QUALITY CRITERIA FOR WATER 1986
UPDATE #1
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*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 concentration 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.
Hu=an Health
For the maximum protection cf 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
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arbier.t 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 nay result in incremental increase'of cancer
risk over the lifetime are estimated at 10~5, 10~6 and lo~7
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.
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 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 10"5, 10~6 and 10"7. 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.
(45 F.R. 79318, November 28, 1980)
SEE APPENDIX B FOR METHODOLOGY
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AMMONIA
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 for pH) ranging from 0.53 to 22.S
mg/L NH3 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
0.14 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 sever.
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.
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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 amr.onia
equilibrium, and sone 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 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 organises
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
families (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 also no clear 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 43, 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 airjnonia with saltwater
organisms are very limited, and insufficient to derive a
saltwater criterion. A few saltwater invertebrate species have
been tested, and the prawn Macrobrachium rosenbergii 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
*s
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.
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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 nur.erical value given by 0.52/FT/FPH/2,
where:
FT = 10°'°3(20"TCAP); TCAP < T < 30
100.03(20-T); o < T < TCAP
FPH =1 ; 8 < pH < 9
1+107.4-pH :
1.25 ; 6.5
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RATIO =16 ? 7.7 < pH <9
= 24 in7-7--
;6.5< pH < 7.7
TCAP = 15 C; Salmonids or other sensitive
coldwater species present
= 20 C; Salmonids and other sensitive
coldwater species absent
(*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 un-
ionized 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
-------
criteria are used in wasteload allocation modeling. For exar.ple,
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.
Data available for saltwater species are insufficient to
derive a criterion for saltwater.
The recommended excesdancs frequency of 3 years is the
Agency's best scientific judgment of the average amount of tine
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 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 1Q5 or 1Q10 for
Criterion Maximum Concentration design flow and 7Q5 or 7Q10 for
the Criterion Continuous Concentration design flow in steady-
state models for unstressed and stressed systems respectively.
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(2) 4-aar e»e<-age concentration! for awnonla.*
0 C
5 C
10 C
15 C
20 C
kJ C
50 C
A. SeHWildl Or Other Sensitive Celd»ater Soeelet
Un-lonlied Anwonla (mj/llttr
6.50
6.75
7.00
7.25
7.50
7.75
8.00
8.25
8.50
8.75
9.00
6.50
6.75
7.00
7.25
7.50
7.75
.00
.25
,50
.75
.00
0.0007
0.0012
0.0021
0.0037
0 .0066
0.0109
0.0126
0.0126
0.012S
0.0126
0.0126
2.3
2.5
2.3
2,5
2.5
2.3
1.53
0.87
0,49
0.28
0.16
8. S»l«onid» 'and Other
6.50
6.75
7.00
7.25
7.30
7.75
8.00
8.25
8.50
8.75
9.00
6.30
6.75
7.00
7.25
7.30
7.75
8.00
8.25
8.50
8.75
9.00
0,0007
0.0012
0.0021
0.0037
0.0066
0.0109
0.0126
0.0126
0.0126
0.0126
0.0126
2.
2.
2.
2.
2.
2.
1.53
0.87
0.49
0.28
0.16
0.0009
0.0017
0.0029
0.0052
0.0093
0.0153
0.0177
0.0177
0.0177
0.0177
0.0177
Total
2.4
2.4
2.4
2.4
2.4
2.2
1.44
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
Ammo.il*
2.2
2.2
2.2
2.2
2.2
2.1
1.37
0.78
0.45
0.26
0.16
Sensitive Cold«ater
Un-lonl
0.0009
0.0017
0.0029
0.0052
0.0093
0.0153
0.0177
0.0177
0.0177
0.0177
0.0177
Total
2.4
2.4
2.4
2.4
2.4
2.2
1.44
0.82
0.47
0.27
0.16
zed A*w»o*
0.0013
O.OC23
0.0042
0.0074
0.0132
0.022
0.025
0.025
0.025
O.C25
0.023
Aiwonla
2.2
2.2
2.2
2.2
2.2
2.1
1.37
0.78
0.45
0.26
0.16
0.0019
0.0033
0.0059
0.0105
0.0186
0.031
0.035
0.035
0.035
0.035
0.035
(»oy liter
2.2
2.2
2.2
2.2
2.2
2.0
1.33
0.76
0.44
0.27
0.16
0.0019
0.0033
0.0059
0.0105
0.0166
0,031
0.033
0.033
0.035
0.035
0.033
NM3>
.49
.49
.49
.30
.50
.4.0
0.93
0.34 •
0.32
0.19
0.13
0.0019
0.0033
0.0039
0.0105
0.0186
0.031
0.033
0.033
0.033
0.033
0.033
1.04
1.04
1.04
1.04
1.05
0.99
O.M
0.39
0.23
- 0.15
0.10
0.0019
0.0033
0.0059
0.0103
0.0186
0.031
0.033
0.035
0.035
0.035
0.035
0,73
0.73
0.74
0.74
0.74
0.71
0.47
0.28
0.17
0.11
0.08
Species Absentt
i\» ( *g/ 1 1
0.0019
0.0033
0.0059
0.0103
0.0186
0.031
0.035
0.035
0.035
0.035
0.035
(•»/ liter
2.2
2.2
2.2
2.2
2.2
2.0
1.33
0.76
0.44
0.27
0.16
fer NHj)
0.0026
0.0047
0.0083
0.0148
0.026
0.043
0.050
0.050
0.050
0.050
0.030
MHj)
2.1
2.1
2.1
2.1
2.1
1.98
1J1
0.76
0.43
0.27
0.17
.
0.0026
0.0047
0.0083
O.OU8
0.026
0.043
0.030
0.030
0.030
0.030
0.030
.*«
.47
.47
.48
.49
.39
0.93
0.34
0.33
0.21
0.14
0.0026
0.0047
0.0083
0.0148
0.026
0.043
0.050
0.030
0.050
0.050
0.050
.03
.04
.04
.05
.06
.00
0.67
0.40
0.25
0.16
o.n
• To convert ttie»e viluts to •£/llt«r N, Multiply by 0.822.
t SIte-tpeclfle criteria d«v«loo"«nt Is §tro«gly twggettetf at tewperttve* «bw»e 20 C
b*ceu»e o* the limited d«ta available to g*"«rir* rna criteria reeo«M*«atlo«, and
•t tvuptrituret b*lo* 20 C 6*aut* of ti* II»IT«J data «r* 6«au»« Mil Oi»*gt« In
the criteria My htv« ilgnlflc»nt l»p«et on the level of treatment required In
Meting the reeoj»*endefl criteria.
-------
(1)
eonc»otrtTlon» 'or *i"
PM
.
6.30
6.73
7.00
7.23
7.30
i.'oo
8JJ
8J5
9.00
0 C
laonldt or Ot*«r
0.0091
O.OU9
0.023
0.034
0.043
0.036
0.063
0.063
0.063
0.063
0.063
3 C
S.«.ltiv.C
0.0129
0.021
0.033
0.048
0.064
0.080
0.092
0.092
0.092
0.092
0.092
10 C
old»tt«<
IZ«J Am»<
0.0182
0.030
0.044
0.068
0.091
0.113
0.130
0.130
0.130
0.130
0.130
13 C
SpKlM Pi
jnl. (*o/l 1
0.026
0.042
0.066
0.093
0.128
0.139
0.184
0.184
0.184
0.184
0.184
Total Ammonia {*j/l|t»r
6,30
6.73
7.00
7.23
7.30
7.73
8.00
1.23
8.30
8.73
9.00
8. Sa l
33
32
28
23
17.4
12.2
8.0
4.3
• 2.6
1 .47
0.&6
•oHdf ana otfiar
33
30
26
22
16J
11.4
7.3
4.2
2.4
1.40
0.83
S-.ltlv. C
31
28
23
20
15.3
10.9
7.1
4.1
2J
1.37
0.83
:oU..».r
30
27
24
19.7
U.9
10.3
6.9
4.0
2J
1.38
0.86
SDK!.. *
Uft*lonlz*d Ammonia (*g/ll
6.30
6.73
7.00
7.23
7.30
7.75
8.00
8.25
8.30
8.73 -
9.00
6.30
6.73
7.00
7.23
7.30
7.73
8.00
8.23
8.30
8.75
9.00
0.0091
O.OU9
0.023
0.034
0.043
0.054
0.063
0.065
0.063
0.063
0.063
33
32
28
23
17.4
12.2
8.0
4.3
2.6
1.47
0.86
0.0129
O.C21
0.033
0.048
0.064
0.083
0.092
0.092
0.092
0.092
0.092
Total
33
30
26
22
16J
11.4
7.3
4.2
2.4
1.40
0.83
0.0182
0.030
0.046
0.068
0.091
O.H3
O.l JO
0.130
0.130
O.i JO
0.130
.—...
31
28
23
20
15.5
10.9
7.1
4.1
2.3
1.37
0.83
0.026
0.042
0.066
0.093
0.128
0.159
0.184
0.184
0.184
0.184
0.184
C-5/Ht.r
30
27
24
19.7
U.9
10.3
6.9
4.0
2.3
1.38
0.86
20 C
••f.nt
0.036
0.059
0.093
0.133
0.181
0.22
0.26
0.26
0.26
0.26
0.26
1 NH.)
29
27
23
19.2
14,6
10.3
6.8
3.9
2J
1.42
0.91
Df.nt
tar NH.)
0.036
0.059
0.093
0.133
0.181
0.22
0.26
0.26
0.26
0.26
0.26
NHj)
29
27
23
19.2
U.6
10.J
6.8
3.9
2 .3
1.42
0.91
23 C
0.036
0.039
0.093
0.133
0.181
0.22
0.26
0.26
0.26
0.26
0.26
20
18.6
16.4
13.4
10.2
7.2
4.6
2.8
1.71
1.07
0.72
0.031
0.084
0.131
0.190
0.26
0.32
0.37
0.37
0.37
0.37
0.37
29
26
23
19.0
U.3
10.2
6.6
4.0
2.4
1.32
1.01
JC C
O.C36
0.059
0.093
0.135
0.18)
0.22
0.26
0.25
0,26
0.26
0.26
14.3
13.2
11.6
9.3
7.3
5.2
3.3
2.1
1.28
0.93
0.38
0.051
O.CS4
0.131
0.190
0.26
0.32
0.37
0.37
0.37
0.37
0.37
20
18.6
16.4
13.3
10.3
7.3
4.9
2.9
1.81
1.18
0.82
To wwtrt
vtluts tc mg/1 lT»r N, *uiTlfily BY 0.822.
-------
The Agency acknowledges that the Criterion Continuous
Concentration strear. 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 exceeder.ces
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 METHODOLOGY
-------
BERYLLIUM
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 berylliur. 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 ingesticn
of contaminated water and contaminated aquatic organisms, the
ambient water concentration should be zero, based on the ncr.
threshold assumption for this chemical. However, zero level may
not be attainable at the present time. Therefore, the levels
which ma'y" 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 68 ng/L, 6.8 ng/L, and
0.68 ng/L, respectively. If these estimates are made for
-------
ccnsur.ption of aquatic organises only, excluding consu-ptic- cf
water, the levels are 1170 ng/L, 117.0 ng/L, and 11.71 ng/L,
respectively.
(45 F.R. 79318, November 28, 1980)
SEE APPENDIX B FOR METHODOLOGY
-------
BORON
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 or calcium borate salt. Boron salts
are used in fire retardants, the production of glass, leather
tanning and finishing industries, cosmetics, photographic
r.aterials, 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 r.g/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 forrr,
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 °C 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 Devlaninck, 1955: Le Clerc, 1960).
In the dairy cow, 16 to 2O 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), in a 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 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 METHODOLOGY
-------
CHLORINATED BENZENES
CRITERIA
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 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
trichlcrobenzenes, a criterion cannot be derived at this tire
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 hunan 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 arJoient 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, zero
-------
level IT.ay not be attainable at the present time. Therefor, the
levels which may result in incrar.ental increase of cancer risk
over the lifetime are estimated at 10~5, 10~6, and 10~7. The
corresponding recommended criteria are 7.2 ng/L, 0.72 ng/L, and
0.072 ng/L, respectively. If the above estimates are nade 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. 79318, Nover.ber 28, I960)
SEE-. APPENDIX B FOR METHODOLOGY
-------
DICHLOROPROPAKZS/DICHLOROPROPENES
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 aq\iatic 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 life occurs at concentrations as
low as 79.0 ug/L and would occur at lower concentrations ar.ong
species that are more sensitive than those tested. No data
are available concern ir. g 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.
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 aquatir.
organisms alone, the ambient water criterion is determined to be
14.1 mg/L.
(45 F.R. 79318, November 28, 1980)
SEE APPENDIX B FOR METHODOLOGY
-------
*ENDRIN
CRITERIA:
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 tir.e-
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 organises. The
calculated value is comparable to the present standard. For
this reason a selective criterion based on exposure solely frcr.
ccnsur.ption 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
-------
HZPTACHLOR
CRITERIA;
Aguatic 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 tine.
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 r.ay 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 2.78 ng/L, 0.28 ng/L, and
0.028 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
-------
HEXACHLOROCYCLOHEXANE
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
tine.
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 lover
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 lover
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 huir.an 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 10~5, 10-6^ and io~7. 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 of human 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 nay 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 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 gar.a-
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 10~5, 10*~6, and 10~7. 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 ray
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 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.
-------
Using the present guidelines, satisfactory criteria cannot be
derived at this tiroe for delta and epsilon hexachlorocyclohexane
because of insuf-ficient available data.
(45 F.R. 79318, November 28, 1980)
SEE APPENDIX B FOR METHODOLOGY
-------
MIREX
CRITERION:
0.001 ug/L for freshwater and marine aquatic life.
RATIONALE;
Mirex is used to control the imported fire ant Solenopsis
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 85 percent corncob
grits. The mirex bait often is applied at a rate of 1.4 kg/ha,
equivalent to 4.2 grams of toxicant per hectare.
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 to mirex 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 nirex bait.
Procambarus blandingi juveniles were exposed to 1 or 5 ug/L
for 6 to 144 hours, transferred to clean water and observed for
10 days. After 5 days in clean water, 95 percent of the animals
exposed to 1 ug/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,
-------
Procar.barus 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 (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 95 percent were
dead in 7 days. Water analysis indicated ir.irex concentrations of
0.86 ug/L. In feeding experiments, 108 crayfish each wers 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 oirex 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 xnirex on fish has been
concentrated" on species which have economic and sport fishery
importance. Hyde et al. (1974) applied oirex bait (0.3 percent
jnirex) at the standard rate (1.4 Xg/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 applicaticr
-------
(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.
In another study, Van Valin et al. (1968) exposed bluegills,
Lepomis macrochirus, and the goldfish, Carassius auratus, to
mirex by feeding a mirex-treated diet (1, 3, and 5 og 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 shovr.
that the insecticide is accumulated through the food chair.
Borthwick et al. (1973) reported the accumulation of mirex ir.
South Carolina estuaries. Their data revealed that mirex was
transported from treated land and marsh to the estuary aniTr.il =
and that accumulation, especially in predators, occurred. In t-e
test area, water samples consistently were less than 0.01 ug l
-------
Residues in fish varied from non-detectable to 0.8 ug/g with 15
percent of the sar.ples 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 to 4.4 ug/g and 78 percent of the
birds contained residues up to 17 ug/g. Nagvi and de la Cruz
(1973) reported average residues for molluscs (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 roirex/ha). Crayfish residues ranged from 0.04 to
0.16 ug/g. Fish residues were about 2 to 20 times greater than
the controls and averaged from 0.01 to 0.76 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 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 adverse effect at 3 ug/g with mallards and 13 ug/g with
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 all organochlorine compounds tested except
-------
for DDE. Delayed mortality occurred among birds subjected to
doses above expected environmental concentration.
A summary ex-anination of the data available at^ this time
shows a mosaic of effects. Crayfish and channel catfish survival
.iff-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 aguatic ecosystem is unknown. There is evidence that mirex
is very persistent in bird tissue. Considering the extreme
toxicity and potential fcr 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 r.ud
crab, Rhithropanopeus harrisii, reduced survival was observed in
-G.l-ug/L mirex (Bookhout et al. 1972). In three of four 28-day
seasonal flow-through experiments, Tagatz et al. (1975) found
reduced 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 marine
-------
crustaceans were observed only after considerable tire had
elapsed, it seeras reasonable that length of exposure is an
important consideration for this chemical. This nay not be the
case in fresh water since the crayfish were affected within 48
hours. Therefore, a 3- to 4-week exposure might be considered
"acute" 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 METHODOLOGY
-------
NICKEL
CRITERIA:
Aquatic Life
For 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[ln(hardness) ]+l.06) as a
24-hour average, and the concentration (in ug/L) should not
exceed the numerical value given by e(0.76[ln (hardness) ]+4.02)
at any time. For example, at hardnesses of 50, 100, and 200 mg/L
as CaCO3 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 the Guidelines is 7.1
ug/L as a 24-hour average, and the concentration should not
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 is determined to be 13.4
ug/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 METHODOLOGY
-------
2,3,7,8-TETRACHLORODIBENZO-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,
concentrations >0.0000l 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 organisms, the
ambient water concentration should be zero. This criterion is
-------
based on the nonthreshold assurption for 2,3,7,5-TCDD. However,
zero may not be an attainable level at this tine. Therefore, the
levels that may result in an increase of cancer risk over the
lifetime are estimated at 10""5, 10~6, and 10~7. The
— 7 ~ 8
corresponding recommended criteria are 1.3x10 , 1.3x10 ° and
1.3xlO~9 ug/L, respectively. If the above estimates are made for
consumption of aquatic organisms only, excluding consumption cf
water, the levels are 1.4xlO~7, 1.4xlO~8 and 1.4xlO~9 ug/L,
respectively. If these estimates are made for consumption cf
water only, the levels are 2.2xlO~6, 2.2xlO~7 and 2.2xlO"c ug/L,
respectively.
(49 F.R. 5831, February 15, 1984)
SEE APPENDIX B FOR METHODOLOGY
-------
ALKALINITY
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-------
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-------
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-------
PH
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-------
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-------
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TAINTING SUBSTANCES
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TEMPERATURE
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BIBLIOGRAPHIC INFORMATION
PB95-207395
Report Nos:
Title: Quality Criteria for Water, 1986. Update Number 1.
Date: 1995
Performing Organization: Environmental Protection Agency, Washington, DC. Office of
water.
Supplemental Notes: Portions of this document are not fully legible. See also
NTIS Field/Group Codes: 68D* (Water Pollution & Control), 68G (Environmental Health f
baretyj
Price: PC A04/MF A01
Availability: Available from the National Technical Information Service, Springfield,
VA. zz
Number of Pages: 58p*
Keywords : *Water quality, *Water pollution, ^Criteria, Contaminants, Sedimentation,
Productivity, Biological effects, Water pollution effects, Public health, *Ambient
water quality criteria, ^Quality criteria.
Abstract: This is the first of several updates to the 1986 Quality Criteria for water
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