United States
Environmental Protection
Agency
Water
Office of Water
Regulations and Standards
Criteria and Standards Division
Washington, DC 20460
EPA 440/5-88-004
April 1989
oEPA
Ambient Water Quality
Criteria for Ammonia
(Saltwater)-1989
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AMBIENT AQUATIC LIFE WATER QUALITY CRITERIA FOR AMMONIA
(SALT WATER)
U.S. ENVIRONMENTAL PROTECTION AGENCY
OFFICE OF RESEARCH AND DEVELOPMENT
ENVIRONMENTAL RESEARCH LABORATORY
NARRAGANSETT, RHODE ISLAND
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NOTICES
This report has been reviewed by the Criteria and Standards Division,
Office of water Regulations and standards, U.S. Environmental Protection
Agency, and approved for publication.
Mention of trade names of commercial products does not constitute
endorsement or recommendation for use.
This document is available to the public through the National Technical
Information Service (NTIS), 5285 Port Royal Road, Springfield, VA 22161.
i i
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FOREWORD
Section 304(a)(l) of the Clean Water Act of 1977 (P.L. 95-217
requires the Administrator of the Environmental Protection Agency to
publish water quality criteria that accurately reflect the latest
scientific knowledge on the kind and extent of all identifiable effects on
health and welfare which might be expected from the presence of
pollutants in any body of water, including ground water. This document is a
revision of proposed criteria based upon a consideration of comments
received from other Federal agencies, State agencies, special interest
groups, and individual scientists. Criteria contained in this document
replace any previously published EPA aquatic life criteria for the same
pollutants.
The term "water quality criteria" is used in two sections of the
Clean water Act, section 304 (a)(l) and section 303 (c)(2). The term
has a different program impact in each section. In section 304, the
term represents a non-regulatory, scientific assessment of ecological
effects. Criteria presented in this document are such scientific assess-
ments. If water quality criteria associated with specific stream uses are
adopted by a state as water quality standards under section 303,
they become enforceable maximum acceptable pollutant concentration in
ambient waters within that state. Water quality criteria adopted in
State water quality standards could have the same numerical values as
the criteria developed under section 304. However, in many situations
States might want to adjust water quality criteria developed under section
304 to reflect local environmental conditions and human exposure patterns
before incorporation into water quality standards. It is not until
their adoption as part of State water quality standards that the criteria
become regulatory.
Guidelines to assist the States in the modification of criteria
presented in this document, in the development of water quality standards,
and in other water-related programs of this Agency, have been developed by
EPA.
Martha G. Prothro
Director
Office of Water Regulations and Standards
111
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ACKNOWLEDGEMENTS
Don C. Miller David J. Hansen
(saltwater author) (saltwater coordinator)
U.S. Environmental Protection Agency U.S. Environmental Protection Agency
Environmental Research Laboratory Environmental Research Laboratory
South Ferry Road south retry Road
Narragansett, Rhode Island 02882 Narragansett, Rhode Island 02882
IV
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CONTENTS
Foreword iii
Acknowledgements iv
Tables vi
Introduction 1
Acute Toxicity to Saltwater Animals 7
Chronic Toxicity to Saltwater Animals 14
Toxicity to Aquatic Plants 17
Other Data 18
Unused Data 22
Summary 24
National Criteria 27
References 48
v
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TABLES
1. Acute Toxicity Of Ammonia to Saltwater Animals 32
2. Chronic Toxicity of Ammonia to Aquatic Animals 39
3. Ranked Genus Mean Acute Values with Species Mean Acute-
Chronic Ratios 43
4. Other Data on Effects of Ammonia on Saltwater Organism 45
VI
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INTRODUCTION*
in aqueous solutions, the ammonium ion dissociates to un-ionized ammonia
and the hydrogen ion. The equilibrium equation can be written:
H2O + NW+ J • NH3 + H3O+ (1)
The total ammonia concentration is the sum of NH3 and NH4+.
The toxicity of aqueous ammonia solutions to aquatic organisms is
primarily attributable to the un-ionized form, the ammonium ion being less
toxic (Armstrong et al. 1978; Chipman 1934; Tabata 1962; Thurston et al.
1981; Wuhrmann et al. 1947; Wuhrmann and Woker 1948). It is necessary,
therefore, to know the percentage of total ammonia which is in the un-ionized
form in order to establish the corresponding total ammonia concentration
toxic to aquatic life. The percentage of un-ionized ammonia (UIA) can be
calculated from the solution pH and pKa , the negative log of stoichiometric
dissociation,
* -1
% UIA = 100 [ 1 + 10 ((pKa " pH)] (2)
The stoichmetric dissociation constant is defined:
[NH3] [H+]
(3)
[NH4+]
where the brackets represent molal concentrations. Ka is a function of the
temperature and ionic strength of the solution.
An understanding of the "Guidelines for Deriving Numerical National
Water Quality Criteria for the Protection of Aquatic Organisms and Their
Uses" (Stephan et al. 1985), hereafter referred to as the Guidelines, and the
Response to public Comment (U.S. EPA 1985c), is necessary in order to
understand the following text, tables, and calculations.
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Whitfield (1974 developed theoretical models to determine the pKa of
the ammonium ion in seawater. He combined his models with the infinite
dilution data of Bates and Pinching (1949) to define general equations for
the pKa of ammonium ion as a function of salinity and temperature.
Whitfield's models allow reasonable approximations of the percent un-
ionized ammonia in sea water and have been substantiated experimentally by
Khoo et al. (1977). Hampson's (1977) program for Whitfield's full seawater
model has been used to calculate the un-ionized ammonia fraction of measured
total ammonia concentrations in toxicity studies conducted by EPA and also in
the derivation of most other acute and chronic ammonia values which
contribute to the criteria. The equations for this model are:
% UIA = 100 [ 1 + 10 (X + 0.0324 (298-T) + 0.0415 P/T - pH)]"1 (4)
where
P = 1 ATM for all toxicity testing reported to date;
T - temperature (°K);
X = pKas or the stoichiometric acid hydrolysis constant of ammonium ions in
saline water based on I,
I = 19.9273 S (1000-1.005109 S)"1 (5)
where
I = molal ionic strength of the sea water;
S = salinity (g/kg).
The Hampson program calculator the value for I for the test salinity (Eq. 5),
finds the corresponding pKas, then calculates % UIA (Eq. 4).
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The -ra^cr factcrs ir.fluer.cir.g the degree -f anaacr.ia disscciaticn are ;H
and temperature. 3oth correlate positively with '.^n-icnized ammonia.
Salir.ity, the least influential of the three water quality factors that
control the fraction of un-ionized ammonia, is inversely correlated.
In ammonia toxicity testing, the pH is normally calibrated using low
ionic strength National Bureau of Standards (NBS) buffers. In contrast,
Khoo et al. (1977) used the free hydrogen ion sea water scale (ph(FM in
their measurements of ammonium ion hydrolysis in sea water, while the pn(F)
scale is desirable from the thennodynamic standpoint, these seawater buffers
are not available from a central source, precluding their use in toxicity
testing. Calibration of pH with NBS buffers does contribute an error in the
calculation of \ un-ionized annonia, although, fortuitously the error is
small, presumably due to a compensation of the liquid junction potential by
changes in activity coefficients (Bates and Culberson 1977). Millero (1986)
found the pH(NBS) scale to overestimate pH relative to the free hydrogen ion
scale by 0.02 pH unit at 30 g/xg salinity, 0.045 unit at 20 g/xg and 0.075
unit at 10 g/xg. The residual junction potential is a property of the
reference electrode used and may vary + 0.03 pH unit with salinity, time, and
electrode type (Whitfield et al. 1985).
controlling pH in salt water ammonia toxicity tests is difficult.
Ammonium salt solutions are acidic, but are slow to reach equilibrium in sea
water. Consequently, pH typically declines during toxicity tests and the
decline may b« amplified by metabolism of test organisms. Also, tests
conducted above or below the seawater equilibrium pH (7.8-8.2) experience
strong shifts toward the buffered state. Inconsistency in degree of control
of test pH is a major source of variability in ammonia toxicity studies
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especially :n sea vater. A * T.l pH ur.it variance wculd resume :n a
nusesciaation of the NH- effect concentration of about * 25% at pH 8 and
25«C.
A number of analytical methods are available for direct detenu nation of
total ammonia concentrations in aqueous solutions (Richards and Healey 1984).
Once total amneria is measured, and the pH, salinity and temperature of the
solution dete; the concentration of NH^ present can be calculated based
on the amaonia-seawaier equilibrium expression.
AnBonia concentrations have been reported in a variety of forms in the
aquatic toxicity literature, such as NH^, NH4*, NHj-N, NH4
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ature, and salinity data to enacle calculation of NTi concentrations; sucn
papers were not used but are cited under "'Jnused Data". In some instances
information missing in published papers on experimental conditions was
obtained through correspondence with authors; data obtained in this manner
are so indicated by footnotes and are available from U.S. EPA, ERL,
Narragansett.
A number of criteria documents, review articles and books dealing with
ammonia as an aquatic pollutant are available. Armstrong (1979), Becker and
Thatcher (1973), Colt and Armstrong (1981), Epler (1971), Hampson (1976),
Liebmann (1960), McKee and wolf (1963), Steffens (1976), and Tsai (1975) have
published summaries of ammonia toxicity. Literature reviews, including
factors affecting ammonia toxicity and physiological consequences of ammonia
toxicity to aquatic organisms, have been published by Kinne (1976), Lloyd
(1961), Lloyd and Herbert (1962), Lloyd and Swift (1976), Vise* (1968), and
Warren (1962). Literature reviews of ammonia toxicity information relating
to criteria recommendations have been published by Alabaster and Lloyd
(1980), European Inland fisheries Advisory Commission (1970), National
Academy of Sciences and National Academy of Engineering (1974), National
Research Council (1979), U.S. Environmental Protection Agency (1976, 1980,
1985a), U.S. Federal voter Pollution Control Administration (1968),
willinghaa (1976), and Willinghaa et al. (1979).
The criteria presented herein supersede previous saltwater aquatic life
water quality criteria for ammonia because these new criteria were derived
using improved procedures and additional information. Whenever adequately
justified, a national criterion may be replaced by a site-specific criterion
(U.S. EPA 1983a), which may include not only site-specific criterion
5
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concentrations and siixing zone considerations .U.S. EPA, 1983b), but also
site-specific durations of averaging periods and site-specific frequencies
of allowed exc*«d«nces (U.S. EPA 1985b). This criterion does not apply to
saltwater lake*. These water bodies may require development of site-
specific water quality criteria. The latest comprehensive literature
search for information for this document was conducted in June, 1986; s
more recent information has been included.
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ACUTE TOXICITY TO SALTWATER ANIMALS
The acute toxicity of ammonia to saltwater animals has been studied in
crustaceans, bivalve mollusks, and fishes. Acute values are summarized in
Table 1 for 21 species in 18 genera. The winter flounder, Pseudopleuronectes
americanus. represents the most sensitive gems, with a Species Mean Acute
Value (SMAV) of 0.492 (Cardin 1986). Fourteen (eight fish, five crustaceans
and one mollusc) of the remaining 17 genera have Genus Mean Acute Values
within the order of magnitude of that for the winter flounder. The three
most tolerant species are mollusks. The SMAVs are 19.1 mg/L for the Eastern
oyster, Crassostrea virginica. 5.36 mq/L for the quahog clam, Mercenaria
mercenaria. and 3.08 mg/L for the brackish water clan, Rangia cuneata.
Except for these mollusks, there is no phyletic pattern in acute sensitivity
to ammonia. Fishes and crustaceans are well represented among both the more
sensitive and the more tolerant species tested.
Few consistent trends or patterns are evident in the acute toxicity
values cited in Table 1 with respect to biological or environmental vari-
ables. Contributing to this, in part, is test variability. This is evident
in multiple tests with the same species, even when conducted under closely
comparable conditions. Variability in acute toxicity values for ammonia may
reflect differences in coalition of the test organisms, changes in the
exposure conditions during testing, particularly pH, and variance incurred
through calculation of un-ionized ammonia concentrations. As noted in the
Introduction, pH has a strong influence on the concentration of un-ionized
ammonia in water, such that a variation of ± 0.1 pH unit during the test my
result in ± 25% variation in the NH3 exposure concentration. The NH3
exposure concentrations are calculated values dependent on accurate
7
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measurement of exposure pH. However, pH monitoring during a test may not
always detect potentially significant pH excursions. Also, non-systematic
errors on the order of ± 0.03 pH unit may also occur with seawater pH
measurements due to variation in the liquid junction potential between and
within electrode pairs. In addition to these sources of error,
interpretation of test results should consider known replicability of
toxicity tests. Intra- and inter-laboratory comparisons of acute toxicity
test results using saltwater species show LC50s may differ by as much as a
factor of two for the same chemical tested with the same species (Hansen
1984; Schimmel 1986). In light of all these sources of variability, LC50s
for un-ionized ammonia are in this document considered similar unless they
differ by at least a factor of two.
Few marked differences are evident in the acute toxicity of ammonia with
respect to differences in life stage or size of the test organism. Yolk-sac
larval striped bass (Morone saxatilis) seem slightly less sensitive to un-
ionized ammonia (LC50s - 0.70 and 1.09 mg/L) than 9 or 10 day old post-yolk
sac larvae (LC50s - 0.33 and 0.58 mg/L) (Poucher 1986). Juvenile striped
bass also seem less sensitive than post yolk-sac larvae (LC50s range from
0.91 to 1.66 mg/L) in tests by EA Eng. (1986) and Hazel et al. (1971). Acute
values for striped mullet (Mugil cephalus) suggest a factor of two decrease
in sensitivity (LC50 - 1.19 vs. 2.38 mg/L) to ammonia with increase in weight
from 0.7 to 10.Og (Venkataramiah et al. 1981). Larval grass shrimp
(Palaemonetes pugio) appear to be more acutely sensitive (LC50 - 1.06) (EA
Eng. 1986) than juveniles and adults (LC50 - 2.57) (Fava et al. 1984),
although the contrasting life stages were tested at different salinities. A
slight decrease in the acute sensitivity of Eastern oysters, Crassosrtrea
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virqinica, is evident r-etveen 13 and 1" TTO LCSC - 3.5 12 13 .ijg/1, and -il :c
52 am (LCSO - 24 to 43 rcg/L) Epifano and Srna 1975). No size related
difference in acute sensitivity to ammonia was seen between 4.7 to 5.2 aa and
28 to 32 ram quahog clans, (Mercenaria mercenaria) (Epifanio and Srna 1975).
Several data sets in Table 1 permit an evaluation of the influence cf
salinity, temperature and pH on the acute toxicity of ammonia to saltwater
animals. Few differences are evident in acute toxicity at different
salinities in tests with similar life stages and similar pH and temperature
conditions. Mysids (Mysidopsis bahia) have overlapping LCSOs at four
salinities in tests at pH > 7.8 and 25*C. At 10 to 11 gAg salinity, NH3
LCSOs range from 1.04 to 3.19 rag/L; at 20 gAg, 2.82 to 2.87 mg/L; at 30
gAg, 1.47 to 3.41 mg/L (Cardin 1986); and at 14 to 18 gAg, 0.92 to 1.68
mg/L HA Eng. 1986). At pH 7.0, the LCSO was lower at a low salinity by •
factor of 2.2 (Cardin 1986) (LCSO - 0.23 mg/L at 11 gAg; 0.50 and 0.54 mg/L
at 31 gAg salinity). Acute values for larval inland silversides (ttenidia
beryllina) tested at pH 8 and 25*C are approximately a factor of 2 lower at
11 gAg salinity with the LCSO • 0.88 mg/L, relative to 1.94 rng/L at 19 gAg
and 1.77 mg/L at 30 gAg salinity (Poucher 1986). However, at pH 7 and 9, the
LCSOs for these larva* are slightly higher at 11 gAg than at 31 gAg
salinity (by a factor of 1.7 and 1.5, respectively, comparing flow through
test values only). Atlantic silverside (Henidia menidia) juveniles at pH 8
and > 20*C have m? LCSOt ranging froa 0.97 to 1.24 mg/L at 9 to 10 gAg
salinity (A tog. 1986) which corresponds well with the 0.98 mg/L value
reported at 30 g/ltg salinity by Fava et al. (1984). Acute values overlap for
two fishes tested at low and high salinities by Hazel et al. (1971). For the
thre« spined stickleback (Gasterosteus aculeatus), LCSOs rang* froa 2.09 to
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;.~5 sg/l a- apprcxisateiv 11 ;.•
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Text Table 1.
Acute Toxicity of Ui-ionized AMonia to the Prawn (Macrobrachiua rosenber gi i ) . Mysid (Hysidopsis
larval Inland Silverside (Henidia becyllina). and Juvenile Atlantic Silverside (Henidi^TiiSUdiM
pH Conditions. Toxicity expressed as LC50, mq htK/L. Flow-through test results underlined,
and salinity condition* indicated.
PH
6.5-6.
7.0-7.
7.5-7.
8.0-8.
Praun
(Armstrong
et al. 1978)
28-C. 12 g/kg 24
9 0.38
4
9 0.95
4 1.3
Hysid
I Cardin
1966)
.5*C, llg/kg
-
0.28
1.18
1.04, 3.19
i Cardin
1986)
25"C, 31 gA9
-
0.50. 0.54
1.47
1.70. 2.49
(EA Eng.
1986)
20»C, 31 g/kg
-
0.27
0.40, 0.92,
1.0
0.76
Inland
Silverside
(Pouchec
1986)
25BC. 11 g/kg
-
1.64
—
0.88
Atlantic
(Pouchec (EA Eng.
1986) 1986)
25"C, 31 g/kg 22°C, 9.5 g/k.j
-
0.9i. 0.97, 0.97
1.06
1.40 l.OS, 1.12
1.77, 1.75 0.97, l.O/
OB, 3.41 1.10, 1.24
8.5-8.9 - - 2.76. 0.77 1.51, 1.68 - 1.08 1.47
9.0-9.4 - 2.02 - - 1.16 0.75, 0.49 1.21
11
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segregated =y the temperature ir.d salinity renditions cf tr.e tests to
preclude variability from these sources; LCSOs also are listed by author so
any interlaboratory variability rnay b« reccgnized. For the two invertebrate
species, the acute sensitivity to NH3 is greater (> factor 2) at low pH for
the prawn (pH 6.83) (Armstrong et al. 1978) and for the rnysid (pH 7.0)
(Cardin 1986; EA Eng. 1986), than at higher pH values. This response with
raysids was consistent at low and high salinity. The two fishes tested differ
from the mysid and prawn in their response to pH. Larval inland silverside
(Menidia beryllina) do show increased acute sensitivity to asnonia as pH
decreases from 8 to 7, but differ from the nysid response at pH 9.0, with
appreciably increased sensitivity (> factor of 2) in 31 g/kg salinity. In
contrast, in 11 g/fcg salinity water, inland silverside have a nearly two-
fold decrease in acute sensitivity at pH 7.0,while mysids have a two-fold
increase in acute sensitivity at pH 7.0. A further contrast exists in the
response of juvenile Atlantic silverside (Menidia aenidia), with test pH over
the range of 7.0 to 9.0 having little effect on the acute toxicity of
ammonia (EA Eng. 1986). The influence of pH on aaeonia toxicity in these two
saltwater fishes is also a marked contrast with the response of several
freshwater fishes (EricJcson 198S) and may reflect basic differences in
osmotic and ionic regulatory physiology which could influence their response
to elevated external aeaonia concentrations of over a range of pfl, salinity
and temperature condition*.
EPA believes that the data available on all water quality-toxicity
relationships for un-ionized amecrua are insufficient to conclude that any of
these factors, when acting alone, has a consistent major influence on NH3
toxicity in salt water. Therefore, a water quality dependent function was
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net derived f:r t.K.e rir.al Acuts value fcr _-.water ::ganisms and Knus ^
Acute values (Table 3) have fc-een used to calculate the Final Acute Value.
The 13 available saltwater Genus .M.ean Acute values range from 0.492
:ng NH3/L for Pseudopleuronectes to 19.102 mg NH3/L for Crassestrea, a factor
of less than 100. Acute values are available for more than one species in
three genera. The rang* of Species Mean Acute Values within two of these
genera is less than a factor of 1.2; in the remaining genus, they differ by a
factor of 4.5. Eighty-eight percent of the Genus Mean Acute Values were
within a factor of ten and 71 percent were a factor of five of the acute
value for Pseudopleuronectes. A saltwater Final Acute Value of 0.465 tag
NH,/L was obtained using the Genus Mean Acute Values in Table 3 and the
calculation procedure described in the Guidelines. This value is slightly
lower than Species Mean Acute Value of 0.492 tog/L for winter flounder.
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CHRONIC TOXICITY TO SALTWATER ANIMALS
Chronic toxicity tests have been conducted on ammonia with twelve
freshwater and saltwater species of aquatic organisms (Table 2). Of the ten
freshwater species tested, two are cladocerans and eight are fishes. The
details of the results of the freshwater tests are discussed in the "Ambient
Water Quality Criteria for Ammonia - 1984" (U.S. EPA 1985a). In saltwater, a
life-cycle toxicity test has been conducted with the mysid, Mysidopsis bahia.
and an early life-stage test has been completed with the inland silverside,
Menidia beryllina (Table 2).
The effect of ammonia on survival, growth and reproduction of M. bahia
was assessed in a life-cycle toxicity test lasting 32 days (Cardin 1986).
Survival was reduced to 35 percent of that for controls and length of males
and females was significantly reduced in 0.331 mg NH3/L. Although
reproduction was markedly diminished in this concentration, it did not differ
significantly from controls. Lengths of females were significantly reduced
in 0.163 mg/L, but this is not considered biologically significant since
reproduction was not affected. No significant effects on mysids were
detected at 0.092 mg/L. The chronic limits are 0.163 and 0.331 mg/L for a
chronic value of 0.232. The Acute Value from a flow-through test conducted
at similar coalitions (7.95 pH, 26.5°C, 30.5 g/kg salinity) with M. bahia is
1.70 mg/L which results in an acute-chronic ratio of 7.2 with this species.
The effect of ammonia on survival and growth of the inland silverside
(Menidia beryllim) was assessed in an early life-stage test lasting 28 days
(Poucher 1986). Fry survival was reduced to 40 percent in 0.38 mg NH3/L,
relative to 93% survival of control fish, which is a significant difference.
Average weights of fish surviving in concentrations > 0.074 mg/L were
14
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significantly less than weights of controls, an effect which persisted as the
concentration of ammonia increased. No significant effects were detected in
silversides exposed to 0.050 mg/L. Thus, the chronic limits are 0.050 and
0.074 mg/L for a chronic value of 3.061 mg/L. The acute value, derived as
the geometric mean of flow-through tests with this fish at full strength sea
water between pH 7.0 and 8.0, is 1.30 mg/L, resulting in an acute-chronic
ratio of 21.3.
Acute-chronic ratios are available for ten freshwater and two saltwater
species (Table 2). Ratios for the saltwater species are 7.2 for the mysid
and 21.3 for inland silversides. These saltwater species have similar acute
sensitivities to ammonia, with LC50s near the median for the 21 saltwater
species tested. The acute-chronic ratios for the freshwater species vary
from 1.4 to 53, so they should not be directly applied to the derivation of a
Final Chronic Value. Guidance on how to interpret and apply ratios from
tests with freshwater species to derive the freshwater criterion for ammonia
has been detailed in U.S. EPA 1985a which should be consulted. This document
concludes that: (1) acute-chronic ratios of freshwater species appear to
increase with decrease in pH; (2) data on temperature effects on the ratios
ace lacking; and (3) acute-chronic ratios for the most acutely and
chronically sensitive species are technically more applicable when trying to
define concentrationa chronically acceptable to acutely sensitive species.
Therefore, mean acute-chronic ratios were selected from freshwater tests with
species whose chronic sensitivity was less than or equal to the median
conducted at pH > 7.7. These included the channel catfish, with a mean
acute-chronic ratio of 10; bluegill, 12; rainbow trout, 14; and fathead
minnow, 20. The mean acute-chronic ratios for these four freshwater and the
15
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two saltwater species are within a factor of 3. The geometric mean of these
six values, 13.1, which divided into the Final Acute Value of 0.465 mg/L
yields the Final Chronic Value of 0.035 mg NH3/L.
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TOXICITY TO AQUATIC PLANTS
Nitrogen in the saltwater environment is an important nutrient affecting
primary production, the composition of phytoplankton, macroalgal and vascular
plant communities, and the extent of eutrophication. Ammonia is an important
part of nitrogen metabolism in aquatic plants, but excess ammonia is toxic to
saltwater plants (Table 4). Limited data on mixed populations of saltwater
benthic microalgae (Admiraal 1977) show that ammonia is more toxic at high
than at low pH (Admiraal 1977). This suggests that toxicity may be
primarily due to NH3 rather than NH4 .
Information on the toxicity of ammonia to saltwater plants is limited to
tests on ten species of benthic diatoms and on the red macroalgal species,
Champia parvula. A concentration of 0.247 mg NH3/L retarded growth of seven
species of benthic diatoms (Admiraal 1977). A concentration of 0.039 mg/L
reduced reproduction of Champia parvula gametophytes; no effect was observed
at 0.005 mg/L (Thursby 1986). Tetrasporophytes of C. parvula exposed to
0.005 to 0.026 mg/L for 14 days reproduced less but grew faster; no effect
was observed at 0.003 mg/L.
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OTHER DATA
A number of researchers have studied the effects of ammonia under test
conditions that differed from those applicable to acute and chronic test
requirements as specified in the Guidelines (Table 4). Animals studied
included rotifers, nemertine worms, echinoderms, mollusks, arthopods,
polychraetes, and fishes. Concentrations affecting the species tested are
generally greater than than Final Acute Value and are all greater than the
Final Chronic Value.
Among the lower invertebrates, Brown (1974) found the time to 50 percent
mortality of the nemertine worm, Cerebratulus fuscus. exposed to 2.3 mg NH3/L
is 106 minutes. In the rotifer, Brachionus plicatilis. the 24-hr LC50 is 20.9
mg NH3/L, the net reproduction rate was reduced 50 percent by 9.6 mg/L, and
the intrinsic rate of population increase was reduced 50 percent by 16.2
mg/L (Yu and Hirayama 1986).
In tests with mollusks, the rate of removal of algae (Isochryris
galbana) from suspension (filtration rate) was reduced > 50% during a 20-hr
exposure to 0.16 and 0.32 mg NH3/L in juvenile and adult quahog clan
(Mercenaria mercenaria) and to 0.08 mg/L in juvenile eastern oysters
(Crassostrea virginica) (Epifanio and Srna 1975). The rate of ciliary beating
in the mussel, Mytilus edulis. is reduced from 50 percent to complete
inhibition in < 1 hour by 0.097 to 0.12 mg/L (Anderson et al. 1978).
Excretion of ammonia is inhibited in channeled whelk (Busycon
canaliculatum). common rangia (Rangia cuneata). and a nereid worm (Nereis
succinea) exposed to sublethal concentrations of 0.37, 0.85 and 2.7 mg/L,
respectively (Mangum et al. 1978). The authors conclude that ammonia crosses
the excretory epithelium in the ionized form, ad that process is linked to
18
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Na+ and K+ ATPases. In the common bloodworm (Glycera dibrachiata). Sousa et
al. (1977) found no competition exists between NH3 and oxygen in binding
hemoglobin.
Ammonium chloride (about 0.01 mg NH3/L) exposure of unfertilized eggs
of the sea urchins, Lytechinus pictus. Strongylocentrotus purpuratus. and $L
drobachiensis increased the amount and rate of release of "fertilization
acid" above that occurring post-insemination (Johnson et al. 1976; Paul et
al. 1976). Exposure of unfertilized sea urchin (L. pictus) eggs to NH4C1
resulted in stimulation of the initial rate of protein synthesis, an event
that normally follow fertilization (Winkler and Grainger 1978). Activation
of unfertilized L. pictus eggs by NH4C1 exposure (ranging from 0.005 to 0.1
mg NH3/L was demonstrated by an increase in intracellular pH (Shen and
Steinhardt 1978; Steinhardt and Mazia 1973). Ammonia treatment activated
phosphorylation of thymidine and synthesis of histones in unfertilized eggs
of the sea urchin $L purpuratus (Nishioka 1976). Premature chromosome
condensation was induced by ammonia treatment of eggs of L^ pictus and $L
purpuratus (Epel et al. 1974: Krystal and Poccia 1979; Wilt and Mazia 1974).
Ammonium chloride treatment (0.01 mg NH3/L) of $L purpuratus and $L
drobachienris fertilized eggs resulted in absence of normal calcium uptake
following insemination, but did not inhibit calcium uptake if ammonia
treatment preceded insemination (Paul and Johnston 1978).
In exposures of crustaceans, the 7-day LC50 is 0.666 mg NH3/L for the
copepod, Euclaanus elongatus. while 38 percent of the E. pileatus died after
7 days in 0.706 mg/L, (Venkataramiah et al. 1982). No sargassum shrimp
(Latreutes fucorum) died after 21 days in < 0.44 mg/L (Venkataramiah et al.
1982). The EC50 bared on reduction in growth of white shrimp (Penaeus
19
-------
setiferus, after — ree veexs z: exposure is j.~: ag/L Wicxer.s .5"5 ' .
eight-day 1CSO is 1 . "9 :ng/L far the Amen ran iccster : Hotnarus
Delistraty et al. 1977). when blue crabs ( Callir.ectes sapiduai -w«re ncved
frcm water of 28 g/Vg salinity to water of 5 g/kg, a doubling of annonia
excretion rate occurred; addition of excess NH.C1 to the low salinity water
inhibited aaraonia excretion and decreased net acid output (Mangua et al.
1976). Wickins (1976) found that the time to 50 percent mortality for the
prawn, Kacrobrachi.ua rosenbergii, decreased from 1700 minutes at 1.7 rag/L to
560 minutes at 3.4 mg/L. In a six-week test with this prawn, growth was
reduced 32 percent at 0.12 mg/L (Wickins 1976).
The relationship between decrease in toxicity of un- ionized aanonia with
increase in pH seen in 96-hour tests with the prawn ( Maerobrachium
rosenbergii) is also exhibited in data froa tests lasting 24 and 144 hours
(Table 4) (Armstrong et al. 1978). Prawns were three tiaes more sensitive to
NH^ at pH 6.33 than at 7.6. Above pH 7.6, the decrease in acute toxicity was
not as great, declining only by a factor of 1.7 at pH 8.34. A similar effect
of low pH was seen with growth of the prawn, which after seven days at pH
7.60 was reduced in 0.63 og/L and at pH 6.83 by 0.11 ng/L (Armstrong et al.
1978).
few "other data" are available on the effects of aaaonia on saltwater
fishes (Table 4). In three saltwater tests lasting 24 hours, the LCSOs for
chinook salsna (Oncochynchua tshavytscha) ranged frca 1.15 to 2.19 ng NHyL
(Harader and Allan 1983). The 24-hr LCSOs froa two tests with Atlantic
salmon (Salao salar) were 0.115 and 0.28 og/L (Alabaster et al. 1979).
Mortality of the Atlantic silverside (Henidia menidia) was higher in 0.44
mg/L than the 43 percent control mortality in a 28-day early life-stage test
20
-------
EA Ir.g. 1586.. .he 96-hr 1C 50 fcr •-•hits cercn ."or:r.e aaeri:ara.' --as :.;
mg/L in a test at pH 5.3, althcugn this pH is rare in natural salt -Caters
i Stevenson 1977 ) .
21
-------
UNUSED DATA
Studies conducted with species that are not resident to North America
were not used (Alderson 1979; Arizzi and Nicotra 1980; Brown and Currie 1973;
Brownell 1980; Chin 1976; Currie et al. 1973; Greenwood and Brown 1974;
Inamura 1951; Nicotra and Arizzi 1980; Oshima 1931; Reddy and Menon 1979;
Sadler 1981; Yamagata and Niwa 1982). Other data were not used because
exposure concentrations were not reported for un-ionized ammonia and/or data
on salinity, temperature, and pH necessary to calculate NH3 concentrations
were not available (Binstock and Lecar 1969; Linden et al. 1978; Oshima 1931;
Pinter and Provasoli 1963; Pruvasoli and McLaughlin 1963; Sigel et al. 1972;
Sousa et al. 1974; Thomas et al. 1980; Zgurvskaya and Kustenko 1968). Data
of Hall et al. (1978) were not used since the form of ammonia reported in the
results is not stated. Data were also not used if ammonia was a component of
an effluent (Miknea 1978; Natarojan 1970; Okaichi and Nishio 1976: Rosenberg
et al. 1967; Thomas et al. 1980: Ward et al. 1982). Data reported by
Sullivan and Ritacco (1985) were not used because the pH was highly variable
between treatments. Data from a report by Curtis et al. (1979) were not used
because the salt tested, ammonium fluoride, night have dual toxicity. Data
reported by Katz and Pierro (1967) were not used because test exposure time
and salinity cited in the summary data table and appendix do not agree.
Results of a field study by Shilo and Shilo (1953, 1955) were not used since
the ammonia concentration was highly variable. The Ministry of Technology,
U.K. (1963) report was not used because the ammonia toxicity data were
previously published elsewhere and the relevant information is cited in this
document. References were not used if they relate more to ammonia
metabolism in saltwater species than to ammonia toxicity; e.g., Bartberger
22
-------
and Pierce, Jr. 1976; Cameron 1986; Girard and Payan 1980; Goldstein and
Forster 1961; Goldstein et al. 1964; Grollman 1929; Hays et al. 1977; McBean
et al. 1966; Nelson et al. 1977; Read 1971; Raguse-Degener et al. 1980;
Schooler et al. 1966; Wood 1958. Publications reporting the effects of
ammonia as a nutrient in stimulation of primary production were not used,
e.g., Byerrum and Benson (1975).
23
-------
SUMMARY
All of the following concentrations are un-ionized ammonia (NH3) because
NH3, not the ammonium ion (NH4 ), has been demonstrated to be the more toxic
form of ammonia. Data used in deriving the criteria are predominantly from
tests in which total ammonia concentrations were measured.
Data available on the acute toxicity of ammonia to 21 saltwater animals
in 18 genera showed LC50 concentrations ranging from 0.23 to 43 mg NH3/L.
me winter flounder, Pseudopleuronectes americanus. is the most sensitive
species, with a mean LC50 of 0.492 mg/L. The mean acute sensitivity of 88
percent of the species tested is within a factor of ten of that for the
winter fluunder. Fisher and crustaceans are well represented among both the
more sensitive and more resistant species; mollusks are generally resistant.
Water quality, particularly pH and temperature, but also salinity,
affects the proportion of un-ionized ammonia. With freshwater species, the
relationship between the toxicity of un-ionized and pH and
temperature is similar for most species and was used to derive pH and
temperature dependent freshwater criteria for NH3. For saltwater species,
the available data provide no evidence that temperature or salinity have a
major or consistent influence on the toxicity of NH3. Hydrogen ion
concentration does increase toxicity of NH3 at pH below 7.5 in some, but not
all species tested; above pH 8, toxicity may increase, decrease, or be little
altered as pH increases, depending on species.
The chronic effects of ammonia have been evaluated in tests with two
saltwater and ten freshwater species. In a life-cycle test with a myrid,
adverse effects were observed at 0.331 mg NH3/L but not at 0.163 mg/L. In an
early life-stage test with inland silverribs, adverse effects were observed
24
-------
at 0.074 mg/L NH3 but not at 0.050 mg/L. Acute-chronic ratios are available
for 12 species and range from 1.4 to 53. Ratios for the four most sensitive
freshwater species, tested at pH values greater than 7.7, and for the two
saltwater species tested, range from 7.2 to 21.3.
Available data on the toxicity of un-ionized ammonia to plants suggests
significant effects may occur in benthic diatoms exposed to concentrations
only slightly greater than those acutely lethal to salt-water animals.
Ammonia at concentrations slightly less than those chronically toxic to
animals my stimulate growth and reduce reproduction of a red macroalgal
species.
The key research needs that should be addressed in or&r to provide a
more complete assessment of toxicity of ammonia to saltwater species are:
(1) assess reported pH-toxicity relationships and test other species by
conducting additional acute toxicity tests using flow-through techniques and
continuous pH control both with and without pH acclimation; (2) determine the
effects of water quality variables on acute-chronic ratios by conducting
Life-cycle and early life stage tests with saltwater species; (3) investigate
temperature influence by additional acute toxicity tests with species that
can tolerate both low and high temperature extremes; (4) test the effects of
constant total ammonia exposure and cyclic water quality charger to mimic
potential tidal ad dial shifts in salinity and pH; (5) test the effects of
fluctuating and intermittent exposures with a variety of species; and (6)
investigate the total of other water quality variables on ammonia toxicity:
e.g., dissolved oxygen and chlorine; and (7) investigate the contribution of
NH4+ to the toxicity of aqueous ammonia solutions to better resolve how the
25
-------
ammonia criterion should be expressed if pH dependence continued to be
demonstrated.
2 6
-------
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, saltwater aquatic organisms should not be affected
unacceptably if the four-day average concentration of un-ionized ammonia does
not exceed 0.035 mg/L more than once every three years on the average and if
the one-hour average concentration does not exceed 0.233 mg/L more than once
every three years on the average. Because sensitive saltwater animals appear
to have a narrow range of acute susceptibilities to ammonia, this criterion
till probably be as protective as intended only when the magnitudes and/or
durations of excursions are appropriately mall.
Criteria concentrations based cm total ammonia for the pH range of 7.0
to 9.0, temperature range of 0 to 35°C, and salinities of 10, 20 and 30 g/kg
are provided in Text Tables 2 and 3. These values were calculated by
Hampson's (1977) program of Whitfield's (1974) model for hydrolysis of
ammonium ions in sea water.
Three years is the Agency's best scientific judgment of the average
amount of time aquatic ecosystem should be provided between excursions. The
ability of ecosystems to recover differ greatly.
Site-specific criteria may be established if adequate justification is
provided. This site-specific criterion may include not only sits-specific
criteria concentrations, and mixing zone considerations (U.S. EPA, 1983b),
but also site-specific durations of averaging periods and site-specific
frequencies of allowed exceedances (U.S. EPA 1985b).
27
-------
Use of criteria for developing water quality-based permit limits and
for designing waste treatment facilities requires the selection of an
appropriate wasteload allocation model. Dynamic models are preferred for the
application of those criteria (U.S. EPA 1985b). Limited data or other
considerations might make their use impractical, in which case one should
rely on a steady-state model (U.S. &PA 1986).
IMPLEMENTATION
Water quality standards for ammonia developed from then criteria should
specify use of environmental monitoring methods which are comparable to the
analytical methods employed to generate the toxicity data base. Total
ammonia may be measured using an automated idophenol blue method, such as
described by Technicon Industrial System (1973) or U.S. EPA (1979) method
350.1. Un-ionized ammonia concentrations should be calculated during the
dissociation model of Whitfield (1974) as programmed by Hampson (1977). This
program was used to calculate most of the un-ionized values for saltwater
organisms listed in Table 1 and 2 of this document. Accurate measurement of
sample pH is crucial in the calculation of the un-ionized ammonia fraction.
The following equipment and procedures were used by EPA in the ammonia
toxicity studies to enhance the precision of pH measurements in salt water.
The pH meter reported two decimal places. A Ross electrode with ceramic
junction was used due to its rapid response time; an automatic temperature
compensation probe provided temperature correction. Note that the
responsiveness of a new electrode may be enhanced by holding it in sea water
for several days prior to use. Two National Bureau of Standards buffer
solutions for calibration preferred for their stability were (1) potassium
28
-------
hydrogen phthalate (pH 4.00) and (2) disodium hydrogen phosphate (pH 7.4).
For overnight or weekend storage, the electrode was held in salt water,
leaving the fill hole open. For daily use, the outer half-cell was filled
with electrolyte to the fill hole and the electrode checked for stability.
The electrode pair MS calibrated once daily prior to measuring pH of
samples; it was never recalibrated during a series of measurements.
Following calibration, the electrode was soaked in sea water, of salinity
similar to the sample, for at least 15 minutes to achieve chemical
equilibrium and a steady state junction potential. When measuring pH, the
sample was initially gently agitated or stirred to assure good mixing at the
electrode tip, but without entraining air bubbles in the sample. Stirring
was stopped to read the meter. The electrode was allowed to equilibrate so
the change in meter reading was less than 0.02 pH unit/minute before
recording. Following each measurement, the electrode was rinsed with sea
water and placed in fresh sea water for the temporary storage between
measurements. Additional suggestions to improve precision of saltwater pH
measurements may be found in Zirno (1975), Grasshoff (1983), and Butler et
al. (1985).
29
-------
• atsr quality c
ia :c
Text Tads 2
' saltwater aquati
<--.,..,,, Maximum Concentrations
Criteria
cased on
ta
aamcr. i a
Tempe r ature
( 9C)
10
L5
20
25
30
35
£H
7.0
7.2
7 . 4
7.6
7.8
3.0
8.2
3.4
8.6
3.3
9.0
7.0
7.2
7.4
7.6
7.8
8.0
8.2
3.4
3.6
8.8
9.0
7.0
7.2
7.4
7.6
7.3
8.0
8.2
3.4
3.6
3.3
9.0
270
175
110
69
44
27
18
11
7.3
4.6
2.9
291
183
116
73
46
29
19
12
7.5
4.8
3.1
312
196
125
79
50
31
20
12.7
8.1
5.2
3.3
191
121
77
48
31
19
12
7.9
5.0
3.3
2.1
200
125
79
50
31
20
13
8.1
5.2
3.3
2.3
208
135
85
54
33
21
14
8.7
5.6
3.5
2.3
Sal
131
83
52
33
21
13
8.5
5.4
3.5
2.3
1.5
Sal
137
87
54
35
23
14
8.9
5.6
3.7
2.5
1.6
Sal
148
94
58
37
23
15
9.6
6.0
4.0
2.5
1.7
inity - 10
92
58
35
23
15
9.4
5.8
3.7
2.5
1.7
1.1
inity - 20 g
96
60
37
23
15
9.8
6.2
4.0
2.7
1.7
1.2
inity - 30 9
102
64
40
25
16
10
6.7
4.2
2.7
1.8
1.2
g/k,
62
40
25
16
10
6.4
4.2
2.7
1.8
1.2
0.85
/*9
64
42
27
17
11
6.7
4.4
2.9
1.9
1.3
0.87
/*9
71
44
27
21
11
7.3
4.6
2.9
2.0
1.3
0.94
44
27
17
11
7.1
4.6
2.9
1.9
1.3
0.92
0.67
44
29
18
11
7.5
4.8
3.1
2.0
1.4
0.94
0.69
48
31
19
12
7.9
5.0
3.3
2.1
1.4
1.0
0.71
29
19
12
7.7
5.0
3.1
2.1
1.4
0.98
0.71
0.52
31
20
12
7.9
5.2
3.3
2.1
1.5
1.0
0.73
0.54
33
21
13
8.5
5.4
3.5
2.3
1.6
1.1
0.75
0.56
21
13
3 . 3
5.6
3.5
2.3
1.5
1.0
0.75
0.56
0 .44
21
14
3.7
5.6
3.5
2 .3
1.6
1 . L
0.77
0.56
0. 44
23
15
9.4
6.0
3.7
2.5
1.7
1.1
0.81
0.53
0 .46
30
-------
•••'ate: quality criteria for
Text Tab.e 3
saitvater aquatic life cased en
Tia Continuous Concentrations
t e t a - a 2 3 c ~ 1
Tempe rature
10 15 20
25
30
£H
7.0
7.2
7.4
7.5
7.3
3.0
3.2
8.4
3.6
3.3
9.0
Sal ini ty
41
26
17
10
6.6
4.1
2.7
1.7
1.1
0.69
0.44
29
18
12
7.2
4.7
2.9
1.8
1.2
0.75
0.50
0.31
20
12
7.8
5.0
3.1
2.0
1.3
0.81
0.53
0.34
0.23
1
8
5
3
2
1
0
0
0
0
0
- 10 g/kg
4
.7
.3
.4
.2
.40
.87
.56
.37
.25
.17
9
5
3
2
1
0
0
0
0
0
0
.4
.9
.7
.4
.5
.97
.62
.41
.27
.18
.13
6
4
2
1
1
0
0
0
0
0
0
.6
.1
.6
.7
.1
.69
. 44
.29
.20
.14
.10
4 . 4
2.8
1.8
1.2
0.75
0.47
0.31
0.21
0.15
0.11
0.08
3.1
2.0
1.2
0 .84
0.53
0. 34
0.23
0.15
0.11
0.08
0.07
Salinity - 20 g/kg
7.0
7.2
7.4
7.6
7.8
3.0
3.2
3.4
3.6
3.8
9.0
44
27
18
11
6.9
4.4
2.8
1.8
1.1
0.72.
0.47
30
19
12
7.5
4.7
3.0
1.9
1.2
0.78
0.50
0.34
7.0
7.2
7.4
7.6
7.3
3.0
8.2
3.4
3.6
3.8
9.0
47
29
19
12
7.5
4.7
3.0
1.9
1.2
0.78
0.50
31
20
13
8.1
5.0
3.1
2.1
1.3
0.84
0.53
0.34
21
13
8.1
5.3
3.4
2.1
1.3
0.84
0.56
0.37
0.24
Salinity
22 1
14
8.7
5.6
3.4
2.2
1.4
0.90
0.59
0.37
14
9.0
5.6
3.4
2.3
1.5
0.94
0.59
0.41
0.26
0.18
- 30
5
9.7
5.9
3.7
2.4
1.6
1.0
0.62
0.41
0.27
9.7
6.2
4.1
2.5
1.6
1.0
0.66
0.44
0.28
0.19
0.13
11
0.26
0.19
6.6
4.1
3.1
1.7
1.1
0.69
0.44
0.30
0.20
0.14
6.6
4.4
2.7
1.7
1.1
0.72
0.47
0.30
0.20
0.14
0.10
4.7
3.0
1.9
1.2
0.78
0.50
0.31
0.22
0.15
0.11
0.08
3.1
2.1
1. 3
0 .34
0.53
0 . 34
0.24
0.15
0.12
0 .38
0.07
7.2
4.7
2.9
1.8
1.2
0.75
0.50
0.31
0.22
0.15
0.11
5.0
3.1
2.0
1.3
0.81
0.53
0.34
0.23
0.16
0.11
0.08
3 .4
2.2
1.4
0.90
0 . 56
0. 37
0
31
-------
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•- iS 11
1
4- 2S 11
2
CA En?
f* aV ft" n ii
LA fc II
-------
Spatia* l_jf« stag.
oi • i ta
Nynd. juvaaila
Nyndopiii bah i* i day old
Nyild. jiivaaila
My tidopi i i bah i a j day* aid
Nytid. )uvaaila
My* idoyi » i bahia 4 day aid
Nyild. Juvaaila
Ny»ld. juvaaila
Nyildoptii babia 1 day aid
Nyild. )ttvat>lla
Nyildoptii baa la < > day aid
Nactabi achiua ioaaabarj.il 1-1 day* aid
fi«t*a. laivia
N«c cobt ach i ua foiaabaioii 1-t days aid
Fiawa.. laivaa
Nacrabr *chiua rotanbatjii !-• day* aid
AB«I ica» lobttat, lacwa
Tbcaa sptaad *ticklab«ck. 12-40 M.
Tkcaa Bpiaad cticklaback. 12-aO Mi.
Oa*taca*tau* aculaatui
Tbraa apiaad aticklaback. 12-40 ••.
Tbraa apiaad aticklaback, 12-40 ••.
Taiaa apiaad it»cklab«tk. 12-40 ••.
Tbiaa *plaad *ticklab«ck, 12-40 •• .
Stiipad aullat, 0.4 9
Nuqi 1 i;»(>h* lu»
Cb*B. Ncthodk LC-iO oc SC-SO
(mn/L NN-1)
HH4C1 s.« J.«l
•M4C1 FT.H I Ql
•"M T*ap sal H«(*..nL.
• . /
* •" 24 11. S Caidta 1946
1.2
• '- 2S 11 Caidin 191k
'•0- 2S JO Cardin 194k
' i 1* 1 10.1 r.v. at *1 1914
' ••- 20 0 li Ouikaa* *t *1 1941
1.2
* •! 24 12 Acamtcoa^ »i al 1111
.2 A,..t,on, .t a, „„
••14 21 12 Acattion^ «t al 19)1
••1 21. t 11.4 Daliitcaty«tall*«;
7 SO- 21 "11 Hatal •( .1 19/1
7.7S
7 »S- 21 ~14 Hai»l .t at 19 11
7. tO
7 »1 21 -14 Nat.l .t al 1911
7 »4
7. IS- IS ~11 Mai.l .1 al 1911
7 t7
1.04- IS '14 Natal «l al .1911
0.11
1 II- IS "14 Max«l •( al 1911
0.24
0.00 21 0 10 V.Bkataiaaiab .C al 1 1
1.14 ii 0 10 U«nka(.«t .mi.tv .1 .1 1 1
-------
S p • C 1 • >
St i i|»«d nul 1 •« .
SC I ip*4 nul lat .
Muql 1 c«ph«lu»
Fla««h«a4 fllafiih.
Nonocnatbus kiiptdu*
Planah«ad fil«(l>b,
Monocantbut kitpi4u«
••4 dcua.
Scia«Aop« ocdlatu*
Atlantic tilvatsid*.
Hanl4ia •••|4|«
Atlantic ti|w«r»i4«,
Hcnldla •••444*
Atlantic »ilvar»ida,
H*nid4a •••444*
Atlantic tllv«r»id«.
Manldla ••nidi*
Atlantic »ilv*(»id*.
Atlantic ailvactida.
Atlantic tilvaciida.
N«n>44a •••444*
^:::;:c.::i:::"--
Atlantic »i|w«(*td*.
Hantdia aanidia
Inland »ilv«r*id«.
Lit* il*>J»
01 kit*
1 • 9
10 0 4
0.7 9
• « 1
••bcya-lai va
)wv«ni !•
]uw*n4l«
)uv«ni !•
juvanil*
)UV«*kl«
]uv«ntl*
)uv«nil«
juvani |«
juvani !•
juwnni !•
11.4 ••
lac*.
m,/L°MM-n * *"" I"? t^/iq» «•'•••«-•
""*M •.•« I.OJ 20.* 10.* EA Ena.191*
b
MM4CI S.H 1.J2 1.40 20 1 10 I EA Ln4 Ittt*
b
MM4C1 S.M 107 7 »» 200 »0 EAEa9IV4*
b
MH4C1 S.M 1 10 1 »* JO. 1 91 EAKitf l»l*
b
MM4C1 S.M 0.»7 1.00 24.1 » 7 EA LnS !«•*
ta
MM4C1 S.M 1.24 t.OO 20.2 10.2 EA City 111*
b
NN4C1 rr.H 1.04 l.*2 24.1 9.9 EA £119 l»i»
b
NM4C1 S.M 1.41 0-4 21 1 10 2 EA En? Ill*
b
HU4C1 S.H 1.21 • »• 21.1 10.1 tA tn-h»( IVtk
I I tt I
I !»• I
Hcntdt* t>««y 11 !«•
old
1. I
35
-------
S l> • c I • i
Li
Ifilftnd ktlw*iaitl*,
H*«tdt* b*iytlio«
Inland kilv*ikid*.
Notiidt* boiyllin*
l«l*0d ktlvOfBld*.
Nooidi* boiyllin*
lol**d kilvoitido.
Noaidt* bocylliB4
Intend tilv«c*id*.
Mooidt* bciyllio*
l*k*»d 4ilvoi4ido,
Nootdi* k>orvllia>
1 iil*od tilvoi4ldo,
Nofttdt* Bocw|l4*o.
lol*B.d ktlvoi*t«to,
MOKitft* Botytliao
lultod ttlvof4ido,
Nooidi* b*cyllio*
I»l40d 4ilvof»»do.
N*o.idl« b*cylliB4
lol*od t i 1 voisido.
NoOldt* BOfwIIlM*
lnl«od (tlwoitld*.
M*ntdl* bofwllin*
lnl*od kilwoi4>do.
Hooidt* boiyllia*
lat*«d »tlvoc*>do,
Hooidt* b«fyllt«4
Sh»op*b.o*d oiikoou,
Cypfioodo* v*tto94tuk
Shoop»h«*d o»«oow,
CyniiBOda* v*l>o^*tu*
Sh**p»k«*d •(•now.
CypitnodoH v*fi«q*luk
&h**i>kh»*d oinnow.
1
1
1
1
1
1
I
II
1
1
1
1
1
1
of k 1 IO
1 «l v* NU4C 1 f T. H
u«*k o 1 vl
i«!v« NiMci rr.M
wook old
l«iv« NM4C1 i.«
wook o 1 J
!•(«* NH4C1 S.M
wook old
l»fv» HH4C1 rr.M
wook old
l«fV. NM4C1 fT.M
wook 4 old
locv* MM4CI fT.M
wook old
I4IV* HM4C1 fT.M
• *•»• old
1«(«4 NH4C1 S.M
wook old
!•(«• MM4C1 PT.M
wook old
!«(«• MN4CI S,N
wook old
14IV4 MHtCl ri.N
wook old
t«|V* NH4C1 fT.M
wook old
l*f«4 NN4C1 S.M
wook old
«dult MH4C1 S.M
• dult NIMCI S.M
•dull NM4C1 S.M
«dull NU4CI S.H
UL-10 oi tC-ifl ,,H
(••J/L NM-1|
0 HI k »
)(
• . t
0 ». 4 »-
)i
•
1 04 10
i i
•
1 40 1.4-
} 4
*. f
• •• J •-
• 1
*.(
0 »« ) »-
1 . 1
*. t
i »4 7.a-
• -•
*.f
1 . 77 7.t-
• 1
•
1 . 74 7 t-
t 1
*, t
1.7* 7 »-
t. 1
•
1 01 • «-
14
• .f
1.14 • »-
t .1
».t
0. 74 1 . t-
« »
•
o.«» • o-
». 1
b
i. 71 7 91
b
1 . 14 1 »1
b
1 . »1 7.«*
b
1.17 7 »l
T**>|> S«l M*(*i*nL>
1 <• 1 IV/k>JI
14.4 it 4 Pouch*i IVIi.
144 10 Pouch*! I4lk
14.4 11 4 Pouch*i IVlt
14.0 11 Pouch*i t»lk
14 II Pouch*! 1 «*k
1* 10.4 Pouch*. 144k
^4 19 Pouch*i l»lk
14.4 10.4 Pouchci »»»6
1« i 11 Puuchci l*(6
11.4 10 Pouch*! l»l»
li 11 Pouch*i I»lk
14 11 0 Pouch*! 1914
14 10 Pouch*! 1*14
14 . 4 11.4 Pouch*! I«i4
10.1 » • EA Cnq I»t4
10 4 10 EA tn<| 1 Vtk
10 4 104 LA ti>4 l««k
1« • 10 * LA tns 14»k
modoo v«l I «<< t u>
36
-------
ip.cl.»
Sh**p»h*«d Binnow,
Sh**pkh*kd Binnow.
Sh**p«h*«d Binnow,
Cypiinidon v»ii*o,kluk
St c ip*d bkks .
HOI OB* kklkt 1 1 1 k
St i ip*d bkkk ,
Huion* kkiktilit
St i ip*d bkkk ,
Hoi on* kkikt i 1 ik
St i ip*d bkkk ,
NOf*B* kkMktlllk
SI t ip*d b*kk ,
HOIOB* kkkktlltk
St t ip*d b*kk .
Nat an* kkkkt 1 1 ik
Stiip*d bkkk,
Naion* k*kktllik
St i lp*d bk»« .
Macon* tkkktllik
St I lp*d bkkk ,
HOIOB* kkkktiltk
St i t p*d bkkk .
NOIOB* kkkktlllk
Hoion* k«k*t i 1 ik
Whit* BBICfc.
Noi*n* *B*«it«n»
Snot .
Lit* SI »1»
NM4C1 rr.n
NH4C1 fT.M
NH4C1 FT.M
NM4CI S.H
NM4C1 S.H
HM4CI S.H
•M4C1 S.H
NN4C1 S.H
MM4CI S.H
HH4C1 fT.M
HH4C1 S.N
HM4C1 fT.M
HN4C1 S.N
NM4CI S.H
MM4CI S.H
HM4C1 S.H
LC-40 or CC-40
IB9/L HH-lj
2 . 7« |
1
14 J
7
2.10 1
c
141 7
7
c
1 24 7
7
c
1 *4 7
7
c
10 •
c
c
1.4 •
• .11 7
7
1 .0* 7
0. 70 7
7
• .*• 1
7.
b
0 . »1 7 .
2.11 • .
b
1.04 7
,H
*. (
k-
k -
*. (
. 0-
. 1
4k-
42
. *0
. 71
.04-
Ok-
.11
04-
II
•.t
10-
. 11
4-
1
*.(
2-
t
24-
44
• 7
0
*2
|c) t 9/k>) )
24 10
12.4 12
11 12.4
14 "11
21 "11
21 11
14 -11
14 14
21 -14
21.4 4
II 4
20 4 4
II 4
20 10.2
1* 14
204 » 1
Mk( k 1 *I1L •
fuuch*! IVIb
Puucbki 1 94b
Pouchki l»lt
HkX*l »t *1 | oucn*i 141k
fuuchki IVIfe
Puuchci |>tlt
POUI-|>*I 1446
LA Ca^ . l«lk
St*v*nkoa Ml'
LX tny It to
L*IOItOBU§ «*BtBU»Uk
37
-------
Lit* &(« • • (•••w«l. N • ••••u(«d. U •
»
(«thar tk«« cut hoc »• •djw*t«d pM ««lu*».
•••ant* caaccat f «t io«« |tot*l. HMl-M. HM-H 01 •ft/L|.
calculated •• »• foot»at« c ustaf ••ItBtty, t«*|»(«tuf* *nd pM candltiont tuppkicd to tUL H by tb* *uthoi(»i
»
IUOM »f NCI added to co*t
-------
T.Ll. 1. Ch«on,c To.icity of A.nont* To Au^.tic Ani..l>
SMc...
Cl*duc«i*n.
C«i lodapbni • •ctnlhin*
Cl *doc*r an .
Dtphni* B«o,n*
Cl *doc*< *n ,
Cl cdoc •c«n.
Pink •AlBoa,
Pink •• laon .
Qncoi byncbu* aoibu«cb>
• * tnbow t iom ,
S« IBO 94 t idn«i i
• • inbow t rout ,
S«!BO 4*l(dB«lt
••inbow tfout,
»«!BO 9*1 ldB«r t
••inbow trout,
S«!BO 9-0.0441 0 104 Mount lt»2
174-0. 71i O.S17 Ku.mu .1 *li»«S
.M 0.74 0.41 gu>ku «t »1 Uli
-**"1-' 1-1 Hcinbold 4 V»<.it*lli uti
.0014-0.004 0 0011 lie. 4 B*ll.y lyiu
.0011-0.0014 0.0017 Bic. 4 B*il«y 1460
.010-0. Oii 0.014 C*l«B*n .1 «1 HI)
.0111-0. 0«1« 0.0111 Tbuitton *t *1 1VK
.04 upper llBlt <0.04 Ouikhaltai L. **y« nil
.04-0.11 0.045 Ouckhaltci 4 K>
.001-0.07 0.01 S.nylio i«k»
.044-0.144 0.11 Tnuiktun 1«46
.0*1-0.147 0 11 Thuikton lV4k
.14-0 14 0.11 Suio,«it 4 ii)*ci. 14*1
39
-------
Channel c«lJ t »h,
lct«luiu» punct *tii»
Cbannal c«tfi*b.
ELS
CLS
(•(••n tuafuh.
••ciocbiru*
do to»i«m
Mitiopt»m» dolo» «ut
Sa«llBoutb b**»,
MlCtopt««u»
Sacllaeutb b«»>.
»*
1 *-
1.0
1. 14-
1 »4
l.»
KLX 0.40
SL1 1.14
•LS 1.01
CLS 0.40
T..i,.,.tu,. s«linlty
< C'
Ch.on.c V.lu.
IS 0
a. oii-o.
o.ii-o
o.ii-o i»
Hi
21.1
11.1
0.014J-0 OSiO
0.120 0 Hi
0.411-0.1*0
0. 411-0. «»i
SALTWATCI
Nyctd.
My«ldoi»t»
LC
CLS
1.1-
0.0
l.t-
0.0
2&-11
us-
14 0
10
10-
11.4
0.1*1-0.111
o.a&o-o.oii
a 101
8 lt
o.ii
o.osa*
0.0411
0.110
O.S»9
O.*ll
0 111
0.0*1
H* ( • i «u.
Hob in* I t • 1 v it
Swt<]»it l.
Sat tb «i •! .
Oiudciiu* »c «1
• l oJ«i mi ml < 1
Foucbx
f oaic 0«tio
»P«ct«»
Cl«doc«r*a.
Acuc« V*lu«
IIH1I
Cbioaic V«lu«
•an
acantbin*
Cl»doc«f««.
cl«doc«r*B,
••an*
1-04
1 40
O.tl
0.104
0.411
0 41
14
41
14
40
-------
Acut. Value Chionic V.Iu.
'•9/1 ««>> l-q/L HH)|
Cl«doc«r«o,
Pink «•!•<>•. o 0»0 0. 001)
Oocoi hypchul jor butch*
rink ••laon, 0.040 8.0011
tiout, 0 4ii 0.0)11
29
tout. 0 Jl 0.01* jj
§•!•• i»ir4««i i
BIBBOW, 2 54 0.1) 20
r«tk)**4 •(••OM, i . S» 0.1) 20
1.71 0.22 t 0
cl catflih, 2.42 0.10) li
Ictgtuf uf fu«ct«tu»
Ch*na«l cctCtib. 1.§1 <0.2i «-)4
lct«luiu«
Ch«nii*l c*tr»h. 2.12 0.2«) 71
lct«luiu«
Ch«aa«l catfltk. LSI • l« « •
ict«tuiu»
£(••• •uali*h. 2. Ob 0.11 i 1
L«po»i » cy •••! tut
. l.Ot 0 0»2» 12
••ctgchi »u»
SB«liaouth b«ii. 0.11 0.0417 19
da to«t«m
^••llBouth b«n. 1.14 0.141 7 7
Mlc i
-------
Chi on
Htt I opt «f u»
17
« t «r
•i»v«i»i4«,
1 . !•
• Dkl
af
»lt - 10. •
(•t klu«^tlt« t)
(•t I«»BbaM tfaut - 14 (It It CLS »tu4y tnctudcd)
(•c Cathead •!•••« - ]0 (IS it fLS ttntfy mcl «
(•r aycid - 7 J
(ai
LC • lit* cycle, IL1 • ••fly liC«
fot d*t«il« coMC*c*ta« d»ftv«ttoB of
!*•&• Aabicat Watci Ou«lity Citt*(l« C«i
r««»
U.S.
Motional
. VA.
42
-------
T*Lle 1 Banked oenua riean Acute Valuea uith Specie* nean Acui e/Cb i on l <- Katioi
<••""» Specie* Mean Specie* N..II
^ Mean Acute v«|u. Acute Value Acute-Chionic
Henm I»9/L Ml* 1 ( Specie* I»«/L NMD Balio
•SALTWATER SftClLS
10 19.102 CaateiB ayttet. 1».I02
Cca»«o»ttea vli^inic*
II i J»0 Qu«boq claa, 4.1*0
14\ J - 00 BieckiBa) watei cles, l.Ot
IS l.tll Tbree-ipmed cttcklebeck. 2.»12
14 1.111 Sbeep«he«4 annaow, 2.111
1J 1.11 Lobetei. 2.21
1] 1*41 ««••• ••>!>•>. l.*41
>el»*»o»ietea pu^io
11
1.444
It 1.111 1«1»«4 ellveriide. 1.111 21
I.4SO
1.04 Spot. 1-04
K »»«tliuru«
1 .021
1.012 Stiiped belt. 0.4(1
Nateae »e»»ttIt«
Mklte p«ick." 2.11
0.*2» Copepod, •••*!
Cucelaoui eloaqetu*
0 7*1
tucel*nu» pilettui
-------
*•••"» !>|>*ct*t Nam
H..o Acuta v«lu. Acuta W.lu.
MHII Spaci.t ,
0.17) fi «wo , 0.77)
akciap, 0.77)
l«t t>ut«« tucatu*
••»p» oc«l i«tu»
Mtacac (Iound«(. 0.492
••( ic«nu»
• ••k*
(••ItBtty. t»BB*c*tUf«| «Bd uiiBf tk« fBB»Btrtc •••• ot LC40 v*lu*> (ai pM 7 «od •.
c
Acut*-CBceBic Batto c*lcul«t«d ((OB !••(* with llBllx •IBO«UI* p«t«B*t*(*
|»»lt>kly, DM. *ad t«ap«(«tuc«I
Saltw«t«i final *cnt« ¥«ly« - 0.4*4 B«/L HMl
• •Itwatal Ciit«ft«B HaiiBtiB Co»c»Bt i at to* • 0.4*1 B^/L/J - 0.2)1 Bo,/L ••)
fiBal »cttti»-Chi»Blc tatio • !••• t«»t I
Saltwatar fiBal Chianic Value » 0.441 B«/L|/l).l - 0 OJS B4/L MM)
-------
Table 4 Othe( Data on fcU.cti ot Annonia on Saltwater Oi^.niiBi
Dial OB,
Aaphipror* galudoia
OletOB.
6yro*|a,aa tpenceiii
OlatOB.
Mavicula arena(ia
OlatOB.
•avicula c (ypt ocephala
Diato«,
Mavicula aalinaiuB
Olatoa,
Mltttchia cloate(iuB
OiatOB,
Mltuchl* dl»»lp*ta
Diatoa,
Mltochia dubiforai*
DiatoB,
NltllChl* elan*
Diatoa,
Stauronei* constrict*
"°.J!!";.3"""M"'
... .„... -
• ot i f e( ,
•(tchionu* plicatilii
• ot i f e( .
•(achtonu* plicatill*
• ot i f e( .
•rachlonu* plicatili*
NeBei tine uo(B .
Ce( et>( etulu* fuicuv
MN4C1
HM4C1
M4C1
•N4C1
MM4C1
MH4CI
HH4C1
NM4C1
HN4C1
HM4C1
HH4C1
>. HM4C1
MM4CI
MM4C1
NM4C1
MM4M01
• 0 12 117 J-10 dayi
40 12 IS 0 1-10 days
4.0 12 11.7 1-10 dayi
40 12 IS.O 1-10 day*
•.0 12 15.0 1-10 days
1.0 12 11.7 1-10 dayi
4.0 12 11.7 1-10 day*
40 12 11.7 1-10 day*
4.0 12 IS.O 1-10 day*
4.0 12 11.7 1-10 day*
7.4-7.1 22-24 10 44 BOUCI
7.4-7.* 22-24 10 14 day*
21 22.4 24 koui4
4 S 21 22.4
4.1 21 22.4
79 IS 14 104 Bin*
t f ( • c 1 Coni-ent(aiiun H • ( • i • u L .
44% (eduction in 0.24) Adnitaal l«)J
44% (eduction in 0.24) AdBiiaal it 1 1
ckloiopByll a
2S% (eduction in 0.24) AdBiiaal itli
cnloi ophy 1 1 •
41% reduction in 1.014 Adaiiaal It 1 1
chluiophyll a
14% (eduction in 1.214 Adaiiaal nil
chlorophyll •
77% reduction in 1.214 Adniiatl 1111
chlorophyll a
42% reduction in 0.24) AJnica*! itll
chlorophyll *
71% reduction in 0.24) Ailaiia*! Itll
chlorophyll e
441 reduction in 0.241 Adaiiaal It 1 1
chlorophyll a
11% reduction in 0.247 Adaiiaal I'ill
chlorophyll •
(educed 0.0)9 Thuiiby 1»I6
reproduction.
BO effect at O.OOS
reduced O.OOS- Thuiaby 1*16
reproduction i 0.024
•tiaulated aroHth
•o effect at 0.001
LtSO 20 . » Yu and Ulilymm*
IK*
S0% (eduction in 14.2 »u and Hii*y<>«
population acovth 1144
net production 1*14
LTSO 2 . J Bl own 1114
45
-------
c h • B i <_ • l
PH T.Bp.mu,. S«l,nity Dui.l.on ttt.cl
Loni.*nt i .1 iun H.t.i.,,,.
HI U* BU« 1*1.
Ny t i 1 u» *dul t •
• 1 a* BUI t*l,
Ny t i lu> *dul i k
•lu* BUkl*l ,
Myl l lu» *dul IB
Cup. pott ,
Cuc*l*But *lona«tu*
Cop*pod ,
CUC*|*BUB pil**tu*
Hyiid.
MBit* •hl»*B.
t*B**UI •*tif*CUl
•(•MB ,
MAC robi •chiuB iot*Bb*(flt
"'"oh Ch • [0 *Bb*
Pt«WB,
N*c tobf *CBiuB fo«*ab*i4ii
PC*WB ,
Maccobr «chiuB io**nb*(^tt
N«c t ob( *ch t UB «t«*Bb*iati
PICWB ,
M*c robi *cn i UB co**Bb*catt
t(*MB ,
•r«MB ,
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-------
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