. Jour. 

### Uer. Water 

### works Assn., 52:1326.
dissolved oxygen in water required for normal life 

### of fish. Bull. Jap. SOC. Sci. Fish. 37:273-276. Trans. Amer. Fish SOC., 103:366.

Jackim, E., et a1

# ., 1970. Effects of metal poisoning for five 1iver enzymes in the killifish (Fundulus 

# -heterocl

### itus). Fish. Res. Bd. Can., 27:383. Jour. Jacobson, S.M. and D.B. Boylan, 1973. Effect 

### of seawater soluble fraction of kerosene on chemotaxis in a marine snail, Nassarius obsoletus. Nature, 241:213. Jangaard, P.M. 1970. The roleplayed by the Fisheries Research Board of Canada in the Isredll herring phosphorus pollution crisis in Placentia Bay, Newfoundland. Fisheries Research Board, Atlantic Regional Office (CircularNo. 1) Halifax, Nova Scotia. Jeffries, 

### H.P. and W.C. Johnson, 1974. Seasonal distributions of bottom fishes in the Narragansett Bay area: Seven

-year variations in the abundance of winter flounder

(Pseudopleuronectes americanus)

# . Jour. Fish. Res. Bd. Can., 31:1057. Jensen, L.D. and A.R. Gaufin, 1966. Acute and long

-term effects of organic insecticides on two species of stonefly naiads. Jour. Water Poll. Cont. Fed., 38:1273.Johns Hopkins University, 1956. Final report to the water quality subcommittee of the American Petroleum Institute, Project, PG 49:41. Jones, J.R.E., 1964. Fish and river pollution. Butterworth and Co., Ltd., London. Kaiser, K.L.E., 1974. Mirex: an unrecognized contaminant of fishes from Lake Ontario. Science 185:523. Karnak, R.E. and W.J. Collins, 1974. The susceptibility to selected insecticides and acetylchlolinesterase activity in a 

# 0

~ laboratory colony of midge larvae, Chironomus tentans (Dintera: chironomidae)

# . Bull. Enivorn. Contam. Toxicol., i2

## :-a. Katz, M., 1961. Aucte toxicity of some organic insecticides to three species of salmonids and to the threespine strickleback. Trans. Amer. Fish. SOC., 90:264. Kelly, C.B. and 

### W. Arcisy, 1954. Survival of enteric organisms in shellfish. Pub. Health Repts. 69~1205. Keup, L.E., 1975. Factors in fish kill investigations. Water and Sewage Works, 121:48. Kinne, O., 1970. 

### Temperatur-animals-invertebrates, 

### In: Marine ecology. Klinger, 

### R., 1957. Sodium nitrite, a slow acting fish poison. Schweiz, 2. Hydrol. 19(2):565. Knepp, G.L. and G.F. Arkin, 1973. Ammonia toxicity levels and nitrate tolerance of channel catfish. The Progressive FishCulturist, 35:221.
insecticides to striped bass, Morone szxatilk. Calif. Fish and Game, 60:128. Kopfler, F.C., 1974. The accumulation of organic and inorganic mercury compounds by the eastern oyster (Crassostrea virginica). Bull. Environ. Contam. Toxicol. 11:275.
United States. U.S. Dept. of the Interior, Federal Water Pollution Control Admin., Cincinnati, Ohio. Kovacs, 

### N., 1959. Enteric fever 

### in connection with pollution of seawater. Western Australia. Renort of the Commissioner Of 0. Kinne (ed.), John Wiley and Sons, New York. 

# 0

Korn, S. and R. Earnest, 1974. Acute toxicity of twenty

Kopp, J.F. and R.C. Kroner, 1967. Tracemetals in waters of the

klicHealth for the year 1958. 

## - 

# 0Kraus, as cited by Mitchess, J.W., R.E. Hogson, and C.R. Gaetjens, 1946. Tolerance of farm animals 

### to feed containing 2, 4

-dichlorophenoxyacetic acid. Jour. Animal. Sci., 5:226. Lange, N.A., Ed., 1961. Handbook of chemistry, 10th ed. McGrawHill Book Co., New York. Langelier, W.F., 1936. The analytical control of anti

-corrision water treatment. Jour. Amer. Water Works Assn., 28:1500. Le Clerc, E. and F. Devlaminck, 1955. Fish toxicity tests 

### and water quality. Bull. de Belge Condumeiit Eaux., 28:ll. Le Clerc, E., 1960. The self

-purification 

### of streams and the relationship between chemical and biological tests. Proc. Second symposium on Treatment of Waste Waters, Pergamon Press, London, England, p. 281. Leggett, W.C. R.R. Whitney, 1972. Water temperature and the migrations 

### of American shad, Fish. Bull. 70, 3:659. Lehman, A.J., 1965. Summaries of pesticide toxicity. Association of Food and Drug Officials of the U.S., Topeka, Kansas,pp. 1

-40.
pressure. Inst. Freshwater Res. Drottningholm, Report #29. Fish. Ed. 

### of Sweden (Annual report for 1948), 49

-50.
water. Arch. Hydrobiology, 53: 589. Lindroth, A., 1949. Vitality of salmon parr 

### at low oxygen
Lindroth, 

### A., 1957. Abiogenic gas supersaturation of river Lockhart, E.E., 

## - et -.I 

### a1 1955. The effect of water impurities on Lowe, J.I., et al., 1971. Effects of mirex on selected estuarine the flavor of brewed coffee. Food Research, 20:598. organisms. In: Transactions of 

### the 36th 

### North American Wildlife Resources Conference. pp. 171

-186. Lowman, F.G.,, et al., 1971. Accumulation and redistribution of radionuclides by marine organisms, In: Radioactivity in the Marine Environment,National Academy of Sciences, Washington, 

### D.C., p. 161. Ludke, J.L., et al., 1971. Toxicity of mirex to crayfish, Procambarus blandingi. 

# - Bull. Environ. Contam. Toxicol., 6:89. Lurid, W.A. and G.C. Maltezos, 1970. Movements and migrations of the bluefish, Pomatomus etarix, tagged in waters of New York and southernNew England. Trans. Amer. Fish. SOC., 99:719. Macek, X.J. and McAllister, 1970. Insecticide susceptibility of some common fish family representatives. Trans. her. Fish SOC., 99:20.Macek, K.J., et al., 1974. Chronic toxicity of lindane to selected aquatic invertebrates and fishes. Environmental ProtectionAgency Research Contract Report, Enviornmental Protection Agency Ecol. Res. Series, (In preparation). Mackenthun, K.M., 1973. Toward a cleaner aquatic environment. US. Government Printing Office, Washington, D.C. Malouf, R., 1972. Occurrence of gas bubble disease in three species of bivalve mollusks. Jour. Fish. Res. Bd. Can., 

# 0

29:588. Marcello, 

### R.A., et al., 1975. Evaluation of alternative solutions to gas buble disease mortality of menhaden at Pilgrim Nuclear Power Station. Yankee Atomic Electric Co., Westboro, Mass. YAEC

-1087. Massengill, R.R., 1973. Change in feeding and body condition of brown bullheads overwintering in the heated effluent of a power plant. Ches. Sci. 14,2:138. McCord, C.P., 1951. Beryllium as a sensitizing agent. Ind. Med. Surg., 20:236. McCoy, E.F., 1972. Role of bacteria 

### in thenitrogen cycle in lakes. Enviornmental ProtectionAgency, Water Pollution Control Research Series, U.S. Govenrment Printing Office (EP 2.10:16010 EHR 03/72). Washington, D.C. McKim, J.M., et al., 1976. Long

-term effects of methylmercuric chloride on three generations of brook trout

(Salvelinus

__ fontinalis): Toxicity, accumulation, distribution, and elsination. Jour. Fish. Res. Board Can. 33:2726. McKee, J.E. and H.W. Wolf, 1963. Water quality criteria. State Water Quality Control Board, Sacramento, CAI pub. 3

- A. Merna, J.W. and P.J. Eisele, 1973. The effects of methoxychlor on aquatic biota. U.S. EPA Ecological Res. Series, No. EPA

-R3- 73-046. U.S. Government Printing Office, Washington, D.C.
Bull. World Health Organization, 44:363.
shellfish 

### in esturary waters. Jour. San. Eng. Div. Proc. Amer. SOC. Civ. Eng., 94:595.
selective fish eradicator. Trans. Amer. Fish. SOC., 94:203. Metcalf, 

### R.L., 

### & 

## a&., 1971. Biodegradable analogs of 

### DDT. Metcalf, T.G. and W.C. Stiles, 1968. Viral pollution of

Meyer, F.P., 1965. The experimental use of guthion as a

### Minchew, G.D. and D.E. Ferguson, 1970. 

### Toxicities of six insecticides to resistant and susceptible green sunfish and golden shiners in static bioassays. Jour. Miss. Acad. Sci., 15:29. Mironov, O.G., 

### 1967. Effects of low concentrations of petroleum and its products on thedevelopment of roeoftheBlackSea flatfish. Vop Ikhtiol., 7:557. 

### Mironov, O.G., 1970. 

### The effect of oil pollution on flora and fauna of the Black Sea. In Poceedings: FA0 Conference on Marine Pollution and its effects on living resources and fish. Rome, Dec., 1970., 

### E

-92. Food and Agriculture Organization of the United Nations. Moore, E.W., 1952. 

### Phisiological effects of the consumption of saline drinking water. National Res. Council, Div. of Medical Sciences, Bull. San. Engr., and Environment, Appendix E. Moore, S.F., 

### et al., 1973. A preliminary assessment of the environmental vulnerability of Machias Bay, Maine to 

### oil super- tankers. Mount, 

### D.I., 1960. 

### Effects of various dissolved oxygen levels on fish activity. Ohio State Univ. Natur. Resources Inst., Ann. FisheriesRes. Rept. pp. 13

-33.


### freshwater fishes. In: Biological aspects of thermal pollution. P.A. 

### Krenkel and F.L. Parkers, (eds.) 

## , Vanderbilt University Press. survival, growth and reproduction. Water Res., 7:987. 

### acceptable toxicant limits for fish

-malathion and the butoxyethanol ester of 2,4-D. Trans. Amer. Fish. SOC., 

### 21:185. Mulla, M.S. and A.M. Khasawina, 1969. 

### Laboratory and field evaluations of larvicides against chironomid midges. Jour. Econ. Entomol., 62:37. National Academy of Sciences

# - Conmittee 

### on Biologic Effects of 

### Atmospheric Pollutants, 1972. 

### Lead: Airborne lead in perspective. The National Academy of Sciences, Washington, D.C. National Acadmey of Sciences,National Academy of 

### Engineering, Mount, D.I., 1969. 

### Developing thermal requirements for

Mount, D.I., 1973. Chronic effect of low pH 

### on fathead minnow
Mount, D.T. and C.E. Stephan, 1967. A method for establishing

1974. Water quality criteria, 1972, U.S. 

### Government Printing Office, Washington, D.C.

### National Institute for Occupational Safety and Health, 1972. Occupational exposure to beryllium. U.S. Department of Health, Education and Welfare, Health Services and Mental Health Admin., National Institute for Occupational Safety and Health. U.S. Government Printing Off ice, Washington, D.C. National Research Council, 1954. Sodium restricted diets. Publication 325, 

### Food and Nutrition Board, Washington, D.C. National Technical Advisory Committee to the Secretary of the Interior, 1968. 

### Water quality criteria, U.S. Government Printing Office, Washington, D.C. Nagvi, S.M. and D.E. Ferguson, 1969. 

### Pesticide tolerances of selected freshwater invertebrates. Jour. Miss. Acad. Sci.

## , 14: 

### 121. Nebeker, A.V. and A.R. Gaufin, 1964. Bioassays to determine pesticide toxicity to the amphipod crustacean, Gammarus lactuis. Proc. UtahAcad. Sci. Arts and Letters, 41:64. 

### Nebeker, A.V., et al., 1976a. Nitrogen, oxygen, and carbon dioxide as factors affecting fish survival in gas supersaturated water. Trans. Amer. Fish. SOC. 

### (In Press).
salmon molts in seawater after exposure to gas supersaturated water. Trans. Amer. Fish. SOC. 

### (In Press).
water on freshwater invertebrates. Proc. Gas Bubble Disease Workshop. Battelle Northwest, ERDA Special Report (In Press). Neill, 

### W.H. and J.J. Magnuson, 1974. Distributional ecology and behavioral thermoregulation of fishes in relation to heated effluent from a power plant at Lake Monona, Wisconsin. Trans. Amer. Fish. SOC. 103, 4:663. 

### animals, p. 273

-380. In: P. 

### Hepple (ed.), Water Pollution by oil. I.P. London. Copiea No., 55:37. chloramphenical, amphicillin and other anrimicrobial agents: Strains isolated during an extensive typhoid fever epidemic in Mexico. Antimicrobial Agents and Chmeothearpy, 4:597. 

# 0

Nebeker, A.V., et al., 197633. 

### Survival of coho and sockeye
Nebeker, A.V., et al., 1975. Effects of gas supersaturated

Nelson

-Smith, A., 1971. 

### Effects of oil on marine plants and
Nichols, J.T., 1918. 

### An abnormal winter flounder and others. Olearte, J. 

### and E. Galindo, 1973. 

# - Salmonella typhi resistance to

Olla, B.L. and A.L. Studholme, 1971. The effect of temperature on the activity of bluefish, Pomatomus saltatrix (1) Biol. Bull., 141:337.

# 0 Olson, G.F., 

## -_ et al., 1975. Mercury residues in fathead minnows, Pimephalespromelas Rafinesque, chronically exposed tomethyl- mercury 

### in water. Bull. Environ. Contam. Toxcol., 14:129. hydrogen sulfide to Gammarus psedol -imnaeus. Trans. her. Fish. 

### sac., 103 

### (Inpress). Oseid, D.M. and L.L. Smith,Jr., 197a. Chronic toxicity of
Oseid, D.M. and L.L. Smith, 197413. Long

-term effects of hydrogen sulfide on Hexaqenia limbata (Ephemeroptera) 

# . Environmental Ecology 

### (In press). oseid, D.M. and L.L. Smith, 1974c. Factors influencing acute toxicity estimates of hydrogen sulfide 

### to freshwater invertebrates. Water Research 8 (In press). Palmer, J.S. and R.D. Radeleff, 1964. The toxicologic effects of certain fungicides and herbicides on sheep and cattle. Ann. N.Y. Acad. Sci., 111:729. Paris, D.F., et all 1975. Rates of degradation of malathion by bacteria isolated from aquatic systems. Environ. Sci. & Technol., 9:135. Parker, F.L. and P.A. Krenkel, 1969. Thermal pollution: Status of the art. Report No. 3, Vanderbilt University, School of Engineering, Nashville, Tennessee. Patrick R., 1969a. Some effects of temperature on freshwater algae. In Biological aspects of thermal pollution. P.A. Krenkel and F.L. Parker, (eds.) 

## , Vanderbilt University Press. Patrick, R., 1969b. Discussion of engineering aspects, soucres and magnitude of thermal pollution. 

### By P.A. Krenkel and F.L. Parker. In: Biological aspects of thermal pollution. P.A. Krenkel and F.L. Parker, (eds.)

## , Vanderbilt University Press. mineralized water on houshold plumbing and appliances. Jour. Amer. Water WorksAssn., 60:1060. Pearce, J.B., 1969. Thermal addition and the benthos, Capd Cod Canal. Ches. Sc., 10:227. Pearse, J.S., 1970. Reproductive periodicities 

### of Indo-Pacific invertebrates in the 6ulf 

### of Suez. 111. The echinoid Diadema setosum (Leske). Bull. Mar. Sci., 20, 3:697. organisms after contamination of the bottom of Long Harbour, Placentia Bay, Newfoundland 

### with elemental phosphorus. 

### In: Effects of Elemental Phosphorus on Marine Life, Fish. Res. Bd4 of Canada, Circular 2, pp. 181-186. Patterson, W.L. and R.F. Banker, 1968. Effects of highly

Peer, D.L., 1972. Observations on mortalities of e\benthisPhelps, E.B., 1944. Stream sanitation. John Wiley and sons, Phillips, A.M., Jr., D.L. Livingston and R.F. Dumas, 1960. Inc.

## ,New York.
Effects 

### of starvation on the chemical composition of brook trout. Prog. Fish. Cult., 22:147. phosphorus inseFticides to different species of warmwater fishes. Trans. Amer. Fish. SOC., 91:175. Plotkin, S.A. and M. Katz, 1967. Minimal infective doses of viruses for man by the oral route. 

### In: Transmission of Viruses by the Water Route, G. Berg, Ed., John Wiley Interscience,N.Y., p. 155. using standard methods. In: Marine pollution and sea life

(Ruivo, Ed.). Fishing News (Books) Ltd, London, England, pp. 212-217. Pickering, Q.H., et 

## a&., 1962. The toxicity of organic

Portman, J., 1972. Results of acute tests with marine organisms,

Post, G. 

### and T.R. Schroeder, 1971. The toxicity of four insecticides to four salmonid species. Bull. Environ. Contam. Toxicol., 6:144. Post, G. and R.A. Leasure, 1974. Sublethal effect of malathion 

### to 

### three salmonid species. Bull. Environ. Contam. Toxicol., 12:312. Presnell,N., 1974. Discussion of fecal coliforms for shellfish growing waters. Proc. 7th National Shellfish Sanitation Workshop, Oct. 21

-22, 1971. Ratcliff and Wilt, Eds., FDA., Washington, D.C. Raney, E.C., 1969. Discussion of effects of heated discharges 

### on freshwater fish in Britian. By J.S. Alabaster. In: Biological aspects of thermal pollution. 

### P.A. KrenkeL and F.L. Parker (eds.)

## , Vanderbilt University Press. Rawson,D.S. and J.E. Moore, 1944. The saline lakes of Saskatchewan. Canadian Jour. of Res.

## , 22:141. Reeves, A.L., 1965. Absorption of beryllium from the gastrointestinal tract. A.M.A. Arch. Envir. Health, 11:209. Reid, L.C. and D.A. Carlson, 1974. Chlorine disinfection of low temperature waters. Jour. Environ. Eng. Div., ASCE, Vol. 100, No. EE2:339. Reitler, R. and R. Seligaman, 1957. Pseudomonas aeruginosa in drinking water. Jour. Appl. Bact., 20:145. Renfro, W.C., 1963. Gas bubble mortality of fishes in Galveston Bay, Texas. Trans. Amer. Fish. SOC., 92:320.Richards, L.A. (Ed.)

## , 1954. Diagnosis and improvement of saline., and alkali soils. Agriculture Handbook.No. 60, U.S. Government Printing Office, Washington, D.C.
humans. Am. J. Physiol., 126:l. supplies. Jour. Amer. Water Works Assn., 50:680.
elements 

### in species of phytoplankton grown 

### in culture. Jour. Mar. Biol. Assn. U.X., 51:63. Ringem, L.M. and C.H. Drake, 1952. 

### A study of the incidence of Ricter, C.O., and 

### A. MacLean, 1939. Salt taste threshold of Riddick, J.M., et al., 1958. Iron and Manganese in water Riley, J.P. and 

### I. Roth, 1971. The distribution of trace

Pkeudomonas aeruginesa from various national sources. Jour. Bact.

## , 64:841. Romney, E.M., et al., 1962. Beryllium and the growth of bush
Romney, E.M. and J.D. Childress, 1965. Effects of beryllium in beans. Science, 135:786. 'plants and soil. Soil Sci., 100:210. Rounsefell, G.A. and W.H. Everhart, 1953. Fishery science, its methods and applications. John Wiley and Sons, Inc., New York. Rucker, R.R., 1974. Gas bubble disease: Mortalities of coho salmon, Oncorhynchus kisutch, 

### in water 

### with constant total gas pressure and different oxygen-nitrogen ratios. National Oceanic and 

### Atmas. 

### Admain., Natl. Mar. Fish. 

### Serv., Northwest Fish Center, Seattle, Washington, unpublished manuscript. 

# 0

Rulifson, R.L. and G. -el, 1971. Nitrogen suspesaturation 

### in the Columbia and Snake Rivers. Tech Rept. TS-09-70-208-016.2, Environmental Protection Agency, Region X, Seattle, Washington.

trout (Salmon 

### ---- gaikdneri). 

## --- Russo, R.C., et al., 1974. Acute toxicity of nitrite to rainbow Jour. Fish. Res, Bd. Can., 31:1653. Russo, R.C. and R.V. Thurfiton, 1975, Acute toxicity of nitrite to cutthroat trout (Salmon clarki). Fisheries Bioassay Laboratory Tech. Report No. 75-3, Montana State University. Saeki, A., 1965. Stu6ie.s on fish culture in filtered closedcirculating aquaria. 11. 

### on the carp culture experiments in the systems. Bull. Jap. Soa. Sci. Fish., 31:916. Sanders, H.O., 1969. Toxicity 

### of pesticides 

### to the crustacean, Gammarus lacustris. US. Department of the Interior, Washington, D.C., Bureau of Sport Fisheries and Wildlife Technical Paper-No. 25. -

### Sanders, H.O., 1972. 

### Toxicity of some insecticides to four
- 

### species of malacostracan crustaceans. U.S. Department of the Interion, Washington, D.C. Bureau of Sport Fisheries and Wild- life Technical Paper No. 66. 

### pesticides to two species of cladocerans. Trans. Amer. Fish. Sanders, H.O. and O.B. 

### Cope, 1966. Toxicities of several ' 

### SOC., 95:165. .? 

### Sanders, H.O. and O.B. Cope, 1968. The relative toxicities of several pesticides to naiads of three species of stonefly. Limnol. & 

### Oceanong., 13:112. Sastry, A.N., 1975. Physiology and ecology of reproduction in marine invertebrates. In: F.J. and W.B. Vernberg (eds.)

## , Physiological ecology of estuarine organisms. Belle W. Baruch Library of Marine Species, Univ. South Carolina Press, Columbia, South Carolina. Sattlemacher, P.G., 

### 1962. Methemoblobinemia from nitrates in drinking water. SchrReihe. Ver. Wasser

-, Boden-u. Luthyg. No. 21, Fishcer, Stuttgart. Hi1

### 1

## , New York.

as indicators of sewage pollution. from Sear Outfalls. Pergamon Press. Seabury, J.H., 1963. 

### Toxicity 

### of 2, 

### 4

-dichlorophenoxyacatic acid forman and dog. Arch. Envir. Health, 7:202. Shumway, D.L. and J.R. Palensky, 1973. Impairment of the flavor 

### of fish by water pollutants. U.S. Environmental Protection Agency, EPA-R3-73-OlOI U.S. Government Printing Office, Washington, D.C. Shuval, H.J., et aJ., 

### 1971. Natural inactivation processes 

### of viruses =seawater. Proc. Natural Specialty Conf. on Disinfection. Amer. SOC. of Civil Engineers, N.Y. Saywer, C.N., 1960. 

### Chemistry for sanitary engineers. McGrawScarpino, D., 1974. 

### Human enteric virsuses and bacteriolphages International Symposium 

# 0

Siefert, R.E., et al., 1973. Effects of reduced oxygen concentrations on northern pike (Esox 

## - - lucius) embryos and larvae. J. Fish. Res. Bd. Canada. 30:849-852. 

### concentrations on the early life stages of mountain whitefish, smallmouth bass, and white bass. Accepted for publication in the Prog. Fish. Cult. Siefert, R.E., et al., 1975. Effects of reduced oxygenSiefert,.RE. and W.A. Spoor., 1974. Effects of reduced oxygeriie 

### concantrations 

### on embryos and 

### larvae of white.sucker, coho 

### salmon, brook trout, and 

### walleye. Procaedings'..of: 

### an ' International Symposium 

### on the Early Life History of Fish. Springer

-Verlag Berlin Heidelberg NewYork.
diseasessf herring. from the 

### western North 

### Atlantic.. Spec.: Publ. Corn. Horthw. Atlantic Fish. No. 6:603-610. Slanetz, L.W., et a1 1965. Correlation of coliform and fecal streptococci indices.with'thepresence of Salmonella 

# -- and,

, ' enteric viruses 

### in sea water and she2lfish. .Adv....inWater Pollution Res. 2nd International Confr., Tokyo, 3:17. Slonim, A.R:, 1973. Acute toxicity of beryllium sulfateto the common guppy. 

### Jour. Water Poll. Cont. Fed. 45:2110. Slonim, A.R. and E.E. Ray, 1975. Acute.toxic y of beryllium sulfate to salamander 

### larvae (Ambystoma 

### q~). ' 'Bull. 

### Envir. Contam. Toxicol.

## , 13: 307. Slonim, C.B. and 

### A.R..; 

### sibnim, 1973.. Effecf':oi 5 hardness ,on the tolerance of the guppy toberylliumzsul~f Bull. Envir. Contam. Toxicol., 10:295. Smith, R.S., et 

### al., 1951. Bathing water.quality and he.alth. I. Great Lakes (U.S. Public Health Service, Cincinnati, ohio). Smith, L.L., 1971. Influence of hydrdgen.sulfide

## .bn'.fish and -' arthropods. Environinental Protection Agency, :,Project 18050 PCG, Washington, D.C. Smith, L.L. and' D.K. Oseid, 1972. Effects of .hydrogen sulfide-& fish eggs and fry. Water Research, 6:7P1. Smith, R.S. and 

### T.B. Woolsey, ,1932. ''"'Bathing

### wator quality and.'. health. 11. Inland 

### river and pool. '(U.S.. ,&bl'ic Health
I Smith, K.S. and T.D. Woolsey, 1961. Bathing 'water quality and:"

'Obarr, Scotland, May 17

-23, 1973, Edited by J.H.S. .,Blaxter, '*<. pp.-487-495,

.. , Sinderman, C.J., 1965. Effects of environment on several

: .. ..

- -,.? 

## - -.I

. .. , . ... . !> " r;, ,,

..

..

.,

,. .. 

### Service, 

### Cincinnati, Ohio).

~ . .,
Public Health. III. Coastal Waters (U.5; 'Public Health Snow, J.R., 1958. 

### A preliminary report 

### on the comparative .-,

.. .. .. .. .. ., .. . 1. .., .. 

### . Serviee, Cincinnati, Ohio).

.. testing of.some of the 

### newer herbicides. Proc. 11th Ann. .'Conf., Southeast ASSOC. Game Fish COI~IIB.,. pp. ,125-132.

,Report of the Commissioner 'uf hblicHealt i .... .. Snow, D.J.R., 1959. Typhoid and City Beach. 

### Western Australia, or the year 1958; p. 52.
Philadel phia, Pennsylvania. Sollman, 

### T.H.., 1957. 

### A manual of pharmacology. W.B. Saunders,South, G.E. and 

### R.D. Hill, 1970. Stud$e,s.

### on marine a.lgae.of.. -: Newfoundland. I. Occurrence and-distr.ibutionof-, free

......iiG.hg
., .' Ascophyl

__ lum nOdOSum in Newfoundian&"

... 

### : Can. Jour. Bot.,

.............. ./46:1697. Sprague, J.B., 1963. Resistance

### .'& f6ur:.fresh,wat 

### to lethal,high temperature and,low

... oxygen. J.. Canada.

## , 20:387.
1971. 13th Edition, APHA, Amer. .- ... ; Cont. Fed. .'~
....

.. Standard. Methods for the Examinatio

- Stev~enson,A.H., - 1.953.

~ Studies..of bathing 

### water. quality

... and ' '' Stewart, B.A., et al., i96 N'itrate and other p utants under fields 

### and feedl.ots.. .~ ..Emir.. _. Sci.

.... Tech.,:,

... .1:73.6..

... Stewart, N.E., et'al., 1967. Influence of oxygen concentration on the growth of juvenile.,.largemouthbass,, J. 

### Fish.,Re's. Bd. Canada., 24~475-494. .. health.. Amer, Sour. 'hblic .- .... Health, 43~529;

........ ...

..

- .., ,.. . ......... ........ 

### . .

.. ..

........

~ . . ,. , Stickel, L.F., 1973. Pesticide residues 

### in-bi'rds.and mammals.

~ In: Environmental.,po&lution 

### ides.,Jc.p. Edwards, Ed..) Stiff, M.J., 1971. Copper/bicarbonate equilibria in solutions of Plenum Pxess, New York. pp., 

### ..... :. .

.... ..

bicarbonate ion at concentrations simi.lart,otho.se found in natural water.

.Water

...Research,

... ........ 5:171.:

...... experimental beryl1i.mpoisoning. Jour.:

...... Lab. C1 in. Med., 38:173.
and sons, 

### Inc., New

...york', ,.Chapter'4.

.. 

### Iiiiting factor.; r. striped

. .., ..... bass.

. ' Tran 

### 'her. Fish. soc., Special Pub., 3:3i:

... .. ..... Stokinger, H.E. and C.A.:.Stroud, 1951, Anemia inacute

... .Stiim, W. and J.J. Morgan, .L970. Aquat.ic-.

...... Chemistry.. John Wiley Talbot, G.B., ,1966 ,..,. stuarine environmental requirements and

. -. 

### .

..

. I.. Tarzwell, C.M. .and A.R.. Gaufin,

. ,1953.. some^ important biolbgica3.

..- effects of pollution

### .otte proceedings of the 8th 

### PU Reprinted in Biology of Water Pollution, i967. DepCOf Interior, Washington, - D.c.

. .. , .. ..

sregarded 

### instream surveys, ., %.:

indistriai

..

'waste confeyence.,,

.. ~

..- , ... . J. '2 Tarzwell, C.M. and C. Henderson,. 1960. $aylor, 

### E.W., 1968. $oFdrty-secop 

### f

.Director of Water:. .-' Toxicity

.. of less'.co

. 

## .~-. . , metals to fishes. ' Industrial .Wastes, 5i12. Examination, 1965-66

## , Metropo 

### er Board, Londori,'~$:~117.

.. ....... ..... ...... .. . . -. _. ^,*.>

.... .... ..I.

... .~ ?.~,.:-.

.. .. > .. =.Vc .:



# -

.,- ..
. ._.U.S. Bureau of Sp.o.rtFisheries and Wildlife, 1970. Resource wa&hinGtok, &Q~;. .?!<.I 

# . i:

# . Ci

..... .. .... ii_ _:_.. :.-i:2 ::i ?;,,-.:,:,~.v:%.:; 2,- U.S. Environmental 

### Protection Agency. 1985s. Techiii&alF*Sup@oft Document for Water Qualitv-Based Toxics Control. Office of .. ... i, ...... :__- I 5 ,,'.2<, L.. : \_">Van Donsel, .D:.J..- :and..E.E.

.Geld Relations.bips of c,dciT; sediments,:

.. 

# -W$*k- .BgS:'- ,togecal.colifo

. . 

### .&',. -1 v; .- ,. . ... .~.2..,'.,'~IZsi;

.. .-~ Van Horn, W.M., 1958.
Van Ords+%nd, 'H. The effect of pul~p and paper mill wastes" on 

### aquatic.-1.iif.e

. ,.€'roc.

..Ontari 

### nf.,, 5~50. ,. .s..;:<ie.ri:

.. :.- .. Amer. Med. Assn., 1=:1084.

van &?a 

### 1,in
,.. C,zF. w.ate.r .f iqhes.

.
a0:1119. nput_qutput, mqdeJ!s.r Schweiz 2.

waters. Sewage Ind. Wastes,

:.r+~.at+ng 

# ..,to infant aminated water. Amer.""' 

### ..'i.'( ,~,. , . . .~ . ~*.Lli::. 29.:4 95

# . .. ,..

. .

, ~ .. . ., . . _._



# - I..., :",L,-., .,.*

~ - - r.."...- ~. .. . i,

*,uJ. QOVERNMENT PRlNTlNQOFflCE] 9 8 6 -1 5 9- 3 0 0 5 0 4 72QUALITY CRITERIA FOR WATER 1986

UPDATE 

### #I*ALDRIN-DIELDRIN CRITERIA: Aquatic Life Dieldrin For dieldrin the criterion to protect freshwater aquatic life
as derived using the Guidelines is 0.0019 ug/L as a 24

-hour average, and the concentration should not exceed 2.5 ug/L at any time.
For dieldrin the criterion to protect saltwater aquatic life
as derived using the Guidelines is 0.0019 ug/L as 

### a 24

-hour average, and the concentration should not exceed 0.71 ug/L at any time. Aldrin

For freshwater aquatic life the conckntration of aldrin should not exceed 3.0 ug/L at any time. No data are available concerning the chronic toxicity of aldrin to sensitive freshwater aquatic life. For saltwater aquatic life the concentration of aldrin should not exceed 1.3 ug/L at any time. No data are available concerning the chronic toxicity of aldrin to sensitive saltwater aquatic life. Human Health For the 

### maximum protection of human health from the potential carcinogenic effects of exposure to aldrin through ingestion of contaminated water and contaminated aquatic organisms, the *Indicates suspended, canceled or restricted by U.S. EPA office of Pesticides and Toxic Substancesambient water concentration should be zero, based on the nonthreshold assumption for this chemical. However, zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase'of cancer risk over the lifetime are estimated at and The corresponding recommended criteria are 0.74 ng/L, 0.074 ng/L, and 0.0074 ng/L, respectively. If these estimates are made for consumption of aquatic organisms only, excluding consumption of water, the levels are 0.79 ng/L, 0.079 ng/L, and 0.0079 ng/L, respectively. 

# 0

For the maximum protection of human health from the potential carcinogenic effects of exposure to dieldrin through ingestion of contaminated water and contaminated aquatic organisms, the ambient water conceqtration should be zero, based on the nonthreshold assumption for this chemical. However, zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer risk over the lifetime are estimated at loe6 and The corresponding recommended criteria are 0.71 ng/L, 0.071 ng/L, and 0.0071 nq/L, respectively. If these above estimates are made for consumption of aquatic organisms only, excluding consumption of water, the levels are 0.76 ng/L, 0.076 ng/L, and 0.0076 ng/L, respectively.

(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYAMMONIA sUMlrmy:
~11 concentrations used herein are expressed asun-ionized ammonia (NH3), because NH3, not the ammonium ion (NH4') has been demonstrated to be the principal toxic form of ammonia. The data used in deriving criteria are predominantly from flow through tests in which ammonia concentrations were measured. Ammonia was reported to be acutely toxic to freshwater organisms at concentrations (uncorrected for pH) ranging from 0.53 to 22.8 mg/L NHj for 19 invertebrate species representing 14 families and 16 genera and from 0.083 to 4.60 mg/L NH3 for 29 fish species from 9 families and 18 genera. Among fish species, reported 96- hour LC50 ranged from 0.083 to 1.09 mg/L for salmonids and from 

# 0

0.14 to 4.60 mg/L NH3 for nonsalmonids. Reported data from chronic tests on ammonia with two freshwater invertebrate species, both daphnids, showed effects at concentrations (uncorrected for pH) ranging from 0.304 

### to 1.2 mg/L NH3, and with nine freshwater fish species, from five families and seven genera, ranging from 0.0017 to 0.612 mg/L NH3. Concentrations of ammonia acutely toxic to fishes may cause loss of equilibrium, hyperexcitability, increased breathing, cardiac output and oxygen uptake, and, in extreme cases, convulsions, coma, and death. At lower concentrations ammonia has many effects on fishes, including a reduction in hatching success, reduction in growth rate and morphological development, and pathologic changes in tissues of gills, livers, and kidneys.Several factors have been shown to modify acute NH3 toxicity in fresh water. Some factors alter the concentration of unionized ammonia in the water by affecting the aqueous ammonia equilibrium, and some factors affect the toxicity Of un-ionized ammonia itself, either ameliorating or exacerbating the effects of ammonia. Factors that have been shown to affect ammonia toxicity include dissolved oxygen concentration,temperature, p~, previous acclimation to ammonia, fluctuating or intermittent exposures, carbon dioxide concentration, salinity, and the presence of other toxicants. The most well

-studied of these is pH; the acute toxicity of NH3 has been shown to increase as pH decreases. Sufficient data exist from toxicity tests conducted at different pH values to formulate a mathematical expression to describe pH

-dependent acute NH3 toxicity. The very limited amount of data regarding effects of pH on chronic NH3 toxicity also indicates increasing NH3 toxicity with decreasing pH,but the data are insufficient to derive a broadly applicable toxicity/pH relationship. Data on temperature effects on acute NH3 toxicity are limited and somewhat variable, but indications are that NH3 toxicity to fish is greater as temperature decreases. There is no information available regarding temperature effects on chronic NH3 toxicity. Examination of pH and temperature

-corrected acute NH3 toxicity values among species and genera of freshwater organisms showed that invertebrates are generally more tolerant than fishes, a notable exception being the fingernail clam. There is
no clear trend among groups of fish; the several most sensitivetested species and genera include representatives from diverse faailies (Salmonidae, Cyprinidae, Percidae, and Centrarchidae). Available chronic toxicity data for freshwater organisms also indicate invertebrates (cladocerans,one insect species) to be
more tolerant than fishes, again with the exception of the fingernail clam. When corrected for the presumed effects of temperature and pH,there is alsonocleartrend among groupsof fish for chronic toxicity values, the most sensitive species including representatives from five families (Salmonidae, Cyprinidae, Ictaluridae, Centrarchidae, and Catostomidae) and having chronic values ranging by not much more than a factor or two. The range of acute

-chronic ratios for 10 species from 6 familieswas 3 to 43, and acute

-chronic ratioswere higher for the species having chronic tolerance below the median. Available data indicate that differences in sensitivitiesbetween
warm and coldwater families of aquatic organisms are inadequate to warrant discrimination in the national ammonia criterion between bodies of water with "warm" and "coldwater" fishes: rather, effects of organism sensitivities on the criterion are most appropriately handled by site

-specific criteria derivation procedures. Data for concentrations of NH3 toxic to freshwater phytoplankton and vascular plants, although limited, indicate that freshwater plant species are appreciably more tolerant to NH3 than are invertebrates or fishes. The ammonia criterion appropriate for the protection of aquatic animals will therefore in all likelihood be sufficiently protective of plant life.Available acute and chronic data for ammonia with saltwater organisms are very limited, and insufficient to derive a saltwater criterion. A few saltwater invertebrate species have been tested, and the prawn Macrobrachiurn



# _ _-- rosenbergiA was the most sensitive. The few saltwater fishes tested suggest greater sensitivity than freshwater fishes. Acute toxicity of NH3 appears to be greater at low pH values, similar to findings in freshwater. Data for saltwater plant species are limited to diatoms, which appear to be more sensitive than the saltwater invertebrates for which data are available. More quantitative information needs to be published on the toxicity of ammonia to aquatic life. Several key research needs must be addressed to provide a more complete assessment of ammonia toxicity. These are: (1)acute tests with additional saltwater fish species and saltwater invertebrate species; (2) life

-cycle and early life

-stage tests with representative freshwater and saltwater organisms from different families, with particular attention to trends of acute

-chronic ratios; (3) fluctuating and intermittent exposure tests with a variety of species and exposure patterns; (4) more complete tests of the individual and combined effects of pH and temperature, especially for chronic toxicity; (5) more histopathological an6 histochenical research with fishes, which would provide a rapid
means of identifying and quantifying sublethal ammonia effects; and (6) studies on effects of dissolved and suspended solids on acute and chronic toxicity.NATIONAL CRITERIA: The procedures described in the Guidelines for Deriving Numerical National Water Quality Criteria for the Protection of Aquatic Organisms and Their Uses indicate that, except possibly where a locally important species is very sensitive, freshwater aquatic organisms and their uses should not be affected unacceptably if: 

# 8

(1) the 1

-hour* average concentration of un-ionized ammonia (in mg/L NH3) does not exceed, more often than once every 3 years
on the average, the numerical value given by 0.52/FT/FPH/2, where:

FT - - 10°.03 20-TCAP); TCAP < T 

### 5 30 - 0.03 20-T); 0 < T < TCAP 10 

## - - FPH = 1 ;8<pH<9 1+107.4-PH 1.25 ; 6.5<pH 

## - - < 7.7 TCAP = 20 C; Salmonids or other sensitive coldwater species present coldwater species absent = 25 C; Salmonids and other sensitive (*An averaging period of 1 hour may not be appropriate if excursions of concentrations to greater than 1.5 times the average occur during the hour; in such cases, a shorter averaging period may be needed.) (2) the 4

-day average concentration of u n-ionized ammonia (in mg/L NH3) does not exceed, more often than once every 3 years
on the average, the average* numerical value given by 0.80/FT/FPH/RATIO, where FT and FPH are as above and:RATIO = 16 : 7.7 - < pH - <9

TCAP = 15 C; Salmonids or other sensitive coldwater species present

coldwater species absent = 20 

### c; Salmonids and other sensitive (*Because these formulas are nonlinear in pH and temperature, the criterion should be the average of separateevaluationsof the formulas reflective of the fluctuations of flow, pH, and temperature within the averaging period; it is not appropriate in general to simply apply the formula to average pH, temperature, and flow.) The extremes for temperature (0, 30) and pH (6.5, 9) given in the above formulas are absolute. It is not permissible with current data to conduct any extrapolations beyond these limits. In particular, there is reason to believe that appropriate criteria atpH > 9 will be lower than theplateau between pH 6 and 9 given above. Criteria concentrations forthe pH range 6.5 to9.0 and the temperature range 0 C to 30 C are provided in the following tables. Total ammonia concentrations equivalent toeach unionized ammonia concentration are also provided in these tables. There are limited data on the effect of temperature on chronic toxicity. EPA will be conducting additional research on the effects of temperature on ammonia toxicity in order to fill perceived data gaps. Because of this uncertainty, additional site

- specific information should be developed before these 

# 0criteria are used in wasteload allocationmodeling. For example, the chronic criteria tabulated for sites lacking salmonids are less certain at temperatures much below 20 C than those tabulated at temperatures near 20 C. Where the treatment levels needed to meet these criteria below 20 C may be substantial, use of sitespecific criteria is strongly suggested. Development of such criteria should be based upon site

-specific toxicity tests. 

# I)

Data available for saltwater species are insufficient to derive a criterion for saltwater. The recommended exceedence frequency of 3 years is the Agency's best scientific judgment of the average amount of time it will take an unstressed system to recover from a pollution event in which exposure to ammonia exceeds the criterion. A stressed system, for example, one in which several outfalls occur in a limited area, would be expected to require more time for recovery. The resilience of ecosystems and their ability to
recover differ greatly, however, and site

-specific criteria may be established if adequate justification is provided. The use of criteria in designing waste treatment facilities requires the selection of an appropriate wasteload a1location model. Dynamic models are preferred for the application of these criteria. Limited data or other factors may make their use impractical, in which case one should rely on a steady

-state model. The Agency recommends the interim use of 1Q5 or lQlO for Criterion Maximum Concentration design flow and 745 or 7410 for the Criterion Continuous Concentration design flow in steadystate models for unstressed and stressed systems respectively.12) 4-day average concentrations for mmnla.. \ PU oc 5c I0 c 15 C 20c 25 c WC
L. SalmI6a or Other Smsltlv. Cold.ater SD~CI~S Present Un-1onlz.d Amonla lmg/lltr NH,) 6.50 6.75 7.w 7.25 7.50 7.73 8.00 8.25 8.50 8.75 9.oo

6.50 6.75 7.oo 7.25 7.40 7.75 8.00 8.25 8.50 8.75 9

### .oo 0.0007 0.0012 0.0021 0.0037 0.0066 0.0105 0.0126 0.0126 O.Ol2t 0.0126 0.0126

2.5 2.5 2.5 2.5 2.5 2.3 1.53 0.87 0.49 0.28 0.16 0.oow 0.0017 0.0029 0.0052 0.0093 0.01 53 0.0177 0.0177 0.0177 0.0177 0.0177

2.4 2.4 2.4 2.4 2.4 2.2 I .44 0.82 0.47 0.27 0.16 0.0013 0.0023 0.0042 0.0074 0.0132 0.022 0.025 0.025 0.025 0.025 0.025 0.0019 0.0033 0m59 0.0105 0.0186 0.03 1 0.035 0.035 0.035 0.035 0.035 0.0019 0.0033 0.0059 0.0105 0.0186 0.03 I 0.035 0.035 0.035 0.035 0.035

2.2 2.2 2.2 2.2 2.2 2.1 1.37 0.70 0.45 0.26 0.16 2.2 2.2 23 2.2 2.2 2.o I .33 0.76 0.44 0.27 0.16 1A9 I ,49 1.49 I.50 I .% I.40 0.93 0.54 0.32 0.19 0.13 0.0019 0.0033 0.00% 0.0105 0.0186 0.031 0.a35 0.035 0.035 0.035 0.035

I .M 1.04 1.04 I .M 1.05 0.99 0.66 0.39 0.23

.. 0.15 0.10 0.0019 0.0033 0.0059 0.0105 0.0186 0.031

-0.035

0.035 0.035 0.035 0.035

0.73 0.73 Q.74 0.74 0.74 0.71 0.47 0.28 0.17 0.11 0.oc

8;oo 0;0126 8.25 0.0126 8.50 0.0126 8.75 0.0120 9.00 0.0126

8.50 o;r9 8.75 0.28 9.oo 0.16 0.0009 0.0017 0.0029 0.0052 0.0093 0.0153 0.0177 0.0177 0.0177 0.0177 0.0177 0.0013 0.0023 0.0042 0.0074 0.0132 0.022 0.025 0.025 0.025 0.025 0.025 0.0019 0.0033 0.0059 0.0105 0.0186 0.03 1 0.035 0.035 0.035 0.035 0.035 0.0026 0.0047 0.Og83 0.0148 0.026 0.043 0.0% 0.050 0.0% 0.050 0.050 Total Amonla (mg/lltor NH,) 2.1 2. I 2.1 2. I 2.1 I.98 1.51 0.76 c.45 0.27 0.17 0.0026 0.0047 0.0083 0.0148 0.026 0.043 0.0% 0.050 0.0% 0.0% o.om

I .a IA7 IA7 I .48 1A9 1.39 0.93 0.54 0.33 0.21 0.14 0.W26 0.0047 0.0083 0.0148 0.026 0.043 0.050 0.050 0.050 0.050 0.050

I.03 1-04 1.04 1.05 I.06 I.oo 0.67 0.40 025 0.16 0.11

To convert meso valws to np/ll?er N, multlply by 0.822. t Sltc~p~~ltIc crltrla dorolopment Is rtronplv ruggost.d at TmDOratyr" abwm 20 C buause of the Iln1t.d data avallable to generato tho crltula rrm.nd.tlon, and at tmperatur*s blow 20 C bWuse of Tb lim1t.d data and boauY mall hmgor In the crltorla may have rlgnlflcant Impact on the Inol Of trmtl(lt r.qu1r.l In Irotlng tho r.6umNnd.d crltorla.oc 5c 10 c I5 c MC 25 C KJC vH
A. Salmcnldr or Omer Sensltlve CoId.atu 5pul.r Present

6.50 35 6.75 32 i

### ;oo 28 7-25 23 7.50 17.4 7.75 12.2 8

### .oo 8.o 8.25 4.5 8.30
. 2.6 8.75 I .47 9

### .oo 0.86 Vn-lonlz.d Amanla 0.0129 0.0182 0.02 1 0.030 0.033 0.w 0.048 0.W8 0

### .ow 0.091 o.oa0 0,113 0.092 0.133 0.092 0.130 0.092 0.130 0.092 0.130 0.092 0.1x (mq/llter 0.026 0.042 0.W6 0.095 0.128 0.159 0.1W 0.184 0.lW 0.184 0.184 NH3) 0.036 0.059 0.093 0.135 0.181 0.22 026 0.26 026 0.26 036

33 33 26 22 I63 11.4 7.5 4.2 I .40 0.83 2.4 31 28 25 20 15.5 10.9 7.I 4.1 2.3 I .37 0.83 30 27 24 19.7 14.9 10.5 6.9 2.3 I .)8 036 4.0 29 27 23 19.2 14.6 10.3 6.8 3.9 2.3 1.42 0.91 0.0s 0.059 0.093 0.135 0.101 0.22 0.26 0.26 0.26 0.26 0.26

20 18.6 16.4 13.4 10.2 ,

7.2 4.8 2.8 1.71 1.07 0.72 0.036 0.059 0.093 0.135 0.181 0.22 036 0.26 0.26 0.26 026

14.3' 13.2 11.6 9.5 7.3 5.2 3.5 2.1 1.28 0.83 0.58

6.50 6.75 7.w 7;25 7.w 7.75 8.oo 8.25 8:59 8.75 9

### .oo

6.50 6.75 1.00 7.25 7.50 7.7) 8.oo 0.25 8.50 8.75 9.w 0.009 I 0.0149 0.023 0.034 0.045 0.056 0.065 0.065 0.065 0.065 0.065

35 32 28 2) 17A 12.2 8.o 4.5 2.6 I.41 0.86 0.0129 0.02 I 0.033 0.046 0;OM 0.080 0.ox 0.092 0.092 0.092 0.on 0.0182 0.030 0.046 0.068 0.091 0.113 0.130 0.130 0.130 0.150 0.130

3s 30 26 22 16.3
4.2 2.4 I .40 0.83 0.026 0.042 0.066 0.095 0.128 0.159 0.184 0.184 0.184 0.184 0.184 0.036 0.059 0.093 ~.~

~ 0.135 0.181 0.22 0.26 0.26 0;26 0.26 0.26

31 28 25 20 15.5 10.9 7.I 4;l 2.3 1.31 0.83 30 27 24 19.7 14.9 10.5 6.9 4.0 2i3 1.33 0.86 29 27 23 19.2 14.6 10.3 6.8 3.9 2.3 1.42 0.91 0.051 0.084 0.131 0.190 026 0.32 0.37 0.31 0.37 0.37 037

29 26 23 19.0 14.5 10.2 6.8 4.O 2;4 1.52 1.01 0.051 0.131 0.190 0.26 0.32 0.37 0.37 0.37 0.37 0.37 0.084

20 18.6 16.4 13.5 10.3 7.3 4.9 2;9 1.el 1.18 0.82The Agency acknowledges that the Criterion Continuous Concentration stream flow averaging period used for steady

- state wasteload allocation modeling may be as long as 30 days in situations involving POTWs designed to remove ammonia where limited variability of effluent pollutant concentration and resultant concentrations in receiving waters can be demonstrated. In cases where low variability can be demonstrated, longer averaging periods for the ammonia Criterion Continuous Concentration (e.g., 3 0

- day averaging periods) would be acceptable because the magnitude and duration of exceedences above the Criterion Continuous Concentration would be sufficiently limited. These matters are discussed inmore detail in the Technical Support Document for Water Quality

-BasedToxics Control (U.S. EPA, 1985a).

(50 F.R. 30784, July 29, 1985) SEE APPENDIX A FOR METHODOLOGYBERYLLIUM
CRITERIA: 

# 8 Aquatic 

### Life
The available data for beryllium indicate that acute and chronic toxicity to freshwater aquatic life occur at concentrations as low as 130 and 5.3 ug/L, respectively, and would occur at lower concentrations among species that are more sensitive than those tested. Hardness has a substantial effect on acute toxicity. The limited saltwater data base available for beryllium does not permit any statement concerning acute or chronic toxicity.

Human Health
For the maximum protection of human health from the potential carcinogenic effects of exposure to beryllium through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentration should be zero, based on the non threshold assumption for this chemical. However, zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer risk over the lifetime are estimated at and The corresponding recommended criteria are 68 ng/L, 6.8 ng/L, and 0.68 ng/L, respectively. If these estimates are made forconsumption of aquatic organisms only, excluding consumption of water, the levels are 1170 ng/L, 117.0 nq/L, and 11.71 ng/L, respectively.

(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGY



# aBORON CRITERION:
750 ug/L for long

-term irrigation on sensitive crops.
INTRODUCTION: Boron is not found in its elemental form in nature: it is usually found as a sodium orcalcium borate salt. Boron salts
are used in fire retardants, the production of glass, leather tanning and finishing industries, cosmetics, photographic materials, metallurgy and for high energy rocket fuels. Elemental boron also can be used 

### in nuclear reactors for neutron absorption. Borates are used as "burnable"poisons.

RATIONALE: Boron is an essential element for growth of plants butthere is no evidence that it is required by animals. The maximum concentration found in 1,546 samples of river and lake waters from various parts of the United States was 5.0 mg/L: the mean value was 0.1 mg/L (Kopp and Kroner, 1967). Ground waters could contain substantially higher concentrations atcertain places. The concentration in seawater is reported as 4.5 mg/L in the forn of borate (NAS, 1974). Naturally occurring concentrations of boron should have no effects on aquatic life. The minimum lethal dose for minnows exposed to boric acid at 20 OC for 6 hours was reported to be 18,000 to 19,000 mg/L in distilled water and 19,000 to 19,500 mg/L in hard water (Le Clerc and Devlaminck, 1955: Le Clerc, 1960).
In the dairy cow, 16 to 20 g/day of boric acid for 40 daysproduced no ill effects (McKee and Wolf, 1963). Sensitive crops have shown toxic effects at 1000 ug/L or less of boron (Richards, 1954). Bradford (1966), ina review of boron deficiencies and toxicities, stated that when the boron concentration in irrigation waters was greater than 0.75 ug/L,
some sensitive plants such as citrus began to show injury. Biggar and Fireman (1960) showed that with neutral and alkaline soils of high absorption capacities, water containing 2 ug/L boron might be used for some time without injury tosensitive plants. The criterion of 750 ug/L is thought to protect sensitive crops during long

-term irrigation.

(QUALITY CRITERIA €OR WATER, JULY 1976) PB

-263943 SEE APPENDIX C €OR METHODOLOGYCHLORINATED BENZENES
CRITERIA 

# e Aquatic 

## Life The available data for chlorinated benzenes indicate that acute toxicity to fresh water aquatic life at concentrations as low as 250 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No data are available concerning the chronic toxicity of themore toxic of the chlorinated benzenes to sensitive freshwater aquatic life but toxicity occurs at concentrations as low as 50 ug/L for a fish species exposed for 7.5 days. The available data for chlorinated benzenes indicate that acute and chronic toxicity to saltwater aquatic life occur at concentrations as low as 160 and 129 ug/L, respectively, and would occur at lower concentrations among species that are more sensitive than those tested.

Human Health For comparison purposes, two approaches were used to derive criterion levels for monochlorobenzene. Based on available toxicity data, for the protection of public health, the derived level is 488 ug/L. Using available organoleptic data, for controlling undesirable taste and odor quality of ambient water, the estimated level is 20 ug/L. It should be recognized that organoleptic data as a basis for establishing a water quality criteria have limitations and have no demonstrated relationship to potential adverse human health effects.Trichlorobenzenes Due to the insufficiency in the available information for the trichlorobenzenes, a criterion cannot be derived at this time using the present guidelines. 1,2,4,5-Tetrachlorobenzene For the protection of human health from the toxic properties of 1,2,4,5-tetrachlorobenzene ingested through water and contaminated aquatic organisms, the ambient water criterion is determined to be 38 ug/L. For the protection of human health from the toxic properties of 1,2,4,5-tetrachlorobenzene ingested through contaminated aquatic organisms alone, the ambient water criterion is determined to be 48 ug/L. Pentachlorobenzene For the protection of human health from the toxic properties of pentachlorobenzene ingested through water and contaminated aquatic organisms, the ambient water criterion is determined to be 74 ug/L. For the protection of human health from the toxic properties of pentachlorobenzene ingested through contaminated aquatic organisms alone, the ambient water criterion is determined to be 85 ug/L. Hexachlorobenzene For the maximum protection of human health from the potential carcinogenic effects due to exposure of hexachlorobenzene through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentration should be zero based
on the non-threshold assumption for this chemical. However, zerolevel may not be attainable at the present time. Therefor, the levels which may result 

### in incramental increase of cancer risk 

# 0 over the lifetime are estimated at and The corresponding recommended criteria are 7.2 ng/L, 0.72 ng/L, and 0.072 ng/L, respectively. If the above estimates are made for consumption of aquatic organisms only, excluding consumption of water, the levels are 7.4 ng/L, 0.74 ng/L and 0.074. ng/L respectively. (45 F.R. 79316, November 28, 1980) SEE APPERDIX B FOR METHODOLOGYDICHMROPROPANES/DICHMROPROPENES CRITERIA: Aquatic Life The available data for dichloropropanes indicate that acute and chronic toxicity to freshwater aquatic life occurs at concentrations as low as 23,000and 5,700ug/L, respectively, and would occur at lower concentrations among species that are more sensitive than those tested. The available data for dichloropropene indicate that acute and chronic toxicity to freshwater aquatic life occurs at concentrations as low as 6,060 and 244 ug/L, respectively, and would occur at lower concentrations among species that are more sensitive than those tested.
The available data for dichloropropane indicate that acute and chronic toxicity to saltwater aquatic life occur at concentrations as low as 10,300 and 3,040 ug/L, respectively, and would occur at lower concentrations among species that are more sensitive than those tested. The available data for dichloropropene indicate that acute toxicity to saltwater aquatic 1ife occurs at concentrations as low as 790 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No data
are available concerning the chronic toxicity of dichloropropene to sensitive saltwater aquatic life.Human Health Using the present guidelines, a satisfactory criterion cannot be derived at this time because of insufficient avaiiable data for dichloropropanes. For the protection of human health from the toxic properties of dichloropropenes ingested through water and contaminated aquatic organisms, the ambient water criterion 

### is determined to be 87 ug/L. For the protection of human health from the toxic properties of dichloropropenes ingested through contaminated aquatic organisms alone, the ambient water criterion is determined to be 14.1 mg/L.

(45 F.R. 79318, November 28, 1980) SEE APPENDIX B €OR METHODOLOGYCRITERIA:

- For endrin the crit *ENDRIN
Aquatic Life rion to protect fr shwater aquatic li e
as derived using the Guidelines is 0.0023 ug/L as a 24

-hour average, and the concentration should not exceed 0.18 ug/L at any time. For endrin the criterion to protect saltwater aquatic life as derived using the Guidelines is 0.0023 ug/L as a 24

-hour average, and the concentration should not exceed 0.037 ug/L at any time.

Human Health The ambient water quality criterion for endrin is recommended to be identical to the existing water standard which is 1.0 ug/L. Analysis of the toxic effects data resulted in a calculated level which is protective of human health against the ingestion of contaminated water and contaminated aquatic organisms. The calculated value is comparable to the present standard. For this reason a selective criterion based on exposure solely from consumption of 6.5 g of aquatic organisms was not derived.

*Indicates suspended, canceled or restricted by U.S. EPA Office of Pesticides and Toxic Substances

(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYHEPTACHMR CRITERIA: Aquatic Life For heptachlor the criterion to protect freshwater aquatic 

# 0

life as derived using the Guidelines is 0.0038 ug/L as a 24

-hour average, and the concentration should not exceed 0.52 ug/L at any time. For heptachlor the criterion to protect saltwater aquatic life as derived using the Guidelines is 0.0036 ug/L as a 24

-hour average, and the concentration should not exceed 0.053 ug/L at any time.
Human Health For the maximum protection of human health from the potential carcinogenic effects of exposure to heptachlor through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentration should be zero, based on the non threshold assumption for this chemical. However, zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer risk over the lifetime are estimated at and The corresponding recommended criteria are 2.78 ng/L, 0.28 ng/L, and 0.026 ng/L, respectively. If these estimates are made for consumption of aquatic organisms only, excluding consumption of water, the levels are 2.85 ng/L, 0.29 ng/L, and 0.029 ng/L, respectively.

(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYCRITERIA : HE?ACHLOROCYCU3HEXANE
Aquatic Life

€or lindane the criterion to protect freshwater aquatic life
as derived using the Guidelines is 0.080 ug/L as a 24

-hour average and the concentration should not exceed 2.0 ug/L at any time. For saltwater aquatic life the concentration of lindane should not exceed 0.16 ug/L at any time. No data are available concerning the chronic toxicity of lindane to sensitive saltwater aquatic life. BHC The available data for a mixture of isomers of BHC indicate that acute toxicity to freshwater aquatic life occurs at concentrations as low as 100 ug/L and would occur at lower concentrations anong species that are more sensitive than those tested. No data are available concerning the chronic toxicity of
a mixture of isomers of BHC to sensitive freshwater aquatic life. The available data for a mixture of isomers of BHC indicate that acute toxicity to saltwater aquatic life occurs at concentrations as low as 0.34 ug/L and would occur at lower concentrations among species that are more sensitive than those tested. No data are available concerning the chronic toxicity of
a mixture of isomers of BHC to sensitive saltwater aquatic life.Human Health For the maximum protection of human health from the potential carcinogenic effects of exposure 

### to alphahexachlorocyclohexane through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentrations should be zero,based on the nonthreshold assumption for this chemical. However, zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer risk over the lifetime 

### are estimated at 10

-6 and The corresponding recommended criteria are 92 ng/L, 9.2 ng/L, and .92 ng/L, respectively. If these estimates are made for consumption of aquatic organisms only, excluding consumption of water, the levels are 310 ng/L, 31.0 ng/L, and 3.10 ng/L, respectively. For the maximum protection ofrhuman health from the potential carcinogenic effects of exposure to beta

-hexachlorocyclohexane through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentrations should be zero, based
on the nonthreshold assumption for this chemical. However, zero level may not be attainable at the present time. Therefore, thc levelswhich may result in incremental increase of cancer risk
over the lifetime are estimated at lo+, and The corresponding recommended criteria are 163 ng/L, 16.3 ng/L, and 1.63 ng/L, respectively. If these estimates are made for consumption of aquatic organisms only, excluding consumption of water, the levels are 547 ng/L, 54.7 ng/L, and 5.47 ng/L, respectively.For the maximum protection of human health from the potential carcinogenic effects due to exposure of gamahexachlorocyclohexane through ingestion of contaminatedwater and contaminated aquatic organisms, the ambient water concentrations should be zero,based on the nonthreshold assumption for this chenical. However, zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer risk over the lifetime are estimated at lom5, and The corresponding recommended criteria are 186 ng/L, 18.6 ng/L, and 1.86 ng/L, respectively. If these estimates are made for consumption of aquatic organisms only, excluding consumption of water, the levels are 625 ng/L, 62.5 ng/L, and 6.25 ng/L, respectively. For the maximum protection of human health from the potential carcinogenic effects of exposure to technicalhexachlorocyclohexane through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentrations should be zero, based on the nonthreshold assumption for this chemical. However, zero level may not be attainable at the present time. Therefore, the levels which may result in incremental increase of cancer risk over the lifetime are estimated at and The corresponding recommended criteria are 123 ng/L, 12.3 ng/L, and 1.23 ng/L, respectively. If these estimates are made for consumption of aquatic organisms only, excluding consumption of water, the levels are 414 ng/L, 41.4 ng/L, and 4.14 ng/L, respectively. 

# 0Using the present guidelines, satisfactory criteria cannot be derived at this tine for delta and epsilon hexachlorocyclohexane because of insufficient available data. 

# a

(45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGYMIREX CRITERION: 0.001 ug/L for freshwater and marine aquatic life. RATIONALE: 

# 0

Mirex is used tocontrol the imported fire ant Solenssis saevissima richteri in the southeastern United States. Its use is essentially limited to the control of this insect and it is always presented in bait. In the most common formulation, technical grade mirex is dissolved in soybean oil and sprayed on corncob grits. The bait produced in this manner consists of 0.3 

## __

percent mirex, 14.7 percent soybean oil and 85percent corncob grits. bait often is applied ata rate of 1.4 kg/ha, equivalent to 4.2 grams of toxicant per hectare. The mirex
Relatively few studies have been made of the effects of mirex
on freshwater invertebrates of 'these, only Ludke et al. (1971) report chemical analyses of mirex in the water. Their study reported effects on two crayfish species exposed tomirex by three techniques. First, field

- collected crayfish were exposed to several sublethal concentrations of technical grade mirex solutions for various periods of time: second, crayfish were exposed to 

### mirex leached from bait (0.3 percent active ingredient); and third, the crayfish were fed mirex bait. Procambarus - blandingi juveniles were exposed to 1 or 5 ug/L for 6 to 144 hours, transferredtocleanwater and observed for 10 days. After 5 days in clean water, 95 percent of the animals exposed to 1ug/L for 144 hours were dead. Exposure to 5 ug/L for 6, 24, and 58 hours resulted in 26, 50, and 98 percent mortality 10 days after transfer to clean water. Crayfish,Procambarus 

# w,were exposed to 0.1 and 0.5 ug/L for 48 hours. Four days after transfer to clean water, 65 percent of the animals exposed to 0.1 ug/L were dead. At the 0.5 ug/L concentration, 71percent of the animals were dead after 4 days in clean water. Tissue residue accumulations (wet weight basis) ranged from 940- to 27,210

-fold abovewater concentrations. In leached bait experiments, 10 bait particles were placed in 2 liters of water but isolated from 20 juvenile crayfish. Thirty percent of the crayfish were dead in 4 days and 95percent were dead in 7 days. Water analysis indicated mirex concentrations of 0.86 ug/L. In feeding experiments, 108 crayfish each were fed one bait particle. Mortality was noticed on the first day after feeding, and by the sixth day 77 percent were dead. In another -

*

experiment, all crayfish were dead 4 days after having been fed 2 bait particles each. From this report it is obvious that mirex is extremely toxic to these species of crayfish. Mortality and accumulation increase with time of exposure to the insecticide. Concentrations as low as 0.1 ug/L or the ingestion of one particle resulted in death. Research to determine effects of mirex on fish has been concentrated on species which have economic and sport fishery importance. Hyde et al. (1974) applied mirex bait (0.3 percent mirex) at the standard rate (1.4 kg/ha) in four ponds containing channel catfish, 

# - Ictalurus punctatus. Three applications were made over an 8

-month period with the first application 8 days after fingerling (average weight 18.4 g) catfish were placed in the ponds. Fish were collected at each subsequent application

- *(approximately 4

-month intervals). Two and one half months after the final application, the ponds were drained, all fish were measured and weighed, and the percent survival was calculated. Mirex residues in the fish at termination of the experiment ranged from 0.015 ug/g (ppm) in the fillet to 0.255 ug/g in the fat. 

# 0

In another study, Van Valin et al. (1968) exposed bluegills,


## - LeEmis 

## -_ macrochirus, -- and the goldfish, Carassius auratus, to mirex by feeding a mirex

-treated diet (1, 3, and 5 mg mirex per kg body weight) or by treating holding ponds with mirex bait (1.3, 100, and 1000 ug/L computed water concentration). They reported no mortality or tissue pathology for the bluegills: however, after 56 days of exposure, gill breakdown in goldfish was found in the 100 and 1000 ug/L contact exposure ponds, and kidney breakdown was occurring in the 1000 ug/L ponds. Mortality in the feeding experiments was not related to the level of exposure, although growth of the bluegills fed 5 ug/L mirex was reduced. In laboratory and field test systems, reported concentrations of mirex usually are between 0.5 and 1.0 ug/L (VanValin et al. 1968: Ludke et al. 1971). Although mirex seldom is found above 1 ug/L in the aquatic environment, several field studies have shown that the insecticide is accumulated through the food chain. Borthwick et al. (1973) reported the accumulation of mirex in South Carolina estuaries. Their data revealed thatmirex was transported from treated land and marsh to the estuary animals and that accumulation, especially in predators, occurred. In the test area,water samples consistentlywere less than 0.01 ug/L.Residues in fishvaried from non- detectableto0.8 ug/g with 15 percent of the samples containing residues. The amount of 

### mirex and the percent of samples containing mirex increased 

### at higher trophic levels. Fifty

- four percent of the raccoons sampled contained mirex residues up to4.4 ug/g and 78 percent of the birds contained residues up to 17 ug/g. Nagvi and de laCruz (1973) reported average residues formolluscs (0.15 ug/g), fish (0.26 ug/g), insects (0.29 ug/g), crustaceans (0.44 ug/g) and annelids (0.63 ug/g). They also reported thatmirex was found inareasnot treatedwithmirex which suggestsmovement of the pesticide in the environment. Wolfe and Norment (1973) sampled
an area for one year following an aerial application of 

### mirex bait (2.1 g mirex/ha). Crayfish residues ranged from 0.04 to 0.16 ug/g. Fish residues were about 2 to20 timesgreaterthan the controls and averaged from 0.01 to0.76 ug/g. Kaiser (1974), reported the presence of 

### mirex in fish from the Bay of Quinte, Lake Ontario, Canada. Concentrations range from 0.02 ug/g in the gonads of the northern long nose gar, Lepistosteus osseus, to 0.05 ug/g in the post

-anal fin of the northern pike, 

## Esox lucius. Mirex has never been registered for use in Canada. Mirex does not appear tobe greatly toxic to birds, with LC5O's for the young of four species ranging from 547 to greater than 1667 ug/g (Heath et al. 1972). Long

-term dietary dosages caused no adverseeffect at3ug/gwithmallards and 13ug/gwith pheasants (Heath and Spann, 1973). However, it has been reported (Stickel et al. 1973) that the persistence of 

### mirex in bird tissue exceeds that of allorganochlorine compounds tested exceptfor DDE. Delayed mortality occurred among birds subjected to doses above expected environmental concentration. A summary examination of the data available a*this time shows a mosaic of effects. Crayfish and channel catfish survival .isaffected by mirex in the water or by ingestion of the bait particles. - Bioaccumulation is well established for 

### a wide variety of organisms but the effect of this bioaccumulation on the aquatic ecosystem is unknown, There is evidence that mirex is very persistent in bird tissue. Considering the extreme toxicity and potential for bioaccumulation, every effort should be made to keepmirex bait particles out of water containing aquatic organisms and water concentrations should not exceed 0.001 uq/L mirex. This value is based upon an application factor of.0.01 applied to the lowest levels at which effects on crayfish have been observed. Data upon which tobase a marine criterion involve several estuarine and marine crustaceans. A concentration of 0.1 ug/L technical grade mirfx in flowing seawater was lethal to juvenile pink shrinp, Penaeus durorarum, in a 3

-week exposure (Lowe et al. 1971). In static tests with larval stages (megalopal) of the mud crab, Rhithropanopeus harrisii, reduced survival was observed in B.l-ug/Lmirex (Bookhout et al. 1972). 

### In three of four 28

-day seasonal flow

-through experiments, Tagatz et 

### al. (1975) found Educed survival of Callinectes sapidus, Penaeus durorarum, and grass shrimp, Palaemonetes pugio, at levels 

### of 0.12 ug/L in summer, 0.06 ug/L in fall and 0.09 ug/L 

### in winter. Since two reports, Lowe et al. (1971) and Bookhout et al. (1972), stated that effects of mirex on estuarine and marinecrustaceans were observed only after considerable time had elapsed, it seems reasonable that length of exposure 

### is an important consideration for this chemical. This may not be the
case in fresh water since the crayfish were affected within 48 hours. Therefore, a 3- to 4

-week exposure night be considered tlacutetB and by applying an application factor of 0.01 to 

### a reasonable average of toxic

-effect levels as summarized above, 

### a recommended marine criterion of 0.001 ug/L results.

(QUALITY CRITERIA FOR WATER, JULY 1976) PB

-263943 SEE APPENDIX C FOR METHODOMGYNICKEL CRITERIA: Aquatic

## Life For total recoverable nickel the criterion (in ug/L) to 

# 0

protect freshwater aquatic life as derived using the Guidelines is the numerical value given by e(0.76[ln(hardness)]+l.06) as a 24

-hour average, and the concentration (in ug/L) should not exceed the numerical value given by .(0.76[ In (hardness) ]+4.02) at any time. For example, athardnesses of 50, 100, and 200 mg/L
as CaC03 the criteria are 56, 96, and 160 ug/L, respectively, as 24

-hour averages, and the concentrations should not exceed 1,100, 1,800, and 3,100 ug/L, respectively, at any time. For total recoverable nickel the criterion to protect saltwater aquatic life as derived using theGuidelines is 7.1 ug/L as a 24

-hour average, and'the concentration should not 

# 0 exceed 140 ug/L at any time.
Human Health For the protection of human health from the toxic properties of nickel ingested through water and contaminated aquatic organisms, the ambient water criterion isdetermined tobe 13.4 W/L. For the protection of human health from the toxic properties of nickel ingested through contaminated aquatic organisms alone, the ambient water criterion is determined to be 100. Ug/L* (45 F.R. 79318, November 28, 1980) SEE APPENDIX B FOR METHODOLOGY2,3,7,8-TETRACHLORODIBENZO-P-DIOXI€l CRITERIA: Aquatic Life Not enough data are available concerning the effects of 

# a
2,3,7,8-TCDDon aquatic life and its uses to allow derivation of national criteria. The available information indicates that acute values for some freshwater animal species are >1.0 ug/L; some chronic values are <0.01 ug/L; and the chronic value for rainbow trout is <0.001 ug/L. Because exposures of
some species of fishes to 0.01 ug/L for <6 days resulted in substantial mortality several weeks later, derivation of aquatic life criteria for 2,3,7,8-TCDD may require special consideration. Predicted bioconcentration factors (BCFs) for 2,3,7,8-TCDD range from 3,000 to 900,000, but the available measured BCFs range from 390 to 13,000. If the BCF is 5,000, concentrations >0.00001 ug/L should result 

### in concentrations in edible freshwater and saltwater fish and shellfish that exceed levels identified in a US. FDA health advisory. If the BCF is >5,000 or if uptake in a field situation is greater than that in laboratory tests,the value of 0.00001ug/L will be too high. 

# 0

Human Health €or the mxirnux protection of human health from the potential carcinogenic effects of 2,3,7,8-TCDD exposure through ingestion of contaminated water and contaminated aquatic organisms, the ambient water concentration should be zero. This criterion isbased on the nonthreshold assumption for 2,3,7,8-TCDD. However, zeromaynotbe an attainablelevel atthistime. Therefore, the levels that may result in an increase of cancer risk over the lifetime are estimated at and The corresponding recommended criteria are 1.3~10-~, 1.3~10-~ and 1.3x10-’ ug/L, respectively. If the above estimates are made for consumption of aquatic organisms only, excluding consumption of water, the levels are 1.4x30-~, 1.4x10-* and 1.4x10-’ ug/L, respectively. If these estimates are made for comsumption of water only, the levels are 2.2~10-~, 2.2xlO-’ and 2.2~10-~ ug/L, respectively.

(49 F.R. 5831, February 15, 1984) SEE APPENDIX B €OR METHODOLOGYALKALINITY

BARIUM

REFERENCES CITED Browning,E1961.Toxicityofindustrialmetals. Butterworth,London. btr.M., etd.1970. EffeetaofpollutiononfmhMe, heavymea AnndLiterature review.Jw. WaterPoll.ContFed.42W. L.ngr.NA1961.Handbookof cbemistry.lorhed Yd;fiw-Hill, BookCo.. New Ywk. little,A.D. 1971.Iwrg.oiccbemicalpollutionof fnahwater.Waterqdty &la lmk Val.2.US. EnvimnmentalProteetionAgency, la010DPV.pp.2e26. McKee, J.E. ud W.W. Wolf. 1963.Water quality criteriaCalif& Skte Watm

Muma ContrdBoard,Pub.No.3

-A National AademyofSeieooes.NationalAcademyof Engioeering. 191+Waterqwlity

criteria,1972US GovernmentPrintingOff=, W.shin@n, D.C. Patty,FAl962lndustrialbygieneudtoximlogy,VoL1I.JohnAWiley,NerYatpp

%loo2 CitedinUS. DepartmentofHealth,EduatianudWelfare. 1M. Public Health SeMce. 1WB.Drinkingwater quality of rkasdintast.te eUria

watersupplies.U.S.Depar(mentof HealthEduatianudWelfy W..hin%on,D.C. Sollmann. T.H. 1957.A manudofpharmamlogyanditsapplitionto ud

toljcolcgy.8thed.W.B. SaundenCo.Philadelphia Stokinger,H.E.,radRLWmdwaardl968.Toljcdogiemetbodrfaat.blirhin~

waterstandards.Jour.Ame?.WaterWorlrs h. 50.615. U.S Deprtment of Health, Education and Welfue. 1968. Preliminvy air pdlutioa

rwey ofbuiurnanditscompouinja,aliteraturereview.NaW AirPoUdnCODtml AdministntionPubliationNo.AITD69-23,Raleigh,N.C.

BORON

REFERENCES CITED Bw. J.W.. andM.Fireman 1960.Boron *tion andmlean~ bymikSoilsd.SOe Amer.Ra2-l: 115. Bdwd.G.R 1966. hn [toxicity, indicator plants], indi.gwstic criteriafor plants and .oikH.D.Chapman. ed UnivwsityofCalifornia, DiviaionofAgridtural Science, Berkeley,p.53. Le ClemE 1960.The self-purifkationofstramsudtherelatia~hip betweenchemical md biologid test& Ra Seeond Symposium on Treatment of Want? Watem. Pergamonh. London,p.231. LeClem.E,andF.DevhindL1456.Fiahtoxicitytatsandwaterqdty. Bull.deBeige CondumentE.u. 28:11. KoppJ.F.. udRC. Kmner. 1961.Tracemet& in watenoftheUnitEdSlate.. Fed4

WaterPollutionConbolAdministration,US. DepartmentofInterior,Cincinnati.Ohio. YcKee,J.E, udA.W. Wolf. 1963.Waterquality criteriaStateWaterQrulityConmi Bcwd.haamento,Calif.Pub.3-A. National ArdemyofSeieocpa,NationalAcademyofEngineering.1974Waterpdity

mi- 1972US. GovernmentPrintingOffii.W.shingon, D.C. RiW. LA. ed.1954.DiagnosisandimpmvementofsalinemdIwi mi.AgrieultHmdbmkNo.€U.US. GovernmentF’rinting Offioe,Wpshington,D.C.CHMROPHENOXY HERBICIDES
REFERENCES CITED Knua.u dted by Mitcheaa. J.W.,REHogmn,andC.R. Gaetjem. 1946.Tol- of

fum .ni& to feed mnUining2,4diehlomphenoxyacetiedb Jour. Anid.sd. 5:226. Lthrmn.AJ. 1986. Sum- of pticidetoxidty. Assodrtbn of Food md Dnrg

OificialnoftheUS..Toph KAM. pp.1-40, Palmer. J.S.. and RD.Radeleff. 1964.The toximlcgkelf& ofcertainfungiddea md

herbicidaonsheepandcattle.Ann.N.Y.Ad. Sei. 111:729. Wury,J.H. 1963Toxicity of24dichloruphenoxyacetic acidforman anddog. Arch.

EnvirHealth.7:282

COLOR

REFERENCES CITED hceriom WaterWorksAssodrtion.1971.WaterqudityandtreatmentBrdedMdmwBirge. EX.md C. Juday. 1990.A amnd reporton .oh radiationandinland Up.. BU A.P., andRF.chrisrmaal96sachvrrtMstw
. ofcoloredsurfacewatersJau. HillBookCO.,NewYork Tnns. Wk. Ad. Science,AM.Let.

### a: 285. ' hmer. Waterworkskdn.55:7s. El&. AP..and RF.chrisrmaa 1953b.Cbemi~I rby.ctaufKI ' offdvkddaJau.

'

~~ Akner.w.7eTworksAasa,55:w. Natio~l Ademyof MencmNationalAcademyofEngirraing.1974Wstaqdty N~tio~l Technical Adviawy Committeeto tbe SecreqoftbeIntpiOr.1988.Wata Public iiealth service. 1952 Drinkirawaterst.nduda,1962PASF'uM No. SS6.US.

criterir1972US. GovernmentRintingOffice.Wnhingmn,D.C. qualitycriteriaUS. GovernmentPrintingOffice,Wuhingron,D.C. GovernmentPrintingoifii, Washir;gOn.D.C. Sawyer.C.N. 1960.Chemistryfor ..nitary engineera. Mdmw-HillBodrCo.,NewYOrL. Shn~w. J. lSiEffectofyellow ode ddsonLon md other meubinwater.Jour. A'-: Waterworkshti 56:1062' Stllldvdmethodsfortheexaminationofwaterandwastewater.l8tbed.1971.Editedby

MichaelC. Rand.etd.Moan PublicHealthAran. AmericanWsterWorks kdn. WaterPollutionConmlFederation.Wrahington.D.C. Welch,P.S. 1952Imnology.M&nw-Hill BookCO.,NewYork.

DEMETON

REFERENCES CITED Butler, PA.1964. COmwrd.l fiiheryisvestigatbm. P.ges 61BinPedicide vildliie

atudiea.1969.U.S.bh mdWildlifeWee Cinuh149.WMhingtOn,D.C. fuh.TnnhAmer.FishSa67:39. Ludenunn,D., radH.Neurmnn ubediewirh~ng derdtlichen konwdnsedd. tidde aufdietieredeauasr.mers.'higufurschdlingskundeundPILuneMut~. s:5. Mek.€3.. mdW.A. MeAllkter.1970.lnseetiddeausoeptibilityof *wemmmonfuh funilyrepesentativea.Tnna Ama. hh. Sa992l. toxiclevelsofpatieidesTnnaAmer.Fiahk101:817. -of oumw~terfiishesTnns.Amer.Fiah.~81:175. Henderson.C.. mdQ.H.Mering.EX8. Toxicityof organicpimphawi- to

YcCmn,JA., mdRLJq. WRVcrrebnl d.nugetoMueeilbexpxedto rutely Pickering,Q.H., etd.196LTbetoxieity ofap.niephoaphow inaect*idpatodifferentSanders, H.O. 1912 Toxicity of come iMeetiddes to four SpeCKaof malamstracan wtxmns. Burnu of Sport Fisheries and Wildlife, Tech Plpu No. 66 US. DepartmentoftbeInkria,Washington.D.C.pp.S-19. We&+ C.M. 1968ThlQtamirution of cholinedtemeinthehaintimueofthR0lpgies

offnshwstuTubmdibiructividoninvim.Emlogy,89: 194 We&. C.M. 1968. Reapo~ of fish to sublethal expos- of

# -* phmphom iweeticidea.Sew.andInd.Wastes.31:580. Web. C.M. 1961. PhVsologieal effect of organic phosphorus inseetieides on several

speciesolfish.Trans.Amer.M. Soc.90:143 Web.C.M.. andJ.H.Gakstatter. 1964s.Detection of -ticides inwaterby biwhemical aaaay.Jour.WaterPoll.Cant.Fed.36:240. Weisa. C.M.. and J.H. Gakatatter. 1Wb.The decay of anticholineste- activity of

organic phmphorua inseeticideaon storage in waters of differentpH. Advances in WaterPoll.Research,I:&%.

GASSES, TOTAL DISSOLVED

REFERENCES CITED buck.G.R,etal. 1975.Monality.saltwater adaptationandreproductionoffMhexpeed

to gas supmaturated water. US. Environmental RoteaionAgency,WesternFish ToxicologyStation.Cawallis.OR.Unpublishedreprt. Clay, A.. et al. 1975. Erperimental induction of gas bubble W in menhaden.

PRsented atthe AmericanFisheries Society,September 1975,IraVegu,Nev. New EnglandAquarium,Boston. Dewley. EM.,and WJ. &I. 1975. Effect, of various mnoenhLions of diaaolved

atmmphencgeonjuvenilechinooksalmon. Onmrhynchwtdmqfda, andateelhesd trout.Fish.Bull. Dawley, E,et al. 1975. BioaaMp of total dissolved gas pmu~ National Mviw FisheriesSen&, Seattle,WaabUnpublhhed ~prt DeMont,J.D., and RB'.Miller.1972firstreportedincideweofpbubbledkw inthe heated effluent of a steam electric generating station. Roe. Bth landmeeting, SoutheratAssoe.ofGameandFiahCommi\aown Ebel,WJ., etal. 1975. Effect of atmospheric gassuperssturationcarvedbydamson salmonandsteelheadtroutoftheSnakeandColumbiaRiven.FinalReport. Nhwest Fisheries Center.NationalMpriwFisheriesService.Seattle.Wash. Keup.L.E1975.Howtoreadafishkill.WaterandSew%ge Work8,121:18. Lindmth,A 1957.Abiogenic gasiupnstmtionofriver water.Arch.Iiydrobiology,59:

589. Mrlouf, R 1972Oenurenoeofg.sbubble diseasein Wspeciesofbivalve mollusks

Jour.Fish.Res.Bd.Can.B:SBB. Mlsoello, RA, et al. 1975. Evaluation of alternative mlutio~ togas bubble disease monalityof menhaden atPilgrimNudearPowerStation.YankeeAtomicElectricCa.. Weatborn.M- YAEX-IoB7.

~~~ ~~ ,~~~ ~ ~~~ Kaoonal Academyof Saenapa. National Academyof hgimennp.1974Waterquality

cntena. 1972V.S.Governmenthung Office.Washington.D.C. Nebeker.AV.,etal. 1975. Effectsof gas supmaturate

-wateronfreshwaterinverteb

ntes.Roe.GasBubble MWorlrshop.BattelleNorthwest, EnergyReeeychlad DevelopmentAgencySpgialReport Nebeker.AV.,etal.1976~.Nitrogen,oxygen,andcartondioxideasfactomdfdng fMh BhVd h8yNpenatmtedwater. h. her. Fish.SOe Nebeker. AV.,etal. 197%.SvVivalofmhoandscckeyesalmonsmolt,inseawaterdter

exposuretogas8upenaUMt.dwater.TraM.Amer.FishSoe. Renfm,W.C. 1W. Gas bubble morlality offlahes in Gilveston Bay,Tex. h. Amer. Fish.5% 92320. Ruder.RR 1974.Gasbubbledisease:Monalitiesofmhosalmon,Chmrh&ud &A,

in water with mustant total gas presure and different oxygen-nitrogen ntim. National Oceanicand Atmm. Admix,Natl.bhr.Fish.SW., NorthwestFishCenter, Seattle.WMhUnpublishedmuscript Rulifmn,RL and G: Abel. 197LNivogen supenaturationintheColumbiaand Snake

Riven. Ted Rep; TS-Cr%'/O-Z%0162 U.S. EnvLonmental Rotenion Agency, won X,Seattle,Wash. Van Slyke. D.D., et al. IW.Studiesofgaa mdelectrolyteequilibri.inMoo&XVIII.

Solubility and phyxieal stateof atmphericni-n inbloodfell8 andplramaJour. Biol.Chem.1&:571.GUTHION REFERENCES CITED Adelmn.I.R,mdLL Smith.UnpublisheddataDeprtmentofhtomlogy,Fisberiea

andW'ildlife,UniversityofMinnesota,StPaul. Benlre, G.M.. md S.D. Murphy. 1974. Anticbollnesterase setion of wthylpurtbjon,

ppnrhion and ezinphoamethylin mi@andfmh:Onsetudremveryofinhibition.Bull. Envimn. Contam.Toxiwl.12:117. Butler, PA1963. CommerCial fuheries investiptiona. In Peaticirk-wildlife rtudim

during 1961 and 19EZ US. Fish and Wildlife Service Circ 167. W.abin%on, D.C. Caner,F.L 1971.In tIwstudiesofbrainacetylcholines- inhibitionby wkwpbosp

bateand earbarnateinseetieidesinfishPhD.Dhenation,LouLiuuStateUniverrity. BatonRouge Coppage.D.L 1972Orgmophosphateperticidea:Speific levelofbninACHEinhibition

relawdtodenthinsheepheadminnows.Trans.Amer.FishSoe.101:534 Coppcge,D.L. andT.W. Duke. 1971.Effeetsofpenicidfaineatuvicadongthegulfand mutheart Atlantic mas-. In C.H. Schmidt, ed. F?a+nga ofthe 2nd gulf mt mnference on mquita suppmion and wildlife management National Mosquito Control-Fish andWidlife Management CoordinatingCommittee, Wuhingtan.D.C. Coppage,D.LandE Mrtthews. lPi4.Sbontermeffectsoforgawpholph.tepticidca

on eholinfaterace ofestuarinefuheaandpinkahrimp.Bull.Envimn.ContamToxiool. 11:483. Coppage. D.Letal. Inpreaa. Brainseetylcholinesteraseinhibition infmh Madiagnmk

of environmental poisoning by malathion. 0,Mmethyl S(l.24imrbethoxyethyl) phoaphorodithioate.PesticideBiochemistryandPhysiology. Davis,H.C.. andH. Hidu. 1969.Effectsofpesticidesonembryonicdevelopmentofdm

andopteraandon survivalandgrowthofthelarvae.U.S.FishandWildlife Service, FisheryBulletin,67: 993. aton.J.G. 1970. Chmnic malathion toxicity to the blvegiU (kpomis &inrs

ILfinesque). WaterResearrh,4:6iS. Flinl, D.R. etd.1970.Soilrunoff,leaching. md.dsorption .ndwater stabilitystudies

withguthion.Chew ReptNo.m. Gaufn, A.R. et d.1965. The toxicity of 10 organic insecticides to,vviow4ustic

invertebratea.WaterandSew.Worlw. 112276. Hollnnd. H.T., et al. 1967.Useof fmhbrain acetylehaliretermetomonitorpollutionby

organopbmphorucpesticides.Bull.Envimn.ContanToximl.2: 156. Jensen.LD.,andAR Caufn.1966.Acute and lpng termeffeetsoforganicinmaicides

ontwoSpeciesofstowflynriadr.Jour.WaterPolLContFed. 98:1zTJ. btr.M.1961.Acute tadcityofmmeorganicinseeriddestothrse @ofvlrnonida

andtothethresapinesdddeback.Tm. Amer.Fish.Soc90:!264. Wv. Y.,and S. Sai+g. 1989.Se~itivity of pondfuhtomtnion(uinphmethyl)ud panthion.Bamidgeh.21:67. Macek,KJ.. et a]. 1969.Theeffectsoftemperature onthesuseoptibilityofthebluegills

nndrainbowmuttoselectedpesticide%Bull.hvimn.ConramToxiad.3174. Macel,KJ.,andW.A. MeAllister. 1970.Insecticide susoeptibilityofsomemmmon fmh familyrepmntativea.TMaher. Fish.sOe.99:P. Meyer. F.P. 1965.The experimental u8eof guthionas aselectivefvheradicator.Trms

Am. FiahSor44:'ZX. Nebeker,A.V.. and A.R Gnuh1964.Bioaaraystodeterminepsticidetodcityto ilw

amphipal mwn. Gummanu hcwtris.Roe.UtahAd. sd.Ma and Letters. 41:64. Piekering,Q.H., etal. 1962Thetoxicityoforganicphaphonuinsecticidca todifferent speciesofwmwaterfmheaTrana.d. Fish.k91:1'75. Ponman.J. 1912 Resulfsof acutetestawithmarineorganisms.usingitandvdmethods.

P.ges212-217 inRuivo. ed.Menepollution and se~ life.FishingNem(Books)Ltd.. London. PmL G..andRA. Lersure.1974.Sublethaleffectofmalathiontothreedmnidspied. Bull.hvimn.Conulm.Toximl.12:912 sudem.H.O. 1969.Toxicityofpesticides tothematacean.Gammanuhcwtri~ BWU of SportFisheriesandWildlifeTwb.PaperNo. 25,US.Depanmentofthe Interior, WMbinRWn.D.C. Wen.KO.197!2 Toxicity of wome i&dea to four apeEiea of

# --

cn~- US.Deprtmentof the Interior. Bureruof SportFisberieaandWildlife TecbParerNo.66.Wnhington,D.C. Wen, E.O., ud O.B. Cape.19BB.Tnerelativetoxicitiesofwedptiddeato nrids Tucker. RK. mdD.G.Crabtree. 1970. Handbook oftoxicityofpeatiades to wildlife.

BvreruofSpwrFLbericaud Wildlife RaavorF'ubl. No.slUS Ikprrmantoftbe Interior,W.rhin%on, D.C. We% C.Y 1868Tbedetermimtionof eholinertansein thebnintissueofthroespedea

offreshwaterfuhuditrrrivationisviw.Emloay.S:1% Weim, C.Y. 1868. Rasponr of 

### rito mbleth.l expama of 0rp.niC

id& Sew.andIndW.stea,31:580. W&. C.M. 1961. Physiological effects of wp.nic pbaspkru ineriddpson severr.! Web,CX, ladJ.H.c.Lsuttu. 1864Detectionof mdea inGtuby bkkw ofLhree~ofatoneiliea~ol.~oceanog.l3:1lz

.Fe&of Ti TMaAmu. Fhh

### kso:143. UUY. Jw. WaterPoll. ContFed.86:240. 

# aHARDNESS



# a REFERENCES CITED Doudomff,P.and M.btz.1953.Critical reviewcfli+rstweon thetoxicityofinduarrial

wastesand theirmmponenh tofish. 11: Themetabasa.d@.Sew.andind.Wasted,25: Bm National Academyof Science.National Academyof Engineering. 1974.Waterquality

criteria.1912.US GovernmenttintingOffice.Washingon,D.C. National Technical Ad-r). Committee to the Secretaryof theInterior. 1963.Water

qualityenterin.US. GovernmenttintingOffice.Washington,D.C. Sawyer.C.H. 1960.Chemisqfor sanitaryengineen.McGraw-HillBookCo..NewYork. Stiff, MJ. 1971. Copper/biearbonatP equilibria in mlutio~ of bicarbonate ion at mncentrationssimilartothm foundinnatd water.WaterResearch.5:171.

MALATHION REFERENCES CITED Andemon. B.G. 1W. The toxicity oforganicinsecticidestohphniaSemadSeminaron Biol. Pmblemsin Water Pollution. Robert A.TaftSanitaryhgineeringCenterTgh. ReportW603,Cincinnati,Ohio. Bender,M.E19%. Thetoxicity ofthehydrolysisandbreakdownpduaaofmaLthionto

thefatheadminnow(Anuphaler pmmcloa Rainesque).Water&a8:571. BwnuofSportFisheriesandWildlife. 1970.ResournPublication106.W.abiagton, D.C. Butler, PA. 1963. Commercial fisherie investigations. In Pd& wildlife studies

during 1961 and 1962U.S.Fish and Wildlife senicecirr 167.Wdiagton, D.C. Coppage,D.L, and T.W. Duke. 19il.~fect3cf~ticidesinestu~es~ongtbe~~

southeast Atlantic masts.In C.H. Schmidt, ed. Roceeding~ of the2nd gulf mt mnference on mosquito suppression and wildlife mamrnent.Natiod Mosquito Control

-Fish and WildlifeManapmeat CcardimtingCommittee,Wdngton.D.C. Coppage. D.L. and E. Matthema. 1974.Shorttermeffectsoforganophosphatepeatieides

oncholinestemof estuarinefiahesandpinkshrimp.Bull.EnvirunCoatamToxiad. 11:w. Coppa@?, D.L.elal. 1975.Brain acetylcholinesterase inhibition in fuh Madiagnosisof

envimnmental poisoning by malathion, 0,Odirnethyl s(l.Zdiearbetboxysthy1) phmphorcdithioste. PeaticideBioehemistrjandPhysiology. Cope. O.B. 1965. Sport fuher). investigations. In The effect3ofpeaticides onfiah and

wiidlife. Fiah and Wildlife Service Cidar 266,US.Depanment of the Interior, Washinkon.D.C. Da\% H.C.. andH.Hidu. 1989.Effeetsofpesticides onembryonic developmentofdam - andopteraandon sUrnvalandgmalhofthe larvae.U.S.Fishe,ndWildlife Service, FisberyBulletin.6i:399. Eaton. J.G.1970. Chronic malathion toxicity to the bluegill (kpomismoFTochltlyl

Rafinesque).WaterRes.4:6?3. Eiehelberger,J.W.. andJJ.Licbtenterg, 1971.Persistenceofpeaticideainriver water.

hvimn.sd. Technol.5541. Eider,R 1988.Acutetoxiatieaofidades tomarinedapd Crust.~1- aa 16:m Eisler.R 1970.Acute toxicitiesoforganochlorineandorganophosphorus i~eetiddea to atuvine fiahes. U.S. Burerru of Sport Fisheries and Wildlife, Tech. Paper 46, Washiwn.D.C. Henderson. C.. and Q.H.Pickering. 1958.Toxicityof organicphosphorusinsecticides to

kh. Tm. Amer.FishSorS: 39. M, RE.and WJ. Collins. 1974. The susceptibility to sekcted insectidea md umtylcholiwsterase activity in a laboratory mlony of midge larvae, Chimnmnus trmonr(Dipters:chimnomidae).Bull.Envimn.Contarn.Toximl.E62 KaqM. 1961.Acute toxicityof someorganicinsecticidesto threespeciesof Sllmonids

andtotbethreespinestickleback.Trana.Amer.FishSoe.W.%. Mad.KJ..andW.A. McAllister. 1970.Inseeticidessuaeeptibilityof~omemmmon fmh familyrepRsentatives.Trans.her.Fish.Soe.99:ZJ. Mount, D.T.. andC.E.Stephan.196i.Amethodforestablishingsxeptahletoxiantlimits

for fish-dathion andthebutoxyethanolesterof44-D. TramArner.Fish Sa21: 185. Mulla.Y.S.,and A.M. Khssauinah. 1969.Laboratory andfield evaluation8ofIddea

.gainstehimnomidmidp. Jour.Ecan.Entomol.6237. Puis. D.F.. et al. 1975. Rates of depadation of malathion by Ma klafedfmm aquaticsystem.Envimn.Sci.Technol.9:la.Piekering.Q.H.. etd.1962Thetoxicity of orpanicphmphominsectickbtodifferent spiesofwmwaterfishes. Trans.Amer.Fish. SOC.91:175. pmt, G., and T.R Sehroder. IKI.The toxicity of fouriruecticidestofour dmonid

speciesBull.Envimn.Contam.Toximl.6: 144. Sanden,H.O. 1W. ToxicityofWticidestothe crustacean.CammnuWnS. BmU of SportFisher% andWildlieTech.Paper No. 25.U.S.Department of the Interior. WashingWn.D.C. Sanden. H.O. I972 Toxicity of some insecticides to four viesof mdrmsWn

cmsu~oedns.Bureau of Sport Fisherier and Wildlife Tech. Paper No. 66, US. DeportmentoftheInterior.Washiwpn,D.C. Sandera. H.O., and O.B.Cope. 1966.Toxicities of several peatieides to two Of

cladmeramTram.Amer.Fish.Soc.%:I&. Sanders,H.O.. andO.B. Gap.196% Therelativetoxicitiesof severalpeatiadesto lyiads ofrhreespeciesofstoneflier.Limnol.Oeeanog.13:112 Weiss,C.M..andJ.H.Gakntatter. 1964.The decayofanticholinesteRasVtintyoforpanic

nhaaohom insecticida on storag~ in waten of diiferent pH. Advmin Water k'oll;tion Fk%e.rch,1:83

YIGANESE
REFERENCES CITED F.irbndge.RW..ed1966.Theencyclopediaofaxanogmpby.Reinhold.NewYork. Griffin.A.E 1960.Si&icanoe ud~moval of rmnganeeeinwateraupdica.Jw. Amer.

.. WaterWorkaAsan.52:1926. Amer.WaterWorLshn. 52:W7. Illig.G.LJr. 1960. Useofdurnheurnetaphosphatein man~.neest.biliutioaJw, McKee.J.E.. andH.W. Wolf. 1963.Water qualityeriterir StateWaterQualityControl Natioml AcademyofSciences,NationalAeademyof Engineering. 1974.Watergdity Riddirk,J.M.. et d.1958. Iron and manganese in water suppliea Jour.Amer. Water

Board.Sacramento.calif.Pub.3-A. criteria,1972.US.GovernmentRintingOffice.Washinkon,D.C. WorksAsan.54:688. sollman.T.H. 1457.Amanualofpharmacology.W.B.Saunden,Philadelphia

METHOXYCHMR

REFERENCES CITED Bdmer. LE..and D.R Nimmo. 1974.Methods to ae.s&as effeets of combinations of

tohtr,salinity,udtemperatureonwtuuine minulaRoe.9thAnndConference onTraceSubmamainhvironmenulHealth,UniversityofYiamuri.Columbia Butler.PA19n.InfluenceofpetiadeaonmMneemsyatems.Roe.RoyalSoibhn, Eisele. PJ. 1974. Theeffeetsof mqbxyehloronquaticinvertohatepapuktionamd

communities.PkD.%is, UniversityofMichigan,Annhrbor. Heath.RG., etd.1972Comparativediewrytoxicities of peStieideato birds.Burerruof SpnFLberiea 4 Wildlife.WidlifeReportNo.1% US. DepvrmeatoftbeIntcrior, WashinrtonD.C. 

### in: 

### sn.

Hodge,Hk.,etd.1954.ShorttermoraltoxiatytestaofmethoxyehlorQntrd

### +.

Jour.Pbumaml.Exo.Theraav 99.la , 

### -,.-- Kern.S.. andR Earnest 1974.Acute toxicityofa, innecrjddmtadipadhrMamtilu. WombFishudGame,60:B Lehnun.AJ. 1W. Summvlesofpeaticidetodaty.&socofFoodudhvgOffdrbof theUS..Topekah. pp. 14. Ym, J.W.. ud PJ.ble.lgls.Theeffemof methoxyebloron 4uciebiota U.S. hvimnmenulRotenion Agency, Ecologid Re. Senea,So. EPA-WXun& U.S. CovemmentPrintingOffice.Wpahiunpn,D.C. , 

### -,.-- Kern.S.. andR Earnest 1974.Acute toxicityofa, innecrjddmtadipadhrMamtilu. WombFishudGame,60:B Lehnun.AJ. 1W. Summvlesofpesticidetodaty.&socofFoodudDrupOffdrbof .--- -...r-_._ rr

~ 

## - Ym, JW.. ud PJ ble.lgls Theeffemof methoxyebloron 4utlebiotaus hvvonmenul Rotenion Agency, EC0logx.i Re. Senea,So EPA-WXun& US Covemmenthung Office.Wpahnpn.DCMcM, RL. etd.1911.Biodegradable analog3ofDM.Bull.WorldHealthOmanhsmden.H.O. 1972 Toxicity oS sue iwetieidea to four sped= of daooanCan BURIU of spwl Fiahenes and Wildlife Tech. Paper No. 66, US. Stkkd, LF. 1919. Pesticide residues in bin$ and mammals. Page4 254-312 in C.A.

tiW.44m.
GovernaclrtRintingOff=. Washinkon.D.C. Ed& ed.Environmentalpollutionbypeaticides.PlenumReas.NewYork.

HIREX

REFERENCES CITED Borthwick,P.W.,etal. 1973.Accumulation and movementofmirexinselwtedesturka

ofSouthCarolina,196s-71.PmtiadedMonitJour.1:6. Bookhout. C.G.. etd.1972 Effm of mirex onthelwaldevelopmentoftwo enbs. Water,Air.and Sail Pollution, 1:Ia. Heath, RG., and J.W. Spann. 1973. Pesticidfs in the environment: A mntinuing

mntmversy.lntemontMed.BmkC~Q.,NewYark,pp.01-4s Heath.RG..et al. 1972Comparative dietarytoxicities ofpesticides tobi&. Bmu of SpnFisherie and Wildlife,WildliIe RepanKO.152,US.Departmentof Inrerior. Wahington.D.C. Hydf.K.M., etal. 1974.TheeffectofmirexonchannelcaUishpduction.Trana.Amer. Fish.Soe.1(n:366. Kaiser,K.L.E. 1974.Mirex:An unremp& conraminant offihesfrom Me Ontario. Seience185:523 Lowe.J.I..et 81. 1971.Effwtsofmirexonselectedestuarineorganisms.Pap 171-186 in Ludke. J.L.,et a]. 1971.Toxicity of mirex to crayfish. Ifomdmblandinqi Bull. Naq\i. S.M.,and A.deIhCw. 1973Mirexinmrporationintheenvlonment: Residuein Stickel. WH.,et al. 1973. Pesticides and the envimnment: Amntinuingmntmvmy. Tapau. M.E., et al. (19%). Seasonal effecfsof leached &x on selected esuurine VanValin,C.. etal.1s. Someeffectsofmirexontwowm waterfihes.Tram.Amer. Wolfe. J.L., and B.R. Nonnent I973 Ammulation of mirex midues in selected

organkmsafteranaerialtreatment.Mississippi,1971-72 PesticidesMonit.Jour.7:lrz Transactionsofthe36thh’onhAmericanWildlifeWum Conference. Environ.Conram.Toxicol.6:89. non-tar@organisms, 1972Pesticides MoNtJoui.7:104. lntermnt.Med.BookCorp..NewYork,pp.43747. animals.hrch.Envimn.Contam.Toxicol.3:371. Fish.Sa. 9i:1%.

NITRATES, NITRITES

REFERENCES CITED Gillette, U, etal. 1952Appraklofachemical we problem byfiah toxicity tests. Humemn.RH.. etd. 1971.The nitratemtuation inIllinoiaJour.Amer.Water Works

SewageIndWastes.24:IS. bn. b3:m. Klinger,K 1957.Sodium nitrite.aslowactingfihpoison.Schweu2Bydml.19(2):565. Kwpp. G.L,and G.F.Arb. 1973. Ammonia toxicity levels .adnitrate tolennceof

channeles~~hTheProgRsJiveFLahCulturist,35:221. U&y, EF.1972RoleofbacteriainthenitrogencycleinInkes.WaterPollutionConml

Reaeuch Series,(EP210:16010 EHR WE), US.hvimnmenulPmWon Agency, US. GovernmentRintingOffice, Washington.D.C. National Ademyof Sciences. 1972Aocumulation of nitrate. National Academy of

Sdenw,Wlshington.D.C. Narionsl Ademyof Sciences.NationalAcademyof Engiarering.W97CWaterquality

criteria,1972US GovernmentRintingOffioe,Wrshingmn,D.C. PublicHdthSernce.1961.Groundwatermnumination:prmedingaof 1961symposium Tph.Rpt W61-5, RA Taft Sanitary Engineering Center,U.S.Public Health Senice,DepartmentofHealth,EducationandWelfare,Cincinnati.Ohio,Ruso,RC..et d.1974.Acutetoxicityofnitritetorainbowhut (Sdmopidmi). Jour. Fish.Res.Bd.Can. 31:1663. Rueo,RC.;and RV.Thurston. 1975.Acutetoxicityofnitritetocutthroattmut (Sdmo

elark'). FkherkaBicamyLsboretoryTech.RepnNo. 754. YontmsStateUwvvaitr. W.A. 1965. Studiaon fshculturein filtereddoeed-drculating quaria 11.Onthe

arp cultureexprimenuinthesyayatems.Bull.Jap.Scc.sd.hab. 31:916. httelmarher,P.G. 1962Methemoglobinemiafmmnitrate.indrinkingntu. SehrReihe. Ver.W.aser-.Boden-u. Lufthyg.Ko.21.*her, Stuttgan Smith,C.E. andW.G. Williams. 1974.Erpenmntalnitritetoxicityin rainbowhut and chinmkdmon.Trans.Amer.Fish.See.laS:389. Stewut.B.A.etal. 1967.Nitrate andotherpollutantsunderfieldsandfeedlots.Envir

Sn. Tech.I:%. .~~~~

~ .~ Trarm.F.B. 19%.The .cutetoxicityofmmmmmonsaltsof mdium.pomsium.and

ddum10 themmmnbluegill (LrpnlamarrochinuRailwsque).RaAd Nat Sci.. Philsdelphie106:185. Vipil,J.. etd. 1965.Nitrates in municipal watersupplies musemetbemoglobinemiain

infanta.PublicHealthRept80:1119. Wdlen.I.E.etd.1957.Toxicity to Gambuaioaffinisofcertainpurechemiakinturbid

watem.SeamInd.Wmm.29:695 Wdton. G. 161. Survey of literature relating to infant methemogiobinemi. due to WVestin. D.T. 1974.Nitrate and nitritetoxicitytosalmonid fuhes.ThewveFishnitraw-cvntaminated water.Amer.Jou.PublicHealth.41:M. C"lt"rist.%!@& WoUf.LA,andWakrman. 1972Nitrates,nitrite.,and niuoaamine.Science,177:15.

OIL AND GREASE
REFERENCES CITED Bellan.et.I. 1972Thesublethaleffeetaofadetergentonthereprodudion. development,

andsettlement in tbepolyeh.etousannelidGpitclbmpilda.YyimBWlo([y. 14:uE3. Blumer, M. 1970. Oil matahnation and the living reanvces of the .e~ Fmd ud Ag~iculture OrgsnizdtjonTechCod. Rome.FIR:MPrlO/Rl,llP. Bugbee, S.L.adC. Y.Walter. 1819.The ~spow ofmaaminvertebratea topenline pollution in a mountain stream. Page 7% in Reventionunl mntml of oil spilla, proeeedingaofsymposiumMarchlb17.W.ahiMton,D.C.

.. - Diaz-Pilerrer. 1962 The effectsof an oil spill on the ahore ofCuania, Puerb Rim Hampaon.G.R,. andH.LSanden.1989.Localoilspill.Oceanus.15:8. Imbmn.S.M..andD.B.Boylan. 19TJ.Mfectofseawatermlublefractionofkemeeneon

chernotaxisinamarine snail,Naamriusddclua.Nature,241:213. JohnsHookinsUniveniQ. 1956.Finalreporttothe waterqualitysubmmmitteeof .the

(ahtract).Ass.Isl.Mar.Late,4thMtg.Cum, 12-13.

Am&& PetmleumI&titute,Project~49.41. MeKee and Wolf. 19'3. Water quality m'teriaSlateWaterResourceControl Board.

Saeramento.Calif. Pub.No.%-A. Yimnov,O.C. 1961.Mfeetsof lowmnaentrations ofptroleum and itspmducts on the

developmentof meoftheBlackSeaflatfish.VopIkhtiol.7:557. Yimnov. 0.G. 1970.Theeffmofoilpollutionon floraandfaunaof theBlackSeaIn

Rmedirq:FA0mnferenoeon marine pollutionanditseffectsonlivingresouroes and fish. Rome. December 1970,692Food and Agriculture Organization of the UnitedNatiom. Moore. S.F..etd. 1973A pmliminwyassessmentoftheenvironmental vulnerabilityof

Machi= Bay.Mainetooilsuperlankem.ReportNo.MITSG 734. Nelsan-Smith. A. 1971.Effectsof oil.onmarine0lmt8andanid. Paae~min P. Hepple.ed.Waterpollutlonby oil.London. . . Nelmn

-Smith,A.1973Oilpollutionand marineemlogyPlenumPreSB.NewYo&.PARATHION REFERENCES CITED Bill&, R.anddeKinkelin.1970.SterilizationoftheMticlesofguppiesby me8116ofnon-

lethaldoeeaofparathion.AnnalesDHydrobiologie,1(1):91., Burke. W.D., and D. E Ferguson. 1989.Toxicities of fourimticidesto&stant and

susoeptiblemosquitofuhinstaticandflowingmlutions.MquitoNews.291):96. Carter,F.L1971.Inmwstudiesofbrainaoetylcholine~terme inhibitionbyorganophmp bateand earbarnateiaseeticidesinfish.Ph.D.&nation, &MUM StateUniversity. BatonRouge. Coppage,D.L1972Orghnophcephatepeaticid-: spedficlevelofbrainAChEinhibition

relatedtodeathin~heepshead minnows.TRM. Amer.Fish.h.'l01:594. ~oppage, D.L.and 1. W. Duke.1971.Effectaofpesticidesinestuariesalongthegulfand mutheas Atlantic mta.In C.H. Sehmidt,ed.Roeeglinga of the2nd GullCaa Conferemon Mcaquito Suppression and Wildlife Management National Mmquitn Conuol-Pish andWildlifeManagementCmdinatingCommittee.R'sahingvn, D.C. Coppape. D.L.andE. Matthews. 1974.Shorttermeffeadoforganophaephatepesticides oncholinestenues ofestuarinefuhesandpinkshrimp.Bull.Environ.ContamToximl. 11:w. Coppage.D.L,etal. 1975.Brain scetylcholinestenueinhibitioninfuh a8adi.gnoaieof

environmental poisoningby malathion, 0.O-dimethyl S(1,ldicarbethoxysthyI)phob phorodithioate.Pesticidebiochemisuyandphpiology. Dowden,B.F. 19%. Effecta offiveinsecticidesontheoxygenmmumptionofthebluegill

sunfish. LqmnWmnnahinu.Ph.D. Thais.LouisianaStateUniversity.Baton

## m. Eaton, J. G.1970.Chronic malathion toxicity to the bluegill, (Lcpmnamannhirw

Winesque).WaterReseueh.4:673. Eichelberger. J.W., andJ.J.Lichtenberg.1971.Penistenoeofpesticidedinriver water.

Environ.Sci.andTechnol.5541. EnrimnmentalhtectionAgency,OfficeofPesticidesProgram. 1975.Initialsientific andminiemnomic reviewof parathion.Repon.No.EF'A-540/1-75ml. US.Environ- mental htgtionAgency.NatiodTechnical Information service,Springfield, Va Gaufin. A. R. et al. 1465. Toxicity of 10 organic insectjades to various aquatic

inuertebnrter.WaterandSew.Works,112276. Gibmn. J.R.et al. 1969.Sourcesof ermrintheuse offish

-brain aoetylcho1ioeste-k

activityasamonitorforpollution.Bull.Envimn.Contam.Toximl.437. Jeaaen,LD.,andA. RGaufin.1964.Lanptermeffectsof organicidcides on two speciesofstoneflynaiads.Trans. Amer.Fish.Soe.93:357. Korn.S.. and R. Earneat 1974.Acutetoxicityof20 insecticides tostripedbass.Mm

&ilk. CalifominFishandGame,60:128. Lahay, M..and S.Sarig. 1989.Sensitivityof pond fuh tomtnion(azinphwmethyl)and

parathion.Bamidgeh. Bull.Fbh.CultIsrael.267. Leland. H.V.!I. 1968.Bimhemidfactonaffectingtoxicity ofparathion and selected

lrnaloptofuhes.UnivemityofMichigan,AnnArbor. Lowe. J. I., etal. 1970.Laboratory bioausys. InFhgrssreportforf4 yy 1969. Pesticide Field Station, Gulf Breeze, FlaU.S. Fish andWildlife ServiceCue 

### F. Ludke. J. L 1970.Mechanism of resistance to parathion in mmquitofuh. GambvM

afini8. Ph.D.Thesis,MississippiStateUnivenity.Univemity. Mount,D. 1.. andH.W. Boyle. 1969.Parathion

## -y9eofblmdmnoentmtiontodiagnose mortalityoffmh.Environ.Sci.andTechnol.3:1163. Mulla,M.S..andA M.Khasa&nah. 1969.Lsborntoryandfieldevaluationoflarvicides

againatChimnomicmid-. Jour.Emn.Entomol.62:s Murphy. S. D..et al. 1963Comparativeanticholineaterase actionof organophosphorus

inseeticidesininvertebra-. Toximl. Appl.Phannaeol.12:P Pcst. G.. andRALeasure.1974.SublethaleffectofmalathiontothRedmonidsped-.

Bull.EnvimnCordam.Toximl.12:312 Sanden. H. 0. 1972 Toxicity of some insecticides to four species of malamstracan

mwtaeeans. Bureau of Sport fisheriea and Wildlife, Tech.Paper No. 66. U. S. DepanmentoftheInterior,Wsahingvn.D.C. Wen.H.0..and 0. B. Cop.19%. Toxicities ofseveralpesticidestotwospeciesof CIadooenuls.TRlu. her. Fish.Sa95:165. Spacie,A. 1975. Acute and chronic parathion toxicity tofuh and invertebrates. U. S.

EnvironmentalPmteetionAgencyEmlogicalReeearehSeries. Web,C.M.195%.The determinationofcholinestersseinthebraintissueofthreea+es

offreshwaterfhhandiuinaeti~.atiDninvivo.Eeology,39: 194. We&, C. M. 1959. hponse of fish !A sublethal expmures of organic phoaphom

insefticides.Sew.andInd.Was@, 91:580. Web.C. M. 1961.Physiological effect of organic phmphorus ilueeticide on severd

speciesoffuh.Trans.Amer.Fish.Soe.90:143. We*, C. M.,and J. H.Gakstatter. 1964. The decsy of anticholinestersse activity of

organic phcephom insecticides on storage in waten of different pH. Adan- in WaterPoll.Res.I:@. 

# 0

# .

REFERENCES CITED Bell,H.L 1971.EffectoflowpHonthesurvivalandemergemofequaticinsetu.Water

ILea.5:313

~~~~ ~ ~ Butterfield.C.T. 1M.Bacterial propettiesoffreeandmmbinedavailablechlorine.Jw.

Am. WaterWorksAssn.40; 1%. Gpuro.LRA.1970. Oeeawgrnphy for practicingengineers.BarnesmdNoble,Inr,

NewYork. DeUino.JJ..andG.F.Lee. 1971.Variation ofmanganese. diamlvedoxygenandrelaled

chemical parametersin thebottom waters of Me Yendota,WM.Waterb. 5 lXY/. Ewpem Inland Fiaheriea Advimry Cornmisaion. 1969. Water qdity aiteria for

European freshwater fish-extreme pH values and inland fuheries.,Repredby EIFAC Working Pnrty on Water QdityCriteria forEumpean hbwbkrhh. WaterReseuch.3:593. Joned.J.RE.1964.Fishandriverpollution.Butterworth,London. Lngelier. W.F. 1936.The rJlalyticalmnmlof antiamionwatertRltmentJ&.

WaterWorkaAsan.28: 1500. MnuncD.I. 1m.~hmnic effectof low PH on fa- minnow mm+v.l, rodand 

### ~..

~ .~

~ reproduction.WaterRea.7:W uiterin.1972US. GovernmentPrintingOffice.Washin@n. D.C. Enviro.EngineeringDiv.,ASCE100:NoEELRorPapers1W43.539. National Aodemyof Soenaes,National Academy ofEngineering, 1974.Waterqdity Reid,L.C., andD.A.Cprlson.1‘374. Chlorinedisinfectionoflowtemperaturewatem.Jour. Sawyz,C.N. 1960.Chemistry for saniuus.engineers.MeGraw-Hill BookCo..NewYork. Stumm.W., andJJ.Morgan.1970.Aquaticchemiaty.JohnWIleyand Sons,I=. New Zirino. A.,and S.Yamamoto. 1572ApHdependentmodelforthechemicalsppi.6~0 of .. York. mpper,nnc.cadmiumandleadinseawater.Limn.andoeploog.11:661.

PHOSPHO

### RUS

REFERENCES CITED Fletcher.G.L.mdRJ.Hoyle. 1972Acutetoxicityofyellowphmphom14Allanticad

(Wudmdua)and Atlantic salmon (Sdmo sdar)smolts.Jour. Fish. Rea Bd.of -29:l.aS. Hutchinmn,G.E1957.Atreatiseonlimnology.JohnWileyandSons,New York. Idler. D.R 1963. Coexistence of a fuhery and a major industy in Plaoentia Bay.

Chembtryin Camda,21(11):16. Imm B.G. IW.Toxicityofelementpryphosphorus. Jour. WaterPoll.ConvolFed. 32:

1312 Jurgaard,P.Y. 1970.Ihemleplayed by theFiaheriea ResearchBoard of Canadainthe “d haringpbosphwuspollutioncrioiainPkcentiaBay.Newfoundland.CircularNo. 1.FLheriesReseuchBard,AtlanticRegionalMfioe,Hrli!u. NovaSmtk Yrkenthun, K.M. 197S. Toaud a derner quaticenvironment. US.Environmental

RoteaionAgency,W.shington. D.C. Pe, D.L 1972Obervationsonmorulitiesoftenthicwgraismsiltercuntaminationof tbebottomof&n!g Hybour,AaoentiaBay,Newfoundl.od withekmental phpb Rpea 181-186 in Eff- .ofelemental phosphorus on mvine life. Fishries r!efsmb Boardofcsnadqcihr 2 Volknweider.RA1973.InputoutputnudelaScbwaebZHydml.SOLIDS (DISSOLVED) AND SALINITY

REFERENCES CITED ApicultureHandbook h'o. 60.19%. Diagnosis andimprovementofsalineandalkalisoils.

L.A.Richards,ed.U.S.Government RintingOffice,Washingl0n.D.C. Bruvold,W.H.,etal.1969.Consumer-meritofmineraltanteindomesticwater.Jour.

Amer.WaterWorkshn.61:515. Capurm. LRA. 1970. Oceanopaphy for'practicing engineem. BarnesandNoble Inc.,

h'eaYork. Griffith,W.H.,Jr. 1963.Saltas apossible limitingfactortothe SuisunManhphearant

population.AnnualreponDeltaRshandWildlifeProtectionStudy,CooperativeStudy ofCalifornia. hhman,J.A. 1964 Control of mmaion in water systems. Jour.Amer.WaterWorks

hn. 56: 1009. Lodihart,EE,etal. 1955.Theeffectofwaterimpuritiesontheflavorofbrewedmffee.

FmdResearch,20:5%. Moore,EW. 1952 Physiological effeetsof the mnsumption of salinedrinkingwater.

National Res. Counal, Div.of MedidSeienw,Bull.San.Engr.,and Environment. AppendixE. National Academy of Sciences,National Academyof Gngineering. 1974.Waterquality

criteria, 1972.US. GovernmentPrintingOffice,Washington,D.C. National Research Council. 1954.Sodium resvicteddiets. Publication 925,Food and

NutritionBoard,Washington,D.C. National Technid Advisory Committee to the SecretaryoftheInterior. 1968.Water

qualitycriteria.US. GovernmentRintingOffice, Washian,D.C. Patterson,W.L.,andRF.Banker. 1963.Effectaofhigblymineralizedwateronhousebold

plumbingandappliances.Jour.Am-. WaterWorkahn. 60:1060. Public Health Service. 1962Drinkingwateratandarda, 1962US. GovernmentPrinting Office,Waahian,D.C. Ra-n. D.S.. andJ.E.Moore.lSi.4.ThedinelakesofSaskatchewan.crnadian Jour.of Res.22:141. Ricter. C.O., andA.MaeLean.1939.Salttantethresholdofhumans.Am.J.Phyiol.126:l. Rouwfell,G.A.,andW.H. Everhart 1953.Fisheryseience,itsmetbodsandapplications. '.

JohnWile?.andSons.he.,NewYork. Sawyer.C.N. 1960.Chembtrjfor3aniUryepgineem.Mffiraw-Hill BookCo., NewYork. Standardmethodsforthe examinationofwaierandwastewater, 18thed.. 1971.Editedby

MichaelC. Rand.et a].American PublicHealthhn.,AmericanWaterWorksAsan., WaterPollutionControlFederation, Washington,D.C.

SOLIDS (SUSPENDED, SETTLEABLE) AND TURBIDITY
REFERENCES CITED Edberg.N. andHofsten,B.V. 1973.Oxygenuptakeofbottom sedimentstudied in-situ

andintheInboratory. WaterResemth, I: 1285. European.Inland fisheries Advisary Commiasion. 1965. Water quality criteria for

Europeanfreshwaterfiih,reportonfinelydividedsolidsandinlandfisheries.InLJour. AirWaterPoll.9:151. Gammon.J.R 1970.The effectofinorganicsedimentonstmambiota WaterPoll.Cont.

Rea. Serieb,18060DWC WO. U.S.Environmental ProteetionAgency.US.GovernmentRintingOffice.Washington,D.C. Mackenthun. K.M.1973. Toward a cleaner aquatic envimnment US. Government

RintingOffice,Washington.D.C. National Academyof Sciences,National Academy of Engineering. 1974.Waterquality

criteria,1972US. GovernmentPrintingOffice, Washington,D.C. Standardmethalafortheeraminationofwater andwastewater, 1971.13th ed.Editedby MictwlC.Rand,etal.American PublicHealthhn.,AmericanWaterWorkshn., WaterPollution ControlFederation. Tmell.C.M.,and A.R Gnufin. 1959. Some importanthiologieal effecta of pollution

often disregardedin StRamsurvey.Roceedingsofthe0thRYdueindustrialwaste mnferrnce. Reprinted in Biology of water pollution, 1367. US.Depanmenr of Interior,Washingl0n.D.C. Tebo,L.B., Jr. 1955.Effectsofsiltation, resultingfromimproper logging,onthebottom

fauna of a smll trout stream in the southern Appalachians. TheRogRaaive fish Culturist. 11: €4.SULFIDE 

# - HYDROGEN SULFIDE

REFERENCES CITED Adelman.1.R.andL.L.Smith.1970.Effectofhy-3 sulfideonnwthernpikeeggaand Rmn.C.W.. andBJ.Follis. 1967.Effectsof hydmrensulfideonchanneleaffuh Tram.

aaefry.Trans.Amer.Fish.Soe99:501.

, Amer Fiih.Scc9631

dmonandmutWash.Ikpt.Fish.Res.Bull.No.5. Jom. 3.R 1364.Fishandriverpollution.Butteworth,London. National Wemy of Sciences.National Academy ofEngineering.1974.WaterqUditY criteria1972U.S. GovernmentPrintingOffioe.WashingWn.D.C. bid.D.M., andL.L Smith,1974aChronictoxicityofhydrogen sulideto Gammnur

pruddimnneus.Trans. Amer. Fish.Soe.Im. hid.D.M.. and L.L Smith. 1974b.LongtermeffectsofhydmgensulfideonHc2ogen~

limbat0(Ephemeroptera).EnvironmentalEcology. hid,D.M., and LL. Smith. 1974~. Facton influencing acute coxicity estimates of hydrogensulfidetofreshwater invertebrates WaterResearch8. Smith, LL 1971. Influence of hydrogen sulfideon fishandarthmpods.Rojd18050

PCG, U.S. EnvironmentalRowtionAgency.WaahingWn,D.C. Smith,L.L..andD.M.hid,1972Effectsofhydrogen sulfideonfisheggsandfry.Water

Reeesrch,G:711. Smith,LL,Jr., andD.M. &id. 1974.Effwt ofhy-n sulfideondevelopment and sunrivalof eightfreshwaterfishspeck.Pagw415-470inJ.H.S. Blaner,ed.Tbeearly life historyoffish.Sprinpr-Verlag.New York. Theede. H., et 81. 1969. Studies on the resistance of marine bottom invertebrates to

oxygendeficiencies andhydrogensulfrde.Mar.Biol.2:325. Van Horn,W.M. 1958.The effect ofpulp andpaper mill wasteson aquaticlikRoe.

OntarioIndust.WmteCod.5 60.

TAINTING SUBSTANCES
REFERENCES CITED Boyie. H.W. 1967.TaJte/dor mntamination offishfromtheOhioRiver.FederalWater

PollutionConmlAdministration, Cincinnati.Ohio. National Academy of Sciences,National Academy ofEngineering. 1974.Water quality

criteria,1972.U.S.GovernmentPrintingOffice.Washington,D.C. Shumwsy,D.L.. and J.R.Palensky. 1973. Impairment of the flavor of fish by water

pollutants.U.S.EnvironmentalPmLectionAgency,EPA-R.3-7M10, US. Government RintingOffice,Waahingwn,D.C. Thomas.N.A. 1973Aasesament of fish fleshtintingsubstances.InJ.Cairnsand K.L.

Dicksan,eds.Biologicalmethodsfortheassessmentofwaterquality.Amer.Soeietyfor Testing andMaterials.Tech.Publ.528.PhiladelphiaTEMPERATURE

REFERENCES CITED Ballentine.RK.,andF.W. Kitmll.1%. Obeervationsoffed mlifominseveral mnt streampollution studies.RoeeedingJof theSymposiumonFecalColiformBacterhin WaterandWatewater,May 21-2,196s. Bureau ofSanituyEqmeering,California StateDepartmentofPublicHealth. BlncL,E.C. 1953.Upper lethal temperatmofMmeBritishColumbiafrsahwaterfiihe.

Jour.Fish.ResBd.Can.10196. BretLJ.RWI. Tempering venuacclimationin theplantingofspgWedbvutTrura. Amer.Fish.Sx.70:391. BretL J.R 1%. Someprinciples inthethermal requirementsofrubes.My Rev. Biol.31:75. BrettJ.R 1W.Thermal requirementsoffwh-threo dsdesofstudy,194&1970. In

C.M. Tarzwell,ed.Biol*cal pmblemin waterpollution. PublicHdthSenriee.U.S. DeptofHealth.EducationandWelfare. Burnson. B. 19S.Seamnal temperarmvariations in relationtoantermtment.Jw.

her. WaterWarlo&an. 30:793. Cairns.J..Jr. 1456.Eifectsof in& temperatureson qutkorgankm Id4

Warn.1:50. CalabRse. A 1968. Individual and mmbined effe of lulinityd temperature on edryoeand lmae of the motclam,MulinkMia (Spy).Biol. Bull. lS7,S:417. Camp,T.R 1963.Water andiwimpurities.ReinholdPublishing%., NewY& Chin, E. 1961. A trawl study of an estuarine nwsery wea in Gdveaton Bay ritb

panicular referenoe lapenaeid rhrimp.Ph.D.Dissenation,UnivvsityofWuhin%on Gmtloa,J.D.. Jr.. dC.G. BmWlout 1971.Theeffectofeydietemplrturaon hd

development in the mud aab, JZhitAmpowp~d haorririi. InD.I. Crisp, ed.Fd EuropeanmarinebiolcgysympiumCambridgeUnivemityRsahdon Coutant. C.C. IW.Thermalpollution

-biologicaleffects:AreviewoftheLiterature of

1967.Jour.WaterPoll.ContFed.40:1M7. Coutant,C.C. 1968.Thermalpollution

-biologicaleffest.5: Areviewoftheliteratureof

1968.Jour. WaterPoll. ContFed.41: 1836. hunt, C.C. 1970,Thermalpllution-biological effects:Areview oftheLiterature of 1989.Jour.WaterPoU.ContFed.4:1025. Couunt,C.C. 1971.Thermalpollution

-biologicaleffects: Areviewoftheliteratureof

1970.Jour.WaterPoU. ContFed.43: 1292 Coumt, C.C. 1972Biological~peets ofthermalpollution, 11.SdentifK hsisforrate temperature at~nduds nt power phnnta. CRCCritical Rev. in hviron Cant 8: L Coutant. C.C. 1975. Temperature selection hy &h-a fmr in pow- plant impact smeaumenfllInSymposium onthephysical dbiologicaleffe ontheenvironment of mlingsrstema d thermal discharp at nuclear pwerationsIntemstjorul AtomichergyAgency. Coumt,C.C.. mdC.P. coodyear. 1972Waterpollution-tkd pdlution:Areviewof

theliteratureof1971Jw. WaterPoll.ContFed.44:1250. CoutlnLC.C., and H.A Pfuderer. 1978.Tbermaleffe-litenture r&ew iawJour.

WaterPoll.ContFed.45:EX. Couunt,C.C.. d HAPfuderer. 1974. Tbernuleffe-titmature reviewiawJour.

WaterPoll.ContFed16:1476. Crisp,DJ.1957.Wfeaoflow temperatureonthekdmg of myiDednvkNature, 179:1x78. De Sylvr, D.P. 1983. l'hretkl mnsidemtionsof tbe effdof heated effluentson

mvine f'sbes InPA KreJel d F.C.Mu, eds.BioloBiaJ .spguof thermal pollutionV.aderbiltUuivemityFreat,NMhville.Tern dtvluuiug,V.L 1971.Tbeeffecboffooddeprivationdvlinityehngesonrepduetive fm&m in the rstuuine pbiidfmh, C;Uiehuy#m'mbilia.Biol.Bull 141: 4.58. devluning, V.L l977. The effeof temperature ud pbotoperiod on reproductive

cycling of tbe mtuuine pbiid fMh, Gilliehuyanirrdilu.fLhryBull. 70,4: 1151. Dow. RL W73. Fluctutiouainmvineapgies.buwhceduringclinuticcyckMu,

TehSx. Jour.7k 5%. Environmental Resevch Lboramy. 1976. prmdwra for developing tempeatwe

miteria for frahwp.ter f& Emlogid Reaeychseries.repfiin-tion ERL' Duluth.Mjm PLdenl Wrtpr Pollution Contml Administnrion l967.Tempentureudquticlife.

L.bontmy laveatigatiorm No. 6. Technical Ad.risory lad Invmtigatiom Branch, Cidti. Ohio. Fry,F.EJ.1967.RmpomzofvertebratepoiLilotbennstotewerstureInAH. Rose.ed. --h=xa eiwr Vorbehandlungnitkoast.nten urd wghaelnden tempentauenutidiehiWemistenrvon GommonusdiwuodI&ta kJuim

## &. Biol.15:12 Clude,J.B. ISM The effdof temperatured psd.toraon the .bundanceofthe

mfubelldrm,dlyoamk,inNewFh&d. TMbAmer. FishSoc& 19. I

' Rcm,NewYokGlynn.P.W. 1963.b moditiesofeehiwidsandocberrpefllrtog.nismsmi~nt 6thmidday.lowwatererposursainPuertoRieo.Mar.Biol.3 226. Gouda.J.G. 1~iZ hM[ vanitionintbereapowof&ne popuhtioytokted warnin tbe vidnity of m gewratangphntPh.D. DLssenrtaon,Umversty of RbodekLnd. Hd. SA etJ.1967.ContmltechniquesformrgulrtiobfdbationJwr.Amer.WaterIT I .I'

I E! ! !

, ... --- ... ~ 

## .., J~VOL .,I..

7.,

## I I

!UNITED STATES ENVIRONMENTAL PROTECTION AGENCY OFFICE OF WATER REGULATIONS AND STANDARDS CRITERIA AND STANDARDS DIVISION

UPDATE t2 to

"QUALITY CRITERIA FOR WATER 1986"

May 1, 1987

This is the second update to the EPA document "Quality Criteria for Water 1986" . Included in this package are criteria summaries for contaminants that were recently revised as well as a criteria summary for a new contaminant. Several hand corrections are also included. 

# @ Revised New Hand corrections INDEX CHLORPYRIFOS AMMONIA SUMMARY CHART CYANJDE NICKEL CHLORINATED ETHANES P

ARATHION PENTACHLOROPHENOL TOXAPHENE ZINC

Directions: a. Replace sections that have been revised with b. Insert new section alphabetically. c. Make the identified hand corrections. new sections.

For additional information contact: EPA's Criteria and Standards Division at (202) 475

-7315.

# I

HAND CORRECTIONS

..

.. .. oaia 

## - page 5, center page, third line of equation should be changed from

.'

. "FPH 

### = 1 : 8 < pH < 9" to

. ., ; 8 5 pH < 9" "FPH = 1 - '

# '.

..



## .................................................................

.. Cyanide 

## - last page, include the following after the last line

.. .. "(45 F-R- 79318,NOV. 28, 1980) (50 F.R. 30784, July 29. 1985)" ."SEEAPPENDIX A FOR METHODOLOGY"

.,
.. ...,.

-.

':.'Chlorinated Ethanes 

## - last page, change

.. 1 "1.03 ug/l" to

"1.03 g/L"

## ,INDEX INTRODUCTION SUMMARY CHART NTIS No. PB 81-117269 PB 81-117277 PB 81-117285 PB-263943 PB-263943 PB 81-117301 PB 85-227114 PB 81-117319 PB 85-227445 PB 81-117335 PB-263943 PB 81-117293 PB 81-117343 PB 81-117350 PB-263943 PB 85-227031 

### PB 81-117376 PB 81-1’17384 PB 81-117392 PB 81-117400 PB 81-117426 PB 85-227429 PB 81-117434 PB 81-117418 PB 81-117442 PB-263943 PB 87-105359 PB 85-227478 PB 81-117459 PB-263943 PB 85-227023 PB 85-227460 PB 81-117491 PB-263943 PB 81-117509 PB 81-117517 PB 81-117525 PB 81-117533 PB 86-158-045 €i PB-263943 Acenaphthene Acrolein Acrylonitrile Aesthetics Alkalinity AldrinDieldrin Ammonia Antimony Arsenic Asbestos Bacteria Barium Benzene Benzidine Beryllium Boron Cadmium Carbon Tetrachloride Chlordane Chlorinated Benzenes Chlorinated Ethanes Chlorinated Naphthalenes Chlorine Chlorinated Phenols Chloroalkyl Ethers Chloroform Chlorophenoxy Herbicides Chlorpyrifos Chromium 2-Chlorophenol Color Copper Cyanide DDT and Metabolites Demeton Dichlorobenzenes Dichlorobenzidine Dichloroethylenes 2.4. 

## - DichloroDhenol Dichloropropanes/Dichloropropenes 2.4. 

## - Dimethylphenol Dinitrotoluene Diphenylhydrazine Endosulfan Endrin Ethylbenzene Fluoranthene Gasses, Total Dissolved PB 81-117541 PB 81-117558 PB 81-117566 PB 81-117731 PB 81-117574 PB 81-117582 PB 81-117590 PB-263943 PB 8i-ii76oaGuthion Haloethers Halomethanes Hardness Heptachlor Hexachlorobutadiene Hexachlorocyclohexane Hexachlorocyclopentadiene Iron Isophorone Lead Malathion Manganese Mercury Methoxychlor Mirex Naphthalene Nickel Nitrates. Nitrites Nitrobenzene Nitrophenols Nitrosamines Oil and Grease Oxygen, Dissolved Parathion Pentachlorophenol Ph Phenol Phosphorus Phthalate Esters Polychlorinated Biphenyls Polynuclear Aromatic Hydrocarbons Selenium Silver Solids (Dissolved) h Salinity Solids (Suspended) h Turbidity Sulfides, Hydrogen Sulfide Tainting Substances Temperature 2.3.7.8-Tetrachlorodibenzo-p-dioxin Tetrachloroethylene Thallium Toluene Toxaphene Trichlorocthylene Vinyl Chloride Zinc PB-263943 

### PB 81-117616 

### PB 81-117624 PB-263943 

### PB 81-117632 

### PB 81-117640 

### PB 81-117657 PB 81-117665 PB-263943 PB 81-117673 PB 85-227437 PB-263943 PB-263943 

### PB 85-227452 PB-263943 PB-263943 PB 81-117707 PB 87-105359 PB-263943 PB 81-117723 PB 81-117749 

### PB 81-117756 PB-263943 PB 86-208253 PB 87-105383 PB 87-105391 PB-263943 

### PB 81-117772 PB-263943 

### PB 81-117780 PB 81-117798 PB 81-117806 

### PB 81-117814 PB 81-117822 PB-263943 1 PB-263943 PB-263943 PB-263943 PB-263943 EPA # 440/5-84-007 PB 81-117830 PB 81-117848 PB 81-117855 PB 87-105375 PB 81-117871 PB 81-117889 PB 87-153581 APPENDIX A Methodology for Developing Criteria APPENDIX B Methodology for Developing Criteria APPENDIX C Methodology €or Developing Criteria BIBLIOGRAPHY 

# aCHLORPYRIFOS

Summary The acute values for eighteen freshwater species in fifteen genera range from 0.11 ug/L for an amphipod to greater than 806 ug/L for two fishes and a snail. The bluegill is the most acutely sensitive fish species with an acute value of 10 ug/L, but seven intervetebrate genera are more sensitive. Smaller organisms seem to be more acutely sensitive than larger ones. Chronic toxicity data are available for one freshwater species, the fathead minnow. Unacceptable effects occurred in second generation larvae at 0.12 ug/L, which was the lowest concentration tested. The resulting acute

-chronic ratio was greater than 1,417. Little information is available on the toxicity of chlorpyrifos to freshwater plants, although algal blooms frequently follow field applications of chlorpyrifos. The only available bioconcentration test on chlorpyrifos with a freshwater species was with the fathead minnow and resulted in a bioconcentration factor of 1,673. The acute toxicity of chlorpyrifos has been determined for 15 species of saltwater animals in 12 genera with the acute values ranging from 0.01 ug/L for the Korean shrimp, Palaemon macrodactvlus, to 1.911 ug/L for larvae of the eastern oyster, Crassostrea virginica. Arthropods are particularly sensitive 

### to chlorpyrifos. Among the 10 species of fish tested, the 96

-hr LC50s range from 0.58 ug/L for striped bass to 520 ug/L for gulftoadfish. Fish larvae are more sensitive than other life stages. Growth of the mysid, Mysidolssis bahia, was reduced at 0.004 ug/L in a life

-cycle test. In early life

-stage tests, the California grunion, Leuresthes tenuis, was the most sensitive of the six 

# a.

fishes, with growth being reduced at 0.30 ug/L. Of the seven acute

-chronic ratios that have been determined with saltwater species, the five lowest range from 

### 1.374 to 

### 12.50,whereas the highest is 228.5. Concentrations of chlorpyrifos affecting six species 

### of saltwater phytoplankton range from 138 to 10,000 ug/L. BCFs ranged from 100 to 5,100when the gulf toadfish was exposed to .oncentrations increasing from 1.4 to 150 ug/L. Steady

-state BCFs averaged from 100 to 757 for five fishes exposed in early life

-stage tests.
National Criteria The procedures described in the "Guidelines for Deriving Numerical National Water Quality Criteria for the Protection of Aquatic Organisms and Their Uses" indicate, that except possibly where a locally important species is very sensitive, freshwater aquatic organisms and their uses should not be affected unacceptably if the four

-day average concentration of chlorpyrifos does not exceed 0.041 ug/L more than once every three years on the average and if the one-hour average concentration does not exceed 0.083 ug/L more than once every three years on the average. The procedures described in the "Guidelines for Deriving Numerical National Water Quality Criteria for the Protection ofAquatic Organisms and Their Uses" indicate, that except possibly 

# a where a locally important species is very sensitive, saltwater aquatic organisms and their uses should not be affected unacceptably if the four

-day average concentration of chlorpyrifos does not exceed 0.0056ug/L more than once every three years on the average and if the one-hour average concentration does not exceed 0.011 ug/L more than once every three years on the average. Three yeaks is the Agency's best scientific judgment of the average amount of time aquatic ecosystems should be provided. between excursions. The resiliences of ecosystems and their abilities to recover differ greatly, however, and site

-specific allowed excursion frequencies may be established if adequate justification is provided. 

# a Use of criteria for developing water quality

-based permit limits and for designing waste treatment facilities requires selection of an appropriate wasteload allocation model. Dynamic models are preferred for the application of these criteria. Limited data or other consideretions might make their use impractical, in which case one must rely on a steady

-state model. (51 F.R. 43665, December 3, 1986) SEE APPENDIX A FOR METHODOLOGY

# a Summary Acute values with twency-one freshwater species in 18 genera range from 1,101 ug/L for a cladoceran to 43,240ug/L for a fish. Fishes and invertebrates are both spread throughout the range of sensitivity. Acute values with four species are significantly correlated with hardness. Data are available concerning the chronic toxicity of nickel to two invertebrates and two fishes in freshwater. Data available for two species indicate that chronic toxicity decreases as hardness increases. The measured chronic values ranged from 14.77 ug/L with DaDhnia maqna in soft water to 526.7 ug/L with the fathead minnow in hard water. Five acutechronic ratios are available for two species in soft and hard water and range from 14 to 122. Nickel appears to be quite toxic to freshwater algae, with 

# a
concentrations as low as 50 ug/L producing significant inhibition. Bioconcentration factors for nickel range from 0.8 for fish muscle to 193 for a cladoceran. I Acute values for twenty

-three saltwater species in twenty genera range from 151.7 ug/L with juveniles of a mysid of to 1,100,000 ug/L with juveniles and adults of a clam. The acute values for the four species of fish range from 7,598 to 350.000 ug/L. The acute toxicity of nickel appears to be related to salinity, but the form of the relationship appears to be speciesdependent. Mysidopsis bahia is the only saltwater species with 

### which an acceptable chronic test has been conducted on nickel. Chronic 

# 0exposure to 141 ug/L and greater resulted in reduced survival and reproduction. The measured acute-chronic ratio was 5.478. 

# 01
Bioconcentration factors in saltwater range from 261.8 with a oyster to 675 with a brown alga. National Criteria The procedures described in the "Guidelines for Deriving Numerical National Water Quality Criteria for the Protection of Aquatic Organisms and Their Uses" indicate, that except possibly where a locally important species is very sensitive, freshwater aquatic organisms and their uses should not be affected unacceptably if the four-day average concentration of nickel (in (0.8460[

### In ug/L) does not exceed the numerical value given by e (hardness)1+1.1645) more than once every three. years on the average and if the one-hour average concentration (inug/L) does not exceed the numerical value given by e(0.846011n 

# 0)

more than once every three years on the (hardness)1+3.3612) average. For example, at hardnesses of 50. 100, and 200 mg/L as CaC03 the four-day average concentrations of nickel are 88, 160. and 280 ug/L, respectively, and the one-hour average concentrations are 790, 1400. and 2500 ug/L. The procedures described in the "Guidelines for Deriving Numerical National Water Quality Criteria for the Protection of Aquatic Organisms and Their Uses" indicate, that except possibly where a locally important species is very sensitive, saltwater aquatic organisms and their uses should not be affected unacceptably if the four-day average concentration of nickel does not exceed 8.3 ug/L more than once every three years on the average and if the one-hour average concentration does not exceed 

# 0)

# a 75 ug/L more than once every three years on the average.

"Acid

-soluble'' is probably the best measurement at present for expressing criteria for metals and the criteria for nickel
were developed on this basis. However, at this time, no EPA approved method for such a measurement is available to implement criteria for metals through the regulatory programs of the Agency and the States. The Agency is considering development and approval of a method for a measurement such as "acid

-soluble. " Until one is approved, however, 

### EPA recommends applying criteria for metals using the total recoverable method. This has two impacts: (1) certain species of some metals cannot be measured because the total recoverable method cannot distinguish between individual oxidation States, and (2) in some cases these criteria might be overly protective when based on the total recoverable method


### . Three years is the Agency's best scientific judgment of the average amount of time aquatic ecosystems should be provided between excursions. The resiliences of ecosystems and their abilities to recover differ greatly, however, and site

-specific allowed excursion frequencies may be established if adequate justification is provided. Use of criteria for developing water quality

-based permit limits and for designing waste treatment facilities requires selection of an appropriate wasteload allocation model. Dynamic models are preferred for the application of these criteria. Limited data or other considerations might make their use impractical, in which case one must rely on a steady

-state model.(51 F.R. 43665, December 3, 1986) SEE APPENDIX A FOR METHODOLOGYPARATHION Summary The acute values for thirty

-seven freshwater species in thirty

-one genera range from 0.04 ug/L for an early instar of a crayfish, Orconectes nais, to 5,230ug/L for two species of tubificid worms. For Daphnia mama, the chronic value and acutechronic ratio are 0.0990 ug/L and 10.10 respectively. Chronic toxicity values are available for two freshwater fish species, the bluegill and the fathead minnow, with chronic values of 0.24 ug/L and 6.3 ug/L, and acute

-chronic ratios of 2.121 and 79.45. respectively. Two freshwater algae were affected by toxaphene concentrations of 30 and 390 ug/L, respectively. Bioconcentration factors determined with three fish species ranged from 27 to 573. The acute values that are available for saltwater species are 11.5 and 17.8 ug/L for the Korean shrimp, Palaemon macrodactvlus. and 17.8 ug/L for the striped bass, Morone saxatilis. No data
are available concerning the chronic toxicity of parathion to saltwater species, toxicity to saltwater plants, or bioaccumulation by saltwater species. Some data indicate that parathion is acutely lethal to commercially important saltwater shrimp at concentrations as low as 0.24 ug/L. Measurement of acetylcholinesterase (AChE) in fish tissue might be useful for diagnosing fish kills caused by parathion. National Criteria The procedures described in the “Guidelines for Deriving Numerical National Water Quality Criteria for the Protection ofAquatic Organisms and Their Uses“ indicate, that except possibly where a locally important species is very sensitive, freshwater 

# a aquatic organisms and their uses should not be affected unacceptably if the four-day average concentration of parathion does not exceed 0.013 ug/L more than once every three years on the average and if the one-hour average concentration does not exceed 0.065 ug/L more than once every three years on the average. The procedures described in the “Guidelines for Deriving Numerical National Water Quality Criteria for the Protection of Aquatic Organisms and Their Uses” require the availability of specified data for the derivation of a criterion. A saltwater criterion for parathion cannot be derived because very few of the required data are available. Three years is the Agency’s best scientific judgment of the 

## .I
average amount of time aquatic ecosystems should be provided between excursions. The resiliences of ecosystems and ‘their abilities to recover differ greatly, however, and site-specific allowed excursion frequencies may be established if adequate justification is provided. Use of criteria for developing water quality-based permit limits and for designing waste treatment facilities requires selection of an appropriate wasteload allocation model. Dynamic models are preferred for the application of these criteria. Limited data or other considerations might make their use impractical, in which case one must rely on a steady-state model. (51 F.R. 43665, December 3, 1986) SEE APPENDIX 

### A FOR METHODOLOGYPENTACHLOROPHENOL (PCP)

Summary The acute and chronic toxicity of PCP to freshwater animals increased as pH and dissolved oxygen concentration of the water decreased. Generally, toxicity also increased with increased temperature. The estimated acute sensitivities of 36 species at pH = 6.5 ranged from 4.355 ug/L for larval common carp to >43,920 ug/L for a crayfish. At pH = 6.5, the lowest and highest estimated chronic values of 11.835 and 79.06 ug/L, respectively,
were obtained with different cladoceran species. Chronic toxicity to fish was affected by the presence of impurities, with industrial

-grade PCP being more toxic than purified samples. Mean acute

-chronic ratios for six freshwater species ranged from 0.8945 to >15.79,but the mean ratios for the four most acutely sensitive species only range 0.8945 to 5.035. Freshwater algae
were affected by concentrations as low as 7.5 ug/L, whereas vascular plants were affected at 189 ug/L and above. Bioconcentration factors ranqed from 7.3 to 1,066 for three species of fish. Acute toxicity values from tests with 18 species of saltwater animals, representing 17 genera, range from 22:63 ug/L for late yolk

-sac larvae of the Pacific herring, Clupea narenqus pallasi, to 18,000 ug/L for adult blue mussels, Mvtllus edulis. The embryo and larval stages of invertebrates and the late larval premetamorphosis stage of ashappear to be the most sensitive 

# 0 life stages to PCF. With few exceptions, Msh are more sensitive

# .J

than invertebrates to PCP. Salinity, temperature, and pR have a slight effect on the toxicity of PCP to some saltwater animals. Life-cycle toxicity tests have been conducted with the sheepshead minnow, Cmrinodon variegatus. and the polychaete worm, Ophrvotrocha diadema. The chronic value for the minnow is 64.31 ug/L and the acute-chronic ratio is 6.873. Unfortunately,
no statistical analysis of the data from the test with the worm is available. The EC506 for saltwater plants range from 17.40 ug/L for the diatom, Skeletonema costatum, to 3.600 ug/L for the green alga, Dunaliella tertiolecta. Apparent steady-state BCFs are available for the eastern oyster. Crassostrea virginica, and two saltwater fishes and range from 10 to 82.
National Criteria The procedures described in Fe "Guidelines for Deriving Numerical National Water Quality Criteria for the Protection of Aquatic Organisms and Their Uses" indicate, that except possibly where a locally important species is very sensitive, freshwater aquatic organisms and their uses should not be affected unacceptably if the four-day average concentration (in ug/L) of pentachlorophenol does not exceed the numerical value given by
e11.005(pH)-5-2901more than once every three years on the average and if the one-hour average concentration (inug/L) does not exceed the numerical value given by e[l.OOS(pH)-4.8301 than once every three years on the average. For example, at pH = 6.5. 7.8, and 9.0 the four-day average concentrations pentachlorophenol are 3.5, 13, and 43 ug/L, respectively, and theone-hour average concentrations are 5.5, 20, and 68 ug/L. At pH

= 6.8, a pentachlorophenol concentration of 1.74 ug/L caused a 50% reduction in the growth of yearling sockeye salmon in a 56- day test. 

# a

The procedures described in the “Guidelines for Deriving Numerical National Water Quality Criteria for the Protection of Aquatic Organisms and Their Uses“ indicate, that except possibly where a locally important species is very sensitive, saltwater aquatic organisms and their uses should not be affected unacceptably if the four

-day average concentration of pentachlorophenol does not exceed 7.9 ug/L more than once every three years on the average and if the one

-hour average concentration does not exceed 13 ug/L more than once every three years on the average. Three years is the Agency’s best scientific judgment of the average amount of time aquatic ecosystems should be provided between excursions. The resiliences of ecosystems and their abilities to recover differ greatly, however, and site

-specific allosred excursion frequencies may be established if adequate justification is provided. Use of criteria for developing water quality

-based permit limits and for designing waste treatment facilities requires selection of an appropriate wasteload allocation model. Dynamic models are preferred for the application of these criteria. Limited data or other considerations might make their we impractical, in which case one must rely on a steady

-state model. (51 F.R. 43665, December 3, 1986) SEE APPENDIX A FOR METHODOLOGYTOXAPHENE

Summary The acute sensitivities of 36 freshwater species in 28 genera ranged from 0.8ug/L to 500 ug/L. Such important fish species as the channel catfish, largemouth bass, chinook and coho salmon, brook, brown and rainbow trout, striped bass, and bluegill had acute senitivities ranging from 0.8 ug/L to 10.8 ug/L. Chronic values for four freshwater species range from less than 0.039 ug/L for the brook trout to 0.1964 ug/L for the channel catfish. The growth of algae was affected at 100 to 1,000 ug/L, and bioconcentration factors from laboratory tests ranged from 3.100 to 90,000. Concentrations 

### in lake trout 

### in the Great Lakes have frequently exceeded the U.S. FDAJactionlevel of 5 mg/kg, even though the concentrations in the water seem to be only 1 to 4 ng/L. These concentrations in lake water are thought to have resulted from toxaphene being transported to the Great Lakes from remote sites, the locations of which are not well known. 

# a

The acute toxicity of toxaphene to 15 species of saltwater animals ranges from 0.53 for pinfish, Laqodon rhomoides. to 460.000 ug/L for the adults of the clam, Ranqia cuneata. Except for resistant species tested at concentrations greater than toxaphene's water solubility, acute values for most species were within a factor of 10. The toxicity of toxaphene was found to decrease slightly with increasing salinity for adult blue crabs. Callinectes sapidus, whereas no relationship between toxicity and salinity was observed with the three spine stickleback,Gasterosteus aculeatus. Temperature significantly affected the toxicity of toxaphene to blue crabs. Early life-stage toxicity tests have been conducted with the sheepshead minnow, Cmrinodon varieqatus, and the longnose killifish, Fundulus similis, whereas life-cycle tests have been conducted with the sheepshead minnow and a mysid. For the sheepshead minnow, chronic values of 1.658 ug/L from the early life-stage test and 0.7141 ug/L from the life-cycle toxicity test are similar to the 96-hr LC50 of 1.1 ug/L. Killifish are more chronically sensitive with effects noted at 0.3 ug/L. 

### In the life-cycle test with the mysid, no adverse effects were observed at the highest concentration tested, which was only slightly below the 96-hr LC50, resulting in an acute-chronic ratio of 1.132. Toxaphene is bioconcentrated by an oyster, Crassostrea 

# 01 virsinica, and two fishes, C. variegatus and 

## z- similis, to concentrations that range from 9,380 to 70.140 times that in the test solution.
National Criteria The procedures described in the "Guidelines for Deriving Numerical National Water Quality Criteria for the Protection of Aquatic Organisms and Their Uses" indicate, that except possibly where a locally important species is very sensitive, freshwater aquatic organisms and their uses should not be affected unacceptably if the four-day average concentration of toxaphene does not exceed 0.0002 ug/L more than once every three years on the average and if the one-hour average concentration does notexceed 0.73 ug/L more than once every three years on the average.



# 0 If the concentration of toxaphene does exceed 0.0002 ug/L. the edible portions of consumed species should be analyzed to determine whether the concentration of toxaphene exceeds the FDA action level of 5 mg/kg. If the channel catfish is as acutely sensitive as some data indicate it might be, it will not be protected by this criterion. The procedures described in the “Guidelines for Deriving Numerical National Water Quality Criteria for the Protection of Aquatic Organisms and Their Uses“ indicate, that except possibly where a locally important species is very sensitive, saltwater aquatic organisms and their uses should not be affected unacceptably if the four

-day average concentration of toxaphene does not exceed 0.0002 ug/L more than once every three years 

### on the average and if the one-hour average concentration does not exceed 0.21 ug/L more than once every three years on the average. If the concentration of toxaphene does exceed 0.0002 ug/L, the edible portions of consumed species should be analyzed 

### to determine whether the concentration of toxaphene exceeds the FDA action level of 5 mg/kg. 

# e

I

Three years is the Agency’s best scientific judgment 

### of the average amount of time aquatic ecosystems should be provided between excursions. The resiliences of ecosystems and their abilities to recover differ greatly, however, and site

-specific allowed excursion frequencies may be established if adequate justification is provided. Use of criteria for developing water quality

-based permit 

# 0 limits and for designing waste treatment facilities requiresselection of an appropriate wasteload allocation model. Dynamic models are preferred for the application of these criteria. Limited data or other considerations might make their use impractical, in which case one must rely on a steady-state model. (51 F.R. 43665, December 3, 1986) SEE 

### APPENDIX A FOR METHODOLOGY 

# 0)Summary Acute toxicity values are available for 43 species of fresl-rateranimals and data for eight species indicate that acute toxicity decreases as hardness increases. When adjusted to a hardness of 50 mg/L, sensitivities range from 50.70 ug/L for CeriodaDhnia reticulata to 88,960 ug/L for a damselfly. Additional data indicate that toxicity increases as temperGture increases. Chronic toxicity data are available for nine freshwater species. Chronic values for two invertebrates ranged from 46.73 ug/L for DaDhnia mama to >5,243 ug/L for the caddisfly, Clistoronla magziifica. Chronic values for seven fish species ranged from 36.41 ug/L for the flagfish, Jordanella 

# 9 floridae, to 854.7 ug/L for the brook trout, Salvelinus fontinalis. Acute

-chronic ratios ranged from 0.2614 to 41.20. but the ratios for the sensitive species were all less than 7.3. The sensitivity range of freshwater plants to zinc is greater than that for animals. Growth of the alga, Selenastrum capriocornutum, was inhibited by 30 ug/L. On the other hand, with several other species of green algae, 4

-day EC5Os exceeded 200,000 ug/L. Zinc was found to bioaccumulate in freshwater animal tissues from 51 to 1,130 times the concentration present in the water. Acceptable acute toxicity values for zinc are available for 33 species of saltwater animals including 26 invertebrates and 7 fish. LCSOs range from 191.5 ug/L for cabezon, ScorDanichthvs 

# amarmoratus to 320.400 ug/L for adults of another clam, Macoma balthica. Early life stages of saltwater invertebrates and 

# 01 fishes are generally more sensitive to zinc than juveniles and adults. Temperature has variable and inconsistent effects on the sensitivity of saltwater invertebrates to zinc. The sensitivity of saltwater vertebrate animals to zinc deyreases with increasing salinity, but the magnitudG of the effect is species-specific. A life-cycle test with the mysid, Mvsidopsia bahia, found unacceptable effects at 120 ug/L, but not at 231 ug/L, and the acute-chronic ratio was 2.997. Seven species of saltwater plants
were affected at concentrations ranging from 19 to 10,100 ug/L. Bioaccumulation data for zinc are available for seven species of saltwater algae and five species of saltwater animals. Steadystate zinc bioconcentration factors for the twelve species range from 3.692 to 23.820.
National Criteria The procedures described in the "Guidelines for Deriving Numerical National Water Quality Criteria for the Protection of Aquatic Organisms and Their Uses" indicate, that except possibly where a locally important species is very sensitive, freshwater aquatic organisms and their uses should not be affected unacceptably if the four-day average concentration of zinc (in (0.847311n ug/L) does not exceed the numerical value given by e
more than once every three years on the (hardness)l+0.7614)
average and if the one-hour average concentration (in ug/L) does (0.8473[In not exceed the numerical value given by e
more than once every three years on the (hardness)]+0.8604)

# 0 average. For example, at hardnesses of 50, 100, and 200 mg/L as CaC03. the four

-day average concentrations of zinc are 59, 110 and 190 ug/L, respectively, and the one-hour average concentrations
are 65, 120, and 210 ug/L. If the striped bass is as sensitive
as some data indicate, it will not be protected by this criterion. The procedures described in the "Guidelines for Deriving Numerical National Water Quality Criteria for the Protection of Aquatic Organisms and Their Uses" indicate, that except possibly where a locally important species is very sensitive, saltwater aquatic organisms and their uses should not be affected unacceptably if the four

-day average concentration of zinc does not exceed 86 ug/L more than once.every three years on the average and if the one-hour average concentration does not exceed 95 ug/L more than once every three years on the average. 

# a

"Acid

-soluble'' is probably the best measurement at present for expressing criteria for metals and the criteria for zinc were developed on this basis. However, at this time no FPA approved method for such a measurement is available to implement criteria for metals through the regulatory programs of the Agency and the States. The Agency is considering development and approval of a method for a measurement such as "acid

-soluble.'' Until one is approved, however, EPA recommends applying criteria for metals using the total recoverable method. This has two impacts: 

### (1) certain species of Some metals cannot be measured because the total recoverable method cannot distinguish between individual oxidation States, and (2) in some cases these criteria might be overly protective when based on the total recoverable method.Three years is the Agency’s best scientific judgment of the average amount of time aquatic ecosystems should be provided 

# a between excursions. The resiliences of ecosystems and their abilities to recover differ greatly, however, and site

-specific allowed excursion frequencies may be established if adequate justification is provided. Use of criteria for developing water quality

-based permit limits and for designing waste treatment facilities requires selection of an appropriate wasteload allocation model. Dynamic models are preferred for the application of these criteria. Limited data or other considerations might make their use impractical, in which case one must rely on a steady

-statemodel. (52 F.R. 6213,March 2. 1987) SEE APPENDIX A FOR METHODOLOGY