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*, uJ. QOVERNMENT PRlNTlNQ OFflCE] 9 8 6  1 5 9 3 0 0 5 0 4 7 2 QUALITY 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 Substances 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. 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 METHODOLOGY AMMONIA sUMlrmy:

~ 1 1 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 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 un

ionized 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 sensitive tested 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 alsonoclear trend 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 chronic values ranging by not much more than a factor or two. The range of acute chronic ratios for 10 species from 6 families was 3 to 4 3 , and acute chronic ratios were higher for the species having chronic tolerance below the median.

Available data indicate that differences in sensitivities between 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:

T h e p r o c e d u r e s d e s c r i b e d i n t h e G u i d e l i n e s f o r D e r i v i n g Numerical National Water Q u a l i t y C r i t e r i a f o r t h e Protection of Aquatic Organisms and T h e i r U s e s i n d i c a t e t h a t , except p o s s i b l y where a l o c a l l y important s p e c i e s is v e r y s e n s i t i v e , freshwater a q u a t i c o r g a n i s m s a n d t h e i r u s e s s h o u l d n o t be a f f e c t e d unacceptably i f : 8 ( 1) t h e 1 hour* average concentration o f un ionized ammonia ( i n mg/ L NH3) does n o t exceed, more o f t e n t h a n once every 3 years on t h e average, t h e numerical v a l u e g i v e n by 0.52/ FT/ FPH/ 2,

where:

FT   10 ° . 03 20 TCAP); TCAP < T 5 3 0

0.03 20 T); 0 < T < TCAP 10

FPH = 1 ; 8 < p H < 9 1+ 107.4 PH 1.25 ; 6.5< pH   < 7 . 7 TCAP = 2 0 C ; Salmonids o r o t h e r s e n s i t i v e coldwater species p r e s e n t coldwater s p e c i e s absent = 25 C; Salmonids and o t h e r s e n s i t i v e (* An a v e r a g i n g p e r i o d of 1 h o u r may n o t be a p p r o p r i a t e i f e x c u r s i o n s o f c o n c e n t r a t i o n s t o g r e a t e r t h a n 1.5 times t h e average occur during t h e hour; i n such c a s e s , a shorter averaging period may be needed.)

( 2) t h e 4 day a v e r a g e c o n c e n t r a t i o n of un ionized ammonia ( i n mg/ L NH3) does n o t exceed, more o f t e n t h a n once every 3 years on t h e a v e r a g e , t h e a v e r a g e * n u m e r i c a l v a l u e g i v e n by 0.80/ FT/ FPH/ RATIO, where FT and FPH a r e as above and: RATIO = 16 : 7.7  < pH  < 9 TCAP = 15 C; S a l m o n i d s o r o t h e r s e n s i t i v e coldwater s p e c i e s p r e s e n t coldwater species absent = 2 0 c ; S a l m o n i d s a n d o t h e r s e n s i t i v e (* Because t h e s e formulas a r e n o n l i n e a r i n pH and temperature, t h e c r i t e r i o n s h o u l d be t h e a v e r a g e of s e p a r a t e e v a l u a t i o n s o f t h e f o r m u l a s r e f l e c t i v e o f t h e f l u c t u a t i o n s of f l o w , pH, and temperature w i t h i n t h e averaging p e r i o d ; it is n o t a p p r o p r i a t e i n g e n e r a l t o simply a p p l y t h e formula t o average p H , temperature,

and flow.)

The extremes f o r temperature ( 0, 30) and pH ( 6.5, 9) given i n t h e a b o v e f o r m u l a s a r e a b s o l u t e . I t is n o t permissible w i t h c u r r e n t d a t a t o conduct any e x t r a p o l a t i o n s beyond these l i m i t s .

I n p a r t i c u l a r , t h e r e i s r e a s o n t o b e l i e v e t h a t a p p r o p r i a t e c r i t e r i a a t p H > 9 w i l l be l o w e r t h a n t h e p l a t e a u between pH 6 and 9 g i v e n above.

C r i t e r i a c o n c e n t r a t i o n s f o r t h e p H r a n g e 6.5 t o 9.0 and t h e t e m p e r a t u r e r a n g e 0 C t o 30 C a r e p r o v i d e d i n t h e f o l l o w i n g t a b l e s . T o t a l ammonia c o n c e n t r a t i o n s e q u i v a l e n t t o e a c h un

ionized ammonia concentration are a l s o provided i n these t a b l e s .

There a r e l i m i t e d d a t a on t h e e f f e c t of t e m p e r a t u r e on c h r o n i c t o x i c i t y . EPA w i l l be c o n d u c t i n g a d d i t i o n a l research on t h e e f f e c t s o f t e m p e r a t u r e on ammonia t o x i c i t y i n o r d e r t o f i l l p e r c e i v e d d a t a g a p s . Because of t h i s u n c e r t a i n t y , a d d i t i o n a l s i t e s p e c i f i c i n f o r m a t i o n s h o u l d be d e v e l o p e d b e f o r e t h e s e 0 criteria 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 site

specific 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 a1 location 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. 12) 4 day average concentrations for m m n l a . . \

PU o c 5 c I0 c 15 C 20 c 25 c W C L . S a l m I 6 a or Other Smsltlv. Cold. ater S D ~ C I ~ S Present Un 1onlz. d Amonla l m g / l l t r 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 . O l 2 t 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 0 m 5 9 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 2 3 2.2 2.2 2 . o I .33 0.76 0.44 0.27 0.16 1 A9 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 I A 7 I A 7 I .48 1 A9 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 0 2 5 0.16 0.11 To convert meso v a l w s to np/ ll? er N, m u l t l p l y by 0.822.

t S l t c ~ p ~ ~ l t I c crltrla dorolopment Is rtronplv ruggost. d a t TmDOratyr" abwm 20 C buause of the Iln1t. d data avallable to generato tho c r l t u l a rrm. nd. tlon, and at t m p e r a t u r * s blow 20 C b W u s e of T b l i m 1 t . d data and b o a u Y mall hmgor In the c r l t o r l a may have rlgnlflcant Impact on the Inol Of trmtl( lt r. qu1r. l In Irotlng tho r. 6umNnd. d crltorla. o c 5 c 10 c I5 c M C 25 C K J C vH A. Salmcnldr or Omer Sensltlve CoId. atu 5 p u l . 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 0 2 6 0.26 0 2 6 0.26 0 3 6 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 0 3 6 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 0 3 6 0.26 0.26 0.26 0 2 6 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) 17 A 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 . o n 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 2 i3 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 0 2 6 0.32 0.37 0.31 0.37 0.37 0 3 7 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 0.82 T h e Agency a c k n o w l e d g e s t h a t t h e C r i t e r i o n C o n t i n u o u s Concentration stream flow averaging period used f o r steady s t a t e w a s t e l o a d a l l o c a t i o n modeling may be a s l o n g a s 30 d a y s i n s i t u a t i o n s i n v o l v i n g POTWs d e s i g n e d t o remove ammonia where l i m i t e d v a r i a b i l i t y o f e f f l u e n t p o l l u t a n t c o n c e n t r a t i o n and r e s u l t a n t concentrations i n r e c e i v i n g waters can be demonstrated.

I n c a s e s where low v a r i a b i l i t y c a n be d e m o n s t r a t e d , l o n g e r a v e r a g i n g p e r i o d s f o r t h e ammonia C r i t e r i o n C o n t i n u o u s C o n c e n t r a t i o n ( e . g . , 30 day a v e r a g i n g p e r i o d s ) would b e a c c e p t a b l e because t h e magnitude and d u r a t i o n of exceedences a b o v e t h e C r i t e r i o n C o n t i n u o u s C o n c e n t r a t i o n w o u l d be s u f f i c i e n t l y l i m i t e d . These m a t t e r s are discussed i n more d e t a i l i n t h e Technical Support Document f o r Water Quality Based Toxics C o n t r o l ( U. S. EPA, 1985a).

( 50 F. R. 30784, J u l y 29, 1985) SEE APPENDIX A FOR METHODOLOGY BERYLLIUM 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 for consumption 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 a BORON CRITERION:

750 ug/ L f o r long term i r r i g a t i o n on s e n s i t i v e crops.

INTRODUCTION:

Boron i s n o t found i n i t s e l e m e n t a l form i n n a t u r e : it i s u s u a l l y found a s a sodium o r c a l c i u m b o r a t e s a l t . Boron s a l t s a r e u s e d i n f i r e r e t a r d a n t s , t h e p r o d u c t i o n of g l a s s , l e a t h e r t a n n i n g and f i n i s h i n g i n d u s t r i e s , c o s m e t i c s , photographic m a t e r i a l s , m e t a l l u r g y a n d f o r h i g h e n e r g y r o c k e t f u e l s .

Elemental boron a l s o can be used i n n u c l e a r r e a c t o r s f o r neutron absorption. Borates a r e used a s " burnable" poisons.

RATIONALE:

Boron is an e s s e n t i a l element f o r growth of p l a n t s b u t t h e r e i s no e v i d e n c e t h a t it is r e q u i r e d by a n i m a l s . The maximum c o n c e n t r a t i o n found i n 1 , 5 4 6 s a m p l e s o f r i v e r and l a k e w a t e r s from v a r i o u s p a r t s o f t h e United S t a t e s was 5.0 mg/ L: t h e mean v a l u e was 0.1 mg/ L ( Kopp and Kroner, 1 9 6 7 ) . Ground waters could c o n t a i n s u b s t a n t i a l l y h i g h e r c o n c e n t r a t i o n s a t c e r t a i n places.

The concentration i n seawater i s reported a s 4.5 mg/ L i n t h e forn o f b o r a t e ( N A S , 1 9 7 4 ) . N a t u r a l l y o c c u r r i n g c o n c e n t r a t i o n s of boron should have no effects on a q u a t i c l i f e .

The minimum l e t h a l dose f o r minnows exposed t o b o r i c acid a t 20 OC f o r 6 h o u r s was r e p o r t e d t o be 1 8 , 0 0 0 t o 19,000 mg/ L i n d i s t i l l e d water and 19,000 t o 19,500 mg/ L i n hard water ( Le Clerc and Devlaminck, 1955: Le C l e r c , 1960).

I n t h e d a i r y cow, 1 6 t o 2 0 g/ day of b o r i c a c i d f o r 4 0 days produced no ill e f f e c t s ( McKee and Wolf, 1963).

S e n s i t i v e c r o p s h a v e shown t o x i c e f f e c t s a t 1 0 0 0 ug/ L o r less o f b o r o n ( R i c h a r d s , 1954). Bradford ( 1966), i n a review o f b o r o n d e f i c i e n c i e s and t o x i c i t i e s , s t a t e d t h a t when t h e boron c o n c e n t r a t i o n i n i r r i g a t i o n w a t e r s was g r e a t e r t h a n 0.75 ug/ L,

some s e n s i t i v e p l a n t s s u c h a s c i t r u s began t o show i n j u r y .

Biggar and Fireman ( 1960) showed t h a t with n e u t r a l and a l k a l i n e s o i l s o f h i g h a b s o r p t i o n c a p a c i t i e s , water c o n t a i n i n g 2 ug/ L boron m i g h t b e u s e d f o r some t i m e w i t h o u t i n j u r y t o s e n s i t i v e p l a n t s . The c r i t e r i o n o f 750 ug/ L i s t h o u g h t t o p r o t e c t s e n s i t i v e c r o p s during long term i r r i g a t i o n .

( QUALITY CRITERIA  OR WATER, JULY 1976) PB 263943 SEE APPENDIX C  OR METHODOLOGY CHLORINATED 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 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 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 4 8 8 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 4 8 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 8 5 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, zero level 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 . 7 4 ng/ L and 0 . 0 7 4 . ng/ L respectively.

( 4 5 F. R. 79316, November 28, 1980) SEE APPERDIX B FOR METHODOLOGY DICHMROPROPANES/ 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 23,000 and 5,700 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 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 1 ife 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 2 8 , 1980) SEE APPENDIX B  OR METHODOLOGY CRITERIA:

 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 METHODOLOGY HEPTACHMR 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 METHODOLOGY CRITERIA : 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 l o w 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 alpha

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 10 6 and The corresponding recommended criteria are 9 2 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 levels which 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 gama

hexachlorocyclohexane through ingestion of contaminated water 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 technical

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 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. 0 Using 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 METHODOLOGY MIREX CRITERION:

0.001 ug/ L f o r freshwater and marine a q u a t i c l i f e .

RATIONALE: 0 Mirex is used t o c o n t r o l t h e imported f i r e a n t S o l e n s s i s saevissima r i c h t e r i i n t h e southeastern United S t a t e s . Its use is e s s e n t i a l l y l i m i t e d t o t h e c o n t r o l of t h i s i n s e c t and it i s a l w a y s p r e s e n t e d i n b a i t . I n t h e most common f o r m u l a t i o n ,

t e c h n i c a l grade mirex i s d i s s o l v e d i n soybean o i l and sprayed on corncob g r i t s . The b a i t produced i n t h i s manner c o n s i s t s of 0.3 __

p e r c e n t mirex, 14.7 p e r c e n t soybean o i l and 85 percent corncob g r i t s . b a i t o f t e n i s a p p l i e d a t a r a t e o f 1 . 4 kg/ ha,

e q u i v a l e n t t o 4.2 grams of t o x i c a n t per hectare. The mirex R e l a t i v e l y f e w s t u d i e s have been made of t h e effects of mirex on freshwater i n v e r t e b r a t e s o f ' these, o n l y Ludke e t a l . ( 1 9 7 1 )

r e p o r t chemical a n a l y s e s of mirex i n t h e w a t e r . T h e i r s t u d y r e p o r t e d e f f e c t s on two c r a y f i s h s p e c i e s exposed t o mirex by three techniques. F i r s t , f i e l d c o l l e c t e d c r a y f i s h were exposed t o s e v e r a l s u b l e t h a l c o n c e n t r a t i o n s o f t e c h n i c a l g r a d e mirex s o l u t i o n s f o r v a r i o u s p e r i o d s o f t i m e : second, c r a y f i s h were e x p o s e d t o m i r e x l e a c h e d f r o m b a i t ( 0.3 p e r c e n t a c t i v e i n g r e d i e n t ) ; and t h i r d , t h e c r a y f i s h were fed mirex b a i t .

Procambarus  blandingi j u v e n i l e s were exposed t o 1 o r 5 ug/ L f o r 6 t o 1 4 4 h o u r s , t r a n s f e r r e d t o c l e a n w a t e r and observed f o r 1 0 days. A f t e r 5 days i n c l e a n water, 95 percent o f the animals exposed t o 1 ug/ L f o r 1 4 4 h o u r s were dead. Exposure t o 5 ug/ L f o r 6 , 2 4 , and 58 h o u r s r e s u l t e d i n 2 6 , 5 0 , and 9 8 p e r c e n t m o r t a l i t y 10 d a y s a f t e r t r a n s f e r t o c l e a n water. C r a y f i s h , Procambarus w, were exposed to 0.1 and 0.5 ug/ L for 48 hours.

Four days after transfer to clean water, 6 5 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 ( wet weight 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 9 5 percent 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 l o w 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 ( 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 data revealed that mirex was transported from treated land and marsh to the estuary animals and that accumulation, especially in predators, occurred. In the test area, water samples consistently were less than 0.01 ug/ L. R e s i d u e s i n f i s h v a r i e d from non d e t e c t a b l e t o 0.8 ug/ g w i t h 1 5 percent of t h e samples containing residues. The amount of mirex and t h e percent of samples containing mirex increased a t higher t r o p h i c l e v e l s . F i f t y f o u r p e r c e n t of t h e raccoons sampled c o n t a i n e d mirex r e s i d u e s up t o 4 . 4 ug/ g and 7 8 p e r c e n t of t h e b i r d s c o n t a i n e d r e s i d u e s up t o 17 ug/ g. Nagvi and d e l a Cruz ( 1 9 7 3 ) r e p o r t e d a v e r a g e r e s i d u e s f o r m o l l u s c s ( 0.15 ug/ g), f i s h ( 0 . 2 6 u g / g ) , i n s e c t s ( 0.29 u g / g ) , c r u s t a c e a n s ( 0.44 ug/ g) and a n n e l i d s ( 0 . 6 3 u g / g ) . They also r e p o r t e d t h a t mirex was found i n a r e a s n o t t r e a t e d w i t h mirex which s u g g e s t s movement of t h e p e s t i c i d e i n t h e environment. Wolfe and Norment ( 1973) sampled a n area f o r one y e a r f o l l o w i n g a n a e r i a l a p p l i c a t i o n of mirex b a i t ( 2 . 1 g mirex/ ha). C r a y f i s h r e s i d u e s ranged from 0.04 t o 0.16 ug/ g. F i s h r e s i d u e s were about 2 t o 2 0 t i m e s g r e a t e r t h a n t h e c o n t r o l s and averaged from 0.01 t o 0.76 ug/ g. K a i s e r ( 1 9 7 4 ) ,

r e p o r t e d t h e p r e s e n c e of mirex i n f i s h from t h e Bay of Q u i n t e ,

Lake O n t a r i o , Canada. C o n c e n t r a t i o n s range from 0.02 ug/ g i n t h e gonads of t h e northern long nose gar, Lepistosteus osseus, t o 0.05 ug/ g i n t h e post anal f i n of t h e northern pike, Esox l u c i u s .

Mirex has never been r e g i s t e r e d f o r use i n Canada.

Mirex does n o t appear t o be g r e a t l y t o x i c t o b i r d s , w i t h LC5O's f o r the young of f o u r s p e c i e s ranging from 547 t o g r e a t e r t h a n 1667 ug/ g ( Heath e t al. 1 9 7 2 ) . Long term d i e t a r y dosages caused no adverseeffect a t 3 u g / g w i t h m a l l a r d s and 13 u g / g w i t h pheasants ( Heath and Spann, 1973). However, it has been reported ( S t i c k e l e t a l . 1 9 7 3 ) t h a t t h e p e r s i s t e n c e of mirex i n b i r d t i s s u e exceeds t h a t of a l l organochlorine compounds tested except for 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 . 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 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 to base 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/ L mirex ( Bookhout et al. 1972). In three of four 28 day seasonal flow through experiments, Tagatz et al. ( 1975) found Educed survival of Call inectes 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 marine crustaceans 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 METHODOMGY NICKEL CRITERIA:

Aquatic Life For t o t a l r e c o v e r a b l e n i c k e l t h e c r i t e r i o n ( i n ug/ L) t o 0 p r o t e c t freshwater a q u a t i c l i f e a s derived using t h e Guidelines i s t h e numerical v a l u e g i v e n by e( 0.76[ ln( hardness)]+ l. 06) a s a 24 hour a v e r a g e , and t h e c o n c e n t r a t i o n ( i n ug/ L) s h o u l d n o t exceed t h e numerical v a l u e given by .( 0.76[ I n ( hardness) ]+ 4.02)

a t any t i m e . For example, a t hardnesses of 50, 1 0 0 , and 200 mg/ L a s CaC03 t h e c r i t e r i a a r e 56, 96, a n d 160 ug/ L, r e s p e c t i v e l y , a s 24 hour averages, and t h e concentrations should n o t exceed 1 , 1 0 0 ,

1 , 8 0 0 , and 3,100 ug/ L, r e s p e c t i v e l y , a t any t i m e .

For t o t a l r e c o v e r a b l e n i c k e l t h e c r i t e r i o n t o p r o t e c t s a l t w a t e r a q u a t i c l i f e a s d e r i v e d u s i n g t h e G u i d e l i n e s i s 7.1 ug/ L a s a 24 hour a v e r a g e , a n d ' t h e c o n c e n t r a t i o n s h o u l d n o t 0 exceed 1 4 0 ug/ L a t any t i m e .

Human Health For t h e p r o t e c t i o n of human h e a l t h from t h e t o x i c p r o p e r t i e s of n i c k e l i n g e s t e d t h r o u g h w a t e r and contaminated a q u a t i c organisms, t h e ambient w a t e r c r i t e r i o n i s determined t o be 1 3 . 4 W / L .

For t h e p r o t e c t i o n of human h e a l t h from t h e t o x i c p r o p e r t i e s of n i c k e l i n g e s t e d t h r o u g h contaminated a q u a t i c organisms a l o n e , t h e ambient water c r i t e r i o n i s determined t o be 1 0 0 .

Ug/ L*

( 45 F. R. 79318, November 2 8 , 1980) SEE APPENDIX B FOR METHODOLOGY 2,3,7,8 TETRACHLORODIBENZO P DIOXI l CRITERIA:

Aquatic Life Not enough data are available concerning the effects of a 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,

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. 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 is based on t h e nonthreshold assumption f o r 2,3,7,8 TCDD. However,

z e r o m a y n o t b e a n a t t a i n a b l e l e v e l a t t h i s time. T h e r e f o r e , t h e l e v e l s t h a t may r e s u l t i n an i n c r e a s e of cancer r i s k over t h e l i f e t i m e a r e e s t i m a t e d a t a n d The c o r r e s p o n d i n g recommended c r i t e r i a a r e 1 . 3 ~ 1 0  ~ , 1 . 3 ~ 1 0  ~ and 1.3x10' ug/ L, r e s p e c t i v e l y . If t h e above estimates are made f o r consumption of a q u a t i c organisms o n l y , excluding consumption of w a t e r , t h e l e v e l s a r e 1 . 4 x 3 0  ~ , 1.4x10* and 1.4x10' ug/ L,

r e s p e c t i v e l y . I f t h e s e e s t i m a t e s a r e made f o r comsumption of water o n l y , t h e l e v e l s are 2 . 2 ~ 1 0  ~ , 2.2xlO' and 2 . 2 ~ 1 0  ~ ug/ L,

r e s p e c t i v e l y .

( 4 9 F. R. 5831, February 15, 1984) SEE APPENDIX B  OR METHODOLOGY ALKALINITY BARIUM REFERENCES CITED Browning, E 1961. Toxicity of industrial metals. Butterworth, London. b t r . M., et d. 1970. Effeeta of pollution on fmh Me, heavy m e a Annd Literature review. J w . Water Poll. Cont Fed. 42W. L. ngr. N A 1961. Handbook of cbemistry. lorh ed Yd; fiw Hill, Book Co.. New Ywk. little, A. D. 1971. Iwrg. oic cbemical pollution of fnah water. Water q d t y & la lmk Val. 2. US. Envimnmental Proteetion Agency, la010 DPV. pp. 2e26. McKee, J. E. ud W. W. Wolf. 1963. Water quality criteria Calif& Skte Watm M u m a Contrd Board, Pub. No. 3 A National Aademy of Seieooes. National Academy of Engioeering. 191+ Water qwlity criteria, 1972 U S Government Printing Off=, W. shin@ n, D. C. Patty, FAl962lndustrialbygieneudtoximlogy, VoL1I. JohnA W i l e y , N e r Y a t p p % loo2 Cited in US. Department of Health, Eduatian ud Welfare. 1M. Public Health SeMce. 1WB. Drinking water quality of rkasd intast. te eUria water supplies. U. S. Depar( ment of Health Eduatian ud Welfy W.. hin% on, D. C. Sollmann. T. H. 1957. A manud of pharmamlogy and its applition to ud toljcolcgy. 8th ed. W. B. Saunden Co. Philadelphia Stokinger, H. E., radRLWmdwaardl968. Toljcdogiemetbodrfaat. blirhin~ water standards. Jour. Ame?. Water Worlrs h. 50.615. U. S Deprtment of Health, Education and Welfue. 1968. Preliminvy air pdlutioa r w e y of buiurn and its compouinja, a literature review. N a W Air P o U d n CODtml Administntion Publiation No. AIT D 69 23, Raleigh, N. C.

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UUY. Jw. Water Poll. Cont Fed. 86: 240. a HARDNESS a REFERENCES CITED Doudomff, P. and M. b t z . 1953. Critical review cf li+ rstweon the toxicity of induarrial wastes and their mmponenh to fish. 11: The metabasa. <EMAIL_ADDRESS>Sew. andind. Wasted, 25: Bm National Academy of Science. National Academy of Engineering. 1974. Water quality criteria. 1912. U S Government t i n t i n g Office. Washingon, D. C. National Technical Ad r). Committee to the Secretary of the Interior. 1963. Water quality enterin. US. Government t i n t i n g Office. Washington, D. C. Sawyer. C. H. 1960. Chemisq for sanitary engineen. McGraw Hill Book Co.. New York. Stiff, MJ. 1971. Copper/ biearbonatP equilibria in m l u t i o ~ of bicarbonate ion at mncentrations similar to t h m found in n a t d water. Water Research. 5: 171.

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McKee. J. E.. and H. W. Wolf. 1963. Water quality eriterir State Water Quality Control Natioml Academy of Sciences, National Aeademy of Engineering. 1974. Water g d i t y Riddirk, J. M.. et d. 1958. Iron and manganese in water suppliea Jour. Amer. Water Board. Sacramento. calif. Pub. 3 A.

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NITRATES, NITRITES REFERENCES CITED Gillette, U, et al. 1952 Apprakl of a chemical w e problem by fiah toxicity tests.

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