v>EPA
United States
Environmental Protection
Agency
Office of Water
Regulations and Standards
Criteria and Standards Division
Washington, DC 20460
EPA 440/5-8W01
January 1985
Water
Ambient
Water Quality
Criteria
for
Ammonia -1984
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AMBIENT AQUATIC LIFE WATER QUALITY CRITERIA FOR
AMMONIA
U.S. ENVIRONMENTAL PROTECTION AGENCY
OFFICE OF RESEARCH AND DEVELOPMENT
ENVIRONMENTAL RESEARCH LABORATORY
DULUTH, MINNESOTA
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DISCLAIMER
This reporc has been reviewed by che Criceria and Standards Division,
Office of Water Regulations and Standards, U.S. Environmental Protection
Agency, and approved for publication. Mention of trade names or commercial
products does not constitute endorsement or recommendation for use.
AVAILABILITY NOTICE
This document is available to the public through the National Technical
Information Service (NTIS), 5285 Port Royal Road, Springfield, VA 22161.
KJTHS f\^€fes«oNj Ov^mfeea - "V^QS-- 227 n 4.
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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 criteria
for water quality accurately reflecting the latest scientific knowledge on
the kind and extent of all identifiable effects on health and welfare which
may 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. The
criteria contained in this document replace any previously published EPA
aquatic life criteria.
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. The criteria
presented in this publication are such scientific assessments. Such water
quality criteria associated with specific stream uses when adopted as State
water quality standards under section 303 become enforceable maximum
acceptable levels of a pollutant in ambient waters. The water quality
criteria adopted in the State water quality standards could have the same
numerical limits as the criteria developed under section 304. However, in
many situations States may 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 the 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.
Edwin L. Johnson
Director
Office of Water Regulations and Standards
lii
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ACKNOWLEDGMENTS
Rosemarle C. Russo Russell J. Erickson
Environmental Research Laboratory Environmental Research Laboratory
Athens, Georgia Duluth, Minnesota
Clerical Support: Terry L. Highland
iv
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CONTENTS
Page
Foreword iii
Acknowledgments iv
Tables vi
Figures vii
Introduction I
Acute Toxicity to Aquatic Animals 7
Chronic Toxicity to Aquatic Animals 48
Toxicity to. Aquatic Plants 69
Bioaccumulacion 74
Other Data 75
Unused Data 86
Summary 90
National Criteria 94
Examples of Site-Specific Criteria 100
References 155
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TABLES
Page
1. Acute Toxicicy of Ammonia co Aquaeic Animals 105
2. Chronic Toxicicy of Ammonia co Aquacic Animals 129
3. Ranked Genus Mean Acute Values wich Species Mean Acuce-Chronic
Ratios 134
4. Toxicicy of Ammonia co Aquacic Planes 139
5. Other Daca on Effeccs of Ammonia on Aquacic Organisms 141
VI
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FIGURES
Page
1. Acuce NH3 Toxicicy at Different pH Values 35
2. Acuce NH3 Toxicicy at Different Temperatures 38
VII
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INTRODUCTION*
la aqueous ammonia solutions, un-ionized ammonia exists in equilibrium
with the ammonium ion and the hydroxide ion. The equation expressing this
equilibrium can be written as:
NH3(g) + nH20(^)^ NH3'rH20(aq)^NH4"1" + OH~ * (n-l)H20(^).
As indicated in this equation, the dissolved ammonia molecule exists in
hydrated form. The dissolved un-ionized ammonia is represented for
convenience simply as NH3« The ionized form is represented as NH^"1".
The term 'total ammonia* refers to the sum of these; I.e., NH3 + NH^+.
The toxlcity of aqueous ammonia solutions to aquatic organisms is
primarily attributable to the NH3 Species, with the NH^"1" species being
relatively less toxic (Chipman 1934; Wuhrmann et al. 1947; Wuhrraann and Woker
1943; Tabata 1962; Armstrong et al. 1978; Thurston et al. 1981c). It is,
therefore, important to know the concentration of NH3 in any aqueous
ammonia solution in order to determine what concentrations of total ammonia
are toxic to aquatic life.
The concentration of NH3 is dependent on a number of factors in
addition to total ammonia concentration (Skarheim 1973; Whitfield 1974;
Emerson et al. 1975; Thurston et al. 1979; Messer et al. 1984). Most
important among these are pH and temperature; the concentration of NH3
Increases with increasing pH and with increasing temperature. The ionic
strength is another important influence on this equilibrium. There is a
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, is neces-
sary In order to understand the following text, tables, and calculations.
1
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decrease in the percentage of un-ionized ammonia as the ionic strength
increases in hard water or in saline water. In most natural freshwater
systems the reduction of percent NH-j attributable to dissolved solids is
negligible. In saline or very hard waters there will be small but measurable
decreases in the percent Nt^.
A number of analytical methods are available for direct determination of
total ammonia concentrations in aqueous solutions. Once total ammonia is
measured, and the pH and temperature of the solution determined, the percent
of total ammonia originally present as NHj can be calculated based on the
ammonia-water equilibrium. A review of analytical methods for ammonia in
aqueous solution has been prepared by Richards and Healey (1984).
Emerson et al. (1975) carried out a critical evaluation of the
literature data on the ammonia-water equilibrium system and published
calculations of values of pKa at different temperatures and of percent
NH-j in ammonia solutions of zero salinity as a function of pti and
temperature. The following table, reproduced from Emerson et al. (1975),
provides values for percent NH^ at one-degree temperature intervals from 0
to 30 C, and pH Intervals of 0.5 pH unit from pH 6.0 to 10.0. An expanded
version of this percent NH3 table is provided inThurston et al. (1979),
which provides tabulated values of the NH3 fraction, expressed as
percentage of total ammonia, at temperature Intervals of 0.2 degree from 0.0
to 40.0 C, and pH intervals of 0.01 pH unit from pH 5.00 to 12.00. For
salt water, reports by Whitfield (1974) and Skarheim (1973) provide
calculations of MH3 as a function of pH, temperature, and salinity. Messer
et al. (1984) Indicate the impact of high total dissolved solids in
fresh water.
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Percent NHj in aqueous ammonia solutions for 0-30 C and pH 6-10.
Temp.
(0
0
1
2
3
4
5
6
7
8
9
10
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
26
27
28
29
30
6.0
.00827
.00899
.00977
.0106
.0115
.0125
.0136
.0147
.0159
.0172
.0186
.0201
.0218
.0235
.0254
.0274
.0295
.0318
.0343
.0369
.0397
.0427
.0459
.0493
.0530
.0569
.0610
.0654
.0701
.0752
.0805
6-75
.0261
.0284
.0309
.0336
.0364
.0395
.0429
.0464
.0503
.0.544
.0589
.0637
.0688
.0743
.0802
.0865
.0933
.101
.108
.117
.125
.135
.145
.156
.167
.180
.193
.207
.221
.237
.254
7.0
.0826
.0898
.0977
.106
.115
.125
.135
.147
.159
.172
.186
.201
.217
.235
.'253
.273
.294
.317
.342
.368
.396
.425
.457
.491
.527
.566
.607
.651
.697
.747
.799
7.5
.261
.284
.308
.335
.363
.394
.427
.462
.501
.542
.586
.633
.684
.738
.796
.859
.925
.996
1.07
1.15
1.24
1.33
1.43
1.54
1.65
1.77
1.89
2.03
2.17
2.32
2.48
PH
8.0
.820
.891
.968
1.05
1.14
1.23
1.34
1.45
1.57
1.69
1.83
1.97
2.13
2.30
2.48
2.67
2.87
3.08
3.31
3.56
3.82
4.10
4.39
4.70
5.03
5.38
5.75
6.15
6.56
7.00
7.46
8.5
2.55
2.77
3.00
3.25
3.52
3.80
4.11
4.44
4.79
5.16
5.56
5.99
6.44
6.92
7.43
7.97
8.54
9.14
9.78
10.5
11.2
11.9
12.7
13.5
14.4
15.3
16.2
17.2
18.2
19.2
20.3
9.0
7.64
8.25
8.90
9.60
10.3
11.1
11.9
12.8
13.7
14.7
15.7
16.8
17.9
19.0
20.2
21.5
22.8
24.1
25.5
27.0
28.4
29.9
31.5
33.0
34.6
36.3
37.9
39.6
41.2
42.9
44.6
9.5
20.7
22 1
23.6
25.1
26.7
28.3
30.0
31.7
33.5
35.3
37.1
38.9
40.8
42.6
44.5
46.4
48.3
50.2
52.0
53.9
55.7
57.5
59.2
60.9
62.6
64.3
65.9
67.4
68.9
70.4
71.8
10.0
45.3
47.3
49.4
51.5
53.5
55.6
57.6
59.5
61.4
63.3
65.1
66.8
68.5
70.2
71.7
73.3
74.7
76.1
77.4
78.7
79.9
81.0
82.1
83.2
84.1
85.1
85.9
86.8
87.5
88.3
89.0
[From Emerson et al. 1975; reoroduced with permission from the Journal of the
Fisheries Research Board of Canada.]
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Concentrations of ammonia have been reported in the aquatic toxicity
literature in terms of a variety of different forms, such as NH^j, NH^"1",
NH-j-H, NH^OH, NH^Cl, and others. The use in a literature article of
the terms NH^, NHj-N, or ammonia-nitrogen nay not necessarily mean
un-ionized ammonia, but may be the author's way of expressing total ammonia.
The use of the term NH^ in this document always means un-ionized ammonia,
and NH^-N means un-ionized ammonia-nitrogen.
Throughout the following, all quantitative ammonia data have been
expressed in terms of un-ionized ammonia, as mg/liter NH^, for ease in
discussion and comparison. Authors' ammonia concentration values are given
as reported if authors provided data expressed as mg/liter NH-j. If authors
reported only total ammonia values, or used concentration units other than
mg/liter, these were used with the reported pH and temperature values to
calculate mg/liter un-ionized NH-j. For calculations of NH-j in fresh
water the table of Thurston et al. (1979) was used. For calculations in salt
water the table of Skarheim (1973) was used.
Of the literature cited in this document, a significant number of papers
provided insufficient pU and temperature data to enable calculation of NH-j
concentrations; such papers were relegated to the section on "Unused Data"
unless they provided useful qualitative or descriptive information. 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.
Compounds used in the ammonia toxicity tests summarized here, and their
formulas and Chemical Abstracts Services (CAS) Registry Numbers, are given
below:
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Compound Formula CAS No.
Ammonia NH3 7664417
Ammonium acetate NH,^^!^ 631618
Ammonium bicarbonate NH^HCOij 1066337
Ammonium carbonate (NH4)2C03 506876
Ammonium chloride NH^Cl 12125029
Ammonium hydrogen phosphate (NH^^HPO^ 7783280
Ammonium hydroxide NH4OH (NH3'H20) 1336216
Ammonium sulfate (NH4)2S04 7783202
Papers stating use of other sources of ammonia were Included if the source
(e.g., excreted NH3 from fish) was deemed satisfactory. Papers using
complex chemicals (e.g., ammonium ferricyanide, decyltrimethylammonium
bromide) were not used. Finally, papers on ammonium compounds (e.g., NlfyF,
(NH^S)) having anlons that either might be themselves toxic or that
would preclude calculation of NH3 concentration from the aqueous ammonia
equilibrium relationship were not used.
A number of review articles or books dealing with ammonia as an aquatic
pollutant are available. Water quality criteria for ammonia have been
recommended in some of these. Liebmann (I960), McKee and Wolf (1963), Epler
(1971), Becker and Thatcher (1973), Tsai (1975), Hampson (1976), Steffens
(1976), Colt and Armstrong (1979), and Armstrong (1979) have published
summaries of ammonia toxicity. Literature reviews including factors
affecting ammonia toxicity and physiological effects of ammonia toxicity to
aquatic organisms have been published by Lloyd (1961b), Lloyd and Herbert
(1962), Warren (1962), Visek (1968), Lloyd and Swift (1976), and Kinne
(1976). Literature reviews of ammonia toxicity information relating to
criteria recommendations have been published by U.S. Federal Water Pollution
5
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Control Adminiscracion (1968), European Inland Fisheries Advisory Commission
(1970), National Academy of Sciences and Nacional Academy of Engineering
(1973), Willingham (1976), U.S. Environmental Protection Agency (1976, 1980),
National Research Council (1979), Willingham et al. (1979), and Alabaster and
Lloyd (1980).
The criteria presented herein supersede previous aquatic life water
quality criteria for ammonia (U.S. Environmental Protection Agency 1976)
because these new criteria were derived using more recent 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 concentrations (U.S. EPA, 1983b),
but also site-specific durations of averaging periods and site-specific
frequencies of allowed exceedences (U.S. EPA, 1985a). The latest literature
search for information for this document was conducted in May, 1984; some
newer information was also used; data frota primary references only were
used.
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ACUTE TOXICITY TO AQUATIC ANIMALS
Freshwater Invertebrates
Acute toxlclty of ammonia to freshwater invertebrate species has been
ouch less studied than that to fishes. The preponderance of available
invertebrate data is comprised of studies with arthropods, primarily
crustaceans and insects. LCSOs and ECSOs are summarized in Table 1 for 12
species representing 14 families and 16 genera.
The acute toxlcity of ammonia to Daphnia magna (Table 1) has been
studied by several investigators, with reported 43-hour LCSOs ranging from
0.53 to 4.94 mg/liter NH3 (Parkhurst et al. 1979, 1981; Reinbold and
Pescitelli 1982a; Russo et al. 1985).
Exposures (48 hours) of _D. magna to NH^Cl in dilution water from two
different sources were conducted by Russo et al. (1985). LCSOs (Table 1)
ranged from 2.4 to 2.8 mg/liter NH3 in water of pH 7.95 to 8.15 and
hardness 192 to 202 mg/liter as CaC03, and from 0.53 to 0.90 mg/liter NH3
in water of pH 7.4 to 7.5 and hardness 42 to 48 mg/liter as CaC03. On an
acute (48-hour LC50) basis, in dilution water from the same source,
Ceriodaphnia acanthina. Simocephalus vetulus, and J). magna all exhibited
similar sensitivities (Table 1) to ammonia (Mount 1982; Russo et al. 1985).
West (1985) reported a LC50 of 2.29 mg/liter NH3 for £. vetulus. The
48-hour LCSO (Table 1) of 1.16 mg/liter NH3 reported by DeGraeve et al.
(1980) for Daphnia pulicaria falls within the range of values reported for £.
magna. Anderson (1948) reported a threshold toxicity value (Table 5) for D_.
magna of 2.4 to 3.6 mg/liter NH3 in Lake Erie water. Threshold
concentration was taken to mean the highest concentration that would just
fail to immobilize the test animals under prolonged exposure (Anderson 1944).
A minimum lethal concentration of 0.55 mg/liter NH3 was reported for IK
7
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magna by telacea (1966), and a 24-hour LC50 of 1.50 mg/liter NH3 was
reported by Gyore and Olah (1980) for Moina rectirostris (Table 5).
Bulkema et al. (1974) reported an EC50 (Table 5) for NH3 toxictty to a
bdellotd rotifer, Philodina acuticornls, to be 2.9-9.1 mg/liter NH3
(calculated using reported pH values of 7.4 to 7.9). Tests of ammonia
toxicity to a flatworm, Dendrocoelum lacteam (Procotyla fluviatilis), and
tubificid worm, Tubifex tubifex, yielded LCSOs (Table 1) of 1.4 and 2.7
mg/liter NH3, respectively (Stammer 1953).
Thurston et al. (19S4a) conducted 25 flow-through toxicity tests with
three mayfly, two stonefly, one caddlsfly, and one isopod species; all tests
were conducted with water of similar chemical composition. Ninety-six-hour
LCSOs ranged from 1.8 to 5.9 mg/liter NH3 (Table 1). Results also
indicated that a 96-hour test is not long enough to determine the acutely
lethal effects of ammonia to the species tested-, inasmuch as an asymptotic
LC50 is not obtained within 96 hours. Percent survival data (Table 5) were
reported for some mayfly, stonefly, and caddisfly tests in which LC50s were
not obtained; 60 to 100 percent survival occurred at test concentrations
ranging from 1.5 to 7.5 mg/liter NH3- Gall (1980) tested NH4C1 with
Ephemerella sp. near excrucians. Organisms were exposed to ammonia for 24
hours, followed by 72 hours in ammonia-free water; mortality observations
were made at the end of the overall 96-hour period. An EC50 (Table 5) of 4.7
mg/liter HH3 was obtained. An LC50 (Table 1) of 8.00 mg/liter was reported
for the beetle (Stenelmis sexlineata) by Hazel et al. (1979). West (1985)
reported a 96-hour LC50 of 4.82 mg/liter NH3 for the mayfly Callibaetis
skolcianus and 10.2 mg/liter NH3 for the caddisfly Philarctus quaeris.
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Ammonia toxicity tests conducted using dilution water from the Blue
River in Colorado resulted in no mortalities of either scud (Gammarus
lacustris) or I), magna after 96 hours' exposure to 0.08 mg/liter NH3. In a
second test using river water buffered with sodium bicarbonate, 13 percent
mortality occurred with scud at several concentrations tested, including the
highest and lowest of 0.77 and 0.12 mg/liter NH3; seven and 13 percent
mortality occurred with D_. magna at the same concentrations (Miller et al.
1981).
Five freshwater mussel species (Amblema j>. plicata, Anodonta imbecillis,
Corbieula manilensia, Cyrtonaias tampicoensis, and Toxolasma texasensis) were
exposed for 165 hours (Table 5) to a concentration of 0.32 mg/liter NH3; T_.
texasensis was most tolerant to ammonia, and A. p_. plicata was most sensitive
(Home and Me In tosh 1979). During the ammonia tolerance tests, the more
tolerant species generally had their shells tightly shut, whereas the least
tolerant species continued siphoning or had their mantles exposed. West
(1985) reported 96-hour LCSOs of 1.59 to 2.49 mg/liter NH3 for the snail
Physa gyrina, 2.76 mg/liter NH3 for the snail Helisoma trivolvis, and 0.93
to 1.29 mg/liter NH3 for the clam Musculium transversum.
Acute exposures of the freshwater crayfish (Orconectes nais) to NH^l
gave LCSOs of 3.15 and 3.82 mg/liter NH3 (Evans 1979; Hazel et al. 1979).
West (1985) reported LCSOs of 22.8 mg/liter NH3 for the crayfish Orconectes
immunis. 1.63 to 5.63 mg/liter NH3 for the amphipod Crangonyx pseudo-
gracilis, and 4.95 mg/liter NH3 for the isopod Asellus racovitzai.
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Freshwater Fishes
Acuce coxicicy cescs wich freshwacer fish species have been conducced
wich 29 differenc species from 9 families and 18 genera, for which 96-hour
LCSOs are summarized in Table 1.
The acuce coxicicy of ammonia co rainbow crouc (Salmo gairdneri) has
been scudied by many invescigacors, wich reported 96-hour LCSOs ranging from
0.16 co 1.1 mg/licer NH3 (Table 1).
Thurscon and Russo (1983) conducced 71 coxicicy cescs wich rainbow crouc
ranging in size from sac fry «0.1 g) co 4-year-old adulcs (2.6 kg), in wacer
of uniform chemical composicion. LCSOs (Table 1) ranged from 0.16 co 1.1
mg/licer NHj for 96-hour exposures. Fish suscepcibilicy co NH3 decreased
wich increasing weighc over che range 0.06-2.0 g, buc gradually increased
above chac weighc range. LCSOs-for 12- and 35-day exposures (Table 5) were
noc greacly differenc from 96-hour values. No scaciscically significanc
differences in resulcs were observed when differenc ammonium sales [NH^Cl,
NH^HCC^, (NH^HPO^, (NH^^SO^ were used as che coxicancs. Grindley
(1946) also reporced observing no appreciable difference in coxicicy becween
coxicanc solucions of NtfyCl and (NH^^SO^ wich rainbow crouc cescs
(Table 5).
LCSOs (Table 1) ranging from 0.16 co 1.04 rag/licer NH3 for 96-hour
exposures of rainbow crouc Co ammonia were reporced by Calamari ec al. (1977,
1981), Broderius and Smich (1979), Hole and Malcolm (1979), DeGraeve ec al.
(1980), Reinbold and Pescicelli (1982b), and Wesc (1985). Ball (1967)
reporced an asyrapcocic (five-day) LC50 of 0.50 rag/licer Nl^. Acuce
exposures co ammonia of rainbow crouc of life scages ranging from one co 345
days' posc-fercilizacion (325 days posc-hacch) were conducced by Calamari ec
al. (1977, 1981). They reporced a cenfold increase in che speed of
10
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intoxication processes between the embryonic and free larval stages; embryos
and fingerlings (about one year old) were found to be less sensitive than the
other life stages studied.
LCSOs ranging from 0.49 to 0.70 mg/liter NH3 for 3-, 24-, and 48-hour
exposures (Table 5) were reported by Herbert (1961, 1962), Herbert and
Shurben (1964, 1965), and Herbert and Vandyke (1964). Rainbow trout (826
days old) subjected to 29.6 mg/liter NH3 reacted rapidly and strongly,
overturned within two to three hours, and died within four hours (Corti 1951)
(Table 5). Rainbow trout embryos and alevins were reported (Rice and Stokes
1975) to tolerate 3.58 mg/liter NH3 during 24-hour exposures;
susceptibility increased during yolk absorption, with the 24-hour LC50 for
85-day-old fry being 0.068 mg/liter NH3 (Table 5). Nehring (1962-63)
reported survival times of 1.3 and 3.0 hours at concentrations of 4.1 and 0.7
rag/liter NH3, respectively (Table 5). Danecker (1964) reported survival
times of 8 to 60 minutes at 0.4 to 4.0 mg/liter NH3, respectively, with
<0.2 mg/liter given as a no-mortality concentration (Table 5). Allan et al.
(1958) reported a median survival time of 1000 minutes at 0.18 mg/liter NH3
(Table 5).
An acute value of 0.2 mg/liter NH3 attributed to Liebmann (1960) has
been widely cited, in the EPA "Red Book" (U.S. Environmental Protection
Agency 1976) and elsewhere, as being the lowest lethal concentration reported
for salmonids* It is worthwhile to mention here a clarification and
correction that was published in the American Fisheries Society's "Red Book
Review" (Willingham et al. 1979): The research reported by Liebmann (1960)
was that of Wuhrmann and Woker (1948); recomputatlon of the Wuhrmann and
Woker data, using more accurate aqueous ammonia equilibrium tables, indicates
11
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an effect level of approximately 0.32 mg/liter NH3, not 0.2 mg/liter NH3
as cited by Liebmann.
A 96-hour LC50 of 0.44 mg/liter NH3 was reported for rainbow trout in
a test conducted using dilution water from the Blue River in Colorado (Miller
et al. 1981). Pitts (1980) conducted toxiclty tests using ammonium chloride
and river water. Tests were conducted with rainbow trout, and LCSOs ranged
from 0.2 to 0.9 mg/liter NH3 for 96-hour exposures at temperatures of 10
and 15 C.
Although acute toxicity studies with salmonids have been conducted
preponderantly with rainbow trout, some data are also available for a few
other salaonid species. Thurston et al. (1978) investigated the toxicity of
ammonia to cutthroat trout (Salmo clarki), and reported 96-hour LCSOs of 0.52
to 0.80 mg/liter NH3 (Table 1). Thurston and Russo (1981) reported a
96-hour LC50 of 0.76 mg/liter MH3 for golden trout (Salmo aguabonita)
(Table 1). Taylor (1973) subjected brown trout (Salmo trutta) to 0.15
mg/liter NH3 for 18 hours, resulting in 36 percent mortality (Table 5);
when returned to ammonia-free water, the test fish recovered after nearly 24
hours. No mortalities occurred during a 96-hour exposure at 0.090 mg/liter
NH3, although fish would not feed. Woker and Wuhrmann (1950) reported 0.8
mg/liter NH3 was not acutely toxic to brown trout (Table 5). A 96-hour
LC50 of 0.47 mg/liter NH3 was reported for brown trout tested using
dilution water from the Blue River in Colorado (Miller et al. 1981).
Phillips (1950) reported that brook trout (Salvellnus fontinalis) evidenced
distress within 1.75 hours at a concentration of 3.25 mg/liter NH3 and
within 2.5 hours at 5.5 mg/liter (Table 5). In replicated tests, Thurston
and Meyn (1984) reported 96-hour LCSOs (Table 1) of 0.60-0.70 mg/liter NH3
for brown trout, 0.96-1.05 mg/liter NH3 for brook trout, 0.40-0.48 mg/liter
12
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4-Day Average Concentration for Ammonia1
Salmonids or Other Sensitive Coldwater Species Absent
PH
PH
Un-ionized Ammonia (mg/liter NH3)
temperature Oe
5 10 15
20
25
Total Ammonia (ing/liter NH3)
temperature Oc
5 10 15 20
30
6.50
6.75
7.00
7.25
7.50
7.75
8.00
8.25
8.50
8.75
9.00
0.0008
0.0014
0.0025
0.0044
0.0078
0.0129
0.0149
0.0149
0.0149
0.0149
0.0149
0.0011
0.0020
0.0035
0.0062
0.0111
0.0182
0.021
0.021
0.021
0.021
0.021
0.0016
0.0028
0.0049
0.0088
0.0156
0.026
0.030
0.030
0.030
0.030
0.030
0.0022
0.0039
0.0070
0.0124
0.022
0.036
0.042
0.042
0.042
0.042
0.042
0.0031
0.0055
0.0099
0.0175
0.031
0.051
0.059
0.059
0.059
0.059
0.059
0.0031
0.0055
0.0099
0.0175
0.031
0.051
0.059
0.059
0.059
0.059
0.059
0.0031
0.0055
0.0099
0.0175
0.031
0.051
0.059
0.059
0.059
0.059
0.059
25
30
6.50
6.75
7.00
7.25
7.50
7.75
8.00
8.25
8.50
8.75
9.00
3.0
3.0
3.0
3.0
3.0
2.8
1.82
1.03
0.58
0.34
0.195
2.8
2.8
2.8
2.8
2.8
2.6
1.70
0.97
0.55
0.32
0.189
2.7
2.7
2.7
2.7
2.7
2.5
1.62
0.93
0.53
0.31
0.189
2.5
2.6
2.6
2.6
2.6
2.4
1.57
0.90
0.53
0.31
0.195
2.5
2.5
2.5
2.5
2.5
2.3
1.55
0.90
0.53
0.32
0.21
1.73
1.74
1.74
1.75
1.76
1.65
1.10
0.64
0.39
0.24
0.163
1.23
1.23
1.23
1.24
1.25
1.18
0.79
0.47
0.29
0.190
0.133
1 to convert these values to mg/liter N, multiply by 0.822
2 These values may be conservative, however, if a more refined
criterion is desired, EPA recommends a site-specific
criteria modification.
-------
4-Day Average Concentration for Ammonia1
Salmonids or Other Sensitive Coldwater Species Present
Un-ionized Ammonia (mg/liter NH3)
temperature Oe
10 15
20
25
30
PH
6.50
6.75
7.00
7.25
7.50
7.75
8.00
8.25
8.50
8.75
9.00
0
0
0
0
0
0
0
0
0
0
0
.0008
.0014
.0025
.0044
.0018
.0129
.0149
.0149
.0149
.0149
.0149
0
0
0
0
0
0
0
0
0
0
0
.0011
.0020
.0035
.0062
.0111
.0182
.021
.021
.021
.021
.021
0.0016
0.0028
0.0049
0.0088
0.0156
0.026
0.030
0.030
0.030
0.030
0.030
0
0
0
0
0
0
0
0
0
0
0
.0022
.0039
.0070
.0124
.022
.036
.042
.042
.042
.042
.042
0
0
0
0
0
0
0
0
0
0
0
.0022
.0039
.0070
.0124
.022
.036
.042
.042
.042
.042
.042
0.0022
0.0039
0.0070
0.0124
0.022
0.036
0.042
0.042
0.042
0.042
0.042
0.0022
0.0039
0.0070
0.0124
0.022
0.036
0.042
0.042
0.042
0.042
0.042
PH
Total Ammonia (mg/liter NH3)
temperature Oc
5 10 15 20 25
30
6.50
6.75
7.00
7.25
7.50
7.75
8.00
8.25
8.50
8.75
9.00
3.0
3.0
3.0
3.0
3.0
2.8
1.82
1.03
0.58
0.34
0.195
2.8
2.8
2.8
2.8
2.8
2.6
1.70
0.97
0.55
0.32
0.189
2.7
2.7
2.7
2.7
2.7
2.5
1.62
0.93
0.53
0.31
0.189
2.5
2.6
2.6
2.6
2.6
2.4
1.57
0.90
0.53
0.31
0.195
1.76
1.76
1.76
1.77
1.78
1.66
1.10
0.64
0.38
0.23
0.148
1.23
1.23
1.23
1.24
1.25
1.17
0.78
0.46
0.28
0.173
0.116
0.87
0.87
0.87
0.88
0.89
0.84
0.56
0.33
0.21
0.135
0.094
to convert these values to nig/liter N, multiply by 0.822
-------
UNITED STATES ENVIRONMENTAL PROTECTION AGENCY
WASHINGTON. D.C. 20460
JUL 301992
OFFICE OF
WATER
MEMORANDUM
SUBJECT: Revised Tables for Determining Average Freshwater
Ammonia Concentrations
FROM: Margarete Heber, Chief
Water Quality Criteria
Kent Ballentine, Chief f ...
Regulation and Policy Section (WH-585)
TO: Water Quality Standards Coordinators
The purpose of this memorandum is to provide you with a
recalculation of the freshwater ammonia tables for Criteria
Continuous Concentration, CCC (4 day average). These revised
tables have been recalculated by removing the controversial white
sucker data. Because the White Sucker was not one of the four
most sensitive organisms, the Criteria Maximum Concentration
remains the same as in the 1985 document.
Attached are the revised tables for determining the CCC for
freshwater ammonia. The Final Acute Chronic Ratio (FACR) was
calculated as in the 1985 ammonia criteria document except the
Acute Chronic Ratio (ACR) for the white sucker was not used in
determining the FACR. The white sucker data was removed because
for many of the data there were not an adequate dose response.
The FACR used is the geometric average of the ACR's of the
channel catfish, bluegill, rainbow trout and fathead minnow. The
result is that the FACR becomes 13.5 instead of the 16 as in the
original tables.
The result of these changes should address concerns over the
use of the white sucker data and result in a simplified
freshwater ammonia criteria. If you have any questions regarding
these changes please contact Margarete Heber at (202) 260-7144.
Attachments
Printed en RtcycltdPaptr
-------
NH3 for chinook salmon (Oncorhynchus tshawytscha), and 0.14-0.47 mg/liter
NH3 for mountain whitefish (Prosopium williamsoni).
Toxicicy tests (Tables 1, 5) on (NH4)2S04 with pink salmon
(Oncorhynchus gorbuacha) at different stages of early life stage development
(Rice and Bailey 1980) showed that late alevins near swim-up stage were the
moat sensitive (96-hour LC50 - 0.083 mg/liter NH^), and eyed embryos were
the most tolerant, surviving 96 hours at >1.5 mg/liter Nl^- Buckley (1973)
reported a 96-hour LC50 of 0.55 mg/liter ^3 for flngerling coho salmon,
Oncorhynchus kisutch (Table 1). Herbert and Shurben (1965) reported a
24-hour LC50 (Table 5) of 0.28 mg/liter NH3 for Atlantic salmon (Salmo
salar). A comparison of relative susceptibilities of salmon smolts and
yearling rainbow trout to 24-hour exposures to Nt^Cl showed that the salmon
ware appreciably more susceptible than the trout in fresh water (Ministry of
Technology, U.K. 1963).
Data are available on the acute toxicity of ammonia to a variety of
non-salmonid fish species. Thurston et al. (1983) studied the toxicity of
ammonia to fathead minnows (Piaephales promelas) of sizes ranging from 0.1 to
2.3 g; LCSOs from 29 tests ranged from 0.75 to 3.4 mg/liter NH3 (Table 1).
Toxicity was not dependent upon test fish size or source. LC50s ranging from
0.73 to 2.35 mg/liter NH3 (Tables 1,5) for fathead minnows were also
reported by Sparks (1975), DeGraeve et al. (1980), Reinbold and Pescitelli
(1982b), Swigert and Spacie (1983), and West (1985). Toxicity tests with
fathead minnows using ammonium chloride and river water yielded 96-hour LCSOs
ranging from 0.6 to 2.4 mg/liter Nt^; fathead minnows exposed to 0.12
mg/liter NH3 in river water for 28 days incurred no mortalities (Pitts
1980).
13
-------
LCSOs (Table 1) for white sucker (Catostomus commersoni) exposed to
ammonium chloride solutions for 96 hours (Reinbold and Pescitelli 1982c) were
1.40 and 1.35 tag/liter NH3; Swigert and Spacie (1983) determined a somewhat
lower 96-hour LC50 of 0.79 mg/liter NH3, while West (1985) reported LCSOs
of 0.76 to 2.22 mg/liter NH3 (Table 1). For mountain sucker (Catostomus
platyrhynchus), Thurston and Meyn (1984) reported LCSOs of 0.67-0.82 mg/liter
NH3 (Table 1).
Reported LCSOs (Table 1) for 96-hour exposures of bluegill (Lepomis
macrochirus) ranged fron 0.26 to 4.60 mg/liter NH3 (Emery and Welch 1969;
Lubinski et al. 1974; Roseboom and Richey 1977; Reinbold and Pescitelli
1982b; Smith et al. 1983; Swigert and Spacie 1983). LCSOs (Table 1) of 0.7
to 1.8 mg/liter NH3 for smallraouth bass (Micropterus dolomieui) and 1.0 to
1.7 mg/liter NH3 for largemouth bass (Micropterus salnoides) were reported
by Broderius et al. (1985) and Roseboom and Richey (1977), respectively, for
96-hour exposures. Sparks (1975) reported 43-hour LCSOs (in parentheses, as
mg/liter NH3) for bluegill (2.30) and channel catfish (2.92), Dowden and
Bennett (1965) reported a 24-hour LC50 for goldfish (Carassius auratus)
(7.2), and Chipman (1934) reported lethal threshold values of 0.97 to 3.8
mg/liter NH3 for goldfish (Table 5). Turnbull et al. (1954) reported a
48-hour LC50 for bluegill to be within the range 0.024 to 0.093 mg/liter
NH3 (Table 5); during the exposure they observed that the fish exhibited a
lack of perception to avoid objects.
Reported 96-hour LCSOs (Table 1) for channel catfish (Ictalurus
punctatus) ranged from 0.5 to 4.2 mg/liter NH3 (Colt and Tchobanoglous
1976; Roseboom and Richey 1977; Reinbold and Pescitelli 1982d; Swigert and
Spacie 1983; West 1985). Vaughn and Simco (1977) reported a 48-hour LC50 for
channel catfish of 1.24 to 1.96 mg/liter NH3, and Knepp and Arkin (1973)
14
-------
reported one-week LCSOs of 0.97 to 2.0 nig/liter NH3 (Table 5). From
studies with bluegill, channel catfish, and largemouth bass, Roseboom and
Richey (1977) reported that bluegill susceptibility was dependent upon fish
weight, with 0.07-g fish being slightly more sensitive than either 0.22- or
0.65-g fish; size had little effect upon channel catfish or bass
susceptibility.
LCSOs (Table 1) were determined with two species of field-collected
fishes indigenous to Kansas streams, orangethroat darter (Etheostoma
spectabile) and red shiner (Notropis lutrensis) (Hazel et al. 1979); 96-hour
LCSOs were 0.90 and 1.07 mg/liter NH3 for darter and 2.83 for shiner.
Commercially obtained largemouth bass, channel catfish, and bluegill (18 fish
of each species) were also exposed for 96 hours to a concentration of 0.21
mg/liter NH3, resulting in zero mortality for bluegill and channel catfish
and one mortality (6 percent) among the largemouth bass tested. Reported
LCSOs for walleye (Stizostedion vitreum) range from 0.51 to 1.10 mg/liter
NH3 (Reinbold and Pescitelli 1982a; West 1985).
LCSOs (Table 1) ranging from 2.4 to 3.2 mg/liter NH3 for (NH^CO^
NH4C1, NH4C2H302, and NH^OH, in 96-hour exposures of mosquitofish
(Gambusia affinis) in waters with suspended solids ranging from <25 to L400
mg/liter were reported by Wallen et al. (1957). Susceptibility of niosquito-
fish to ammonia was studied by Hemens (1966) who reported a 17-hour LC50 of
1.3 mg/liter NH3 (Table 5); he also observed that male fish were more
susceptible than females. Powers (1920) reported the relative suscepti-
bilities of three fish species to ammonium chloride to be (most sensitive to
least sensitive): straw-colored minnow (Notropis blennius) > bluntnose
minnow (Plmephales notatus) > goldfish.
15
-------
Rubin and Elmaraghy (1976, 1977) tested guppy (Pbecilia reticulata) fry
and reported 96-hour LCSOs (Table 1) averaging 1.50 mg/liter NH3; mature
guppy males vere more tolerant, with 100 percent survival for 96 hours at
concentrations of 0.17 to 1.58 mg/liter NH3. LC50s (Table 1) of 0.15 and
0.20 mg/liter NH3 at pH 6.0, and of 0.52 and 2.13 mg/liter NH3 at pH 8.0,
were reported by Stevenson (1977) for white perch (Morone americana). LCSOs
(96 hours) of 1.20 and 1.62 mg/liter NH3 for spotfin shiner (Notropis
spilopterus), and of 1.20 mg/liter NH3 for golden shiner (Notemigonus
crysoleucaa), were reported by Roaage et al. (1979) and Baird et al. (1979),
respectively. Swlgert and Spacie (1983) determined 96-hour LC50s to be 0.72
mg/liter NH3 for golden shiner, 1.35 mg/liter NH3 for spotfin shiner,
1.25 mg/liter NH3 for steelcolor shiner (Notropis whipplei), and 1.72
mg/liter NH3 for stoneroller (Campoatoma anomalma).
Jude (1973), Reinbold and Pescitelli (1982a), and McCormick et al.
(1984) reported 96-hour LCSOs ranging from 0.6 to 2.1 mg/liter NH3 for
green sunfish (Lepomis cyanellua) (Table 1). Pumpklnseed sunfish (Lepomis
gibbosus) were tested by Jude (1973) and Thurston (1981), with reported
96-hour LCSOs ranging from 0.14 to 0.86 mg/liter NH3. Mottled sculpin
(Cottus bairdi) were tested by Thurston and Russo (1981), yielding a 96-hour
LC50 of 1.39 mg/liter NH3 (Table 1). Ball (1967) determined an asymptotic
(six-day) LC50 (Table 5) of 0.44 mg/liter NH3 for rudd (Scardinius
erythrophthalams). He compared the asymptotic LCSOs for this species against
that obtained within two days for rainbow trout. Although the trout had
proven to be more sensitive to ammonia than had rudd during the first day of
the tests, the asymptotic LC50 for both species showed little difference.
16
-------
Rao ec al. (1975) reporced a 96-hour LC50 for carp (Cyprinus carpio) of
1.1 mg/licer NHj (Table 5). Carp exposed co 0.24 mg/licer NH^ exhibited
no adverse effeccs in 18 hours (Vamos 1963). Exposure co 0.67 mg/licer NH3
caused gasping and equilibrium discurbance in IS min, frenecic swimming
accivicy in 25 min, chen sinking co che cank boccom afcer 60 min; afcer 75
min che fish were placed in ammonia-free wacer and all revived. Similar
effeccs were observed ac a concencracion of 0.52 mg/licer NH3 (Table 5).
Pre-creacing fish orally wich 12.5 rag Suprascin (N-diraechyl-aminoechyl-N-p-
chlorobenzyl-a-aminopyridin hydrochlor), a chemical which reduces cell
membrane permeabilicy, somewhac reduced che coxic efface of ammonia.
A lechal concencracion (Table 5) for carp was reporced co be 7.5
mg/licer NH-j (Kempinska 1968). Acuce exposures (Table 5) co ammonium
sulface of biccerling (Rhodeus sericeus) and carp were conducced by Malacca
(1966), who decermined minimum lechal concencracions (i.e., afcer such
exposure, fish placed in ammonia-free wacer were unable co recover) of 0.76
rag/licer NHj for biccerling and 1.4 mg/licer NHj for carp. Nehring
(1962-63) reporced survival cimes of carp co be 2.4 and 6.0 hours ac NH^
concencracions of 9.7 and 2.1 mg/licer Nl^, respeccively (Table 5).
Danecker (1964) reporced survival cime for cench (Tinea cinca) co be 20 co 24
hours ac 2.5 mg/licer NH3 (Table 5). In a 24-hour exposure of creek chub
(Semocilus acromaculacus) co NH^OH solucion (Gillecce ec al. 1952), che
"critical range" below which all cesc fish lived and above which all died was
reporced co be 0.26 co 1.2 mg/licer NH3 (Table 5).
In scacic exposures lascing 9 co 24 hours, wich gradual increases in
NH3 concenc, lechal concencracions (Table 5) were decerained for oscar
(Ascronucus ocellacus) (Magalhaes Bascos 1954); morcalicies occurred ac 0.50
mg/licer NH3 (4 percenc) co 1.8 mg/licer (100 percenc). Tescs on oscar of
17
-------
two different sizes (average weights 1.6 g for "small" fish and 22.5 g for
"median" fish) showed no difference in susceptibility related to fish size.
A 72-hour LC50 (Table 5) of 2.85 mg/liter NH3 was reported by Redner and
Stickney (1979) for blue tilapia (Tilapia aurea).
Factors Affecting Acute Toxicity of Ammonia
There are a number of factors that can affect the toxicity of ammonia to
aquatic organisms. These factors include effects of dissolved oxygen
concentration, temperature, pH, previous acclimation to ammonia, fluctuating
or intermittent exposures, carbon dioxide concentration, salinity, and
presence of other toxicants. Almost all studies of factors affecting ammonia
toxicity have been carried out using only acute exposures.
(a) Dissolved Oxygen
A decrease in dissolved oxygen concentration in the water can increase
ammonia toxicity. Vcunos and Tastiadi (1967) observed mortalities in carp
ponds at ammonia concentrations lower than would normally be lethal, and
attributed this to periodic low concentrations of. oxygen. Based on research
in warawater (20-22 C) fish ponds, Selesi and Vamos (1976) projected a
"lethal line" relating acute ammonia toxicity and dissolved oxygen, below
which carp died. The line ran between 0.2 mg/liter NH3 at 5 mg/liter
dissolved oxygen and 1.2 mg/liter NH3 at 10 mg/liter dissolved oxygen.
Thurston et al. (1983) compared the acute toxicity of ammonia to fathead
minnows at reduced and normal dissolved oxygen concentrations; seven 96-hour
tests were conducted within the range 2.6 to 4.9 mg/liter dissolved oxygen,
and three between 8.7 and 8.9 mg/liter. There was a slight positive trend
between 96-hour LC50 and dissolved oxygen, although it was not shown to be
statistically significant.
18
-------
Alabaster et al. (1979) tested Atlantic salmon smolts In both fresh
water and 30 percent salt water at 9.6-9.5 and 3.5-3.1 mg/liter dissolved
oxygen. The reported 24-hour LCSOs at the higher oxygen concentrations were
about twice that at the lower. Recently, Alabaster et al. (1983) reported
freshwater LC50s for Atlantic salmon in 10.2 and 3.1-3.2 mg/liter dissolved
oxygen as 0.2 and 0.08 mg/liter NH^, respectively.
Several studies have been reported on rainbow trout. Allan (1955)
reported that below 0.12 mg/liter NH^ and at about 30 percent oxygen
saturation, the median survival time was greater than 24 hours, but at the
same concentration with oxygen saturation below 30 percent, the median
survival time was less than 24 hours. Downing and Merkens (1955) tested
fingerling rainbow trout at three different concentrations of NH^ at five
different levels of dissolved oxygen. They reported, in tests lasting up to
17 hours, that decreasing the oxygen from 3.5 to 1.5 mg/liter shortened the
periods of survival at all ammonia concentrations, and that a decrease in
survival time produced by a given decrease in oxygen was greatest In the
lowest concentration of NHj. Merkens and Downing (1957), in tests which
lasted up to 13 days, also reported that the effect of low concentrations of
dissolved oxygen on the survival of rainbow trout was more pronounced at low
concentrations of Nl^. Lloyd (1961a) found NH3 to be up to 2.5 times
more toxic wnen dissolved oxygen concentration was reduced from 100 to about
40 percent saturation. Danecker (1964) reported that the toxicity of ammonia
increased rapidly when the oxygen concentration decreased below two-thirds of
the saturation value.
Thurston et al. (1981b) conducted 15 96-hour acute toxicity tests with
rainbow trout over the dissolved oxygen range 2.6 to 8.6 mg/liter. They
19
-------
reported a positive linear correlation between 96-hour LC50 and dissolved
oxygen over the entire range tested.
Herbert (1956) reported on rainbow trout mortalities in a channel
receiving sewage discharge containing 0.05 to 0.06 tag/liter NH^. They
found that at 25-35 percent dissolved oxygen saturation more than 50 percent
of the fish died within 24 hours, compared with 50 percent mortality of test
fish in the laboratory at 15 percent dissolved oxygen saturation. The
difference was attributed to unfavorable water conditions below the sewage
outflow, Including ammonia, which increased the sensitivity of the fish to
the lack of oxygen.
There is a reduction in fish blood oxygen-carrying capacity following
ammonia exposure (Brockway 1950; Danecker 1964; Reichenbach-Kllnke 1967;
K3rting 1969a,b; Waluga and Flis 1971). Hypoxia would further exacerbate
problems of oxygen delivery and could lead to the early demise of the fish.
(b) Temperature
Information in the literature on the effecta of temperature on ammonia
toxicity is varied. The concentration of XH^ increases with increasing
temperature. Several researchers have reported an effect of temperature on
the toxicity of the un-ionized ammonia species, independent of the effect of
temperature on the aqueous ammonia equilibrium.
Hazel et al. (1971) tested ammonia with striped bass (Morone saxatilis)
and stickleback (Gasterosteus aculeatua) and found little difference in
toxicity between 15 and 23 C in fresh water, although both fish species were
slightly more resistant at the lower temperature. Erickson (1985) noted,
however, that Hazel et al. did not account for the effect of temperature on
ammonia equilibrium; when corrected, their data indicate both species to be
moderately more tolerant at the higher temperature. McCay and Vars (1931)
20
-------
reported that it took three times as long for brown bullheads (Ictalurus
nebulosus) to succumb to the toxicity of ammonia in water at 10-L3 C than at
26 C. The pH of the tested water was not reported; however, within the
probable range tested (pH 7-8), the percent NH-j at the higher test
temperature is approximately three times that at the mean lower temperature.
Powers (1920) reported the toxicity of ammonlun chloride to goldfish,
bluntnose minnow, and straw-colored minnow to be greater at high temperatures
than at low; however, in that study also no consideration was given to the
increase in relative concentration of NH-j as temperature Increased.
Thurston et al. (1983) reported that the acute toxicity of NH3 to
fathead minnows decreased with a rise in.temperature over the range 12 to
22 C. Bluegill and fathead minnow were tested at low and high temperatures
of 4.0 to 4.6 C and 23.9 to 25.2 C, respectively; rainbow trout were tested
at 3.0 and 14.0 C (Reinbold and Pescitelli 1982b). All three species were
,more sensitive to un-ionized ammonia at the low temperatures, with toxicity
being 1.5 to 5 times greater in the colder water;, bluegill appeared to be the
most sensitive of the three species to the effect of low temperature on
ammonia toxicity.
Colt and Tchobanoglous (1976) reported that the toxicity of Ntl3 to
channel catfish decreased with increasing temperature over the range 22 to 30
C. LCSOa for bluegill, channel catfish, and largemouth bass at 28 to 30 C
were approximately twice that at 22 C (Raseboora and Richey 1977). LC50s for
channel catfish tested in Iowa River water were 0.49 mg/liter NH3 at 2.5 C
and 0.56 mg/liter at 5.1 C (Miller and UNLV-EPA 1982). An effluent
containing ammonia as a principal toxic component showed a marked decrease in
toxicity to channel catfish over the temperature range 4.6 to 21.3 C (Gary
1976).
21
-------
Herbert (1962) has reported that experiments with rainbow trout in his
laboratory suggest that the effect of temperature on their susceptibility to
NH3 toxicity is little if at all affected by temperature change; no details
were provided. The Ministry of Technology, U.K. (1968), however, has
reported that the toxicity of NH^ to rainbow trout was jmch greater at 5 C
than at L8 C. Brown (1968) reported that the 48-hour LC50 for rainbow trout
increased with an increase in temperature over the range 3 to IS C; the
reported increase in tolerance between "12 to -18 C was considerably less
than that between -3 to -12 C. Thurston and Russo (1983) reported a
relationship between temperature and 96-hour LCSO for rainbow trout over the
temperature range 12 to 19 C; ammonia toxicity decreased with increasing
temperature.
Lloyd and Orr (1969) investigated the effect of temperature over the
range 10-20 C on urine flow rates of rainbow trout exposed to 0.30 mg/liter
NH3> and found no apparent temperature effect on the total diuretic
response of the fish, although the relative increase in urine production was
less at higher temperatures. From a study of the behavioral response of
blueglll to gradients of ammonia chloride it was hypothesized that low
temperatures increased the sensitivity of blueglll and interfered with their
ability either to detect ammonia after a certain period of exposure or to
compensate behaviorally for physiological stress caused by ammonia gradients
(Lubinski 1979; Lubinski et al. 1980).
The European Inland Fisheries Advisory Commission (1970) has cautioned
that at temperatures below 5 C the toxic effects of un-ionized ammonia may be
greater than above 5 C. The basis for such a statement is not clearly
documented in that report. Nevertheless, there is some merit to the argument
that a decrease in temperature may increase the susceptibility of fish to
22
-------
un-ionized ammonia toxlcity. It is important that this relationship be
further studied. The available evidence that temperature, independent of its
role in the aqueous ammonia equilibrium, affects the toxicity of NH} to
fishes argues for further consideration of the effect of temperature on the
toxicity of ammonia.
West (1985) investigated the seasonal variation of ammonia toxicity for
five species of fish. Marked and generally steady increases of LCSOs with
temperature were observed for rainbow trout from 3.6 to 13.7 C and for
channel catfish from 3.5 to 26 C. For fathead minnow, a similar trend was
found for temperatures from 12 to 26 C, but at 3.4 C, the LC50 was higher
than at 12 C. Similar trends were observed for walleye between 3.7 and 11 C
and for white sucker between 3.6 and 15 C, but both these species showed a
lower LC50 at a higher test temperature (19 C for walleye and 25 C for white
sucker); in both cases, however, this apparent deviation from trends for
other tests is confounded by different sizes of test organisms and, as with
the other species, by seasonal changes other than temperature; also, for the
white sucker test, the test at higher temperature suffered from low dissolved
oxygen. West also examined the seasonal dependence of ammonia toxicity to
three invertebrates (snail Physa gyrina, clam Musculium transversum, and
amphipod Crangonyx paeudogracilis). For all species, the maximum LC50 was at
Intermediate temperature (12-15 C), with lower values at colder and warmer
temperatures. For the two molluscs, the apparent variation with temperature
was not great, the minimum LC50 being only about 30% less than the maximum.
For the amphipod, the variation was two- to three-fold.
(c) pH
The toxicity to fishes of aqueous solutions of ammonia and ammonium
compounds has been attributed to the un-ionlzed (undissociated) ammonia
23
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present in the solution. Although there were observations in the early
literature that ammonia toxicity was greater in alkaline solutions, the
earliest reported thorough study of the pH dependence of ammonia toxicity was
that of Chipman (1934). He concluded from experiments with goldfish,
amphipods, and cladocerans that the toxicity was a function of pH and
therefore of the concentration of undissociated ammonia in the solution.
Wuhrraann et al. (1947) discussed the importance of differentiating
between ^3 and NH^* when considering ammonia toxicity. They
summarized some unpublished experimental data indicating a correlation
between solution pH and ammonia toxicity to fish (indicated by persistent
loss of balance). Wuhrnann and Woker (1943) reported on the experiments
referred to in Wuhrmann et al. (1947); these were conducted using ammonium
sulfate solutions at different pH values on rainbow trout. Either four or
six fish were tested at each of nine ammonium sulfate concentrations. The
authors concluded from the experimental results that NH^ was much more
toxic than NH^. Downing and Merkens (1955) tested rainbow trout at
different concentrations of ammonia at both pU 7 and 8. They reported a
consistency of results when ammonia concentration was expressed as NH^.
Tabata (1962) conducted 24-hour tests (Table 5) on ammonia toxicity to
Daphnia (species not specified) and guppy at different pH values and
calculated the relative toxicity of N^/NH^"*" to be 190 for guppy (i.e.,
NHj is 190 times more toxic than NH^"1") and 48 for Daphnia. From tests
of the toxicity of ammonium chloride to juvenile coho salmon in flow-through
bloassays within the pH range 7.0 to 8.5, the reported 96-hour LC50 for NHj
was approximately 60 percent less at pH 7.0 than at 8.5 (Robinson-Wilson and
Seim 1975).
24
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Armstrong et al. (1978) tested the toxicity of ammonium chloride to
larvae of prawn (Macrobrachium rosenbergii) in six-day tests within the pH
range 6.8 to 8.3; test solutions were renewed every 24 hours. They reported
a 96-hour LC50 for HU^ at pH 6.33 which was approximately 70 percent less
than that for pH 8.34. They concluded that the toxicity of ammonia was not
due solely to the UH^ molecule, that in solutions of different pH and equal
NH3 concentrations survival was greatly reduced as NH^"1" levels
increased. Tomasso et al. (1980) tested the toxicity of ammonia at pH 7, 8,
and 9 on channel catfish and reported that 24-hour NH3 LC50s were
significantly higher at pH 3 than at pH 7 or 9.
Thurston et al. (1981c) tested the toxicity of ammonia to rainbow trout
and to fathead minnows in 96-hour flow-through tests at different pH levels
within the range 6.5 to 9.0. Results showed that the toxicity of ammonia, in
terms of N^, increased at. lower pH values. They concluded that NH^*
exerts some measure of toxicity, and/or that increased H"*" concentration
increases the toxicity of Nf^*
Acute (96-hour) exposures of green sunfish and sraallmouth bass were
conducted by McConnick et al. (1984) and Sroderius et al. (1985) at four
different pH levels over the range 6.5 to 8.7. For both species, NH3
toxicity increased markedly with a decrease in pH, with LC50s at the lowest
pH tested (6.6 for sunfish, 6.5 for bass) being 3.6 (sunfish) and 2.6 (bass)
times smaller than those at the highest pH tested (8.7). LCSOs found with
rainbow trout for the ammonlacal portion (diammonium phosphate) of a chemical
fire retardant at two different pH levels Indicated greater NHj toxicity at
lower pH (Blahm 1978).
25
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(d) Acclimation and Fluctuating Exposures
Tha question of whether fish can acquire an increased tolerance to
ammonia by acclimation to low ammonia concentrations is an important one. If
fish had an increased ammonia tolerance developed due to acclimation or
conditioning to low ammonia levels, they would perhaps be able to survive
what otherwise might be acutely lethal ammonia concentrations.
Observations by MeCay and Vars (1931) indicated that bullheads subjected
to several successive exposures to ammonia, alternated with recovery ia fresh
water, acquired no immunity from the earlier exposures to the later ones. A
greater number of researchers have reported that previous exposure of fishes
to low concentrations of ammonia increases their resistance to lethal
concentrations. Vainos (1963) conducted a single experiment in which carp
which had been revived in fresh water for 12 hours after exposure to 0.67 or
0.52 tag/liter NH3 for 75 tain were placed in a solution containing 0.7
mg/liter NHg. The previously exposed fish exhibited symptoms of ammonia
toxlcity in 60-85 min, whereas control fish developed symptoms within 20 tain.
Redner and Sticttney (1979) reported that blue tllapia acclimated for 35 days
to 0.52 to 0.64 mg/liter NH3 subsequently survived 43 hours at 4.1
mg/liter; the 48-hour LC50 for unacclimated fish was 2.9 mg/liter.
Malacca (1968) studied the effect of acclimation of bitterling to
ammonium sulfate solutions. A group of ten fish was held In an acclimation
solution of 0.26 mg/liter NH3 for 94 hours, after which the fish were
exposed to a 5.1 mg/liter NH^ solution for 240 min; a control group of ten
was treated identically, except their acclimation aquarium did not contain
added (NH^^SO^. The ratio of the mean survival times of "adapted" vs.
"unadapted" fish was 1.13; mean survival times for the adapted and unadapted
26
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fish were 78 and 88 minutes, respectively, indicating somewhat higher ammonia
tolerance for adapted fish.
Proram (1970) measured urea excretion rates of rainbow trout initially
acclimated to either 5 or 0.5 mg/liter NH3, then subjected to 3 mg/liter
NH3« Fish previously exposed to 5 mg/liter NH3 excreted slightly less
urea than those exposed to the lower concentration. Lloyd and Orr (1969)
conducted acclimation experiments with rainbow trout and found that the rate
of urine excretion increased with a rise in the concentration of un-ionized
ammonia to which the fish were exposed. They presented some evidence for
acclimation of rainbow trout to sublethal levels of ammonia, although these
levels may be as low as 12 percent of the "lethal threshold concentration".
Acclimation was retained for 24 hours, but was not retained after three days.
They also suggested that environmental factors, which affect the water balance
of fish may also influence susceptibility to ammonia toxicity. Fromm (1970)
acclimated goldfish to low (0.5 mg/liter) or high (5.0 or 25.0 mg/liter)
ambient NH3 for periods of 20 to 56 days and found that urea excretion rate
in subsequent 24-hour exposures to concentrations ranging from 0.08 to 2.37
mg/liter was independent of the previous acclimation concentration or
duration.
Schulze-Wiehenbrauck (1976) subjected two groups of rainbow trout (56 g
and 110 g) which had been held for at least three weeks at sublethal ammonia
concentrations to lethal ammonia concentrations. In the experiment with
110-g fish, the sublethal acclimation concentrations were 0.007 (control),
0.131, and 0.167 mg/liter NH3; the fish from these three tanks were then
subjected to concentrations of 0.45, 0.42, and 0.47 mg/liter NH3,
respectively, for 8.5 hours. Fish from the two higher sublethal
27
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concentrations had 100 percent survival after 8.5 hours in the 0.42 and 0.47
ing/liter NH3 solutions, whereas fish from the 0.007 mg/liter NH3
concentration had only 50 percent survival in 0.45 mg/liter Nt^. In the
experiment with 56-g fish, the acclimation concentrations were 0.004 tag/liter
NH3 (control) and 0.159 mg/liter NH^; these fish were placed in NH3
concentrations of 0.515 and 0.523 mg/liter, respectively, for 10.25 hours.
There was 100 percent survival of the acclimated fish, and 85 percent
survival of the control fish. The results of these experiments thus showed
an increase in resistance of trout to high ammonia levels after prior
exposure to sublethal ammonia levels.
Alabaster et al. (1979) determined 24-hour LCSOs of NH3 for Atlantic
salmon smolts under reduced dissolved oxygen test conditions. Fish
acclimated to ammonia before oxygen reduction evidenced LC50s 38 and 79
percent higher than fish without prior ammonia acclimation.
Brown et al. (1969) tested rainbow trout in static tests in which fish
were moved back and forth between tanks in which the ammonia concentrations
were 0.5 and 1.5 times a previously determined 48-hour LC50. If fish were
transferred on an hourly basis, the median period of survival for the
fluctuating exposure was reported to be the same as that for constant
exposure (>700 min). If the fish were transferred at two-hour intervals, the
median survival time for the fluctuating exposure was reported to be less
(370 min), indicating that the toxic effects from exposure to the fluctuating
concentrations of ammonia was greater than those from exposure to the
constant concentration.
Thurston et al. (1981a) conducted acute toxicity tests on rainbow trout
and cutthroat trout in which fish were exposed to short-term cyclic
28
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fluctuations of ammonia. Companion testa were also conducted in which test
fish were subjected to ammonia at constant concentrations. LCSOs in terms of
both average and peak concentrations of ammonia for the fluctuating
concentration tests were compared with LCSOs for the constant concentration
tests. Based on comparisons of total exposure, results showed that fish were
more tolerant of constant concentrations of ammonia than of fluctuating
concentrations. Fish subjected to fluctuating concentrations of ammonia at
levels below those acutely toxic were subsequently better able to withstand
exposure to higher fluctuating concentrations than fish not previously so
acclimated.
In renewal exposures to ammonium chloride using river water as the
dilution water, fathead minnows were reported (Pitts 1980) to survive for 28
days exposures fluctuating from 0.1 mg/liter NHj for four days to 0.2 or
0.3 mg/liter NH-j for three days. Four-day excursions above 0.1 mg/llter to
concentrations of 0.42, 0.48, and 0.52 mg/liter resulted in 80 to 100 percent
mortality in 28 days, as did four-day excursions to 0.73 mg/liter. No
constant exposure tests were conducted simultaneously for comparative
purposes; however, constant exposure tests conducted approximately a year
earlier yielded LCSOs ranging from 0.6 to 2.4 mg/liter Nl^.
In summary, there is reasonable evidence that fishes with a history of
prior exposure to some sublethal concentration of ammonia are better able to
withstand an acutely lethal concentration, at least for some period of hours
and possibly days. The relative concentration limits for both acclimation
and subsequent-acute response need better definition and a more complete
explanation. Limited data on fluctuating exposures indicate that fish are
more susceptible to fluctuating than to constant exposure with the same
average NH-j concentrations. Much more research is needed to examine
29
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further the effects of fluctuating and intermittent exposures under exposure
regimes simulating actual field situations.
(e) Carbon Dioxide
An Increase in carbon dioxide concentrations up to 30 mg/liter decreases
total ammonia toxicity (Alabaster and Herbert 1954; Allan et al. 1953).
C02 causes a decrease in pH, thereby decreasing the proportion of
un-ionized ammonia in solution. Lloyd and Herbert (1960) found, however,
that although total ammonia toxicity was reduced at elevated CC>2 levels,
the Inverse was true when considering un-ionized ammonia alone; more NH^ is
required in low C02> high pH water to exert the same toxic effect as seen
in fish in high C02» low pH water. The explanation presented by Lloyd and
Herbert (1960) for the decreased toxlcity of NH3 in low C02 water was
that CO2 excretion across the gills would reduce pH, and therefore NH^
concentration, in water flowing over the gills.
The basic flaw in Lloyd and Herbert's (1960) hypothesis has been
discussed in Broderius et al. (1977). C02 will only form protons very
slowly in water at the tested temperature. The uncatalyzed C02 hydratlon
reaction has a half-time of seconds or even minutes (e.g., at pH 8: 25
seconds at 25 C, 300 seconds at 0 C (Kern I960)), and water does not remain
in the opercular cavity for more than a few seconds, and at the surface of a
gill lamella for about 0.5 to 1 second (Randall 1970; Cameron 1979). Thus
the liberation of C02 will have little, if any, effect on water pH or,
therefore, NH3 levels while the water body is in contact with the gills.
Hence the liberation of C02 across Che gills can have little, if any,
effect on the NH-j gradient across the gills between water and blood.
Szumski et al. (1982) hypothesized that in the course of its excretion CO2
is converted in the gill epithelium to H+ and HC03~ which then pass
30
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directly into the gill chamber where they cause an instantaneous pH reduc-
tion. Their interpretation of the published literature on fish respiratory
physiology is questionable, and experimental evidence in support of cheir
evaluation is required before it can be given serious consideration.
(f) Salinity
Herbert and Shurben (1965) reported that the resistance of yearling
rainbow trout to ammonium chloride increases with salinity up to levels of
30-40 percent seawater; above that level, resistance appears to decrease.
Katz and Pierro (1967) tested fingerling coho salmon at salinity levels of 20
to 30 parts per thousand (57 to 86 percent salt water) and found that
toxicity of an ammonia-ammonium waste increased as salinity increased. These
findings are in agreement at the levels tested with those of Herbert and
Shurben (1965). Atlantic salmon were exposed to ammonium chloride solutions
for 24 hours under both freshwater and 30 percent saltwater conditions; LC50s
(Table 5) were 0.15 and 0.3 mg/liter NH-j, respectively, in the two
different waters (Alabaster et al. 1979). For chinook salmon parr, Harader
and Allen (1983) also found resistance to increase (by about 500Z) as
salinity increased to almost 30Z seawater, with declines occurring as
salinity increased even further.
As was discussed in Willingham et al. (1979), decreased NH3 toxicity
with increased salinity may be partially explained, at least for low salinity
levels, by the fact that there is a slight decrease in the NH3 fraction of
total ammonia as ionic strength increases in dilute saline solutions
(Thurston et al. 1979). At higher salinity levels, however, the toxicity to
fishes of ammonia solutions must be attributable to some mechanism or
mechanisms other than the changes in the NH4+/NH3 ratio. Further work
31
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is needed to confirm results already reported and to clarify the observed
mitigating effect of total dissolved solids.
(g) Presence of Other Chemicals
The presence of other chemicals may have an effect on ammonia toxlcity,
and some experimental work has investigated this topic. Herbert and Vandyke
(1964), testing rainbow trout, determined the 48-hour LC50 for a solution of
ammonium chloride and that for a solution of copper sulfate. They reported
that a solution containing a mixture of one half of each of these LC50s was
also the 43-hour LCSO for the two toxicants combined; i.e., the toxic
response was simply additive. This information was also reported by the
Ministry of Technology, U.K. (1964); it is not clear whether this was a
separate study or the same study.
Shemchuk (1971) measured copper uptake in two-year old carp from
solutions of CuCNHj)^ ; copper uptake in various Eish tissues was
reported, but no information was provided about toxlcity. Vamos and Tasnadi
(1967) applied cupric sulfate to a "carp pond" to reduce the concentration of
free ammonia and reported that this measure proved successful to reduce Che
toxic effect of ammonia; few details were provided.
Ministry of Technology, U.K. (1962, 1963) reported on the results of
tests on rainbow trout in which 43-hour LCSOs were determined for solutions
of ammonium chloride, zinc sulfate and mixtures of these two salts. A.
fraction of each of those 43-hour LCSOs, when combined in such a way that
those fractions equalled unity, provided a mixture with a 43-hour LC50 equal
to that of either of the two toxicants alone. Results were similar for tests
conducted in waters with alkalinitles of 240 and SO mg/llter as CaC03.
32
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Herbert (1962) studied the toxicity to rainbow trout of ammonia-phenol
mixtures. The mixtures contained fractions of the 48-hour LCSOs of phenol
and of ammonia; the combined fractions equaled unity. The coxicity of the
combined fractions approximated the toxicity of either phenol or ammonia when
tested separately but under test conditions of similar water chemical
characteristics. The same information was reported by Ministry of
Technology, U.K. (1961); it is not clear whether this was a separate study or
the same study.
Brown et al. (1969) conducted 43-hour tests on rainbow trout in mixtures
of ammonia, zinc, and phenol; the mixture contained equal portions, by
48-hour LC50, of the three toxicants. They reported that each chemical
nominally contributed equally to the toxicity. In a second series of three
tests in which the mixture was adjusted to include approximately 75 percent
of a 48-hour LC50 of one toxicant and the balance split equally between the
other two, they reported that the principal toxicant contributed about
three-fourths of the toxicity.
Broderlus and Smith (1979), in 96-hour flow-through tests with rainbow
trout, reported a synergistlc effect for NH3 and HCN except at extremely
low concentrations. Rubin and Elmaraghy (1976, 1977) estimated the
individual and joint toxicities of ammonia and nitrate to guppy fry; the
toxiclties of the two in mixture were additive, except at very low
ammonia-to-nitrate ratios. Tomasso et al. (1980) reported that elevated
calcium levels increased the tolerance to ammonia of channel catfish.
33
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Derivation of the Final Acuce Value for Fresh Wacer
(a) pH Dependence of Acuce Ammonia Toxicicy
Erickson (1985) reviewed available daca on che pH-dependence of
un-ionized annonia LC50s. For che pH 5 co 9 range, he noced chac che
principal feacure of plocs of log(LCSO) versus pH was a declining slope wich
increasing pH, wich che slope apparencly approaching zero ac che upper pare of
che range and approaching a conscanc value ac che lower pare of che range. He
proposed che following empirical model for such behavior:
LIM _ (1)
! + 10SLP(PHT-pH)
where LIM * che asyrapcocic LC50 ac high pH, SLP * che asyrapcocic slope ac low
pH, and PHT * a cransicion pH. The fie of chis model co available daca was
found co generally be good, wich che R^ varying from 60Z co >99% for all
daca sees and residual errors being in che range of uncercaincy for coxicicy
cescing. Furchermore, for chose daca sees wich cercain minimum daca
requiremencs necessary for critically evaluacing model fie (ac lease 6
observacions spread over ac lease 4 discincc pHs wich a range of ae lease
1.5), che fie was very good (Figure 1), wich R^s ranging from 96% co >99%.
The paramecer SLP was generally found co be similar among daca sees and a
pooled analysis escimaced ic co be 1.03, indisc inguishable from 1.0 boch for
praccical purposes and from a scandpoinc of scaciscical significance. The
paramecer PHT was also found co be similar among daca sees, usually being in
che pH 7 co 8 range.
This empirical model, however, did noc incorporace indicacions in some
daca (Figure 1) chac LC50s may be declining as pH increases over 8.5. To
minimize possible errors associaced wich such behavior, che model was
slighcly modified for applicacion here by requiring chac LCSOs are conscane
34
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10
5.0
2.0
1.0
0.50
fc 0.20
± 2.0
o
~ 1.0
O
10
O
J 0.50
DophnIa
5.0
2.0
1.0
0.50
0.20
0.10
0.050
7.0 8.0 8.0
Rainbow Trout
0.20
0.10
2.0
1.0
0.50
Fath«ad Minnow
0.20
0.10
I
I
I
7.0 8.0 9.0
pH
0>060
7.0 8.0 9.0
Coho Salmon
7.0 8.0 9.0
Figure 1. Acuta NH3 toxicity at different pU values (data from Tabata 1962,
Thurston et al. 1981c, Robinson-Wilson and Seia 1975). Dashed lines
regression based on individual data set; solid lines » regression
bnsed on oooled data sees and modified model.
35
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ac pH a and above; this will cend to cause che ficced curve co pass slighcly
below che apparent peak ac pH 3.5 and closer co che daca near pH 9.0.
Based on che behavior of SLP noced above, che model was further modified
by assuming che paramecer SLP exaccly equalled 1.0 and dropping ic from che
model. This is equivalenc co assuming che pH dependence of ammonia coxicicy
is due co joinc coxicicy of. NH3 and NH^*, buc the incerprecacion here
will remain scriccly empirical and none of che r ami ficac ions of such a
mechanism, such as cemperacure dependence of PHI, will be considered here due
to absence of sui cable daca.
The modified model for pH dependence cherefore was:
LC50 - LC50(pH-8) ; pH _> 8
i > inPHT-8
LC50 - LC50(pH-8) { ^ {gpHT-pH J pH < 3
where che paramecer LIM has been replaced wich LC50(pH-8) •(! +
thus adopcing a reference pH of 3, where che imposed placeau begins.
Evencual applicacion of chis model co generating a cricerion requires
chac ic concain only one paramecer dependenc on cesc organism, since having
more than one paramecer would require chac chere be LCSOs from mulcipLe pHs
for every cesc organism, when, in face, such information is available for few
of che cescs in Table 1. Clearly, LC50(pH«8) is likely co be organism-
dependenc, since ic represencs che sensicivicy under reference conditions.
PHT muse cherefore be assumed co be constant among Cesc organisms, ac least
uncil addicional testing allows separate estimates for PHT for different
taxa. This assumption is justified to some extent by che observed similarity
of PHT among species noted above.
Using the modified model, a pooled regression analysis of the data in
Figure 1 was conducted employing che procedures of Erickson (1985), resulting
36
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in an escimace 7.4 for the paramecer PHT. The resulting model fie was good,
wich an R* for che pooled data sec of 96Z, liccle worse chan achieved with
individual analyses of each daca sec using che original model (Equation 1).
The slight decrease in fie was solely due co using pooled escimaces for PHT
and SLP. The imposition of the plateau at pH > 8 accually improved che fie
slightly. The fit from chis pooled analysis is indicated in Figure 1.
The final relationship adopted for che pH-dependence of acuce ammonia
toxicicy cherefore was:
LC50 » LC50(pH-8) ; pH _> 8 (3)
LC5Q „ LC50(pH«8)-1.25 ; pH < 8
1 + io?.4-pH
Alchough che proposed relationship cannoc be considered universally
applicable or wichouc error, che alternatives of using no pH relationship or
of basing criteria only on species tested over a range of pHs are clearly
less desirable. A relationship which can be applied with more confidence
requires further experimentation. Of course, in sice-specific applications,
if evidence exists for significantly different pH relationships for species
of importance co seccing criteria, appropriate modifications should be
considered.
(b) Temperacure Dependence of Acuce Ammonia Toxicicy
Erickson (1985) reviewed available data on the temperature-dependence of
un-ionized ammonia LC50s. For daca sees wich more chan two tested tempera-
cures, he noced chat che principal feature was an approximately linear
relationship of log(LCSO) versus temperature (Figure 2). He noted some
indication of declining slopes wich increasing temperature, buc due co che
daca uncercaincy chis crend could noc be adequacely verified or quantified.
37
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4t-
10 20
—Thr««-«pIn«d
-Stick I.book
10
4r~Blu«alll
l~Sunf I
tO 20 30
Temperature (C)
Figure 2. Acute NH-j toxicity at different temperatures (data from Gary 1976,
Thurston and Russo 1983, Thurston et al. 1983, Colt and Tchobanoulous
1976, Ministry of Technology 1968, Reinbold and Pescitelli 1982,
Roseboom and Richey 1977, Hazel et al. 1971). Dashed lines indicate
individual regressions; solid lines indicate pooled regression.
38
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He cherefore proposed the following empirical model for cemperacure
dependence of ammonia coxicicy:
LC50 - LCR • 10SLT(T-20)
where LCR is che LC50 ac a reference cemperacure of 20 C and SLT is che slope
of log(LC50) versus cemperacure. Slope escimaces were found co noc vary
significancly among daca sees, which included variacion in boch organisms and
Cemperacure range cesced. Slopes varied from 0.016 co 0.054, wich an
arichmecic mean of 0.03; incerescingly, chis is approximacely equivalenc co
cocal ammonia being conscanc wich cemperacure. The relationship adopced for
che cemperacure dependence of acuce ammonia coxicicy in fish cherefore was:
LC50 - LC50(T-20) • 10°-03(T-20) (5)
where che paramecer LCR has been replaced wich che more descriptive cerra
LC50(T»20), consiscenc wich che cemiinology adopced for che reference LC50 in
che pH relacionship. For invercebraces, no cemperacure relacionship will be
used; chis assumpcion will cause liccle error because available daca suggest
chac cemperacure effeccs are noc as marked as in fish and because inverce-
braces are generally insensicive co ammonia and chus do noc markedly
influence che criceria.
However, chis relacionship cannoc be applied wichouc some limitations.
As noted above, chere is some indicacion of declining slopes as cemperacure
increases. Also, available daca sees were rescricced co temperatures, ac che
high end, chac were opcimal or only marginally subopcimal. Thus, extrapola-
tion of chis relacionship co high cemperacures muse be rescricced. Ic can be
used co adjusc che daCa in Table 1 co reference condicions since che cescs
for each fish were rarely conducced under unfavorably high cemperacures, but
ic should noc be used for generating criceria ac cemperacures high enough to
constitute a scress co an organism. Where criceria are necessary for such
39
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high cemperacures, ic is recommended here chac ic be che same NHj
concencracion as ac che upper end of che cemperacure range considered
favorable for che organism (i.e., SLT is assumed co be 0.00 racher than 0.03
becween che upper end of che favorable range and higher cemperacures). The
final relationship adopced for che cemperacure dependence of che nacional
cricerion cherefore was:
LC50 - LC50(T-20) • io°-03(TCAP-20). T ^ TCAP (6)
LC50 - LC50CT-20) • 10°-03(T-20) ; T < TCAP
For che purposes of che nacional criteria, when salmonid fish or ocher
sensicive coldwacer species are present, che cemperacure relacionship will be
applied only up co 20 C (TCAP * 20). Temperatures much higher Chan chis are
decrimencal co coldwacer species and daca on che cemperacure dependence of
ammonia coxicicy for such species extends only up co 13 C. Thus, use of che
cemperacure relacionship above 20 C is of doubcful validity and un-ionized
ammonia criceria ac high cemperacures will be assumed co be no higher chan ac
20 C. For sices wichouc salmonids and ocher sensicive coldwacer species,
TCAP * 25 C will be used; a higher TCAP (30 C) may be juscified on a
sice-specific basis when scriccly warmwacer species are presenc. The
increase in che cemperacure cap should noc be beyond where chere is daca co
suggest chac che colerance of che mosc sensicive sice genera continues co
increase with temperature and should not result in a FAV ac any temperature
chac is significancly greacer chan che AVs ac che higher cemperacures cesced
for che mosc sensicive genera ac che sice.
As for che pH relacionship, chis proposed cemperacure relacionship is
imperfect due co che limiced database, but che alcernacives of using no
relacionship or of rescriccing criceria co narrow Cemperacure ranges where
sufficient daca is available are clearly less desirable. Of course, also as
40
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for pH, where data for a species of importance co che seccing of a cricerion
concradiccs che above assumptions regarding temperature, appropriate
modifications should be made.
(c) Application of pH and Temperature Relationships of Acute Ammonia Toxicity
to Determination of Final Acute Values
A Species Mean Acute Value (SMAV) is the geometric average of che acute
values (AVs), usually LCSOs, available for a given species. A Genus Mean
Acute Value (GMAV) is the geometric average of the SMAVs available for a
given genus. A Final Acute Value (FAV) for a material is an estimate of the
GMAV at the 0.05 cumulative proportion in the cumulative distribution of
GMAVs for all genera tested for chat material. These computations (see
Guidelines) are not a subject of this discussion, but their application co pH
and temperature dependent data is.
The existence of pH and temperature dependence in AVs requires that they
be adjusted to a common reference pH and temperature basis before computing a
FAV. After a FAV at this reference pH and temperature is computed, it can be
applied to other pHs and temperatures using the same equations used co
correct the AVs.
The reference pH and temperature are arbitrary insofar as final results
are concerned. The reference temperature selected here was 20 C, as selected
for equation 5, and the reference pH was 8, as selected for equation 2.
These reference conditions furthermore are moderate and near those of most
tests in Table 1, allowing more easy comparisons of values.
It is assumed here that che effects of pH and temperature are not
significantly correlated. There are currently no data to contradict this
assumption, much less mathematically model such a correlation. Equations 3
and 5 can then be combined as follows to provide a unified equation for
41
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adjuscing acute values measured ac any pH and cemperacure co the reference
conditions.
AVref - AV(pH,T) ' FT • FPH (7)
where:
FT , 100.03(20-1) . for fish
* 1 ; for invercebraces
FPH - 1 ; pH ^ 8
- 1 + 107-4-PH ; PH < 8
1.25
Once all AVs available for establishing a criterion are adjusted to
AVrafS, the SMAV for each species at reference conditions (SMAVref)
can be computed as the geometric average of the AVrefS for that species
and the GMAV for each genus at reference conditions (GMAVre£) can be
computed as the geometric average of the SMA7re£9 for that genus. The
FAV at reference conditions (FAVrej) then can be computed from the
GMAVre£S available by the same procedures used for computing FAVs from
GMAVs for any material. A FAV at a particular pH and temperature can finally
be computed by reversing equation 7 (and also applying the restriction from
equation 6 that FT - i<)0.03(20-TCAP) for T >^ TCAP).
Application of these techniques to the data proceeded as follows. AVs
from Table 1 were adjusted for temperature and pH and averaged to obtain the
SMAVre£S and GMAVrefS reported in Table 3. The fifth percentile
was estimated, by the Guidelines method, to be 0.70 mg/liter Nt^. However,
the rainbow trout data in Table 1 indicate that sexually mature fish (M kg)
are significantly more sensitive than the average of the tested fish. Since
a species is not protected if each life stage is not protected, the
-------
FAV ef was lowered co 0.52, the geomecric average of che AVrefS of
rainbow crout in chis size range. Thus, che equation for che FAV is:
FAV(pH.T) - 0.52/FT/FPH (8)
where:
FT - 10°-03(2°-TCAP>; TCAP £ T £ 30
» 100.03(20-T) . 0 £T £ TCAP
FPH - 1 ; 8.0 <. pH _< 9.0
- 1 + 10?.4-pH . 6.5<_pH£8.0
1.25
TCAP « 20 C; Salmonids presenc
* 25 C; Salmonids absenc
(d) Application of che FAV co a Criterion co Protect Against Acute Toxicicy
As specified in the Guidelines, che cricerion co procecc againsc acute
coxicicy will be based on requiring chac 1-hour average concentrations not
exceed, more often on che average chan once every 3 years, one-half of che
FAV specified in Equation 8 above. For ammonia there is considerable
evidence that this short averaging period is justified, even though che FAV
is based on tests with a cypical duracion of 96 hours. The acute response of
some fish co ammonia can be very rapid. For example, McCormick ec al. (1984)
reported LCSOs wich green sunfish to be only 0% co 40% higher ac 3 hours chan
at 96 hours for che pH range 7.2-8.7; furthermore, chis did noc cake inco
consideracion any delayed morcality at the shorter time, so the differences
may be even smaller. Ball (1967) reported a 3-hour LC50 for rainbow crouc co
be jusc 50% greater chan che asymptotic LC50, again not accounting for
delayed mortality (other species, however, did not have such an extreme
relationship). Effects of simple exposures of shorter duracion are unknown,
but LCSOs for 1- to 2-hour periods quite possibly could also be jusc
43
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marginally above that at 96 hours, especially if che 1- or 2-hour period is
preceded and/or followed by concencracions which are aoc markedly lower.
Therefore, a criterion based on 96-hour LCSOs cannoc be creaced as an
average over any appreciable fraccion of che cesc duration, since such
averaging implicitly allows significant excursions over the criterion for an
appreciable fraction of the averaging period and thus allows the occurrence
of a time sequence of concentrations at lesser intervals that would have
greater toxicity than is intended by the criterion. For example, in the case
of the data cited above, even a 4-hour averaging period would allow
concentrations of 2- to 3-hour duration that could have an impact greater
than desired.
Experiments on the effects of fluctuating ammonia concentrations also
support the use of extremely short averaging periods. Thurston et al.
(1981a) exposed rainbow trout to ammonia concentrations that varied from
virtually zero to a peak over a 12- to 24-hour cycle and reported LC50s based
on peak concentrations to be only 16-39Z higher than those based on 96-hour
constant concentration tests and that LCSOs based on the average of che
fluctuating concentrations were 25-42Z less than the 96-hour LCSOs for all
cescs excepc chose on large fish, which tolerated slightly higher peaks.
Since concentrations were near or at che peak for only two hours, this
suggests that, although some excursions above 96-hour LCSOs are permissible
at short durations, the allowable excursions are not large enough to allow
averaging periods of more than a few hours. Brown et al. (1969) exposed
rainbow trout to fluctuating concentrations with an average equal co che
48-hour conscant concentration LCSO, with the fluctuations varying between
1.5X and 0.5X the average over either a 2- or 4-hour cycle. They found chac
toxicity using the 2-hour cycle was similar to that under constant exposure,
44
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but was markedly higher using che 4-hour cycle. This indicates chac, even
for a modesc 50Z excursion over che constant concentration LC50, an averaging
period of longer than 2 hours is inappropriate. For more marked excursions,
shorter periods may be necessary.
Thus, the 1-hour averaging period specified in the Guidelines is
reasonable for ammonia. In fact, this duration may be too long if
substantial excursions above the average occur within the hour. Therefore,
it is further specified here that this 1-hour average criterion is not
applicable to situations where concentrations exceed 1.5 times the average
within the 1-hour period. The 1.5 factor was based on such an excursion
being acceptable based on the fluctuating exposure, studies discussed above,
with no evidence that greater excursions are tolerable.
Saltwater Invertebrates
Data on acute toxicity of ammonia to saltwater invertebrate species are
very limited. LCSOs are summarized in Table 1 for five species representing
five families. A 96-hour LC50 (Table 1) of 1.5 mg/liter NH3 was reported
(Linden et al. 1979) for the copepod, Nitocra spinipes. Lethal effects of
NH^Cl on the quahog clam (Mercenaria mercenaria) and eastern oyster
(Crassostrea virginica) were studied by Epifanio and Srna (1975) (Table 1).
There was no observed difference in susceptibilities between juveniles and
adults of the two species. Armstrong et al. (1978) conducted acute coxicicy
tests (6 days) on ammonium chloride using prawn larvae (Macrobrachium
rosenbergii). LC50s (Tables 1, 5) were highly pH-dependent. Acute toxicicy
of NlfyCl co penaeid shrimp was reported as a 48-hour composite LC50 of 1.6
mg/liter NH-j for seven species pooled, including the resident species
Penaeus setiferus (Wickins 1976). The acute toxicity of NH^Cl to che
45
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caridean prawn, 11. rosenbergii, was reporced (Wickins 1976) as LTSOs of
1700-560 minutes ac concencracions of 1.74 to 3.41 rag/liter NH3 (Table 5).
Hall ec al. (1978) measured che acuce coxicicy of NH^Cl co grass shrimp
(Palaemoneces pugio) (Table 5). Cacedral and cowortcers (1977a,b) investi-
gaced che effecc of NH^Cl on survival and growth of Penaeus monodon; larvae
had lower colerance co ammonia compared wich pose larvae. Brown (1974)
reporced a cime co 50 percent mortality of 106 min for nemertine worm
(Cerebratulus fuscus) at 2.3 mg/liter NH3 (Table 5).
Effects of MH^Cl solutions on American lobster (Homarus americanus)
were studied by Delistraty et al. (1977). Their tests were performed on
fourth stage larvae which they believed co be che most sensitive life stage,
or nearly so. They reported a 96-hour LC50 (Table 1) of 2.2 mg/liter NH3
and an incipient LC50 (Table 5) of 1.7 mg/liter Nt^. A "safe" concentra-
tion of 0.17 mg/liter NHj was tentatively recommended.
Saltwater Fishes
Very few acute toxicity data are available for saltwater fish species.
Holland et al. (I960)- reported the critical level for Chinook salmon
(Oncorhynchus tshawytscha) to be between 0.04 and 0.11 mg/liter NH3 and for
coho salmon to be 0.134 mg/liter NH3. A static test with coho salmon
provided a 48-hour LC50 (Table 5) of 0.50 mg/liter NH3 (Katr and Pierro
1967). Atlantic salmon smolts and yearling rainbow trout tested for 24 hours
in 50 and 75 percent saltwater solutions exhibited similar sensicivicies co
ammonia (Ministry of Technology, U.K. 1963).
Holt and Arnold (1983) report a 96-hour LC50 of 0.47 mg/liter NH3
(Table 1) for red drum (Sciaenops ocellatus). Venkataramiak (1981a) found
46
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96-hour LC50s (Table 1) of 1.2-2.4 mg/licer NH3 for scriped mullec (Mugil
ceohalus) and 0.69 mg/licer NH3 for planehead filefish (Monacanchus
hiapidus).
47
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CHRONIC TOXICITY TO AQUATIC ANIMALS
The following discussion of chronic and partial chronic ammonia toxieity
includes both data used in the derivation of the Final Chronic Value (Table 2
data) and data that were not included in the criterion derivation, but that
are important for an understanding of long-tern lethal and sublethal effects
of ammonia on aquatic organisms (Table 5 data).
Freshwater Invertebrates
Few studies have been conducted on long-term exposure of freshwater
invertebrates to ammonia, and life-cycle tests were conducted only for
cladocerans.
The lowest concentrations affecting reproduction in two life-cycle tests
(Table 2) with _D. magna were 0.74 and 0.76 mg/liter NH3 (Russo et al.
1985); a 28-day LC50 of 1.53 nig/liter NH3 was reported. In a chronic test
(Table 2) conducted by Reinbold and Pescitelli (1982a), reproduction and
growth of J). magna were affected at a concentration of 1.6 mg/liter NH^. A
life-cycle test (Table 2) with C_. acanChina (Mount 1982) showed effects on
reproduction at a. concentration of 0.463 mg/liter NH^.
Two tests lasting 42 days were conducted by Anderson et al. (1978) on
NH^Cl with the fingernail clam, Musculium transversum .(Table 5).
Significant mortalities (67 and 72 percent) occurred in both tests at a
concentration of 0.7 mg/liter Nt^. In one of the experiments, significant
reduction in growth was observed after 14 days of exposure to 0.41 mg/liter
NH-j. Sparks and Sandusky (1981) reported that fingernail clams exposed to
0.23 and 0.63 mg/liter NH3 Incurred 36 and 23 percent mortality,
respectively, in four weeks; after six weeks, 47 percent mortality occurred
at 0.073 mg/liter NH3» and 83 percent mortality occurred at 0.23 and 0.63
48
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mg/liter KRj- No growth at all occurred in all test chambers (concentra-
tions of 0.036 mg/liter NH3 and higher) other than the control after six
weeks (Table 5).
Two partial chronic tests, of 24- and 30-days' duration, were conducted
by Thurston et al. (1984a) with the stonefly Pteronarcella badia (Table 5).
Adult stonefly emergence was delayed with increasing ammonia concentration,
and little or no emergence occurred at concentrations exceeding 3.4 mg/liter
NH^. There was no significant relationship between food consumption rates
of nymphs and concentrations up to 6.9 og/liter NH^- LCSOs for 24- and
30-day exposures were 1.45 and 4.57 mg/liter NHj, respectively.
Freshwater Fishes
A number of researchers have conducted long-term ammonia exposures to
fishes, including complete life-cycle tests on rainbow trout and fathead
minnows. Several kinds of endpoints have been studied, Including effects on
spawning and egg incubation, growth, survival, and tissues.
The effects of prolonged exposure (up to 61 days) to ammonia of pink
salmon early life stages was studied by Rice and Bailey (1980). Three series
of exposures were carried out, beginning at selected times after hatching:
for 21 days prior to completion of yolk absorption, for 40 days up to 21 days
before yolk absorption, and for 61 days up to yolk absorption. All test fish
were sampled for size when the controls had completed yolk absorption. NHj
concentrations ranged from 0 (control) up to 0.004 mg/liter. For fry at the
highest concentration of 0.004 mg/liter NH3 (Table 2), significant
decreases in weight were observed for all three exposure groups. At a
concentration of 0.0024 mg/liter NHj (Table 2) the group of fry exposed for
40 and 61 days were significantly smaller, whereas a concentration of 0.0012
49
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mg/liter had no significant effect on growth. Effects were consistently more
adverse for the 61-day-exposed fish.
Thurston et al. (1984b) tested rainbow trout in a laboratory study in
which adult fish exposed for five months to concentrations of ammonia from
0.01 to 0.07 mg/liter NHj spawned of Cheir own volition; baskets containing
crushed rock served as the spawning substrate. There was no correlation
between ammonia concentration and numbers of egg lots spawned, total numbers
of eggs produced, or numbers of eggs subsequently hatched. Parental fish
were exposed for 11 months, the first filial generation (Pp for four
years, and the second filial generation (?2^ f°c five months. Pathologic
lesions were observed in both parental and Fj_ fish when ammonia concentra-
tions reached and exceeded 0.04 mg/liter NH} (Table 2). Measurements of
blood ammonia concentrations in four-year-old F^ fish showed an increase
when test water conditions reached or exceeded 0.04 mg/liter Nt^. Trout
exposed for 52 months from day of hatching showed no relationship between
growth and concentration at 10, 15, 21, and 52 months.
Burkhalter and Kaya (1977) tested ammonia at concentrations from 0.06 to
0.45 mg/liter NH^ on fertilized eggs and resultant sac fry of rainbow trout.
Eggs were incubated at 12 C for 25 days in one test and at 10 C for 33 days in
another; fry were maintained for 42 days. In neither test was there a
concentration response on egg mortality or on incubation time. Retardation in
early growth and development occurred at NH3 concentrations as low as 0.06
mg/liter NH^, the lowest concentration they tested (Table 2). Fish exposed
to 0.12 mg/liter NHj (Table 2) required one week longer than controls to
achieve a. free-swimming state; fish at 0.34 and 0.45 mg/liter NH3 did not
achieve a. free-swimming state during a 42-day test period. A 21-day LC50 of
0.30 mg/liter NHj was obtained (Table 5). For sac fry exposed for 42 days
50
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after hatching, hypertrophy of secondary gill lamellae epithelium occurred at
0.23 ing/liter NH3, and karyolysis and karyorrhexis in the secondary gill
lamellae were observed after 28 days at 0.34 mg/liter NH3 and higher.
Calamari et al. (1977, 1981) exposed rainbow trout to ammonium chloride
solutions for 72 days, beginning one day after fertilization and ending when
fry were fed for 30 days. A 72-day LC50 of 0.056 mg/liter NH3 was
calculated (Table 5); 23 percent mortality occurred at a concentration of
0.025 mg/liter NH3 (Table 2). Examination of 936 rainbow trout embryos at
hatching stage after exposure to NH3 concentrations of 0.010 to 0.193
mg/liter for 24 days showed an Increase in macroscopic malformations with
increasing ammonia concentration. Kinds of deformities observed were varying
degree of curvature from median body axis, which in extreme cases produced a
complete spiral shape, and various kinds of malformations in the head region
with a number of cases of double heads. At the highest concentration tested,
0.193 mg/liter NH3, 60 percent of the observed fish were malformed.
Microscopic examination at hatching of 123 larvae from the same exposure
showed abnormalities on the epidermis and pronephros that correlated with
ammonia concentrations. The epidermis was thickened with an irregular
arrangement of the various layers of cells and an increase in the number and
dimensions of mucous cells. The pronephros showed widespread yacuolizatlon
of the tubule cells, together with a thickening of the wall. Increasing
abnormalities were observed after exposure to concentrations over 0.025
mg/liter NH3 for epidermis and 0.063 tug/liter NH3 for pronephros.
Broderius and Smith (1979) tested four-week-old rainbow trout fry for 30
days at concentrations of ammonia (reported grahlcally) ranging from -0.06 to
0.32 mg/liter NH3 (Table 5). Growth rate at -0.06 mg/liter NH3 was
comparable to that of controls; above -O.10 mg/liter NH3 growth rate
51
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decreased, correlated with increased NH3 concentration. The survival at
0.32 mg/llter NH-j was reduced to 70 percent that of the controls. Schulze-
Wlehenbrauck (1976) tested juvenile rainbow trout, approximately
one-half-year-old but of different sizes, for periods of time from two to
seven weeks, and at ammonia concentrations from 0.012 to 0.17 mg/liter NH3.
He concluded that 0.05 mg/liter NH3 caused a slight decrease in growth
during the first 14-day interval on nonacclimatized fish, but that decrease
was completely compensated in the next growth interval; exposure to 0.13
mg/liter NH3 (apparently for 3 or 4 weeks) did not affect growth, food
consumption, or food conversion.
Smith (1972) and Smith and Piper (1975) reared young rainbow trout at
three concentrations of ammonia (averaging 0.006, 0.012, and 0.017 mg/liter
NH3) for a period of one year. There was no significant difference in fish
growth reported among the three concentrations at four months. There was,
however, a difference reported at 11 months; the fish at 0.012 and 0.017
mg/liter NH3 weighed 9 and 38 percent less than the fish at 0.006 mg/liter.
Microscopic examination of tissues from fish exposed to the highest
concentration, examined at 6, 9, and 12 months, showed severe pathologic
changes in gill and liver tissues. Gills showed extensive proliferation of
epithelium which resulted in severe fusion of gill lamellae which prevented
normal respiration. Livers showed reduced glycogen storage and scattered
areas of dead cells; these were more extensive as exposure time increased.
Ministry of Technology, U.K. (1968) reported on tests in which rainbow
trout were exposed for three months to concentrations of 0.069, 0.14, and
0.28 mg/liter Nt^. The cumulative mortality of a control group (0.005
mg/liter NH3) was -2 percent. Cumulative mortality at 0.069 and 0.14
mg/liter NH3 was -5 percent, and that at 0.28 mg/liter was ~15 percent.
52
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Reichenbach-Kllnke (1967) performed a aeries of one-week ammonia tests on 240
fishes of nine species (including rainbow trout, goldfish, northern pike
(Esox luclus), carp, and tench) at concentrations of O.I to 0.4 tag/liter
NH3« He observed swelling of and diminishing of the number of red blood
cells, inflammations, and hyperplasia. Irreversible blood damage occurred in
rainbow trout fry in un-ionized ammonia concentrations above 0.27 mg/liter
NHj* lie also noted that low NH3 concentrations inhibited the growth of
young trout and lessened their resistance to disease.
Smart (1976) exposed rainbow trout to 0.30 to 0.36 mg/liter NH3 (Table
5); 31 percent mortality occurred over the 36-day duration of the test, with
most deaths occurring between days 14 and 21. Microscopic examination of the
gills of exposed rainbow trout revealed some thickening of the lamellar
epithelium and an increased mucous production. The most characteristic
feature was a large proportion of swollen, rounded secondary lamellae; in
these the pillar system was broken down and the epithelium enclosed a
disorganized mass of pillar cells and erythrocytes. Gill hyperplasia was not
a characteristic observation.
Frorara (1970) exposed rainbow trout to <0.0005 and 0.005 mg/liter NH3
for eight weeks. Subsequent examination of the gill lamellae of fish from
the trace concentrations showed them to be long and slender with no
significant pathology. Fish exposed to 0.005 mg/liter NH3 had shorter and
thicker gill lamellae with bulbous ends; some consolidation of lamellae was
noticed. Photomicrographs revealed that many filaments showed limited
hyperplasia accompanied by the appearance of cells containing large vacuoles
whose contents stained positive for protein. Other lamellae showed a
definite hyperplasia of the epithelial layer, evidenced by an increase in the
number of cell nuclei.
53
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Thurston et al. (1978) studied the toxicity of ammonia to cutthroat
trout fry in flow-through tests which lasted up to 36 days (Table 5).
Results of duplicate tests on 1.0-g fish both showed 29- and 36-day LCSOs
of 0.56 tag/liter NH3. Duplicate tests on 3.3-g fish provided 29-day LCSOs
of 0.37 and 0.34 mg/liter, slightly less than those of the 1.0-g fish.
Tissues from heart, gastrointestinal tract, and thymus of cutthroat trout fry
exposed to 0.34 mg/liter NHj for 29 days were comparable to those of
control fish. However, gills and kidneys of exposed fish showed degenerative
changes. Gills showed hypertrophy of epithelium, some necrosis of epithelial
cells, and separation of epithelium due to edema; kidneys showed mild
hydropic degeneration and accumulation of hyaline droplets in renal cubule
epithelium; reduced vacuolatlon was observed in livers. Oaoust and Ferguson
(1984) were unable to find rainbow trout gill lesions in NH3 concentrations
of 0.2-0.4 mg/liter.
Samylin (1969) studied the effects of ammonium carbonate on the early
stages of development of Atlantic salmon. The first let of experiments
(temperature * 13 C) was conducted within the range 0.001 to >6.6 mg/liter
NH3 beginning with the "formed embryo" stage; the experiment lasted 53
days. Accelerated hatching was observed with increasing (N^^COj
concentrations, but concentrations XI.16 mg/liter NH^ were lethal in 12-36
hours to emerging larvae. Because (NJ^^CC^ was used as the toxicant,
the pH in the test aquaria increased from 6.7 to 7.6 with increasing NHj
concentration. Growth inhibition was observed at 0.07 mg/liter NHj (Table
2). Tissue disorders were observed in eyes, brains, fins, and blood of
Atlantic salmon embryos and larvae exposed to concentrations from 0.16 to
>6.6 mg/liter NH}, with increased degree of symptom at increased ammonia
concentrations. Effects observed included .erosion of membranes of the eyes
54
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and shedding of the crystalline lens, dilation of blood vessels in liver and
brain, accumulation of blood in the occipital region and in intestines.
Reaction to light and mechanical stimulation gradually disappeared with
increased ammonia concentration, and the pulsebeat slowed. Morphological
differences in development between experimental and control larvae were
observed from the tenth day of exposure, including a lag in yolk resorption,
decrease in growth of the skin fold, and contraction of skin pigment cells
causing the skin color to become paler than it was after hatching. At
concentrations up to 0.07 mg/liter NH3 no significant morphological
differences were ooserved.
A second series of experiments (temperature * 16.5 C) was carried out
in the 0.001 to 0.32 ing/liter NH3 concentration range, and began with
larval salmon (Samylin 1969). Concentrations of 0.21 mg/liter NH3 and
higher were lethal and caused weight loss in fry; 0.001 to 0.09 mg/liter
NH3 caused a decrease in weight gain, although no differences in feeding
activity, behavior, or development were observed in these concentrations
compared to controls. Dissolved oxygen concentrations in this second series
of experiments dropped as low as 3.5 mg/liter.
Burrows (1964) tested flngerling chinook salmon for six weeks In outdoor
raceways into which ammonium hydroxide was introduced. Two experiments were
conducted, one at 6.1 C and the other at 13.9 C, both at pH 7.8. In both
cases fish were subsequently maintained in fresh water for an additional
three weeks. A recalculation of Burrows reported on-ionized ammonia
concentrations, based on more recent aqueous ammonia equilibrium tables,
indicates that the concentrations at 6.1 C were 0.003 to 0.006 mg/liter
NH3, and at 13.9 C were 0.005 to 0.011 mg/liter Nl^. At both
temperatures some fish at all ammonia concentrations showed excessive
55
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proliferation and clubbing of the gill filaments; che degree of proliferacion
was progressive for che firsc four weeks, after which no measurable increase
was discernible. Examination of a sample of che fish cesced ac 6.1 C afcer
chree weeks in fresh wacer indicated no recovery had caken place from che
extensive proliferation. In the experiment with larger fish at 13.9 C a
marked recovery from hyperplasia was noced afcer che chree-week fresh wacer
exposure period. In che first experiment che proliferated areas had
consolidated; in the second chey had not. Burrows postulated chac concinuous
ammonia exposure is a precursor of bacterial gill disease.
Buckley et al. (1979) exposed duplicate groups (90 fish each) of
hatchery-reared coho salmon for 91 days co "river-water" solutions of NH^Cl
at concentrations of 0.019 to 0.33 mg/licer NH-jJ these were compared with
control groups reared ac 0.002 mg/licer Nl^- Hemoglobin concent and
hematocrit readings were reduced slightly, but significantly, ac che highesc
concencracion cesced, and chere was also a greacer percentage of immature
erychrocytes at che highest concentration. Blood ammonia and urea
concentrations were not significantly different after 91 days, regardless of
concencracion of ammonia co which che fish were exposed. Rankin (1979)
conducced ammonia cescs with embryos of sockeye salmon (Oncorhynchus nerka)
from fertilization to hatching. Total embryo mortality occurred at
concentrations of 0.49 to 4.9 rag/liter NH^; times co 50 percenc raorcalicy
ac these concentrations were 40 to 26 days. Morcalicy of che embryos exposed
co 0.12 rag/liter NHj was 30 percent, and cime co 50 percenc mortality was
66 days.
Two full life-cycle ammonia coxicicy cescs (354 and 379 days) were
conducced wich fathead minnows (Thurscon ec al., submitted). These cescs
began wich newly hacched fry and were continued through their growth,
56
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maturation and spawning stages; progeny were exposed from hatching through
growth to 60 days of age. No statistically significant differences were
observed based on spawning data (number of egg lots, egg lot size, egg lots
per female, eggs per female per day) for concentrations up to 0.4 rag/licer
NH3, but large reductions occurred at 0.8-0.9 mg/liter Nh^. There was a
substantial decrease of the percentage of fry hatching at concentrations of
0.19 mg/liter NH3 and higher (Table 2); no effect on hatching success was
observed at concentrations of 0.09 mg/liter Nh*3 and lower. Also, there was
some indication that length of time for incubation from spawning to hatching
increased with increasing NH3 concentrations. No statistically significant
effects on fish growth were observed for either parental fish or progeny
after 30 and 60 days exposure and at exposure termination at concentrations
up to '0.4 mg/liter NH3» but parental fish growth was substantially reduced
at 0.9 mg/liter NH3 after 30 days (at which concentration no progeny
existed). Significant mortalities occurred among the parental generation at
concentrations of 0.9 to 1.0 mg/liter NH3 afcer 30 and 60 days' exposure.
Head tissues from fathead minnows subjected to prolonged (up to 304
days) ammonia exposure were examined (Smith 1984). Growths, some massive,
were observed on heads of several fish exposed co concencrations of 1.25 and
2.17 mg/liter NH3, and swollen darkened areas were observed on heads of
several fish held at 0.639 to 1.07 mg/liter. Similar lesions were noted by
Thurston et al. (submitted) at lower concentrations, with swollen darkened
areas on heads being observed on some fish held at concentracions of 0.22
mg/liter NH^ and growths being observed at concentrations as low as 0.43
mg/liter NH3. Grossly and histologically the severity of the lesions,
which varied from mild to severe, was positively correlated with ammonia
concentration. Lesions appeared to be of a cell type originating from che
57
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primitive meninx covering the brain. The hyperplastic tissue often
completely surrounded the brain but was not observed around the spinal cord.
An early life-stage test initiated at the blastula stage of embryo-
genesis and extending through 39 days post-hatching was conducted with green
sunfish by McCoraick et al. (1984). Retardation of growth of green sunfish
exposed from embryo through juvenile life stages was found at NH-j
concentrations of 0.489 tag/liter and higher, but not at 0.219 mg/liter and
less (Table 2). In a long-tern test with green sunfish, Jude (1973) reported
that for treatments greater than 0.17 mg/liter NH3, mean fish weight
Increased less rapidly than controls after introduction of toxicant over the
next four days. Thereafter, fish exposed to 0.26 and 0.35 tag/liter MHj
grew at an increasing rate while fish exposed to 0.68 and 0.64 mg/liter NH3
remained the same for 12 days before greater increases in growth occurred.
An early life-stage test with bluegill from embryo through 30 days
post-hatch was conducted on ammonia by Smith et al. (1983). Significant
retardation of growth due to ammonia exposure was observed at 0.136 mg/Liter
; the no-observed-effect concentration was reported to be 0.063 mg/liter
(Table 2).
Broderius et al. (198S) conducted four simultaneous early life-stage
ammonia tests with smallmouth bass. These were carried out at four different
pH levels, ranging from 6.6 to 8.7, to examine the effect of pH on chronic
ammonia toxicity. Exposure to ammonium chloride solutions began with two- to
three-day-old embryos and lasted for 32 days. The effect endpoint observed
was growth, and ammonia was found to have a greater effect on growth at lower
pU levels than at high. NH3 concentrations found to retard growth (Table
2) ranged from 0.0558 mg/liter at pH 6.60 to 0.865 mg/liter at pH 8.68.
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Early life-stage Cests (29-31 days' exposure) on ammonium chloride with
channel catfish and white sucker were conducted by Reinbold and Pescitelli
(L982a). No significant effect on percent hatch or larval survival was
observed for channel catfish at concentrations as high as 0.533 mg/liter
NH3 and for white sucker as high as 0.239 mg/liter NH3. Significant
retardation of growth, however, occurred for channel catfish at
concentrations of 0.392 mg/liter NH-j and higher and for white sucker at
0.070 mg/ltter NH3 and higher (Table 2). A delay in time to swim-up stage
was also observed for both species at elevated (0.06 to 0.07 mg/liter NHj)
ammonia concentrations.
Robinette (1976) cultured channel catfish fingerlings for periods of
approximately one month at concentrations of 0.01 to 0.16 mg/liter NH-j.
Growth at 0.01 and 0.07 mg/liter NH3 was not significantly different from
that of control fish; growth retardation at 0.15 and 0.16 mg/liter NH^ was
statistically significant. Colt (1978) and Colt and Tchobanglous (1978)
reported retardation of growth of juvenile channel catfish during a 31-day-
period of exposure to concentrations ranging from 0.058 to 1.2 mg/liter
NH<3* Growth rate was reduced by 50 percent at 0.63 mg/liter NHj, and no
growth occurred at 1.2 mg/liter NH3. The authors hypothesized that growth
may be inhibited by high concentrations of Nti^* and low concentrations of
Na"1" in solution, and/or the NH^/Na"1" ratio. Soderberg et al. (1984)
found histopathologlcal gill lesions in pond cultured channel catfish raised
in NH3 concentrations from 0.02 to 0.067 mg/liter.
Early life-stage tests on ammonium chloride were conducted by Swlgert
and Spacie (1983) with channel catfish and fathead minnow (Table 2). For
both species, growth at ca. 30 days was the most sensitive of reported
responses to ammonia, significant reductions being observed at X>.24 mg/liter
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NH3 for channel catfish and at >0.33 mg/liter NH-j for fathead minnow.
Ammonia exposure for 30 to 40 days of goldfish and tench resulted in
lesions and diffuse necrosis of the caudal fin, causing it to degenerate
progressively to the point of breaking off by degrees, ultimately leaving
only a necrotized stump (Marchetti 1960).
Very little work has been done to investigate effects of different
factors on chronic ammonia toxiclty. The early life-stage tests at different
pH levels conducted by Broderius et al. (1985) with smallmouth bass showed
that NH3 toxicity increased with decreasing pH. Mitchell and Cech (1983)
reported that gill damage to channel catfish exposed to about 0.5 mg/1 NH3
occurred only In the presence of residual chlorine, apparently due to
monochloramine being the proximate agent. Soderberg et al. (1983) suggested
that, under wide diurnal variations of un-Ionized ammonia, growth reductions
of rainbow trout were better correlated with maximum daily concentrations
rather than mean concentrations. Sousa et al. (1974) reduced chronic
toxiclty of ammonia to chinook salmon by reducing pH and increasing salinity.
Derivation of Final Chronic Value for Fresh Water
(a) pH and Temperature Dependence of Chronic Ammonia Toxicity
Only one data set exists (Broderius et al. 1985) for which the same
investigator determined the chronic toxicity of ammonia to a fish over a
suitable pH range. These data (for smallmouth bass) show pH trends
qualitatively similar to those discussed earlier for acute toxicity, but
suggest a greater relative change in the pH 6.5-7.5 range. Interestingly,
total ammonia values were approximately constant at pH 7.8 and below. For
Macrobrachium rosenbergii (a saltwater prawn), Armstrong et al. (1978) also
found a more pronounced effect of pH on chronic toxicity than acute toxicity.
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Chronic effect concentrations expressed as total ammonia were also constant
at pH 7.6 and below.
The available data therefore do not adequately support the application
of the acute ammonia toxlcity pH relationship to chronic ammonia toxicity.
Furthermore, the available data are not sufficient to support the derivation
of a broadly applicable chronic pH relationship upon which even limited
confidence can be placed. Temperature effects on chronic toxicity are
totally lacking in the available data.
(b) Acute-Chronic Ratios
Acute-chronic ratios are available for ten species (Table 2). Because
these ratios vary so widely (3-43), their dependence on species and
physico-chemical factors should be evaluated so that they are properly
applied.
The smallmouth bass data in Table 2 .indicate that acute-chronic ratios
increase with decreasing pH. This is consistent with Che comment earlier
that the effect of ptt on chronic toxicity in the 6.5-7.5 pH range is greater
than the effect of pH on acute toxlcity. The large ratio for pink salmon
also suggests such a pH dependence of Che ratio, if it is assumed salaonids
have similar ratios. The paucity of data makes firm conclusions impossible,
but it is probably inappropriate to apply the pink salmon ratio (-43,
measured at pH 6.4) and the largest smallmouth bass ratio (-18, measured at
pH 6.6) to the pH range (>_7.3) at which other ratios were measured. At pH
greater than about 7.7, there is no clear indication that the pE dependence
of chronic toxicity differs from that of acute toxicity; consequently,
acute-chronic ratios are not expected to vary much, if any, in this pH range.
For temperature, no such clear effect exists. The highest ratio was
measured at low temperature (43 for pink salmon at 4 C), but the high value
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was probably la large part due to pH. The only other ratio at low
temperature is not particularly high (14 for rainbow trout at 9 C). The
second and third highest ratios were at higher temperatures (30 for white
sucker at 19 C and 20 for fathead minnow at 24 C), but all the low ratios
were also in or near this temperature range. In the absence of suitable
data, it will be assuaed here that ratios are not dependent on temperature.
The purpose of applying a ratio is to derive an estimate of a FCV from a
FAV when there is insufficient chronic data available to derive a FCV
directly. Since both a FAV and a FCV are estimates of the fifth percentlles
of their respective data bases, it is necessary that the ratio be appropriate
for applying to the lower part of the range of acute values to derive the
lower part of the range of chronic values. When a wide range of ratios are
present, this purpose requires a selection of those from an appropriate
sensitivity range of acute and chronic values.
Consideration will first be given here to acute-chronic ratios at pH >
7.7, where ratios will be assumed here to be constant wtth pH. The procedure
for selecting the ratios appropriate for determining a FCV from a FAV was as
follows. In this pH range, chronic values and acute-chronic ratios are
available for nine species in Table 2. Consideration was first restricted to
those species with chronic toxicity less than or equal to the median, which
included the channel catfish, rainbow trout, white sucker, bluegill, and
fathead minnow. Species above the median (green sunfish, smallmouth bass,
and two daphnids) had markedly higher chronic values (>0.3 mg/liter ^3)
which are probably well above the range a FCV will assume, especially
considering the diverse nature of the five species selected. The five acute
chronic ratios so selected were 10 (channel catfish), 12 (bluegill), 14
(rainbow trout), 20 (fathead minnow), and 30 (white sucker), with a geometric
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mean of 16. The higher ratio for the fathead minnow was used because it was
for a whole life-cycle test which determined effects of ammonia on
reproduction, apparently a more sensitive endpoint than the growth effects
examined in other studies. The lower ratio for rainbow trout was used in
part because it also was for a whole life-cycle, test and in part because the
other, higher ratio (-22) was for a pH slightly below the range of concern
here.
However, before this average ratio is judged appropriate for deriving a
FCV, greater scrutiny should be given to the data used in its derivation. As
suggested above, an appropriate ratio is one which, when applied to a low
percentile In the distribution of acute values, will produce the same
percentile for chronic values. Thus, while it is appropriate to restrict
consideration of acute-chronic ratios to species with chronic values less
than the median,, the relative acuce values used should also be examined as to
whether they are consistent, on the average, with the chronic values used.
For example, the high ratio for the white sucker is-apparently due to it
being, relative to other species, more chronically sensitive than acutely
sensitive. Other species have apparent biases in the other direction. What
is important is whether the average relative acute and chronic values of the
data used are consistent.
More specifically, the average percentile level of the acute data used
for the ratios should approximately equal that of the chronic data used.
Corrected to reference pH (3.0) and temperature (20 C), the geometric average
of the acute values used for generating the five ratios above is 1.36. This
corresponds to between ranks 12 and 13 in the data in Table 3, which, using
the cumulative probability formula P-Rank/(N+l), is equivalent to about the
35th percentile. Due to the small amount of data and the uncertain effect of
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pH and temperature on chronic toxlcity (and thus the relative chronic
toxicity of the 11 species in Table 2), the average percentile level of the
chronic data used is less easily estimated, but should lie between 30 and 40,
most probably in the middle part of this range. Because of the similarity of
the percentile levels so estimated and because more exact analysis cannot be
supported by the limited database currently available, an acute-chronic ratio
of 16 is recommended here as being most appropriate for the estimation of a
FCV from a FAV when pH > 7.7.
For low pH, few data are present. At pH near 6.5, available ratios are
43 for :he pink salmon and 13 for the smallmouth bass, with a geometric mean
of 28. Even this ratio may be too low if the smallmouth bass is as
relatively insensitive in chronic tests at low pH as it is at high pH. The
higher acute-chronic ratio (-22) for rainbow trout at pH - 7.4 may be
indicative of somewhat higher ratios at moderate pM. No definite conclusion
is made here about appropriate ratios at lower pHs, except that they are
probably greater than 20 and will require further.testing.
(c) Application of Acute-Chronic Ratios and pa Relationship of Chronic
Ammonia Toxicity to Determination of Final Chronic Values
In the absence of sufficient data to directly compute final chronic
values (FCVs), both with respect to the number and variety of chronic tests
in Table 2 and to the Inadequate data on the pH- and temperature-dependence
of chronic toxicity, the following approach was adopted for setting FCVs:
(1) To generate a FCV, an acute-chronic ratio must be applied to an
appropriate FAV. The FAVref used for the 1-hour average
criterion (0.52) is not appropriate since it is based on a life
stage that is more sensitive than those used in generating the
acute-chronic ratios. Furthermore, the fifth-percentile
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FAVref computed earlier (0.70) is also noc appropriace since
ic is strongly influenced by che mouncain whicefish data, which
also was for a sensitive life stage. To compensate for chis
problem, che mouncain whicefish SMAVref was increased by 40%,
from 0.56 co 0.78, based on che difference between che acuce
sensicivicies of rainbow crouc of che size of che cesced whicefish
and of che size used for generacing che acuce-chronic racio. The
FAVref was chen recomputed co be 0.80, which will be used in
subsequenc calculations of FCVs.
(2) Due co cne lack of information on che effects of temperacure on
chronic coxicicy for any organism and due co che lack of any
chronic coxicicy daca for salmonids at temperatures above 15 C, che
temperature relationship implicit in applying an acuce-chronic
racio to a FAV will be capped at 15 C rather than 20 C as in
Equation 8 for sites with salmonids or other sensitive coldwacer
species. For sites without salmonids and other sensitive coldwater
species, TCAP will be 5 C higher, as for acute toxicity. This will
result in the use of the following formula for che factor TCAP when
computing a FCV:
TCAP * 15 C ; salroonids present (9)
• 20 C ; salmonids absent
These temperature caps are again placed here because the national
criterion must be broadly protective and uncercaincies require chis
rescriccion in order co guarancee proceccion for certain organisms.
The cap may be raised in a sice-specific analyses as warranted by
the species present. The increase in the temperature cap should
not be beyond where there is data that indicates the FCV will be
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proceccive of che raosc sensitive genera present at che sice; in
particular, a FCV should noc result ac any cemperacure chac is
significantly greater chan che CV ac che highest cemperacure cesced
for any site genera.
(3) At pH 7.7 and above, an acute-chronic ratio of 16 will be applied
to FAV(pH,T) to calculate FCV(pH.T), this constant ratio being
estimated as described above. The equation for FCV at pH > 7.7
therefore is:
prvfnH TO =- °-80 (10)
FCV(pH.T) - 16.pT.FpH
where FPH is as in equation 8 and FT is as in equation 9.
(4) At pH Below 7.7, the FCV will be based on the observation made
above chac chronic coxicicy has been found to be approximately
constant on a total ammonia basis in this pH range. The FCV as
un-ionized ammonia at any pH and temperature must therefore be sec
so that the corresponding total ammonia is che same as ac pH = 7.7
and chac cemperacure. The applicable equacion is:
1 •»•
FCV(pH,T)-FCV(7.7,T) •
0.80 1 +
19.2-FT 1 * 10PK~PH
where pK is che ammonia speciation stability constant at T. This
formula can be simplified by noting chac, for che pHs and
temperatures of concern, 10PK~PH»1. The equation then
approximately becomes:
FCVUH -n - °'80
FCV(pH.T)
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This equation concaina an implicit: acute-chronic ratio equal to:
19.2-107-7-PH 24-lQ7-7"PH
RATIO(pH) - FpH - n-io/.^-pH (u
which varies from 16 at pH 7.7 to 42 at pH 6.5. This implicit
ratio can probably be applied to sice-specific calculations in this
pH range.
It should be noted that the pH and temperature-dependent FCV so derived
are within a factor of two of the chronic values for several species
(Atlantic salmon, rainbow trout, fathead minnow, white sucker, and bluegill)
in Table 2 if the temperature cap is ignored. It is also close to a chronic
effect concentration for the clam Musculium transversum in Table 5. These
relative differences give some indication that the criteria is approximately
correct, since they are similar to the difference between the acute
sensitivity of these species and the FAVref used and are not so large
that markedly higher criteria are possible without impacting several, species.
That the relative margins do not appear to be markedly different for species
tested at cold temperature than at warm temperature also provides some
reassurance as to the appropriateness of applying che same slope for
temperature dependence to chronic toxicity as to acute toxicity. This should
not be taken, however, as strong evidence for the temperature relationship
used; considerable uncertainty exists in the pH- and temperature-dependence
for chronic toxicity, necessitating further research if more reliable
criteria are to be developed.
(d) Application of the FCV to a Criterion to Protect Against Chronic Toxicity
As specified in the Guidelines, the criterion to protect against chronic
toxicity of the types represented in Table 2 will be based on requiring chat
4-day average concentrations not exceed, more often on the average than once
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every 3 years, an average FCV based on Equations 10 and 12 above. In che
cypical situation, where flows, pHs, and temperatures fluctuate, che average
FCV should not be obtained simply by applying che equations co che average
flow, pH, and cemperacure, but should rather equal or approximate che
arithmetic mean of a time series of FCVs reflective of che fluctuations.
Part of che intent of che short (4-day) averaging period, as opposed co
a longer period (e.g., 30-day) more reflective of the duration of cests in
Table 2, is co preclude time series of concentrations chac would
subscancially exceed che criterion concencration for a substantial fraction
of the longer period. A longer period will be allowed for some situations
where limited variability of concentrations can be demonstrated. This matter
is discussed in more detail in che Technical Support Document for Water
Quality-Based Toxics Control (U.S. EPA, 1985).
Saltwater Animals
Little information is available on long-term effects of sublethal
ammonia exposures on saltwater species, and no chronic data are available for
any saltwater fish species.
Three-week exposure (Wickins 1976) of £. setiferus co NH^Cl yielded an
EC50 (Table 5), based on growth reduction, of 0.72 mg/liter NT^. A
six-week test (Table 5) with tl. rosenbergii resulted in reduction in growth
co 60-70 percent that of controls for prawn exposed to concentrations above
0.12 mg/liter NH^. A "maximum acceptable level" was estimated to be 0.12
rag/liter NHj. Armstrong et al. (1978) conducted growth tests (Table 5) on
NH^Cl using prawn larvae (11. rosenbergii). Retardation in growth was
observed at sublethal concentrations (0.11 mg/liter NH3 at pH 6.83 and 0.63
mg/liter NH^ at pH 7.60), and this effect was greater ac low pH.
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TOXICITY TO AQUATIC PLANTS
Bacteria and Freshwater Plants
Ammonia is known to play an Important part in the nitrogen metabolism of
aquatic plants. In the aquatic environment, nitrogen plays an important role
in determining the composition of phytoplankton and vascular plant communi-
ties and in some cases can act as a limiting nutrient in primary production.
Ammonia can also be toxic at certain concentrations. Data concerning the
toxicity of ammonia to freshwater vascular plants and phytoplankton are
contained in Table 4. Few of the papers examined contained sufficient
information to enable calculation of un-ionized ammonia concentrations,
altough total ammonia solutions were more toxic at high than at low pH, indi-
cating that toxicity was likely due primarily to NH3 rather than NH^.
Some information on ammonia effects on bacteria is also included here.
The bacterial species Escherichia coli and Bacillus subtilis were found
to be sensitive to NH4C1 (Deal et al. 1975); 1100 mg/liter NH3 killed 90
percent of an £_. coli population in 78 minutes. B^ subtilis, an aerobic,
spore-forming bacterium, was destroyed in less than two hours in 620 mg/liter
NHj. NHj inhibition of the bacteria Nitrosomonas (that convert ammonium
to nitrite) and the bacteria Nitrobacter (that convert nitrite to nitrate)
was studied by Anthonisen et al. (1976) and Neufeld et al. (1980). NH3
inhibited the nitrification process at a concentration of 10 mg/liter
(Neufeld et al. 1980). The NH3 concentrations that inhibited nitrosoinonads
(10 to 150 mg/liter) were greater than those that inhibited nitrobacters (0.1
to 1.0 mg/liter), and NH3, not NH^, was reported to be the inhibiting
species (Anthonisen et al. 1976). Acclimation of the nitrifiers to NH3,
temperature, and the number of active nitrifying organisms are factors that
may affect the inhibitory concentrations of NH^ in a nitrification system.
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Langowska and Moskal (1974) investigated the inhibitory effects of
24-hour exposures to NHj on pure cultures of ammonifying and denitrifying
bacteria. Effects examined vere based on ability of the bacteria to produce
some specific metabolic processes, such as proteolysis, ammonification,
denitrlfication, and nitrification. Ammonifying and denitrifying bacteria
were most resistant to NHj; proteolytic and nitrifying bacteria vere the
most sensitive. Concentrations ranging from 0.8 to 170 mg/liter NHj did
not adversely affect denitrifying and asmonifying bacteria; 220 mg/liter
caused reduction of the examined metabolic processes. Froteolytic bacteria
were unaffected at 0.8 mg/liter NH3, but were reduced to zero at 4.2
mg/liter; nitrifying bacteria were unaffected at 2.6 to 5.1 mg/liter and
reduced to zero at 13 to 25 mg/liter.
Experimental data concerning the toxiclty of ammonia to freshwater
phytoplankton are limited. Przytocka-Jusiak (1976) reported ammonia effects
(Table 4) on growth of Chlorella vulgaris with 50 percent inhibition in five
days at 2.4 mg/liter NH3, and complete growth inhibition in five days at
5.5 mg/liter. The NHj concentration resulting in 50 percent survival of C.
vulgaris after five days was found to be 9.8 rag/liter Nl^. In a separate
study, Przytocka-Jusialc et al. (1977) were able to isolate a £. vulgaris
strain with enhanced tolerance to elevated ammonia concentrations, by
prolonged incubation of the alga in ammoniim carbonate solutions. £.
vulgaris was reported to grow well in solutions containing 4.4 mg/liter
NH3, but growth was inhibited at 7.4 mg/liter (Matusiak 1976). Tolerance
to elevated concentrations of MH3 seemed to show a slight increase when
other forms of nitrogen were available to the alga than when ammonia was the
only form of nitrogen in the medium. The effects of ammonia on growth of the
algal species Ochromonas sociabilis was studied by Bretthauer (1978). He
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found that concentrations (assuming pH 6.5 and 30 C) of 0.6 rag/liter NH3
killed the organisms, and at 0.3 mg/liter development of the population was
reduced. Concentrations of 0.06 to 0.15 mg/liter NH3 had insignificant
effect on growth, and 0.015 to 0.03 mg/liter enhanced growth.
Effects of ammonia on four algal species (Table 4) were studied by
Abeliovich and Azov (1976). Ammonia at concentrations over 2.5 mg/liter
NH3 inhibited photosynthesis and growth of the algal species Scenedesmus
obliquus and inhibited photosynthesis of the algae Chlorella pyrenoidosa.
Anacystis nidulans, and Plectonema boryanum. Hosier (1978) reported that
NHj concentrations causing 50 percent reduction in oxygen production by the
green alga Chlorella ellipsoidea and blue-green alga Anabaena subcylindrica
were 16.0 x 10~8 and 251.0 x 10~8 ug NH3-N/cell, respectively.
The rate of photosynthesis in the blue-green alga P\ boryanum was
observed to be stimulated by NH4+, but inhibited by NH3 (Solomonson
1969); the magnitude of these effects was dependent on the sodium-potassium
composition of the suspending media. NH3 inhibition of photosynthesis was
associated with a conversion of inorganic polyphosphate stored in the cells
to orthophosphate.
Champ et al. (1973) treated a central Texas pond with ammonia to a mean
concentration of 25.6 mg/liter ^3. A diverse population of dinoflagel-
lates, diatoms, desmids, and blue-green algae were present before ammonia
treatment. Twenty-four hours after treatment the mean number of
phytoplankton cells/liter was reduced by 84 percent. By the end of two weeks
(NH3 "3.6 mg/liter) the original concentration of cells had been reduced
by 95 percent.
Much of the work concerning the response of freshwater vegetation to
high ammonia concentrations is only descriptive or is a result of research
exploring the possible use of ammonia as an aquatic herbicide.
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Champ et al. (1973) reported virtually complete eradication of rooted
aquatic vegetation (water shield, Brasenla schreberi, and American lotus,
Nelumbq sp.) in a central Texas pond within two weeks after treatment with
anhydrous ammonia; NHj concentration was 25.6 nig/liter 24 hours after
ammonia addition, and 3.6 mg/liter two weeks later. In experiments with
Potamogeton lucena, Litav and Lehrer (1978) observed that ammonia, which
forms a readily available nitrogen source for the plant, can be toxic when
present at high concentrations, with ammonia causing appreciable injury to
detached branches. Ammonia inhibition of growth of Eurasian watermilfoil
(Myrlophyllum spicatum) affected length and weight similarly and affected
roots and shoots similarly (Stanley 1974).
Litav and Agami (1976) studied changes in vegetation in two rivers
subject to increased pollution from agricultural fertilizers, urban sewage,
and industrial wastes, and attributed the changes in plant species
composition primarily to ammonia and detergents. Agami et al. (1976)
transplanted seven species of "clean water" macrophytes to various sections
of river, and found that ammonia affected only Nymphaea caerulea. Use of
high concentrations of ammonia to eradicate aquatic vegetation was described
by Ramachandran (1960), Ramachandran et al. (1975), and Ramachandran and
Ramaprabhu (1976).
Saltwater Plants
Data concerning the toxicity of ammonia to saltwater phytoplankton are
presented in Table 4. Ten species of estuarine benthic diatoms were cultured
for ten days in synthetic media at a range of NH3 concentrations from 0.024
to 1.2 mg/liter NH3 (Admiraal 1977). A concentration of 0.24 mg/liter
NH3 retarded the growth of most of the tested species (Table 4). Relative
tolerance to ammonium sulfate of five species of chrysomonads was studied, by
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Pinter and Provasoli (1963). Coccolithus huxleyi was most sensitive, and
Pavlova gyrana and Hymenomonas sp. were most tolerant, with intermediate
tolerance exhibited by Syracosphaera sp. and Ochrosphaera neapolitana.
Shilo and Shilo (1953, 1955) reported that the euryhaline algae
Prymnesium parvum was effectively controlled with applications of ammonium
sulfate, which exerted a lytlc effect. Laboratory and field tests showed
that the concentration of ammonium sulfate necessary for cell lysis decreased
with increasing pH, indicating that un-tonized ammonia and not the ammonium
ion is responsible for the lytic activity of ammonium sulfate on _P_. parvum.
Effect of ammonia on the dinoflagellate Amphidinium carterae was studied by
Byerrum and Benson (1975), who reported that added ammonium ion at
concentrations found to stimulate the photosynthetlc rate also caused the
algae to release up to 60 percent of fixed * CC>2 to the medium.
Natarajan (1970) found that the concentrations of fertilizer plant
effluent toxic to natural phytoplankton (predominantly diatoms) in Cook
Inlet, Alaska, were between 0.1 percent (1.1 mg/liter NH-j) and 1.0 percent
(11 mg/liter NH-j). At 0.1 percent effluent concentration 14c uptake
was reduced only 10 percent, whereas at 1.0 percent effluent concentration a
24-33 percent reduction in the relative * C uptake was observed. Effects
of ammonium sulfate on growth and photosynthesis of three diatom and two
dinoflagellate species were reported by Thomas et al. (1980), who concluded
that increased ammonium concentrations found near southern California sewage
outfalls would not be inhibiting to phytoplankton in the vicinity. Provasoli
and McLaughlin (1963) reported that ammonium sulfate was toxic to some marine
dinof lagellates only at concentrations far exceeding those in sea water.
No data were found concerning the toxiclty of ammonia to saltwater
vegetation.
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BIOACCUMULATION
No data are available concerning the accumulation of ammonia by aquatic
organisms.
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OTHER DATA
A timber of investigators have studied effects of ammonia on behavior
and various metabolic processes of exposed animals, or have conducted field
studies. This research has dealt predominantly with freshwater fishes.
Freshwater Invertebrates
The effect of ammonia (Table 5) on the ciliary beating rate of clam
gills was investigated by Anderson et al. (1978). Concentrations of 0.036 to
0.11 mg/liter NH3 caused a reduction in ciliary beating rate of fingernail
clams; the effect of these concentrations ranged from 50 percent reduction in
beating rate to complete inhibition of cilia. Adult clams (>5 mm) were more
sensitive than juveniles (<_-5 mm); adults were also slightly more sensitive
than the unionid mussel (Elliptic complanata) and the Asiatic clam (£.
aanllensis). Shaw (1960) investigated effects of ammonium chloride on sodium
influx in the freshwater crayfish, Astacus pallipes. Ammonia produced an
inhibition of sodium influx; a concentration of 18 mg/liter NH^+ reduced
the Influx to about 20 percent of its normal value, and influx reduction was
related to greater ammonia concentration. This effect was attributed to
NH^"*" ions and not to any toxic effect exerted on the transporting cells
by un-ionized ammonia. NH^"*" did not affect chloride influx nor the rate
of sodium loss.
Ammonia was added to a Kansas stream at a 24-hour average concentration
of 1.4 mg/liter NHj, and a 24-hour drift net sampling was conducted
(Liechti and Huggins 1980). No change in diel drift pattern was observed,
but there was an increase in magnitude of drift, a shift in kinds of
organisms present, and changes in benthic standing crop estimates; the
ammonia concentration was concluded to be nonlethal.
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Freshwater Fishes
Herbert and Shurben (1963) investigated the effect on susceptibility to
ammonium chloride solutions of rainbow trout forced to swim continuously
against water currents of different velocities prior to ammonia exposure.
Forcing rainbow trout to swim for one to two days at 85 percent of the
maximum velocity they could sustain increased their susceptibility only
slightly, corresponding to a 20 to 30 percent reduction in the 24- or 43-hour
LC50.
The behavioral response of blacknose dace (Rhinichthys atratulus) to
ammonium chloride solutions has been studied (Tsai and Fava 1975; Fava and
Tsai 1976); the test fish did not avoid concentrations of 0.56 or 4.9
mg/liter NH^, nor did these concentrations cause significant changes in
activity. Avoidance studies were conducted by Westlake and Lubinski (1976)
with bluegill using ammonium chloride solutions. Bluegill detected
concentrations of approximately 0.01 to 0.1 mg/liter NE^, and evidenced a
decrease in general locomotor activity. No apparent avoidance of ammonia was
observed, and there was some indication of an attraction. Behavioral
responses of bluegill to a five-hour exposure to 0.040 rag/liter NHj,
although variable, were related to at least a small amount of physiological
stress either at the gill or olfactory surfaces. At a concentration of 0.004
mg/liter NHj, bluegill evidenced slight temporary increases in both
activity and turning behavior; no preference or avoidance was demonstrated,
with responses seemingly exploratory (Lubinski et al. 1978, 1980). Wells
(1915) investigated the avoidance behavior of bluegill to ammonium hydroxide
solutions and reported that fishes did not avoid ammonia prior to being
killed by it. In a study of the repelling ability of chemicals to green
sunfish, Summerfelt and Lewis (1967) concluded that concentrations of ammonia
76
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high enough to repel fish would be rapidly fatal. In avoidance experiments
with threespine stickleback, solutions of ammonia concentration 0.27 mg/liter
NHj elicited a positive (attraction) response from the test fish (Jones
1948).
Wo1taring et al. (1978), in tests with largemouth bass and mosquito fish,
demonstrated that predator-prey interactions were sensitive to sublethal
concentrations of NH}- Ammonia concentrations of 0.63 and 0.36 mg/llter
NHj decreased prey consumption and bass growth; bass were reported to be
more sensitive than roosqultofish to NH^. The effect of ammonium chloride
on consumption of juvenile chinook salmon by brook trout was studied by
Hedtke and Norris (1980). At the lowest test concentration of 0.29 ing/liter
NHj, trout consumption rates decreased as much as 65 percent. As ammonia
concentration increased, however, consumption of prey increased and was
double that of controls at the highest tested concentration of 0.76 mg/liter
NH-j. Increased consumption rate was related to both increased NH^
concentration and increased prey density. The magnitude of the effect of
ammonia was not the same at all prey densities, having a greater effect on
consumption rate at high than at low prey densities. Mortalities were
observed among prey salmon at the highest ^3 levels, and these were
attributed to the combined effect of NHj and stress from presence of the
predator. Brook trout exhibited toxic effects due to NH-j-
NH^Cl and NH^HCOj solutions were injected intraarterially into
rainbow trout (Hillaby and Randall 1979). The same dose of each compound was
required to kill fish, but there was a more rapid excretion of NH^ after
NI^HCO-j infusions, resulting in higher NH^ concentrations in blood,
than after NH^Cl infusions. Ammonium acetate solutions of different
concentrations were injected intraperitoneally into three species of fishes
77
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(Wilson 1968; Wilson et al. 1969). LDSOs (tnmoles/kg body weight) for channel
catfish for one to four hours was 26.7 to 18.7, for goldfish for one hour
were 29.3 and 29.6 in two separate tests, and for rainbow trout for one hour
was 17.7. Goldfish was the most resistant species tested and rainbow trout
the least resistant. Nehring (1964) compared toxicity of ammonia in the
water to toxicity of ammonia administered orally and concluded that the
threshold and lethal concentrations were considerably lower for ammonia in
water than for ammonia administered orally.
Acute symptoms of NH^ toxicity to brown trout sac fry and 12-day-old
fry were described by Penaz (1965), who exposed fry to concentrations ranging
from 0.08 to 50.0 mg/liter NH^. Symptoms caused by NHj exposures were:
rapid spasm-like movements at concentrations of 2.0 mg/liter NH-j and higher
within 16-17 minutes of exposure; after 40 minutes these symptoms were also
observed at 0.4 mg/liter NH-j. After 2.5 hours these abnormal movements
ceased, and at 10 hours heart activity was decreased and fish lost movement
ability at the higher (XZ.O mg/liter NH}) concentrations. Other symptoms
included inability to react to mechanical stimulation and disorders in rhythm
of mouth movements culminating in the mouth's staying rigidly open. Thumann
(1950), working with rainbow trout and brook (-brown?) trout, described
observed symptoms of ammonia poisoning to fishes to be convulsions and
frequent equilibrium and positional anomalies.
Smart (1978) reported that exposure of rainbow trout to an acutely
lethal concentration of 0.73 mg/liter NH^ resulted in an increase in oxygen
consumption, increase in ventilation volume, decrease in percent oxygen
utilization, increase in respiratory frequency and amplitude (buccal
pressure), decrease in dorsal aortic blood PQO> increase in dorsal aortic
blood pressure, and increase in mean heart rate. Physiological parameters
78
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not significantly affected by NH3 exposure were "cough" rate, dorsal aortic
blood pH, blood P50, erythrocyte count, hematocrit, and hemoglobin
concentration. Coho salmon exposed to concentrations ranging from 0.094 to
0.162 mg/liter NH3 (Sousa and Meade 1977) exhibited hyperexcitability,
hyperventilation, ataxia, and progressive acidemia; methemoglobin
concentrations in blood of exposed fish did not differ significantly from
those of controls. Effects on trout (species not specified) blood with
exposure to accumulated excreted NH3 were investigated by Phillips et al.
(1949) and were reported to include an increase in blood carbon dioxide
content and a decrease in oxygen content.
Arillo et al. (1979d) measured gill sialic acid content in rainbow trout
exposed to NH^OH or NH^Cl solutions ranging from 0.05 to 0.5 mg/liter
NH3, and reported that Increasing NH3 concentrations produced increasing
gill sialic acid content. Elevated gill sialic acid levels were also
produced by higher ammonium ion (NH^***) concentrations at Identical NH3
concentrations, and the authors concluded that NH^"*" was a stressor
causing elevated sialic acid levels. Exposure of rainbow trout (14-ca
length) for four hours to OT^Cl and NH^H solutions of concentrations
ranging from 0.094 to 0.50 mg/liter NH3 resulted in increased proteolytic
activity and free amino acid levels in the fish livers, but no statistically
significant change in fructose 1,6-biphosphatase enzyme activity (Arillo et
al. 1978, 1979a). Renal renin activity was reported (Arillo et al. 1981b) to
increase in rainbow trout exposed to concentrations of 0.043 to 0.61 mg/liter
NH3. A significant decrease in liver glycogen and increase in free glucose
were observed in rainbow trout exposed to NH^Cl solutions for four hours at
a concentration of 0.048 mg/liter NH3, and a decrease in total carbo-
hydrates was observed at 0.12 mg/liter NH3 (Arillo et al. 1979b). For
79
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trout similarly treated with ammonium hydroxide, significant decreases in
glycogen and carbohydrates, and Increase in glucose occurred at 0.097
mg/liter ^3-
A statistically significant increase in rainbow trout liver
concentrations of cyclic-3',5'-adenosine-monophosphate (cAMP) was reported by
Arillo et al. (1979c) to be induced by a four-hour exposure to elevated
ammonia concentrations of 0.011 to 0.124 mg/liter NH3« Decreases in liver
glycogen levels were also measured and were significantly different from
controls only in the trout exposed to 0.048 mg/liter NH3» the highest
exposure used for glycogen measurements. The authors concluded that cAMP
measurements provided a very sensitive means of discerning fish stress even
at very low toxicant concentrations, although quantitative measurement of
stress intensity was not possible. Lysosomal lability was also investigated
as an indicator of stress in rainbow trout due to ammonia exposure (Arillo et
al. 1980), and was reported to increase significantly for fish subjected to
concentrations of 0.048 to 0.61 mg/liter NH3. Exposure of rainbow trout
for four to 48 hours to 0.024 to 0.61 Tig/liter NH3 resulted in changes in
various brain and liver metabolites; the magnitude of the changes was depen-
dent on both exposure time and 1*83 concentration (Arillo et al. 1981a) .
Exposure of walking catfish (Clarias batrachus) to ammonia caused
inhibition of fish brain cholinesterase and kidney peroxldase activity
(Mukherjee and Bhattacharya 1974, 197Sa). Plasma corticosteroid
concentrations were measured (Tomasso et al. 1981) in channel catfish exposed
to 1.1 mg/liter NH3 for 24 hours; corticosteroid levels increased
initially, peaked after eight hours, then decreased. The overall increase
was approximately tenfold over normal levels.
Sorting (1969b) reported that carp exposed to 1 mg/liter NU3 exhibited
an increase in number of blood erythrocytes, reaching an initial maximum
80
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after several hours followed by a gradual decrease; after 50 hours the number
was less than the average for non-exposed fish. Other blood changes from the
ammonia exposure were: thickening of individual erythrocytes, reduction of
osmotic resistance of erythrocytes, increase in concentrations of urea and
lactic acid, and decrease in ATP concentration. Levi et al. (1974) reported
that goldfish exposed for 24 hours to NH^Cl solutions exhibited increases
in cerebral and blood concentrations of glutamine and in other amino acids,
with changes most pronounced in the brain. Concentrations of free amino
acids in livers showed only slight increases of a few amino acids, including
glutamine, and the concentration of I/sine decreased. Mo change in
concentrations of free amino acids was observed in kidneys. Rainbow trout
exposed to 0.33 mg/liter NH3 had significantly higher packed cell volumes;
exposures to concentrations of 0.24 mg/liter NH3 and higher resulted in
significantly raised blood glucose and plasma cortisol concentrations (Swift
1981).
Diuretic response of rainbow trout exposed to. concentrations of 0.09 to
0.45 mg/liter NH3 was studied by Lloyd and Orr (1969). After an initial
lag period, urine production increased rapidly during exposure then returned
to normal within a few hours after discontinuation of NH^ exposure. A
no-observed-effect concentration was reported to be 0.046 mg/liter Nl^.
Goldfish were exposed to solutions containing 1.0 to 1.9 mg/liter NH3
(Fromm 1970; Olson and Fromm 1971); onset of death was characterized by a
gradual cessation of swimming movements and settling to the bottom of the
tank. Some goldfish near death were returned to ammonia-free water in which
they recovered to at least some degree. In similar experiments (Fromm 1970;
Olson and Fromm 1971) rainbow trout were exposed to ambient total ammonia
concentrations of 0.04 to 0.2 mg/liter NHj. There was a. decrease in total
81
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nitrogen excreted with increase in ambient NH3> and a concomitant decrease
in the NHj portion of total nitrogen excreted; urea and protein nitrogen
excretion ratss shoved no changes as ambient NH-j increased* Onset of death
for trout was characterized by violent thrashing movements*
Exposure of rainbow trout to solutions of NH^Cl for 24 hours (Fromm
and Gillette 1968; Fromm 1970) showed that an increase in ambient water NH3
concentration resulted in a corresponding increase in blood NH^
concentrations, and a decrease in total nitrogen and NH3 excretion. The
decrease in NH^ excretion accounted for half or less of the total nitrogen
excretion,, depending on the water NHj concentration, indicating that the
reduction in NU3 excretion was to some extent compensated for by increased
excretion of some other nitrogenous compound(s).
Young fry (2-20 days old) of loach (Misgurunus anguilicaudatus) and carp
were exposed for five to 70 hours to ^N~labeled ammonium chloride
solutions at six concentrations from 0.002 to 0.064 ag/liter NH3 (Ito
1976), and the proportion of ^N relative to total N in the fishes
determined. Ammonia was shown to be directly absorbed by the fry; nitrogen
conversion rate increased with increasing ammonia concentration and exposure
time. Nitrogen conversion rates for carp fry decreased as fry age increased
from 3 to 20 days. After 48 hours of exposure to 0.064 ng/liter NH3
followed by transfer to ammonia-free water, rapid excretion (15-20 percent)
of the absorbed ^*N occurred during the first hour in ammonia-free water.
Excretion rate then slowed, with about 50 percent of the absorbed ^N
being retained after 48 hours in ammonia-free water. Comparison of N
absorption rates between live and sacrificed three-day-old carp fry showed
one-third to one-half the uptake of 15N by dead fry compared with live,
82
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indicating chat the uptake of ammonia from water by live fish occurs not only
by simple membrane permeation but also by metabolic action.
Flagg and Hinck (1978) reported that exposure to NH3 lowered the
resistance of channel catfish to the pathogen Aeromonas hydrophila. In 17-
and 28-day tests, increasing exposure concentrations from 0.02 to 0.04
mg/liter NH3 resulted in increasing numbers of bacteria in host livers.
Schreckenbach et al. (1975) reported that ammonia in pond water leads to
outbreaks of gill necrosis in carp, accompanied by an increase in ammonia
concentration in serum of the fish. This is aggravated at elevated pH levels
due to increasing inhibition of ammonia excretion at increasing pH levels,
with ammonia excretrton being almost totally blocked at pH values above 10.5.
After investigating the possible role of parasites, bacteria, viruses, and
other ultramicroscopic agents in causing gill necrosis, the authors concluded
that pH-dependent intoxication or autointoxication with ammonia was the sole
cause of the gill damage. Studies of the treatment and prophylaxis of gill
necrosis using 28 different therapeutical preparations led to the conclusion
that only those preparations that lowered the water-pH level and/or ammonia
concentrations resulted in an improvement in clinical symptoms.
Increase in frequency of opercular rhythm in fishes was monitored as a
means to measure fish response to sublethal concentrations of ammonia (Morgan
1976, 1977). Ammonia threshold detection concentration (Table 5) for
largemouth bass was approximately 30 percent of the LC50 for that species.
Increases in largemouth bass opercular rhythms and activity were
electronically monitored (Morgan 1978, 1979) to determine threshold effect
ammonia concentrations (Table 5); for a 24-hour exposure the effect
concentration for opercular rhythms was 0.028 mg/liter NH3 and for activity
was 0.0055 mg/liter. Lubinski et al. (1974) observed that ammonia stress
apparently caused bluegill to consume more oxygen.
83
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In field experiments In an Arizona mountain lake, mortalities of caged
rainbow trout were attributed to high un-ionized anmonia concentrations and
high pH levels; 20 to 100 percent of test fish died in 24 hours at NH3
concentrations of 0.109 to 0.225 mg/liter (Fisher and Ziebell 1980). Ammonia
added to a Kansas stream at a 24-hour average concentration of 1.4 mg/liter
NH3 resulted in fry of slender madtom (Notorua exilis), Notropis sp., and
orangethroat darter being collected in large ntnbers in a 24-hour drift net
sampling; these fishes are not normally found in drift net samples, and their
presence was attributed to toxic effects of the ammonia (Liechti and Huggins
1980).
Saltwater Invertebrates
Sublethal toxlcity of NH^Cl to the quahog clam and eastern oyster was
studied by Epifanio and Srna (1975) who measured the effect of ammonia over
20 hours on the rate of removal of algae (Isochrysis galbana) from suspension
(clearing rate) by the clams and oysters. Concentrations of 0.06 to 0.2
mg/liter NH3 affected clearing; no difference was observed between
juveniles and adults. The effect of ammonia on the ciliary beating rate of
the mussel Mytilus edulis was studied by Anderson et al. (1978).
Concentrations of 0.097 to 0.12 mg/liter NH3 resulted in a reduction in
ciliary beating rate from 50 percent to complete inhibition (Table 5).
Exposure of unfertilized sea urchin (Lytechinus pictus) eggs to NH^l
resulted in stimulation of the initial rate of protein synthesis, an event
that normally follows fertilization (Winkler and Grainger 1978). NH^l
exposure of unfertilized eggs of Strongylocentrotus purpuratus, L^. pictus,
and Strongylocentrotus drobachiensis was reported (Paul et al. 1976; Johnson
et al. 1976) to cause release of "fertilization acid", more rapidly and in
greater amounts than after insemination. Activation of unfertilized L^.
pictus eggs by Nt^Cl exposure was also evidenced by an increase in
84
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intracellular pH (Shen and Steiahardc 1978; Sceinhardt and Mazia 1973).
Ammonia treatment was also reported to activate phosphorylatlon of thymidlne
and synthesis of histones in unfertilized eggs of the sea urchin 3_.
purpuratus (Nishioka 1976) . Premature chromosome condensation was induced by
ammonia treatment of eggs of L^ pictus and £. purpuratus (Epel et al. 1974;
Wilt and Mazia 1974; Krystal and Poccia 1979). Ammonia treatment of S_.
purpuratus and _S^ drobachiensis fertilized eggs resulted in absence of the
normal uptake of calciun following insemination, but did not inhibit calcium
uptake if ammonia treatment preceded insemination (Paul and Johnston 1978).
The polychetous annelid (Nereis succinea), the channeled whelk (Busycon
canal!culaturn), and the brackish water clam (Rangia cuneata) were subjected
to ammonia concentrations of 0.85, 0.37, and 2.7 mg/liter !fH-j and ammonia
excretion measured (Mangum et al. 1978). The excretion of ammonia in these
species was inhibited by non-lethal concentrations of ammonia; the authors
concluded that ammonia crosses the excretory epithelium in the ionized form,
and that the process is linked to the activity of the Na"1" •+• K"1" ATPases.
When blue crab (Calllnectes sapidus) were moved from water of 28 ppt salinity
to water of 5 ppt, a doubling of ammonia excretion rate occurred; addition of
excess NH^Cl to the low salinity water inhibited ammonia excretion and
decreased net acid output (Mangum et al. 1976). The effect of gaseous NH^
on hemoglobin from blood of the common marine bloodworm (Glycera dibrachiata)
was examined (Sousa et al. 1977) in an attempt to determine whether there was
competition between NH3 and oxygen in binding to hemoglobin; such an
NH-j/C>2 relationship was not found.
Saltwater Fishes
No other data were found for saltwater fish species.
85
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UNUSED DATA
Many references cited la Che References section were not used in the
text or tables, for a variety of reasons. For those several cases where more
than one reason applies to a given paper, it is listed only under the
principal reason for its not being used.
The following references were not used because the research they
reported was conducted using aquatic organisms not resident in North America:
Alderson (1979), Arizzi and Nicotra (1980), Brown and Currie (1973), Brownell
(1980), Chin (1976), Currie et al. (1974) Dockal and Varecha (1967), D'Silva
and Verlencar (1976), Giussani et al. (1976), Greenwood and Brown (1974),
Grygierek et al. (1978), Inamura (1951), Maclas (1983), Nicotra and Arizzi
(1980), Orzechowski (1974), Reddy and Menon (1979), Sadler (1981), Sana et
al. (1956), Shaffi (1980b), Singh et al. (1967), Stroganov and Pozhitkov
(1941), Thomas et al. (1976), Turoboyski (1960), Vailati (1979), Woker
(1949), Wuhrraann (1952), Wuhrmann and Woker (1953), Wuhrmann and Woker
(1955), Wuhrraann and Woker (1958), Yamagata and Niwa (1982).
The following references were not used because insufficient water
chemical composition data were provided to permit calculation of NH^:
Belding (1927), Binstock and Lecar (1969), Bullock (1972), Chu (1943),
Danielewski (1979), Das (1980), Ellis (1937), Hepher (1959), Joy and
Sathyaneaan (1977), Kawamoto (1961), Mukherjee and Bhattacharya (1978),
Oshima (1931), Oya et al. (1939), Patrick et al. (1968), Rao and Ragothaman
(1978), Roberts (1975), Rushton (1921), Scidmore (1957), Shelford (1917),
Shevtsova et al. (1979), Sigel et al. (1972), Southgate (1950), Wolf (1957a),
Wolf (1957b), Zgurovskaya and KusCenko (1968).
The following references were not used because the authors reported
data published elsewhere which was cited in this document from the other
86
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publication(a): Burkhalter (1975), Colt (1974), Dept. of Environment, U.K.
(1972), Herbert (1955), Hillaby (1978), Laraoyeux and Piper (1973), Ministry
of Technology, U.K. (1960), Ministry of Technology, U.K. (1966), Rice (1971),
Smart (1975), Wilson (1974).
The following references were not used because they were foreign-
language papers for which no translation was available, and no useful
information could be obtained from the abstract: Desavelle and Hubault
(1951), Fedorov and Smirnova (1978), Prahm (1975), Garcia-Romeu and Motais
(1966), Guerra and Coraodo (1972), Guseva (1937), Hubault (1955), Jocque and
Persoone (1970), Kawamoto (1958), Korting (1976), Krauss (1937), Kuhn and
Koecke (1956), Led ere and Devi ami nek (1950), Mamontova (1962), Oya et al.
(1939), Pequignot and Moga (1975), Pora and Precup (1971), Revina (1964),
Rossienbroich and Dohler (1982), Saeki (1965), Schaperclaus (1952), Sen curing
and Leopoldseder (1934), Schreckenbach and Spangenberg (1978), Steirmann and
Surbeck (1922a), Steinmann and Surbeck (1922b), Svobodova (1970), Svobodova
and Groch (1971), Teulon and Simeon (1966), Truelle (1956), Varaos and Tasnadi
(1962a), Vamos and Tasnadi (1962b), Vamos et al. (1974), Yasunaga (1976),
Yoshihara and Abe (1955).
The following references were not used because they relate more to
ammonia metabolism in fishes, than to ammonia toxlcity: Bartberger and
Pierce (1976), Becker and Schraale (1978), Brett and Zala (1975), Cameron and
Heisler (1983), Cowey and Sargent (1979), Creach et al. (1969), Cvancara
(I969a), Cvancara (1969b), De and Bhattacharya (1976), De Vooys (1968), De
Vooys (1969), Driedzic and Hochachka (1978), Fauconneau and Luquet (1979),
Fechter (1973), Fellows and Hird (1979a), Fellows and Hird (1979b), Flis
(1968a), Flis (1968b), Florkin and Duchateau (1943), Forster and Goldstein
(1966), Forster and Goldstein (1969), Fromm (1963), Girard and Payan (1980),
87
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Goldstein and Forster (1961), Goldstein and Forster (1965), Goldstein et al.
(1964), Gordon (1970), Gregory (1977), Grollman (1929), Guerin-Ancey (1976a),
Guerin-Ancey (1976b), Guerin-Ancey (1976c), Guerin-Ancey (1976d), Hays et al.
(1977), Hoar (1958), Huggins et al. (1969), Janicki and Lingis (1970), Katz
(1979), Kaushik and Luquet (1977), Kloppick et al. (1967), Kutty (1978),
Lawrence et al. (1957), Lum and Hamraen (1964), Maetz (1973), Maetz and
Garcia-Romeu (1964), Makarewicz and Zydowo (1962), Mason (1979a), Mason
(1979b), Matter (1966), McBean et al. (1966), McKhann and Tower (1961), Moore
et al. (1963), Morii et al. (1978), Morii (1979), Morii et al. (1979),
Mukherjee and Bhattacharya (1977), Nelson et al. (1977), Payan (1978), Payan
and Maetz (1973), Payan and Matty (1975), Payan and Pic (1977), Pequin and
Serfaty (1963), Pequin and Serfaty (1966), Pequin and Serfaty (1968), Pequin
et al. (1969a), Pequin et al. (1969b), Raguse-Degener et al. (1980), Ray and
Medda (1976), Read (1971), Rice and Stokes (1974), Rychley and Marina (1977),
Savitz (1969), Savitz (1971), Savitz (1973), Savitz et al. (1977), Schooler
et al. (1966), Smith (1929), Smith (1946), Smith and Thorpe (1976), Smith and
Thorpe (1977), Storozhuk (1970), Sukumaran and Kutty (1977), Tandon and
Chandra (1977), Thornburn and Matty (1963), Vellas and Serfaty (1974), Walton
and Cowey (1977), Watts and Watts (1974), Webb and Brown (1976), Wood (1958),
Wood and Caldwell (1978).
The following references were not used because the material the authors
used was a complex compound or had an anion that might in itself be toxic:
Blahm (1978), Curtis et al. (1979), Johnson and Sanders (1977), Kumar and
Krishnamoorthi (1983), Simonin and Pierron (1937), Vallejo-Freire et al.
(1954).
88
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The following references were not used because they dealt with complex
effluents or waste waters, of which ammonia was a primary component: Brown
et al. (1970), Calamari and Marchetti (1975), Gupta et al. (1979), Iwan and
Cella (1979), Janicke and Ludemann (1967), Lee et al. (1982), Lloyd and
Jordan (1963), Lloyd and Jordan (1964), Martens and Servizi (1976), Matthews
and Myers (1976), Mihnea (1978), Nedwell (1973), Okaichi and Nishio (1976),
Parna (1971), Rosenberg et al. (1967), Ruffier et al. (1981), Sahai and Singh
(1977), Shaffi (1980a), Vamos (1962), Varaos and Tasnadi (1972), Ward et al.
(1982).
Three references consisted only of an abstract, providing insufficient
information to warrant their use: Liebmann and Reichenbach-Klinke (1969),
Mukherjee and Bhattacharva (I975b), Redner et al. (1980).
89
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SUMMARY
All concentrations used herein are expressed as un-ionized ammonia
(NHj), because NH^, noc the ammonium ion (NH^*) has been demonscraced
co be che principal coxic form of ammonia. The daca used in deriving che
criteria are predominantly from flow-through tests in which ammonia
concentrations were measured. Ammonia was reported to be acutely toxic co
freshwater organisms at concentrations (uncorrected for pH) ranging from 0.53
to 22.8 rag/liter NH3 for 19 invertebrate species representing 14 families
and 16 genera and from 0.083 to 4.60 mg/liter NH3 for 29 fish species from
9 families and 18 genera. Among fish species, reported 96-hour LCSOs ranged
from 0.083 to 1.09 mg/licer for salmonids and from 0.14 to 4,60 mg/licer
NH-j for non-salmonids. 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 co 1.2 mg/licer NH3,
and with nine freshwater fish species, from five families and seven genera,
ranging from 0.0017 to 0.612 mg/liter NH3-
Concentrations of ammonia acutely coxic to fishes may cause loss of
equilibrium, hyperexcitabilicy, increased breaching, cardiac oucpuc and
oxygen uptake, and, in extreme cases, convulsions, coma and death. Ac lower
concentrations ammonia has many effects on fishes including a reduction in
hatching success, reduccion in growth race and morphological development, and
pathologic changes in tissues of gills, livers, and kidneys.
Several factors have been shown co modify acute NH*3 toxicity in fresh
water. Some factors alter the concentration of un-ionized ammonia in che
water by affecting the aqueous ammonia equilibrium, and some factors affect
the toxicity of un-ionized ammonia itself, either ameliorating or exacer-
bating the effects of ammonia. Factors chac have been shown to affect
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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 NH^ 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 ^3 toxicity also indicate
increasing NH3 toxicity with decreasing pH, but the data are insufficient
to derive a broadly applicable toxiclty/pH relationship. Data on temperature
effects on acute Cfi^ toxicity are limited, and somewhat variable, but
indications are that NH3 toxicity to fish is greater as temperature
decreases. There is no information available regarding temperature effects
on chronic NH3 toxicity.
Examination of pH- and temperature-corrected acute NH3 toxicity values
among species and genera of freshwater organisms showed that invertebrates
are generally more tolerant than fishes, a notable exception being the
fingernail clam. There is no clear trend among groups of fish, the several
most sensitive tested species and genera including representatives from
diverse families (Salmonldae, Cyprinidae, Percldae, and Centrarchidae).
Available chronic toxicity data for freshwater organisms also indicates
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 (Salaonidae, Cyprinidae,
Ictaluridae, Centrarchidae, and Catostomldae) and having chronic values
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ranging by not much more than a factor or two. The range of acute-chronic
ratios for ten species from six 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
cold water families of aquatic organisms are inadequate to warrant discrimi-
nation in the national ammonia criterion between bodies of water with "warm"
and "cold" water fishes; rather, effects of organism sensitivities on the
criterion are most appropriately handled by site-specific criteria derivation
procedures.
Data for concentrations of NHj toxic to freshwater phytoplankton and
vascular plants, although limited, indicate that freshwater plant species are
appreciably more tolerant to NH3 than are Invertebrates or fishes. The
ammonia criterion appropriate for the protection of aquatic animals will
therefore in all likelihood be sufficiently protective of plant life.
Available acute and chronic data for ammonia with saltwater organisms
are very limited, and insufficient to derive a saltwater criterion. A few
saltwater invertebrate species have been tested, and the prawn 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. There are some key research needs that need to be
addressed in order to provide a more complete assessment of ammonia toxicity.
These are: (1) acute tests with additional saltwater fish species and
saltwater invertebrate species; (2) life-cycle and early life-stage tests
92
-------
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 toxiclty; (5) more
histopathologlcal and histochemical research with fishes, which would provide
a rapid means of identifying and quantifying sublethal ammonia effects; (6)
studies on effects of dissolved and suspended solids on acute and chronic
toxicity.
93
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NATIONAL CRITERIA
The procedures described in che "Guidelines for Deriving Numerical
Nacional Wacer 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 one-hour* average concentration of un-ionized ammonia (in
mg/liter NH^) does not exceed, more often than once every three
years on the average, the numerical value given by 0.52/FT/FPH/2 ,
where:
FT , 100.03(20-TCAP). TCAP £ T <_ 30
100.03(20-T) . o <_.T <_ TCAP
FPH - 1 ; 8 <_ pH £ 9
TCAP * 20 C; Salmonids or other sensitive coldwater species
present
• 25 C; Salmonids and other sensitive coldwater soecies
absent
(*An averaging period of one hour may not be appropriate if
excursions of concentrations to greater than 1.5 times the average
occur during the hour; in such cases, a shorter averaging period may
be needed.)
(2) the 4-day average concentration of un-ionized ammonia (in mg/licer
NHj) does not exceed, more often than once every three years on
the average, the average* numerical value given by
0.80 /FT/ FPH/ RATIO, where FT and FPH are as above and:
94
-------
RATIO - /6 ; 7.7 <_ pH _< 9
/e^ in7.7-pH
• 1 ifl1Q7.l-pH ; 6.5£pH< 7.7
TCAP * 15 C; Salmonids or ocher sensicive coldwacer species
presenc
• 20 C; Salmonids and ocher sensicive coldwacer species
absenc
(^Because chese formulas are nonlinear in pH and cemperacure, che
cricerion should be the average of separate evaluacions of che
formulas refleccive of che fluctuations of flow, pH, and cemperacure
wichin che averaging period; ic is noc appropriace in general co
simply apply che formula co average pH, cemperacure and flow.)
The extremes for cemperacure (0, 30) and pH (6.5, 9) given in che above
formulas are absolute. Ic is noc permissible wich currenc daca co conduce
any excrapolacions beyond chese limics. In particular, there is reason co
believe chac appropriace criceria at pH > 9 will be lower than che placeau
given above bee ween pH 8 and 9.
Criceria concencracions for che uH range 6.5. co 9.0 and che cemperacure
range 0 C co 30 C are provided in che following cables. local ammonia
concencracions equivalent to each un- ionized ammonia concencracion are also
provided in chese cables. There is limiced daca on che effecc of cemperacure
on chronic coxicicy. EPA will be conduce ing addicional research on che
effeccs of cemperacure on ammonia coxicicy in order co fill perceived daca
gaps. Because of chis uncercaincy, addicional sice-specific informacion
should be developed before chese criceria are used in was ce load allocation
modelling. For example, che chronic criceria tabulated for sites lacking
95
-------
(1) One-hour average concentrations for ammonia.
PH
0 C
5 C
10 C
15 C
20 C
25 C
30 C
A. Salmonlds or Otner Sensitive Coldwater Species Present
Un- 1 on I zed Ammonia (mq/ liter NH
6.50
6.75
7.00
7.25
7.50
r-.n
8.00
8.25
8.50
8.75
9.00
6.50
6.75
7.00
7.25
7.50
7.75
8.00
8.25
8.50
8.75
9.00
0.0091
0.0149
0.023
0.034
0.045
0.056
0.065
0.065
0.065
0.065
0.065
35
32
28
23
17.4
12.2
8.0
4.5
2.6
1.47
0.86
0.0129
0.021
0.033
0.048
0.064
0.080
0.092
0.092
0.092
0.092
0.092
Total
33
30
26
22
16.3
11.4
7.5
4.2
2.4
1.40
0.83
0.0182
0.030
0.046
0.068
0.091
0.113
0.130
0.130
0.130
0.130
0.130
Ammonia
31
28
25
20
15.5
10.9
7.1
4.1
2.3
1.37
0.83
0.026
0.042
0.066
0.095
0.128
0.159
0.184
0.184
0.184
0.184
0.184
(mg/ liter
30
27
24
19.7
14.9
10.5
6.9
4.0
2.3
1.38
0.86
0.036
0.059
0.093
0.135
0.181
0.22
0.26
0.26
0.26
0.26
0.26
NHj)
29
27
23
19.2
14.6
10,3
6.8
3.9
2.3
1.42
0.91
0.036
0.059
0.093
0.135
0.131
0.22
0.26
0.26
0.26
0.26
0.26
20
18.6
16.4
13.4
10.2
7.2
4.8
2.8
1.71
1.07
0.72
0.036
0.059
0.093
0.135
0.181
0.22
0.26
0.26
0.26
0.26
0,26
14.3
13.2
11.6
9.5
7.3
5.2
3.5
2.1
1.28
0.83
0.58
8. Salmonlds and Other Sensitive Coldxater Speclea Absent
Un-1 on I zed Ammon I a (mg/11 ter NH
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
8.00
8.25
8.50
8.75
9.00
0.0091
0.0149
0.023
0.034
0.045
0.056
0.065
0.065
0.065
0.065
0.063
35
32
28
23
17.4
12.2
8.0
4.5
2.6
1.47
0.86
0.0129
0.021
0.033
0.048
0.064
0.080
0.092
0.092
0.092
0.092
0.092
Total
33
30
26
22
16.3
11.4
7.5
4.2
2.4
1.40
0.83
0.0182
0.030
0.046
0.068
0.091
0.113
0.130
0.130
0.130
0.130
0.130
Ammonia
31
28
25
20
15.5
10.9
7.1
4.1
2.3
1.37
0.83
0.026
0.042
0.066
0.095
0.128
0.159
0.134
0,184
0.184
0.184
0.184
( mg/ 1 1 ter
30
27
24
19.7
14.9
10.5
6.9
4.0
2.3
1.38
0.86
0.036
0.059
0.093
0.135
0.181
0.22
0.26
0.26
0.26
0.26
0.26
NH3>
29
27
23
19.2
14.6
10.3
6.8
3.9
2.3
1.42
0.91
0.051
0.084
0.131
0.190
0.26
0.32
0.37
0.37
0.37
0.37
0.37
29
26
23
19.0
14.5
10.2
6.8
4.0
2.4
1.52
1.01
0.051
0.084
0.131
0.190
0.26
0.32
0.37
0.37
0.37
0.37
0.37
20
18.6
16.4
13.5
10.3
7.3
4.9
2.9
1.31
1.18
0.32
To convert these values to mg/llter N, multiply by 0.822.
96
-------
(2) 4-day average concentrations for ammonia.*
pH
0 C
5 C
10 C
15 C
20 C
30 C
A. Salmonlds or Other Sensitive Coldwater Species Present
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
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
2.5
2.5
2.5
2.5
2.5
2.3
1.53
0.87
0.49
0.28
0.16
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 Ammonia (mg/llter NHj)
0.0013
0.0023
0.0042
0.0074
0.0132
0.022
0.025
0.025
0.025
0.025
0.025
Ammonia
2.2
2.2
2.2
2.2
2.2
2.1
1.37
0.73
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
( mg/ 1 1 ter
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
0.0186
0.031
0.035
0.035
0.035
0.035
0.035
NH3)
1.49
1.49
1.49
1.50
1.50
1.40
0.93
0.54
0.32
0.19
0.13
0.0019
0.0033
0.0059
0.0105
0.0186
0.031
0.035
0.035
0.035
0.035
0.035
1.04
1.04
1.04
1.04
1.05
0.99
0.66
0.39
0.23
0.15
0.10
0.0019
0.0033
0.0059
0.0105
0.0186
0.031
0.035
0.035
0.035
0.035
0.035
0.73
0.73
0.74
0.74
0.74
0.71
0.47
0.28
0.17
0.11
0.08
8. Salmonlds and Other Sensitive Coldv
-------
salmonids are less cercain ac temperatures much below 20 C chan chose cabu-
laced at temperatures near 20 C. Where che creacmenc levels needed co meec
chese criteria below 20 C may be substantial, use of sice-specific criteria
is strongly suggested. Development of such criteria should be based upon
sice-specific toxicity tests.
Data available for saltwater species are insufficient co derive a
criterion for salt water.
The recommended exceedence frequency of three years is the Agency's best
scientific judgment of the average amount of time it will take an unstressed
system co recover from a pollution event in which exposure co ammonia exceeds
che criterion. Stressed systems, for example, one in which several outfalls
occur in a limited area, would be expected co require more cime for recovery.
The resilience of ecosystems and their ability co recover differ greatly, .
however, and sice-specific criteria may be established if adequate justifica-
tion is provided.
The use of criteria in designing waste treatment facilities requires che
selection of an appropriate wasteload allocation model. Dynamic models are
preferred for the application of chese criteria. Limited daca or other
factors may make their use impractical, in which case one should rely on a
steady-state model. The Agency recommends che interim use of 1Q5 or 1Q10 for
Criterion Maximum Concentration (CMC) design flow and 7Q5 or 7QIO for che
Criterion Continuous Concentration (CCC) design flow in steady-state models
for unstressed and stressed systems respectively. The Agency acknowledges
chac che CCC stream flow averaging period used for steady-state wasteload
allocation modelling may be as long as 30 days in situations involving POTWs
designed to remove ammonia where limited variability of effluent pollutanc
concentration and resultant concentrations in receiving waters can be
98
-------
demonscraced. In cases where low variabilicy can be demonscraced, longer
averaging periods for the amoonia CCC (e.g., 30-day averaging periods) would
be accepcable because the magnitude and duracion of exceedences above che CCC
would be sufficiencly limited. These maccers are discussed in more decail in
che Technical Supporc Document for Wacer Quality-Based Toxics Control (U.S.
EPA, 1985a).
99
-------
EXAMPLES OF SITE-SPECIFIC CRITERIA
National criteria are subject to modification, if appropriate, co
reflect local conditions. One method provided in the Site-Specific Criteria
Guidelines (U.S. Environmental Protection Agency 1982) for such modification
is to base certain calculations only on those species that occur in the body
of water of interest. As an example of how site-specific criteria for
ammonia may differ from the national criteria, such recalculations were
performed for several sites.
The sites were chosen on the basis of readily available information on
the presence of fish and invertebrate species and on a reasonable diversity
between sites. The sites were:
(1) Naugatuck River, Waterbury, Connecticut
(U.S. Environmental Protection Agency 1985a)
(2) Five Mile Creek, Birmingham, Alabama
(U.S. Environmental Protection Agency 1985b)
(3) Piceance Creek, Colorado
(Goettl and Edde 1978; Gray and Ward 1978)
(4) Ottawa River, Lima, Ohio
(Mount et al. 1984)
The calculations here are for pHs of 7 and 8 and temperatures of 10 and 20 C.
This exercise is meant just to illustrate how variation in organisms among
sites will result in different criteria formulations than the national
criteria; specific design conditions for each site were not addressed.
For each site, available surveys of species occurrence were used to
identify which of the genera tested for acute toxicity (Table 3) were
present. Minimum data requirements for diversity of organisms were net
except where inappropriate to a site (U.S. Environmental Protection Agency
100
-------
1982). The national GMAVref (Table 3) was used for each genus, even if based
in part or whole on species not occurring at the site. If a family was
present at a site, but none of Che site genera were tested or the sice genera
were not identified, Che FMAVref for Chat family (the geometric mean of che
GMAV efS available for Che family) was also used. The data so developed
for each site are listed in the following table.
Sites 1 and 3 included salmonids, so the temperature caps (TCAP) for Che
log-linear temperature relationship for FAVs and FCVs were set as specified
in the national criterion for sites with salmonids (20 C for FAVs, 15 C for
FCVs). For sites 2 and 4, the TCAP was raised to 25 C for FAVs and 20 C for
FCVs, as specified in the national criterion for sices lacking salmonids.
The Guidelines method for estimating the FAV as Che fifth percentile of
MAVs was applied to the set of GMAVrefs selected for each sice. If the
FAVrefS so computed exceeded the SMAVfef of an important species at a site,
or Che MAVref of an important size class of an important species, Che
FAVref was lowered Co Che lowesC such MAVref. The FAVs at each sice were
Chen computed by adjusting the FAVref Co Che specified ceraperaCure and pH
using Che relationship FAVreg/FT/FPH, where FT and FPH are as specified for the
national cricerion. The one-hour average concenCracion criceria were sec co
one-half of the site FAVs.
The FCVs at each site at each particular temperature and pH were
computed by the formula FAVref/FT/FPH/RATIO, where FT, FPH, and RATIO
are as specified for the national cricerion. If the FAVre£ was reduced
for Che 1-hour criceria Co reflecc an age/size class, it was restored for che
above calculation to what it would be without such a reduction. If a
resultant FCV at a site exceeded the chronic value of an important species
present at Che sice, FCVs at all pHs and temperatures were proportionally
101
-------
lowered until Che chronic value was not exceeded. The 4-day average
concentration criteria were set to the FCVs.
For site 3, which includes the mountain whitefish (Prosopium), the fifth
percentile FAVreg is about 15% lower than for the national criterion, due to
Che lower number of total genera causing the fifth percentile to be closer to
the acute value for the whitefish. for the other sites, lacking the
whitefish, the fifth percentile FAVref is above that for the national
criterion, but by only several percent due to the presence of other sensitive
genera and the lower number of total organisms partly compensating for the
lack of the whitefish.
Only site 3 included rainbow trout, so only its FAVref was lowered
to the MAVreg of adult rainbow trout, as for the national criterion. As
a consequence, the 1-hour average -criterion for this site is identical to the
national criterion. For the other three sites, the 1-hour average criterion
is about 40% greater than the national number for a wide range of species
composition. This greater value is not necessarily due to differences in
general species sensitivities, but could reflect unavailability of informa-
tion on the sensitivity of different age/size classes for species other than
rainbow trout; these higher numbers should therefore be treated with caution
as perhaps providing relatively less protection than the national criterion.
For the 4-day average concentration, the difference among sites and
between sites and the national criterion are even less. The FAVrefS
used for computing the 4-day average concentration at the four sites are the
same or slightly (<10%) less than for the national criterion. Consequently,
Che criterion for 4-day average concentrations at the sites are virtually the
same as for the national criterion.
102
-------
Some ocher sicea may show higher sice-specific criteria, hue these
increases will not be major. Due to the numerous, diverse genera with
GMAVrefS in the 1.1-1.4 mg/liter NH3 range, few sites will have a
FAVre£ greater than 1.1, resulting in 1-hour average concentration
criteria little more than twice the national criteria at T<20 C and 4-day
average criteria no more than 402 greater than the national criteria at T<15
C. At higher temperatures, greater increases are possible if temperature
caps for the log-linear temperature relationship are raised, but at low
temperatures additional increases are unlikely given current data on acute
sensitivity and acute-chronic ratios.
103
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Site-specific ammonia criteria examples for four sites
Site Number
Genus
Prosop 1 UM
Notamlgonus
EthexMtoma
Salmo
Muscul 1 urn
Leoomls
Sttzostedlon
Notropls
Oncorhynchus
Campostoma
Mlcropterus
Oendrocoelum
Poecllla
Qapnnta
Ictalurus
Morone
Salvel t nus
Catostoiwis
Slmocaphalus
Physa
Cerlodaphnta
Ptmephales
Arcynopteryx
Cottus
Gambusla
Tubl f ex
Hellsoma
Crangonyx
Calltbaetls
A sell us
Ephemerel la
Stenelmls
Orconectes
Pht larctus
FAVref <5th twcentl le)
1-hour average concen- pH"7; T»10:
tratlon (mg/ liter NHj) T-20:
pH-8; T»10:
T-20:
4-day average concen- pH-7; T-10:
tratlon (mg/ liter NH3) T-20:
pH-8; T-10:
T-20:
1
a
0.76
0.38
1.10
a
1.16
a
1.23
a
a
1.34
1.40
a
1.49
1.63
a
a
1.79
1.89
1.95°
1.96
a
a
a
a .
2.70b
2.76
a
3.18
4.02
a
a
8.48^
11. 4b
0.75
0.067
0.133
0.188
0.38
0.0039
0.0035
0.023
0.032
2
&MAV,
a
0.76
0.38
a
a
1.16
a
1.23
a
1.30
1.34
1,40
a
b
1.63
a
a
1.79°
1.79b
1.95
b
a
a
2.35
2.48
2.70
a.
3.18
4.025
a
8.00
8.48
a
0.73
0.065
0.130
0.183
0.37
0.0038
0.0076
0.023
0.046
3
:»*
0.56
a
a
1.10
1.10°
a
a
1.23
a
a
a
a
a
a
1.63
a
1.69
1.79
a
1.95
a
2.07
2.29b
2.35
a
a .
2.76°
3.12b
3.18
4.02
5.25
8.00°
a
M.4b
0.60c'd
0.046
0.093
0.130
0.26
0.0042
0.0059
0.025
0.034
4
a
0,76
0.88
a
a
1.16
a
1.23
a
1.30
1.34
1.40
a
b
1.63
a
a
1.79
l.79b
1.95
b
2.07
a
a
a
2.70
a
a
3.18
a
a
8.00
8.48
a
0.72
0.064
0.127
0.180
0.36
0.37
0.75
0.22
0.45
(a) Genus and farat ly absent from site.
(b) Genus absent or unidentified, but family present; FMAVrvf used.
(e) For 1-hour average, FAVr-f lowered to the MAVref of adult rainbow
trout (0.52).
(d) For 4-day average, FAVr-f recalculated as 0.80 after GMAVr^f of Prosoplu*
raised to 0.78 to reflect Impact of size on acute toxlclty.
104
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Table I. Acute Toxlclty of Ammonia to Aquatic Animals
Species
Life Stage
or Size
Chemical Method*
Effectb
Concentration
(mo/L NH«)
Temperature
FRESHWATER SPECIES
Flatworm,
Dendrocoelum lacteum
(Procotyla fluvlatlll s)
Tub! field worm.
Tublfex tublfex
Snail,
Physa gyrlna
Snail.
Physa gyrlna
Snail,
Physa gyrlna
Snail,
Physa gyrlna
Snail,
Physa gyrlna
Snail,
Physa gyrlna
Snail,
Hellsoma trlvolvls
Clam,
Muscullum transversum
Clam,
Muscullum transversum
Clam,
Muscullum transversum
Cladoceran.
Adult
Adult
Adult
Adult
Adult
Adult
Adult
Adult
Adult
Adult
<2-h
NH4C| S.U
NH4C| S.U
NH4CI FT.M
NH4CI FT.M
W4CI FT.M
w4ci FT.M
MH4C| FT.M
NH4C| FT.M
NH4CI FT.M
NH4CI FT.M
NH4C| FT.M
NH4C| FT.M
NH4C| FT.M
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
l£50
LC50
LC50
1.59
2.09
2.49
2.16
1.78
1.71
2.76
0.93
U29
1.10
0.770d
8.2
8.2
8.0
8.2
8.1
8.2
8.0
8.0
8.2
8.2
8.1
8.6
7.06
18
12
4.0
5.5
12.1
I2.B
13.3
24.9
12.9
5.4
14.6
20.5
24
0.0.
(mg/U
12.5
12.3
10.0
9.5
10.4
7.1
9.5
12.3
9.6
8.6
4.8-5.3
Reference
Stammer 1953
Stammer 1953
West 1985
West 1985
West 1985
West 1985
West 1985
West 1985
West 1985
West 1985
West 1985
West 1985
Mount 1982
Cerlodaphnla acanthlna
105
-------
TabI* 1. (Continued)
Species
Cladoceran,
Oapnnla oaqna
Cladoceran,
Daphnla »agna
Cladoceran,
Oapnnla maqna
Cladoceran,
Daphnla aagna
Cladoceran,
Daphnla aagna
Cladoceran,
Paphnla «aqna
Cladoceran,
Daphnla aagna
Cladoceran,
Daphnla utagna
Cladoceran,
Daphnla *agna
Cladoceran,
Daphnla »agna
Cladoceran,
Daphnla eagna
Cladoceran,
Daphnla pullcarla
Cladoceran,
Sleocephalus vetulus
Cladoceran,
Life Stege
or Size
Mixed
ages
<24-h
old
<24-h
old
<24-h
old
<24-h
old
old
<24-h
old
<24-h
old
<24-h
old
<24-h
old
<24-h
old
-
<24-h
old
Adult
Chealcal
NH4C|
NH4C|
™4C|
NH4C|
NH4C|
NH4C|
NH4CI
NH4C|
NH4C,
NH4C|
NH4Cl
NH4CI
NH4C|
Method*
S.M
S.M
S.M
S.M
S.M
S.M
S.M
S.M
S.M
S.M
FT.M
FT.M
FT.M
FT.M
Effect6
LC50
CC50
UC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
Concentration
(•0/L HH,)
2.08
2.45
2.69
2.50
2.77
2.38
0.75
0.90
0.53
0.67
4.94C
1.16
0.613d
2.29
Te
J*l
8.2
7.95
8.07
8.09
8.15
8.04
7.51
7.53
7.4
7.5
8.11-
8.58
8.0-
8.1
7.06
8.3
•perature
CO
25
22.0
19.6
20.9
22.0
22.8
20.1
20.1
20.6
20.3
19.7
14
24
17.0
D.O.
7.0-8.5
-
7.4
6.8
-
-
7.6
8.0
8.0
8.0
95;
Saturated
7.2-
7.4
4.8-
5.3
9.5
Reference
Parkhurst et
I9BH
Russo et al.
Russo et al.
Russo et al.
Russo et al.
Russo et al.
Russo et al.
Russo et al.
Russo et al.
Russo et al.
al. 1979,
1965
1985
1985
1985
1985
1985
1985
1985
1985
Ralnbold & Pescltel
I982a
DeGraeve et
Mount 1982
West 1985
II
al. 1980
Slmocephalus vetulus
106
-------
Table I. (Continued)
Species
Isopod,
Asa II us racovltzal
racovltzalf
Isopod,
Asallus racovltzal
Amphlpod.
Crangonyx pseudogracl 1 1 s
A.*phlpod,
Crangonyx pseudogracl 1 Is
Amphlpod,
Crangonyx pseudogracl 1 1 s
Amphlpod.
Cranqonyx psaudogracl 1 1 s
Amphlpod,
Cranqonyx pseudoqrac 1 1 1 s
Crayfish.
Orconectas nals
Crayfish,
Orconactas Immunls
Mayfly,
Calllbaatls sp. near
nontanus
Mayfly.
Ca 1 1 1 baat 1 s skok 1 anus
Mayfly.
Ephemeral la grand Is
Mayfly.
Ephemeral 1 a grand 1 s
Mayfly.
Life Stag*
or Slza
12 mm
Adult
Adult
Adult
Adult
Adult
Adult
2.78 cm
Adult
10 mm
Nymph
II mm
II mm
10 mm
Chemical
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
Method*
FT,M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
Effactb
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
Concantratloa Temperature
<»0/L NHjJ oH CO
2.94
4.95
2.76
5.63
3.56
3.29
1.63
3.15
22.8
1.60
4.82
4.96
5.88
3.86
7.81
8.0
8.0
8.0
8.2
8.0
8.0
7.6-
9.0
8.2
7.81
7.9
7.84
7.85
7.84
11.9
4.0
4.0
12.1
13.0
13.3
24.9
26-27
4.6
11.9
13.3
12.8
12.0
13.2
0.0.
(•fl/U
9.1
12.6
12.6
' ?
10:1
9.5
10.4
7.1
7.8-
8.2
12.4
9.1
10.3
8.3
8.8
8.4
Reference
Thurston at al.
West 1985
West 1985
West 1985
Wast 1985
Wast 1985
West 1985
Evans 1979
West 1985
Thurston et al.
West 1985
Thurston et al.
Thurston et al.
Thurston et al.
I983a
1984a
1984a
1984a
I984a
-------
Table I. (Continued)
Species
Stonef !y.
Arcynopteryx
Stonaf ly,
Arcynopteryx
paral lela
paraltela
Caddlsfly,
Ph I 1 arctus quaer 1 s
Beetle,
Stenalmls sexl Ineata
Pink salmon,
Oncorhynchus
Pink salmon,
Oncorhynchus
Coho salmon,
Oncorhynchus
Coho salmon,
Oncorhynchus
Coho salmon,
Oncorhynchus
Coho salmon.
Oncorhynchus
Coho salmon,
Oncorhynchus
Coho salmon,
Oncorhynchus
Coho salmon,
Oncorhynchus
Coho salmon,
Oncorhynchus
oorbuscha
qorbuscha
klsutch
klsutch
klsutch
klsutch
klsutch
klsutch
klsutch
klsutch
Lit* Stag*
or Size
!9 ssa
19 mm
Larvaa
2.8 mm
Late alavlns
Fry
Juvenile
Juvenl la
Juvenile
Juvenile
Juvanl la
Juvenl la
Juvanl la
6. g
Chasica!
NH4Cj
NH4C|
NH4C|
NH4CI
80$ Buckley 1978
Saturated
1975
1975
1975
1975
1975
1975
1975
108
-------
Table 1. (Continual
Species
Chinook salmon,
Oncorhynchus tshawytscha
Chinook salmon,
Oncorhynchus tshawytscha
Chinook salmon,
Oncorhynchus tshawytscha
Golden trout.
Sal mo aguabonlta
Cutthroat trout,
Salmo clarkl
Cutthroat trout,
Salno clarkl
Cutthroat trout,
Salmo clarkl
Cutthroat trout,
Salmo clarkl
Rainbow trout,
Sal.no galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Lite Stag*
or Size
15.3 g
18.1 g
14.4 g
0.09 g
1.0 g
1.0 g
3.3 g
3.4 g
l-d-old
sac fry
5-d-old
sac fry
13-d-old
17-d-old
51-d-old,
1.7-1.9 cm
325-d-old,
8-10 cm
Chemical
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
MH4C|
NH4C|
NH4CI
NH4C|
NH4CI
NH4C|
NH4C|
Method*
FT.M
FT.M
FT,M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
Ef«ectb
LC50
LCSO
LCSO
LCSO
LCSO
LCSO
LCSO
LCSO
LCSO
LCSO
LCSO
LCSO
LCSO
LCSO
Concentration Temperature
(ma/L NHx) pH fC)
0.476
0.4S6
0.399
0.755
0.60
0.66
0.62
0.52
X).486
X).486
0.325
0.370
0.160
0.440
7.82
7.84
7.87
8.06
7.81
7.80
7.80
7.78
7.4
7.4
7.4
7.4
7.4
7.4
12.2
12.3
13.5
13.2
13.1
12.8
12.4
12.2
14.5
14.5
14.4
14.5
14.5
14.5
0.0.
(mg/L)
7.78
7.87
7.26
8.9
8.6
8.4
8.2
8.3
>BQ%
Saturated
>80f
Saturated
>60f
Saturated
>80*
Saturated
>80jf
Saturated
>eoj
Saturated
Reference
Thurston & Meyn
Thurston & Meyn
Thurston & Meyn
Thurston & Russo
Thurston et al.
Thurston et al.
Thurston et al .
Thurston et al.
Calamarl et al.
Calamarl et al.
Calamarl et al.
Calamarl et al.
Calamarl et al.
Calamarl et al.
1984
1984
1984
1981
1978
1978
1978
1978
1977.
1977,
1977,
1977,
1977,
1977,
1981
1981
1981
1981
1981
1981
109
-------
Table I. (Continued)
Specie*
Rainbow trout.
Sal no galrdnerl
Rainbow trout.
Sal no qnlrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout.
Sal no galrdnerl
Rainbow trout.
Sal no galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout.
Sal MO galrdnerl
Rainbow trout,
o _ • • * _t
Life Stag*
or Size
1.48
0.06
0.06
0.06
0.06
0.12
0.14
0.15
0.15
0.18
0.18
0.23
9
9
9
9
9
9
9
9
9
9
9
9
Chemical
NH4C|
NH4CI
NH4CI
w4ci
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
Method*
FT.M
S,M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
Effect*
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
Concentration
(mo/L NHx)
0.697
0.4
0.77
0.436
0.446
0.478
0.291
0.232
0.336
0.347
0.474
0.440
0.392
0.426
i Temperature
PH CO
7.95
7.5
8.0-8.1
7.90
7.90
7.91
7.91
7.88
7.88
7.87
7.95
7.87
7.87
7.88
10
15
14
12.7
13.4
13.0
13.1
12.8
12.9
12.9
12.5
13.0
12.9
13.4
0.0.
(mg/L)
80*
Saturated
Aerated
7.2-7.4
8.8
8.6
8.6
8.5
9.2
8.8
8.8
9.0
8.9
8.9
8.9
Reference
Broderlus 1 Smith I97S
Holt & Malcolm 1979
OeGraeve et al. I960
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
4 Russo 1983
& Russo 1983
& Russo 1983
& Russo 1983
& Russo 1983
& Russo 1983
& Russo 1983
& Russo 1983
& Russo 1983
& Russo 1983
& Russo 1983
Salmo galrdnerl
110
-------
Table I. (Continued)
Uf« Stagi
Specie* or Size
Rainbow trout, 0.23 g
Sal no qalrdnerl
RaInbox trout, 0.33 g
Sal «»o galrdnerl
RaInbox trout, 0.33 g
Salmo galrdnerl
Rainbow trout, 0.36 g
Salmo flalrdnerl
Rainbow trout, 0.47 g
Salmo galrdnerl
Rainbow trout, 0.47 g
Salmo galrdnerl
Rainbow trout, 0.61 g
SoIPO galrdnerl
Rainbow trout, 1.01 g
SBlao galrdnerl
Rainbow trout, 1.02 g
Sal»o galrdnerl
Rainbow trout, 1.7 g
SalMO galrdnerl
Rainbow trout, 1.7 g
Salmo galrdnerl
Rainbow trout, 1.8 g
Salmo galrdnerl
Rainbow trout, 2.3 g
Salmo galrdnerl
Rainbow trout, 2.5 g
Salao galrdnerl
Chemical
NH4C|
NH4C|
NH4CI
NH4CI
NH4C|
NH4C|
W4C|
NH4C|
NH4C|
NH4CI
NH4C|
NH4C|
NH4C|
Methods* Effectb
FT.M LC50
FT.M
FT.M
FT.M
FT.M
fT,M
FT.M
FT.M
FT.M
FT.M
FT,M
FT.M
FT.M
FT.M
LC50
LC50
UC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
Concentration
(•g/L NHx)
0.400
0.497
0.421
0.758
0.572
0.570
0.673
1.09
0.641
0.696
0.772
0.683
0.812
0.632
Temperature 0.0.
CC) (ag/L) Reference
7.67 13.1
7.86 13.4
7.86
B. 08
7.86
7.85
7.85
8.06
7.85
7.79
7.86
7.84
7.80
7.85
13.0
12.8
12.7
12.5
13.1
13.2
12.3
12.4
14.1
13.8
12.4
13.1
8.9 Thurston A Russo 1983
9.0 Thurston & Russo 1983
9.0 Thurston & Russo 1983
9.4 Thurston & Russo 1983
9.0 Thurston & Russo 1983
9.0 Thurston & Russo 1983
8.7 Thurston & Russo 1983
8.8 Thurston & Russo 1983
8.7 Thurston & Russo 1983
8.6 Thurston & Russo 1983
8.8 Thurston & Russo 1983
9.0 Thurston & Russo 1983
8.6 Thurston & Russo 1983
8.7 Thurston & Russo 1983
-------
Table I. (Continued)
Specie*
Rainbow trout,
Saleo qnlrdnarl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salao galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salao galrdnerl
Rainbow trout,
Sal»o galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Sal*o galrdnerl
Rainbow trout,
Salroo galrdnerl
Rainbow trout,
Salao galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Sali»o galrdnerl
Rainbow trout,
Saleo galrdnerl
Rainbow trout,
Salmo galrdnerl
Life Stage
or Size
2.6 g
4.0 g
4.3 g
4.3 g
4.6 g
5.7 g
6.3 g
6.7 g
7.0 g
7.9 g
8.0 g
8.0 g
8.1 g
9.0 g
Chemical
NH4C|
NH4C|
NH4C|
NH4CI
NH4C|
NH4CI
NH4C|
NH4C|
NH4C|
NH4CI
NH4C|
NH4C|
NH4C|
NH4C|
Methods*
FT.M
FT,M
FT.M
FT,M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
Effect6
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
Concentration Temperature
<«o/L MM pH CC)
0.618
0.410
0.390
0.752
0.662
0.763
0.250
0.449
0.392
0.464
0.243
0.635
0.510
0.623
7.87
7.71
7.71
7.84
7.83
7.80
7.44
7.84
7.87
7.90
7.50
7.82
7.75
7.84
12.1
11.4
11.5
13.0
13.5
13.3
12.8
12.2
12.2
11.9
14.5
13.2
12.3
12.9
(•g/L) Reference
9.2 Thurston & Russo 1983
8.3 Thurston & Russo 1983
8.3 Thurston & Russo 1983
8.4 Thurston & Russo 1983
8.6 Thurston & Russo 1983
7.7 Thurston & Russo 1983
8.6 Thurston & Russo 1983
8.1 Thurston & Russo 1983
7.9 Thurston & Russo 1983
8.2 Thurston & Russo 1983
8.1 Thurston & Russo 1983
7.5 Thurston & Russo 1983
6.9 Thurston & Russo 1983
7.9 Thurston & Russo 1983
112
-------
TabU 1. (Continued)
Specie*
Rainbow trout,
Sal«o galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salao galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
So I cno galrdnerl
Rainbow trout,
SB Imo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salno galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Sal»o galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Satmo galrdnerl
Life Stag*
or Size
9.3 g
9.5 g
9.7 g
II. 1 g
11.2 g
12.3 g
14.8 g
15.1 g
18.9 g
22.6 g
22.8 g
23.6 g
24.5 g
25.8 g
Chemical
NH4C|
NH4C|
NH4C|
uu pi
NrljUl
*4c,
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
UU fl
Nii4ui
NH4C|
NH4C|
NH4C|
Methods*
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
EHectb
LC50
LC50
LC50
LC50
LC50
LC50
LC50
L£50
LC50
LC50
LC50
LC50
LC50
LC50
Concentration Temperature
(M/L NH,) pH CO
0.833
0.432
0.796
0.714
0.326
0.404
0.389
0.375
0.364
0.382
0.367
0.392
0.281
0.456
7.90
7.70
7.90
7.87
7.80
7.65
7.67
7.62
7.64
7.66
7.65
7.69
7.60
7.75
13.0
13.9
13.0
13.0
9.7
14.3
14.0
14.4
13.1
13.6
13.2
13.4
12.9
11.8
0.0.
(•g/L) Reference
6.6 Thurston & Russo 1983
8.0 Thurston & Russo 1983
6.1 Thurston & Russo 1983
7.8 Thurston & Russo 1983
9.2 Thurston & Russo 1983
7.3 Thurston & Russo 1983
7.4 Thurston & Russo 1983
7.2 Thurston & Russo 1983
7.2 Thurston & Russo 1983
7.0 Thurston & Russo 1983
7.3 Thurston & Russo 1983
6.8 Thurston & Russo 1983
7.3 Thurston & Russo 1983
7.9 Thurston & Russo 1983
-------
Table 1. (Continued)
Specie*
Rainbow trout,
galrdnerl
Rainbow trout,
So lao galrdnerl
Rainbow trout,
Sal mo galrdnerl
Rainbow trout,
Sal mo galrdnerl
Rainbow trout,
Sal«o galrdnerl
Rainbow trout,
Sal mo galrdnerl
Rainbow trout,
Sal«o qalrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
SB I mo galrdnerl
Rainbow trout,
Sal«o galrdnerl
Rainbow trout,
Salgo galrdnerl
Rainbow trout,
Sal no galrdnerl
Rainbow trout,
Sal mo galrdnerl
Rainbow trout,
Salop galrdnerl
Life Stage
or Size
26.0 g
28.0 g
29.6 g
29.8 g
38.0 g
42.0 g
48.6 g
52.1 g
152 g
248 g
380 g
513 g
558 g
1122 g
Chemical
NH4C|
NH4C|
NH4C|
NH4CI
NH4C|
NH4C|
NH4CI
NH4C|
NH4CI
HH4C|
NH4C|
NH4CI
NH4C|
NH4CI
Methods*
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
Effectb
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
Concentration Temperature
(•g/L NHO pH CC)
0.
0.
0.
0.
0.
0.
0.
0.
0.
432
268
307
351
448
552
580
484
297
0.327
0.
0.
0.
0.
289
262
312
201
7.66
7.60
7.63
7.59
7.68
7.77
7.86
7.88
7.69
7.74
7.76
7.66
7.64
7.69
12.8
13.0
12.9
12.7
13.0
13.6
10.2
10.0
10.7
10.4
10.0
9.8
10.0
10.4
0.0.
(«fl/L>
7.2
7.3
7.2
7.3
7.1
6.2
8.8
9.4
8.3
7.7
7.6
7.6
6.9
7.1
Reference
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
& Russo
& Russo
& Russo
& Russo
& Russo
& Russo
& Russo
& Russo
& Russo
& Russo
& Russo
& Russo
& Russo
& Russo
1983
1983
1983
1983
1983
1983
1983
1983
1983
1983
1983
1983
1983
1983
114
-------
Table I. (Continued)
Species
Rainbow trout,
SalMO galrdnerl
Rainbow trout,
SalMO galrdnerl
Rainbow trout,
SalMO galrdnerl
Rainbow trout,
SalMO galrdnerl
Rainbow trout,
SalMO galrdnerl
Rainbow trout,
SalMO galrdnerl
Rainbow trout,
SalMO galrdnerl
Rainbow trout,
SalMO galrdnerl
Rainbow trout,
SalMO galrdnerl
Rainbow trout,
SalMO galrdnerl
Rainbow trout,
SalMO galrdnerl
Rainbow trout,
SalMO galrdnerl
Rainbow trout,
SalMO galrdnerl
Rainbow trout.
Life Stag*
or Size
1140 g
1496 g
1698 g
2596 g
1.7 g
1.8 g
1.7 g
2.1 g
1.8 g
2.1 g
9.4 g
11.9 g
7.1 g
10.1 g
Chemical
NH4C|
NH4C|
NH4C|
NH4C|
NH4HC03
NH4HC03
(NH4)2HP04
(NH4)2HP04
(NH4)2S04
(NH4)2S04
NH4C|
NH4C|
NH4C|
Methods*
FT.M
FT.M
FT.M
FT,M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
Effectb
LCSO
LCSO
LCSO
LCSO
LCSO
LCSO
LCSO
LCSO
LCSO
LCSO
LCSO
LCSO
LCSO
LCSO
Concentration Temperature
(MQ/L NH^I pH CC)
0.234
0.249
0.192
0.163
0.677
0.662
0.636
0.694
0.764
0.921
0.856
0.801
0.897
0.942
7.69
7.64
7.65
7.62
8.10
8.12
7.94
7.98
7.89
7.94
7.85
7.88
7.91
7.91
10.7
9.8
9.8
7.9
13.9
13.6
12.8
12.5
12.4
12.5
16.1
16.7
19.0
19.1
0.0.
(«Q/L)
7.0
7.2
6.6
7.7
8.8h
9.1"
9.2h
9.1h
9.2"
9.0h
6.6
6.3
7.1
6.2
Reference
Thurston I
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
&
&
&
&
&
A
4
&
&
&
&
&
Russo 1983
Russo 1983
Russo 1983
Russo 1983
Russo 1983
Russo 1983
Russo 1983
Russo 1983
Russo 1983
Russo 1983
Russo 1983
Russo 1983
Russo 1983
Russo 1983
SalMo galrdnerl
115
-------
Table I. (Continued)
Specie*
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Sal mo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Life Stage
or Size
8.6 g
10.6 g
9.0 g
8.2 g
9.0 g
10.0 g
10.4 g
4.0 g
3.7 g
5.7 g
5.0 g
4.6 g
3.2 g
18.1 g
Chemical
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4CI
NH4C|
NH4C|
Methods*
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
Effectb
UC50
LC50
UC50
LC50
LC50
LC50
UC50
1.C50
LC50
IJC50
UC50
LC50
UC50
LC50
Concentration
(mo/L NHO
0.931
O.I58C
O.I84C
0.454C
0.799C
0.664°
0.648°
0.683
0.704
0.564
0.610
0.497
0.643
0.56°
Temperature
pH CO
7.96
6.51
6.80
7.30
8.29
8.82
9.01
7.83
7.79
7.75
7.76
7.75
7.75
8.10-
8.57
19.2
14.1
14.1
14.0
14.1
13.9
14.5
12.8
12.9
12.5
12.5
12.7
13.0
5.0
D.O.
(ma/l)
6.4
7.9
7.9
8.0
7.8
6.1
7.4
7.57
7.37
6.60
6.57
5.66
5.47
51-88*
Saturated
Reference
Thurston & Russo
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Relnbold
19826
et al.
et al.
et al.
et al.
et al.
et al.
et al.
et al.
et al.
et al.
et al.
et al.
1983
198lc(
I981c'
I98IC1
I98lc'
I98IC1
1981c'
19816
19816
19816
19816
1981 b
19816
« Peso Itelll
116
-------
Table 1. (Continued)
Specie*
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnarl
Rainbow trout,
Salmo gatrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnert
Rainbow trout,
Sal«p qalrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Brown trout,
Salmo trutta
Brown trout,
Salmo trutta
Brown trout,
Salmo trutta
Brook trout,
Salvellnus fontlnalls
Brook trout,
Salvellnus fontlnalls
LIU Stag*
or Si to
20.6 g
0.61 g
0.86 g
0.76 g
1.47 g
10.9 g
14.0 g
10.3 g
22.4 g
3.3 g
1.17 g
0.91 g
1.20 g
3.40 g
3.12 g
Chemical
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
Methods* Effect**
FT,M LC50
FT.M
FT,M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
LC50
LC50
LC50
UC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
Concentration
(«q/L NH,)
0.79C
0.40
1.02
0.77
0.97
0.26
0.61
0.59
0.43
1.04
0.701
0.677
0.597
1.05
0.962
Temperature
8.02-
8.55
8.30-
8.56
8.03-
8.29
8.45-
8.76
8.32-
8.69
7.7
7.7
7.9
7.9
8.3
12.8
3.0
14.2
3.3
14.9
3.6
16.2
18.7
7.86 13.8
7.82 14.2
0.0.
(•q/U
47-85*
Saturated
86-100*
Saturated
76-93*
Saturated
74-95*
Saturated
74-87*
Saturated
12.4
9.8 9.6
11.3 8.7
7.3
7.3
8.65
8.99
7.85 13.2 9.28
7.94 10.6
7.83 13.6
8.48
Reference
Relnbold I Pose I tell I
1982b
Relnbold & Pescltel II
1982b
Relnbold & Pescltel11
1982b
Relnbold & Peso I tall I
I982b
Relnbold & Pescltel 11
19825
West 1985
West 1985
West 1985
West 1985
West 1985
Thurston & Meyn 1984
Thurston & Meyn 1984
Thurston & Meyn 1984
Thurston & Meyn 1984
Thurston & Meyn 1984
117
-------
Table 1. (Continued)
Specie*
Mountain whlteflsh.
Prosoplum wllllamsoni
Mountain whlteflsh,
Prosop 1 urn will) amson 1
Mountain whlteflsh.
Prosop 1 urn will) amson 1
Golden shiner,
Notemlgonus crysoleucas
Red shiner,
Notropls lutrensls
Red shiner,
Notropls lutrensls
Spotfln shiner,
Notropls spllopterus
Spotfln shiner,
Notropls spllopterus
Spotfln shiner,
Notropls spllopterus
Steal co lor shiner,
Notropls whtpplel
Stonerol l«r,
Campos toma anonalum
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow.
Life Stage
or Size
56.9 g
63.0 g
177 g
8.7 g
0.43 g
0.40 g
31-65 mm
4 1-78 mm
0.5 g
0.5 g
2.1 9
0.09 g
0.09 g
Chemical
NH4CI
NH4C|
NH4C|
NH4C|
NH4C|
m4Cl
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
Methods*
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
Ef«ectb
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
Concentration Temperature D.O.
(mg/L NHj) pH <*C)
0.473
0.358
0.143
0,72C
2.83C
3.I6C
I.20C
I.62C
I.35C
1.25°
1.72C
1.59
1.50
1.10
7.84
7.80
7.68
7.5
8.2-
8.4
9.0-
9.2
7.7-
8.2
7.8-
8.5
7.9
7.9
7.8
8.0-
a.t
7.91
7.89
12.4
12.3
12.1
24.5
24
24
26.5
26.5
25.7
25.7
25.7
14
16.3
13.1
7.74
7.69
6.19
7.7
7.6-
8.2
7.5-
8.0
81-89*
Saturated
86-9 If
Saturated
7.3
7.3
6.4
7.2-
7.4
8.1
8.7
Reference
Thurston A Meyn 1984
Thurston & Meyn I9B4
Thurston & Meyn 1984
Swlgert & Spade 1983
Hazel et al . 1979
Hazel et al . 1979
Rosage et al. 1979
Rosage et al. 1979
Swlgert & Spacle 1983
Swlgert & Spacle 1983
Swlgert & Spacle 1983
DeGraeve et al . 1980
Thurston et al . 1983
Thurston et al. 1983
118
-------
Table I. (Continued)
Specie*
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promalas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promeias
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow.
Life Stage
or Size
0.13 g
0.19 g
0.22 g
0.22 g
0.26 g
0.31 g
0.31 g
0.35 g
0.42 g
0.42 g
0.47 g
0.47 g
0.50 g
0.8 g
1.0 g
Chemical
NH4C|
NH4C|
NH4C|
NH4C|
NH4CI
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4CI
NH4C|
NH4CI
NH4C|
NH4C|
Methods*
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT,M
FT.M
FT.M
Effect1*
LC50
LC50
LC50
LC50
LC50
t£50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
Concentration Tempereture
(mq/L NH,) nH CO
0.754
0.908
2.73
2.59
0.832
2.33
2.17
1.61
1.27
0.775
1.51
1.85
1.73
1.22
1.31
7.64
7.68
8.03
8.06
7.67
8.05
8.05
7.94
7.76
7.66
7.87
7.83
7.91
7.77
7.77
13.6
13.5
22.1
22.0
13.9
13.0
13.6
19.1
19.0
13.4
15.8
22.0
18.9
14.3
14.1
0.0.
(mg/L) Reference
8.8 Thurston
8.8 Thurston
7.6 Thurston
7.6 Thurston
8.5 Thurston
9.0 Thurston
8.9 Thurston
7.8 Thurston
8.2 Thurston
8.8 Thurston
8.3 Thurston
7. 1 Thurston
7.6 Thurston
8.6 Thurston
8.6 Thurston
[_
et
et
et
et
et
et
et
et
et
et
et
et
et
et
et
al.
al.
al.
al.
al.
al.
al.
al.
al.
al.
al.
al.
al.
al.
al.
1983
1983
1983
1983
1983
1983
1983
1983
1983
1983
1983
1983
1983
1983
1983
119
-------
Table 1. (Continued)
Species
Fathead Minnow,
PlMephales promalas
Fathead Minnow,
PlMephales proaelas
Fathead Minnow,
PlMephales promalas
Fathead Minnow.
Plmephales promelas
Fathead minnow.
PNephales promalas
Fathead winnow,
PlMephales promelas
Fathead Minnow,
PlMephales promalas
Fathed Minnow.
Plaephales promelas
Fathead Minnow,
Plmephales promelas
Fathead Minnow,
PlMophales promelas
Fathead Minnow,
PlMephales promelas
Fathead Minnow,
Plmephales promalas
Fathead Minnow,
PlMephales promalas
Fathead Minnow,
PlMephales promelas
Fathead minnow.
Life Stag*
or Size
1.4 g
1.4 g
1.4 g
1.4 g
1.4 g
1.4 g
1.5 g
1.7 g
2.1 g
2.2 g
2.3 g
1.8 g
2.0 g
2.0 g
1.8 g
Chemical
NH4CI
NH4C|
NH4C|
NH4C|
NH4CI
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
Methods*
FT,M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
Effect6
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
L£50
UC50
LC50
LC50
LC50
Coflcentratloa
, (M/L NH»)
2.16
2.73
3.44
2.04
1.23
1.10
1.73
2.03
1.09
0.796
1.34
0.240C
0.452C
1.08C
0.793C
> Tamperature
fH CCI
8.04
a.oe
8.16
7.88
7.68
7.63
7.76
7.84
7.76
7.74
7.91
6.51
7.01
7.82
7.83
22.4
21.4
21.4
21.7
12.9
13.2
12.9
21.7
13.1
12.8
15.9
13.0
13.8
12.0
11.8
0.0.
(•a/U
6.7
6.8
6.8
6.3
8.9
8.7
8.8
6.2
9.0
9.0
8.0
9.3
9.6
9.9
9.6
Refer enc<
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurston
Thurs ton
i
et al.
et al.
et al.
et al.
et al.
et al.
et al.
et al.
et al.
et al.
et al.
et al.
et al.
et al.
et al.
1983
1983
1983
1983
1983
1983
1983
1983
1983
1983
1983
I96lc
I98lc
I98lc
I98lc'
Plmephales promelas
120
-------
Table 1. (Continued)
Species
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promejas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
White sucker,
Catostomus commersonl
White sucker,
Catostomus commersonl
White sucker.
Life Stage
or Size
2.0 g
1.8 g
0.030 g
0.032 g
0.063 g
0.066 g
0.2 g
0.5 g
1.9 g
1.8 g
1.6 g
1.7 g
6.3 g
6.3 g
11.4 g
Chemical
NH4C|
NH4C|
NH4C|
NH4Ci
NH4C|
NH4C|
MH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
Methods*
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
Effect*
LC50
LC50
l£50
LC50
LC50
UC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
Concentration
(mo/L Mk>
I.68C
1.47=
0.73C
I.24C
0.80C
I.65C
I.75C
1.87C
2.41
1.83
1.97
2.55
1.40C
1.35C
0.79C
Ten
PH
8.51
9.03
8.21-
6.70
7.86-
8.18
8.13-
8.38
8.01-
8.32
7.78
7.8
7.9
8.1
8.0
8.1
8.07-
8.26
8.00-
8.28
7.8
iperature
TCI
13.5
13.2
4.t
23.9
4.6
25.2
25.9
25.6
3.4
12.1
17.1
26.1
15.0
15.4
22.5
0.0.
(•g/L)
9.8
9.5
87-96*
Saturated
73-79*
Saturated
88-96*
Saturated
73-79*
Saturated
7.1
7.2
12.4
9.8
8.0
6.3
93*
Saturated
88*
Saturated
7.4
•Reference
Thurston et al. 1981 c1
Thurston et al. 198lc!
Relnbold & Pesclteltl
1982b
Relnbold & Pesciteiil
19826
Relnbold & Pesciteiil
19826
Relnbold & Pesciteiil
19826
Swlgert & Spade 1983
Swlgert & Spade 1983
West 1985
West 1985
West 1985
West 1985
Relnbold & Pesciteiil
I982c
Relnbold & Pesciteiil
I982c
Swlgert & Spacla 1983
-------
Table 1. (Continued)
Species
White sucker.
Catostomus cooraer son 1
White sucker,
Catostomus commersonl
White sucker,
Catostomus coamersonl
tfhfte sucker,
Catostomus comer son 1
Mountain sucker,
Catostomus ptatyrhynchus
Mountain sucker,
Catostomus platyrhynchus
Mountain sucker,
Catostomus platyrhynchus
Channel catfish,
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Channel catfish,
Ictnlurus punctatus
Life Stage
or Size
5.6 g
5.2 g
6.1 g
9.6 g
63.3 g
47.8 g
45.3 g
50-70 mm
50-76 mm
50-76 mm
20.3 g
7.1-12.7 g
4.5-8.3 g
12.8 g
12.8 g
Chemical
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
f«4C|
NH4CI
NH4C|
NH4CI
W4C|
W4C|
W4C|
NH4C|
NH4C|
NH4C|
Methods8
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
S.U
S.U
S.U
FT.M
FT.M
FT.M
FT.M
FT.M
Effect6
LC50
LC50
LC50
LC50
LC50
LC50
LC50
l£50
LC50
LC50
LC50
LC50
LC50
LC50
UC50
Concentration Temperature
tmtfL NH,) PH co
0.76
1.87
1.73
2.22
0.819
0.708
0.668
2.4
2.9
3.8
I.95C
2.IK
4.2*
1.76C
I.75C
7.8
a.i
8.2
8.2
7.67
7.73
7.69
8.6-
8.8
8.6-
8.8
8.6-
8.8
8.34-
8.44
7.77-
8.41
7.91-
8.25
7.75-
8.20
7.77-
8.12
3.6
11.3
12.6
15.3
12.0
11.7
13.2
22
26
30
28
22
28
23.8
23.8
i D.O.
<«a/U
12.5
9.4
9.2
9.7
6.68
7.45
6.59
Near
saturation
Near
saturation
Near
saturation
7.6
80-89f
Saturated
80-90}
Saturated
89f
Saturated
86*
Saturated
Reference
West 1985
West 1965
West 1985
West 1985
Thurston & Meyn 1984
Thurston 4 Meyn 1984
Thurston & Meyn 1984
Colt & Tchobanoglous 1976
Colt & Tchobanoglous 1976
Colt & Tchobanoglous 1976
Colt & Tchobanoglous 1978
Rosabooa A Rlchey 1977
Roseboora & Rlchey 1977
Relnbold & Pescltel II
19826
ftetnbofd i Pescltel II
I982d
-------
Table 1. (Continued)
Sp*cl*«
Channel catfish,
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Mosqultoflsh,
Gambusla afflnls
Mosqultoflsh,
Gambusla afflnls
Mosqultoflsh,
Gambusla afflnls
Mosqultoflsh,
Gambusla afflnls
Guppy,
Poecllla retlculata
Guppy,
Poecllla retlculata
Guppy,
Poecllla retlculata
White perch,
Morone amerlcana
White perch,
• • . . _ _ _ • _
Life Stag*
or Size
0.5 g
5.6 g
6.4 g
3.6 g
3.5 g
7.4 g
Adult
females
Adult
females
Adult
females
Adult
females
8.0
mm
8.2
mm
8.7
mm
76 mm
76 mm
Chemical
NH4C|
NH4C|
NH4C|
NH4C|
HH4C|
NH4C|
-------
Table 1. (Continued)
Specie*
Green sun fish,
Lepomls cyanejlus
Green sunflsh,
Lepomts cyanellus
Green sunflsh,
Lepomls cyanellus
Green sunflsh,
Lepomls cyanellus
Green sunflsh,
Lepomls cyanellus
Green sunflsh,
Lepomls cyanel lus
Pumpklnseed,
Lepomls glbbosus
Punpklnseed,
Lepomls glbbosus
Pumpklnseed,
Lopomls glbbosus
Pumpklnseed,
Lepomls glbbosus
Blueglll,
Lepomls macrochlrus
Blueglll,
Lepomls macrochlrus
Blueglll.
Lepomls macrochlrus
Blueglll,
Lepomls «acrochlrus
Blueglll,
Lepomls macrochlrus
Life Stag*
or Size
8.4 g
9-d old
63.1 mg
63.1 mg
63.1 «g
63.1 mg
4.5 g
16.7 g
18.0 g
18.9 g
22.0-55.2
am
41.0-67.1
urn
35.3-65.5
nm
0.072 g
0.217 g
Chemical
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
M14C|
NH4C|
NH4C|
NH4C|
NH4CI
NH4C|
NH4C|
NH4C|
NH4C|
Methods*
FT,M
FT.M
FT.M
FT.M
FT.M
FT,M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT,M
Effect*
UC50
LC50
LC50
UC50
LC50
LC50
UC50
LC50
LC50
UC50
LC50
LC50
UC50
LC50
LC50
Concejitratlo* Te
(•g/l. NH,) oH
0.6ld
I.08C
0.59
1.29
1.64
2.11
O.I4d
0.78
0.86
0.61
0.89
2.97
2.57
0.55k
0.68k
7.84
8.09-
8.46
6.6
7.2
7.7
8.7
7.77
7.77
7.77
7.71
7.96-
8.26
7.95-
8.54
8.50-
9.00
8.01-
8.13
7.89-
8.12
•peratur*
CO
12.3
26.2
22.4
22.4
22.4
22.4
12.0
14.5
14.0
15.7
18.5
18.5
18.5
22
22
i D.O.
C»g/U
a. 3
88|
Saturated
8.1
8.1
8.1
8.1
8.4
8.37
8.36
7.16
9.1
9.1
9.1
95*
Saturated
95*
Saturated
Reference
Jude 1973
Relnbold i Pescltelll
I982a
McCormlck et al. 1984
McCoralck et al. 1984
McCormlck et al. 1984
McCormlck et al. 1984
Jude 1973
Thurston 1981
Thurston 1981
Thurston 1981
Emery & Welch 1969
Emery & Melon 1969
Emery & Welch 1969
Rosebooro & Rlchey 197;
Roseboora & Rlchey 197:
124
-------
TabU I. (Continued)
Specie*
Blueglll,
Lepomls macrochlrus
Blueglll,
Lepcmls macrochlrus
Blueglll,
Lepoals macrochlrus
Blueglll,
Lepomls macrochlrus
Blueglll,
Lepomls nacrochlrus
Blueglll,
Lepomls macrochlrus
Blueglll,
Lepomls mocrochlrus
Blueglll,
Lepcmls macrochlrus
Blueglll.
Lepomls macrochlrus
Blueglll,
Lepomls macrochlrus
Smal Imouth bass,
Hlcropterus dolomleul
Smal Imouth bass,
Hlcropterus dolomleul
Smal Imouth bass.
Hlcropterus dolomleul
Smal Imouth bass,
Hlcropterus dolomleul
Largemouth bass,
Hlcropterus sal mo Ides
Life Stag*
or Size
0.646 g
0.342 g
0.078 g
0.111 g
0.250 g
0.267 g
49.2 mg
0.9 g
0.9 g
1.2 g
265 mg
265 mg
265 mg
265 mg
2.0-6.3 g
Chemical
NH4C|
NH4C|
NH4C|
w4ci
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4CI
NH4CI
NH4C|
NH4C|
NH4C|
NH4C|
Methods*
FT.M
FT.M
FT.M
FT.M
FT,M
FT.M
FT,M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
Effect6
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
Concentration Temperature 0.0.
(•o/L NHjl. nH CO (mo/L)
1.lk
l.8k
0.50C
I.98C
0.26C
I.35C
0.94
I.35C
1.75C
1.76C
0.694
I.Ot
1.20
1.78
1.0k
7.89-
7.97
8.12-
8.28
8.32-
8.47
7.98-
8.25
8.06-
8.26
7.98-
8.20
7.60
7.8
7.6
7.8
6.53
7.16
7.74
8.71
7.82-
8.11
22
28
4.
0
25.0
4.5
24.
21.
24.
26.
26.
22.
22.
22.
22.
22
8
7
2
5
6
3
3
3
3
93*
Saturated
91*
Saturated
73-100*
74-83*
Saturated
87-97*
Saturated
74-89*
Saturated
7.89
6.4
7.0
7.2
7.93
7.90
7.97
8.00
85-94*
Saturated
Reference
Roseboom
Roseboom
Relnbold
IQfl?h
Re Into It
I982b
Relnbold
19825
Relnbold
1982b
Smith et
Swlgert &
Swlgert &
Swlgert &
Broderlus
Broderlus
Broderlus
Broderlus
& Rlchey 1977
& Rlchey 1977
& Pescltelll
& Pescltelll
& Pescltelll
& Pescltelll
al. 1983
Spacle 1983
Spacle 1983
Spacle 1983
et al. 1985
et al. 1985
et al. 1985
et al. 1985
Roseboom & Rlchey 1977
125
-------
Table I. (ContlMMd)
Specie*
Largamouth bass,
Mlcropterus salmoldes
Orangethroat darter,
Etheostoma spectablle
Orangethroat darter,
Etheostoma spectablle
Wai leye,
Stlzoatedlon vitreum
vitreum'
Wai leye,
Stlzostedlon vitreum
Walleye,
Stlzostedlon vitreum
Walleye,
Stlzostedlon vitreum
Mottled sculpln,
Cottus balrdl
Sar-jassum shrimp,
Latreutes fucorum
Prawn.
Macrobrachlum rosenberqll
Prawn,
Macrobrach 1 urn rosen berg 1 1
Prawn,
K« „_• t^ • _ _ _ t • 1
Life Stage
or Size
0.09-0.32 g
0.78 g
0.71 g
6-d
old
22.6 g
19.4 g
13.4
1.8 g
0.045 g
3-8 days
old
3-8 days
old
3-8 days
_ • -A
Chemical
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
Methods*
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
FT.M
S.M
R.M
R.M
R.M
Effect6
LC50
LC50
LC50
LC50
LC50
LC50
UC50
LC50
SALTWATER
LC50
LC50
LC50
LC50
Concentratloi
(mg/L NHxL
0.90C
I.07C
0.85C
0.52
1.10
0.51
1.39
SPECIES
0.936
1.3*
0.95*
0.38*
i Temperature
PH CO
7.98-
8.10
8.4
7.7-
8.5
7.84-
8.31
7.9
7.7
8.3
8.02
8.07
8.34
7.60
6.83
28
21
22
18.2
3.7
11.1
19.0
12.4
23.4
28
28
28
D.O.
(ma/L) Reference
83-88* Roseboom I Rlchey 1977
Saturated
7.6- Hazel et al. 1979
8.1
7.5- Hazel et al. 1979
8.1
97* Ralnbold & Pescltelll
Saturated 1982a
11.7 Wast 1985
9.0 Wast 1985
6.9 Wast 1985
8.9 Thurston & Russo 1981
6.7 Venkataramlak et al. 1981 a
7.3 Armstrong et al. 1978
7.3 Armstrong at al. 1978
7.3 Armstrong et al. 1978
-------
Table 1. (Continued)
Specie*
Eastern oyster,
Crassostrea virgin lea
Eastern oyster,
Crassostrea virgin lea
Qua hog clam,
Mercenarla nercenarla
Quahog clam,
Mercenarla marcenarla
Cop apod,
Nltocra splnlpas
American lobster,
Homarus amarlcanus
Red drum,
Sclaenops ocellatus
Striped mullet,
Muql 1 cephalus
Striped owl let,
Mugl 1 cephalus
Striped imillat,
Muqll cephalus
Striped mullet,
Muqll cephalus
Planehead flleflsh,
Life Stag*
or Size
46-62
13-17
28-32
an
4.7-5.2
an
3-6 »k
old
22-63
mg
larva
0.4 g
0.7 g
1.6 g
10.0 g
P.7 g
Chemical
NH4C|
NH4C|
NH4C|
NH4C|
NH3
NH4C|
(NH4)S04
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
Methods'
S,M
S,M
S.M
S,M
S,U
S.M
S.M
S.M
S.M
S.M
S.M
S.M
Effect5
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
LC50
Concentration
24-37d.»
8. 3-1 3d ••
3.2-5.0d'«
4.6-7.2d««
1.5««
2.2d
0.47
1.23
1.19
1.63
2.38
0.690
Teapereture
fH CC)
7.70-
8.23
7.70-
8.23
7.70-
8.23
7.70-
8.23
7.8
8.1
8.0-
8.2
8.08
8.14
7.99
8.00
8.07
20
20
20
20
21
21.9
25-
26
21.0
22.0
23.3
23.3
23.4
0.0.
(•Q/L)
7.0-
8.2
7.0-
8.2
7.0-
8.2
7.0-
8.2
i5
6.9
5.4-
6.4
7.9
7.8
7.6
7.5
6.7
Reference
Eplfanlo & Srna 1975
Epl fanlo & Srna 1975
Eplfanlo A Srna 1975
Eplfanlo & Srna 1975
Linden et al. 1979
Dellstraty et al. 1977
Holt and Arnold, 1983
Venkataramlak, 19 81 a
Vankataramlak, 1981 a
Venkataramlak, 1981 a
Venkataramlak, 1981 a
Venkataramlak, 1981a
Monacanthus hlspldus
127
-------
Table I. (Continued)
8 FT • flow-through, S • static, R " renewal, M » measured, U » unmeasured.
b Duration of exposure for Invertebrates either 48 h or 96 h; duration of exposure for fishes 96 h.
c Recalculated from authors' NHj-N values.
** Recalculated from authors' total ammonia values.
* pH data used In NHj calculation obtained from: Epl fanlo, C. E., personal communication.
f 96-h LC50 or EC50 estimated from authors* graph.
9 EC50: 50% of test animals motionless.
" Dissolved oxygen data obtained from: Thurston, R.V., personal communication.
' Dissolved oxygen and fish size data obtained from: Thurston, R.V., personal communication.
J Information on test conditions obtained from: Parkhurst, B., personal communication.
* Recalculated from authors* NHyN values with re-correction for percent NHj per authors' text.
128
-------
Table 2. Chronic Toxlcity of Ammonia to Aquatic Animals
Species
Cladoceran,
Cerlodaphnla acanthi na
Cladocaran,
Daphnla magna
Cladoceran,
Daphnla magna
Cladocaran,
Daphnla magna
Pink saloon,
Oncorhynchus gorbuscha
Pink salmon,
Oncorhynchus gorbuscha
Pink salmon,
Qncorhynchus gorbuscha
Rainbow trout.
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Atlantic salmon,
Salmo salar
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales promelas
Method*
LC
LC
LC
LC
ELS
ELS
ELS
ELS
LC
ELS
ELS
ELS
LC
LC
T
JJH
7.0-
7.5
8.09
7.6
7.63-
6.16
6.3-
6.5
6.3-
6.5
6.3-
6.5
7.4
7.69-
7.72
7.4-
7.6
7.4-
7.6
6.7-
7.5
8.01
7.99
emperature
CO
0.0.
(mg/L)
Halts Chronic Value
(mq/L MH,) (mq/L MH,)
Reference
FRESHWATER SPECIES
24.0-
25.0
22.1
20.2
17.8-
20.8
4
4
4
14.5
9.3
10-
12
10-
12
13
24.0
24.2
5.7-
6.4
6.9
7.7
88-9 It
Saturated
-
-
-
>BO%
Saturated
7.3-
7.6
>8
>8
10
6.3
6.5
0.199-0.463^
0.378-0.735
0.53-0.76
0.96-l.6b
0.0024-0.004
0.0012-0.0024
0.0012-0.0024
0.010-0.025
0.0221-0.0439
<0.06
0.06-0.12
0.002-0.079
0.088-0.188
0.092-0.187
0.304
0.527
0.63
1.2
0.0031
0.0017
0.0017
0.016
0.0311
<0.06C
0.085
0.01
0.13
0.13
Mount 1982
Russo et al. 1985
Russo. et al. 1985
Relnbold & Pescltelll
I982a
Rice & Bailey 1980
Rice & Bailey 1980
Rice & Bailey 1980
Calamarl et al. 1977
1981
Thurston et al. I984b
Burkhalter & Kaya
1977
Burkhalter & Kaya
1977
Samylln 1969
Thurston et al.
(Submitted)
Thurston et al.
(Submitted)
129
-------
Table 2. (Continued)
Species
Fathead minnow,
Plmephales promelas
White sucker,
Catostomus commersonl
Channel catfish,
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Green sun fish,
Lepomls cyanellus
Blueglll,
Lepomls macrochlrus
Smal Imouth bass,
Mlcropterus dolomleul
Smal Imouth bass,
Mlcroptarus dolomleul
Smal Imouth bass,
Mlcropterus dolomleul
Smal Imouth bass,
Mlcropterus dolomleul
Temperature
Method* pH CO
ELS
ELS
ELS
J1
j'
ELS
ELS
ELS
ELS
ELS
ELS
ELS
7.63-
8.13
8.01-
8.65
7.6-
7.8
8.30-
8.44
7.53-
8.37
7.34-
7.95
7.9
7.74
6.60
7.25
7.83
8.68
22.7-
26.3
16.9-
20.5
25.1-
25.3
27.8-
28.0
24.8-
28.4
23.5-
28.0
22
22
22.5
22.2
22.3
22.2
0.0.
-------
Table 2. (Continued)
Acute-Chronic Ratio
Species
Cladoceran.
Daphnla magna
Cladoceran,
Daphnla magna
Cladoceran,
Daphnla magna
Pink salmon,
Oncorhynchus gorbuscha
Pink salmon,
Oncorhynchus gorbuscha
Pink salmon,
Oncorhynchus gorbuscha
Rainbow trout.
Sal mo galrdnerl
Rainbow trout.
Sal mo galrdnerl
Fathead minnow,
Plroephales promelas
Fathead minnow,
Plmephales promelas
Fathead minnow,
Plmephales pronto las
White sucker,
Catostomus commersonl
Channel catfish,
Ictalurus punctatus
Channel catfish.
Acute Value1
(mq/L NH?)
2.68
0.878
4.6
0.090d
0.090d
0.090d
0.422*
0.35*
2.54f
2.56*
I.758
l.75«
2.42
1.95
Chronic Value
(mo/L NH,)
0.527
0.63
1.2
0.0017
0.0017
0.0031
0.0311
0.016
0.13
0.13
0.22
0.058
0.103
<0.25
Ratio
5.1
1.4
3.9
53
53
29
14
22h
20
20
8.0h
30
I5J
a-34k
Ictalurus punctatus
131
-------
Table 2. (Continued)
Acute-Chronic Ratio
Specie*
Channel catfish,
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Green sun fish,
Lepomls cyaneMus
Blueglll,
Lepomls macrochlrus
Smal (mouth bass,
Hlcropterus dolomleul
Smal (mouth bass,
Hlcropterus dolomleul
Snal (mouth bass,
Mlcropterus dolomleul
Sraal Iroouth bass,
MJcroptarus dolomleul
Acute Value1
(mo/L NH?)
2.I2«
1.5B
2.05
1.08
0.81
1.14
1.30
1.77
Chronic Value
(ma/L NHj)
0.283
0.18
0.33
0.0926
0.0437
0.148
0.599
0.612
Ratio
7.5
8.8
6.3
12
19
7.7
2.2
2.9
Geometric mean of acute-chronic ratios for Daphnla magna • 3.0
for pink salmon * 43
for fathead minnow =• 20 (15 If ELS study Included)
for smallmouth bass « 5.4 (3.6 for pH^. 7.25)
for channel catfish - 10
for rainbow trout » 14 (18 If ELS study Included)
132
-------
TabU 2. (Continued)
• LC • life cycle, ELS - early life stage, J * juvenile.
b Recalculated from author's NH3~N values.
c Lowest concentration tested, above control, affected growth (P<0.05).
d Estimated front authors' graph.
* Acute value geometric mean of acute tests In same Maters as used for respective chronic tests.
* Acute value geometric mean of acute tests with juveniles In same water as used for chronic test.
9 Recalculated from author's total ammonia values.
n Value not used In criteria calculations because results are available from life cycle test with same species (see Guidelines).
' Value corrected to pH of chronic value.
J Acute value Is for 24 hours, acute-chronic ratio multiplied by 0.65 » average ratio of 96-hour LC50 to 24-hour LC50 for several acute
studies on channel catfish (range » 0.50 - 0.75).
k Upper limit for ratio based on control concentration (0.06 mg/llter NHj).
' Juvenile tests Included because same or greater sensitivity shown as for embryo-larval ELS tests.
133
-------
Tabla 3. Ranfcad Gwius Maan Acuta Valuas with Spaclas Maaa Acuta/Chroalc Ratios
Rafaranca Ganus Rafaranca Spaclas
Maan Acuta Valua Maan Acuta Valua
lank* Imn/L NH,)b Spaclas
-------
TabU 3. (Continued)
Rank*
22
21
20
19
18
17
16
15
14
13
Reference Genus Reference Specie* Species Mean
MM* Acute Value Mean Acute Value Acute-Chronic
(wa/L NH,)b Sp«cl«S iKl/L NHx)ft Ratio
2.07
1.96
1.95
1.89
1.79
1.69
1.68
1.63
1.49
1.48
Fathead Minnow,
Plmaphales proaielas
Cladocaran,
Cerlodaphnla acanthi na
Snail,
Physa gyrlna
Cladocaran,
Slmocephalus vetulus
White sucker,
CatostOHuis confer son!
Mountain sucker,
Cstostcmus platyrhynchus
Brook trout,
Salve! Inus fontlnalls
White perch,
Morone anerlcana
Channel catfish,
1 eta tor us punctatus
Cladocaran,
Oaphnla magna
Cladocaran,
Oaphnla pull car la
Guppy,
2.07 20
1.96 3.5
1.95
1.89
2.15 30
1.49
1.69
1.68
1.63 7.5
1.91 3.1
1.16
1.48
Poecllla retlculata
135
-------
Table 3. (Continued)
Rank*
12
11
10
9
8
7
Reference Genus Reference Specie* Species Mean
Mean Acute Value Mean Acute Value Acute-Chronic
f«o/L NH5>b Sp*clM («Q/L NH,)6 Ratio'.
1.40 Flatwonn,
Oandrocoelun lacteum
(Procotyla ^luvlatllls)
1.34 SmallMOuth bass,
Mlcroptarus
-------
Table 3. (Continued)
Rank"
6
5
4
3
2
1
9
8
Reference Genus Reference Species Specie* Keen
MMn Acute Value Mean Acute Value Acuta-Chronlc
(•g/L NH?)D Spaclas («q/L NH»)D Ratio
1.10 Clam,
Huscullum transversuM
1.10 Golden trout.
Sal mo aquabonlta
Cutthroat trout.
Sal mo clarkl
Rainbow trout.
Sal mo galrdnerl
Brown trout,
Salmo trutta
1.07 Walleye.
Stlzostedlon vltreum
v 1 treum
0.88 Orangethroat darter,
Etheostoma spectablle
0.76 Golden shiner,
Notemlgonus crysoleucas
0.56 Mountain Mhlteflsh,
Prosoplum wllllamsonl
SALTWATER SPECIES
18.3 Eastern oyster,
Crassostrea vlrglnlca
5.0) Quahog clam.
1.10
1.21
1.20
0.93 14
1.10
1.07
0.88
0.76
0.56
18.3
5.01
Mercenarla mercenarla
137
-------
Tabis 3. (Ccr.tir.uedi
Reference Genut Reference Specie* Specie* Mean
Maaa Acute Vaius Meaa Acute Value Ac«te-Cisro«!e
Reek* (ea/L NH,»6 Specie* (ea/L MHO* Ratio
7
6
5
4
3
2
1
1.93
1,56
0.76
1.31
2.13
0.55
0.32
American lobster,
Homarus oMericanus
Copepod.
Nltocra splnlpes
Prawn,
Macrobrachlun rosenbergll
Striped «ullet.
Mug II cephalus
Sargassum shrlep,
Latreutes fucoruai
Planehead flleflsh,
Honacanthus hlsgldus
Red drum,
Sclaenops ocellatus
2.20
1.68
1.32
1.31
0.94
0.55
0.32
8 Ranked from least sensitive to most sensitive based on Genus Mean Acute Values.
b See text for discussion of reference conditions. Mid-range pH and temperature values used where given as a range In
test results from Table 1.
Freshwater FAVref = 0.70 «g/L NH3 (calculated froa GMAVrefs).
Freshwater FAVrat = 0.52 mg/L NHj (lowered to protect rainbow trout - see text).
138
-------
Table 4. Toxlclty of Amonla to Aquatic Plants
Species
Temperature
Chemical pH CO
Effect
Concentration
(ma/L NH,)
FRESHWATER SPECIES
Alga,
Scenedesmus obllquus
Alga,
Scenedesmus obllquus
Alga,
Scenedesmus obllquus
Alga,
Anacystis nldulans
Alga,
Anacystis nldulans
Alga,
Plectonema boryanum
Alga,
Plectonema boryanum
Alga,
Chlorella pyrenoidosa
Alga,
Ch 1 ore 1 1 a pyreno 1 dosa
Alga,
Chlorella vulgarls
Alga,
Chi ore 1 la vulgar Is
NH4C| 8.8 30
NH4C| 7.9 30
NH4C| 9.0 30
NH4C| 7.0 30
NH4C| 9.0 30
NH4C| 7.0 30
NH4C| 9.0 30
NH4C| 7.0 30
NH4C| 9.0 30
(NH4)2C03 7.0 26
(NH4)2COj 7.0 26
EC50, oxygen
evolution Inhibition
\0% reduction In
(X>2 Photoasslml latlon
rate
Q&% reduction In
002 Photoass Imitation
rate
}Q% reduction In
C02 photoasslml latlon
rate
11% reduction In
C02 photoasslml latlon
rate
I6< reduction In
C02 photoasslml lation
rate
92% reduction In
002 Photoasslml latlon
rate
\\% reduction In
CCU photoasslml latlon
rate
T)% reduction In
002 Photoasslml latlon
rate
LC50
EC50, growth
Inhibition
lia.b
5.la
38a
0.68a
38a
0.68a
38a
0.68a
38a
9.8a
2.4a
Reference
Abellovlch & Azov 1976
Abellovlch & Azov 1976
Abellovlch A Azov 1976
Abellovlch & Azov 1976
Abellovlch & Azov 1976
Abellovlch & Azov 1976
Abellovlch & Azov 1976
Abellovlch & Azov 1976
Abellovlch & Azov 1976
Przytocka-Juslak 1976
Przytocka-Juslak 1976
139
-------
TabU 4. (Continued)
Diatom,
Navlcula arenarla
Diatom,
Nltzschla c.f. dlsslpata
01 atom,
Nltzschla dublformls
Diatom,
Nltzschla closterlum
Diatom,
Amphlprora c.f. pa 1 udosa
Diatom,
Stauronels con strict a
Diatom,
Navlcula cryptocephala
Diatom.
Nav 1 cu 1 a sa 1 1 nar urn
Diatom,
Gyros 1 gma spencer 1 1
Diatom,
Nltzschla slgma
Chemical pH
MH4C| 8.0
NH4C| 8.0
NH4C| 8.0
NH4C| 8.0
NH4C| 8.0
NH4C| 8.0
NH4C| 8.0
NH4C| 8.0
NH4C| 8.0
NH4C| 8.0
Temperature
(*C) EMect
Concentration
(mo/L MHO
Refer enci
>
SALTWATER SPECIES
12
12
12
12
12
12
12
12
12
12
25$ reduction
chlorophyll a
62$ reduction
chlorophyll a
73$ reduction
chlorophyll a
77$ reduction
chlorophyll _a_
46$ reduction
chlorophyll _a_
33$ reduction
chlorophyll a
14$ reduction
chlorophyll a
18$ reduction
chlorophyl 1 _a_
66$ reduction
chlorophyll a
66$ reduction
chlorophyll a
In
In
In
In
In
In
In
In
In
In
0.24*
0.24*
0.24*
1.2*
0.24*
0.24*
0.24*
0.24*
0.24*
0.24a
Admlraal
Admlraal
Admlraal
Admlraal
Admlraal
Admlraal
Admlraal
Admlraal
Admlraal
Admlraal
1977
1977
1977
1977
1977
1977
1977
1977
1977
1977
0 Recalculated from authors' total ammonia values.
k Estimated from authors' graph.
140
-------
Table 5. Other Data on Effects of Ammonia on Aquatic Organisms
Species Chemical
Temperature
OH CO
Concentration
Duration Effect (mg/L MHO
Reference
FRESHWATER SPECIES
Rotifer, NH4C|
Phllodlna acutlcornls
Mussel, NH4C|
Elllptlo complanata
Mussel, NH.Cl
Elllptlo complanata
Mussel, NH4C|
Elllptlo complanata
Mussel, NH4HCOj
Amblema p. p 1 1 cat a
Mussel. NH.HCO,
Anodonta Imbed II Is
Mussel, NH4HCO}
Cyr tonal as tamp 1 coens Is
Mussel, NH4HC03
Toxolasma texasensls
Asiatic clam, NH4C|
Corblcula roanllensls
Asiatic clam, NH4C|
Corblcula man I lens Is
Asiatic clam, NH4C|
Corblcula man liens Is
Asiatic clam, NH4HC03
Corblcula manllensls
7.4-
7.9
7.5
7.5
7.5
7.8-
8.2
7.8-
8.2
7.8-
8.2
7.8-
8.2
7.5
7.5
7.5
7.8-
8.2
20
18
18
IB
24-
26
24-
26
24-
26
24-
26
18
18
18
24-
26
96 h EC50 (No re-
sponse to 1 Ight)
<1 h 50* reduction
In ciliary
beating rate
<\ h 90* reduction
In ciliary
beating rate
-------
Table 5. (Continued)
Species
Fingernail clam,
Muscullum transversum
Fingernail clam,
Muscullum transversum
Fingernail clam,
Muscullum transversum
Fingernail clam,
Muscullum transversum
Fingernail clam,
Muscullum transversum
Fingernail clam,
Muscullum transversum
Fingernail clam,
Muscullum transversum
Fingernail clam,
Muscullum transversum
Fingernail clam,
Muscullum transversum
Fingernail clam,
Muscullum transversum
Fingernail clam,
Muscullum transversum
Temperature
Chemical
NH4C|
NH.CI
«t
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
Iti
8.09-
8.20
8.08-
8.18
8.08-
8.18
7.5
7.5
7.5
7.5
7.5
7.5
7.75-
7.85
7.75-
7.85
CO
23.5
22.9
22.9
18
18
18
IB
18
18
21.7-
21.9
21.7-
21.9
Concentration
Duration Effect
42 d 67*
Mortality0
42 d 72*
Mortality0
14 d Reduction
In growth
_O h 50* reduction
In ciliary
beating rate
of >5 mm clams
5 mm clams
£l h 90* reduction
In ell lary
beating rate
of _<5 mm clams
5 mm
clams
<1 h Complete In-
hibition of
cilia of _<5 rnn
clams
6 wk 47*
Mortality
4 wk 36*
Mortality
(rnoA MHO
0.72b
0.73b
0.4 lb
0.036b
0.073r
0.085b
0.049b
0.097b
0.061-
0.073b
0.097-
0.1 lb
0.073b
0.23b
Reference
Anderson
Anderson
Anderson
Anderson
Anderson
Anderson
Anderson
Anderson
Anderson
Sparks &
Sparks &
et al. 1978
et al. 1978
et al. 1978
et al. 1978
et al. 1978
et al. 1978
et al. 1978
et al. 1978
et al. 1978
Sandusky I9(
Sandusky I9£
142
-------
Table 5. (Continued)
Species
Chemical
Temperature
CO
Duration Effect
Concentration
(mg/L NHxL Reference
Fingernail clam,
Muscullum transversum
Fingernail clam,
Muscullum transversum
Cladoceran,
Daphnla magna
Cladoceran,
Daphnla magna
Cladoceran,
Daphnla magna
Cladoceran,
Daphnla magna
Cladoceran,
Molna rectlrostrls
Daphnla
(sp. not specified)
Daphnla
(sp. not specified)
Daphnla
(sp. not specified)
Mayfly.
Ephemeral la doddsl
Mayfly,
Ephemeral la doddsl
Mayfly,
Ephemeral la doddsl
Mayfly,
C _&. ___._ II. ^j^ftttf I
NH4C|
NH4C|
(NH4)2S04
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
7.75-
7.85
7.75-
7.85
8.2-
8.4
8
7.9
8.09
8.3
6.0
7.0
8.0
7.85
7.91
7.83
7.91
21.7-
21.9
21.7-
21.9
25
19
22
22.1
25
25
25
25
12.0
13.6
10.7
11.0
4 Mk
6 Mk
64 h
2 d
50 h
28 d
24 h
24 h
24 h
24 h
96 h
96 h
96 h
96 h
23*
Mortality
Complete
growth Inhibi-
tion
Threshold
value
Minimum lethal
concentration
LC50
LC50
LC50
LC50
LC50
LC50
60*
Survival
80*
Survival
100*
Survival
90*
0.63b
0.036b
2.4-3.6
0.55
2.0a»f
1.53
1.50
0.17a'c
1.4a.c
5.1a'c
6.20
5.46
2.64
2.20
Sparks & Sandusky 1981
Sparks & Sandusky 1981
Anderson 1948
Malacca 1966
Dowden & Bennett 1965
Russo et al. (In prep.)
Gyore & Olah 1980
Tabata 1962
Tabata 1962
Tabata 1962
Thurston et al. 1984a
Thurston et al. 1984a
Thurston et al. 1984 a
Thurston et al. I984a
143
-------
Table 5. (Continued)
Species
Mayfly,
Ephemeral la grandIs
Mayfly.
Ephemeral la grandIs
Mayfly,
Ephemeral la grandIs
Mayfly,
Ephemeral la grand Is
Mayfly,
Ephemeral la sp. near
excruclans
Stonefly,
Pteronarcella bad Ia
Stonefly,
Pteronarcella bad I a
Stonefly,
Pteronarce11a badI a
StonefIy,
Pteronarce11 a bad I a
Stonefly,
Pteronarce11 a bad I a
Stonefly,
Arcynopteryx para I lei a
Stonefly,
Arcynopteryx parallela
Stonefly,
Arcynopteryx parallela
Stonefly,
Arcynopteryx parallela
Che* leal
NH4C|
NH4C|
NH4C|
MH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
Temperature
^H CO
8.06
7.83
7.91
7.68
8.53
7.66-
7.91
8.04
8.04
7.81
7.81
7.88
7.84
7.95
7.88
13.5
10.7
II. 0
10.5
20
10.7-
13.3
12.1
12.1
13.2
13.2
13.3
12.8
13.3
13.6
Duration
96 h
96 h
96 h
96 h
24 h +
72 h
recovery
96 h
30 d
30 d
24 d
24 d
96 h
96 h
96 h
96 h
Concmtratli
Effect (»gA NH,L
90%
Survival
60%
Survival
60%
Survival
80*
Survival
EC50
(Mortality at
96 h after
24-h exposure)
too*
Survival
l£50
Inhibition of
emergence
LC50
Inhibition of
emergence
100$
Survival
80$
Survival
90*
Survival
60*
Survival
4.66
2.64
2.20
1.54
4.7b
1.35-7.49
4.57
3.7
1.45
3.4
7.49
6.24
4.05
3.03
Thurston et al. I984a
Thurston et al. 1984a
Thurston et al. I984a
Thurston et al. 1984a
Gal I 1980
Thurston et al. I984a
Thurston et al. I984a
Thurston et al. I984a
Thurston et al. I984a
Thurston et al. 1984a
Thurston et al. 1984a
Thurston et al. I984a
Thurston et al. I984a
144
-------
Table 5. (Continued)
Species
Caddlsfly,
Arctopsycha grand Is
Caddlsfly,
Arctopsycha grand Is
Pink salmon,
Oncorhynchus qorbuscha
Coho salmon,
Oncorhynchus klsutch
Sockaye salmon,
Oncorhynchus nerka
Sockaya salmon,
Oncorhynchus nerka
Chinook salmon,
Oncorhynchtis tshaxytscha
Chinook salmon,
Oncorhynchus t showy tscha
Cutthroat trout.
Sal no dark)
Cutthroat trout.
Sal mo clarkl
Cutthroat trout.
Sal mo clarkl
Cutthroat trout,
Salmo clarkl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
<*_• ^ __i__j__.»l
Chemical
NH4C|
NH4C|
(NH4>2S04
NH4OH
NH4C|
NH4C|
NH4OH
NH4C|
NH4C|
m4ci
NH4C|
NH4d
(NH4)2S04
NH4OH
NH4C|
Temperature
fH CO
7.88
7.92
6.3-
6.5
8.0
8.42
8.45
7.6
7.59-
7.90
7.81
7.80
7.80
7.78
7.55
9.42
7.2
13.3
13.8
3.7
4.8
14.2
10
10
15.3
11.7
13.1
12.8
12.4
12.2
14
13.5
15.2
Duration
96 h
96 h
96 h
72 h
62 d
62 d
72 h
24 h
36 d
36 d
29 d
29 d
360 mln
3.5 h
1000 mln
Effect
90%
Survival
80J
Survival
No harm
to eyed
embryos
critical
level
30J
Mortality
100|
Mortality
critical
level
l£50
LC50
LC50
LC50
LC50
time to
death
activity
ceased
median
.1 • A i
Concentration
(mq/L NH}1 Reference
7.49
4.19
>l.5
0.13*
0.12b
0.49b
0.04-
0.11a
0.36
0.56
0.56
0.37
0.34
0.32h
29.6a
O.I8b
Thurston et al. I984a
Thurston et al. 1984 a
Rice & Bailey 1980
Holland et al. I960
Rankln 1979
Rankln 1979
Holland et al. 1960
Harader and Allen 1983
Thurston et al. 1978
Thurston et al. 1978
Thurston et al. 1978
Thurston et al. 1978
Muhrmann & Wokar
1948
Cortl 1951
Allan et al . 1958
145
-------
TabU 5. (Continued)
Species
Rainbow trout,
Salmo galrdnerl
Rainbow trout
Sal mo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo qalrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Sal mo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Sal BO galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo qalrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo galrdnerl
Chemical
NH4C|
NH4C|
Urea
Urea
NH4C|
NH4C|
Manure
1 eachate
Manure
1 eachate
NH4C|
NH4C|
NH4C|
NH4C|
(NH4)2S04
IOOO mln
29.8 mln
1-4 d
Concentration
Effect
-------
Tabla 5. (Continued)
SpecIas
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo qalrdnerl
Rainbow trout,
Salmo qalrdnerl
Rainbow trout (embryo),
Sal mo qalrdnerl
Rainbow trout,
Salmo qalrdnerl
Rainbow trout,
Salmo qalrdnerl
Rainbow trout,
Salmo qalrdnerl
Rainbow trout,
Sal mo qalrdnerl
Rainbow trout,
Salmo qalrdnerl
Rainbow trout,
Salmo qalrdnerl
Rainbow trout,
Salmo qalrdnerl
Rainbow trout,
Salmo galrdnerl
Rainbow trout,
Salmo qalrdnerl
Rainbow trout.
Salmo galrdnerl
Chemical
Endogenous
NH3-N
(NH4)2S04
_
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
WC|
Temperature
^H CO
7.75
8.3
7.6
7.4
7.4
7.4-
7.6
7.95
7.85
7.90
7.9
7.66
7.64
7.81
7.89
10
10
15
14.5
14.5
10-12
10
13.1
11.9
13
9.8
10.0
13.0
12.6
Duration
12 inon
24 h
36 d
96 h
72 d
21 d
30 d
12 d
12 d
12 d
12 d
12 d
35 d
35 d
(
Effect
Hlstopatho-
loglcal
effects with
juveniles
LC50
81}
Mortality
LC50
LC50
LC50
Reduced
growth
LC50
LC50
LC50
LC50
LC50
LjCSO
LC50
!oncentratl<
(mg/L NH3)
0.0155
0.068
0.30-0. 36 '
X).486
0.056
0.30b
X). 10
0.490
0.464
0.684
0.262
0.312
0.483
0.598
Reference
Smith & Piper 1975
Rice & Stokes 1975
Calamarl et al. 1977,
1981
Calamarl et al. 1977,
1981
Burkhalter & Kaya 1977
BrOder I us 1 Smith 1979
Thurston & Russo 1983
Thurston & Russo 1983
Thurston & Russo 1983
Thurston & Russo 1983
Thurston & Russo 1983
Thurston & Russo 1983
Thurston & Russo 1983
147
-------
Table 5. (Continued)
Species
Rainbow trout,
Sal mo qairdnerl
Rainbow trout,
Sal mo galrdnerl
Rainbow trout,
Sal mo qairdnerl
Rainbow trout.
Sal mo galrdnerl
Rainbow trout.
Sal mo galrdnerl
Atlantic salmon.
Sal mo salar
Atlantic salmon,
Salmo salar
Atlantic salmon,
Salmo salar
Atlantic salmon,
Salmo salar
Atlantic salmon,
Salmo salar
Brown trout,
Salmo trutta
Brown trout.
Salmo trutta
Brook trout.
Chemical
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4OH
NH3 excreted
Temperature
gH CO Duration
7.69
7.69
7.9
7.82-
8.06
7.7
7.81
7.69
7.92
8.12
8.05
7.8
7-8
7.0
13.2 35 d
13.2 35 d
13 35 d
8-12 90 d
9.3 5 yr
13.6 24 h
12.0 24 h
12.0 24 h
10.7 24 h
11.5 24 h
11 18 h
15 "Un-
limited"
12.8 1.75 h
Concentration
Effect (mg/L NH,) Reference
LC50
LC50
LC50
No gill
lesion
HI stopath-
ologlcal
effects In
parental and
juveniles
0.426
0.322
0.659
0.2-
0.4
>0.04
LC50 0.28"
LC50 In 0.15
freshwater
LC50 In 30* 0.3
seawater
LC50 (10 0.2
mg/L dissolved
oxygen)
LC50 (3.2 0.08
mg/L dissolved
oxygen)
36*
mortality
No observed
effect
dl stress
0.1 5a
0.8
3.25
Thurston & Russo
Thurston & Russo
Thurston & Russo
1983
1983
1983
Oaoust & Ferguson 1984
Thurston et al. I984b
Herbert & Sh urban
Alabaster et al.
Alabaster et al.
Alabaster et al.
Alabaster et al.
Taylor 1973
Woker & Wuhrmann
Phillips 1950
1965
1979
1979
1983
1983
1950
Salvellnus fontlnalls
from fish
148
-------
TabU 5. (Continued)
Species
Brook trout.
Salvellnus fontlnalls
Goldfish,
Carasslus auratus
Goldfish.
(sp. not spec! fled)
Goldfish,
(sp. not specified)
Goldfish,
(sp. not specified)
Carp,
Cyprlnus carplo
Carp,
Cyprlnus carplo
Carp,
Cyprlnus carplo
Carp,
Cyprlnus caprlo
Carp,
(sp. not specified)
Carp,
(sp. not specified)
Carp,
(sp. not specified)
Carp,
(sp. not specified)
Carp,
(sp. not specified)
Fathead minnow.
Plmephales prone las
Chemical
NhU excreted
from fish
NH4CI
NH4CI
(NH4 >2S04
(NH4)2CO}
Urea
Urea
(NH4)2S04
NH4CI
Manure
1 eachate
-
(NH4)2S04
(NH4)2S04
(NH4)2S04
NH4Cl
Temperature
pH CO
7.0 15
7.9 22
7.65 18.8-
20.5
7.60 18.80
20.5
8.0 18.80-
20.5
8.75 16-18
8.35 16-18
7.8 24.5
7.4 28
15-17
_ _
7.8 18
8.2 25
22
7.59- 21.6-
7.82 21.9
Concentration
Duration Effect («g/L NH^L
2.5 h distress
24 h LC50
15 d Lethal
threshold
15 d Lethal
threshold
15 d Lethal
threshold
2.42 h time to
death
6.0 h time to
death
4 d Minimum
lethal
concentration
96 h LC50
"Unlimited" No observed
effect
4 h death
18 h Not lethal
17 mln Loss of
equilibrium
45 mln Loss of
equl 1 Ibrlum
72 h LC50
5.5
7.2*.'
1.4-1.5"
0.97-1.1*
3.4-3.8*
9.7
2.1
l.4a
I.I
<1.5
7.5«>
0.24
0.67
0.52
1.68
Refer Mice
Phillips 1950
Doxden & Bennett 1965
Chlpman 1934
Chlpman 1934
Chlpman 1934
Nehrlng 1962-63
Nehrlng 1962-63
Malacea 1966
Rao et al . 1975
Danecker 1964
Kemplnska 1968
Vamos 1963
Vamos 1963
Vamos 1963
Sparks 1975
149
-------
Table 5. (Continued)
Temperature
Species Chemical ^H (*CI
Fathead minnow. NH4C| 8.0 25
Plaephales promelas
Bitter I Ing. (NH4>2S04 7.8 24.5
ftnodeus serlceus
Rudd, NH4C| 8.05- 12.2-
Scardlnlus erythrophthalmus 8.30 13.2
Creek chub, W4OH 8.3 15-21
Semot11us atromacuIatus
Tench, Manure - 18
Tinea tinea leachate
Channel catfish, M4j excreted 7.7 21.1
Ictalurus punctatus from fish
Channel catfish. NH} excreted 7.8 21.7
Ictalurus punctatus from fish
Channel catfish, tHj excreted 7.8 22.8
Ictalurus punctatus from fish
Channel catfish, NH3 excreted 8.0 22.8
Ictalurus punctatus from fish
Channel catfish, NH4C| 7.73- 19.8-
Ictalurus punctatus 8.16 20.0
Channel catfish, - -
Ictalurus punctatus
Channel catfish, NH4C| 7.0 21-
Ictalurus punctatus 25
Channel catfish, NH4C| 7.0 21-
Ictalurus punctatus 25
Duratloa Effect
Concwttratk
(•g/L
304 d Hlstopath- >0.639
ologlcal
Intracerettral
lesions
4 d
Minimum
lethal
concentration
0.76a
6 d asymptotic 0.44b
LC50
24 h "critical 0.26-1.2a
range"
20-24 h time to
death
I Mk LC50
LC50
l£50
I Mk
48 h
48 h
24 h
24 h
LC50
LC50
LC50
LC50
l£50
2.5
0.974*
1.27*
1.41-
l.97a
2.92
1.24-
1.96
l.69b
2.171
Reference
Smith 1984
Malacea 1966
Ball 1967
Gillette et al. 1952
Oanecker 1964
Knepp & ArkIn 1973
Knepp & ArkIn 1973
Knepp & Ark In 1973
Knepp & ArkIn 1973
Sparks 1975
Vaughn & Slmco 1977
Tomasso et al. 1980
Tomasso et al. 1980
150
-------
Table 5. (Continued)
Temperature
Specie*
Channel catfish.
Ictalurus punctatus
Channel catfish.
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Mosqultoflsh,
Gambusla afflnls
Guppy,
Poecllla retlculata
Guppy,
Poecllla retlculata
Green sun fish.
Lepomls cyanel lus
BlueglH,
Lepomls macrochlrus
Blueglll,
Lepomls macrochlrus
Blueglll.
Lepomls macrochlrus
Largemouth bass.
Mlcropterus salmoldes
Largemouth bass.
Mlcropterus salmoldes
Chemical
m4ci
NH4C|
Excreted by
fish
NH.CI
*•
NH4CI
NH4C|
NH4CI
NH4CI
NH4CI
NH4OH
—
_
pH
8.0
9.0
-
7.8
7.0
8.0
7.82-
8.56
7.72-
8.00
7.9
6.9-
7.5
7.0
7.0
CC)
21-
25
21-
25
-
21.8
25
25
23.3-
27,3
21.9-
22.1
22
20
22
22
Concentration
Duration Effect
24 h LC50
24 h LC50
7 mo Hlstopath-
ologlcal
gl 1 1 lesions
In pond
cultures
17 h LC50
24 h LC50
24 h LC50
31 d Larval
mortality
48 h LC50
96 h LC50
48 h LC50
24 h Opercular
rhythm
frequency
1 ncrease
5 d Threshold
value
(Increase In
activity)
(•0/L NHx)
2.21b
1.81b
0.020-
0.067
1.3
0.8a
1.4°
0.80
2.30
Reference
Tomasso et al. 1980
Tomasso et al. 1980
Soderberg et al.
Hemens 1966
Tabata 1962
Tabata 1962
Relnbold & Pescltel
1982a
Sparks 1975
1984
II
8.1a»f Do-den & Bennett 1965
0.024-
0.093*
0.028
0.0055"
Turnout 1 et a|. 1954
Morgan 1976, 1977
Morgan 1978, 1979
151
-------
TabU 3. (Continued)
Specie*
Largemouth bass.
Mlcropterus salmoldes
Oscar,
Astronotus ocellatus
Oscar,
Astronotus ocellatus
Blue tllapla.
Tllapla aurea
Newertine worm,
Cerebratulus fuscus
Mussel,
Mytllus edulls
Mussel,
Mytllus edulls
Mussel,
Mytllus edulls
Copepod.
Eucalanus elongatus
Copepod,
Eucalanus plleatus
Prawn,
Penaeus setlferus
Chemical
Temperature
OH ro
7.0 22
Duration
5 d
8.4 25.5 9-24 h
-
NH4C|
W4N03
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
8.5 25.5
7.3- 25
7.4
SALTWATER
7.9 15
7.5 18
7.5 18
7.5 18
8.1 20
8.2 20
28
13 d
72 h
SPECIES
106 mln
<\ h
£1 h
.66
X).65
0.72b»a
Morgan 1978. 1979
Magalhaes Bastos
Magalhaes Bastos
195'
195'
Redner I Stlckney 19
Brown 19 749
Anderson et al.
Anderson et al.
Anderson et al.
Venkataramlak et
VenkataramiaX et
Wlcklns 1976
1978
1978
1978
al.
al.
152
-------
Table 5. (Continued)
Specie*
Prawn,
Macrobrachlum rosenbergll
Prawn,
Macrobrachlum rosenbergll
Prawn,
Macrobrachlum rosenbargll
Prawn,
MacrobrachIurn rosenbergll
Prawn,
Macrobrachluro rosenbergll
Prawn,
MacrobrachIum rosenbargll
Prawn,
MacrobrachI urn rosenberg11
Prawn,
Macrobrachlum rosenbergll
Prawn,
HacrobrachIum rosenbergll
Prawn,
Macrobrachlum rosenbergll
Prawn,
MacrobrachIurn rosenberg11
Prawn,
HacrobrachIum rosenbergll
Grass shrimp,
Palaeroonetes puglo
Chemical
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH4C|
NH.Cl
NH4C|
NH4Cl
NH4CI
NH4C|
NH4C|
Temperature
£"
7.0
7.0
7.0
«.
6.83
6.83
7.60
7.60
8.34
8.34
6.83
7.60
8.0-
8.2
1C)
29.2
29.2
29.2
28
28
28
28
28
28
28
28
28
20
Duration
1700
mln.
1400
mln.
560
mln.
6 wk
24 h
144 h
24 h
144 h
24 h
144 d
7 d
7 d
48 h
Effect
LT50
LT50
LT50
30-40*
Growth
reduction
LC50
LC50
LC50
LC50
LC50
LC50
Reduction In
growth rate
Reduction In
growth rate
LC50
Concentration
(mg/L NHyL
l.7b
2.7b
3.4b
O.I2b
0.66
0.26
2.10
0.80
3.58
1.35
0.11
0.63
0.34-
0.53C
Reference
Wlcklns 1976
Wlcklns 1976
Wlcklns 1976
Wlcklns 1976
Armstrong et
Armstrong et
Armstrong et
Armstrong et
Armstrong et
Armstrong et
Armstrong et
Armstrong et
Hal 1 et at. 1
153
-------
Table 9. (ContUuMl)
So«cle*
Lobster,
Homarus amerlcanus
Coho salmon,
Oncorhynchus klsutch
Atlantic salmon.
Sal mo solar
Chemical
NH4C|
NH4CI
NH4C|
-2"
a.i
7.46-
7.90
Temperature
CC)
21.9
15.5-
16
11.9-
13.8
Duration
a d
48 h
24 h
Effect
LC50
LC50
LC50
Coftcentratlo*
-------
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