United States Office of Water EPA-822-D-09-001
Environmental Protection 4304T December 2009
Agency
vvEPA
DRAFT 2009 UPDATE
AQUATIC LIFE AMBIENT WATER
QUALITY CRITERIA FOR
AMMONIA - FRESHWATER
Supersedes 1999 Update
-------
11
-------
EPA-822-D-09-001
Draft 2009 Update Aquatic Life
Ambient Water Quality Criteria For
Ammonia - Freshwater
December 2009
Supersedes 1999 Update
U.S. Environmental Protection Agency
Office of Water
Office of Science and Technology
Washington, DC
in
-------
NOTICES
This update provides guidance to States and Tribes authorized to establish water quality
standards under the Clean Water Act (CWA), to protect aquatic life from acute and chronic
effects of ammonia. Under the CWA, States and Tribes are to establish water quality criteria to
protect designated uses. State and tribal decision makers retain the discretion to adopt approaches
on a case-by-case basis that differ from this guidance when appropriate. While this update
constitutes EPA's scientific recommendations regarding ambient concentrations of ammonia that
protect freshwater aquatic life, this update does not substitute for the CWA or EPA's regulations;
nor is it a regulation itself. Thus, it cannot impose legally binding requirements on EPA, States,
Tribes, or the regulated community, and might not apply to a particular situation based upon the
circumstances. EPA may change this guidance in the future. This document has been approved
for publication by the Office of Science and Technology, Office of Water, U.S. Environmental
Protection Agency. Mention of trade names or commercial products does not constitute
endorsement or recommendation for use.
ACKNOWLEDGMENT
This update is a modification of the 1999 Update of Ambient Water Quality Criteria for
Ammonia. The 2009 modifications were prepared by Lisa Huff (EPA Work Assignment
Manager), Charles Delos, and Charles Stephan with the majority of written and technical support
provided by EPA Contractors: Tyler Linton, Christopher Tarr and Keith Taulbee of Great Lakes
Environmental Center, Inc. Portions of the 1999 Update carried into the 2009 Update, were
written by Russell Erickson, Charles Stephan, and Charles Delos. EPA received substantial input
from James (Russ) Hockett of the EPA's NHEERL Mid-Continent Ecology Division, Duluth,
MN.; and Cindy Roberts, EPA Headquarters. Please submit comments or questions to: Lisa
Huff, U.S. EPA, Mail Code 4304, Washington, DC 20460 (e-mail: huff.lisa@epa.gov).
IV
-------
EXECUTIVE SUMMARY
Following the directives established under the Clean Water Act (CWA) to periodically review
and revise 304(a) Ambient Water Quality Criteria (AWQC) as necessary to ensure the criteria
are adequately protective based on the latest science, EPA reviewed and updated the freshwater
ammonia aquatic life AWQC. The process of updating the freshwater ammonia criteria was
initiated to include all new acute and chronic data published since the criteria document in
1984/1985, including any new toxicity data published for several freshwater mussel species in
the family Unionidae. Based upon the literature, it appears that many states in the continental
USA have freshwater mussel fauna in at least some of their waters (Abell et al. 2000, Williams et
al. 1993, Williams and Neves 1995). Moreover, approximately one-quarter of freshwater
unionid mussel species and subspecies in the United States are Federally-listed as endangered,
threatened or are of special concern. While declining mussel populations may be due to many
factors, the newly published ecotoxicological data indicate that freshwater mussels are more
sensitive to ammonia when compared to other freshwater aquatic organisms. Given the wide
distribution of freshwater mussels, including unionid mussels, it is important that this criteria
update consider ammonia toxicity information specific to freshwater mussels. Because ammonia
is particularly toxic to freshwater unionids, EPA updated the numeric freshwater acute and
chronic aquatic life criteria for ammonia to ensure they are protective of unionids.
Several literature searches dating back to 1985 were conducted to locate results of laboratory
toxicity tests compiled that quantify the adverse effects of ammonia on freshwater aquatic life,
with particular attention given to tests conducted with freshwater mussels and snails since such
data were not available for many of these species at that time. Acceptable values for these and
other test species were used to re-calculate the freshwater ammonia acute and chronic aquatic life
criteria.
Acute and chronic toxicity data acceptable for criteria derivation were identified and selected
following EPA's "Guidelines for Deriving Numerical National Water Quality Criteria for the
Protection of Aquatic Organisms and Their Uses" (Stephan et al. 1985). During the evaluation of
the new toxicity data, including new data on other threatened and endangered species, EPA
-------
identified several technical issues about the interpretation and use of toxicity data for studies
with glochidia of freshwater mussels, juvenile mussels, and with the freshwater amphipod
species, Hyalella azteca. In this document, EPA presents its scientific analysis, approach, and
rationale for addressing these issues. The rationale on the technical issues and the draft criteria
document were externally peer reviewed and the final draft reflects consideration of those
reviewer's comments.
The criteria contained herein account for the influence of pH and temperature on toxicity, the
greater sensitivity of freshwater invertebrates (particularly freshwater mussels) to acute and
chronic ammonia toxicity, and the greater sensitivity offish early life stages than juvenile and
adult stages to chronic toxicity of ammonia. The pH and temperature relationships used to
account for the influence of these two abiotic factors on ammonia toxicity were the same as those
established in the 1999 AWQC document.
This ammonia criteria update document recommends an acute criterion of 2.9 or 5.0 mg N/L (at
pH 8 and 25°C) depending on whether freshwater mussels are present or absent, and a chronic
criterion of either 0.26 or 1.8 mg N/L depending on the same (at pH 8 and 25°C and whether
freshwater mussels present or absent). For this document, the use of the EC20 for deriving the
CCC was retained as in the 1999 document. Additionally, the 30 day averaging period was
retained with the restriction that the highest 4-day average within the 30 days is no greater than
2.5 times the CCC (or 0.65 or 4.5 mg N/L freshwater mussels present or absent, respectively).
VI
-------
TABLE OF CONTENTS
NOTICES iv
ACKNOWLEDGMENT iv
EXECUTIVE SUMMARY v
INTRODUCTION 1
BACKGROUND INFORMATION ON AMMONIA 4
DATA COLLECTION 5
RESULTS 6
Criterion Maximum Concentration (CMC) 6
Justification for Exclusion ofHyalella azteca Data from Acute and Chronic Ammonia
Criteria Development 10
Criterion Continuous Concentration (CCC) 14
Review and Analysis of Chronic Data 14
Calculation of Chronic Values 15
Evaluation of the Chronic Data Available for Each New Species 17
Other Chronic Toxicity Data 21
Update of the CCC 29
Temperature and pH-Dependent Criteria Calculation 33
Temperature Extrapolation of Acute Toxicity 34
Temperature Extrapolation of Chronic Toxicity 35
THE NATIONAL CRITERIA FOR AMMONIA IN FRESH WATER 37
UNUSED DATA 47
REFERENCES 48
LIST OF TABLES
A. Comparison of the four taxa used to calculate the FAV and CMC between this update of the
acute criterion and the current (1999) acute criterion 8
B. Comparison of the four taxa used to calculate the FAV and CMC in this update with and
without freshwater bivalve data from the Family Unionidae 9
C. Comparison of the four taxa used to calculate the CCC in this update with and without
freshwater bivalve data from the Family Unionidae 31
1. Acute Toxicityof Ammonia to Aquatic Invertebrates and Vertebrates 63
2. Other Acute Ammonia Toxicity for Glochidia Life Stage of Freshwater Mussels 107
3. Ranked Genus Mean Acute Values - Freshwater Mussels Present 109
4. Other Acute Ammonia Toxicity for Hyalella azteca 114
5. Chronic Toxicity of Ammonia to Aquatic Animals 115
6. Other Chronic Ammonia Toxicity Data 118
7. Genus Mean Acute-Chronic Ratios 121
8. Ordered Genus Mean Acute-Chronic Ratios 123
9. Unused Acute Studies Potentially Influential for Freshwater Ammonia Criteria Development.
125
vn
-------
10. Unused Chronic Studies Potentially Influential for Freshwater Ammonia Criteria
Development 131
LIST OF FIGURES
1. Ranked Freshwater Genus Mean Acute Values (GMAVs) with Criterion Maximum
Concentrations (CMCs) 60
2. Ranked Freshwater Genus Mean Chronic Values (GMCVs) with Criterion Continuous
Concentrations (CCCs) 61
3. CMC Extrapolated Across a Temperature Gradient at pH=8 62
4. CCC Extrapolated Across a Temperature Gradient at pH=8 62
LIST OF APPENDICES
A EPA Final Draft Position Statement on: Acute Toxicity Tests using Freshwater Mussels.. 137
B EPA Final Draft Position Statement on: Toxicity Tests on Ammonia using Hyalella azteca
142
C EPA Final Draft Position Statement on: 28-day Toxicity Tests using Juvenile Freshwater
Mussels 149
D Conversion of Acute Results of Toxicity Tests 152
E Conversion of Chronic Results of Toxicity Tests 154
F Results of Regression Analyses of New Chronic Data 156
G Unused (Non-influential) Acute and Chronic Studies for Freshwater Ammonia Criteria
Development - Screened Out Studies with Code List 163
Vlll
-------
INTRODUCTION
National Ambient Water Quality Criteria (AWQC) are established by the United States
Environmental Protection Agency (EPA) following directives set forth in the Clean Water Act
(CWA). Periodically EPA will review and revise 304(a) AWQC as necessary to ensure the
criteria are adequately protective based on the latest science. The section 304(a) aquatic life
criteria serve as recommendations to states and tribes in defining water column concentrations
that should protect against adverse ecological effects to aquatic life resulting from exposure to a
single pollutant found in the water column from direct contact or ingestion. Aquatic life criteria
address the Clean Water Act 101(a)(2) & (3) goals and policy of attaining "water quality which
provides for the protection and propagation offish, shellfish, and wildlife," and are the basis for
deriving permit limits, which prevent the discharge of toxic pollutants in toxic amounts.
EPA published a Federal Register Notice in July 2004 notifying the public of EPA's intent to re-
evaluate the ammonia aquatic life AWQC. At that time, EPA requested all new information
particularly related to ammonia toxicity to freshwater mussel species. Based upon the literature,
it appears that many states in the continental USA have freshwater mussel fauna in at least some
of their waters (Abell et al. 2000, Williams et al. 1993, Williams and Neves 1995). Moreover,
approximately one-quarter of freshwater unionid mussel species and subspecies in the United
States are Federally-listed as endangered, threatened or are of special concern. While the
number of species is less and the distribution is sparse in the dry western states, even New
Mexico and Arizona have at least one native mussel species (Williams et al 1993). Given the
wide distribution of freshwater mussels, including unionid mussels, it is important that this
criteria update consider ammonia toxicity information specific to freshwater mussels. Because
ammonia is particularly toxic to freshwater unionids, EPA is re-assessing the numeric freshwater
acute and chronic aquatic life criteria for ammonia to ensure they are protective of unionids.
Several literature searches dating back to 1985 have been conducted to locate results of
laboratory toxicity tests compiled that quantify the adverse effects of ammonia on freshwater
aquatic life, with particular attention given to tests conducted with freshwater mussels since such
data were not available for many of these species at that time. Acceptable values for these and
1
-------
other test species were used in reviewing the 1999 freshwater ammonia acute and chronic aquatic
life criteria (U.S. EPA 1999) and developing the recommended acute and chronic values
presented in this notice .
EPA's national numeric aquatic life criteria recommendations are calculated to protect aquatic
organisms from unacceptable toxicity during acute (short) and chronic (long) exposures in the
water column of a water body. EPA's acute criterion recommendation is called the Criterion
Maximum Concentration (CMC). The CMC is derived from a set of LCSOs or ECSOs for a
variety of aquatic species. An LC50 represents the lethal concentration of a chemical that causes
50% mortality. An EC50 represents the 50% effect concentration when organisms are killed or
effectively dead (e.g., immobilized). To provide aquatic organisms a reasonable level of
protection, the CMC is set to one-half of the fifth percentile of the Genus Mean Acute Values
(GMAVs) for the various species tested. To make exceeding this level of toxicity a rare event,
EPA's "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, recommends that the one-hour average exposure concentrations should not exceed
the CMC more than once every three years. Following this guidance, a new CMC for ammonia
was calculated.
EPA's chronic criterion recommendation is called the Criterion Continuous Concentration
(CCC). Under the Agency's 1985 Guidelines, the CCC is normally derived from a set of chronic
values (CVs), which have been defined as the geometric mean of the highest no observed effect
concentrations (NOECs) and lowest observed effect concentrations (LOECs) for survival,
growth, or reproduction in chronic tests. However, in the case of the Criterion Continuous
Concentration for the Agency's 1999 ammonia recommended ammonia criteria, this procedure
resulted in significant variation between the magnitudes of the effects corresponding to the
individual CVs due to variation in the power of the statistical tests used, the selected dilution
series and number of concentrations tested, and the size and variability of the samples used to
calculate the no and low effect thresholds (Stephan and Rogers 1985). To make CVs reflect a
more uniform level of effect, logistic regression analysis was used to calculate the 20 percent
effect concentration (EC20) for each chronic test to derive the 1999 freshwater CCC for
-------
ammonia (U.S. EPA 1999). Then by direct calculation, the CCC was set to an estimated fifth
percentile of CVs. In order to make exceeding the level of toxicity associated with the CCC a
rare event, EPA's Technical Support Document (U.S. EPA 1991) recommends that four-day
average exposure concentrations should not exceed the CCC more frequently than once every
three years. For the 1999 ammonia criteria, however, this recommendation was extended such
that the 30-day average exposure concentration should not exceed the CCC more frequently than
once every three years based on duration of exposure needed to elicit chronic effects. The use of
the EC20 (or an equivalent 20 percent inhibition concentration or IC20) for deriving the CCC
has been maintained in this update of the 1999 AWQC freshwater CCC, as appropriate, as has
the 30 day averaging period with the restriction that the highest 4-day average within the 30 days
is no greater than 2.5 times the CCC (see U.S. EPA 1999, page 81).
The 1999 criteria are expressed on the basis of total ammonia nitrogen (TAN) as a function of
pH (fish) or pH and temperature (invertebrates) (see U.S. EPA 1999 for specific calculations). In
the 1999 freshwater AWQC document, the CMC differs based on the presence or absence of
salmonids, and the CCC differs based on the presence or absence offish early life stages.
-------
BACKGROUND INFORMATION ON AMMONIA
Ammonia is considered one of the most important pollutants in the aquatic environment not only
because of its highly toxic nature and ubiquity in surface water systems (Russo 1985), but also
because many effluents have to be treated extensively in order to keep the concentrations of
ammonia in surface waters from being unacceptably high. Ammonia can enter the aquatic
environment via direct means such as municipal effluent discharges, and indirect means such as
nitrogen fixation and the excretion of nitrogenous wastes from animals. While much of the early
information regarding lethal concentrations of ammonia was driven by the consequences of
ammonia buildup in aquaculture systems (i.e., fish culture ponds, hatchery raceways, and fish
holding and transporting tanks), the introduction of large amounts of ammonia into surface water
systems from industrial processes, agricultural run-off, and sewage effluents has also received
considerable attention since the 1980s (Alabaster and Lloyd 1980, U.S. EPA 1985).
The chemical form of ammonia in water consists of two species, the more abundant of which is
the ammonium ion (NH4+) and the less abundant of which is the non-dissociated or un-ionized
ammonia (NHs) molecule; the ratio of these species in a given aqueous solution is dependent
upon both pH and temperature (Emerson et al. 1975, Erickson 1985, Thurston 1988, Wood
1993). In general, the ratio of un-ionized ammonia to ammonium ion in fresh water increases by
10-fold for each rise of a single pH unit, and by approximately 2-fold for each 10°C rise in
temperature from 0-30°C (Erickson 1985).
Chemically, ammonia in an aqueous medium behaves as a moderately strong base with pK
values ranging from approximately 9 to slightly above 10 as a function of temperature and ionic
strength (Emerson et al. 1975, Whitfield 1974). The total ammonia in solution will consist of the
gas NH3 and the cation NH4+, the sum of which is most commonly expressed as total ammonia-
nitrogen (TAN) (Thurston et al. 1984a). Each separate fraction of TAN can be calculated in
freshwater (note: this relationship changes with salinity, see Hampson 1977 and Whitfield 1974)
from the Henderson-Hasselbach equation if the pH and appropriate pK are known:
-------
NH4+ = Total ammonia/(l+ antilog (pH-pK)) = Total ammonia - NH3 (Wood 1993)
and,
pK = 0.09018 + (2729.927(273.2 + T)) (Emerson et al. 1975)
where T is temperature in °C. In keeping with the recommendations made in the 1999 AWQC
document, the concentrations of ammonia affecting freshwater animals in this criteria update are
expressed on thi
(invertebrates).
expressed on the basis of TAN (mg N/L), and normalized to pH=8 (fishes) or to pH=8 and 25°C
DATA COLLECTION
The acute and chronic ammonia toxicity data used here to update the 1999 AWQC acute and
chronic criteria were collected from a literature search of EPA's ECOTOX database, EPA's
Ambient Aquatic Life Water Quality Criteria for Ammonia (U.S. EPA 1985, 1998, 1999), data
provided by the U.S. Fish and Wildlife Service and the National Marine Fisheries Service
(collectively known as the Services), and EPA regional and field offices. Relevant papers were
identified, by title and abstract, and their data selected according to recommendations described
in the Guidelines. The primary focus of this update was on tests with freshwater mussels (and
secondarily snails); however, acute and chronic toxicity values published since 19851 for other
aquatic animals were incorporated into the appropriate ammonia AWQC tables and used to
recalculate the CMC and the CCC, following the methods briefly described above and outlined
in complete detail in the Guidelines. The most recent literature search was conducted in February
2009.
1 Note: Although the freshwater criteria for ammonia were updated in 1999, the 1999 Update presented an overview
of ammonia toxicology in order to provide the background needed to explain the revisions of the freshwater
ammonia criterion made in 1998. Then the equations used in the older documents to address the temperature- and
pH-dependence of ammonia toxicity in fresh water were revised to take into account newer data, better models, and
improved statistical methods. For both the 1998 and 1999 updates, the CMC (acute criterion) was derived from the
acute toxicity data in the 1984/1985 criteria document, pH-normalized using the new equations. Some new and old
chronic toxicity data were evaluated and used to derive a CCC (chronic criterion). In the 1999 Update, the chronic
averaging period was also addressed.
This 2009 Update differs from the preceding Updates in that this document incorporates a comprehensive literature
search while utilizing the same temperature- and pH-dependence equations to normalize and calculate the new
criteria for ammonia.
-------
RESULTS
All acceptable acute and chronic values for freshwater aquatic animal species, including those
from the 1999 AWQC document, are presented in Tables 1 (acute) and 5 (chronic). Because
data on the acute and chronic toxicity of ammonia to freshwater mussels have recently become
available, it is prudent to discuss these data and their inclusion in the AWQC calculations. There
are concerns that have been raised about the appropriateness of using data obtained from tests
conducted with the parasitic bivalve glochidia life-stage of freshwater mussels (for more detail,
see Appendix A). Since glochidia of different species have different life history strategies for
finding an appropriate fish host, glochidia may be free living in the water column (and
potentially exposed to pollutants) for a duration ranging from seconds to days, depending on the
particular species. In order for the toxicity test results with glochidia to be ecologically relevant,
the duration of the test must be comparable to the duration of the free-living proportion of the
glochidia on a species-by-species basis. For glochidia that become juveniles, there appears that
little or no useful information is available concerning the average duration of the free-living
portion of the glochidia life stage of any species of freshwater mussel. Therefore, as discussed in
more detail in Appendix A, results of acute toxicity tests with glochidia that lack this information
are not used in the derivation of water quality criteria for aquatic life. For this update, only
acceptable acute toxicity data from the juvenile life-stages of these species have been included;
these are provided in Table 1. Other acute toxicity data from the glochidia life stage, while
excluded from calculation of the acute criterion, are provided in Table 2 (acute data from several
unused tests/studies are also included in Table 9).
Criterion Maximum Concentration (CMC)
Data considered acceptable for inclusion in Table 1, according to the Guidelines, now includes
46 species offish, 48 species of invertebrates and 4 species of amphibians. There are now 67
genera represented in the freshwater acute toxicity dataset for ammonia, as opposed to only 34
genera in the 1999 AWQC document. Of the 67 genera represented in Table 1 and listed
according to sensitivity in Table 3, approximately half are invertebrates. Freshwater bivalve
mollusks and snails are the predominant group of genera ranked in the lowest quartile, and the
four most sensitive genera are all bivalves (see text Table A). Overall, invertebrates represent
-------
the eight most sensitive genera, and six of these are bivalves (see Table 3). This is in contrast to
the four lowest ranked GMAVs in the 1999 AWQC document where all taxa were fish (text
Table A). Note that in this update of the 1999 AWQC document, the SMAVs and GMAVs for
invertebrates were not only normalized to pH=8, but to a temperature of 25°C as well; this
temperature normalization accounts for some of the difference observed in GMAVs between the
two documents. The GMAVs ranked according to sensitivity, the 1999 AWQC CMC values,
and the CMC values re-calculated in this update of the acute criterion for ammonia in freshwater
are shown in Figure 1. The GMAVs represent LCSOs or ECSOs, whereas the CMC values
represent concentrations that are lethal to a minimal percentage of the individuals in either the
fifth percentile genus or a sensitive commercially or recreationally important species.
-------
Table A. Comparison of the four taxa used to calculate the FAV and CMC between this
update of the acute criterion and the current (1999) acute criterion2.
Update of the Acute Criterion
SPECIES 2
Oyster mussel,
Epioblasma capsaeformis
Asiatic clam,
Corbicula fluminea
Lampsilis sp.(Unionidae),
includes:
L. abrupta, L. cardium, L.
fasciola, L. higginsii, L.
rafinesqueana, and L.
siliquoidea
Rainbow mussel,
Villosa iris
FAV
CMC
GMAV
(mgN/L)
6.037
6.018
5.919
5.036
5.734
2.9
Current (1999) Acute Criterion
SPECIES 2
Oncorhynchus sp. (salmonids),
includes:
O. aquabonita, O. clarki,
O. gorbuscha, O. kisutch,
O. mykiss, and O. tshawytscha
Orangethroat darter,
Etheostoma spectabile
Golden shiner,
Notemigonus crysoleucas
Mountain whitefish,
Prosopium williamsoni
FAV3
CMC
GMAV
(mgN/L)
21.95
17.96
14.67
12.09
11.23
5.6
As previously mentioned, freshwater mussels are among some of the most sensitive genera in the
dataset, and therefore, significantly influence the FAV calculation. Since freshwater mussels
may not be present in all waters, we are recommending two acute criteria, one to be applied, as
appropriate, to waters where mussels are present and another criterion to be applied where
mussels are absent. With the freshwater mussel data removed from the dataset for the mussels
Note, as per the Guidelines, whenever there are 59 or greater GMAVs in the acute criteria dataset, the FAV is
calculated using the four GMAVs which have cumulative probabilities closest to 0.05. For example, in this 2009
draft update, the four GMAVs shown above with cumulative probabilities closest to 0.05 are sensivity rank 2-5, the
most sensitive species Lasmigon subviridus is not included. If there are less than 59 GMAVs, the four lowest
GMAVs are used to calculate the FAV regardless of cumulative probabilities.
3 The FAV in the 1999 AWQC document was lowered to 11.23 mg N/L in order to protect large rainbow trout
which were shown in Thurston and Russo (1983) to be measurably more sensitive than other life stages. The FAV
prior to adjusting it to protect the commercially and recreationally important adult rainbow trout was calculated to be
14.32 mg N/L (CMC = 7.2 mg N/L).
-------
absent criteria derivation, three of the five most sensitive genera are invertebrates (snails and
Asiatic clam) in the Phylum Mollusca (see text Table B).
Table B. Comparison of the four taxa used to calculate the FAV and CMC in this update
with and without freshwater bivalve data from the Family Unionidae.
Including All Data
SPECIES 2
Oyster mussel,
Epioblasma capsaeformis
Asiatic clam,
Corbicula fluminea
Lampsilis sp. (Unionidae),
includes:
L. abrupta, L. L. cardium, L.
fasciola, L. higginsii, L.
rajinesqueana, and L.
siliquoidea
Rainbow mussel,
Villosa iris
FAV
CMC
GMAV
(mgN/L)
6.037
6.018
5.919
5.035
5.734
2.9
Excluding Freshwater Mussel Data
SPECIES 2
Lost River sucker
Deltistes luxatus
Mountain whitefish,
Pros opium williamsoni
Snail (adult),
Pleurocera uncial
Snail,
Potamopyrgus antipodarum
FAV
CMC
GMAV
(mgN/L)
13.18
12.09
10.54
7.605
9.935
5.0
-------
Justification for Exclusion ofHyalella azteca Data from Acute and Chronic Ammonia Criteria
Development
For this update of the 1999 freshwater ammonia AWQC, the SMAV and SMCV for//, azteca
were not used to calculate the CMC or CCC. For a full description of EPA's rationale for this
decision, see Appendix B. Briefly, data were not included because several laboratories have
recently reported regular or intermittent difficulty obtaining consistent results and acceptable
survival and growth of//, azteca during testing and culturing. At this time, the water quality
conditions that promote optimal health are not known. However, laboratory evidence suggests
that chloride (and possibly bromide) is an important water quality parameter for improving //.
azteca health. The importance of chloride to H. azteca health has been suggested by the results
of the following studies:
a. Smith et al. (1997) reformulated moderately hard water with 34 mg Cl/L and saw
improved H. azteca control survival of >80% during 96-hr tests. Survival during prior
tests, which used moderately hard water with 2 mg/L chloride, was never >70%.
b. Soucek (2007) demonstrated that increasing chloride from 5 to 25 mg/L in acute toxicity
tests of//, azteca exposed to sulfate significantly increased the LC50 value (decreased
acute toxicity).
c. Borgmann (1996) raised the water concentration of chloride for H. azteca laboratory
cultures from 0 to 21.3 mg Cl/L and observed a large improvement in organism survival.
From these and other observations, it appears that H. azteca are healthier when the range of
chloride concentration is between 25 and 100 mg Cl/L.
The uncertain health status of//, azteca used in the laboratory-based toxicity tests with ammonia
may be an important contributing factor in the extreme variability of LCSOs (between 1.70 and
83.9 mg N/L) observed for this species (see Table 4). Seven studies report results of ammonia
toxicity to H. azteca. The following paragraphs provide a brief summary of those studies and the
test conditions reported in each.
10
-------
Sarda (1994) reported conducting 96 h tests with H. azteca, but only presents survival data after
48 h. The tests were assumed to be static as no information was provided to indicate otherwise.
The test material was ammonium chloride. During testing, the author states pH was altered, but
no details were provided describing how pH was altered, and no results were provided for H.
azteca at the various levels of pH. Temperature was measured daily, whereas pH was measured
at the beginning and end of the tests. Total ammonia was measured using an electrode, but no
information was provided on when the measurements were made. Tests were performed in two
waters (a reconstituted water and creek water) that differed with respect to pH and hardness.
Hardness, alkalinity, and pH changed substantially during the tests. Although control survival
was acceptable, the concentration of chloride in the creek water is not known. One of the
ingredients of the reconstituted water was mineral water. According to the company that
produces the mineral water, the concentration of chloride in the water was likely 26 mg Cl/L, but
because the test material was ammonium chloride, the concentration of chloride differed between
treatments. The results of these tests were not considered for use in the derivation of aquatic life
criteria because, among other things, hardness, alkalinity, and pH changed substantially during
the tests and the concentration of chloride changed from one treatment to another.
Borgmann (1994) performed a variety of toxicity tests, two of which were 10-week water-only
life-cycle tests in which the test solutions were renewed weekly. Ammonia was measured at the
beginning and end of each renewal. The measured concentrations were close to nominal and the
ratio of final to initial measured ammonia concentration averaged 1.09. The pH of the test
solutions was measured three times per week. Ten-week control survival averaged 66.3 percent.
The test material was ammonium chloride and the dilution water was dechlorinated tap water
that contained 26 mg Cl/L. On the basis of the nominal concentrations of total ammonia,
increased chloride concentration due to the added ammonium chloride at the lowest tested
concentration of ammonia was 3.5 mg Cl/L, whereas the increase at the highest tested
concentration of ammonia was 64 mg Cl/L. Thus the concentration of chloride in the treatments
ranged from about 30 mg Cl/L to about 90 mg Cl/L.
Ankley et al. (1995) performed 96-hr water-only toxicity tests in which the test solutions were
renewed daily. The test organisms were cultured in hardened, unaltered Lake Superior water,
11
-------
and tests were performed at three levels of pH in each of three waters (soft water = Lake
Superior water; moderately-hard water = hardened Lake Superior water; ASTM hard water =
salts added to Millipore water4). The test material was ammonium chloride and hydrochloric
acid was used to acidify some test solutions. The chloride concentration of Lake Superior water
has been reported as 1.2 and 1.4 mg/L by Biesinger and Christensen (1972) and Tiffany et al.
(1969), respectively. The concentration of chloride in the hardened Lake Superior water was
about 19 mg/L, based on information provided for culturing H. azteca at the USEPA Laboratory
in Duluth, Minnesota. The concentration of chloride in the ASTM hard water used in these tests
was probably near 4 mg Cl/L. The increase in the concentration of chloride due to acidification
is not known. On the basis of the nominal concentrations of total ammonia, the increase in
chloride at the lowest and highest reported LCSOs was 44 mg Cl/L and 516 mg Cl/L, but the
range within any one test would not be nearly this large.
Whiteman et al. (1996) compared the toxicity of ammonia in a spiked-sediment exposure versus
a water-only exposure. The water-only toxicity test was a flow-through 96-hr test and the test
material was ammonium chloride. The dilution water was dechlorinated tap water from
Superior, WI, which was drawn from a well in a sandy area near Lake Superior. The
concentration of chloride in this water was probably less than 2 mg/L (see above). Ammonia,
temperature, and pH were measured sufficiently often. The increase in the concentration of
chloride due to the test material at the 96-hr LC50 was 23 mg Cl/L; thus the total chloride
concentration would be less than 25 Cl/L in treatments below the LC50, but greater than 25 mg
Cl/L in treatments above the LC50. The results of these tests were not considered for use in the
derivation of water quality criteria because of the low concentration of chloride in Lake Superior
water.
Borgmann and Borgmann (1997) performed water-only toxicity tests in which the test solutions
were renewed weekly. The test material was ammonium chloride, and hydrochloric acid was
per American Society for Testing and Materials. 2007. Standard guide for conducting acute toxicity
tests on test materials with fishes, macroinvertebrates, and amphibians. Standard E 729-96 in Vol. 11.06
of the Annual Book of ASTM Standards. American Society for Testing and Materials, West
Conshohocken, PA. 218 pp.
12
-------
used to acidify some solutions. The authors reported that both sodium and potassium affected
the toxicity of ammonia to H. azteca, and that the effect of pH on the toxicity of ammonia to H.
azteca depends on hardness and on the concentrations of sodium and potassium. On the basis of
some dilution tests, they concluded that calcium, magnesium and anions did not affect the
toxicity of ammonia, but they did not explicitly study the effect of a series of closely-spaced
concentrations of calcium, magnesium, or any anion on the toxicity of ammonia.
Besser et al. (1998) performed 96-hr static acute toxicity tests on two sediments spiked with a
solution prepared by adding ammonium chloride to a 50-50 mixture of well water and deionized
water. One sediment was from Little Dixie Lake and the other was a formulated sediment. The
concentrations of chloride and bromide in the dilution water were not reported; it is possible that
one or both of the sediments increased or decreased the concentrations of chloride and/or
bromide in the test solutions. The results of these tests were not considered for use in the
derivation of water quality criteria because the concentration of ammonia in the pore water was
not determined.
Wang et al. (2008) performed 48-h toxicity tests on ammonia at pH = 6.5, 7.5, 8.0, 8.5, and 9.0
using a combination of ammonium chloride and ammonium hydroxide. The pH of some
solutions was adjusted using hydrochloric acid. The dilution water was reconstituted hard water
that contained 7.9 mg Cl/L. At only two of the pH levels tested was the concentration of
ammonia sufficiently high to kill more than 20 percent of the H. azteca in any of the treatments.
In both of these tests, there was an unusual concentration response where percent survival was
higher at higher test concentrations. Moreover, the LCSOs and confidence limits at pH = 9.0 do
not agree with the data at elevated pH for H. azteca. These LCSOs should not be used in the
derivation of an aquatic life criterion for ammonia for the reasons given.
Data reported by Besser et al. (1998), Sarda (1994), and Wang (2008) concerning the sensitivity
ofH. azteca to ammonia were not considered for use in the derivation of an aquatic life criterion
for ammonia for the reasons specified. Data from the other publications are deemed
questionable because of concerns regarding:
• the importance of chloride (and possibly bromide and/or other ions) to H. azteca;
13
-------
• the possible effect of chloride and/or bromide on the toxicity of ammonia to H. azteca;
• the use of ammonium chloride as the test material;
• the use of hydrochloric acid to acidify some test solutions;
• the use of dilution waters that contained low concentrations of chloride in some of the
tests; and
• other aspects of the methodology used in some of the tests.
At this time it is not known how much of the wide range of ammonia LCSOs obtained with H.
azteca is due to water quality, the methodology used in some of the tests, and/or the health of the
organisms. It appears that some of the lowest acute values were obtained using dilution waters
that contained low concentrations of chloride.
Criterion Continuous Concentration (CCC)
Review and Analysis of Chronic Data
The freshwater final chronic value, or CCC, was updated using newly acquired chronic data for
three freshwater mussel species and three fish species (Table 5). Each chronic dataset was
reviewed following the three-step review process described in the 1999 AWQC document.
Briefly, the first step was to determine whether the test methodology was acceptable. A test was
considered acceptable if the dilution water, control mortality, experimental design, organism
loading, etc., were consistent with ASTM Standards for tests with fish and invertebrates, i.e.,
El 193, E1241, and E1295 (ASTM 2004, 2005, and 2006b, respectively), and specifically for
freshwater mussels via E2455-06 (ASTM 2006a). The concentration of dissolved oxygen was
also reviewed to determine acceptability based on the general limits specified in the 1999
AWQC document.
If the test methodology was acceptable, the second step of the review process was to determine
whether the test satisfied one of the definitions provided in the Guidelines for a life-cycle, partial
life-cycle, and early life-stage test. In general, if the test did not satisfy one of the definitions
given in the Guidelines for a life-cycle, partial life-cycle, or early life-stage test, a third step was
14
-------
necessary to determine whether the toxicant used in the test caused an unacceptable reduction in
(a) survival, reproduction, and/or hatchability over any period of at least seven days, or (b)
growth ( if the duration of the test is judged sufficiently long to capture growth reductions that
are not temporary - as determined on a species-specific basis). If it caused either kind of
unacceptable reduction, the test could provide an upper limit on a CV or it might lower a CV
from an early life-stage test. If it did not cause either kind of unacceptable reduction, the test
cannot provide a CV or an upper or lower limit on a CV, but the test might provide other useful
information.
Consistent with the rationale above, and in accordance with the Guidelines, 28-d survival and
growth tests using juvenile and adult freshwater snails and juvenile freshwater mussels do not
qualify as chronic toxicity tests for use in the derivation of aquatic life criteria (because the 28-d
survival and growth test using juvenile or adult animals is neither a life-cycle test nor a partial
life-cycle test, and early life-stage tests are used as predictors of life-cycle tests for fishes only5).
Nevertheless, a concentration that causes a reduction in survival of 20% or more can usually be
used as an upper limit on a Species Mean Chronic Value (SMCV). Reduction in growth cannot
be similarly used at this time because of uncertainties concerning these data6. Growth data from
28-day tests with juvenile and adult snails and mussels will be included in a criteria document as
"other data" (Table 6) and might influence a criterion by means of sections X and XII.B of the
Guidelines. For a full description of EPA's rationale for this decision, see Appendix C.
As indicated in the 1999 AWQC document, it was not necessary, nor appropriate, to consider
CVs based on histopathological effects as in the 1984/1985 ammonia criteria document.
Calculation of Chronic Values
To help achieve consistency among studies, regression analysis was used, both to demonstrate
that a concentration-effect relationship was present, and to estimate CVs with a consistent level
5 The basis for and use of early-life stage toxicity tests with fish as an acceptable surrogate for life-cycle tests with
fish was established by McKim (1977).
See Appendix C this document for more explanation and additional detail.
15
-------
of effect. Use of regression analysis is discussed on page 39 of the Guidelines (Stephan et al.
1985). Precise estimates of effect concentrations can generally be made for a 50 percent
reduction (EC50); however, such a major reduction is not necessarily consistent with chronic
criteria. In contrast, a concentration that caused a low level of reduction, such as an ECS or
EC 10, is rarely significantly different from the control treatment based on conventional statistical
analysis. As a suitable compromise, the EC20 (or equivalent IC20) values are used to estimate a
low level of effect observed in chronic datasets that are available for ammonia (U.S. EPA 1999).
With only a few exceptions (indicated in the text as such), regression analysis was performed on
a chronic dataset only if the dataset met the general conditions specified in the 1999 AWQC
document:
(1) it contained a control treatment to anchor the curve at the low end,
(2) it contained at least four concentrations of ammonia to provide at least two error degrees of
freedom when the three-parameter equation is fit to a set of data,
(3) the highest tested concentration of ammonia caused >50 percent reduction relative to the
control treatment to anchor the curve at the high end, and
(4) at least one tested concentration of ammonia caused <20 percent reduction relative to the
control treatment to ensure that the EC20 was bracketed by tested concentrations of ammonia.
For life-cycle and partial life-cycle tests, the toxicological variables used in these regression
analyses were survival, embryo production, and embryo hatchability. For early life-stage tests,
the variables used were embryo hatchability, fry/larval survival, and fry/larval growth; if
ammonia reduced both survival and growth, the product of these variables (biomass) was
analyzed (when possible), rather than analyzing them separately. For other acceptable chronic
tests, the toxicological variable analyzed was survival, reproduction, hatchability, and/or growth
as appropriate, based on the requirements stated above concerning acceptability of chronic tests.
When applicable, the regression analysis was performed using EPA's Toxicity Relationship
Analysis Program (TRAP, Version 1.00, 11/29/02) if possible, or via A Linear Interpolation
Method for Sublethal Toxicity: The Inhibition Concentration Approach (ICpin, Version 2.0,
06/03).
16
-------
Evaluation of the Chronic Data Available for Each New Species
The following presents a species-by-species discussion of each new freshwater chronic dataset
evaluated for this update of the 1999 AWQC for ammonia. Also presented are the results of
regression analysis of each dataset from an acceptable chronic test that met the data requirements
to perform such regression analysis. For each such dataset, Appendix F contains a figure of the
data and fitted regression line, a table with the regression parameters, and effect concentration
estimates (e.g., EC20 values). All analyses were conducted in terms of total ammonia nitrogen,
either as reported by the authors or as converted from the reported values for un-ionized
ammonia, pH, and temperature using the speciation relationship applied in the 1999 AWQC
document (i.e., Emerson et al. 1975). When an EC20 could be determined, it was first reported as
calculated by regression analysis of the data at the pH and temperature of the test. Then, to
facilitate comparisons of sensitivities within and between species, each EC20 was adjusted to
pH=8 using Equation 12 in the 1999 AWQC document, and for invertebrates, adjusted to a
temperature of 25°C using Equation 5 with a slope of-0.028, per the discussions of the
temperature and pH dependency sections in the 1999 AWQC document. SMCVs were derived
when justified by the data, and Genus Mean Chronic Values (GMCVs) were calculated when
justified by the SMCVs. All of the EC20 values, SMCVs, and GMCVs derived are tabulated
and included with the existing values from the 1999 AWQC document in Table 5. Note that for
some of the new chronic data for species presented below, authors reported EC20 values (or an
equivalent IC20 value) on the basis of total ammonia nitrogen. In such cases these reported CVs
were normalized to pH 8 and 25°C (temperature normalization for invertebrates only), as per the
1999 AWQC document, and utilized for the analysis.
Lampsilis fasciola (wavy-rayed lampmussel)
Wang et al. (2007a) recently published their results of the effect of ammonia on survival and
growth of 2-month old juvenile freshwater mussels whose length averaged 0.66 mm. The test
was part of a series of studies designed to refine the methods for conducting acute and chronic
toxicity tests with early life stages of freshwater mussels. Dissolved oxygen was maintained
above 7.0 mg/L during the 28-day test. Survival in the control treatment and lowest ammonia
17
-------
concentration (0.13 mg N/L) were 100 and 83%, respectively. Survival decreased to 30% at 1.02
mg N/L, and zero at 1.98 mg N/L. Shell length sampled as a measure of growth was no different
from controls up to the 0.44 mg N/L exposure. The reported IC25 values based on survival and
shell length were 0.39 and 0.57 mg N/L, respectively, at 20°C and pH=8.2. The corresponding
IC10 values were <0.13 and 0.48 mg N/L. The survival IC25 for this freshwater mussel species
is 0.38 mg N/L when adjusted to pH=8 and 25°C. The survival IC20 for this freshwater mussel
species, calculated using EPA's ICpin program, is 0.23 mg N/L when adjusted to pH=8 and
25°C. Using EPA's TRAP (piecewise linear regression model with full convergence), the
adjusted IC20 value is 0.39 mg N/L (see Appendix F).
Lampsilis siliquoidea (fatmucket)
As part of the same study summarized above, Wang et al. (2007a) also determined the effect of
ammonia on survival and growth of 2-month old juvenile fatmucket whose length averaged 0.62
mm. The 28 day test was conducted following the same methods (see ASTM 2006a). Survival in
the control treatment and lowest ammonia concentration (0.13 mg N/L) were 98 and 83%,
respectively. Survival decreased to 18% at 0.49 mgN/L, 45% at 1.00 mgN/L, and 13% at 1.99
mg N/L, respectively. Shell length sampled as a measure of growth was no different from
controls up to the 0.28 mg N/L exposure. The reported IC25 values based on survival and shell
length were 0.32 and 0.44 mg N/L, respectively, at 20°C and pH=8.2. The corresponding IC10
values were <0.13 and 0.32 mg N/L, while the survival IC25 for juvenile fatmucket is 0.31 mg
N/L when adjusted to pH=8 and 25°C. The survival IC20 for this freshwater mussel species,
calculated using EPA's ICpin program, is 0.30 mg N/L when adjusted to pH=8 and 25°C (Table
5). Note: Using EPA's TRAP the adjusted value is 0.17 mg N/L, but the piecewise linear
regression indicated a large standard error for steepness and for YO, and therefore, the adjusted
IC20 value of 0.30 mg N/L was retained for the test (results of TRAP analysis not included in
Appendix F).
18
-------
Villosa iris (rainbow mussel)
The effect of ammonia on survival and growth of a third freshwater mussel species was also
reported in the study by Wang et al. (2007a). Juvenile (2 month old) rainbow mussels whose
length averaged 0.90 mm were tested under similar conditions as described above. Survival was
> 98% up to the 0.81 mg N/L exposure, but fell to 15% at 1.67 mg N/L. In contrast, shell length
was reduced by approximately 13% at 0.40 mg N/L compared to controls, and by 28% when
exposed to 0.81 mg N/L. The reported IC25 values based on survival and shell length were 1.0
and 0.73 mg N/L, respectively, at 20°C and pH=8.2. The corresponding IC10 values were 0.89
and <0.40 mg N/L. The survival IC25 for this freshwater mussel species is <0.98 mg N/L when
adjusted to pH=8 and 25°C. The survival IC20 for this freshwater mussel species, calculated
using EPA's ICpin program, is also 0.98 mg N/L when adjusted to pH=8 and 25°C. Note:
EPA's TRAP could not be used to generate a corresponding EC20 value for this species based on
survival.
Considering the above, and with the exception of the rainbow mussel, juvenile mussel survival
was the more sensitive endpoint in the 28-day tests. The calculated EC20 value using TRAP for
L. fasciola and IC20 values using ICpin for L. siliquoidea and V. iris were deemed sufficiently
representative of the mussel's sensitivity to be included in Table 5. For all three freshwater
mussel species, and as per the text presented earlier in this document, the EC20 and IC20 values
presented in Table 5 are considered an upper limit CV for the species because the values are
based on survival of juveniles, which might not be as sensitive to ammonia toxicity as other
chronic test endpoints, such as reproduction. Thus, the SMCVs for all three freshwater mussel
species have been ascribed a less than sign. Note: Equivalent IC25 values based on growth for
the three mussel species are included in Table 6 (refer to Appendix C for further explanation
regarding this decision).
19
-------
Cyprinus carpio (common carp)
Mallet and Sims (1994) conducted a 28-day early life-stage test starting with eggs approximately
6 hours post-fertilization. The measured DO concentrations reported for the test ranged from 79
to 94% of saturation. Ammonia had no effect on hatching success at the highest concentration
tested (19.6 mg N/L); although survival of the post-hatch stages was significantly reduced at this
level compared to controls (average fry survival in the control treatment was 86%). Growth of
fry was the most sensitive endpoint, and mean fry wet weights were inhibited at concentrations
>10.4 mg N/L. Even though the number of larvae in each replicate vessel was not made uniform
on hatching, at least one vessel per concentration contained an equivalent stocking density (23 to
29 carp), so the mean wet weight of carp in the one selected replicate per concentration was
analyzed using regression analysis. The resulting EC20 value was 8.36 mg N/L at 23°C and
pH=7.85 (see Appendix F), which was calculated to be 6.82 mg N/L at pH=8.
Oncorhynchus clarki (cutthroat trout)
Table 6 in the 1999 AWQC document contains the value of <19.7 mg N/L for cutthroat trout
estimated from a 29-day lethality study with fish whose average weights were 3.3 and 3.4 g,
respectively (see Thurston et al. 1978). Because EC20 values could not be calculated and the
test was not conducted with an early life stage, the true SMCV is assumed lower than 19.7 mg
N/L. Thus, this value was not used in the calculation of a SMCV for the species (see U.S. EPA
1999).
Koch et al. (1980) exposed Lahontan cutthroat trout (Oncorhynchus clarki Henshawi) for 103
days in an early-life stage test. The measured dissolved oxygen concentrations for the entire
study ranged from 7.0 mg/L to 8.9 mg/L, with an overall average of 7.88 mg/L. Survival of
embryos in the control treatment was 80%, with approximately 95% surviving through the fry
stage, and 80% surviving as fingerlings up to day 94 of the test. There were no successful
hatches at exposure levels of 148 mg N/L or higher, and no significant mortality at exposure
levels below 32.9 mg N/L. Regression analysis of the survival data using an arcsine
20
-------
transformation resulted in a calculated EC20 value of 20.80 mg N/L at 13.7 °C and pH=7.57 (see
Appendix F). The EC20 value is 12.38 mg N/L when adjusted to pH=8.
As noted in the 1999 AWQC document, five other studies have reported results of chronic tests
conducted with ammonia and other salmonids including Oncorhynchus mykiss and
Oncorhynchus nerka. There is a lack of consistency among the chronic values obtained from
these tests, and several tests produced "greater than" and "less than" values (Table 5).
Consequently, in keeping with the decision made in the 1999 AWQC document, a GMCV is not
derived for Oncorhynchus. Instead, the results of the chronic tests were used to assess the
appropriateness of the CCC.
Esox lucius (northern pike)
Harrahy et al. (2004) conducted a 52-day early life-stage test starting with newly-fertilized
northern pike embryos. The mean dissolved oxygen concentration in test water ranged from 8.7
to 9.1 mg/L during the test. There was no effect of ammonia on hatching success up to 62.7 mg
N/L, and larval survival of control fish was 100%. A significant reduction in larval survival and
growth was observed at concentrations of total ammonia >30.4 and 15.1 mgN/L, respectively, at
pH=7.6 and 8.7°C. The estimated EC20 value reported for biomass was 13.44 mg N/L, which
was calculated by the authors to be 8.40 mg N/L at pH=8. Thus, the CV of 8.40 mg N/L reported
for biomass in the study was retained for northern pike in Table 5 of this document.
Other Chronic Toxicity Data
There were several other freshwater invertebrate and fish studies that were excluded from Table
5 and subsequent SMCV and GMCV calculation because the tests did not include the appropriate
life stage for the test, or did not meet other general Guidelines requirements for use in calculating
the CCC. These tests are summarized below and in Table 6.
21
-------
Invertebrates:
Besser et al. (2009), in a USGS study report recently completed for EPA7, conducted 28-day
flow-through survival and growth tests with five species of snails. All tests were conducted in
ASTM hard water (mean hardness and alkalinity of 169 and 121 mg/L as CaCOs, respectively)
as the dilution water which had a pH range of 8.20-8.29 and a temperature range of 19-21°C
during testing. Total ammonia (mg N/L) concentrations in tests were measured weekly with the
percent of nominal concentrations ranging from 83 to 101 (most test concentrations averaged >
90 percent of nominal except two concentrations in one of the tests - test designated as #5 in the
report). Test results were based upon the mean of the measured concentrations. For all snail
exposures, the effect of ammonia on growth was not determined for test species that were of
mixed ages at test initiation (as explained further below); growth, however, was not as sensitive
of an endpoint as survival for the two snail species where both growth and survival were
measured (see summaries of the Lymnaea stagnalis and Pyrgulopsis idahoensis tests below).
Normalized chronic values reported for the five snail species are provided in Table 6. A
summary of the Besser study results for each snail species is as follows:
Fluminicola sp. (Pebblesnail)
For the survival tests with Fluminicola sp., mixed-aged adult and young-adult organisms (from 6
to 12 months) were used because the acclimation cultures produced only approximately 200
neonates for testing that were collected over a period of about four months. Fluminicola sp. did
not show statistically significant mortality at any of the test concentrations compared to the
controls because of the extreme variation between replicates at the highest test concentrations.
Because of this extreme variability among treatment replicates, the NOEC and LOEC for
survival were reported as 7.9 mg N/L and >7.9 mg N/L, respectively. It is worth noting,
however, that snails in the control treatment exhibited 100% survival, while snails exposed to the
highest ammonia concentration (7.9 mg N/L) exhibited 0% survival, but because of the extreme
variability between replicate groups of snails in the 1.7 and 3.6 mg N/L treatments (all alive
7 Available via EPA Public Comment Docket #OW-2009-0921.
22
-------
versus all dead), the ANOVA for the test was not significant (p=0.339). The lack of a statistically
significant ANOVA for snail survival in the test precluded post hoc comparison of means
testing. Based on the reported mean survivals for Fluminicola sp., the reported EC20 for
Fluminicola sp. was estimated to be 1.02 mg N/L, or 1.19 mg N/L when adjusted to pH 8 and 25
°C (see Table 6). The EC20 calculated for the test is not considered reliable, however, due to the
extreme variability in survival among replicates in the 1.7 and 3.6 mg N/L test concentrations
(i.e., the all-or-none response in the replicates of these two treatments, which, when averaged
and analyzed as means instead of analyzing the replicates separately in the regression, allows
estimation of an EC20 that would otherwise be incalculable because of the extreme variability
between treatment replicates). Thus, the upper limit chronic value for the test is uncertain. The
value clearly is some concentration below 7.9 mg N/L, but exactly where that point lies cannot
be determined at this time.
Fontigens aldrichi (Ozark springsnail)
As part of the same study summarized above, Besser et al. (2009) also determined the effect of
ammonia on survival of F. aldrichi. Because F. aldrichi did not reproduce during culturing and
acclimation, field-collected organisms of "older" (adult) mixed-ages were used for ammonia
exposures. F. aldrichi exposed to ammonia in the 28-day test exhibited a NOEC based on
survival of 0.45 mg N/L and a LOEC of 0.83 mg N/L. Similar to the adult pebblesnail study, the
replicates associated with the LOEC (0.83 mg N/L) in this study were characterized by high
variability. In addition, field-collected F. aldrichi did not reproduce in captivity and animals in
the control group did not grow during testing. The reported EC20 for F. aldrichi survival was
0.61 mg N/L, or 0.71 mg N/L when adjusted to pH 8.0 and 25 °C (Table 6).
Lymnaea stagnalis (pulmonate pondsnail)
The effect of ammonia on survival and growth of a third freshwater snail species, L. stagnalis,
was also reported in Besser et al. (2009). L. stagnalis tests used organisms that were <1 week
post-hatch due to the abundance of young produced during culturing. L. stagnalis exposed to
ammonia in a 28-day flow-through chronic test exhibited a survival NOEC and LOEC of 8.0 and
23
-------
>8.0 mg N/L, and a growth NOEC and LOEC of 1.0 and 1.8 mg N/L (Note: an EC20 could not
be calculated using the growth endpoint because the magnitude of the growth reduction was so
small, i.e., 6% at 1.8 mg N/L and only 16% at 8 mg N/L). Because of the apparent negligible
effect of ammonia on growth, the EC20 value for both survival and growth were reported as >7.9
mg N/L, or >8.5 mg N/L when adjusted to pH 8 and 25 °C. Note: For the purposes of this
document, the EC20 based on survival for this test species is included in Table 6 because of the
uncertainty of this value (> 8.5 mg N/L) as an upper limit SMCV for the species.
Besser et al. (2009) also determined the effect of ammonia on survival and growth on two snail
species that were listed under the Endangered Species Act at the time of testing. One of these
snail species, P. idahoensis, has since been de-listed.
Pyrgulopsis idahoensis (Idaho springsnail)
Two separate 28-day tests with one of the two listed species at the time of testing, P. idahoensis,
included exposing juvenile organisms that were 7-9 and 11-13 weeks post-hatch (organisms in
each cohort tested as separate replicates in the same test; test identified as test #3 in the report),
as well as a cohort of mixed-age adults for all subsequent tests (test identified as test #5 in the
report). The older life stages were chosen for testing because of the high control mortality
demonstrated in preliminary tests using 2-3 week post-hatch P. idahoensis.
For P. idahoensis juveniles (both the 7-9 and 11-13 week post-hatch juveniles), the survival
NOEC and LOEC were 1.8 and 3.6 mg N/L respectively, while the EC20 for survival was <0.48
mg N/L, or <0.52 when adjusted to pH 8 and 25 °C. It is important to note that juvenile snails in
four of the test concentrations in this test exhibited <44.4 percent survival and were considered
significantly less than the control survival of 100 percent, except for those snails in the middle
tests concentration of 1.8 mg N/L, which demonstrated 62.5 percent survival and was not
considered significantly different from the control. Thus, the NOEC and LOEC values for
juvenile survival were viewed with skepticism due to the poor concentration-response
relationship, and therefore, are not included with the other chronic toxicity data found in Table 6.
24
-------
The NOEC, LOEC and EC20 for P. idahoemis growth was 8.0, >8.0 and >8.0 mg N/L
respectively. When adjusted to pH 8 and 25 °C, the EC20 value is >8.62 mg N/L (see Table 6).
The chronic tests initiated with mixed-aged adult P. idahoensis (4 to 8 months of age) exhibited
a survival NOEC, LOEC and EC20 of 3.6, 7.9 and 3.24 mg N/L, respectively. The EC20
adjusted to pH 8 and 25 °C is 3.77 mg N/L (Table 6). Comparison of the juvenile and adult P.
idahoensis survival results indicates that juveniles are possibly the more sensitive of the two life
stages; however, due to unreliability of the juvenile data, specifically the survival concentration-
response relationship, such an assertion is uncertain at this time.
Taylorconcha serpenticola (Bliss Rapids snail)
The second snail species listed under the Endangered Species Act, Taylorconcha serpenticola,
was exposed to ammonia by Besser et al. (2009) in 28-day flow-through chronic tests. Because
T. serpenticola did not reproduce or grow well during culturing and acclimation, field-collected
organisms of "older" (adult) mixed-ages were used. The EC20 for survival of T. serpenticola
was 3.42 mg N/L, or 3.98 mg N/L at pH 8.0 and 25 °C (Table 6). The reported EC20 (3.42 mg
N/L) was double the LOEC value of 1.7 mg N/L, where 15 percent mortality (or 85 percent
survival) was observed compared to the control survival of 100 percent. The next highest
concentration tested (3.6 mg N/L) exhibited 80 percent survival.
Fish:
Table 6 includes data for several fish species in addition to the other chronic invertebrate data
described above. The chronic results from these several studies are summarized in brief as
follows:
1. Sadler (1981) reported that the growth rate of juvenile European eel (Anguilla anguilla)
weighing approximately 2.8 g was inhibited after 77 days of exposure to a concentration of
15.2 mg N/L at 23°C and pH=7.53; when adjusted to pH=8, the LOEC value was 8.54 mg
N/L.
25
-------
2. In a 35-day study of the effects of sublethal ammonia on juvenile Nile tilapia (Oreochromis
niloticus; 6 g - a non-indigenous species located in the southern United States), the
concentration of total ammonia that resulted in an approximate 20% reduction in weight gain
was approximately 7 mg N/L at 28°C and pH=7.8 (Abdalla and McNabb 1999). At pH=8,
this results in a value of 5.41 mg N/L. No mortalities were observed in the control fish or
fish exposed to any of the ammonia concentrations tested up to 22.5 mg N/L.
3. Similarly, juvenile Nile tilapia weighing 20 g and exposed to total ammonia concentrations
of 5.3 mg N/L or greater experienced a reduction in specific growth rate over 75 days at
pH=7.45 (El-Shafai et al. 2004). The temperature during the exposure ranged from 26 to
34°C, and the measured dissolved oxygen concentration was 7.7 mg/L. The LOEC of 5.3 mg
N/L for the study corresponds to a value of 2.84 mg N/L at pH=8.
4. Beamish and Tandler (1990) exposed juvenile lake trout (Salvelinus namaycush) for 60 days
on two different diets and observed a significant reduction in rate of weight gain when total
ammonia was 6.44 mg N/L at pH 8.02 and temperature was 11.6°C. Food intake by fish was
initially decreased at this concentration of total ammonia, but was no different from controls
by the end of the test. The growth LOEC for the study, when adjusted to pH=8, was
calculated to be 6.63 mg N/L.
A final chronic study for a freshwater vertebrate worth mentioning here is Jofre and Karasov
(1999), in which pre-metamorphic (Gosner stage 24-26) green frog (Rana clamitans) tadpoles
were exposed to ammonia for 103 days under renewal conditions. Tadpoles were evaluated in
two different experiments conducted in successive years. In the 1997 experiment, survival and
growth were not significantly different from controls at the highest concentration tested, or 2.2
mg N/L at pH=8.7 and 24°C, although only approximately 50% of the frogs survived at this
concentration compared to the controls (98% survival). Note: survival was reduced to
approximately 78% at 0.94 mg N/L at test temperature and pH. Growth, measured as total
length, was no different between treatments. The frogs grew from an average total length of
approximately 7.5 mm at test initiation to approximately 50 mm in all treatments. The NOEC
for growth of green frog tadpoles in the study (which does not represent an early life-stage or
partial life-cycle study) is >6.90 mg N/L at pH=8.
26
-------
In addition to the several "other" chronic studies identified above, three studies provide useful
information with which to assess the appropriateness of the CCC on its protectiveness to
threatened and endangered fish species (data included in Table 6 for convenience).
In order to determine if whole effluent toxicity testing is protective of threatened and endangered
fish species, Dwyer et al. (2005) conducted 7-day chronic toxicity tests with Ceriodaphnia dubia
(neonates, <24 h old) and fathead minnow larvae (Pimephalespromelas, <24 h) in addition to
the following six threatened and endangered fish species: boneytail chub (Gila elegans), spotfm
chub (Cyprinella monocha), Cape Fear shiner (Notropis mekistocholas), gila topminnow
(Poeciliopsis occidentalis), Colorado pike minnow (Ptychocheilus Indus), and razorback sucker
(Xyrauchen texanus). The age of the six threatened and endangered fish species used during the
7-day ammonia exposures ranged from <1 to 7 days. The mean temperature during the tests was
25°C and the pH of the ASTM hard water used in tests was in the range of 7.8 to 8.0. Actual test
concentrations were not measured in the tests, although test solutions were renewed daily.
Results were based on nominal total ammonia nitrogen (mg N/L). The combined effect on test
species survival and growth were determined as IC25 values. Tests were repeated anywhere
from one to six times for each species, and the reported IC25 values are the geometric mean of
replicate IC25 values when applicable. The reported IC25 values for C. dubia and fathead
minnow are 1.3 and 7.2 mg N/L, or 1.08 and 5.97 mg N/L when adjusted to a pH of 8.0 and 25
°C (C. dubia only). The six endangered species, presented in the same order as they are listed
above, have reported IC25 values of: 11.0, 15.8, 8.8, 24.1, 8.9 and 13.4 mg N/L, or 9.12, 13.10,
7.30, 19.99, 7.38 and 11.11 mg N/L when adjusted to a pH of 8.0. Based on the results, the two
species typically used for whole effluent toxicity testing (C. dubia and P. promelas) were more
sensitive to ammonia and are protective of the six listed fish species when used as surrogate test
species.
Meyer and Hansen (2002) conducted a 30-day toxicity test with late-stage larvae (0.059 g) of
Lost River suckers (Deltistes luxatus) at pH=9.5. The exposure duration and pH were chosen to
represent the period of combined elevated un-ionized ammonia concentrations and elevated pH
that occur during cyanobacterial blooms in surface waters of Upper Klamath Lake, which have
been shown to last for several weeks to a month. Mean measured temperature during the study
27
-------
was 22.3°C and dissolved oxygen was 6.2 mg/L. Survival decreased significantly at 1.23 and
2.27 mg N/L, whereas the highest NOEC for all endpoints (survival, growth, body ions, and
swimming performance) was 0.64 mg N/L. Most deaths in the 2.27 mg N/L exposure occurred
during the first three days of the test, while mortality of larvae in the 1.23 mg N/L treatment
occurred gradually from days 2 to 24. The 29% average mortality in the 0.64 mg N/L treatment
was all due to an unexplained complete loss of one replicate between days 5 and 7 of the
exposure. Control survival was > 90%. The calculated LOEC of 1.23 mg N/L total ammonia
normalized to pH=8 corresponds to a value of 10.43 mg N/L.
Fairchild et al. (2005) conducted 28-day toxicity tests with early life-stages of Colorado
pikeminnow (Ptychocheilus lucius) and razorback sucker (Xyrauchen texanus\ and compared
the results of those tests with a test using a surrogate fish species, the fathead minnow
(Pimephalespromelas). Tests were initiated 2 days after swim-up when the larvae were feeding
exogenously (or at 8-d post hatch for Colorado pikeminnow, 9-d post hatch for razorback sucker,
and 4-d post-hatch for fathead minnow). Temperature, pH and dissolved oxygen over the 28-day
test period averaged 19.9°C, 8.24, and 7.4 mg/L (80% saturation) over the course of the three
studies. Control mortality was 7% (fathead minnows and Colorado pikeminnow) or less (3%,
razorback sucker) on day 28. Effect concentrations based on the survival and growth endpoints
of the fathead minnow and razorback sucker tests were not different; however, growth was the
more sensitive endpoint for the Colorado pikeminnow test. The 28-d growth LOEC for the
Colorado pikeminnow was 8.60 mg N/L, or 12.26 mg N/L at pH=8. The 28-d survival LOEC
for the razorback sucker was 13.25 mg N/L, or 19.20 mg N/L at pH=8. Both endangered fish
species exhibited similar sensitivity to ammonia as the fathead minnow (LOEC of 13.48 mg N/L
at pH=8; see Table 6). The same can be said for the Lost River sucker, which indicates that
these particular endangered fish species will be protected by the CCC value calculated in this
update and provided below.
28
-------
Update of the CCC
Twelve GMCVs are presented in Table 5. Although Table 5 contains additional SMCVs for two
species within the genus Oncorhynchus, no GMCV was derived for this genus because of the
large range in EC20 values; the 1999 AWQC document has evaluated whether the CCC poses a
risk to this genus, and concluded that it does not.
As was the case in the 1999 AWQC chronic dataset, Table 5 still does not contain data for an
insect genus. However, available information for a stonefly (Thurston et al. 1984b) indicates that
at least one aquatic insect species is relatively insensitive to ammonia (U.S. EPA 1999).
Therefore, calculation of the fifth percentile directly from the GMCVs in Table 5 should be
protective of insects and should adequately reflect the intent of the Guidelines.
For the calculation of the CCC in this update of the 1999 recommendation, the number of tested
genera is considered to be 13 because the GMCV for H. azteca was not used (see previous
o
discussion), and a GMCV for an insect is assumed to be greater than the four lowest GMCVs .
The fifth percentile value calculated by this procedure could be considered to be a "less than"
value because three of the four lowest GMCVs are "less than" values. The relevant relationships
for formulating a seasonal, pH- and temperature-dependent chronic criterion remain as specified
in the 1999 AWQC document, and are as follows:
• The acute pH dependence is not applied to chronic toxicity because the measured acute-
chronic ratios change substantially with pH. Equation 12, presented in the 1999 AWQC
document, describes the shape of chronic pH dependence.
• This criteria formulation assumes no temperature dependence for fish endpoints.
• The temperature dependence for invertebrate chronic endpoints is set to the chronic slope
of-0.028 above 7°C; the slope is then set to zero below 7°C. Thus, invertebrate chronic
endpoints are temperature normalized in Table 5.
8 For this reassessment of the 1999 chronic criterion concentration, the addition of a thirteenth genus representative
of an aquatic insect species increases the number of GMAVs to 13, which is the number used in the calculation of
the fifth percentile value or Final Chronic Value, as per the calculation provided in the Guidelines.
29
-------
Similar to the 1999 AWQC approach, this update of the CCC also begins with a baseline chronic
criterion calculated at 25°C. This reference temperature was selected because: a) it is the same
temperature used to normalize the chronic invertebrate toxicity data in the 1999 AWQC
document, and b) it is close to the temperature for the chronic test with the four most sensitive
genera (Lampsilis, Villosa, Musculium andLepomis; 20-20.8°C). Consequently, temperature
extrapolation uncertainties are minimized. Table 5 presents the GMCVs normalized to 25°C.
The GMCVs for the four most sensitive species are thus as follows:
< 0.3443 mg N/L for Lampsilis
< 0.9805 mg N/L for Villosa
< 2.260 mg N/L for Musculium
2.852 mg N/L for Lepomis
With N=13 (i.e., the 12 GMCVs provided in Table 5 plus the hypothetical GMCV for insects),
this results in a CCC of 0.26 mg N/L at 25°C and pH=8. Figure 2 shows the ranked GMCVs all
at pH=8 and 25°C.
If all data from the Family Unionidae were removed from the dataset, the total number of genera
is reduced from 13 to 11 (10 GMCVs provided in Table 5 plus the hypothetical GMCV for
insects). With the freshwater mussel (Unionidae) data removed from the dataset, one of the four
most sensitive genera is an invertebrate (long fingernail clam) in the Phylum Mollusca, while the
other three are fish species (see text Table C). The removal of the Unionidae data results in a
CCC seven times greater than the CCC of 0.26 mg N/L calculated with the two freshwater
mussel genera, or 1.8 mg N/L at 25°C and pH=8.
30
-------
Table C. Comparison of the four taxa used to calculate the CCC in this update with and
without freshwater bivalve data from the Family Unionidae.
Including All Data
SPECIES
Bluegill
Lepomis macrochirus
Long fingernail clam
Musculium tramversum
Rainbow mussel,
Villosa iris
Lampsilis sp. (Unionidae),
includes:
L. fasciola and L. siliquoidea
CCC
GMCV
(mgN/L)
2.852
<2.260
O.9805
O.3443
0.26
Excluding Freshwater Mussel Data
(Family Unionidae)
SPECIES
Smallmouth bass,
Micropterus dolomieui
Fathead minnow,
Pimephales promelas
Bluegill
Lepomis macrochirus
Long fingernail clam
Musculium transversum
CCC
GMCV
(mgN/L)
4.562
3.093
2.852
<2.260
1.8
At 25°C and pH 8, this 2009 update of the current CCC (with freshwater mussels present) is
approximately 4.8 times lower than that listed in the 1999 document (CCC=1.2 mg N/L), due to
the addition of the two freshwater mussels. The updated CCC of 0.26 mg N/L in this document is
26 percent lower than the lowest GMCV (0.34 mg N/L for Lampsilis). As discussed in the 1999
AWQC document, the alternative of calculating the CCC directly from new sets of GMCVs for
each pH and temperature combination results in different degrees of extrapolation that would not
be reasonable here.
The most important difference between the calculation of the CCC in this update and the 1999
AWQC document is that the GMCVs for bivalve mollusks, particularly the two new GMCVs for
freshwater mussels, control the value of the criterion.
Although the CCC was calculated directly from CVs using the fifth percentile procedure as it
was in the 1999 AWQC document (U.S. EPA 1999), it is prudent to consider how this new CCC
compares a CCC calculated using acute-chronic ratios (ACRs). Consistent with the approach in
31
-------
the 1999 AWQC document, ACRs were determined for most of the EC20s in Table 5 that are
used in the derivation of a GMCV and for which comparable acute values were found. All
relevant acute and chronic values were adjusted to pH=8 and are expressed in terms of mg N/L,
where N is total ammonia nitrogen. (Note that for this comparison, the acute and chronic values
for invertebrates were not adjusted to 25°C.) The resulting ACRs are provided in Table 7, along
with the resulting Genus Mean Acute-Chronic Ratios (GMACRs).
Three new ACRs were added to the 1999 AWQC dataset. Two of the ACRs were for freshwater
mussels in the genus Lampsilis (Table 7). The ACRs within the genus were in good agreement.
A third ACR was added for the freshwater mussel species Villosa iris. The ACR for this
sensitive species was roughly half that of Lampsilis (Table 7), but very close to the median ACR
(6.3) of the other freshwater and invertebrate species for which information is available.
Two additional ACRs for endangered fish species, though not included in Table 7 because they
were not from studies using true early life-stage fish, are worth noting here. ACRs of 2.772 and
2.135 were estimated for the Colorado pikeminnow (P. lucius) and razorback sucker (X.
texanus), respectively. These ACRs are lower than most other freshwater fish species owing to
their relatively high tolerance to chronic ammonia exposure (see Table 6).
Table 8 provides the GMACRs beside the ranked GMAVs to demonstrate whether there is a
trend, because ACRs for some chemicals are higher for resistant species than for sensitive
species (U.S. EPA 1985). No trend is obvious and the range of the GMACRs is 1.8 to 18. The
findings are similar to those reported in the 1999 AWQC document.
The problem with using the ACR procedure for calculating a CCC for ammonia in the 1999
AWQC document was that ACRs were not available for the most sensitive species. For the
current document GMACRs are available for the two most sensitive genera: Lampsilis (GMACR
= >18.27) and Villosa (GMACR = >6.129). At pH=8 and 25°C, the hypothetical FACR at the
new CCC corresponds to (5.734 mg N/L)/(0.26 mg N/L) or 22.05 using the calculated FAV
when freshwater mussels are present. The hypothetical FACR is reasonable under this scenario
(i.e., 17% higher than the SMACR of 18.27 for Lampsilis), and thus, direct calculation of the
32
-------
CCC using the fifth percentile calculation appears to be an acceptable, appropriately
conservative procedure. In addition, the CCC obtained using the fifth percentile procedure
agrees well with the available chronic data (i.e., at pH 8 and 25°C, the CCC is 24 percent lower
than the lowest GMCV).
Temperature and pH-Dependent Criteria Calculation
As indicated in the 1999 AWQC document, part of a criterion derivation is the estimation of the
CMC or CCC based on the set of toxicity values available for different genera. The CMC or
CCC estimate is intended to be what would be obtained by simple inspection if many genera had
been tested. Generally, this CMC or CCC is below the lowest value. For small datasets (<19) it
is assumed that the lowest toxicity value is below the fifth percentile (i.e., if many more genera
were tested, the fifth percentile would likely be more sensitive than any value in the small
dataset). Because the CMC is one half of the fifth percentile (i.e., FAV/2), it is typically lower
than the lowest GMAV even in large datasets. Because the extrapolation procedure used to
calculate the CMC or CCC is based on the slope of the four most sensitive genera, if the genera
vary widely in sensitivity, the extrapolated criterion value is further below the lowest value than
if the criteria were tightly grouped. This is statistically appropriate because when variance is
high (i.e., values are widely spaced), the fifth percentile of the distribution would be expected to
lie further below the lowest value of a small dataset than if the variance was low.
However, this extrapolation procedure, while appropriate for criteria derivations across
chemicals with different variances for genus sensitivities, is not necessarily appropriate when the
genera are following different temperature or life stage dependencies. Sensitivities change with
temperature or life stage, and as a result, the spread of the four lowest GMAVs or GMCVs, and
the resulting degree of extrapolation to the fifth percentile of sensitivity also changes. Rather
than develop separate sets of GMAVs and GMCVs for each temperature and computing the
CMC or CCC from the four most sensitive GMAVs or GMCVs at each temperature-pH
combination, the extrapolation approach described below will be used.
This issue of extrapolation to different temperatures and pHs with regard to chronic toxicity was
addressed in the 1999 AWQC document for ammonia by first calculating the ratio of the CCC to
33
-------
the lowest GMCV, and then applying that ratio to subsequent criteria calculations for all possible
pH and temperature combinations. The rationale of this approach was that it offered a degree of
extrapolation that was modest and reasonable given the relatively low number of tested genera,
and that it was a preferable approach to the alternative procedure of calculating CCCs directly
from new sets of GMCVs for each pH-temperature combination, as each combination could
result in different degrees of extrapolation, some of which could be more than 50% below the
lowest GMCV. Because fish GMCVs are not affected by temperature, and because the most
sensitive fish species was an early life stage (ELS) ofLepomis, this analysis was conducted
separately for the scenarios of when fish ELS were included or not included in the calculation of
the CCC. The reason for this is because even though the lowest GMCV at 25°C was for an
invertebrate, as temperature decreases, invertebrates, but not fish, become less sensitive to
ammonia, and below a particular temperature threshold, fish become the most sensitive genera.
This consequence was described in detail in the 1999 AWQC document, and will be described
further below.
Finally, in the 1999 Update, the most sensitive GMAVs were fish, and because their sensitivities
to ammonia did not vary with temperature, no temperature extrapolation was performed. In
contrast, the lowest GMAVs in this document are for invertebrates, and as a consequence, the
temperature extrapolation procedure will be similarly applied to the CMC as well as the CCC.
Temperature Extrapolation of Acute Toxicity
When freshwater mussels are present, the lowest GMAV is 3.539 mg N/L for Lasmigona
subviridus (Table 3). The resulting CMC when mussels are present of 2.87 mg N/L is 18.9%
lower than the lowest GMAV. When freshwater mussels are absent, the lowest GMAV is 6.018
mg N/L for Corbicula fluminea (Table 3). The resulting CMC when mussels are absent of 4.97
mg N/L is 17.4% lower than the lowest GMAV. In both cases, the most sensitive fish species is
the salmonid Prosopium williamsoni, with a GMAV of 12.09 mg N/L (Table 3). Because the
most sensitive genera are invertebrates, regardless of whether freshwater mussels are included or
excluded, the criterion will vary with temperature according to the invertebrate acute temperature
34
-------
relationship, but cannot exceed the extrapolated ratio multiplied by the lowest (most sensitive)
fish GMAV.
When freshwater mussels are present, at pH=8, the CMC would be expressed as:
CMC = 0.811 * MJJV(l2,09J3.539 *
This function increases steadily with decreasing temperature (T), until it reaches a maximum
(0.81 1 * 12.09 = 9.805 mg N/L) at 10.2°C, below which it remains constant (Figure 3).
When freshwater mussels are absent, at pH=8, the CMC would be expressed as:
CMC = 0.826 * M IN (12. 09, 6.018 * iQaci36H2S-T>)
This function increases steadily with decreasing temperature (T), until it reaches a maximum
(0.826 * 12.09 = 9.99 mg N/L) at 16.6°C, below which it remains constant (Figure 3). The
slightly higher maximum concentration is the result of the higher CMC/lowest GMAV ratio
calculated when freshwater mussels are present (0.826) versus when freshwater mussels are
absent (0.8 11).
Temperature Extrapolation of Chronic Toxicity
When freshwater mussels are present, the lowest GMCV is <0.3443 mg N/L for Lampsilis sp.
(Table 5). The resulting CCC when mussels are present of 0.256 mg N/L is 25.6% lower than
the lowest GMCV, as noted above. When freshwater mussels are absent, the lowest GMCV is
<2.260 mg N/L for Musculium tramversum (Table C). The resulting CCC when mussels are
absent of 1.84 mg N/L is 18.6% lower than the lowest GMCV. In both cases, the most sensitive
fish species is the early life stage ofLepomis macrochirus with a GMCV of 2.852 mg N/L (Table
C). Because the most sensitive genera are invertebrates, regardless of whether freshwater
mussels are included or excluded, the criterion will vary with temperature according to the
35
-------
invertebrate chronic temperature relationship, but cannot exceed the extrapolated ratio multiplied
by the lowest fish GMCV.
When freshwater mussels are present, at pH=8, the CCC would be expressed as:
CCC = 0.744 * ( 0.3443 *
This function increases steadily with decreasing temperature (T), until it reaches a maximum at
7°C, below which it remains constant (Figure 4). The rationale for the 7°C plateau in
extrapolated invertebrate sensitivities was described in detail in the 1999 AWQC document. In
summary, the assumption of invertebrate insensitivity to temperatures of 7°C and below is based
on an interpretation of the empirical relationship between acute ammonia toxicity of
invertebrates and temperature, first described by Arthur et al (1987), and reproduced in the 1999
document as Figure 6. Because the highest possible extrapolated CCC (0.817 mg N/L at 0-7°C
and pH=8) is lower than the extrapolated value for the early life stage of the most sensitive fish
species (0.744*2.852=2. 12 mg N/L at pH=8), fish are not considered in the CCC temperature
extrapolations when freshwater mussels are present (Figure 4).
When freshwater mussels are absent and fish ELS are absent, at pH=8, the CCC would be
expressed as:
CCC = 0.814 * (2.260 * ^.KS^S-MAX^
This function increases steadily with decreasing temperature (T), until it reaches a maximum at
7°C, below which it remains constant (Figure 4), following the same rationale for the 7°C
plateau as described in the case with mussels present. As described in the 1999 document, when
early life stages are absent, the ELS GMCV of 2.852 mg N/L for Lepomis would have been
replaced by the 8.78 mg N/L GMCV for juvenile and adult Lepomis. Because the highest
extrapolated CCC (5.87 mg N/L at 0-7°C and pH=8) is lower than the extrapolated value for the
most sensitive juvenile or adult fish species (0.814*8.78=7.15 mg N/L at pH=8), juvenile and
adult fish are not considered in the CCC temperature extrapolations when freshwater mussels are
absent (Figure 4).
36
-------
When freshwater mussels are absent and fish ELS are present, at pH=8, the CCC would be
expressed as:
CCC = 0.814 * ,M/Ar(2.852,,2,26G * 1Q^2EK25-T}
This function is analogous to the functions described in the two acute scenarios, and increases
steadily with decreasing temperature (T), until it reaches a maximum (0.814 * 2.852 = 2.32 mg
N/L) at 21.3°C, below which it remains constant (Figure 4).
THE NATIONAL CRITERIA FOR AMMONIA IN FRESH WATER
The available data for ammonia, evaluated using the procedures described in the Guidelines,
indicate that, except possibly where an unusually sensitive species is important at a site,
freshwater aquatic life should be protected if both of the following conditions are satisfied for the
temperature, T, and pH of the waterbody:
1. The one-hour average concentration of total ammonia nitrogen (in mg N/L) does not exceed,
more than once every three years on the average, the CMC calculated using the following
equations:
Where freshwater mussels are present:
/ 0.0489 6.95 \ ,
CMC = 0.811 * - ^TTI — [H -- „ .„,, * MLV(12, 09, 3,539 * iQ^&fus-, A
-7-204-* - *-7-20 ' J
Or where freshwater mussels are absent:
CMC = 0.826 * ( —-—- J "„ _„,) * A«W (12.09,6.018 * io0-M6*<2S-T>)
Vl- lQ7,2Q4-ptf 110pH-7.204 ^ V }
37
-------
2 A. The thirty-day average concentration of total ammonia nitrogen (in mg N/L) does not
exceed, more than once every three years on the average, the CCC (chronic criterion) calculated
using the following equations:
Where freshwater mussels are present and fish early life stages are present or absent:
CCC = 0,744 * - + - * 0.3443
'
Or where freshwater mussels are absent and fish early lifte stages are absent:
CCC = 0,814 * - ' „ -- '' ft * (2,260
7'6SS~tf ' - tf~7l63S
2B. The thirty-day average concentration of total ammonia nitrogen (in mg N/L) does not
exceed, more than once every three years on the average, the CCC (chronic criterion) calculated
using the following equation.
When freshwater mussels are absent and fish early life stages are present:
0,0676 2.912
CCC = 0.814* - -rrr — -^, -- „ „_, * MIN 2.852, 2,260*
" -~ '
2C. In addition, the highest four-day average within the 30-day exceedence period should not
exceed 2.5 times the CCC.
Several points should be noted concerning the updated acute and chronic criteria:
38
-------
Acute:
1. Unlike in the 1999 AQWC document, the lowest GMAV when freshwater mussels are
present or absent in this update is an invertebrate species; thus, the CMCs under both conditions
are pH- and temperature-dependent.
2. Because the most sensitive genera are invertebrates, the criterion will vary with temperature
according to the invertebrate acute temperature relationship, but cannot exceed 81.1% of the
lowest fish GMAV (mussels present) or 82.6% of the lowest fish GMAV (mussels absent). The
lowest seasonal GMAV for fish is 12.09 mg N/L for the salmonid Prosopium williamsoni, the
mountain whitefish. Therefore, the CMC equals 81.1% (or 82.6%) times the lower of (a) the
temperature adjusted lowest invertebrate GMAV, or (b) the lowest fish GMAV (Figure 3).
3. When a threatened or endangered species occurs at a site and sufficient data indicate that it is
sensitive at concentrations below the CMC, it is appropriate to consider deriving a site-specific
criterion.
Chronic:
1. The four lowest GMC Vs are all "less than" values. The CCC might be lower if early life
stages of the two freshwater mussel genera (Lampsilis and Villosd) are more sensitive than the
juvenile life stages tested. The CCC might also be lower if a point estimate (e.g. EC20), rather
than a "less than" value, could have been derived from the studies with the fingernail clam.
2. The laboratory data for some of the snail species, particularly non-pulmonates, which might
be considered to have special ecological importance at some sites, indicate that these species
could be affected at concentrations below the CCC when freshwater mussels are absent, but not
when freshwater mussels are present. Other data indicate that these species might not be affected
by such concentrations. At most sites the intermittency of exposures would probably reduce risk.
4. Likewise, some of the laboratory and field data for the fingernail clam also indicate that this
species could be affected at concentrations below the CCC when freshwater mussels are absent,
but not when freshwater mussels are present. Other data indicate that it would not be affected by
such concentrations. Again, at most sites the intermittency of exposures would probably reduce
risk.
5. The central tendency of the available chronic EC20s for salmonids (5.4 mg /L), even though
not used directly in the calculation of the CCC, indicates that these species will be protected by
39
-------
the CCC when freshwater mussels are present, and will probably be protected when freshwater
mussels are absent, although the data suggest there might be important differences between
strains of rainbow trout, and some tests indicated effects at concentrations slightly below the
CCC.
6. All new chronic data added to this update of the 1999 AWQC for fish is from early life stage
tests of the species (see new data for Oncorhynchus clarki Henshawi, Esox lucius, and Cyprinus
carpio in Table 5); thus, the justification for the derivation of a CCC for fish early stages present
and absent established in the 1999 AWQC document also applies in this document.
8. As above, when a threatened or endangered species occurs at a site and sufficient data
indicate that it is sensitive at concentrations below the CCC, it is appropriate to consider deriving
a site-specific criterion.
9. And, as previously explained in the 1999 AWQC document, the CCC is based on a 20
percent reduction in survival, growth, and/or reproduction, which is a risk management decision
by EPA also retained for this document.
In addition to the above, the following general points also hold true for this document:
1. The Recalculation Procedure, the WER Procedure, and the Resident Species Procedure may
be used to derive site-specific criteria for ammonia, but most WERs that have been determined
for ammonia are close to 1.
2. The CMC, CCC, and chronic averaging period presented above supersede those presented in
previous guidance on the aquatic life criterion for ammonia in fresh water. The 1998, 1999 and
this update do not address or alter the past recommendation of a one-hour averaging period for
the CMC or the past recommendation of a once-in-three years on the average allowable
frequency for exceeding the CMC or CCC. Many issues concerning the implementation of
aquatic life criteria are discussed in the "Technical Support Document for Water Quality based
Toxics Control" (U.S. EPA 1991).
3. If concentrations in 95 percent of grab or 24-hour composite samples do not exceed the CCC,
then the 30-day average concentrations are unlikely to exceed the CCC more than once in three
years (Delos 1999). This assumes that concentrations are log normally distributed, with first-
order log serial correlation coefficient between 24-hour composite samples approximately 0.86 -
0.94 (or less), and a log standard deviation of 0.5 - 0.8 (or less).
40
-------
4. Finally, because the ammonia criteria are a function of both pH and temperature, calculation
of the appropriate weighted average temperature or pH is complicated. For some purposes,
calculation of an average pH and temperature can be avoided. For example, if samples are
obtained from a receiving water over a period of time during which pH and/or temperature was
not constant, the pH, temperature, and the concentration of total ammonia in each sample should
be determined. For each sample, the criterion should be determined at the pH and temperature of
the sample, and then the concentration of total ammonia nitrogen in the sample should be divided
by the criterion to determine a quotient. The criterion is attained if the mean of the quotients is
less than 1 over the duration of the averaging period.
The temperature and pH-dependent values for the CMC and CCC are provided in the tables
below for a given scenario, i.e., freshwater mussels present or absent, fish early life stages
present or absent. The same values are presented graphically for ease of understanding in
Figures 3 (temperature- and pH-dependence of the CMC) and 4 (temperature- and pH-
dependence of the CCC).
Available data indicate that freshwater mussels exhibit the same general response to ammonia at
higher pH such that total ammonia ECSOs decrease with increasing pH similar to the average
relationship for other taxa as established in the 1999 AWQC document (Wang et al. 2008). For
this update of the freshwater ammonia AWQC the relationship between the acute and chronic
toxicity of ammonia to freshwater mussels and temperature is assumed to be similar to other
invertebrate species, i.e., sensitivity to ammonia decreases at lower ambient water temperatures.
41
-------
Temperature and pH-Dependent Values of the CMC (Acute Criterion): Mussels Present
pH
6.5
6.6
6.7
6.8
6.9
7.0
7.1
7.2
7.3
7.4
7.5
7.6
7.7
7.8
7.9
8.0
8.1
8.2
8.3
8.4
8.5
8.6
8.7
8.8
8.9
9.0
0
57.0
54.7
52.0
49.0
45.7
42.1
38.3
34.5
30.6
26.8
23.2
19.9
16.9
14.2
11.8
9.81
8.11
6.68
5.50
4.53
3.74
3.09
2.57
2.15
1.82
1.54
14
41.5
39.8
37.9
35.7
33.3
30.7
27.9
25.1
22.3
19.5
16.9
14.5
12.3
10.3
8.61
7.15
5.91
4.87
4.01
3.30
2.72
2.25
1.87
1.57
1.32
1.13
CMC:
16
35.2
33.7
32.1
30.2
28.2
26.0
23.7
21.3
18.9
16.5
14.3
12.3
10.4
8.74
7.30
6.06
5.00
4.12
3.40
2.80
2.31
1.91
1.59
1.33
1.12
0.953
Mussels
Present, mg N/L
Temperature,
18 20
29.8
28.6
27.2
25.6
23.9
22.0
20.1
18.0
16.0
14.0
12.1
10.4
8.81
7.41
6.18
5.13
4.24
3.49
2.88
2.37
1.95
1.62
1.35
1.13
0.949
0.808
25.2
24.2
23.0
21.7
20.2
18.7
17.0
15.3
13.6
11.9
10.3
8.81
7.47
6.28
5.24
4.35
3.59
2.96
2.44
2.01
1.66
1.37
1.14
0.954
0.804
0.684
C
22
21.4
20.5
19.5
18.4
17.2
15.8
14.4
12.9
11.5
10.1
8.71
7.46
6.33
5.32
4.44
3.68
3.04
2.51
2.07
1.70
1.40
1.16
0.966
0.808
0.681
0.580
24
18.1
17.4
16.5
15.6
14.5
13.4
12.2
11.0
9.73
8.52
7.38
6.32
5.36
4.50
3.76
3.12
2.58
2.13
1.75
1.44
1.19
0.984
0.818
0.685
0.577
0.491
26
15.4
14.7
14.0
13.2
12.3
11.3
10.3
9.29
8.24
7.22
6.25
5.35
4.54
3.82
3.19
2.64
2.18
1.80
1.48
1.22
1.01
0.833
0.693
0.580
0.489
0.416
28
13.0
12.5
11.9
11.2
10.4
9.61
8.75
7.87
6.98
6.12
5.30
4.54
3.85
3.23
2.70
2.24
1.85
1.53
1.26
1.03
0.853
0.706
0.587
0.491
0.414
0.353
30
11.0
10.6
10.1
9.48
8.84
8.15
7.42
6.67
5.92
5.18
4.49
3.84
3.26
2.74
2.29
1.90
1.57
1.29
1.06
0.876
0.723
0.598
0.497
0.416
0.351
0.299
42
-------
Temperature and pH-Dependent Values of the CMC (Acute Criterion): Mussels Absent
pH
6.5
6.6
6.7
6.8
6.9
7.0
7.1
7.2
7.3
7.4
7.5
7.6
7.7
7.8
7.9
8.0
8.1
8.2
8.3
8.4
8.5
8.6
8.7
8.8
8.9
9.0
0
58.0
55.7
53.0
49.9
46.5
42.9
39.1
35.1
31.2
27.3
23.6
20.2
17.2
14.4
12.0
9.99
8.26
6.81
5.60
4.61
3.81
3.15
2.62
2.19
1.85
1.57
14
58.0
55.7
53.0
49.9
46.5
42.9
39.1
35.1
31.2
27.3
23.6
20.2
17.2
14.4
12.0
9.99
8.26
6.81
5.60
4.61
3.81
3.15
2.62
2.19
1.85
1.57
CMC
16
58.0
55.7
53.0
49.9
46.5
42.9
39.1
35.1
31.2
27.3
23.6
20.2
17.2
14.4
12.0
9.99
8.26
6.81
5.60
4.61
3.81
3.15
2.62
2.19
1.85
1.57
Mussels Absent, mg
18
58.0
55.7
53.0
49.9
46.5
42.9
39.1
35.1
31.2
27.3
23.6
20.2
17.2
14.4
12.0
9.99
8.26
6.81
5.60
4.61
3.81
3.15
2.62
2.19
1.85
1.57
Temperature, C
20 22
43.7
41.9
39.9
37.6
35.1
32.3
29.4
26.4
23.5
20.6
17.8
15.3
12.9
10.9
9.07
7.53
6.22
5.13
4.22
3.48
2.87
2.37
1.97
1.65
1.39
1.19
37.0
35.5
33.8
31.9
29.7
27.4
24.9
22.4
19.9
17.4
15.1
12.9
11.0
9.21
7.69
6.38
5.27
4.34
3.58
2.95
2.43
2.01
1.67
1.40
1.18
1.00
N/L
24
31.4
30.1
28.6
27.0
25.2
23.2
21.1
19.0
16.8
14.8
12.8
10.9
9.28
7.80
6.51
5.40
4.47
3.68
3.03
2.50
2.06
1.70
1.42
1.19
1.00
0.851
26
26.6
25.5
24.3
22.9
21.3
19.7
17.9
16.1
14.3
12.5
10.8
9.27
7.86
6.61
5.52
4.58
3.78
3.12
2.57
2.11
1.74
1.44
1.20
1.00
0.847
0.721
28
22.5
21.6
20.6
19.4
18.1
16.7
15.2
13.6
12.1
10.6
9.18
7.86
6.66
5.60
4.67
3.88
3.21
2.64
2.18
1.79
1.48
1.22
1.02
0.851
0.718
0.611
30
19.1
18.3
17.4
16.4
15.3
14.1
12.8
11.5
10.2
8.98
7.77
6.66
5.64
4.74
3.96
3.29
2.72
2.24
1.84
1.52
1.25
1.04
0.862
0.721
0.608
0.517
43
-------
Temperature and pH-Dependent Values of the CCC (Chronic Criterion): Mussels Present
CCC: Mussels Present, mg N/L
pH
6.5
6.6
6.7
6.8
6.9
7.0
7.1
7.2
7.3
7.4
7.5
7.6
7.7
7.8
7.9
8.0
8.1
8.2
8.3
8.4
8.5
8.6
8.7
8.8
8.9
9.0
0
2.24
2.21
2.16
2.11
2.05
1.98
1.90
1.81
1.71
1.59
1.47
1.34
1.20
1.07
0.940
0.817
0.704
0.602
0.512
0.433
0.366
0.309
0.261
0.222
0.190
0.163
14
1.43
1.40
1.38
1.35
1.31
1.26
1.21
1.15
1.09
1.01
0.933
0.850
0.765
0.681
0.598
0.521
0.449
0.384
0.326
0.276
0.233
0.197
0.166
0.141
0.121
0.104
16
1.25
1.23
1.21
1.18
1.15
1.11
1.07
1.01
0.955
0.890
0.820
0.747
0.673
0.598
0.526
0.458
0.394
0.337
0.287
0.243
0.205
0.173
0.146
0.124
0.106
0.0914
18
1.10
1.09
1.06
1.04
1.01
0.977
0.937
0.891
0.839
0.782
0.721
0.657
0.591
0.526
0.462
0.402
0.347
0.296
0.252
0.213
0.180
0.152
0.129
0.109
0.0934
0.0804
Temperature, C
20 22
0.968
0.954
0.936
0.914
0.889
0.858
0.823
0.783
0.738
0.688
0.634
0.578
0.520
0.462
0.406
0.354
0.305
0.261
0.221
0.187
0.158
0.134
0.113
0.0960
0.0821
0.0707
0.851
0.838
0.823
0.804
0.781
0.755
0.724
0.688
0.648
0.604
0.557
0.508
0.457
0.406
0.357
0.311
0.268
0.229
0.195
0.165
0.139
0.117
0.0994
0.0844
0.0721
0.0621
24
0.748
0.737
0.723
0.707
0.687
0.663
0.636
0.605
0.570
0.531
0.490
0.446
0.402
0.357
0.314
0.273
0.235
0.201
0.171
0.145
0.122
0.103
0.0874
0.0742
0.0634
0.0546
26
0.658
0.648
0.636
0.621
0.604
0.583
0.559
0.532
0.501
0.467
0.431
0.392
0.353
0.314
0.276
0.240
0.207
0.177
0.150
0.127
0.107
0.0908
0.0768
0.0652
0.0557
0.0480
28
0.578
0.569
0.559
0.546
0.531
0.513
0.492
0.467
0.440
0.411
0.379
0.345
0.310
0.276
0.243
0.211
0.182
0.156
0.132
0.112
0.0945
0.0798
0.0675
0.0573
0.0490
0.0422
30
0.508
0.501
0.491
0.480
0.466
0.451
0.432
0.411
0.387
0.361
0.333
0.303
0.273
0.243
0.213
0.186
0.160
0.137
0.116
0.0983
0.0831
0.0701
0.0593
0.0504
0.0431
0.0371
44
-------
Temperature and pH-Dependent Values of the CCC (Chronic Criterion): Mussels Absent and
Fish Early Life Stages Absent
CCC: Mussels Absent
pH
6.5
6.6
6.7
6.8
6.9
7.0
7.1
7.2
7.3
7.4
7.5
7.6
7.7
7.8
7.9
8.0
8.1
8.2
8.3
8.4
8.5
8.6
8.7
8.8
8.9
9.0
0
16.1
15.8
15.5
15.2
14.8
14.3
13.7
13.0
12.2
11.4
10.5
9.59
8.63
7.68
6.75
5.87
5.06
4.33
3.68
3.11
2.63
2.22
1.88
1.60
1.36
1.17
14
10.2
10.1
9.90
9.67
9.40
9.08
8.71
8.28
7.80
7.27
6.70
6.11
5.50
4.89
4.30
3.74
3.22
2.76
2.34
1.98
1.67
1.41
1.20
1.02
0.868
0.747
16
9.00
8.87
8.70
8.50
8.26
7.98
7.65
7.28
6.86
6.39
5.89
5.37
4.83
4.30
3.78
3.29
2.83
2.42
2.06
1.74
1.47
1.24
1.05
0.893
0.763
0.657
and Fish
18
7.91
7.79
7.65
7.47
7.26
7.02
6.73
6.40
6.03
5.62
5.18
4.72
4.25
3.78
3.32
2.89
2.49
2.13
1.81
1.53
1.29
1.09
0.924
0.785
0.671
0.577
Early
Life Stages
Temperature, C
20 22
6.96
6.85
6.72
6.57
6.38
6.17
5.91
5.62
5.30
4.94
4.55
4.15
3.73
3.32
2.92
2.54
2.19
1.87
1.59
1.35
1.14
0.960
0.812
0.690
0.589
0.508
6.11
6.02
5.91
5.77
5.61
5.42
5.20
4.94
4.66
4.34
4.00
3.65
3.28
2.92
2.57
2.23
1.92
1.64
1.40
1.18
0.999
0.844
0.714
0.606
0.518
0.446
Absent,
24
5.37
5.29
5.19
5.08
4.93
4.76
4.57
4.35
4.09
3.82
3.52
3.21
2.89
2.57
2.26
1.96
1.69
1.45
1.23
1.04
0.878
0.742
0.628
0.533
0.455
0.392
mgN/L
26
4.72
4.65
4.57
4.46
4.34
4.19
4.02
3.82
3.60
3.36
3.09
2.82
2.54
2.26
1.98
1.72
1.49
1.27
1.08
0.914
0.772
0.652
0.552
0.469
0.400
0.345
28
4.15
4.09
4.01
3.92
3.81
3.68
3.53
3.36
3.16
2.95
2.72
2.48
2.23
1.98
1.74
1.52
1.31
1.12
0.949
0.804
0.679
0.573
0.485
0.412
0.352
0.303
30
3.65
3.60
3.53
3.45
3.35
3.24
3.10
2.95
2.78
2.59
2.39
2.18
1.96
1.74
1.53
1.33
1.15
0.982
0.835
0.706
0.597
0.504
0.426
0.362
0.309
0.266
45
-------
Temperature and pH-Dependent Values of the CCC (Chronic Criterion): Mussels Absent and
Fish Early Life Stages Present
CCC: Mussels Absent and
pH
6.5
6.6
6.7
6.8
6.9
7.0
7.1
7.2
7.3
7.4
7.5
7.6
7.7
7.8
7.9
8.0
8.1
8.2
8.3
8.4
8.5
8.6
8.7
8.8
8.9
9.0
0
6.36
6.26
6.15
6.00
5.84
5.64
5.41
5.14
4.84
4.52
4.16
3.79
3.41
3.04
2.67
2.32
2.00
1.71
1.45
1.23
1.04
0.878
0.742
0.631
0.539
0.464
14
6.36
6.26
6.15
6.00
5.84
5.64
5.41
5.14
4.84
4.52
4.16
3.79
3.41
3.04
2.67
2.32
2.00
1.71
1.45
1.23
1.04
0.878
0.742
0.631
0.539
0.464
16
6.36
6.26
6.15
6.00
5.84
5.64
5.41
5.14
4.84
4.52
4.16
3.79
3.41
3.04
2.67
2.32
2.00
1.71
1.45
1.23
1.04
0.878
0.742
0.631
0.539
0.464
18
6.36
6.26
6.15
6.00
5.84
5.64
5.41
5.14
4.84
4.52
4.16
3.79
3.41
3.04
2.67
2.32
2.00
1.71
1.45
1.23
1.04
0.878
0.742
0.631
0.539
0.464
Fish Early
Life Stages Present,
Temperature, C
20 22
6.36
6.26
6.15
6.00
5.84
5.64
5.41
5.14
4.84
4.52
4.16
3.79
3.41
3.04
2.67
2.32
2.00
1.71
1.45
1.23
1.04
0.878
0.742
0.631
0.539
0.464
6.11
6.02
5.91
5.77
5.61
5.42
5.20
4.94
4.66
4.34
4.00
3.65
3.28
2.92
2.57
2.23
1.92
1.64
1.40
1.18
0.999
0.844
0.714
0.606
0.518
0.446
24
5.37
5.29
5.19
5.08
4.93
4.76
4.57
4.35
4.09
3.82
3.52
3.21
2.89
2.57
2.26
1.96
1.69
1.45
1.23
1.04
0.878
0.742
0.628
0.533
0.455
0.392
mgN/L
26
4.72
4.65
4.57
4.46
4.34
4.19
4.02
3.82
3.60
3.36
3.09
2.82
2.54
2.26
1.98
1.72
1.49
1.27
1.08
0.914
0.772
0.652
0.552
0.469
0.400
0.345
28
4.15
4.09
4.01
3.92
3.81
3.68
3.53
3.36
3.16
2.95
2.72
2.48
2.23
1.98
1.74
1.52
1.31
1.12
0.949
0.804
0.679
0.573
0.485
0.412
0.352
0.303
30
3.65
3.60
3.53
3.45
3.35
3.24
3.10
2.95
2.78
2.59
2.39
2.18
1.96
1.74
1.53
1.33
1.15
0.982
0.835
0.706
0.597
0.504
0.426
0.362
0.309
0.266
46
-------
UNUSED DATA
For this criteria update document, EPA considered those data referenced in the document that
met the test quality requirements described in the Guidelines (see Stephan et al. 1985). Some of
the data referenced in the document, however, did not meet these basic QA/QC requirements. In
such cases, EPA further scrutinized those studies where either: (1) the study included tests with a
species associated with one of the four most sensitive GMAVs or GMCVs used to derive the
criterion; (2) the study included test with a freshwater mussel species that could have been used
to derive the criterion, i.e., was a test with a freshwater mussel species with a pH and
temperature normalized EC50 less than 6.018 mg N/L or a normalized CV less than 2.852 mg
N/L; or (3) the study included tests with a species associated with a GMAV or GMCV within a
factor of approximately three of the fourth ranked most sensitive GMAV or GMCV. For
example, all studies with species associated with genera in the acute dataset with freshwater
mussels present that were within three times the GMAV of 6.018 mg N/L for Corbicula
fluminea, or 18 mg N/L (rounded to 20 mg N/L), were further scrutinized: thus including all
species within the range of the GMAVs for the genera Lasmigona through Micropterus in Table
3. EPA undertook this additional review of the tests in those cases where the outcome of the
review could actually lead to a different decision regarding the protectiveness of the criteria. For
each study that was potentially influential, but did not pass the additional review, the study was
not used in the determination and the rationale for its exclusion is detailed in Tables 9 (acute
studies) and 10 (chronic studies). A list of all other studies considered but "screened out" from
consideration or use in deriving the criteria is provided in Appendix G with a code (and in some
cases comments) indicating the reason for exclusion.
47
-------
REFERENCES
Abdalla, A.A.F. and C.D. McNabb. 1999. Acute and sublethal growth effects of un-ionized ammonia to
Nile tilapia Oreochromis niloticus. In: Nitrogen production and excretion in fish. Randall D.J. and D.D.
Mackinlay (Eds.), Department of Fisheries and Oceans, Vancouver, BC, Canada and Towson University,
Baltimore, MD. pp. 35-48.
Abell, R.A., D.M. Olson, E. Dinerstein, P.T. Hurley et al. 2000. Freshwater Ecoregions of North
America. A Conservation Assessment. Island Press (WWF), Washington, DC, 368 pp. ISBN 1-
55963-734-X
Alabaster, J.S. and R. Lloyd. 1980. Ammonia. In: Water quality criteria for fish. Alabaster J.S. and R.
Lloyd (Eds.). Butterworths, London, pp. 85-102.
Alonso, A. and J.A. Camargo. 2003. Short-term toxicity to ammonia, nitrite, and nitrate to the aquatic
snail Potamopyrgus antipodarum (Hydrobiidae, Mollusca). Bull. Environ. Contam. Toxicol. 70: 1006-
1012.
American Society for Testing and Materials. 2004. Standard guide for conducting renewal life-cycle
toxicity tests with Daphnia magna. Standard El 193-97 in Vol. 11.06 of the Annual Book of ASTM
Standards. American Society for Testing and Materials, West Conshohocken, PA.
American Society for Testing and Materials. 2005. Standard guide for conducting early life-stage toxicity
tests with fishes. Standard E1241-05 in Vol. 11.06 of the Annual Book of ASTM Standards. American
Society for Testing and Materials, West Conshohocken, PA.
American Society for Testing and Materials. 2006a. Standard guide for conducting laboratory toxicity
tests with freshwater mussels. Standard E2455-06 in Vol. 11.06 of the Annual Book of ASTM Standards.
American Society for Testing and Materials, West Conshohocken, PA.
American Society for Testing and Materials. 2006b. Standard guide for conducting three-brood, renewal
toxicity tests with Ceriodaphnia dubia. Standard E1295-01 in Vol. 11.06 of the Annual Book of ASTM
Standards. American Society for Testing and Materials, West Conshohocken, PA.
Andersen, H. and J. Buckley. 1998. Acute toxicity of ammonia to Ceriodaphnia dubia and a procedure to
improve control survival. Bull. Environ. Contam. Toxicol. 61(1): 116-122.
Anderson, K.B., R.E. Sparks and A.A. Paparo. 1978. Rapid assessment of water quality, using the
fingernail clam, Musculium transversum. WRC Research Report No. 133, University of Illinois, Water
Resources Center, Urbana, IL.
Ankley, G.T., M.K. Schubauer-Berigan and P.D. Monson. 1995. Influence of pH and hardness on toxicity
of ammonia to the amphipod Hyalella azteca. Can. J. Fish. Aquat. Sci. 52(10): 2078-2083.
Arthur, J.W., C.W.West, K.N. Allen and S.F. Hedtke. 1987. Seasonal toxicity of ammonia to five fish and
nine invertebrates species. Bull. Environ. Contam. Toxicol. 38(2): 324-331.
Ashe, D., J.R. Tomasso, A.G. Eversole and T.I.J. Smith. 1996. Toxicity of ammonia to fingerling white
bass: Effect of selected environments on uptake dynamics. Prog. Fish Cult. 58(4): 277-280.
Augspurger T., F.J. Dwyer, C.G. Ingersoll and C.M. Kane. 2007. Editorial: Advances and opportunities in
assessing the contaminant sensitivity of freshwater mussel early life stages. Environ. Toxicol. Chem.
48
-------
26:2025-2028.
Bader, J.A. and J.M. Grizzle. 1992. Effects of ammonia on growth and survival of recently hatched
channel catfish. J. Aquat. Anim. Health. 4(1): 17-23.
Bailey, H.C., J.R. Elphick, R. Krassoi and A. Lovell. 2001. Joint acute toxicity of diazinon and ammonia
to Ceriodaphnia dubia. Environ. Toxicol. Chem. 20: 2877-2882.
Beamish, F.W.H. and A. Tandler. 1990. Ambient ammonia, diet and growth in lake trout. Aquat. Toxicol.
17: 155-166.
Beketov, M.A. 2002. Ammonia toxicity to larvae of Erythromma najas (Hansemann), Lestes sponsa
(Hansemann) and Sympetrum flaveolum (Linnaeus) (Zygoptera: Coenagrionidae, Lestidae; Anisoptera:
Libellulidae). Odonatologica31(3): 297-304.
Belanger, S.E., D.S. Cherry, J.L. Farris, K.G. Sappington and J.J. Cairns. 1991. Sensitivity of the Asiatic
clam to various biocidal control agents. J. Am. Waterworks Assoc. 83(10): 79-87.
Besser, J.M., C.G. Ingersoll, E.N. Leonard and D.R. Mount. 1998. Effect of zeolite on toxicity of
ammonia in freshwater sediments: Implications for toxicity identification evaluation procedures. Environ.
Toxicol. Chem. 17(11): 2310-2317.
Besser, J.M., D.L. Hardesty, I.E. Greer and C.G. Ingersoll. 2009. Sensitivity of freshwater snails to
aquatic contaminants: Survival and growth of endangered snail species and surrogates in 28-day
exposures to copper, ammonia and pentachlorophenol. Administrative Report (CERC-8335-FY07-20-10),
U.S. Geological Survey, Columbia Environmental Research Center, Columbia, Missouri.
Biesinger, K.E. and G.M. Christensen. 1972. Effects of various metals on survival, growth, reproduction,
and metabolism ofDaphnia magna. J. Fish. Res. Bd. Canada. 29(12): 1691-1700.
Black, M. 2001.Water quality standards for North Carolina's endangered mussels. Department of
Environmental Health Science, Athens, GA.
Blahm, T.H. 1978. Toxicity of chemical fire retardants to juvenile coho salmon and rainbow trout: Ph.D.
Thesis, University of Idaho, Moscow, ID. Available from: Diss. Abstr. Int. B Sci. Eng. 39(9): 4115.
Borgmann, U. 1994. Chronic toxicity of ammonia to the amphipod Hyalella azteca; importance of
ammonium ion and water hardness. Environ. Pollut. 86: 329-335.
Borgmann, U. 1996. Systematic analysis of aqueous ion requirements of Hyalella azteca; A standard
artificial medium including the essential bromide ion. Arch. Environ. Cont. Toxicol. 30:356-363.
Borgmann, U and A.I. Borgmann. 1997. Control of ammonia toxicity to Hyalella azteca by sodium,
potassium and pH. Environ. Pollut. 95(3):325-331.
Broderius, S.J. and L.L. Smith, Jr. 1979. Lethal and sublethal effects of binary mixtures of cyanide and
hexavalent chromium, zinc, or ammonia to the fathead minnow (Pimephales promelas) and rainbow trout
(Salmo gairdneri}. J. Fish. Res. Board Can. 36(2): 164-172.
Broderius, S., R. Drummond, J. Fiandt and C. Russom. 1985. Toxicity of ammonia to early life stages of
the smallmouth bass at four pH values. Environ. Toxicol. Chem. 4(1): 87-96.
49
-------
Buckley, J.A. 1978. Acute toxicity of un-ionized ammonia to fingerling coho salmon. Prog. Fish Cult.
40(1): 30-32.
Buhl, K.J. 2002. The relative toxicity of waterborne inorganic contaminants to the Rio Grande silvery
minnow (Hybognathus amarus) and fathead minnow (Pimephales promelas) in a water quality simulating
that in the Rio Grande, Albuquerque, NM. U.S. Fish and Wildlife Service.
Buhl, K.J. and S.J. Hamilton. 2000. Acute toxicity of fire-control chemicals, nitrogenous chemicals, and
surfactants to rainbow trout. Trans. Am. Fish. Soc. 129(2): 408-418.
Burkhalter, D.E. and C.M. Kaya. 1977. Effects of prolonged exposure to ammonia on fertilized eggs and
sac fry of trout (Salmo gairdneri). Trans. Amer. Fish. Soc. 106: 470-475.
Calamari, D., R. Marchetti and G. Vailati. 1977. Effect of prolonged treatments with ammonia on stages
of development of Salmo gairdneri. Nuovi. Ann. Ig. Microbiol. 28(5): 333-345.
Calamari, D., R. Marchetti and G. Vailati. 1981. Effects of long-term exposure to ammonia on the
developmental stages of rainbow trout (Salmo gairdneri). Rapp. P.-V. Reun. Cons. Int. Explor. Mer. 178:
81-86.
Colt, J. and G. Tchobanoglous. 1976. Evaluation of the short-term toxicity of nitrogenous compounds to
channel catfish, Ictalurus punctatus. Aquaculture 8: 209-224.
Colt, J. and G. Tchobanoglous. 1978. Chronic exposure of channel catfish, Ictalurus punctatus, to
ammonia: Effects on growth and survival. Aquaculture 15: 353-372.
Cowgill, U.M. and D.P. Milazzo. 1991. The response of the three brood Ceriodaphnia test to fifteen
formulations and pure compounds in common use. Arch. Environ. Contam. Toxicol. 21(1): 35-40.
Craig, G.R. and G.L. Beggs. 1979. Evaluation offish loading rates in regulatory static bioassays. Fish
Mar. Serv. Tech. Rep. 862 In: Proceedings of the fifth annual aquatic toxicity workshop, Hamilton,
Ontario, November 7-9, 1978. Wong, P.T.S., P.V. Hodson, A.J. Niimi, V.W. Cairns and U. Borgmann
(Eds.). Great Lakes Biolimnology Laboratory, Canada Centre for Inland Waters, Burlington, Ontario,
Canada, pp. 146-160 (Author Communication Used).
DeGraeve, G.M., R.L. Overcast and H.L. Bergman. 1980. Toxicity of underground coal gasification
condenser water and selected constituents to aquatic biota. Arch. Environ. Contam. Toxicol. 9(5): 543-
555.
DeGraeve, G.M., W.D. Palmer, E.L. Moore, J.J. Coyle and P.L. Markham. 1987. The effect of
temperature on the acute and chronic toxicity of un-ionized ammonia to fathead minnows and channel
catfish. Battelle, Columbus, OH.
Dekker, T., G.D. Greve, T.L. Ter Laak, M.E. Boivin, B. Veuger, G. Gortzak, S. Dumfries, S.M.G.
Lucker, M.H.S. Kraak, W. Admiraal and H.G. van der Geest. 2006. Development and application of a
sediment toxicity test using the benthic cladoceran Chydorus sphaericus. Environ. Poll. 140: 231-238.
Diamond, J.M., D.G. Mackler, W.J. Rasnake and D. Gruber. 1993. Derivation of site-specific ammonia
criteria for an effluent-dominated headwater stream. Environ. Toxicol. Chem. 12(4): 649-658.
Dwyer, F.J., O.K. Hardesty, C.E. Henke, C.G. Ingersoll, D.W. Whites, T. Augspurger, T.J. Canfield, D.R.
50
-------
Mount and F.L. Mayer. 2005. Assessing contaminant sensitivity of endangered and threatened aquatic
species: Part III. Effluent toxicity tests. Arch. Environ. Contam. Toxicol. 48: 174-183.
EA Engineering, S.a.T.I. 1985. Proposed modified effluent limitations for ammonia: Application for a
301(g) demonstration for the Sparrows Point Plant. Bethlehem Steel Corp., Sparrows Point, MD.
El-Shafai, S.A., F.A. El-Gohary, F.A. Nasr, N.P. Vander Steen and H.J. Gijzen. 2004. Chronic ammonia
toxicity to duckweed-fed tilapia (Oreochromis niloticus). Aquaculture 232(1-4): 117-127.
Emerson, K., R.C. Russo, R.E. Lund and R.V. Thurston. 1975. Aqueous ammonia equilibrium
calculations: Effect of pH and temperature. J. Fish. Res. Bd. Can. 32:2379-2383.
Emery, R.M. and E.B. Welch. 1969. The toxicity of alkaline solutions of ammonia to juvenile bluegill
sunfish (Lepomis macrochirus Raf). Tennessee Valley Authority, Division of Health and Safety,
Chattanooga, TN.
Environment Canada - Pacific Environmental Science Centre. 2004. Acute lethality results from 96 hour
LC50 ammonia toxicity testing with rainbow trout. (Oncorhynchus mykiss). North Vancouver, BC,
Canada.
Erickson, R.J. 1985. An evaluation of mathematical models for the effects of pH and temperature on
ammonia toxicity to aquatic organisms. Water Res. 19:1047-1058.
Evans, J.W. 1979. The construction and use of a continuous-flow bioassay apparatus to determine a
preliminary un-ionized ammonia 96-hour LC50 for the crayfish. M.S. Thesis, University of Kansas,
Lawrence, KS.
Fairchild, J.F., A.L. Allert, L.C. Sappington and B. Waddell. 2005. Chronic toxicity of un-ionized
ammonia to early life-stages of endangered Colorado pikeminnow (Ptchocheilus lucius) and razorback
sucker (Xyrauchen texanus) compared to the surrogate fathead minnow (Pimephales promelas). Arch.
Environ. Contam. Toxicol. 49: 378-384.
Fontenot, Q.C., J.J. Isely and J.R. Tomasso. 1998. Acute toxicity of ammonia and nitrite to shortnose
sturgeon fmgerlings. Prog. Fish Cult. 60: 315-318.
Gersich, P.M. and D.L. Hopkins. 1986. Site-specific acute and chronic toxicity of ammonia to Daphnia
magna Straus. Environ. Toxicol. Chem. 5(5): 443-447.
Gerisch, P.M., D.L. Hopkins, S.L. Applegath, C.G. Mendoza, and D.P. Milazzo. 1985. The sensitivity of
chronic end points used in Daphnia magna Straus life-cycle tests. In: Aquatic toxicology and hazard
assessment: Eighth Symposium, Fort Mitchell, KY., USA, Apr. 15-17, 1984. Banner, R C. and D. J.
Hansen (Ed.). ASTM STP 891. American Society for Testing and Materials. Philadelphia, PA. pp. 245-
252.
Goudreau, S.E., R.J. Neves, and R.J. Sheehan. 1993. Effects of wastewater treatment plant effluents on
freshwater mollusks in the upper Clinch River, Virginia, USA. Hydrobiologia 252(3): 211-230.
Gulyas, P. and E. Fleit. 1990. Evaluation of ammonia toxicity on Daphnia magna and some fish species.
Aquacult. Hung. 6: 171-183.
Hampson, B.L. 1977. Relationship between total ammonia and free ammonia in terrestrial and ocean
51
-------
waters. J. Cons. Int. Explor. Mer. 37(2): 117-122.
Harcke, J.E. and H.V. Daniels. 1999. Acute toxicity of ammonia and nitrite to different life stages of
reciprocal cross hybrid striped bass eggs and larvae. Aquaculture 30: 496-500.
Harrahy, E.A., M. Barman, S. Geis, J. Hemming, D. Karner and A. Mager. 2004. Effects of ammonia on
the early life stages of northern pike (Esox Indus). Bull. Environ. Contam. Toxicol. 72: 1290-1296.
Harris, R.R., S. Coley, S. Collins and R. McCabe. 2001. Ammonia uptake and its effects on
ionoregulation in the freshwater crayfish Pacifastacus Leniusculus (Dana). J. Comp. Physiol. B. 171:
681-693.
Hasan, M.R. and D.J. Macintosh. 1986. Acute toxicity of ammonia to common carp fry. Aquaculture
54(1-2): 97-107.
Hazel, C.R., W. Thomsen and S.J. Meith. 1971. Sensitivity of striped bass and stickleback to ammonia in
relation to temperature and salinity. Calif. Fish Game. 57(3): 138-153.
Hazel, R.H., C.E. Burkhead and D.G. Huggins. 1979. The development of water quality criteria for
ammonia and total residual chlorine for the protection of aquatic life in two Johnson County, Kansas
streams. Project completion report for period July 1977 to September 1979. Kansas Water Resources
Research Institute, University of Kansas.
Hickey, C.W. and M.L. Vickers. 1994. Toxicity of ammonia to nine native New Zealand freshwater
invertebrate species. Arch. Environ. Contam. Toxicol. 26(3): 292-298.
Holt, G.J. and S.A. Malcolm. 1979. Evaluation offish loading rates in regulatory static bioassays. Tech.
Rep. Fish. Mar. Serv. (Can.). 862: 146-160.
Ingersoll, C. 2004. Data call for the national consultation on the Clean Water Act 304(a) aquatic life
criteria for ammonia, cyanide, chromium III, and chromium VI. U.S. Geological Survey. Columbia, MO.
(Memorandum to G. Noguchi, U.S. Fish and Wildlife Service, Arlington, VA. July 20.)
Ip, Y.K., A.S.L. Tay, K.H. Lee and S.F. Chew. 2004. Strategies for surviving high concentrations of
environmental ammonia in the swamp eel Monopterus albus. Physiol. Biochem. Zool. 77: 390-405.
Jofre, M.B. and W.H. Karasov. 1999. Direct effect of ammonia on three species of North American
anuran amphibians. Environ. Toxicol. Chem. 18(8): 1806-1812.
Jude, D.J. 1973. Sublethal effects of ammonia and cadmium on growth of green sunfish (Lepomis
cyanellus). Ph.D. Thesis, Michigan Department of Fish and Wildlife, Michigan State University, East
Lansing, MI.
Keller, A.E. 2000. Memorandum to Rob Pepin. Subject: Water quality and toxicity data for unpublished
unionid mussels tests.
Knoph, M.B. 1992. Acute toxicity of ammonia to Atlantic salmon (Salmo salar) parr. Comp. Biochem.
Physiol. Comp. Pharmacol. Toxicol. 10(2): 275-282.
Koch, D.L., E.L. Lider and S.C. Vigg. 1980. Evaluation of the combined effects of ammonia, nitrite and
' ' OO "
nitrate on the egg incubation, hatching and fry development of Lahontan cutthroat trout (Salmo clarki
52
-------
Henshawi). University of Nevada. Desert Research Institute.
Kumar, N.J. and K.P. Krishnamoorthi. 1983. Evaluation of toxicity of ammoniacal fertiliser effluents.
Environ. Pollut. Ser. A. 30(1): 77-86.
Lubinski, K.S., R.E. Sparks and L.A. Jahn. 1974. The development of toxicity indices for assessing the
quality of the Illinois River. WRC Research Report No. 96, University of Illinois, Water Resources
Center, Urbana, IL.
Mallet, M.J. and I. Sims. 1994. Effects of ammonia on the early life stages of carp (Cyprinus carpio) and
roach (Rutilus rutilus). In: Sublethal and chronic effects of pollutants on freshwater fish. Muller, R. and
R. Lloyd (Eds.), Fishing News Books, London, pp. 211-228.
Manning, T.M., S.P. Wilson and J.C. Chapman. 1996. Toxicity of chlorine and other chlorinated
compounds to some Australian aquatic organisms. Bull. Environ. Contam. Toxicol. 56(6): 971-976.
Markle, P.J., J.R Gully, R.B. Baird, K.M. Nakada and J.P. Bottomley. 2000. Effects of several variables
on whole effluent toxicity test performance and interpretation. Environ. Toxicol. Chem. 19: 123-132.
Mayes, M.A., H.C. Alexander, D.L. Hopkins and P.B. Latvaitis. 1986. Acute and chronic toxicity of
ammonia to freshwater fish: A site-specific study. Environ. Toxicol. Chem. 5(5): 437-442.
McCormick, J.H., S.J. Broderius and J.T. Findt. 1984. Toxicity of ammonia to early life stages of the
green sunfish Lepomis cyanellus (with erratum). Environ. Pollut. Series A 36: 147-163.
McKim, J.M. 1977. Evaluation of tests with early life stages offish for predicting long-term toxicity. J.
Fish. Res. Bd. Canada. 34:1148-1154.
Meyer, J.S. and J.A. Hansen. 2002. Subchronic toxicity of low dissolved oxygen concentrations, elevated
pH, and elevated ammonia concentrations to Lost River suckers. Trans. Amer. Fish. Soc. 131: 656-666.
Monda, D.P., D.L. Galat, S.E. Finger and M.S. Kaiser. 1995. Acute toxicity of ammonia (NH3-N) in
sewage effluent to Chironomus riparius: II. Using a generalized linear model. Arch. Environ. Contam.
Toxicol. 28(3): 385-390.
Mount, D.I. 1982. Ammonia toxicity tests with Ceriodaphnia acanthina and Simocephalus vetulus. U.S.
EPA, Duluth, MN. (Letter to RC. Russo, U.S. EPA, Duluth, MN.)
Mummert, A.K., R.J. Neves, T.J. Newcomb and D.S. Cherry. 2003. Sensitivity of juvenile freshwater
mussels (Lampsilis fasciola, Villosa iris) to total and un-ionized ammonia. Environ. Toxicol. Chem. 22:
2545-2553.
Myers-Kinzie, M. 1998. Factors affecting survival and recruitment of unionid mussels in small
midwestern streams. Purdue University, West Lafayette, IN.
Neves, R. 2004. Propagation of endangered freshwater mussels in North America. J Conchol. Spec.
Public. 3:69-80.
Newton, T.J. and M.R. Bartsch. 2007. Lethal and sublethal effects of ammonia to juvenile lampsilis
mussels (Unionidae) in sediment and water-only exposures. Environ. Toxicol. and Chem. 26(10):2057-
2065.
53
-------
Newton, T.J., J.W. Allran, J.A. O'Donnell, M.R. Bartsch and W.B. Richardson. 2003. Effects of ammonia
on juvenile unionid mussels (Lampsilis cardium) in laboratory sediment toxicity tests. Environ. Toxicol.
Chem. 22(10): 2554-2560.
Nimmo, D.W.R., D. Link, L.P. Parrish, G.J. Rodriguez, W. Wuerthele and P.H. Davies. 1989.
Comparison of on-site and laboratory toxicity tests: Derivation of site-specific criteria for un-ionized
ammonia in a Colorado transitional stream. Environ. Toxicol. Chem. 8(12): 1177-1189.
Oppenborn, J.B. and C.A. Goudie. 1993. Acute and sublethal effects of ammonia on striped bass and
hybrid striped bass. J. World Aquacult. Soc. 24(1): 90-101.
Parkhurst, B.R., A.S. Bradshaw, J.L. Forte and G.P. Wright. 1979. An evaluation of the acute toxicity to
aquatic biota of a coal conversion effluent and its major components. Bull. Environ. Contam. Toxicol.
23(3): 349-356.
Parkhurst, B.R., J.S. Meyer, G.M. DeGraeve and H.L. Bergman. 1981. Reevaluation of the toxicity of
coal conversion process waters. Bull. Environ. Contam. Toxicol. 26(1): 9-15.
Prenter, J., C. MacNeil, J.T.A. Dick, G.E. Riddell and A.M. Dunn. 2004. Lethal and sublethal toxicity of
ammonia to native, invasive, and parasitised freshwater amphipods. Wat. Res. 38: 2847-2850.
Qureshi, A.A., K.W. Flood, S.R Thompson, S.M. Janhurst, C.S. Inniss and D.A. Rokosh. 1982.
Comparison of a luminescent bacterial test with other bioassays for determining toxicity of pure
compounds and complex effluents. In: Aquatic toxicology and hazard assessment, 5th conference.
Pearson, J.G., R.B. Foster and W.E. Bishop (Eds.). ASTM STP 766. American Society for Testing and
Materials, Philadelphia, PA. pp. 179-195.
Rani, E.F., M. Elumalal and M.P. Balasubramanian. 1998. Toxic and sublethal effects of ammonium
chloride on a freshwater fish Oreochromis mossambicus. Water Air Soil Pollut. 104:1-8.
Rankin, D.P. 1979. The influence of un-ionized ammonia on the long-term survival of sockeye salmon
eggs. Fisheries and Marine Service Technical Report No. 912. Pacific Biological Station, Nanaimo, B.C.,
Canada.
Rao, T.S., M.S. Rao and S.B.S.K. Prasad. 1975. Median tolerance limits of some chemicals to the fresh
water fish Cyprinus carpio. Indian J. Environ. Health 17(2): 140-146.
Reinbold, K.A. and S.M. Pescitelli. 1982a. Effects of exposure to ammonia on sensitive life stages of
aquatic organisms. Project Report, Contract No. 68-01-5832, Illinois Natural History Survey, Champaign,
IL.
Reinbold, K.A. and S.M. Pescitelli. 1982b. Effects of cold temperature on toxicity of ammonia to rainbow
trout, bluegills and fathead minnows. Project Report, Contract No. 68-01-5832. Illinois Natural History
Survey, Champaign, IL.
Reinbold, K.A. and S.M. Pescitelli. 1982c. Acute toxicity of ammonia to the white sucker. Final Report to
the U.S. EPA, Contract No. 2W-3946 NAEX, Illinois Natural History Survey, Champaign, IL.
Reinbold, K.A. and S.M. Pescitelli. 1982d. Acute toxicity of ammonia to channel catfish. Final report to
the U.S. EPA, Contract No. J 2482 NAEX. Illinois Natural History Survey, Champaign, IL.
54
-------
Rice, S.D. and J.E. Bailey. 1980. Survival, size and emergence of pink salmon, Oncorhynchus gorbuscha,
alevins after short and long-term exposures to ammonia. Fish. Bull. 78(3): 641-648.
Robinson-Wilson, E.F. and W.K. Seim. 1975. The lethal and sublethal effects of a zirconium process
effluent on juvenile salmonids. Water Resour. Bull. 11(5): 975-986.
Rosage, T.F., R.M. Schutsky and K.M. Rapp. 1979. Toxicity of un-ionized ammonia to the spotfin shiner
(Notropis spilopterus). Proc. Pa. Acad. Sci. 53: 39-42.
Roseboom, D.P. and D.L. Richey. 1977. Acute toxicity of residual chlorine and ammonia to some native
Illinois fishes. Report of Investigations 85. U.S. NTIS PB-170871. Office of Water Research and
Technology, Washington, B.C.
Rubin, A.J. and M.A. Elmaraghy. 1976. Studies on the toxicity of ammonia, nitrate and their mixtures to
the common guppy. Water Resource Center Report No.490. U.S. NTIS PB-255721 Ohio State
University, Columbus, OH.
Russo, R.C. 1985. Ammonia, nitrite, and nitrate. In: Fundamentals of aquatic toxicology and chemistry.
Rand, G.M. and S.R. Petrocelli (Eds.). Hemisphere Publishing Corp., Washington, D.C. pp. 455-471.
Russo, R.C., A. Pilli and E.L. Meyn. 1985. Memorandum to N.A. Jaworski. March 1985.
Sadler, K. 1981. The toxicity of ammonia to the European eel (Anguilla anguilla L.). Aquaculture 26(1-
2): 173-181.
Saiki, M.K., D.P. Monda and B.L. Bellerud. 1999. Lethal levels of selected water quality variables to
larval and juvenile Lost River and shortnose suckers. Environ. Pollut. 105(1): 37-44.
Sarda, N. 1994. Spatial and temporal heterogeneity in sediments with respect to pore water ammonia and
toxicity of ammonia to Ceriodaphnia dubia and Hyalella azteca. MS Thesis. Wright State University,
Dayton, OH.
Scheller, J.L. 1997. The effect of dieoffs of Asian clams (Corbicula fluminea) on native freshwater
mussels (unionidae). Virginia Polytechnic Institute and State University, Blacksburg, VA.
Schubauer-Berigan, M.K., P.O. Monson, C.W. West and G.T. Ankley. 1995. Influence of pH on the
toxicity of ammonia to Chironomus tentans and Lumbriculus variegatus. Environ. Toxicol. Chem. 14:
713-717.
Schuytema, G.S. and A.V. Nebeker. 1999a. Comparative effects of ammonium and nitrate compounds on
Pacific treefrog and African clawed frog embryos. Arch. Envion. Contain. Toxicol. 36: 200-206.
Schuytema, G.S. and A.V. Nebeker. 1999b. Comparative toxicity of ammonium and nitrate compounds to
Pacific treefrog and African clawed frog tadpoles. Environ. Toxicol. Chem. 18(10): 2251-2257.
Servizi, J. and R. Gordon. 1990. Acute lethal toxicity of ammonia and suspended sediment mixtures to
chinook salmon (Oncorhynchus tshawytschd). Bull. Environ. Contain. Toxicol. 44(4):650-656.
Smith, M.E., J.M. Lazorchak, L.E. Herrin, S. Brewer-Swartz, and W.T. Thoeny. 1997. A reformulated,
reconstituted water for testing the freshwater amphipod, Hyalella azteca. Environ. Toxicol. Chem.
16(6): 1229-1233.
55
-------
Smith, W.E., T.H. Roush and J.T. Fiandt. 1984. Toxicity of ammonia to early life stages of bluegill
(Lepomis macrochirus). Internal Report 600/X-84-175. Environmental Research Laboratory-Duluth,
U.S.EPA, Duluth, MN.
Soderberg, R.W. and J.W. Meade. 1992. Effects of sodium and calcium on acute toxicity of un-ionized
ammonia to Atlantic salmon and lake trout. J. Appl. Aquacult. 1(4): 82-92.
Solbe, J.F.D. and D.G. Shurben. 1989. Toxicity of ammonia to early life stages of rainbow trout (Salmo
gairdneri). Water Res. 23(1): 127-129.
Soucek, D.J. 2007. Comparison of hardness- and chloride-regulated acute effects of sodium sulfate on
two freshwater crustaceans. Environ. Toxicol. Chem. 26(4):773-779.
Sparks, R.E. 1975. The acute, lethal effects of ammonia on channel catfish (Ictalurus punctatus), bluegills
(Lepomis macrochirus) and fathead minnows (Pimephales promelas). Report to Illinois, Project No.
20.060. Institute for Environmental Quality, Chicago, IL.
Sparks, R.E. and M.J. Sandusky. 1981. Identification of factors responsible for decreased production of
fish food organisms in the Illinois and Mississippi Rivers. Final Report Project No. 3-291-R. Illinois
Natural History Survey, River Research Laboratory, Havana, IL.
Stammer, H.A. 1953. The effect of hydrogen sulfide and ammonia on characteristic animal forms in the
saprobiotic system (Der einfly von schwefelwasserstoff und ammoniak auf tierische leitformen des
sparobiensystems). Vom Wasser. 20: 34-71.
Stephan, C.E. and J.W. Rogers. 1985. Advantages of using regression analysis to calculate results of
chronic toxicity tests. In: Aquatic toxicology and hazard assessment: Eighth Symposium. R.C. Bahner
and D.J. Hansen, Eds. ASTM STP 891. American Society for Testing and Materials, Philadelphia, PA.
pp. 328-338.
Stephan, C.E., D.I. Mount, D.J. Hansen, J.H. Genile, G.A. Chapman, and W. A. Brungs. 1985. Guidelines
for deriving numerical national water quality criteria for the protection of aquatic organisms and their
uses. PB85-227049. National Technical Information Service, Springfield, VA.
Stevenson, T.J. 1977. The effects of ammonia, pH and salinity on the white perch, Morone americana.
Ph.D. thesis. University of Rhode Island, Kingston, RI. Available from: Diss. Abstr. Int. B Sci. Eng.
39(1): 35 (Author Communication Used).
Strayer D.L., J.A. Downing, W.R. Haag, T.L. King, J.B. Layzer, T.J. Newton and S.J. Nichols. 2004.
Changing perspectives on pearly mussels, North America's most imperiled species. BioScience. 54:429-
439.
Swigert, J.P. and A. Spacie. 1983. Survival and growth of warmwater fishes exposed to ammonia under
low-flow conditions. Technical Report 157. Purdue University, Water Resource Research Center, West
Lafayette, IN.
Thurston, R.V. 1981. Memorandum to R.C. Russo. November 16, 1981.
Thurston, R.V. 1988. Ammonia toxicity to fishes. In: Fish physiology, fish toxicology, and fisheries
management: Proceedings of an International Symposium, Guangzhou, PRC. EPA/600/9-90/01, pp. 183-
196.
56
-------
Thurston, R.V. and E.L. Meyn. 1984. Acute toxicity of ammonia to five fish species from the northwest
United States. Technical Report No.84-4. Fisheries Bioassay Laboratory, Montana State University,
Bozeman, MT.
Thurston, R.V. and R.C. Russo. 1981. Acute toxicity of ammonia to golden trout (Salmo aguabonita) and
mottled sculpin (Coitus bairdf). Technical Report No. 81-1. Fisheries Bioassay Laboratory, Montana
State University, Bozeman, MT.
Thurston, R.V. and R.C. Russo. 1983. Acute toxicity of ammonia to rainbow trout. Trans. Am. Fish. Soc.
112: 696-704.
Thurston, R.V., R.C. Russo and C.E. Smith. 1978. Acute toxicity of ammonia and nitrite to cutthroat trout
fry. Trans. Am. Fish. Soc. 107(2): 361-368.
Thurston, R.V., C. Chakoumakos and R.C. Russo. 198 la. Effect of fluctuating exposures on the acute
toxicity of ammonia to rainbow trout (Salmo gairdneri) and cutthroat trout (S. clarki). Water Res. 15(7):
911-917.
Thurston, R.V., G.R. Phillips, R.C. Russo and S.M. Hinkins. 1981b. Increased toxicity of ammonia to
rainbow trout (Salmo gairdneri) resulting from reduced concentrations of dissolved oxygen. Can. J. Fish.
Aquat. Sci. 38(8): 983-988.
Thurston, R.V., R.C. Russo and G.A. Vinogradov. 198 Ic. Ammonia toxicity to fishes: Effect of pH on
the toxicity of the un-ionized ammonia species. Environ. Sci. Technol. 15(7): 837-840.
Thurston, R.V., R.C. Russo and G.R. Phillips. 1983. Acute toxicity of ammonia to fathead minnows.
Trans. Am. Fish. Soc. 112(5): 705-711.
Thurston, R.V., R.C. Russo, R.J. Luedtke, C.E. Smith, E.L. Meyn, C. Chakoumakos, K.C. Wang and
C.J.D. Brown. 1984a. Chronic toxicity of ammonia to rainbow trout. Trans. Am. Fish. Soc. 113(1): 56-73.
Thurston, R.V., R.J. Luedtke and R.C. Russo. 1984b. Toxicity of ammonia to freshwater insects of three
families. Technical Report No. 84-2. Fisheries Bioassay Laboratory, Montana State University, Bozeman,
MT.
Thurston, R.V., R.C. Russo, E.L. Meyn, R.K. Zajdel and C.E. Smith. 1986. Chronic toxicity of ammonia
to fathead minnows. Trans. Am. Fish. Soc. 115(2): 196-207.
Tietge, J.E., G.T. Ankley, D.L. DeFoe, G.W. Holcombe and K.M. Jensen. 2000. Effects of water quality
on development ofXenopus laevis: A frog embryo teratogenesis assay-Xenopus assessment of surface
water associated with malformations in native anurans. Environ. Toxicol. Chem. 19(8): 2114-2121.
Tiffany, M.A., J.W. Winchester and R.H. Loucks. 1969. Natural and pollution sources of iodine, bromine,
and chlorine in the Great Lakes. J. Wat. Pollut. Cont. Fed. 41(7): 1319-1329.
Tomasso, J. and G. Carmichael. 1986. Acute toxicity of ammonia, nitrite, and nitrate to the Guadalupe
bass,Micropterus treculi. Bull. Environ. Contam. Toxicol. 36(6): 866-870.
United States Environmental Protection Agency. 1985. Ambient water quality criteria for ammonia -
1984. EPA-440/5-85-001. National Technical Information Service, Springfield, VA.
57
-------
United States Environmental Protection Agency. 1989. Ambient Water Quality Criteria for Ammonia
(Saltwater) - 1989. EPA 440/5-88-004. National Technical Information Service, Springfield, VA.
United States Environmental Protection Agency. 1991. Technical support document for water quality-
based toxics control. EPA/505/2-90-001. National Technical Information Service, Springfield, VA.
United States Environmental Protection Agency. 1998. 1998 Update of ambient water quality criteria for
ammonia. EPA-822-R-98-008. National Technical Information Service, Springfield, VA.
United States Environmental Protection Agency. 1999. 1999 Update of ambient water quality criteria for
ammonia. EPA-822-R-99-014. National Technical Information Service, Springfield, VA.
Wade, D., J. Posey and D.J. Simbeck. 1992. Definitive evaluation of Wheeler Reservoir sediments
toxicity using juvenile freshwater mussels (Andodonta imbecillis Say). TVA/WR-92/25. Tennessee
Valley Authority, Water Resources Division.
Wallen, I.E., W.C. Greer and R. Lasater. 1957. Toxicity to Gambusia affinis of certain pure chemicals in
turbid waters. Sewage Ind. Wastes. 29: 695-711.
Wang, N., C.G. Ingersoll, O.K. Hardesty, I.E. Greer, D.J. Hardesty, C.D. Ivey, J.L. Kunz, W.G.
Brumbaugh, F.J. Dwyer, A.D. Roberts, J.T. Augspurger, C.M. Kane, R.J. Neves and M.C. Barnhart.
2007a. Contaminant sensitivity of freshwater mussels: Chronic toxicity of copper and ammonia to
juvenile freshwater mussels (Unionidae). Environ. Toxicol. Chem. 26(10):2048-2056.
Wang, N., C.G. Ingersoll, O.K. Hardesty, C.D. Ivey, J.L. Kunz, T.W. May, F.J. Dwyer, A.D. Roberts, T.
Augspurger, C.M. Kane, R.J. Neves and M.C. Barnhart. 2007b. Contaminant sensitivity of freshwater
mussels: Acute toxicity of copper, ammonia, and chlorine to glochidia and juveniles of freshwater
mussels (Unionidae). Environ. Toxicol. Chem. 26(10):2036-2047.
Wang, N., J.T. Augspurger, M.C. Barnhart, J.R Bidwell, WG. Cope, F.J. Dwyer, S. Geis, I.E. Greer,
C.G. Ingersoll, C.M. Kane, T.W. May, RJ. Neves, T.J. Newton, A.D. Roberts and D.W. Whites. 2007c.
Contaminant sensitivity of freshwater mussels: Intra- and inter-laboratory variability in acute toxicity tests
with glochidia and juveniles of freshwater mussels (Unionidae). Environ. Toxicol. Chem. 26(10):2029-
2035.
Wang, N., RJ. Erickson, C.G. Ingersoll, C.D. Ivey, E.L. Brunson, T. Augspurger and M.C. Barnhart.
2008. Influence of pH on the acute toxicity of ammonia to juvenile freshwater mussels (Fatmucket,
Lampsilis siliquoidea). Environ. Toxicol. Chem. 27:1141-1146.
Weirich, C.R., J.R. Tomasso and T.I.J. Smith. 1993. Toxicity of ammonia and nitrite to sunshine bass in
selected environments. J. Aquat. Anim. Health 5(1): 64-72.
West, C.W. 1985. Acute toxicity of ammonia to 14 freshwater species. Internal Report. U.S. EPA,
Environmental Research Laboratory, Duluth, MN.
Whiteman, F.W., G.T. Ankley, M.D. Kahl, D.M. Rau and M.D. Balcer. 1996. Evaluation of interstitial
water as a route of exposure for ammonia in sediment tests with benthic macroinvertebrates. Environ.
Toxicol. Chem. 15(5): 794-801.
Whitfield, M. 1974. The hydrolysis of ammonium ions in sea water- atheoretical study. J. Mar. Biol.
Assoc. U.K. 54:565-580.
58
-------
Wicks, B.J. and D.J. Randall. 2002. The effect of feeding and fasting on ammonia toxicity in juvenile
rainbow trout, Oncorhynchus mykiss. Aquat. Toxicol. 59(1-2): 71-82.
Wicks, B.J., R. Joensen, Q. Tang and D.J. Randall. 2002. Swimming and ammonia toxicity in salmonids:
The effect of sub-lethal ammonia exposure on the swimming performance of coho salmon and the acute
toxicity of ammonia in swimming and resting rainbow trout. Aquat. Toxicol. 59(1-2): 55-69.
Williams, K.A., D.W.J. Green and D. Pascoe. 1986. Studies on the acute toxicity of pollutants to
freshwater macroinvertebrates. 3. Ammonia. Arch. Hydrobiol. 106(1): 61-70.
Williams, J. D., M.L. Warren, K.S. Cummins, J.L. Harris and R.J. Neves. 1993. Conservation status of
freshwater mussels of the United States and Canada. Fisheries. 18:6-22.
Williams, J.D. and RJ. Neves. 1995. Freshwater musssels: A neglected and declining aquatic
resource. Pages 177-199 In: in E.T. LaRoe, G.S. Farris, C.E. Puckett, P.O. Doran, and MJ.
Mac, editors. Our Living Resources. National Biological Service, Washington, DC. xi, 530 pp.
Willingham, T. 1987. Acute and short-term chronic ammonia toxicity to fathead minnows (Pimephales
promelas) and Ceriodaphnia dubia using laboratory dilution water and Lake Mead dilution water. U.S.
EPA, Denver, CO.
Wilson, E.F. 1974. The lethal and sub-lethal effects of a zirconium process effluent on juvenile
salmonids. Ph.D. thesis. Oregon State University, Corvallis, OR.
Wood, C.M. 1993. Ammonia and urea metabolism and excretion. In: The physiology of fishes. Evans,
D.H. (Ed.). CRC Press, Ann Arbor, MI. pp 379-424.
Zhao, I.H., T.I. Lam and I. Guo. 1997. Acute toxicity of ammonia to the early stage-larvae and juveniles
of Eriocheir sinensis H. Milne-Edwards, 1853 (Decapoda: Grapsidae) reared in the laboratory. Aquacult.
Res. 28: 514-525.
59
-------
Figure 1. Ranked Freshwater Genus Mean Acute Values (GMAVs) with Criterion Maximum
Concentrations (CMCs).
_ 1000 q
<0
Q)
4-1
!_
Q>
IO
04
T3
C
S
CO
Q.
IS
D)
0
100 :
m -
IU -
* Freshwater Unionid Mussel
O Other Freshwater Mollusks
Q Freshwater Invertebrates
• Freshwater Fish
A Freshwater Amphibian
*D
DD
1999 CMC salmonids absent = 8.4 mg N/L
1999 CMC salmonids present = 5.6 mg N/L
New CMC (freshwater mussels absent) = 5.0 mg N/L
New CMC (freshwater mussels present) = 2.9 mg N/L
I I I I I I I I I I
0.0 0.1 0.2 0.3 0.4 0.5 0.6 0.7 0.8 0.9 1.0
Ranked Genera
60
-------
Figure 2. Ranked Freshwater Genus Mean Chronic Values (GMCVs) with Criterion Continuous
Concentrations (CCCs).
% 100 3
2
.a
0>
4->
1_
0
>
c
O
0
tf)
CM
eo
II
o>
O
§
O
10 :
1 :
0.1
•ff Freshwater Unionid Mussel
O Other Freshwater Mollusks
D Freshwater Invertebrates
• Freshwater Fish
O value is <2.26 mg NIL
value is <0.98mg NIL
value is <0.34 mg NIL
D
D
1999 CCC = 1.2 mg H/L
New CCC (freshw ater mussels present) = 0.26 mg N/L
I I I I I I I I I I
0.0 0.1 0.2 0.3 0.4 0.5 0.6 0.7 0.8 0.9 1.0
Ranked Genera
61
-------
Figure 3. CMC Extrapolated Across a Temperature Gradient at pH=8.
Extrapolated CMC Across a Temperature Gradient at pH=8
12
10
U
•a
ai
_
o
a.
re
S 4
•+M
' -M
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
Temperature °C
f +M = Mussels Present, -M = Mussels Absent
Figure 4. CCC Extrapolated Across a Temperature Gradient at pH=8.
Extrapolated CCC Across a Temperature Gradient at pH=8
—-M,-ELS
.. -M, +ELS
«+M,± ELS
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
Temperature °C
t -M, -ELS = Mussels Absent, Fish ELS Absent; -M, +ELS = Mussels Absent, Fish ELS Present; +M, ±ELS
Mussels Present, Fish ELS Present or Absent
62
-------
Table 1. Acute Toxicity of Ammonia to Aquatic Invertebrates and Vertebrates
Species
Chemical Name
Duration
Methods
pH
Temp
(°C)
Total Ammonia
(mg N/L)
Total Ammonia3
(mg N/L)
at pH=8 and 25°C
SMAV
(mg N/L)
GMAV
(mg N/L)
Reference
Freshwater Invertebrates
Flatworm,
Dendrocoelum lacteum
Oligochaete, worm,
Lumbriculus variegatus
Oligochaete, worm,
Lumbriculus variegatus
Oligochaete, worm (10-25 mm),
Lumbriculus variegatus
Oligochaete, worm (adult),
Lumbriculus variegatus
Oligochaete, worm (adult),
Lumbriculus variegatus
Oligochaete, worm (adult),
Lumbriculus variegatus
Oligochaete, worm (adult),
Lumbriculus variegatus
Tubificid worm (30-40 mm),
Limnodrilus hoffmeisteri
Tubificid worm, Oligochaete,
Tubifex tubifex
Snail (3.6mm),
Potamopyrgus antipodarum
Snail (2-3 mm),
Potamopyrgus antipodarum
Snail (2-3 mm),
Potamopyrgus antipodarum
Snail (2-3 mm),
Potamopyrgus antipodarum
Snail (2-3 mm),
Potamopyrgus antipodarum
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
S,U
S,M
S,M
R,M
F,M
F,M
F,M
F,M
F,M
S,U
R,U
R,M
R,M
R,M
R,M
8.2
7.56
6.69
8.2
6.5
6.5
8.1
8.1
7.9
8.2
8.3
7.6
8.2
8.2
8.2
18
23
23
15
25
25
25
25
11.5
12
20.4
15
20
25
15
22.37
286.0
302.0
13.66
100.0
200.0
34.00
43.50
96.62
66.67
26.77
23.67
4.727
4.081
8.711
18.37
112.21
47.86
8.75
17.21
34.42
41.12
52.61
26.17
33.30
32.59
5.098
4.583
5.988
5.579
18.37
33.64
26.17
33.30
7.605
18.37
33.64
26.17
33.30
7.605
Stammer 1953
Besseretal. 1998
Besseretal. 1998
Hickey and Vickers 1994
Schubauer-Berigan et al. 1995
Schubauer-Berigan et al. 1995
Schubauer-Berigan et al. 1995
Schubauer-Berigan et al. 1995
Williams et al. 1986
Stammer 1953
Alonso and Camargo 2003
Hickey and Vickers 19 94
Hickey and Vickers 1994
Hickey and Vickers 1994
Hickey and Vickers 1994
63
-------
Table 1. (continued)
Species
Snail (adult),
Pleurocera unciale
Great pond snail (25-30 mm),
Lymnaea stagnalis
Ramshorn snail,
Helisoma trivolvis
Ramshorn snail,
Helisoma trivolvis
Pouch snail,
Physa gyrina
Pouch snail,
Physa gyrina
Pouch snail,
Physa gyrina
Pouch snail,
Physa gyrina
Pouch snail,
Physa gyrina
Pouch snail,
Physa gyrina
Pleasantshell (juvenile),
Actinonaias pectorosa
Pleasantshell (juvenile),
Actinonaias pectorosa
Oyster mussel,
Epioblasma capsaeformis
Oyster mussel (Newly-transformed
juveniles),
Epioblasma capsaeformis
Pink mucket (2 mo old juveniles),
Lampsilis abrupta
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
R,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
S,M
S,M
S,M
R,M
R,M
pH
8.1
7.9
7.9
8.2
8
8.2
8.1
8.2
8
8
7.90
7.95
8.3
8.3
8.3
Temp
fC)
22
11.5
22
12.9
4
5.5
12.1
12.8
13.3
24.9
25
25
20
20
20
Total
Ammonia
(mg N/L)
11.18
50.33
47.73
63.73
114.9
85.13
76.29
50.25
62.39
26.33
14.06
14.08
5.700
4.610
1.860
Total
Ammonia3
(mgN/L)
at pH=8 and
25°C
10.54
13.63
30.87
34.30
20.15
24.81
31.67
26.82
23.64
26.10
11.66
12.81
6.712
5.430
2.191
SMAV
(mg
N/L)
10.54
13.63
32.54
25.29
12.22
6.037
2.191
GMAV
(mg
N/L)
10.54
13.63
32.54
25.29
12.22
6.037
Reference
Goudreau et al. 1993
Williams et al. 1986
Arthur etal. 1987
Arthur etal. 1987
Arthur etal. 1987
Arthur etal. 1987
Arthur etal. 1987
Arthur etal. 1987
Arthur etal. 1987
Arthur etal. 1987
Keller 2000
Keller 2000
Ingersoll 2004
Wang et al. 2007b
Wang et al. 2007b
64
-------
Table 1. (continued)
Species
Plain pocketbook (juvenile),
Lampsilis cardium
Plain pocketbook (juvenile),
Lampsilis cardium
Plain pocketbook
(1 -2 d old juvenile),
Lampsilis cardium
Plain pocketbook
(1 -2 d old juvenile),
Lampsilis cardium
Wavy-rayed lampmussel
(6 -d juvenile),
Lampsilis fasciola
Wavy-rayed lampmussel
(juvenile),
Lampsilis fasciola
Wavy-rayed lampmussel (Newly-
transformed juveniles),
Lampsilis fasciola
Higgin's eye (1-2 d old juvenile),
Lampsilis higginsii
Higgin's eye (1-2 d old juvenile),
Lampsilis higginsii
Neosho mucket (4-d juvenile),
Lampsilis rafinesqueana
Neosho mucket (Newly-
transformed juveniles),
Lampsilis rafinesqueana
Fatmucket (Newly-transformed
juveniles),
Lampsilis siliquoidea
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
S,M
S,M
F,M
F,M
S,M
R,M
R,M
F,M
F,M
S,M
R,M
R,M
pH
8.2
8.2
7.6
7.1
8.3
7.83
8.3
7.6
7.1
8.3
8.3
8.3
Temp
(°C)
20.5
21.2
21.2
21.2
20
12.6
20
21.2
21.2
20
20
20
Total
Ammonia
(mgN/L)
23.50
23.70
23.10
38.90
7.400
14.90
5.987
19.50
31.70
11.00
8.900
8.090
Total
Ammonia3
(mgN/L)
at pH=8 and
25°C
23.75
25.38
8.101
7.298
8.714
3.893
7.049
6.860
5.692
12.95
10.48
9.526
SMAV
(mg
N/L)
7.689
6.207
6.249
11.65
GMAV
(mg
N/L)
Reference
Newton et al. 2003
Newton et al. 2003
Newton and Bartsch 2007
Newton and Bartsch 2007
Ingersoll 2004
Mummert et al. 2003
Wang et al. 2007b
Newton and Bartsch 2007
Newton and Bartsch 2007
Ingersoll 2004
Wang et al. 2007b
Wang et al. 2007b
65
-------
Table 1. (continued)
Species
Fatmucket (juvenile),
Lampsilis siliquoidea
Fatmucket (2 mo old juveniles),
Lampsilis siliquoidea
Fatmucket (10 d old juvenile),
Lampsilis siliquoidea
Fatmucket (10 d old juvenile),
Lampsilis siliquoidea
Fatmucket (10 d old juvenile),
Lampsilis siliquoidea
Fatmucket (10 d old juvenile),
Lampsilis siliquoidea
Fatmucket (10 d old juvenile),
Lampsilis siliquoidea
Fatmucket (10 d old juvenile),
Lampsilis siliquoidea
Green floater (juvenile),
Lasmigona subviridus
Green floater (juvenile),
Lasmigona subviridus
Giant floater mussel (adult),
Pyganodon grandis
Giant floater mussel (adult),
Pyganodon grandis
Pondshell mussel (8-day old
juvenile),
Utterbackia imbecillis
Pondshell mussel (juvenile),
Utterbackia imbecillis
Pondshell mussel (juvenile),
Utterbackia imbecillis
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride,
ammonium hydroxide
Ammonium chloride,
ammonium hydroxide
Ammonium chloride,
ammonium hydroxide
Ammonium chloride,
ammonium hydroxide
Ammonium chloride,
ammonium hydroxide
Ammonium chloride,
ammonium hydroxide
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
S,M
R,M
F,M
F,M
F,M
F,M
F,M
F,M
R,M
R,M
S,M
S,M
R,M
R,M
R,M
pH
8.3
8.3
7.6
8.1
8.5
9
6.6
8.1
7.73
7.92
8
8
7.8
8.16
8.17
Temp
(°C)
24
20
20
20
20
20
20
20
24
24.8
25
25
24
25
25
Total
Ammonia
(mgN/L)
1.275
3.964
11.00
5.200
3.400
0.9600
88.00
11.00
6.613
3.969
18.84
25.13
14.29
5.254
5.781
Total
Ammonia3
(mgN/L)
at pH=8 and
25°C
2.092
4.668
3.586
4.155
5.893
4.026
10.43
8.789
3.728
3.360
18.84
25.13
9.104
7.134
8.003
SMAV
(mg
N/L)
5.646
3.539
21.76
GMAV
(mg
N/L)
5.919
3.539
21.76
Reference
Myers-Kinzie 1998
Wang et al. 2007b
Wang et al. 2008
Wang et al. 2008
Wang et al. 2008
Wang et al. 2008
Wang et al. 2008
Wang et al. 2008
Black 2001
Black 2001
Schellerl997
Schellerl997
Wadeetal. 1992
Black 2001
Black 2001
66
-------
Table 1. (continued)
Species
Pondshell mussel (juvenile),
Utterbackia imbecillis
Pondshell mussel (juvenile),
Utterbackia imbecillis
Pondshell mussel (juvenile),
Utterbackia imbecillis
Pondshell mussel (juvenile),
Utterbackia imbecillis
Pondshell mussel (juvenile),
Utterbackia imbecillis
Rainbow mussel (Newly-
transformed juveniles),
Villosa iris
Rainbow mussel (Newly-
transformed juveniles),
Villosa iris
Rainbow mussel (juvenile),
Villosa iris
Rainbow mussel (juvenile),
Villosa iris
Rainbow mussel (juvenile),
Villosa iris
Rainbow mussel (2 mo old
juveniles),
Villosa iris
Rainbow mussel (2 mo old
juveniles),
Villosa iris
Asian clam (juv., Iwk),
Corbiculafluminea
Asian clam (juv., Iwk),
Corbiculafluminea
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
R,M
R,M
S,M
S,M
S,M
R,M
R,M
S,M
S,M
S,M
R,M
R,M
S,M
S,M
pH
8.29
8
7.9
8.35
7.9
7.3
8.3
8.3
8
8
8.3
8.3
8
8
Temp
(°C)
25
25.1
24
25
25
12.5
20
20
25
25
20
20
25
25
Total
Ammonia
(mgN/L)
8.845
2.734
8.235
3.269
9.355
20.60
5.100
3.000
7.070
7.810
2.427
8.899
1.000
1.780
Total
Ammonia3
(mgN/L)
at pH=8 and
25°C
15.46
2.755
6.287
6.422
7.760
2.343
6.002
3.533
7.070
7.810
2.858
10.48
1.000
1.780
SMAV
(mg
N/L)
7.164
5.036
GMAV
(mg
N/L)
7.164
5.036
Reference
Black 2001
Black 2001
Keller 2000
Keller2000
Keller2000
Mummert et al. 2003
Wang et al. 2007b
Ingersoll 2004
Schellerl997
Schellerl997
Wang et al. 2007b
Wang et al. 2007b
Schellerl997
Schellerl997
67
-------
Table 1. (continued)
Species
Asian clam (juv., <48 h),
Corbicula fluminea
Asiatic clam (12.0-25.0 mm SL),
Corbicula fluminea
Asiatic clam (5.0-8.5 mm SL),
Corbicula fluminea
Long fingernail clam,
Musculium transversum
Long fingernail clam,
Musculium transversum
Long fingernail clam,
Musculium transversum
Water flea,
Ceriodaphnia acanthina
Water flea,
Ceriodaphnia dubia
Water flea,
Ceriodaphnia dubia
Water flea,
Ceriodaphnia dubia
Water flea,
Ceriodaphnia dubia
Water flea,
Ceriodaphnia dubia
Water flea (<24hrs),
Ceriodaphnia dubia
Water flea (<24hrs),
Ceriodaphnia dubia
Water flea (<24hrs),
Ceriodaphnia dubia
Water flea (<24hrs),
Ceriodaphnia dubia
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium hydroxide
Ammonium sulfate
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4.1 d
4.2 d
4d
4d
4d
2d
2d
2d
2d
2d
2d
2d
2d
2d
2d
Methods
S,M
F,M
F,M
F,M
F,M
F,M
F,M
S,M
R,M
R,NR
R,M
R,M
S,M
S,M
S,M
S,M
pH
8
8.05
8.05
8.1
8.2
8.6
7.06
8.08
8.4
7.4
7.8
8.2
8.02
7.5
7.5
8.16
Temp
(°C)
25
29.4
30.3
14.6
5.4
20.5
24
24.75
26.4
23
25
7
24.8
25
25
22
Total
Ammonia
(mgN/L)
2.250
6.316
2.125
32.83
38.18
6.429
104.8
15.60
7.412
48.59
33.98
16.65
21.265
47.05
56.84
24.77
Total
Ammonia3
(mgN/L)
at pH=8 and
25°C
2.250
9.996
3.623
16.76
11.03
14.03
23.73
17.61
18.01
15.06
23.52
5.494
21.71
19.88
24.01
26.23
SMAV
(mg
N/L)
6.018
13.74
23.73
GMAV
(mg
N/L)
6.018
13.74
Reference
Schellerl997
Belanger et al. 1991
Belanger et al. 1991
Arthur etal. 1987
Arthur etal. 1987
Arthur etal. 1987
Mount 1982
Andersen and Buckley 1998
Cowgill and Milazzo 1991
Manning et al. 1996
Nimmoetal. 1989
Nimmoetal. 1989
Andersen and Buckley 1998
Bailey etal. 2001
Bailey etal. 2001
Black 2001
68
-------
Table 1. (continued)
Species
Water flea (<24hrs),
Ceriodaphnia dubia
Water flea (<24hrs),
Ceriodaphnia dubia
Water flea,
Ceriodaphnia dubia
Water flea,
Ceriodaphnia dubia
Water flea (<24hrs),
Ceriodaphnia dubia
Water flea (<24 hrs),
Chydorus sphaericus
Water flea,
Daphnia magna
Water flea,
Daphnia magna
Water flea,
Daphnia magna
Water flea,
Daphnia magna
Water flea,
Daphnia magna
Water flea,
Daphnia magna
Water flea,
Daphnia magna
Water flea,
Daphnia magna
Water flea,
Daphnia magna
Water flea,
Daphnia magna
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
2d
2d
2d
2d
2d
4d
2d
2d
2d
2d
2d
2d
2d
2d
2d
2d
Methods
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
R,U
S,M
S,M
S,M
S,M
S,M
S,M
pH
8.4
8.4
7.85
7.85
8
8
8.5
7.92
8.2
8.34
8.07
7.51
7.53
7.50
7.40
8.09
Temp
(°C)
23
23
23
23
25
20
20
21
25.0
19.7
19.6
20.1
20.1
20.3
20.6
20.9
Total
Ammonia
(mgN/L)
28.06
32.63
28.65
28.77
14.52
37.88
26.34
9.463
20.71
51.92
51.09
48.32
55.41
43.52
42.31
41.51
Total
Ammonia3
(mgN/L)
at pH=8 and
25°C
51.45
59.83
18.38
18.45
14.52
25.01
45.66
5.792
30.38
64.46
37.28
13.80
16.32
12.46
10.75
35.06
SMAV
(mg
N/L)
20.64
25.01
GMAV
(mg
N/L)
22.13
25.01
Reference
Black 2001
Black 2001
Sardal994
Sardal994
Schellerl997
Dekker et al. 2006
Gersich and Hopkins 1986
Gulyas and Fleit 1990
Parkhurst et al. 1979,1981
Reinbold and Pescitelli 1982a
Russoetal. 1985
Russoetal. 1985
Russoetal. 1985
Russoetal. 1985
Russoetal. 1985
Russoetal. 1985
69
-------
Table 1. (continued)
Species
Water flea,
Daphnia magna
Water flea,
Daphnia magna
Water flea,
Daphnia magna
Water flea,
Daphnia pulicaria
Water flea (adult),
Simocephalus vetulus
Water flea (adult),
Simocephalus vetulus
Water flea,
Simocephalus vetulus
Water flea,
Simocephalus vetulus
Aquatic sowbug,
Asellus racovitzai
Aquatic sowbug (adult),
Asellus racovitzai
Aquatic sowbug,
Asellus racovitzai
Amphipod (4-6 mm),
Crangonyx pseudogracilis
Amphipod,
Crangonyx pseudogracilis
Amphipod,
Crangonyx pseudogracilis
Amphipod,
Crangonyx pseudogracilis
Amphipod,
Crangonyx pseudogracilis
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
2d
2d
2d
2d
2d
2d
2d
2d
4d
4d
d
4d
4d
4d
4d
4d
Methods
S,M
S,M
S,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
S,U
F,M
F,M
F,M
F,M
pH
7.95
8.15
8.04
8.05
8.3
8.1
7.25
7.06
7.8
8
7.5
8
8
8
8
Temp
(°C)
22
22
22.8
14
17
20.4
24.5
24
22
4
12
4
12.1
13.3
24.9
Total
Ammonia
(mgN/L)
51.30
37.44
38.70
34.50
31.58
21.36
83.51
83.51
148.8
357.8
176.0
43.36
199.5
216.0
115.3
25.10
Total
Ammonia3
(mgN/L)
at pH=8 and
25°C
36.40
38.88
34.77
15.23
29.00
17.64
24.15
18.90
80.34
62.72
41.87
6.24
34.97
74.09
43.70
24.88
SMAV
(mg
N/L)
24.25
15.23
21.98
59.53
GMAV
(mg
N/L)
19.22
21.98
59.53
Reference
Russoetal. 1985
Russoetal. 1985
Russoetal. 1985
DeGraeve et al. 1980
Arthur etal. 1987
Arthur etal. 1987
Mount 1982
Mount 1982
Arthur etal. 1987
Arthur etal. 1987
Thurston et al. 1983
Prenter et al. 2004
Arthur etal. 1987
Arthur etal. 1987
Arthur etal. 1987
Arthur etal. 1987
70
-------
Table 1. (continued)
Species
Amphipod,
Crangonyx pseudogracilis
Amphipod (13 d),
Crangonyx sp.
Amphipod (8-42 d),
Crangonyx sp.
Crayfish,
Orconectes immunis
Crayfish (adult),
Orconectes immunis
Crayfish (2.78 cm),
Orconectes nais
Crayfish (Adult Intermoult),
Pacifastacus leniusculus
Red swamp crayfish (2.1 cm),
Procambarus clarkii
Red swamp crayfish (<2.5 cm),
Procambarus clarkii
Chinese mitten crab (juvenile),
Eriocheir sinensis
Mayfly,
Callibaetis skokianus
Mayfly,
Callibaetis skokianus
Mayfly (middle to late instar),
Callibaetis sp.
Mayfly (middle to late instar),
Drunella grandis
Mayfly (middle to late instar),
Drunella grandis
Mayfly (middle to late instar),
Drunella grandis
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
2d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
R,M
F,M
F,M
F,M
F,M
F,M
F,M
pH
8.2
8
8
7.9
8.2
8.3
8.2
8
8
7.81
7.7
7.9
7.81
7.84
7.84
7.85
Temp
(°C)
13
12
20
17.1
4.6
26.5
15
20
12
22
10.8
13.3
11.9
12.8
13.2
12
Total
Ammonia
(mgN/L)
81.60
79.23
19.83
488.1
999.4
23.15
88.20
26.08
76.92
31.60
263.6
211.7
107.8
259.1
195.6
319.0
Total
Ammonia3
(mgN/L)
at pH=8 and
25°C
44.28
26.96
13.09
210.3
270.3
46.73
56.49
17.22
26.17
14.30
47.26
66.56
25.64
70.07
54.69
82.22
SMAV
(mg
N/L)
41.61
18.79
238.4
46.73
56.49
21.23
14.30
56.09
25.64
68.05
GMAV
(mg
N/L)
27.96
105.6
56.49
21.23
14.30
37.92
68.05
Reference
Arthur etal. 1987
Diamond etal. 1993
Diamond etal. 1993
Arthur etal. 1987
Arthur etal. 1987
Evans 1979
Harris etal. 2001
Diamond etal. 1993
Diamond etal. 1993
Zhao etal. 1997
Arthur etal. 1987
Arthur etal. 1987
Thurston et al. 1984b
Thurston et al. 1984b
Thurston et al. 1984b
Thurston et al. 1984b
71
-------
Table 1. (continued)
Species
Dragonfly (< 233 d),
Pachydiplax longipennis
Dragonfly (<140 d),
Pachydiplax longipennis
Damselfly (8-10 mm),
Enallagma sp.
Insect (8th- 1 Oth instar),
Erythromma najas
Insect (8th- 10th instar),
Erythromma najas
Insect (8th- 10th instar),
Erythromma najas
Stonefly, Little golden stonefly
(middle to late instar),
Skwala americana
Stonefly, Little golden stonefly
(middle to late instar),
Skwala americana
Beetle,
Stenelmis sexlineata
Caddisfly,
Philarctus quaeris
Caddisfly,
Philarctus quaeris
Midge (10-d (2-3 instar)),
Chironomus riparius
Midge,
Chironomus tentans
Midge,
Chironomus tentans
Midge (2nd instar),
Chironomus tentans
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonia
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonia
Ammonia
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
F,M
F,M
F,M
R,U
R,U
R,U
F,M
F,M
F,M
F,M
F,M
R,M
S,M
S,M
F,M
pH
8
8
7.9
7.5
8.7
9.1
7.81
7.76
8.7
7.8
7.8
7.7
6.69
7.56
6.5
Temp
(°C)
12
20
11.5
25
25
25
13.1
13.8
25
21.9
13.3
21.7
23
23
25
Total
Ammonia
(mgN/L)
76.92
74.37
93.10
589.0
168.0
49.20
109.3
119.6
29.70
296.5
561.7
357.7
430.0
564.0
371.0
Total
Ammonia3
(mgN/L)
at pH=8 and
25°C
26.17
49.11
25.22
248.8
640.4
363.1
28.72
30.50
113.2
158.7
147.4
158.3
68.14
221.3
63.85
SMAV
(mg
N/L)
35.85
25.22
386.8
29.60
113.2
153.0
158.3
GMAV
(mg
N/L)
35.85
25.22
386.8
29.60
113.2
153.0
Reference
Diamond etal. 1993
Diamond etal. 1993
Williams et al. 1986
Beketov 2002
Beketov 2002
Beketov 2002
Thurston et al. 1984b
Thurston et al. 1984b
Hazel etal. 1979
Arthur etal. 1987
Arthur etal. 1987
Mondaetal. 1995
Besseretal. 1998
Besseretal. 1998
Schubauer-Berigan et al. 1995
72
-------
Table 1. (continued)
Species
Midge (2nd instar),
Chironomus tentans
Midge (2nd instar),
Chironomus tentans
Midge (2nd instar),
Chironomus tentans
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4d
4d
Methods
F,M
F,M
F,M
pH
8.1
6.5
8.1
Temp
(°C)
25
25
25
Total
Ammonia
(mgN/L)
78.10
368.0
50.50
Total
Ammonia3
(mgN/L)
at pH=8 and
25°C
94.45
63.33
61.07
SMAV
(mg
N/L)
69.49
GMAV
(mg
N/L)
104.9
Reference
Schubauer-Berigan et al. 1995
Schubauer-Berigan et al. 1995
Schubauer-Berigan et al. 1995
Table 1. (continued)
Species
Chemical Name
Duration
Methods
pH
TempfC)
Total
Ammonia
(mg N/L)
Total
Ammonia1"
(mg N/L)
at pH=8
SMAV
(mg
N/L)
GMAV
(mg
N/L)
Reference
Freshwater Vertebrates
Common eel (0.20 g),
Anguilla anguilla
Common eel (2.8 g),
Anguilla anguilla
Swamp eel (200-250g),
Monopterus albus
Golden trout (0.09 g, 24 cm),
Oncorhynchus aguabonita
Cutthroat trout (3. 6 g),
Oncorhynchus clarki
Cutthroat trout (3. 6 g),
Oncorhynchus clarki
Cutthroat trout (4.1 g),
Oncorhynchus clarki
Cutthroat trout (4.1 g),
Oncorhynchus clarki
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
4d
4d
4d
4d
4d
4d
4d
4d
F,M
F,M
R,M
F,M
F,M
F,M
F,M
F,M
7.5
7.5
7
8.06
7.7
7.7
7.7
7.7
23
23
28
13.2
10
10
10
10
110.6
136.6
3478
23.30
17.30
29.10
19.30
26.30
46.73C
57.73C
809.6
26.10
10.07
16.93
11.23
15.30
51.94
809.6
26.10
51.94
809.6
Sadler 1981
Sadler 1981
Ip et al. 2004
Thurston and Russo 1981
Thurstonetall981a
Thurston etal 198 la
Thurston etal 198 la
Thurston etal 198 la
73
-------
Table 1. (continued)
Species
Cutthroat trout (3. 4 g),
Oncorhynchus clarki
Cutthroat trout (3. 3 g),
Oncorhynchus clarki
Cutthroat trout (l.Og),
Oncorhynchus clarki
Cutthroat trout (l.Og),
Oncorhynchus clarki
Pink salmon (late alevins),
Oncorhynchus gorbuscha
Pink salmon (fry),
Oncorhynchus gorbuscha
Coho salmon,
Oncorhynchus kisutch
Coho salmon,
Oncorhynchus kisutch
Coho salmon,
Oncorhynchus kisutch
Coho salmon,
Oncorhynchus kisutch
Coho salmon,
Oncorhynchus kisutch
Coho salmon,
Oncorhynchus kisutch
Coho salmon,
Oncorhynchus kisutch
Coho salmon (6 g),
Oncorhynchus kisutch
Coho salmon,
Oncorhynchus kisutch
Coho salmon,
Oncorhynchus kisutch
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium sulfate
Ammonium sulfate
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
F,M
F,M
F,M
F,M
S,M
S,M
F,U
F,U
F,U
F,U
F,U
F,U
F,U
F,M
F,M
F,M
pH
7.78
7.8
7.8
7.81
6.4
6.4
7
7
7.5
7.5
8
8
8.5
8.1
7
7
TempfC)
12.2
12.4
12.8
13.1
4.3
4.3
15
15
15
15
15
15
15
17.2
15
15
Total
Ammonia
(mg N/L)
32.57
36.55
37.75
43.72
230.5
211.1
81.96
84.43
50.68
52.80
21.64
21.98
9.090
11.59
82.02
84.43
Total
Ammonia1"
(mg N/L)
at pH=8
21.76
25.30
26.13
30.81
38.33
46.18
19.08
19.66
21.41
22.30
21.64
21.98
23.85
14.02
19.10
19.66
SMAV
(mg
N/L)
18.37
42.07
GMAV
(mg
N/L)
Reference
Thurstonetal 1978
Thurstonetal 1978
Thurstonetal 1978
Thurstonetal 1978
Rice and Bailey 1980
Rice and Bailey 1980
Wilson. 1974
Wilson. 1974
Wilson. 1974
Wilson. 1974
Wilson. 1974
Wilson. 1974
Wilson. 1974
Buckley 1978
Robinson- Wilson and Seim
1975
Robinson- Wilson and Seim
1975
74
-------
Table 1. (continued)
Species
Coho salmon,
Oncorhynchus kisutch
Coho salmon,
Oncorhynchus kisutch
Coho salmon,
Oncorhynchus kisutch
Coho salmon,
Oncorhynchus kisutch
Coho salmon,
Oncorhynchus kisutch
Rainbow trout (0.5-3.0 g),
Oncorhynchus mykiss
Rainbow trout (McConaughy
strain, 251 mg),
Oncorhynchus mykiss
Rainbow trout (0. 80 g),
Oncorhynchus mykiss
Rainbow trout (0.60 g),
Oncorhynchus mykiss
Rainbow trout (0.63 g),
Oncorhynchus mykiss
Rainbow trout (0. 80 g),
Oncorhynchus mykiss
Rainbow trout (0. 80 g),
Oncorhynchus mykiss
Rainbow trout (0. 90 g),
Oncorhynchus mykiss
Rainbow trout (2.01 g),
Oncorhynchus mykiss
Rainbow trout (1.30 g),
Oncorhynchus mykiss
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium sulfate
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
F,M
F,M
F,M
F,M
F,M
S,U
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
pH
7.5
7.5
8
8
8.5
7.95
6.84
6.95
6.97
7.02
7.02
7.03
7.18
7.45
7.47
TempfC)
15
15
15
15
15
15
12
14.7
14.5
15.4
14.6
15.1
15.1
15.1
14.7
Total
Ammonia
(mg N/L)
50.65
52.76
21.63
22.00
9.093
51.06
112.0
163.6
144.0
146.7
159.0
156.6
141.6
104.4
72.65
Total
Ammonia1"
(mg N/L)
at pH=8
21.40
22.29
21.63
22.00
23.86
46.46
23.02
36.52
32.67
34.77
37.68
37.45
39.39
40.99
29.36
SMAV
(mg
N/L)
20.27
GMAV
(mg
N/L)
Reference
Robinson- Wilson and Seim
1975
Robinson- Wilson and Seim
1975
Robinson- Wilson and Seim
1975
Robinson- Wilson and Seim
1975
Robinson- Wilson and Seim
1975
Qureshietal. 1982
Buhl and Hamilton 2000
Environment Canada 2004
Environment Canada 2004
Environment Canada 2004
Environment Canada 2004
Environment Canada 2004
Environment Canada 2004
Environment Canada 2004
Environment Canada 2004
75
-------
Table 1. (continued)
Species
Rainbow trout (0.78 g),
Oncorhynchus mykiss
Rainbow trout (0.40 g),
Oncorhynchus mykiss
Rainbow trout (1 .64 g),
Oncorhynchus mykiss
Rainbow trout,
Oncorhynchus mykiss
Rainbow trout (1 . 1 3 g),
Oncorhynchus mykiss
Rainbow trout (1 .50 g),
Oncorhynchus mykiss
Rainbow trout (1 .38 g),
Oncorhynchus mykiss
Rainbow trout (0. 90 g),
Oncorhynchus mykiss
Rainbow trout (1. 00 g),
Oncorhynchus mykiss
Rainbow trout (1.30 g),
Oncorhynchus mykiss
Rainbow trout (1 .26 g),
Oncorhynchus mykiss
Rainbow trout (1 .60 g),
Oncorhynchus mykiss
Rainbow trout (1 .30 g),
Oncorhynchus mykiss
Rainbow trout (1.11 g),
Oncorhynchus mykiss
Rainbow trout (1 .40 g),
Oncorhynchus mykiss
Rainbow trout (0. 90 g),
Oncorhynchus mykiss
Chemical Name
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
pH
7.47
7.51
7.54
7.55
7.59
7.87
7.93
7.97
7.98
8.03
8.04
8.34
8.39
8.4
8.44
8.46
TempfC)
14.5
14.2
14.6
15
13.9
15.1
15.2
15.2
15.1
14.9
14.3
15.3
15.3
14.9
14.7
14.5
Total
Ammonia
(mg N/L)
79.67
73.71
75.30
34.23
59.40
42.90
41.15
36.17
35.29
23.03
25.84
19.15
12.05
12.84
14.41
11.82
Total
Ammonia1"
(mg N/L)
at pH=8
32.20
31.61
33.81
15.61
28.84
33.68
36.08
33.85
33.97
24.36
27.86
36.89
25.58
27.79
33.69
28.72
SMAV
(mg
N/L)
GMAV
(mg
N/L)
Reference
Environment Canada 2004
Environment Canada 2004
Environment Canada 2004
Craig and Beggs 1979
Environment Canada 2004
Environment Canada 2004
Environment Canada 2004
Environment Canada 2004
Environment Canada 2004
Environment Canada 2004
Environment Canada 2004
Environment Canada 2004
Environment Canada 2004
Environment Canada 2004
Environment Canada 2004
Environment Canada 2004
76
-------
Table 1. (continued)
Species
Rainbow trout (1 .26 g),
Oncorhynchus mykiss
Rainbow trout (1 .01 g),
Oncorhynchus mykiss
Rainbow trout (1 .44 g),
Oncorhynchus mykiss
Rainbow trout (1. 42 g),
Oncorhynchus mykiss
Rainbow trout,
Oncorhynchus mykiss
Rainbow trout (129 mm),
Oncorhynchus mykiss
Rainbow trout (1.7-1.9 cm),
Oncorhynchus mykiss
Rainbow trout,
Oncorhynchus mykiss
Rainbow trout (Stage 11,8-10
cm),
Oncorhynchus mykiss
Rainbow trout (129 mm),
Oncorhynchus mykiss
Rainbow trout (10. 9 g),
Oncorhynchus mykiss
Rainbow trout (14.0 g),
Oncorhynchus mykiss
Rainbow trout (22.4 g),
Oncorhynchus mykiss
Rainbow trout (10.3 g),
Oncorhynchus mykiss
Rainbow trout (3.3 g),
Oncorhynchus mykiss
Chemical Name
Phosphoric acid,
Diammonium salt
Ammonium chloride
Ammonium chloride
Ammonium chloride
Phosphoric acid,
Diammonium salt
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
S,M
S,M
S,M
S,M
S,M
F,U
F,U
F,U
F,U
F,U
F,M
F,M
F,M
F,M
F,M
pH
8.47
8.93
8.93
9.46
7.5
7
7.4
7.4
7.4
8
7.7
7.7
7.9
7.9
8.3
TempfC)
14.3
14.2
15
14.6
15.0
15
14.5
14.5
14.5
15
3.6
9.8
16.2
11.3
18.7
Total
Ammonia
(mg N/L)
17.20
4.800
5.400
1.600
38.37
207.5
20.03
46.31
55.07
70.00
38.52
55.15
15.23
30.15
12.75
Total
Ammonia1"
(mg N/L)
at pH=8
42.60
27.24
30.65
18.40
16.21
48.32
7.33
16.94
20.15
70.00
22.41
32.09
12.63
25.01
22.72
SMAV
(mg
N/L)
GMAV
(mg
N/L)
Reference
Environment Canada 2004
Environment Canada 2004
Environment Canada 2004
Environment Canada 2004
Holt and Malcolm 1 979
Blahml978
Calamari et al. 1981
Calamari et al. 1981
Calamari et al. 1981
Blahml978
Arthur etal. 1987
Arthur etal. 1987
Arthur etal. 1987
Arthur etal. 1987
Arthur etal. 1987
77
-------
Table 1. (continued)
Species
Rainbow trout (53 mm, 1 .48 g),
Oncorhynchus mykiss
Rainbow trout (Stage 8),
Oncorhynchus mykiss
Rainbow trout,
Oncorhynchus mykiss
Rainbow trout (45(35-55) mm,
0.86(0. 32-1. 75) g),
Oncorhynchus mykiss
Rainbow trout (1 19(95-145)
mm, 20. 6(10.0-32.6) g),
Oncorhynchus mykiss
Rainbow trout (115(103-134)
mm, 18. 1(10.0-32.6) g),
Oncorhynchus mykiss
Rainbow trout (42(32-50) mm,
0.61(0.23-1. 03) g),
Oncorhynchus mykiss
Rainbow trout (52(33-5 1 ) mm,
1. 47(0.26-1.3 l)g),
Oncorhynchus mykiss
Rainbow trout (44(37-65) mm,
0. 76(0.41-3.07) g),
Oncorhynchus mykiss
Rainbow trout (6. 3 g, 8.1 cm),
Oncorhynchus mykiss
Rainbow trout (8.0 g, 8.9 cm),
Oncorhynchus mykiss
Rainbow trout (2 9. 8 g, 13.1 cm),
Oncorhynchus mykiss
Rainbow trout (28.0 g, 13.1 cm),
Oncorhynchus mykiss
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
pH
7.95
7.4
8.05
8.16
8.28
8.34
8.43
8.5
8.6
7.44
7.5
7.59
7.6
TempfC)
10
14.4
14
14.2
12.8
5
3
14.9
3.3
12.8
14.5
12.7
13
Total
Ammonia
(mg N/L)
35.14
40.99
22.90
23.39
15.40
17.32
11.86
10.09
15.27
32.49
24.20
32.62
23.80
Total
Ammonia1"
(mg N/L)
at pH=8
31.97
14.99
25.17
31.76
26.40
33.37
27.20
26.47
48.40
12.57
10.22
15.84
11.74
SMAV
(mg
N/L)
GMAV
(mg
N/L)
Reference
Broderius and Smith Jr. 1979
Calamari et al. 1977
DeGraeve et al. 1980
Reinbold and Pescitelli 1982b
Reinbold and Pescitelli 1982b
Reinbold and Pescitelli 1982b
Reinbold and Pescitelli 1982b
Reinbold and Pescitelli 1982b
Reinbold and Pescitelli 1982b
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
78
-------
Table 1. (continued)
Species
Rainbow trout (24.5 g, 12.7 cm),
Oncorhynchus mykiss
Rainbow trout (2596 g, 57.0
cm),
Oncorhynchus mykiss
Rainbow trout (15.1 g, 10.7 cm),
Oncorhynchus mykiss
Rainbowtrout (29.6 g, 13.3 cm),
Oncorhynchus mykiss
Rainbow trout (1496 g, 48.5
cm),
Oncorhynchus mykiss
Rainbow trout (1 8.9 g, 1 1 .6 cm),
Oncorhynchus mykiss
Rainbowtrout (558 g, 37.0 cm),
Oncorhynchus mykiss
Rainbowtrout (1698 g, 50.9
cm),
Oncorhynchus mykiss
Rainbowtrout (22.8 g, 12.3 cm),
Oncorhynchus mykiss
Rainbow trout (12. 3 g, 10.2 cm),
Oncorhynchus mykiss
Rainbowtrout (513 g, 35.9 cm),
Oncorhynchus mykiss
Rainbowtrout (22.6 g, 12.3 cm),
Oncorhynchus mykiss
Rainbowtrout (26.0 g, 13.0 cm),
Oncorhynchus mykiss
Rainbowtrout (14.8 g, 10.5 cm),
Oncorhynchus mykiss
Rainbowtrout (38.0 g, 14.4 cm),
Oncorhynchus mykiss
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
pH
7.6
7.62
7.62
7.63
7.64
7.64
7.64
7.65
7.65
7.65
7.66
7.66
7.66
7.67
7.68
TempfC)
12.9
7.9
14.4
12.9
9.8
13.1
10
9.8
13.2
14.3
9.8
13.6
12.8
14
13
Total
Ammonia
(mg N/L)
25.14
20.53
28.62
25.65
25.82
29.28
31.85
19.46
28.64
29.02
25.95
28.27
33.97
27.30
33.15
Total
Ammonia1"
(mg N/L)
at pH=8
12.40
10.46
14.58
13.28
13.59
15.41
16.77
10.41
15.33
15.53
14.12
15.38
18.48
15.10
18.65
SMAV
(mg
N/L)
GMAV
(mg
N/L)
Reference
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
79
-------
Table 1. (continued)
Species
Rainbow trout (1 122 g, 45.6
cm),
Oncorhynchus mykiss
Rainbow trout (1 140 g, 46.4
cm),
Oncorhynchus mykiss
Rainbowtrout (152 g, 23.4 cm),
Oncorhynchus mykiss
Rainbowtrout (23.6 g, 13.2 cm),
Oncorhynchus mykiss
Rainbowtrout (9.5 g, 9.4 cm),
Oncorhynchus mykiss
Rainbowtrout (4.3 g, 7.1 cm),
Oncorhynchus mykiss
Rainbowtrout (4.0 g, 7.0 cm),
Oncorhynchus mykiss
Rainbowtrout (248 g, 25.2 cm),
Oncorhynchus mykiss
Rainbowtrout (25.8 g, 13.6 cm),
Oncorhynchus mykiss
Rainbow trout (8.1 g, 9.3 cm),
Oncorhynchus mykiss
Rainbowtrout (380 g, 32.4 cm),
Oncorhynchus mykiss
Rainbowtrout (42.0 g, 16.0 cm),
Oncorhynchus mykiss
Rainbow trout (1 .7 g, 5.7 cm),
Oncorhynchus mykiss
Rainbow trout (1 1 .2 g, 10.0 cm),
Oncorhynchus mykiss
Rainbowtrout (5.7 g, 8.4 cm),
Oncorhynchus mykiss
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
pH
7.69
7.69
7.69
7.69
7.9
7.71
7.71
7.74
7.75
7.75
7.76
7.77
7.79
7.8
7.8
TempfC)
10.4
10.7
10.7
13.4
12.7
11.5
11.4
10.4
11.8
12.3
10
13.6
12.4
9.7
13.3
Total
Ammonia
(mg N/L)
17.75
20.18
25.62
27.51
20.03
30.22
32.02
25.76
31.53
33.94
22.44
31.81
41.97
23.65
42.02
Total
Ammonia1"
(mg N/L)
at pH=8
10.16
11.55
14.66
15.74
16.61
17.89
18.95
16.05
19.99
21.52
14.48
20.89
28.54
16.37
29.09
SMAV
(mg
N/L)
GMAV
(mg
N/L)
Reference
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
80
-------
Table 1. (continued)
Species
Rainbow trout (2.3 g, 6.1 cm),
Oncorhynchus mykiss
Rainbow trout (8.0 g, 9.5 cm),
Oncorhynchus mykiss
Rainbow trout (4.6 g, 7.4 cm),
Oncorhynchus mykiss
Rainbow trout (6.7 g, 8.6 cm),
Oncorhynchus mykiss
Rainbow trout (9.0 g, 9.3 cm),
Oncorhynchus mykiss
Rainbow trout (1 .8 g, 5.7 cm),
Oncorhynchus mykiss
Rainbow trout (4.3 g, 7.1 cm),
Oncorhynchus mykiss
Rainbow trout (0.47 g, 4.0 cm),
Oncorhynchus mykiss
Rainbow trout (2.5 g, 6.0 cm),
Oncorhynchus mykiss
Rainbow trout (0.61 g, 4.3 cm),
Oncorhynchus mykiss
Rainbow trout (1 .02 g, 4.9 cm),
Oncorhynchus mykiss
Rainbow trout (9.4 g, 9.6 cm),
Oncorhynchus mykiss
Rainbow trout (0.33 g, 3.6 cm),
Oncorhynchus mykiss
Rainbow trout (0.33 g, 3.6 cm),
Oncorhynchus mykiss
Rainbow trout (0.47 g, 4.0 cm),
Oncorhynchus mykiss
Rainbow trout (1 .7 g, 5.8 cm),
Oncorhynchus mykiss
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
pH
7.8
7.82
7.83
7.84
7.84
7.84
7.84
7.85
7.85
7.85
7.85
7.85
7.86
7.86
7.86
7.86
TempfC)
12.4
13.2
13.5
12.2
12.9
13.8
13
12.5
13.1
13.1
12.3
16.1
13
13.4
12.7
14.1
Total
Ammonia
(mg N/L)
47.87
33.67
33.55
24.54
32.30
33.09
38.69
29.77
31.55
33.59
33.99
34.17
20.70
23.71
28.77
34.95
Total
Ammonia1"
(mg N/L)
at pH=8
33.14
24.15
24.50
18.25
24.02
24.61
28.77
22.54
23.89
25.43
25.73
25.87
15.96
18.28
22.18
26.95
SMAV
(mg
N/L)
GMAV
(mg
N/L)
Reference
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
81
-------
Table 1. (continued)
Species
Rainbowtrout (48.6 g, 15.2 cm),
Oncorhynchus mykiss
Rainbow trout (0. 1 5 g, 2.7 cm),
Oncorhynchus mykiss
Rainbow trout (0. 1 8 g, 2.9 cm),
Oncorhynchus mykiss
Rainbowtrout (0.23 g, 3.2 cm),
Oncorhynchus mykiss
Rainbowtrout (7.0 g, 8.8 cm),
Oncorhynchus mykiss
Rainbow trout (0. 1 8 g, 2.9 cm),
Oncorhynchus mykiss
Rainbowtrout (2.6 g, 6.2 cm),
Oncorhynchus mykiss
Rainbow trout (11.1 g, 9.9 cm),
Oncorhynchus mykiss
Rainbowtrout (0.12 g, 2.4 cm),
Oncorhynchus mykiss
Rainbowtrout (0.14 g, 2.6 cm),
Oncorhynchus mykiss
Rainbowtrout (0.23 g, 3.2 cm),
Oncorhynchus mykiss
Rainbowtrout (52.1 g, 15.5 cm),
Oncorhynchus mykiss
Rainbowtrout (1.8 g, 5.9 cm),
Oncorhynchus mykiss
Rainbow trout (0.06 g, 1 .7 cm),
Oncorhynchus mykiss
Rainbow trout (0.06 g, 1 .7 cm),
Oncorhynchus mykiss
Rainbowtrout (7.9 g, 9.2 cm),
Oncorhynchus mykiss
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium sulfate
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
pH
7.86
7.87
7.87
7.87
7.87
7.87
7.87
7.87
7.88
7.88
7.88
7.88
7.89
7.9
7.7
7.9
TempfC)
10.2
12.9
12.9
13.1
12.2
13
12.1
13
12.8
12.9
13.4
10
12.4
13.4
13.9
11.9
Total
Ammonia
(mg N/L)
35.31
16.81
18.99
19.08
20.02
21.15
31.80
34.32
11.07
15.91
19.43
28.60
36.73
19.44
28.54
22.65
Total
Ammonia1"
(mg N/L)
at pH=8
27.22
13.20
14.91
14.98
15.72
16.61
24.97
26.95
8.85
12.72
15.54
22.87
29.91
16.12
16.61
18.79
SMAV
(mg
N/L)
GMAV
(mg
N/L)
Reference
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
82
-------
Table 1. (continued)
Species
Rainbow trout (9.7 g, 9.7 cm),
Oncorhynchus mykiss
Rainbow trout (9.3 g, 9.0 cm),
Oncorhynchus mykiss
Rainbow trout (0.08 g, 2.0 cm),
Oncorhynchus mykiss
Rainbow trout (0.06 g, 1 .7 cm),
Oncorhynchus mykiss
Rainbow trout (7.1 g, 8.4 cm),
Oncorhynchus mykiss
Rainbowtrout (10.1 g, 9.8 cm),
Oncorhynchus mykiss
Rainbow trout (1 .7 g, 5.8 cm),
Oncorhynchus mykiss
Rainbowtrout (2.1 g, 6.2 cm),
Oncorhynchus mykiss
Rainbow trout (0. 1 5 g, 2.7 cm),
Oncorhynchus mykiss
Rainbowtrout (8.6 g, 8.9 cm),
Oncorhynchus mykiss
Rainbowtrout (2.1 g, 6.2 cm),
Oncorhynchus mykiss
Rainbow trout (1 .01 g, 4.6 cm),
Oncorhynchus mykiss
Rainbowtrout (0.36 g, 3.4 cm),
Oncorhynchus mykiss
Rainbow trout (1 .7 g, 5.9 cm),
Oncorhynchus mykiss
Rainbowtrout (1.8 g, 5.8 cm),
Oncorhynchus mykiss
Rainbow trout (2596 g),
Oncorhynchus mykiss
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Phosphoric acid,
Diammonium salt
Ammonium sulfate
Ammonium chloride
Ammonium chloride
Phosphoric acid,
Diammonium salt
Ammonium chloride
Ammonium chloride
Ammonium bicarbonate
Ammonium bicarbonate
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
pH
7.9
7.9
7.91
7.91
7.91
7.91
7.94
7.94
7.95
7.96
7.98
8.06
8.08
8.1
8.12
7.62
TempfC)
13
13
13.1
13
19
19.1
12.8
12.5
12.5
19.2
12.5
13.2
12.8
13.9
13.6
7.9
Total
Ammonia
(mg N/L)
35.75
37.41
12.68
20.99
25.36
26.44
26.49
39.25
19.75
23.21
27.02
33.64
23.05
18.14
17.34
21.60
Total
Ammonia1"
(mg N/L)
at pH=8
29.65
31.03
10.71
17.73
21.43
22.34
23.66
35.06
17.97
21.52
26.01
37.68
26.83
21.94
21.79
11.01
SMAV
(mg
N/L)
GMAV
(mg
N/L)
Reference
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston and Russo 1983
Thurston et al. 1981a
83
-------
Table 1. (continued)
Species
Rainbow trout (2080 g),
Oncorhynchus mykiss
Rainbow trout (293 g),
Oncorhynchus mykiss
Rainbow trout (230 g),
Oncorhynchus mykiss
Rainbow trout (244 g),
Oncorhynchus mykiss
Rainbow trout (230 g),
Oncorhynchus mykiss
Rainbow trout (247 g),
Oncorhynchus mykiss
Rainbow trout (1 8 g),
Oncorhynchus mykiss
Rainbow trout (21 g),
Oncorhynchus mykiss
Rainbow trout (4.6 g, 7.3 cm),
Oncorhynchus mykiss
Rainbow trout (5.7 g, 8.0 cm),
Oncorhynchus mykiss
Rainbow trout (5.0 g, 7.6 cm),
Oncorhynchus mykiss
Rainbow trout (5.7 g, 8.0 cm),
Oncorhynchus mykiss
Rainbow trout (4.0 g, 7.2 cm),
Oncorhynchus mykiss
Rainbow trout (9.5 g, 9.4 cm),
Oncorhynchus mykiss
Rainbow trout (9.5 g, 9.4 cm),
Oncorhynchus mykiss
Rainbow trout (9.5 g, 9.4 cm),
Oncorhynchus mykiss
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
pH
7.67
7.71
7.72
7.72
7.74
7.74
7.86
7.86
7.75
7.75
7.76
7.79
7.83
6.51
6.8
7.3
TempfC)
7.7
8.5
8.2
8.1
8.3
8.1
9.6
9.7
12.7
12.5
12.5
12.9
12.8
14.1
14.1
14
Total
Ammonia
(mg N/L)
17.00
20.70
10.50
19.80
22.30
28.00
19.30
31.60
32.09
36.97
39.08
40.88
36.49
157.4
94.05
74.20
Total
Ammonia1"
(mg N/L)
at pH=8
9.405
12.25
6.322
11.92
13.90
17.45
14.88
24.36
20.35
23.44
25.21
27.80
26.65
27.18
18.82
23.78
SMAV
(mg
N/L)
GMAV
(mg
N/L)
Reference
Thurston et al. 1981a
Thurston et al. 1981a
Thurston et al. 198 la
Thurston et al. 1981a
Thurston et al. 1981a
Thurston et al. 1981a
Thurston et al. 1981a
Thurston et al. 1981a
Thurston et al. 1981b
Thurston et al. 1981b
Thurston et al. 1981b
Thurston et al. 1981b
Thurston et al. 1981b
Thurston et al. 1981c
Thurston et al. 1981c
Thurston et al. 1981c
84
-------
Table 1. (continued)
Species
Rainbow trout (9.5 g, 9.4 cm),
Oncorhynchus mykiss
Rainbow trout (9.5 g, 9.4 cm),
Oncorhynchus mykiss
Rainbow trout (9.5 g, 9.4 cm),
Oncorhynchus mykiss
Rainbow trout (juvenile),
Oncorhynchus mykiss
Rainbow trout (40.0 g;
swimming fish),
Oncorhynchus mykiss
Rainbow trout (40.0 g; resting
fish),
Oncorhynchus mykiss
Chinook salmon (1 .0-7 g),
Oncorhynchus tshawytscha
Chinook salmon (14.4 g, 1 1.9
cm),
Oncorhynchus tshawytscha
Chinook salmon (15.3 g, 12.1
cm),
Oncorhynchus tshawytscha
Chinook salmon (18.1 g, 12.7
cm),
Oncorhynchus tshawytscha
Mountain whitefish (177 g, 27.0
cm),
Prosopium williamsoni
Mountain whitefish (56.9 g,
19.1 cm),
Prosopium williamsoni
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonia
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
F,M
F,M
F,M
F,M
F,M
F,M
S,M
F,U
F,U
F,U
F,U
F,U
pH
8.29
8.82
9.01
7.2
6.97
6.97
7.96
7.87
7.82
7.84
7.68
7.84
TempfC)
14.1
13.9
14.5
10
16.6
16.6
7
13.5
12.2
12.3
12.1
12.4
Total
Ammonia
(mg N/L)
13.85
3.950
2.510
174.0
32.38
207.0
28.03
18.47
27.23
24.74
11.30
25.47
Total
Ammonia1"
(mg N/L)
at pH=8
24.21
18.63
16.18
49.50
7.347
46.97
25.98
14.50
19.53
18.40
6.357
18.94
SMAV
(mg
N/L)
19.30
19.18
GMAV
(mg
N/L)
23.09
Reference
Thurston et al. 1981c
Thurston et al. 1981c
Thurston et al. 1981c
Wicks and Randall 2002
Wicks et al. 2002
Wicks et al. 2002
Servizi and Gordon 1990
Thurston and Meyn 1 984
Thurston and Meyn 1 984
Thurston and Meyn 1 984
Thurston and Meyn 1 984
Thurston and Meyn 1 984
85
-------
Table 1. (continued)
Species
Mountain whitefish (63.0 g,
20.4 cm),
Prosopium williamsoni
Atlantic salmon (4.8-9.2 cm),
Salmo salar
Atlantic salmon (4.8-9.2 cm),
Salmo salar
Atlantic salmon (4.8-9.2 cm),
Salmo salar
Atlantic salmon (4.8-9.2 cm),
Salmo salar
Atlantic salmon (4.8-9.2 cm),
Salmo salar
Atlantic salmon (4.8-9.2 cm),
Salmo salar
Atlantic salmon (4.8-9.2 cm),
Salmo salar
Atlantic salmon (4.8-9.2 cm),
Salmo salar
Atlantic salmon (4.8-9.2 cm),
Salmo salar
Atlantic salmon (4.8-9.2 cm),
Salmo salar
Atlantic salmon (4.8-9.2 cm),
Salmo salar
Atlantic salmon (4.8-9.2 cm),
Salmo salar
Atlantic salmon (4.8-9.2 cm),
Salmo salar
Atlantic salmon (4.8-9.2 cm),
Salmo salar
Chemical Name
Ammonium chloride
Ammonium sulfate
Ammonium sulfate
Ammonium sulfate
Ammonium sulfate
Ammonium sulfate
Ammonium sulfate
Ammonium sulfate
Ammonium sulfate
Ammonium sulfate
Ammonium sulfate
Ammonium sulfate
Ammonium sulfate
Ammonium sulfate
Ammonium sulfate
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
F,U
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
pH
7.8
6.4
6.4
6
6
6.05
6.05
6
6
6.45
6.45
6.45
6.45
6.05
6.05
TempfC)
12.3
1.8
1.8
2.1
2.1
2.5
2.5
7.3
7.3
7.4
7.4
12.5
12.5
12.5
12.5
Total
Ammonia
(mg N/L)
21.20
123.0
133.9
297.2
341.1
400.0
491.7
581.5
587.6
171.3
214.4
230.6
248.3
403.5
451.5
Total
Ammonia1"
(mg N/L)
at pH=8
14.68
20.45
22.27
45.42
52.12
61.56
75.67
88.86
89.79
28.95
36.24
38.98
41.97
62.10
69.49
SMAV
(mg
N/L)
12.09
GMAV
(mg
N/L)
12.09
Reference
Thurston and Meyn 1 984
Knophl992
Knophl992
Knophl992
Knophl992
Knophl992
Knophl992
Knophl992
Knophl992
Knophl992
Knophl992
Knophl992
Knophl992
Knophl992
Knophl992
86
-------
Table 1. (continued)
Species
Atlantic salmon (4.8-9.2 cm),
Salmo salar
Atlantic salmon (4.8-9.2 cm),
Salmo salar
Atlantic salmon (1.5 g),
Salmo salar
Atlantic salmon (1.5 g),
Salmo salar
Atlantic salmon (36 g),
Salmo salar
Atlantic salmon (36 g),
Salmo salar
Brown trout (1 .20 g, 5.4 cm),
Salmo trutta
Brown trout (1.1 7 g, 5.3 cm),
Salmo trutta
Brown trout (0.91 g, 4.9 cm),
Salmo trutta
Brook trout (3.12 g, 7.2 cm),
Salvelinus fontinalis
Brook trout (3.40 g, 7.4 cm),
Salvelinus fontinalis
Lake trout, siscowet (0.9 g),
Salvelinus namaycush
Lake trout, siscowet (0.9 g),
Salvelinus namaycush
Lake trout, siscowet (8 g),
Salvelinus namaycush
Lake trout, siscowet (8 g),
Salvelinus namaycush
Chemical Name
Ammonium sulfate
Ammonium sulfate
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d.
4d
4d
4d
4d
4d
4d
4d
Methods
S,M
S,M
S,M
S,M
S,M
S,M
F,U
F,U
F,U
F,U
F,U
S,M
S,M
S,M
S,M
pH
6.05
6.05
7.45
7.45
7.45
7.45
7.85
7.86
7.82
7.86
7.83
7.45
7.45
7.45
7.45
TempfC)
17.1
17.1
8.5
8.5
8.5
8.5
13.2
13.8
14.2
13.6
13.8
8.5
8.5
8.5
8.5
Total
Ammonia
(mg N/L)
356.1
373.0
60.29
35.74
118.2
70.62
29.58
32.46
33.30
45.21
52.03
90.43
110.2
96.25
83.11
Total
Ammonia1"
(mg N/L)
at pH=8
54.80
57.41
23.67
14.03
46.40
27.72
22.40
25.03
23.89
34.86
38.00
35.50
43.27
37.78
32.62
SMAV
(mg
N/L)
42.66
23.75
36.39
37.10
GMAV
(mg
N/L)
31.83
36.74
Reference
Knophl992
Knophl992
Soderberg and Meade 1992
Soderberg and Meade 1992
Soderberg and Meade 1992
Soderberg and Meade 1992
Thurston and Meyn 1 984
Thurston and Meyn 1 984
Thurston and Meyn 1 984
Thurston and Meyn 1 984
Thurston and Meyn 1 984
Soderberg and Meade 1992
Soderberg and Meade 1992
Soderberg and Meade 1992
Soderberg and Meade 1992
87
-------
Table 1. (continued)
Species
Central stoneroller (2.1 g),
Campostoma anomalum
Rainbow dace,
Cyprinella lutrensis
Rainbow dace,
Cyprinella lutrensis
Spotfin shiner (31-85 mm),
Cyprinella spiloptera
Spotfin shiner (41-78 mm),
Cyprinella spiloptera
Spotfin shiner (0.5 g),
Cyprinella spiloptera
Steelcolor shiner (0.5 g),
Cyprinella whipplei
Common carp (206 mg),
Cyprinus carpio
Common carp (299 mg),
Cyprinus carpio
Common carp (4-5 cm),
Cyprinus carpio
Rio Grande silvery minnow (3-5
days old),
Hybognathus amarus
Golden shiner,
Notemigonus crysoleucas
Golden shiner,
Notemigonus crysoleucas
Golden shiner (8.7 g),
Notemigonus crysoleucas
Fathead minnow (Larva, 14 d),
Pimephales promelas
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
F,M
F,M
F,M
F,M
F,M
F,M
F,M
R,M
R,M
R,M
R,M
S,M
S,M
F,M
S,U
pH
7.8
8.3
9.1
7.95
8.15
7.9
7.9
7.72
7.72
7.4
8
7.5
7.55
7.5
7.6
TempfC)
25.7
24
24
26.5
26.5
25.7
25.7
28
28
28
25
19.6
19.5
24.5
20
Total
Ammonia
(mg N/L)
38.97
24.37
6.502
18.52
16.27
24.52
22.71
51.78
48.97
45.05
16.90
89.61
73.85
34.73
37.56
Total
Ammonia1"
(mg N/L)
at pH=8
26.97
43.43
47.99
16.85
21.67
20.34
18.83
31.18
29.48
16.48
16.90
37.86
33.67
14.67
18.53
SMAV
(mg
N/L)
26.97
45.65
19.51
18.83
24.74
16.90
14.67
GMAV
(mg
N/L)
26.97
25.60
24.74
16.90
14.67
Reference
Swigert and Spacie 1983
Hazel etal. 1979
Hazel etal. 1979
Rosageetal. 1979
Rosageetal. 1979
Swigert and Spacie 1983
Swigert and Spacie 1983
Hasan and Macintosh 1986
Hasan and Macintosh 1986
Rao etal. 1975
Buhl 2002
EA Engineering 1985
EA Engineering 1985
Swigert and Spacie 1983
Markle et al. 2000
-------
Table 1. (continued)
Species
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow (4-6 days old),
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow (1 .9 g),
Pimephales promelas
Fathead minnow (1 .8 g),
Pimephales promelas
Fathead minnow (1 .6 g),
Pimephales promelas
Fathead minnow (1 .7 g),
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow (4-5 mo. old),
Pimephales promelas
Fathead minnow (4-5 mo. old),
Pimephales promelas
Fathead minnow (4-5 mo. old),
Pimephales promelas
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
S,M
S,M
S,M
S,M
S,M
R,M
R,M
R,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
pH
7.52
7.48
7.52
7.48
7.48
8.01
8
8
7.9
8.1
8
8.1
8.05
7.46
7.46
7.41
TempfC)
20.25
19.85
20.25
19.85
19.85
25
20
20
3.4
12.1
17.1
26.1
14
6
10
15
Total
Ammonia
(mg N/L)
36.73
40.93
37.49
41.79
43.49
14.40
5.389
6.100
229.7
56.07
52.22
29.23
47.29
97.27
101.7
76.58
Total
Ammonia1"
(mg N/L)
at pH=8
15.87
16.79
16.20
17.14
17.84
14.67
5.389
6.100
190.5
67.81
52.22
35.35
51.97
38.74
40.50
28.40
SMAV
(mg
N/L)
GMAV
(mg
N/L)
Reference
EA Engineering 1985
EA Engineering 1985
EA Engineering 1985
EA Engineering 1985
EA Engineering 1985
Buhl 2002
Diamond etal. 1993
Diamond etal. 1993
Arthur etal. 1987
Arthur etal. 1987
Arthur etal. 1987
Arthur etal. 1987
DeGraeve et al. 1980
DeGraeve et al. 1987
DeGraeve et al. 1987
DeGraeve et al. 1987
89
-------
Table 1. (continued)
Species
Fathead minnow (4-5 mo. old),
Pimephales promelas
Fathead minnow (4-5 mo. old),
Pimephales promelas
Fathead minnow (4-5 mo. old),
Pimephales promelas
Fathead minnow (4-5 mo. old),
Pimephales promelas
Fathead minnow (4-5 mo. old),
Pimephales promelas
Fathead minnow (0.28 g, 26.6
mm),
Pimephales promelas
Fathead minnow (10 mm
length),
Pimephales promelas
Fathead minnow (10 mm
length),
Pimephales promelas
Fathead minnow (10 mm
length),
Pimephales promelas
Fathead minnow (10 mm
length),
Pimephales promelas
Fathead minnow (25 mm
length),
Pimephales promelas
Fathead minnow (25 mm
length),
Pimephales promelas
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
pH
7.41
7.45
7.4
7.41
7.44
8.14
7.9
8.2
7.8
7.8
8.1
8.2
TempfC)
20
20
25
25
30
22
20.6
6.2
20.1
19.8
19.6
6.2
Total
Ammonia
(mg N/L)
78.22
66.94
81.81
91.40
64.12
25.16
28.90
7.320
18.73
32.12
24.89
11.56
Total
Ammonia1"
(mg N/L)
at pH=8
29.01
26.28
29.93
33.90
24.81
32.86
23.97
10.74
12.96
22.23
30.10
16.96
SMAV
(mg
N/L)
GMAV
(mg
N/L)
Reference
DeGraeve et al. 1987
DeGraeve et al. 1987
DeGraeve et al. 1987
DeGraeve et al. 1987
DeGraeve et al. 1987
Mayesetal. 1986
Nimmoetal. 1989
Nimmoetal. 1989
Nimmoetal. 1989
Nimmoetal. 1989
Nimmoetal. 1989
Nimmoetal. 1989
90
-------
Table 1. (continued)
Species
Fathead minnow (25 mm
length),
Pimephales promelas
Fathead minnow (25 mm
length),
Pimephales promelas
Fathead minnow (25 mm
length),
Pimephales promelas
Fathead minnow (15(9-24) mm,
0.0301(0.0009-0.1195)),
Pimephales promelas
Fathead minnow (16(9-25) mm,
0.0315(0.0076-0.1107)),
Pimephales promelas
Fathead minnow (19(14-34)
mm, 0.0629(0.0102-0.3467)),
Pimephales promelas
Fathead minnow (21(16-28)
mm, 0.0662(0.0322-0.1597)),
Pimephales promelas
Fathead minnow (5.2 (4.6-5.5)
cm, 1.1 (0.6-1. 6) g),
Pimephales promelas
Fathead minnow (0.2 g),
Pimephales promelas
Fathead minnow (0.5 g),
Pimephales promelas
Fathead minnow (1 .9 g, 5.2 cm),
Pimephales promelas
Fathead minnow (1 .9 g, 5.2 cm),
Pimephales promelas
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
pH
8.1
8.1
7.7
8.46
8.02
8.26
8.16
7.7
7.78
7.8
7.83
7.82
TempfC)
5.8
5.8
20.1
4.1
23.9
4.6
25.2
21.65
25.9
25.6
11.8
12
Total
Ammonia
(mg N/L)
19.94
21.44
32.25
18.54
19.55
30.57
17.65
63.02
40.85
42.65
45.71
62.72
Total
Ammonia1"
(mg N/L)
at pH=8
24.12
25.93
18.77
45.05
20.29
50.40
23.96
36.67
27.30
29.53
33.38
44.99
SMAV
(mg
N/L)
GMAV
(mg
N/L)
Reference
Nimmoetal. 1989
Nimmoetal. 1989
Nimmoetal. 1989
Reinbold and Pescitelli 1982b
Reinbold and Pescitelli 1982b
Reinbold and Pescitelli 1982b
Reinbold and Pescitelli 1982b
Sparks 1975
Swigert and Spacie 1983
Swigert and Spacie 1983
Thurston et al. 1981c
Thurston et al. 1981c
91
-------
Table 1. (continued)
Species
Fathead minnow (1 .9 g, 5.2 cm),
Pimephales promelas
Fathead minnow (1 .9 g, 5.2 cm),
Pimephales promelas
Fathead minnow (1 .9 g, 5.2 cm),
Pimephales promelas
Fathead minnow (1 .9 g, 5.2 cm),
Pimephales promelas
Fathead minnow (0.09 g, 2.0
cm),
Pimephales promelas
Fathead minnow (0.09 g, 2.1
cm),
Pimephales promelas
Fathead minnow (0.13 g, 2.3
cm),
Pimephales promelas
Fathead minnow (0.19 g, 2.6
cm),
Pimephales promelas
Fathead minnow (0.22 g, 2.7
cm),
Pimephales promelas
Fathead minnow (0.22 g, 2.9
cm),
Pimephales promelas
Fathead minnow (0.26 g, 3.0
cm),
Pimephales promelas
Fathead minnow (0.31 g, 3.0
cm),
Pimephales promelas
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
pH
6.51
9.03
8.51
7.01
7.91
7.89
7.64
7.68
8.03
8.06
7.67
8.05
TempfC)
13
13.2
13.5
13.8
16.3
13.1
13.6
13.5
22.1
22
13.9
13
Total
Ammonia
(mg N/L)
260.0
5.940
18.88
145.9
51.55
50.20
58.40
64.70
47.60
42.60
58.80
74.65
Total
Ammonia1"
(mg N/L)
at pH=8
44.91
39.49
50.49
34.27
43.55
40.88
30.74
36.40
50.36
47.72
32.53
82.04
SMAV
(mg
N/L)
GMAV
(mg
N/L)
Reference
Thurston et al. 1981c
Thurston et al. 1981c
Thurston et al. 1981c
Thurston et al. 1981c
Thurston et al. 1983
Thurston et al. 1983
Thurston et al. 1983
Thurston et al. 1983
Thurston et al. 1983
Thurston et al. 1983
Thurston et al. 1983
Thurston et al. 1983
92
-------
Table 1. (continued)
Species
Fathead minnow (0.31 g, 3.1
cm),
Pimephales promelas
Fathead minnow (0.35 g, 3. 1
cm),
Pimephales promelas
Fathead minnow (0.42 g, 3.0
cm),
Pimephales promelas
Fathead minnow (0.42 g, 3.6
cm),
Pimephales promelas
Fathead minnow (0.47 g, 3.2
cm),
Pimephales promelas
Fathead minnow (0.47 g, 3.2
cm),
Pimephales promelas
Fathead minnow (0.5 g, 3.8 cm),
Pimephales promelas
Fathead minnow (0.8 g, 4.2 cm),
Pimephales promelas
Fathead minnow (1 .0 g, 4.6 cm),
Pimephales promelas
Fathead minnow (1 .4 g, 4.9 cm),
Pimephales promelas
Fathead minnow (1 .4 g, 5.0 cm),
Pimephales promelas
Fathead minnow (1 .4 g, 5.0 cm),
Pimephales promelas
Fathead minnow (1.4 g, 5.1 cm),
Pimephales promelas
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
pH
8.05
7.94
7.76
7.66
7.87
7.83
7.91
7.77
7.77
8.04
8.08
8.16
7.88
TempfC)
13.6
19.1
19
13.4
15.8
22
18.9
14.3
14.1
22.4
21.4
21.4
21.7
Total
Ammonia
(mg N/L)
66.48
42.30
50.28
58.20
58.91
50.60
49.30
66.70
72.71
36.59
44.80
47.39
50.90
Total
Ammonia1"
(mg N/L)
at pH=8
73.06
37.78
32.44
31.67
46.25
36.95
41.65
43.79
47.74
39.45
52.14
64.34
40.70
SMAV
(mg
N/L)
GMAV
(mg
N/L)
Reference
Thurston et al. 1983
Thurston et al. 1983
Thurston et al. 1983
Thurston et al. 1983
Thurston et al. 1983
Thurston et al. 1983
Thurston et al. 1983
Thurston et al. 1983
Thurston et al. 1983
Thurston et al. 1983
Thurston et al. 1983
Thurston et al. 1983
Thurston et al. 1983
93
-------
Table 1. (continued)
Species
Fathead minnow (1 .4 g, 5.4 cm),
Pimephales promelas
Fathead minnow (1 .4 g, 5.5 cm),
Pimephales promelas
Fathead minnow (1 .5 g, 5.6 cm),
Pimephales promelas
Fathead minnow (1 .7 g, 5.2 cm),
Pimephales promelas
Fathead minnow (2.1 g, 6.1 cm),
Pimephales promelas
Fathead minnow (2.2 g, 6.2 cm),
Pimephales promelas
Fathead minnow (2.3 g, 6.3 cm),
Pimephales promelas
White sucker (5.6 g),
Catostomus commersoni
White sucker (5. 2 g),
Catostomus commersoni
White sucker (12.6 g),
Catostomus commersoni
White sucker (9.6 g),
Catostomus commersoni
White sucker (110 mm length),
Catostomus commersoni
White sucker (1 10 mm length),
Catostomus commersoni
White sucker (92(71-1 1 9) mm,
6.3(2.6-13.2) g),
Catostomus commersoni
White sucker (92(71-1 1 9) mm,
6.3(2.6-13.2) g),
Catostomus commersoni
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
pH
7.68
7.63
7.76
7.84
7.76
7.74
7.91
7.8
8.1
8.2
8.2
7.8
7.8
8.16
8.14
TempfC)
12.9
13.2
12.9
21.7
13.1
12.8
15.9
3.6
11.3
12.6
15.3
20.2
20.2
15
15.4
Total
Ammonia
(mg N/L)
91.80
89.85
107.5
55.43
66.73
52.20
47.43
89.57
60.86
40.85
43.01
31.21
18.93
30.28
29.65
Total
Ammonia1"
(mg N/L)
at pH=8
51.65
46.53
69.38
41.22
43.05
32.53
40.07
62.00
73.60
59.94
63.10
21.61
13.10
41.11
38.73
SMAV
(mg
N/L)
37.07
GMAV
(mg
N/L)
37.07
Reference
Thurston et al. 1983
Thurston et al. 1983
Thurston et al. 1983
Thurston et al. 1983
Thurston et al. 1983
Thurston et al. 1983
Thurston et al. 1983
Arthur etal. 1987
Arthur etal. 1987
Arthur etal. 1987
Arthur etal. 1987
Nimmoetal. 1989
Nimmoetal. 1989
Reinbold and Pescitelli 1982c
Reinbold and Pescitelli 1982c
94
-------
Table 1. (continued)
Species
White sucker (1 1 .4 g),
Catostomus commersoni
Mountain sucker (63.3 g, 18.2
cm),
Catostomus platyrhynchus
Mountain sucker (45.3 g, 16.2
cm),
Catostomus platyrhynchus
Mountain sucker (47.8 g, 15.9
cm),
Catostomus platyrhynchus
Shortnose sucker (0.53-2.00 g),
Chasmistes brevirostris
Shortnose sucker,
Chasmistes brevirostris
Lost River sucker (0.49-0.80 g),
Deltistes luxatus
Lost River sucker (larvae),
Deltistes luxatus
Channel catfish,
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Channel catfish (larvae (1 d)),
Ictalurus punctatus
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
F,M
F,U
F,U
F,U
F,M
F,M
F,M
F,M
S,U
S,U
S,U
S,M
S,M
R,M
pH
7.8
7.67
7.69
7.73
8
8
8
8
8.7
8.7
8.7
7.49
7.53
8.2
TempfC)
22.5
12
13.2
11.7
20
20
20
20
26
22
30
19.7
19.75
23.8
Total
Ammonia
(mg N/L)
22.30
66.91
47.59
51.62
11.42
22.85
16.81
10.35
10.56
10.19
10.88
131.5
99.67
13.03
Total
Ammonia1"
(mg N/L)
at pH=8
15.44
37.02
27.23
31.62
11.42
22.85
16.81
10.35
40.26
38.85
41.47
54.72
44.06
19.11
SMAV
(mg
N/L)
36.68
31.70
16.15
13.19
GMAV
(mg
N/L)
34.10
16.15
13.19
Reference
Swigert and Spacie 1983
Thurston and Meyn 1 984
Thurston and Meyn 1 984
Thurston and Meyn 1 984
Saikietal. 1999
Saikietal. 1999
Saikietal. 1999
Saikietal. 1999
Colt and Tchobanoglous 1 976
Colt and Tchobanoglous 1 976
Colt and Tchobanoglous 1 976
EA Engineering 1985
EA Engineering 1985
Bader and Grizzle 1992
95
-------
Table 1. (continued)
Species
Channel catfish (juvenile (7 d)),
Ictalurus punctatus
Channel catfish (3.5 g),
Ictalurus punctatus
Channel catfish (5. 8 g),
Ictalurus punctatus
Channel catfish (6.4 g),
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Channel catfish (3-1 1 mo. old),
Ictalurus punctatus
Channel catfish (3-1 1 mo. old),
Ictalurus punctatus
Channel catfish (3-1 1 mo. old),
Ictalurus punctatus
Channel catfish (3-1 1 mo. old),
Ictalurus punctatus
Channel catfish (3-1 1 mo. old),
Ictalurus punctatus
Channel catfish (3-1 1 mo. old),
Ictalurus punctatus
Channel catfish (3-1 1 mo. old),
Ictalurus punctatus
Channel catfish (<1 10 d),
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Channel catfish (4.5-10.8 g),
Ictalurus punctatus
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
R,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
pH
8.2
7.8
8
8.1
8.4
7.46
7.41
7.41
7.45
7.4
7.41
7.44
8
7.94
7.98
8.08
TempfC)
23.9
19.6
3.5
14.6
28
10
15
20
20
25
25
30
20
23.8
23.8
28
Total
Ammonia
(mg N/L)
17.22
44.71
37.64
24.94
10.71
124.8
113.1
89.63
72.15
89.41
85.69
65.25
15.09
33.10
30.49
44.44
Total
Ammonia1"
(mg N/L)
at pH=8
25.27
30.95
37.61
30.16
23.19
49.70
41.95
33.24
28.32
32.70
31.78
25.25
15.09
29.57
29.35
51.72
SMAV
(mg
N/L)
GMAV
(mg
N/L)
Reference
Bader and Grizzle 1992
Arthur etal. 1987
Arthur etal. 1987
Arthur etal. 1987
Colt and Tchobanoglous 1978
DeGraeve et al. 1987
DeGraeve et al. 1987
DeGraeve et al. 1987
DeGraeve et al. 1987
DeGraeve et al. 1987
DeGraeve et al. 1987
DeGraeve et al. 1987
Diamond etal. 1993
Reinbold and Pescitelli 1982d
Reinbold and Pescitelli 1982d
Roseboom and Richey 1977
96
-------
Table 1. (continued)
Species
Channel catfish (7.1-12.7 g),
Ictalurus punctatus
Channel catfish (14.3(13.0-
15.7)cm, 19.0(14. 9-25.7)g),
Ictalurus punctatus
Channel catfish (0.5 g),
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Western mosquitofish,
Gambusia affinis
Western mosquitofish,
Gambusia affinis
Western mosquitofish,
Gambusia affinis
Western mosquitofish,
Gambusia affinis
Guppy(0.13g,2.03cm),
Poecilia reticulata
Guppy(8.0(7.1-11.0)mm),
Poecilia reticulata
Guppy (8.25(6.3-1 1.0) mm),
Poecilia reticulata
Guppy (8.70(6.8-10.6) mm),
Poecilia reticulata
Threespine stickleback (juv.-
adult, 32-60 mm),
Gasterosteus aculeatus
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonia
Ammonia
Ammonia
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
F,M
F,M
F,M
F,M
F,M
S,U
S,U
S,U
S,U
S,U
S,U
S,U
S,U
S,M
pH
8.09
7.93
7.8
8
8.1
7.75
8.2
8.5
8
7.5
7.22
7.45
7.45
7.1
TempfC)
22
20
25.7
26
17
19
19.5
23
24
27.55
25
25
25
23.3
Total
Ammonia
(mg N/L)
32.33
74.35
32.85
32.34
40.83
129.6
34.54
14.64
42.53
5.929
129.4
75.65
82.95
198.1
Total
Ammonia1"
(mg N/L)
at pH=8
38.36
64.58
22.74
32.34
49.38
82.17
50.68
38.41
42.53
2.505
37.66
29.70
32.56
50.40
SMAV
(mg
N/L)
33.14
51.07
17.38
GMAV
(mg
N/L)
33.14
51.07
17.38
Reference
Roseboom and Richey 1977
Sparks 1975
Swigert and Spacie 1983
West 1985
West 1985
Wallenetal. 1957
Wallenetal. 1957
Wallenetal. 1957
Wallenetal. 1957
Kumar and Krishnamoorthi
1983
Rubin and Elmaraghy 1 976
Rubin and Elmaraghy 1 976
Rubin and Elmaraghy 1 976
Hazel etal. 1971
97
-------
Table 1. (continued)
Species
Threespine stickleback (juv.-
adult, 32-60 mm),
Gasterosteus aculeatus
Threespine stickleback (juv.-
adult, 32-60 mm),
Gasterosteus aculeatus
Threespine stickleback (juv.-
adult, 32-60 mm),
Gasterosteus aculeatus
Threespine stickleback (juv.-
adult, 32-60 mm),
Gasterosteus aculeatus
Threespine stickleback (juv.-
adult, 32-60 mm),
Gasterosteus aculeatus
Threespine stickleback (juv.-
adult, 32-60 mm),
Gasterosteus aculeatus
White perch (76 mm),
Morone americana
White perch (76 mm),
Morone americana
White bass (4.4 g),
Morone chrysops
Striped bass (20-93 mm),
Morone saxatilis
Striped bass (20-93 mm),
Morone saxatilis
Striped bass (20-93 mm),
Morone saxatilis
Striped bass (20-93 mm),
Morone saxatilis
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
pH
7.15
7.25
7.5
7.5
7.5
7.5
8
6
7.09
7.4
7.5
7.35
7.5
TempfC)
15
23.3
15
23.3
23.3
15
16
16
19.7
23.3
23.3
15
15
Total
Ammonia
(mg N/L)
577.0
203.8
143.9
78.70
115.4
259.0
14.93
418.4
132.4
92.17
73.45
259.8
182.2
Total
Ammonia1"
(mg N/L)
at pH=8
155.4
61.46
60.78
33.25
48.76
109.4
14.93
63.94
33.52
33.72
31.03
88.22
76.99
SMAV
(mg
N/L)
65.53
30.90
33.52
GMAV
(mg
N/L)
65.53
Reference
Hazel etal. 1971
Hazel etal. 1971
Hazel etal. 1971
Hazel etal. 1971
Hazel etal. 1971
Hazel etal. 1971
Stevenson 1977
Stevenson 1977
Asheetal. 1996
Hazel etal. 1971
Hazel etal. 1971
Hazel etal. 1971
Hazel etal. 1971
98
-------
Table 1. (continued)
Species
Striped bass (20-93 mm),
Morone saxatilis
Striped bass (20-93 mm),
Morone saxatilis
Striped bass (20-93 mm),
Morone saxatilis
Striped bass (20-93 mm),
Morone saxatilis
Striped bass (126.6 (35.0-313.4)
g),
Morone saxatilis
Sunshine bass (larvae (12 h)),
Morone saxatilis chrysops
Sunshine bass (367.2 (62.1-
928.7) g),
Morone saxatilis x chrysops
Sunshine bass (42.7 g),
Morone saxatilis x chrysops
Sunshine bass (42.7 g),
Morone saxatilis x chrysops
Sunshine bass (42.7 g),
Morone saxatilis x chrysops
Sunshine bass (42.7 g),
Morone saxatilis x chrysops
Sunshine bass (42.7 g),
Morone saxatilis x chrysops
Sunshine bass (42.7 g),
Morone saxatilis x chrysops
Sunshine bass (42.7 g),
Morone saxatilis x chrysops
Sunshine bass (42.7 g),
Morone saxatilis x chrysops
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
pH
7.93
7.5
7.84
7.5
8.3
8.5
8.3
7
7
7
7
7
7
7
7
TempfC)
23.3
23.3
15
15
21
18.7
21
25
25
25
25
25
25
25
25
Total
Ammonia
(mg N/L)
48.03
125.9
165.7
354.9
12.86
3.903
8.147
63.62
83.06
56.55
65.39
60.09
64.51
79.53
86.60
Total
Ammonia1"
(mg N/L)
at pH=8
42.10
53.20
122.1
149.9
22.92
10.24
14.52
14.81
19.34
13.17
15.22
13.99
15.02
18.52
20.16
SMAV
(mg
N/L)
57.32
GMAV
(mg
N/L)
Reference
Hazel etal. 1971
Hazel etal. 1971
Hazel etal. 1971
Hazel etal. 1971
Oppenbom and Goudie 1993
Harcke and Daniels 1999
Oppenbom and Goudie 1993
Weirichetal. 1993
Weirichetal. 1993
Weirichetal. 1993
Weirichetal. 1993
Weirichetal. 1993
Weirichetal. 1993
Weirichetal. 1993
Weirichetal. 1993
99
-------
Table 1. (continued)
Species
Sunshine bass (42.7 g),
Morone saxatilis x chrysops
Sunshine bass (42.7 g),
Morone saxatilis x chrysops
Green sunfish (larvae, 9 d swim
up fry),
Lepomis cyanellus
Green sunfish,
Lepomis cyanellus
Green sunfish (62.5 mg),
Lepomis cyanellus
Green sunfish (62.5 mg),
Lepomis cyanellus
Green sunfish (62.5 mg),
Lepomis cyanellus
Green sunfish (62.5 mg),
Lepomis cyanellus
Pumpkinseed (4.13-9.22 g),
Lepomis gibbosus
Pumpkinseed,
Lepomis gibbosus
Pumpkinseed,
Lepomis gibbosus
Pumpkinseed,
Lepomis gibbosus
Bluegill,
Lepomis macrochirus
Bluegill,
Lepomis macrochirus
Bluegill,
Lepomis macrochirus
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
S,M
S,M
F,U
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
S,M
S,M
S,M
pH
7
7
8.28
7.84
7.2
6.61
7.72
8.69
7.77
7.77
7.77
7.71
7.51
7.51
7.52
TempfC)
25
25
26.2
12.3
22.4
22.4
22.4
22.4
12
14
14.5
15.7
20.35
20.35
20.65
Total
Ammonia
(mg N/L)
95.43
105.2
8.430
33.09
142.8
254.5
55.79
9.240
9.110
48.09
42.02
34.43
40.41
41.96
41.90
Total
Ammonia1"
(mg N/L)
at pH=8
22.22
24.48
14.45
24.61
40.64
45.86
33.59
34.59
5.981
31.58
27.59
20.38
17.20
17.86
18.24
SMAV
(mg
N/L)
16.35
35.10
18.05
GMAV
(mg
N/L)
31.39
Reference
Weirichetal. 1993
Weirichetal. 1993
Reinbold and Pescitelli 1982a
Jude 1973
McCormick et al. 1984
McCormick et al. 1984
McCormick et al. 1984
McCormick et al. 1984
Jude 1973
Thurstonl981
Thurstonl981
Thurstonl981
EA Engineering 1985
EA Engineering 1985
EA Engineering 1985
100
-------
Table 1. (continued)
Species
Bluegill,
Lepomis macrochirus
Bluegill,
Lepomis macrochirus
Bluegill,
Lepomis macrochirus
Bluegill (1.7 cm),
Lepomis macrochirus
Bluegill,
Lepomis macrochirus
Bluegill (20.0-70.0 mm, young
of year),
Lepomis macrochirus
Bluegill (20.0-70.0 mm, young
of year),
Lepomis macrochirus
Bluegill (20.0-70.0 mm, young
of year),
Lepomis macrochirus
Bluegill (20.0-70.0 mm, young
of year),
Lepomis macrochirus
Bluegill (20.0-70.0 mm, young
of year),
Lepomis macrochirus
Bluegill (20.0-70.0 mm, young
of year),
Lepomis macrochirus
Bluegill (20.0-70.0 mm, young
of year),
Lepomis macrochirus
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
S,M
S,M
S,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
pH
7.51
7.52
7.52
8
8
8.11
8.24
8.75
9.05
9.19
9.62
9.85
TempfC)
20.35
20.65
20.65
20
12
18.5
18.5
18.5
18.5
18.5
18.5
18.5
Total
Ammonia
(mg N/L)
44.30
42.63
44.10
21.56
25.12
16.73
42.01
12.70
6.581
3.755
0.7859
1.346
Total
Ammonia1"
(mg N/L)
at pH=8
18.85
18.56
19.20
21.56
25.12
20.62
66.62
52.95
45.11
31.44
10.44
20.88
SMAV
(mg
N/L)
GMAV
(mg
N/L)
Reference
EA Engineering 1985
EA Engineering 1985
EA Engineering 1985
Diamond etal. 1993
Diamond etal. 1993
Emery and Welch 1969
Emery and Welch 1969
Emery and Welch 1969
Emery and Welch 1969
Emery and Welch 1969
Emery and Welch 1969
Emery and Welch 1969
101
-------
Table 1. (continued)
Species
Bluegill,
Lepomis macrochirus
Bluegill (5.2(3.7-6.7) cm,),
Lepomis macrochirus
Bluegill (0.38 g, 26.3 mm),
Lepomis macrochirus
Bluegill (19(1 5 -25) mm,
0.0781(0.0417-0.1940)),
Lepomis macrochirus
Bluegill (22(17-27) mm,
0.1106(0.0500-0.2384)),
Lepomis macrochirus
Bluegill (28(2 1-36) mm,
0.250(0. 123-0. 555) g),
Lepomis macrochirus
Bluegill (30(23 -40) mm,
0.267(0.1 52-0.698) g),
Lepomis macrochirus
Bluegill (217 mg),
Lepomis macrochirus
Bluegill (342 mg),
Lepomis macrochirus
Bluegill (646 mg),
Lepomis macrochirus
Bluegill (72 mg),
Lepomis macrochirus
Bluegill,
Lepomis macrochirus
Bluegill (4.8 (4.6-5.2) cm, 1.1
(0.9-1.3) g),
Lepomis macrochirus
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
pH
8.6
7.9
8.1
8.4
8.12
8.16
8.09
8
8.2
7.93
8.07
7.6
7.85
TempfC)
24
24.25
22
4
25
4.5
24.8
22
28
22
22
21.7
22.05
Total
Ammonia
(mg N/L)
5.509
33.06
19.39
14.64
23.37
12.55
17.22
12.75
14.81
24.08
8.846
44.03
59.93
Total
Ammonia1"
(mg N/L)
at pH=8
17.46
27.42
23.45
31.68
29.37
17.04
20.43
12.75
21.72
21.11
10.10
21.72
45.38
SMAV
(mg
N/L)
GMAV
(mg
N/L)
Reference
Hazel etal. 1979
Lubinski et al. 1974
May es etal. 1986
Reinbold and Pescitelli 1982b
Reinbold and Pescitelli 1982b
Reinbold and Pescitelli 1982b
Reinbold and Pescitelli 1982b
Roseboom and Richey 1977
Roseboom and Richey 1977
Roseboom and Richey 1977
Roseboom and Richey 1977
Smith etal. 1984
Sparks 1975
102
-------
Table 1. (continued)
Species
Bluegill (0.9 g),
Lepomis macrochirus
Bluegill (0.9 g),
Lepomis macrochirus
Bluegill (1. 2 g),
Lepomis macrochirus
Smallmouth bass (26-29 mm,
264-267 mg),
Micropterus dolomieui
Smallmouth bass (26-29 mm,
264-267 mg),
Micropterus dolomieui
Smallmouth bass (26-29 mm,
264-267 mg),
Micropterus dolomieui
Smallmouth bass (26-29 mm,
264-267 mg),
Micropterus dolomieui
Largemouth bass (0.086-0.322
g),
Micropterus salmoides
Largemouth bass (2.018-6.286
g),
Micropterus salmoides
Guadalupe bass (6.5 g),
Micropterus treculi
Johnny darter (38 mm length),
Etheostoma nigrum
Johnny darter (38 mm length),
Etheostoma nigrum
Johnny darter (38 mm length),
Etheostoma nigrum
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
S,M7
F,M
F,M
F,M
pH
7.8
7.6
7.8
7.16
6.53
7.74
8.71
8.04
7.96
8
7.9
8
8.2
TempfC)
24.2
26.5
26.6
22.3
22.3
22.3
22.3
28
22
22
20.6
20.1
6.2
Total
Ammonia
(mg N/L)
33.88
58.69
37.52
123.4
359.9
39.30
7.560
19.59
20.48
12.70
28.90
24.61
6.937
Total
Ammonia1"
(mg N/L)
at pH=8
23.45
28.95
25.97
33.59
62.67
24.49
29.34
21.12
18.99
12.70
23.97
24.61
10.18
SMAV
(mg
N/L)
24.34
35.07
20.03
12.70
GMAV
(mg
N/L)
24.89
20.74
Reference
Swigert and Spacie 1983
Swigert and Spacie 1983
Swigert and Spacie 1983
Broderius et al. 1985
Broderius et al. 1985
Broderius et al. 1985
Broderius et al. 1985
Roseboom and Richey 1977
Roseboom and Richey 1977
Tomasso and Carmichael
1986
Nimmoetal. 1989
Nimmoetal. 1989
Nimmoetal. 1989
103
-------
Table 1. (continued)
Species
Johnny darter (38 mm length),
Etheostoma nigrum
Johnny darter (38 mm length),
Etheostoma nigrum
Johnny darter (38 mm length),
Etheostoma nigrum
Orangethroat darter,
Etheostoma spectabile
Orangethroat darter,
Etheostoma spectabile
Walleye,
Sander vitreus
Walleye (22.6 g),
Sander vitreus
Walleye (1 9.4 g),
Sander vitreus
Walleye (13.4 g),
Sander vitreus
Walleye (3.0 g, 65.6 mm),
Sander vitreus
Mozambique tilapia (juvenile),
Oreochromis mossambicus
Nile Tilapia (adults 3 g),
Oreochromis niloticus
Nile Tilapia (adults 45 g),
Oreochromis niloticus
Nile Tilapia (adults 1 1 g),
Oreochromis niloticus
Nile Tilapia (adults 1 1 g),
Oreochromis niloticus
Mottled sculpin (1 .8 g, 5.4 cm),
Cottus bairdi
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
F,M
F,M
F,M
F,M
F,M
F,U
F,M
F,M
F,M
F,M
R,U
F,M
F,M
F,M
F,M
F,M
pH
8.1
8.1
8
8.1
8.4
8.08
7.9
7.7
8.3
8.06
7.2
8.1
8
8.2
8.2
8.02
TempfC)
5.8
5.8
20.1
22
21
18.2
3.7
11.1
19
21.5
28
28
28
23
33
12.4
Total
Ammonia
(mg N/L)
11.47
13.46
15.63
16.12
7.650
17.43
48.37
89.93
6.123
21.49
151.5
16.75
40.40
31.01
18.55
49.83
Total
Ammonia1"
(mg N/L)
at pH=8
13.87
16.28
15.63
19.49
16.56
20.29
40.12
52.33
10.91
24.07
43.11
20.25
40.40
45.50
27.22
51.72
SMAV
(mg
N/L)
16.64
17.97
27.25
43.11
31.73
51.72
GMAV
(mg
N/L)
17.29
27.25
36.98
51.72
Reference
Nimmoetal. 1989
Nimmoetal. 1989
Nimmoetal. 1989
Hazel etal. 1979
Hazel etal. 1979
Reinbold and Pescitelli 1982a
Arthur etal. 1987
Arthur etal. 1987
Arthur etal. 1987
May es etal. 1986
Rani etal. 1998
Abdalla and McNabb 1999
Abdalla and McNabb 1999
Abdalla and McNabb 1999
Abdalla and McNabb 1999
Thurston and Russo 1981
104
-------
Table 1. (continued)
Species
Shortnose sturgeon (fingerling),
Acipenser brevirostrum
Leopard frog (fertilized eggs),
Rana pipiens
Leopard frog (8 day),
Rana pipiens
Spring peeper (fertilized),
Pseudacris crucifer
Spring peeper,
Pseudacris crucifer
Pacific tree frog (embryo),
Pseudacris regilla
Pacific tree frog (embryo),
Pseudacris regilla
Pacific tree frog (embryo),
Pseudacris regilla
Pacific tree frog (90 mg,
GOSNER STAGE 26-27),
Pseudacris regilla
Pacific tree frog (60 mg,
GOSNER STAGE 26-27),
Pseudacris regilla
Clawed toad (embryo),
Xenopus laevis
Clawed toad (embryo),
Xenopus laevis
Clawed toad (embryo),
Xenopus laevis
Clawed toad (embryo),
Xenopus laevis
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium nitrate
Ammonium chloride
Ammonium sulfate
Nitric acid ammonium
salt
Ammonium sulfate
Ammonium sulfate
Ammonium sulfate
Ammonium nitrate
Ammonium sulfate
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
S,M
F,M
F,M
F,U
F,U
R,M
R,M
R,M
R,M
R,M
R,M
R,M
R,M
R,M
pH
7.05
8
8
8
8
6.7
6.7
6.7
7.3
7.3
7.2
7.2
7.2
7.2
TempfC)
18
20
12
12
20
22
22
22
22
22
22
22
24
24
Total
Ammonia
(mg N/L)
149.8
31.04
16.23
17.78
11.42
41.19
60.44
103.1
136.6
116.4
33.20
102.9
32.37
60.71
Total
Ammonia1"
(mg N/L)
at pH=8
36.49
31.04
16.23
17.78
11.42
7.77
11.40
19.45
43.80
37.30
9.524
29.52
9.208
17.27
SMAV
(mg
N/L)
36.49
22.43
14.24
19.49
GMAV
(mg
N/L)
36.49
22.43
16.66
Reference
Fontenot et al. 1998
Diamond etal. 1993
Diamond etal. 1993
Diamond etal. 1993
Diamond etal. 1993
Schuytema and Nebeker
1999a
Schuytema and Nebeker
1999a
Schuytema and Nebeker
1999a
Schuytema and Nebeker
1999b
Schuytema and Nebeker
1999b
Schuytema and Nebeker
1999a
Schuytema and Nebeker
1999a
Schuytema and Nebeker
1999a
Schuytema and Nebeker
1999a
105
-------
Table 1. (continued)
Species
Clawed toad (17 mg, Gosner
Stage 26-27),
Xenopus laevis
Clawed toad (17 mg, Gosner
Stage 26-27),
Xenopus laevis
Clawed toad (21 mg, Gosner
Stage 26-27),
Xenopus laevis
Clawed toad (embryo),
Xenopus laevis
Clawed toad (embryo),
Xenopus laevis
Chemical Name
Nitric acid ammonium
salt
Ammonium sulfate
Ammonium chloride
Ammonium phosphate
Ammonium phosphate
Duration
4d
4d
4d
4d
4d
Methods
R,M
R,M
R,M
R,M
R,M
pH
7.15
7.15
7.15
8.43
8.62
TempfC)
22
22
22
25
25
Total
Ammonia
(mg N/L)
101.4
135.9
128.3
37.30
28.70
Total
Ammonia1"
(mg N/L)
at pH=8
27.29
36.59
34.56
85.55
94.43
SMAV
(mg
N/L)
28.51
GMAV
(mg
N/L)
28.51
Reference
Schuytema and Nebeker
1999b
Schuytema and Nebeker
1999b
Schuytema and Nebeker
1999b
Tietge et al. 2000
Tietge et al. 2000
a Acute values are normalized to pH 8 and temperature 25°C as per the equations provided in the 1999 criterion document (see Appendix D for an example calculation).
b Acute values (LC50 or EC50, except where noted otherwise) are normalized to pH 8 as per the equations provided in the 1999 criterion document (see Appendix D for an example calculation).
c Value reported is the concentration associated with the lethal time to 50% mortality, or LT50. The LT50 was reached at 4-d, and therefore, is appropriate for inclusion in Table 1.
Note: Each SMAV was calculated from the associated bold-face number(s) in the preceding column.
106
-------
Table 2. Other Acute Ammonia Toxicity for Glochidia Life Stage of Freshwater Mussels.
Species
Mucket (glochidia),
Actinonaias ligamentina
Mucket (glochidia),
Actinonaias ligamentina
Mucket (glochidia),
Actinonaias ligamentina
Mucket (glochidia),
Actinonaias ligamentina
Mucket (glochidia),
Actinonaias ligamentina
Mucket (glochidia),
Actinonaias ligamentina
Mucket (glochidia),
Actinonaias ligamentina
Mucket (glochidia),
Actinonaias ligamentina
Dwarf wedgemussel (glochidia),
Alasmidonta heterodon
Wavy -rayed lampmussel (glochidia),
Lampsilisfasciola
Wavy-rayed lampmussel (glochidia),
Lampsilisfasciola
Neosho mucket (glochidia),
Lampsilis rafinesqueana
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
2d
2d
2d
2d
2d
2d
2d
2d
2d
2d
2d
2d
Methods
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
pH
8.3
8.3
8.3
8.3
8.45
8.45
8.45
8.45
8.3
8.3
8.3
8.3
Temp
(°C)
20
20
20
20
20
20
20
20
20
20
20
20
Total Ammonia
(mg N/L)
3.99
3.18
2.30
5.14
3.99
2.30
5.14
3.18
10.14
4.26
2.91
3.85
Total Ammonia3
(mgN/L)
at pH=8 and 25°C
4.70
3.74
2.71
6.05
6.28
3.62
8.09
5.00
11.94
5.01
3.42
4.54
Reference
Wang et al, 2007c
Wang et al., 2007c
Wang et al., 2007c
Wang et al., 2007c
Wang et al., 2007b
Wang et al., 2007b
Wang et al., 2007b
Wang et al., 2007b
Wang et al., 2007c
Wang et al., 2007c
Wang et al., 2007c
Wang et al., 2007c
107
-------
Table 2. (continued)
Species
Fatmucket (glochidia),
Lampsilis siliquoidea
Fatmucket (glochidia),
Lampsilis siliquoidea
Fatmucket (glochidia),
Lampsilis siliquoidea
Fatmucket (glochidia),
Lampsilis siliquoidea
Fatmucket (glochidia),
Lampsilis siliquoidea
Fatmucket (glochidia),
Lampsilis siliquoidea
Fatmucket (glochidia),
Lampsilis siliquoidea
Fatmucket (glochidia),
Lampsilis siliquoidea
Fatmucket (glochidia),
Lampsilis siliquoidea
Fatmucket (glochidia),
Lampsilis siliquoidea
Fatmucket (glochidia),
Lampsilis siliquoidea
Pink papershell (glochidia),
Potamilus ohiensis
Ellipse (glochidia),
Venustaconcha ellipsiformis
Rainbow mussel (glochidia),
Villosa iris
Rainbow mussel (glochidia),
Villosa iris
Chemical Name
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Ammonium chloride
Duration
2d
2d
2d
2d
2d
2d
2d
2d
2d
2d
2d
2d
2d
2d
4d
Methods
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
S,M
PH
8.3
8.3
8.3
8.3
8.3
8.3
8.35
8.35
8.35
8.35
8.35
8.30
8.3
8.3
8
Temp
CO)
20
20
20
20
20
20
20
20
20
20
20
20
20
20
20
Total Ammonia
(mg N/L)
10.00
6.15
8.11
8.79
3.52
5.41
6.15
8.11
5.41
8.79
3.52
4.93
1.83
6.22
3.29
Total Ammonia3
(mg N/L)
at pH=8 and 25°C
11.78
7.24
9.55
10.35
4.14
6.37
7.98
10.53
7.02
11.40
4.56
5.81
2.15
7.32
2.17
Reference
Ingersoll 2004
Wangetal.,2007b
Wangetal.,2007b
Wangetal.,2007b
Wangetal.,2007b
Wangetal.,2007b
Wang et al, 2007c
Wangetal.,2007c
Wangetal.,2007c
Wangetal.,2007c
Wangetal.,2007c
Wangetal.,2007b
Wangetal.,2007b
Wang et al., 2007b
Schellerl997
a Acute values are normalized to pH 8 and temperature 25°C as per the equations provided in the 1999 criterion document (see Appendix D for an example calculation).
108
-------
Table 3. Ranked Genus Mean Acute Values - Freshwater Mussels Present.
Rank
67
66
65
64
63
62
61
60
59
58
57
56
55
54
53
52
51
50
GMAV
(mg N/L)
809.6
386.8
153.0
113.2
105.6
104.9
68.05
65.53
59.53
56.49
51.94
51.72
51.07
37.92
37.07
36.98
36.74
36.49
Species
Swamp eel,
Monoptents albus
Insect,
Erythromma najas
Caddisfly,
Philarctus quaeris
Beetle,
Stenelmis sexlineata
Crayfish,
Orconectes nais
Crayfish,
Orconectes immunis
Midge,
Chironomus tentans
Midge,
Chironomus riparius
Mayfly,
Drunella grandis
Threespine stickleback,
Gasterosteus aculeatus
Aquatic sowbug,
Asellus racovitzai
Crayfish,
Pacifastacus leniusculus
Common eel,
Anguilla anguilla
Mottled sculpin,
Coitus bairdi
Western mosquitofish,
Gambusia affinis
Mayfly,
Callibaetis sp.
Mayfly,
Callibaetis skokianus
Fathead minnow,
Pimephales promelas
Nile Tilapia,
Oreochromis niloticus
Mozambique tilapia,
Oreochromis mossambicus
Lake trout, siscowet,
Salvelinus namaycush
Brook trout,
Salvelinus fontinalis
Shortnose sturgeon,
Acipenser brevirostrum
SMAV
(mg N/L)
809.6
386.8
153.0
113.2
46.73
238.4
69.49
158.3
68.05
65.53
59.53
56.49
51.94
51.72
51.07
25.64
56.09
37.07
31.73
43.11
37.10
36.39
36.49
109
-------
Table 3. (continued)
Rank
49
48
47
46
45
44
43
42
41
40
39
38
37
36
GMAV
(mg N/L)
35.85
34.10
33.64
33.30
33.14
32.54
31.83
31.39
29.60
28.51
27.96
27.25
26.97
26.17
Species
Dragonfly,
Pachydiplax longipennis
Mountain sucker,
Catostomus platyrhynchus
White sucker,
Catostomus commersoni
Oligochaete, worm,
Lumbriculus variegatus
Tubificid worm, Oligochaete,
Tubifex tubifex
Channel catfish,
Ictalurus punctatus
Ramshorn snail,
Helisoma trivolvis
Brown trout,
Salmo trutta
Atlantic salmon,
Salmo salar
Sunshine bass,
Morone saxatilis x chrysops
Striped bass,
Morone saxatilis
White bass,
Morone chrysops
White perch,
Morone americana
Stonefly, Little golden stonefly,
Skwala americana
Clawed toad,
Xenopus laevis
Amphipod,
Crangonyx sp.
Amphipod,
Crangonyx pseudogracilis
Walleye,
Sander vitreus
Central stoneroller,
Campostoma anomalum
Tubificid worm,
Limnodrilus hoffmeisteri
SMAV
(mg N/L)
35.85
31.70
36.68
33.64
33.30
33.14
32.54
23.75
42.66
16.35
57.32
33.52
30.90
29.60
28.51
18.79
41.61
27.25
26.97
26.17
110
-------
Table 3. (continued)
Rank
35
34
33
32
31
30
29
28
27
26
25
GMAV
(mg N/L)
25.60
25.29
25.22
25.01
24.89
24.74
23.09
22.43
22.13
21.98
21.76
Species
Steelcolor shiner,
Cyprinella whipplei
Spotfin shiner,
Cyprinella spiloptera
Rainbow dace,
Cyprinella lutrensis
Pouch snail,
Physa gyrina
Damselfly,
Enallagma sp.
Water flea,
Chydorus sphaericus
Bluegill,
Lepomis macrochirus
Pumpkinseed,
Lepomis gibbosus
Green sunfish,
Lepomis cyanellus
Common carp,
Cyprinus carpio
Chinook salmon,
Oncorhynchus tshawytscha
Rainbow trout,
Oncorhynchus mykiss
Coho salmon,
Oncorhynchus kisutch
Pink salmon,
Oncorhynchus gorbuscha
Cutthroat trout,
Oncorhynchus clarki
Golden trout,
Oncorhynchus aguabonita
Leopard frog,
Rana pipiens
Water flea,
Ceriodaphnia dubia
Water flea,
Ceriodaphnia acanthina
Water flea,
Simocephalus vetulus
Giant floater mussel,
Pyganodon grandis
SMAV
(mgN/L)
18.83
19.51
45.65
25.29
25.22
25.01
24.34
18.05
35.10
24.74
19.18
19.30
20.27
42.07
18.37
26.10
22.43
20.64
23.73
21.98
21.76
111
-------
Table 3. (continued)
Rank
24
23
22
21
20
19
18
17
16
15
14
13
12
11
10
9
GMAV
(mg N/L)
21.23
20.74
19.22
18.37
17.38
17.29
16.90
16.66
16.15
14.67
14.30
13.74
13.63
13.19
12.22
12.09
Species
Red swamp crayfish,
Procambarus clarkii
Guadalupe bass,
Micropterus treculi
Largemouth bass,
Micropterus salmoides
Smallmouth bass,
Micropterus dolomieui
Water flea,
Daphnia pulicaria
Water flea,
Daphnia magna
flatworm,
Dendrocoelum lacteum
Guppy,
Poecilia reticulata
Orangethroat darter,
Etheostoma spectabile
Johnny darter,
Etheostoma nigrum
Rio Grande Silvery Minnow,
Hybognathus amarus
Pacific tree frog,
Pseudacris regilla
Spring peeper,
Pseudacris crucifer
Shortnose sucker,
Chasmistes brevirostris
Golden shiner,
Notemigonus crysoleucas
Chinese mitten crab,
Eriocheir sinensis
Long fingernail clam,
Musculium transversum
Great pond snail,
Lymnaea stagnalis
Lost River sucker,
Deltistes luxatus
Pleasantshell,
Actinonaias pectorosa
Mountain whitefish,
Prosopium williamsoni
SMAV
(mgN/L)
21.23
12.70
20.03
35.07
15.23
24.25
18.37
17.38
17.97
16.64
16.90
19.49
14.24
16.15
14.67
14.30
13.74
13.63
13.19
12.22
12.09
112
-------
Table 3. (continued)
Rank
8
7
6
5
4
3
2
1
GMAV
(mg N/L)
10.54
7.605
7.164
6.037
6.018
5.919
5.036
3.539
FAV = 5.734
CMC = 2.9
Species
Snail,
Pleurocera unciale
Snail,
Potamopyrgus antipodarum
Pondshell mussel,
Utterbackia imbecillis
Oyster mussel,
Epioblasma capsaeformis
Asiatic clam,
Corbicula fluminea
Fatmucket,
Lampsilis siliquoidea
Neosho mucket,
Lampsilis rafmesqueana
Higgin's eye,
Lampsilis higginsii
Wavy-rayed lampmussel,
Lampsilis fasciola
Plain pocketbook,
Lampsilis cardium
Pink mucket,
Lampsilis abrupta
Rainbow mussel,
Villosa iris
Green floater,
Lasmigona subviridus
SMAV
(mgN/L)
10.54
7.605
7.164
6.037
6.018
5.646
11.65
6.249
6.207
7.689
2.191
5.036
3.539
113
-------
Table 4. Other Acute Ammonia Toxicity for Hyalella azteca.
Species
Scud (7- 14 D),
Hyalella azteca
Scud (7- 14 D),
Hyalella azteca
Scud (7- 14 D),
Hyalella azteca
Scud (7- 14 D),
Hyalella azteca
Scud (7- 14 D),
Hyalella azteca
Scud (7- 14 D),
Hyalella azteca
Scud (7- 14 D),
Hyalella azteca
Scud (7- 14 D),
Hyalella azteca
Scud (7- 14 D),
Hyalella azteca
Scud,
Hyalella azteca
Scud,
Hyalella azteca
Scud (juvenile, <7 d old),
Hyalella azteca
Scud (juvenile, <7 d old),
Hyalella azteca
Scud,
Hyalella azteca
Scud,
Hyalella azteca
Scud (14-2 Id),
Hyalella azteca
Chemical Name
Ammonium
chloride
Ammonium
chloride
Ammonium
chloride
Ammonium
chloride
Ammonium
chloride
Ammonium
chloride
Ammonium
chloride
Ammonium
chloride
Ammonium
chloride
Ammonia
Ammonia
Ammonium
chloride
Ammonium
chloride
Ammonium
chloride
Ammonium
chloride
Ammonium
chloride
Duration
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
4d
Methods
R,M
R,M
R,M
R,M
R,M
R,M
R,M
R,M
R,M
S,M
S,M
S,M
S,M
R,M
R,M
F,M
pH
7.49
6.5
8.21
8.45
8.3
7.31
6.43
7.41
6.55
6.69
7.56
7.85
7.85
6.85
6.28
6.82
Temp
(°C)
25
25
25
25
25
25
25
25
25
23
23
23
23
23
23
23
Estimated
Cl
mg/L
44-516
Note: Values
represent the
range of Cl
concentrations
at the respective
LCSOs within
the study
a
a
Min of 26 +
contribution
fromNH4Cl
Min of 26 +
contribution
fromNH4Cl
Approx. 25
Overlying water
a
Pore water
Approx. 25
Water-only
Total
Ammonia
(mg N/L)
17.50
22.80
24.00
35.20
39.80
64.00
105.00
140.00
204.00
117.00
126.00
60.32
63.00
9.70
82.0
9.20
Total Ammonia3
(mg N/L)
at pH=8 and 25°C
7.28
3.92
35.90
83.90
70.93
20.78
17.63
51.93
35.81
18.54
49.43
38.69
40.41
1.70
11.18
1.58
Reference
Ankleyetal. 1995
Ankleyetal. 1995
Ankleyetal. 1995
Ankleyetal. 1995
Ankleyetal. 1995
Ankleyetal. 1995
Ankleyetal. 1995
Ankleyetal. 1995
Ankleyetal. 1995
Besseretal. 1998
Besseretal. 1998
Sardal994
Sardal994
Whiteman et al. 1996
Whiteman et al. 1996
Whiteman et al. 1996
a Could not be estimated.
114
-------
Table 5. Chronic Toxicity of Ammonia to Aquatic Animals.
Species
Test and Effect
PH
Temp
fC)
Total Ammonia
(mgN/L)
Chronic value3
Adjusted to pH 8 (all
organisms) and 25°C
(invertebrates)
(mgN/L)
SMCV
(mgN/L)
GMCV
(mg N/L)
Reference
Freshwater Invertebrates
Wavy-rayed lamp mussel (2
mo old juveniles),
Lampsilis fasciola
Fatmucket (2 mo old
juveniles),
Lampsilis siliquoidea
Rainbow mussel (2 mo old
juveniles),
Villosa iris
Long fingernail clam,
Musculium transversum
Long fingernail clam,
Musculium transversum
Water flea,
Ceriodaphnia acanthina
Water flea,
Ceriodaphnia dubia
Water flea,
Ceriodaphnia dubia
Water flea,
Ceriodaphnia dubia
Water flea,
Daphnia magna
Water flea,
Daphnia magna
28-d Juv
Survival
28-d Juv
Survival
28-d Juv
Survival
42-d Juv
Survival
42-d Juv
Survival
7-dLC
Reproduction
7-dLC
Reproduction
7-dLC
Reproduction
7-dLC
Reproduction
21-dLC
Reproduction
21-dLC
Reproduction
8.2
8.2
8.2
8.15
7.8
7.15
7.8
7.8
8.57
8.45
7.92
20
20
20
23.5
21.8
24.5
25
25
26
19.8
20.1
0.3981
0.3076
0.9965
5.820
1.230
44.90
15.20
15.20
5.80
7.370
21.70
<0.3917
<0.3027
(IC20)
0.9805
(IC20)
6.630
0.7659
19.14
11.63
11.63
15.57
10.83
14.15
<0.3917
<0.3027
0.9805
<2.260
19.14
13.46
12.38
0.3443
0.9805
<2.260
16.05
12.38
Wang et al. 2007a
Wang et al. 2007a
Wang et al. 2007a
Anderson et al. 1978
Sparks and Sandusky 1981
Mount 1982
Nimmoetal. 1989
Nimmoetal. 1989
Willinghaml987
Gerischetal. 1985
Reinbold and Pescitelli 1982a
115
-------
Table 5. (continued)
Species
Test and Effect
pH
Temp
(°C)
Total Ammonia
(mgN/L)
Chronic value3
Adjusted to pH 8 (all
organisms) and 25 °C
(invertebrates)
(mgN/L)
SMCV
(mgN/L)
GMCV
(mg N/L)
Reference
Freshwater Vertebrates
Cutthroat trout (juvenile;
3.3-3.4 g),
Oncorhynchus clarki
Lahontan Cutthroat Trout
(fertilized),
Oncorhynchus clarki
henshawi
Rainbow trout (fertilized),
Oncorhynchus mykiss
Rainbow trout,
Oncorhynchus mykiss
Rainbow trout (fertilized),
Oncorhynchus mykiss
Rainbow trout,
Oncorhynchus mykiss
Sockeye salmon,
Oncorhynchus nerka
Northern pike (eggs,
larvae),
Esox lucius
Common carp (larvae),
Cyprinus carpio
Fathead minnow (embryo-
larvae),
Pimephales promelas
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
29-d Juv
Survival
103-d ELS
Survival
42-d ELS
Survival
72-d ELS
Survival
73-d ELS
Survival
5-year LC
62-d Embryos
Hatchability
52-d ELS
Biomass
28-dELS
Weight
28-d ELS
Survival
30-d ELS
Biomass
LC
Hatchability
8.0
7.57
7.5
7.4
7.52
7.7
8.42
7.62
7.85
8
7.82
8
12.2-13.1
13.7
10
14.5
14.9
7.5-10.5
10
8.7
23
24.8
25.1
24.2
20.80
33.60
2.600
2.550
8.000
2.130
13.44
8.360
5.120
3.730
1.970
<19.70b
12.38
<18.75b
1.336b
<1.449b
>5.445b
<4.160
8.401
6.815
5.124
2.927
1.972
12.38C
<4.160C
8.401
6.815
3.093
8.401
6.815
3.093
Thurston et al. 1978
Kochetal. 1980
Burkhalter and Kaya 1 977
Calamari et al. 1977,1981
Solbe and Shurben 1989
Thurston et al. 1984b
Rankinl979
Harrahy et al. 2004
Mallet and Sims 1994
Mayesetal. 1986
Swigert and Spacie 1983
Thurston et al. 1986
116
-------
Table 5. (continued)
Species
White sucker (3 d old
embryos),
Catostomus commersoni
Channel catfish,
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Green sunfish,
Lepomis cyanellus
Green sunfish,
Lepomis cyanellus
Bluegill,
Lepomis macrochirus
Smallmouth bass,
Micropterus dolomieui
Smallmouth bass,
Micropterus dolomieui
Smallmouth bass,
Micropterus dolomieui
Smallmouth bass,
Micropterus dolomieui
Test and Effect
30-d ELS
Biomass
30-d ELS
Weight
30-d Juv
Survival
30-d ELS
Biomass
30-d ELS
Biomass
30-d ELS
Survival
30-d ELS
Biomass
32-d ELS
Biomass
32-d ELS
Biomass
32-d ELS
Biomass
32-d ELS
Biomass
pH
8.32
7.8
8.35
7.76
7.9
8.16
7.76
6.6
7.25
7.83
8.68
Temp
(°C)
18.6
25.8
27.9
26.9
22
25.4
22.5
22.3
22.3
22.3
22.3
Total Ammonia
(mg N/L)
2.900
12.20
5.020
11.50
5.610
5.840
1.850
9.610
8.620
8.180
1.540
Chronic value3
Adjusted to pH 8 (all
organisms) and 25°C
(invertebrates)
(mg N/L)
4.790
9.338
8.717
8.386
4.884
7.444
1.349
3.565
4.009
6.500
4.662
SMCV
(mg N/L)
>4.790
8.805
6.030
1.349
4.562
GMCV
(mg N/L)
>4.790
8.805
2.852
4.562
Reference
Reinbold and Pescitelli 1982a
Reinbold and Pescitelli 1982a
Colt and Tchobanoglous 1978
Swigert and Spacie 1983
McCormick et al. 1984
Reinbold and Pescitelli 1982a
Smith etal. 1984
Broderius et al. 1985
Broderius et al. 1985
Broderius et al. 1985
Broderius et al. 1985
a The chronic value is an EC20 value calculated using EPA's TRAP (Versions 1.0 and 2.1), or, where indicated, an IC20 value calculated using EPA's ICpin (Version 2.0). Note: all chronic values
were normalized to pH 8 (all organisms) and 25°C (invertebrates) as per the equations provided in the 1999 criterion document (see Appendix E for an example calculation).
b Not used in the calculation of the SMCV because of the uncertainty of the chronic value, and because of the profound differences in chronic values for tests with rainbow trout (see Text in
Evaluation of the Chronic Data Available for Each New Species).
0 Not used in the calculation of the GMCV for Oncorhynchus because of the profound differences in chronic values for other species within the genus (also see Text in Evaluation of the Chronic Data
Available for Each New Species).
117
-------
Table 6. Other Chronic Ammonia Toxicity Data.
Species
Test and Effect
Method
pH
Temp
(°C)
Total
Ammonia
(mg N/L)
Chronic value
Adjusted to pH 8
(all organisms)
and25°C
(invertebrates)
(mg N/L)
Reference
Freshwater Invertebrates
Pulmonate pondsnail (<1 week post-hatch)
Lymnaea stagnalis
Pulmonate Pondsnail (<1 week post hatch),
Lymnaea stagnalis
Idaho springsnail (mixed aged, adults)
Pyrgulopsis idahoensis
Idaho Springsnail (7-9 and 11-13 week post
hatch juveniles ),
Pyrgulopsis idahoensis
Pebblesnail (mixed aged, field collected)
Fluminicola sp.
Ozark springsnail (mixed age, field collected)
Fontigens aldrichi
Bliss Rapids snail (mixed age, field collected)
Taylorconcha serpenticola
Wavy-rayed lamp mussel (2 mo old
juveniles),
Lampsilis fasciola
Fatmucket (2 mo old juveniles),
Lampsilis siliquoidea
Rainbow mussel (2 mo old juveniles),
Villosa iris
Water flea, (<24hrs),
Ceriodaphnia dubia
28-d Juv
NOEC - Survival
28-d
NOEC - Growth
28-d Juv
EC20 - Survival
28-d
NOEC - Growth
28-d Juv
EC20 - Survival
28-d Juv
EC20 - Survival
28-d Juv
EC20 - Survival
28-d
IC25 - Growth
28-d
IC25 - Growth
28-d
IC25 - Growth
3 broods in control
IC25 Reproduction
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
F,M
R,M
8.25
8.25
8.26
8.25
8.26
8.26
8.26
8.2
8.2
8.2
7.9
20.1
20.1
20.8
20.1
20.8
20.8
20.8
20.1
20.1
20.1
25.0
>7.90
>7.90
3.24
>8.00
1.02
0.61
3.42
0.57
0.44
0.73
1.3
>8.51
>8.51
<3.77
>8.62
<1.19
<0.71
<3.98
0.56
0.43
0.72
1.08
Besser et al. 2009
Besser et al. 2009
Besser et al. 2009
Besser et al. 2009
Besser et al. 2009
Besser et al. 2009
Besser et al. 2009
Wang et al. 2007a
Wang et al. 2007a
Wang et al. 2007a
Dwyer et al. 2005
118
-------
Table 6. Continued
Species
Bonytail chub (2 and 7-d post hatch),
Gila Elegans
Spotfin chub (<24hrs),
Cyprinella monocha
Cape Fear shiner (<24hrs),
Notmpis mekistocholas
Gila topminnow (<24, 48 and 72hrs),
Poeciliopsis occidentalis
European eel (2.8 g),
Anguilla anguilla
Fathead minnow (24hrs),
Pimephales promelas
Fathead minnow (4-d post hatch),
Pimephales promelas
Colorado pike minnow (5 and 6-d post hatch),
Ptychocheilus lucius
Colorado pikeminnow (juvenile, 8-d),
Ptychocheilus lucius
Razorback sucker (7-d post hatch),
Xyrauchen texanus
Razorback sucker (9-d),
Xyrauchen texanus
Lost River sucker (Late-stage larva),
Deltistes luxatus
Lake trout, siscowet,
Salvelinus namaycush
Tilapia (Juvenile),
Oreochromis niloticus
Test and Effect
7-d
IC25 - Growth
7-d
IC25 - Growth
7-d
IC25 - Growth
7-d
IC25 - Growth
77-d Juv
LOEC- Growth Rate
7-d
IC25 - Growth
28-d Juv
LOEC- Survival
7-d
IC25 - Growth
28-d Juv
LOEC- Growth
7-d
IC25 - Growth
28-d Juv
LOEC- Survival
30-d Juv
LOEC-Survival
60-d Juv
LOEC- Weight gain
75-d Juv
LOEC- Specific growth
weight
Method
R,M
R,M
R,M
R,M
F,M
R,M
R,M
R,M
R,M
R,M
R,M
F,M
F,M
F,M
pH
7.9
7.9
7.9
7.9
7.53
7.9
8.34
7.9
8.23
7.9
8.25
9.5
8.02
7.45
Temp
(°C)
25.0
25.0
25.0
25.0
23.0
25.0
19.9
25.0
19.9
25.0
19.9
22.3
11.6
30
Total
Ammonia
(mg N/L)
11.0
15.8
8.8
24.1
15.2
7.2
7.9
8.9
8.6
13.4
13.25
1.23
6.44
5.30
Chronic value
Adjusted to pH 8
(all organisms)
and25°C
(invertebrates)
(mg N/L)
9.12
13.10
7.30
19.99
8.54
5.97
13.48
7.38
12.26
11.11
19.20
10.43
6.63
2.84
Reference
Dwyer et al. 2005
Dwyer et al. 2005
Dwyer et al. 2005
Dwyer et al. 2005
Sadler 1981
Dwyer et al. 2005
Fairchild et al. 2005
Dwyer et al. 2005
Fairchild et al. 2005
Dwyer et al. 2005
Fairchild et al. 2005
Meyer and Hansen 2002
Beamish and Tandler 1990
El-Shafai et al. 2004
119
-------
Table 6. Continued
Species
Nile Tilapia (6 g),
Oreochromis niloticus
Green frog (STAGE 24-26),
Rana clamitans
Test and Effect
35-d Juv
LOEC- Weight gain
103-d Juv
NOEC- Growth
Method
F,M
R,M
PH
7.8
8.7
Temp
(°C)
28
24
Total
Ammonia
(mg N/L)
7.07
2.20
Chronic value
Adjusted to pH 8
(all organisms)
and2S°C
(invertebrates)
(mg N/L)
5.41
>6.90
Reference
Abdalla and McNabb 1999
Jofre and Karasov 1999
120
-------
Table 7. Genus Mean Acute-Chronic Ratios
Species
V. iris
L.fasciola
L. siliquoidea
C. acanthina
C. dubia
D. magna
C. commersoni
I. punctatus
Acute and
Chronic
Test
Endpoint
LC50
EC20
LC50
EC20
LC50
EC20
LC50
EC20
LC50
EC20
LC50
EC20
LC50
EC20
LC50
EC20
LC50
EC20
LC50
EC20
pH
8.3
8.2
8.3
8.2
8.3
8.2
7.06
7.15
7.8
7.8
8.61
8.57
8.5
8.45
8.34
7.92
8.16
8.32
7.8
7.76
Temp
(oC)
20
20
20
20
20
20
24
24.5
25
25
26
26
20
19.8
19.7
20.1
15
18.6
25.7
26.9
Concentration
Normalized to
pH 8 (all organisms) and
25°C (invertebrates)
(mgN/1)
8.293a
<1.353
10.67
O.5407
7.065
O.4178
25.78
19.77
23.52
11.63
47.80
14.60
69.12
15.14
100.0
19.41
39.89a
>4.790
22.74
8.386
Reference(s)
Wang et al. 2007b
Wang et al. 2007a
Wang et al. 2007b
Wang et al. 2007a
Wang et al. 2007b
Wang et al. 2007a
Mount 1982
Nimmoetal. 1989
Willinghaml987
Gersichetal. 1985
Reinbold and Pescitelli 1982a
Reinbold and Pescitelli
1982c
Swigert and Spacie 1983
ACR
>6.129
>19.73
>16.91
1.304
2.022
3.274
4.565
5.152
<8.330
2.712
SMACR
>6.129
>19.73
>16.91
1.304
2.573
4.850
<8.330
2.712
GMACR
>6.129
>18.27
1.832
4.850
<8.330
2.712
121
-------
Table 7. (continued)
Species
L. cyanellus
L. macrochirus
M. dolomieui
P. promelas
Acute and
Chronic
Test
Endpoint
LC50
EC20
LC50
LC50
EC20
LC50
EC20
LC50
EC20
LC50
EC20
LC50
EC20
LC50
EC20
LC50
EC20
LC50
EC20
PH
7.72
7.9
8.28
7.6
7.76
6.53
6.6
7.16
7.25
7.74
7.83
8.71
8.68
7.76
8
8.14
8
7.78
7.82
Temp
(oC)
22.4
22
26.2
21.7
22.5
22.3
22.3
22.3
22.3
22.3
22.3
22.3
22.3
19
24.2
22
24.8
25.9
25.1
Concentration
Normalized to
pH 8 (all organisms) and
25°C (invertebrates)
Cms NAD
33.59
4.884
14.5
21.73
1.349
62.67
3.565
33.60
4.009
24.49
6.500
29.35
4.662
40.68b
1.972
32.86
5.124
28.39a
2.927
Reference(s)
McCormick et al. 1984
Reinbold and Pescitelli 1982d
Smith etal. 1984
Broderius et al. 1985 at pH 6.5
Broderius et al. 1985 at pH 7.0
Broderius et al. 1985 at pH 7.5
Broderius et al. 1985 at pH 8.5
Thurston et al. 1983
May es etal. 1986
Swigert and Spacie 1983
ACR
6.878
1.941
16.11
17.58
8.380
3.768
6.295
20.63
6.413
9.700
SMACR
3.654
16.11
7.688
10.86
GMACR
7.671
7.688
10.86
122
-------
Table 8. Ordered Genus Mean Acute-Chronic Ratios
Rank
67
66
65
64
63
62
61
60
59
58
57
56
55
54
53
52
51
50
49
48
47
46
45
44
43
42
41
40
39
38
37
36
35
34
33
32
31
30
29
28
Genus
Monopterus
Erythromma
Philarctus
Stenelmis
Orconectes
Chironomus
Drunella
Gasterosteus
Asellus
Pacifastacus
Anguilla
Cottus
Gambusia
Callibaetis
Pimephales
Oreochromis
Salvelinus
Acipenser
Pachydiplax
Catostomus
Lumbriculus
Tubifex
Ictalurus
Helisoma
Salmo
Morone
Skwala
Xenopus
Crangonyx
Sander
Campostoma
Limnodrilus
Cyprinella
Physa
Enallagma
Chydorus
Lepomis
Cyprinus
Oncorhynchus
Rana
GMAV
Adjusted to pH=8
(all organisms)
and 25°C
(invertebrates only)
809.6
386.8
153.0
113.2
105.6
104.9
68.05
65.53
59.53
56.49
51.94
51.72
51.07
37.92
37.07
36.98
36.74
36.49
35.85
34.10
33.64
33.30
33.14
32.54
31.83
31.39
29.60
28.51
27.96
27.25
26.97
26.17
25.60
25.29
25.22
25.01
24.89
24.74
23.09
22.43
GMACR
10.86
<8.330
2.712
7.671
123
-------
Table 8. (continued)
Rank
27
26
25
24
23
22
21
20
19
18
17
16
15
14
13
12
11
10
9
8
7
6
5
4
O
2
1
Genus
Ceriodaphnia
Simocephalus
Pyganodon
Procambarus
Micropterus
Daphnia
Dendrocoelum
Poecilia
Etheostoma
Hybognathus
Pseudacris
Chasmistes
Notemigonus
Eriocheir
Musculium
Lymnaea
Deltistes
Actinonaias
Prosopium
Pleurocera
Potamopyrgus
Utterbackia
Epioblasma
Corbicula
Lampsilis
Villosa
Lasmigona
GMAV
Adjusted to pH=8
(all organisms)
and 25°C
(invertebrates only)
22.13
21.98
21.76
21.23
20.74
19.22
18.37
17.38
17.29
16.90
16.66
16.15
14.67
14.30
13.74
13.63
13.19
12.22
12.09
10.54
7.605
7.164
6.037
6.018
5.919
5.036
3.539
GMACR
1.832
7.688
4.850
>18.27
>6.129
124
-------
Table 9. Unused Acute Studies Potentially Influential for Freshwater Ammonia Criteria Development.
Reference:
Organism:
Reported or Normalized Acute
Value expressed as Total
Ammonia (mg N/L) at pH=8
and 25°C, where applicable
Rationale for Omission:
Anderson, E.G. 1948. The Apparent
thresholds of toxicity to Daphnia
magna for chlorides of various
metals when added to Lake Erie
water. Trans. Am. Fish. Soc. 78:96-
113.
Daphnia
magna
Normalized EC50 = 133.6
LC50 based on a non-standard (64 h) test
duration for species.
Babu, T.R., P. Surendranath and
K.V. Ramana Rao. 1987.
Comparative evaluation of DDT and
fenvalerate toxicity on Penaeus
indicus (H. Milne Edwards).
Mahasagar20(4):249-253.
Daphnia
magna
Reported LCSOs:
60 (25 h),
32 (50 h),
20 (100 h)
pH not reported - LCSOs could not be
normalized.
Black, M. 2001.Water quality
standards for North Carolina's
endangered mussels. Department of
Environmental Health Science,
Athens, GA.
Fusconaia
masoni
Normalized LC50 = 2.49
Other data for other species from this study was
used in Table 1. LC50 based on a 24 h (non-
standard) test duration.
Diamond, J.M., D.G. Mackler, WJ.
RasnakeandD. Gruber. 1993.
Derivation of site-specific ammonia
criteria for an effluent-dominated
headwater stream. Environ. Toxicol.
Chem. 12:649-658.
Daphnia
magna
Normalized LCSOs = 16.68, 33.56
Test duration not reported.
Dowden, B.F. 1961. Cumulative
toxicities of some inorganic salts to
Daphnia magna as determined by
median tolerance limits.
Proc. La. Acad. Sci. 23:77-85.
Daphnia
magna
Reported LCSOs:
161 (48 h),
206 (24 h)
pH not reported - LCSOs could not be
normalized.
125
-------
Reference:
Organism:
Reported or Normalized Acute
Value expressed as Total
Ammonia (mg N/L) at pH=8
and 25°C, where applicable
Rationale for Omission:
Dowden, B.F. and HJ. Bennett.
1965. Toxicity of selected
chemicals to certain animals. J.
Water Pollut. Control Fed.
37(9):1308-1316.
Daphnia
magna
Reported LCSOs:
202 (24 h),
423 (25 h),
161 (48 h),
433 (50 h),
67 (72 h),
50 (96 h),
202, 139 (100 h)
pH not reported - LCSOs could not be
normalized.
Lymnaea sp.
Reported LCSOs:
241(24h),
173 (48 h),
73 (72 h),
70 (96 h)
pH not reported - LCSOs could not be
normalized.
Ewell, W.S., J.W. Gorsuch, R.O.
Kringle, K.A. Robillard and R.C.
Spiegel. 1986. Simultaneous
evaluation of the acute effects of
chemicals on seven aquatic species.
Environ. Toxicol. Chem. 5(9):831-
840.
Daphnia
magna
Reported LC50 in paper = >100;
Reported LC50 in ECOTOX =
>20
Insufficient controls. pH that varied from 6.5-8.5
during the exposure. LC50 based on a 96 h (non-
standard) test duration.
Goudreau, S.E., RJ. Neves, and RJ.
Sheehan. 1993. Effects of
wastewater treatment plant effluents
on freshwater mollusks in the upper
Clinch River, Virginia, USA.
Hydrobiologia 252(3): 211-230.
Villosa iris
Normalized LC50 = 4.03
LC50 based on a 24 h (non-standard) test
duration.
Hazel, R.H., C.E. Burkhead and
D.G. Huggins. 1982. Development
of water quality criteria for
ammonia and total residual chlorine
Etheostoma
spectabile
Normalized LCSOs = 19.49, 16.56
Same data as in Hazel (1979) - see E. spectabile
in Table 1.
126
-------
Reference:
Organism:
Reported or Normalized Acute
Value expressed as Total
Ammonia (mg N/L) at pH=8
and 25°C, where applicable
Rationale for Omission:
for the protection of aquatic life in
two Johnson County, Kansas
Streams. In: J.G. Pearson, R.B.
Foster, and W.E. Bishop (Eds.),
Proc. Annu. Symp. Aq. Tox.,
ASTM STP 766, Philadelphia, PA:
381-388.
Hecnar, SJ. 1995. Acute and
chronic toxicity of ammonium
nitrate fertilizer to amphibians from
Southern Ontario. Environ. Toxicol.
Chem. 14(12):2131-2137.
Pseudacris
triseriata
triseria
Reported values:
100-dNOEC = 2.5,
100-dLOEC = 10
4-dLC50= 17
4-d NOEC = 5,
4-d LOEC = 45
pH was not reported - normalized effect
concentrations could not be calculated.
Hong, M., L. Chen, X. Sun, S. Gu,
L. Zhang and Y. Chen. 2007.
Metabolic and immune responses in
Chinese mitten-handed crab
(Eriocheir sinesnsis) juveniles
exposed to elevated ambient
ammonia. Comp. Biochem. Phys. C.
145:363-369
Eriocheir
sinesnsis
Normalized LCSOs:
65.27 (24 h),
56.44 (48 h),
40.47 (72 h),
31.04 (96 h)
Used municipal water as test water with no
chemical description of sourcewater quality. No
water quality information provided for crab farm
where animals were obtained. No control to
calculate LCSOs.
Home, F.R. and S. Mclntosh. 1979.
Factors influencing distribution of
mussels in the Blanco River of
Central Texas. Nautilus 94(4): 119-
133.
Cyrtonaias
tampicoensis
Normalized LC50 = 4.12
LC50 based on a 7 d (non-standard) test duration.
Toxolasma
texasensis
Normalized LC50 = 4.12
LC50 based on a 7 d (non-standard) test duration.
Corbicula
manilensis
Normalized LC50 = 4.12
LC50 based on a 7 d (non-standard) test duration.
Kaniewska-Prus, M. 1982. The
Effect of ammonia, chlorine, and
chloramine toxicity on the mortality
Daphnia
magna
Normalized LC50 = 0.30
LC50 based on a 24 h (non-standard) test
duration.
127
-------
Reference:
Organism:
Reported or Normalized Acute
Value expressed as Total
Ammonia (mg N/L) at pH=8
and 25°C, where applicable
Rationale for Omission:
ofDaphnia magna Straus. Pol.
Arch. Hydrobiol. 29(3/4):607-624.
Khatami, S.H., D. Pascoe and M.A.
Learner. 1998. The acute toxicity of
phenol and unionized ammonia,
separately and together, to the
ephemeropteran Baetis rhodani
(Pictet). Environ. Pollut. 99: 379-
387.
Baetis rhodani
Normalized 24-hr LC50 = 103.6
Species not resident in North America. LC50
based on a 24 h (non-standard) test duration.
Lee, D.R. 1976. Development of an
invertebrate bioassay to screen
petroleum refinery effluents
discharged into freshwater. Ph.D.
Thesis, VAPolytech. Inst. 108 pp.
Daphniapulex
Normalized LCSOs:
71,22, 35, 66, 85(24 h);
68, 18, 28, 35, 66(48 h);
13, 14, 29(96 h)
D. pulex used in the tests were 5-6 days old
(instead of <24 hold).
Mangas-Ramirez, E. S.S.S. Sarma
and S. Nandini. 2001. Acute and
chronic toxicity of ammonium
chloride to the cladoceran Daphnia
pulex Leydig in relation to algal
food density. Bull. Environ.
Contam. Toxicol. 67:834-840.
Daphniapulex
Normalized LCSOs = 32.36,
35.57,36.28
LC50 based on a 24 h (non-standard) test
duration.
Meyer, J.S. and J.A. Hansen. 2002.
Sub chronic toxicity of low
dissolved oxygen concentrations,
elevated pH, and elevated ammonia
concentrations to Lost River
suckers. Trans. Amer. Fish. Soc.
131: 656-666.
Deltistes
luxatus
Normalized LCSOs =15.81,
10.21, 18.41
LC50 based on a 48 h (non-standard) test
duration.
Morgan, W.S.G. 1979. Fish
Locomotor Behavior Patterns as a
Micropterus
salmonides
Normalized EC50 = 1.17
Acute toxicity evaluated electronically based on
activity. Exposure was only 24 h (non-standard)
128
-------
Reference:
Organism:
Reported or Normalized Acute
Value expressed as Total
Ammonia (mg N/L) at pH=8
and 25°C, where applicable
Rationale for Omission:
Monitoring Tool. J. Water Pollut.
Control. Fed. 51(3):580-589.
in test duration. Concentrations were nominal.
Morgan, W.S.G. 1976. Fishing for
toxicity: Biological automonitor for
continuous water quality control.
Effl. Water Treat. J. 16(9):471-475.
Micropterus
salmonides
Normalized EC50 = 1.17
Added nominal concentrations equivalent to 48 h
LC50 from previous literature values, then
monitored opercular rhythm activity for 24 h.
Morgan, W.S.G., and P.C. Kuhn.
1974. A method to monitor the
effects of toxicants upon breathing
rate of largemouth bass
(Micropterus salmoides Lacepede).
Water Res. 8(l):67-77
Micropterus
salmonides
Lacepede
Normalized ECSOs:
25.68(11 h),
7.29 (22 h),
25.68 (23 h),
0.36 (44 h)
Similar to Morgan (1976). This is not an actual
toxicity test. Rather, it is a test of a monitoring
system that relates nominal LC50 concentrations
(based on literature values), to breathing rate
monitored over 24 h.
Morgan, W.S.G. 1978. The use of
fish as a biol. sensor for tox. comp.
in potable water. Prog. Water Tech.
10:395-398.
Micropterus
salmonides
Normalized LC50 = 2.12
Similar to other Morgan studies listed in this
table. Nominal ammonia concentrations based on
literature LC50 concentrations are added to tanks,
and breathing rate and activity level are
monitored electronically for 24 h.
Passell, H.D., C.N. Dahm and EJ.
Bedrick. 2007. Ammonia modeling
for assessing potential toxicity to
fish species in the Rio Grande,
1989-2002. Ecol. Appl. 17(7):2087-
2099.
Hybognathus
amarus
Secondary data; reported LC50
from Buhl 2002 =1.01 mg/L
NH3-N
In this study the frequency of acute ammonia
exceedences were modeled by relating discharge,
pH, temperature, and stream ammonia
concentrations to literature LC50 values.
Rubin, AJ. and G.A. Elmaraghy.
1977. Studies on the toxicity of
ammonia, nitrate and their mixtures
to guppy fry. Water Res.
ll(10):927-935.
Poecilia
reticulata
Normalized LCSOs = 37.7, 29.7,
32.6
Same 96 h LCSOs as reported in Rubin and
Elmaraghy (1976) - see Table 1.
Tabata, K. 1962. Toxicity of
ammonia to aquatic animals with
Poecilia
reticulata
Normalized LCSOs = 28.76, 23.05
LCSOs based on a 24 h (non-standard) test
duration.
129
-------
Reference:
Organism:
Reported or Normalized Acute
Value expressed as Total
Ammonia (mg N/L) at pH=8
and 25°C, where applicable
Rationale for Omission:
reference to the effect of pH and
carbonic acid. Bull. Tokai. Reg.
Fish. Res. Lab. 34:67-74.
Tonapi, G.T. and G. Varghese.
1987. Cardio-Physiological
Responses of Some Selected
Cladocerans to Three Common
Pollutants. Arch. Hydrobiol.
110(l):59-65.
Daphnia
carinata
Reported value = 0.5%
pH and temperature were not reported.
Value based on a physiological endpoint obtained
from a 15 minute exposure.
Watton, AJ. and H.A. Hawkes.
1984. The acute toxicity of
ammonia and copper to the
gastropod Potamopyrgus jenkimi
(Smith). Environ. Pollut. Ser. A
36:17-29.
Potamopyrgus
jenkinsi
Normalized ECSOs:
6.47 (48 h),
4.18 (96 h)
Species not resident inNorth America.
Weltering, D.M., et al. 1978.
Predator-prey interactions of fishes
under the influence of ammonia.
Trans. Am. Fish. Soc. 107(3):500-
504.
Micropterus
salmonides
Normalized value:
LOEC = 7.12, 15.68
Alternative endpoint obtained from a 10 d
exposure where pH and temperature were not
reported.
130
-------
Table 10. Unused Chronic Studies Potentially Influential for Freshwater Ammonia Criteria Development.
Reference:
Organism:
Reported or Normalized
Chronic Value expressed as
Total Ammonia
(mg N/L) at pH=8 and 25°C,
Where Applicable
Rationale for Omission:
Biswas, J.K., D. Sarkar, P. Chakraborty,
J.N. Bhakta and B.B. Jana. 2006. Density
dependent ambient ammonia as the key
factor for optimization of stocking
density of common carp in small holding
tanks. Aquacult. 261(3):952-959
Cyprinus
carpio
N/A
Fry were stocked at different densities
at a single initial ammonia
concentration. Ammonia
concentration was allowed to increase
during the study as a function of
excretion, which varied across
densities, and all tanks received
equivalent fertilizer amendments
during the study.
Colt, J. and G. Tchobanoglous. 1978.
Chronic exposures of channel catfish,
Ictaluruspunctatus, to ammonia: Effects
on growth and survival. Aquaculture
15(4):353-372.
Ictalurus
punctatus
Normalized NOEC = 8.72
One of the chronic tests with channel
catfish was a 31-day test of juvenile
growth and survival by Colt and
Tchobanoglous (1976). These authors
did not provide complete data on
survival at each concentration, but the
information provided indicated that (a)
at 5.0 mg N/L (total ammonia) and
below, mortality averaged about 2%,
(b) at 5.7 mg N/L mortality was
between 28 and 45% (based on a
reported range of 11 to 62% mortality
in three replicates), (c) at 6.8 mg N/L
mortality was 83%, and (d) at 9.5 mg
N/L and above mortality was 100%.
This indicates that the LC20 was
between 5.0 and 5.7 mg N/L (at
pH=8.35 and T=28°C), or between 8.7
and 9.9 mg N/L when adjusted to
131
-------
Reference:
Organism:
Reported or Normalized
Chronic Value expressed as
Total Ammonia
(mg N/L) at pH=8 and 25°C,
Where Applicable
Rationale for Omission:
pH=8 based on the chronic pH
relationship. While this test was not
used in deriving the GMCV, it did
indicate that juvenile channel catfish
were as sensitive as early life stages
and was included as support that the
GMCV derived from the early life
stage tests was reasonable. In fact, if
the factor of 1.5 is applied to this
number to make it more applicable to
longer chronic exposures, the GMCV
would be around 6.2 mg N/L — below
the GMCV (8.84 mg N/L) derived
from the early life stage tests. Because
the 1.5 adjustment factor has
questionable applicability to channel
catfish, the GMCV from Table 5 is the
most appropriate number to use for
both early-life-stage and juvenile
sensitivity.
DeGraeve, G.M., W.D. Palmer, E.L.
Moore, JJ. Coyle and P.L. Markham.
1987. The effect of temperature on the
acute and chronic toxicity of un-ionized
ammonia to fathead minnows and
channel catfish. Battelle, Columbus, OH.
Pimephales
promelas
Normalized EC20s = 9.45,
9.72, 19.35, 17.54
Study evaluated the effect of ammonia
on 30-day survival of juvenile fathead
minnows at several temperatures. The
tests at 15 and 20°C did not have
ammonia concentrations sufficiently
high to cause effects, but survival was
significantly decreased at the higher
concentrations of ammonia in the tests
run at 6, 10, 25, and 30°C. At 30°C,
the mean measured DO concentration
132
-------
Reference:
Diamond, J.M., D.G. Mackler, WJ.
Rasnake andD. Gruber. 1993. Derivation
of site-specific ammonia criteria for an
effluent-dominated headwater stream.
Environ. Toxicol. Chem. 12:649-658.
Organism:
Ictalurus
punctatus
Crangonyx sp.
Procambarus
clarkii
Reported or Normalized
Chronic Value expressed as
Total Ammonia
(mg N/L) at pH=8 and 25°C,
Where Applicable
Normalized NOEC = 0.23
Normalized NOEC = 5. 16
Normalized NOEC = 5.47
Rationale for Omission:
in most of the treatments was below
5.5 mg/L, but it was above 60% of
saturation in all treatments. EC20s
based on survival were calculated to
be 11.9, 13.8, 39, and 39 mg N/L at
temperatures of 6.0, 10.0, 25.4, and
30.2°C and pHs of 7.83, 7.73, 7.35,
and 7.19, respectively. When adjusted
to pH=8, the EC20s are 9.45, 9.72,
19.35, and 17.54 mgN/L, respectively.
Although these EC20s were used to
assess the effect of temperature on the
chronic toxicity of ammonia, they
were not used in the derivation of the
SMCV in the 1999 ALC document
because they indicate that 30-day
survival of juveniles is not as sensitive
to ammonia as the life-cycle and early
life-stage tests available for the species
from other studies.
According to the 1999 update,
problems with the channel catfish
chronic tests precluded effective
use of those data.
The NOEC based on a 21-d (non-
standard) chronic exposure. The
dissolved oxygen level in this test was
abnormally low.
The NOEC based on a 21-d (non-
standard) chronic exposure. The
133
-------
Reference:
Organism:
Reported or Normalized
Chronic Value expressed as
Total Ammonia
(mg N/L) at pH=8 and 25°C,
Where Applicable
Rationale for Omission:
dissolved oxygen level in this test was
abnormally low.
Diamond, J.M., SJ. Klaine and J.B.
Butcher. 2006. Implications of pulsed
chemical exposures for aquatic life
criteria and wastewater permit limits.
Envir. Sci. & Tech. 40(16):5132-5138.
Daphnia
magna
Growth and survival endpoints
assessed following intermittent
exposures in static renewal systems at
concentrations too closely spaced to
construct a dose-response relationship.
Pimephales
promelas
Omitted for the same reasons as was
Daphnia magna.
Flis, J. 1963.
Anatomicohistopathological changes
induced in carp (Cyprinus carpio L.) by
ammonia water. Part 1. Effects of toxic
concentrations. ActaHydrobiol.
10(l/2):205-224.
Cyprinus
carpio
Normalized results:
l-dNOEC = 23.98
l-dLOEC = 24.85
35-dLOEC = 3.62
Two static renewal tests of non-
standard test durations (1 and 35 d).
Hermanutz, R.O., S.F. Hedtke, J.W.
Arthur, R.W. Andrew and K.N. Allen.
1987. Ammonia effects on
microinvertebrates and fish in outdoor
experimental streams. Environ. Pollut.
47:249-283.
Pimephales
promelas
Normalized NOEC = 3.92
Hermanutz et al. (1987) studied the
survival, growth, and reproduction of
fathead minnows in experimental
streams. Two generations were each
exposed for periods of approximately
two months, during which pH
averaged 7.5 to 7.7 and temperature
averaged 19.6°C. Deleterious effects
on biomass were not apparent at or
below the highest tested concentration
of ammonia, which was 3.92 mg N/L
when adjusted to pH=8. These results
are not included because they are from
a field study where ammonia
concentrations were highly variable.
134
-------
Reference:
Organism:
Reported or Normalized
Chronic Value expressed as
Total Ammonia
(mg N/L) at pH=8 and 25°C,
Where Applicable
Rationale for Omission:
Ictalurus
punctatus
Normalized NOEC = 1.80
Omitted for the same reasons as was
Pimephales promelas.
Hernandez, C., M. Martin, G. Bodega, I.
Suarez, J. Perez and B. Fernandez. 1999.
Response of carp central nervous system
to hyperammonemic conditions: An
immunocytochemical study of glutamine
synthetase (GS), glial fibrillary acidic
protein (GFAP) and 70 kDa heat-shock
protein (HSP70). Aquat. Tox.
45(2/3): 195-207.
Cyprinus
carpio
Normalized values:
60-dLOEC = 26.01
48-hr 100% lethal cone. =
52.03
Alternative endpoints used to assess
toxicity not defensible; effects based
on nominal concentrations from a
static renewal test. Chronic effects
were observed at a nominal
concentration of 4mM after a 60 d
exposure. One hundred percent
lethality was observed at a nominal
concentration of 8mM after 48 h.
Manissery, J.K., and M.N. Madhyastha.
1993. Haematological and
histopathological effect of ammonia at
sublethal levels on fmgerlings of
common carp Cyprinus carpio. Sci. Tot.
Envir. (Suppl.):913-920.
Cyprinus
carpio
Normalized values:
LOECs = 2.73 and 8.92
Effects of ammonia were based on
nominal concentrations from a 45 d
static renewal exposure.
Meador, M.R. and D.M. Carlisle. 2007.
Quantifying tolerance indicator values
for common stream fish species of the
United States. Ecol. Indicators 7:329-
338.
Multiple
species
N/A
No toxicity tests were performed in
this study. Rather, field surveys were
conducted classifying species as
tolerant or sensitive to a suite of
abiotic stressors following statistical
(PCA) analysis.
Ram, R.N. and A.G. Sathyanesan. 1986.
Inclusion bodies: Formation and
degeneration of the oocytes in the fish
Channapunctatus (Bloch) in response to
ammonium sulfate treatment. Ecotoxicol.
Environ. Saf ll(3):272-276.
Channa
punctatus
N/A
Species is not resident to North
America.
Sadler, K. 1981. The toxicity of ammonia
Anguilla
Normalized NOEC = 4.91
The first five weeks of this test had
135
-------
Reference:
Organism:
Reported or Normalized
Chronic Value expressed as
Total Ammonia
(mg N/L) at pH=8 and 25°C,
Where Applicable
Rationale for Omission:
to the European eel (Anguilla anguilla
L.). Aquaculture 26(1/2):173-181.
anguilla
high mortality rates, leaving some
tanks with too few survivors to
estimate growth
Smith, C.E. 1984. Hyperplastic lesions of
the primary meninx of fathead min., P.
promelas, induced by ammonia: Sp. pot.
for carcin. test. In: K.L. Hoover (ed.),
Use of small fish species in
carcinogenicity testing, Monogr. Ser.
Natl. Cancer Inst. No. 65, Nffl Publ. No.
84-2653, U.S. Dept. Health Hum. Serv.,
Natl. Cancer Inst., Bethesda, MD, pp.
119-125.
Normalized chronic values:
18.26(60d)
32.97 (133 d)
60 d chronic value was based on
histological endpoints. Chronic effects
were based on nominal concentrations.
Suski, C.D., J.D. Kieffer, S.S. Killen and
B.L. Tufts. 2007. Sub-lethal ammonia
toxicity in largemouth bass. Comp.
Biochem. Phys. A. 146:381-389.
Micropterus
salmonides
Normalized LOEC =
11.43 (swimming and
ventilation rates)
A variety of chronic endpoints were
assessed via exposure to only two
ammonia concentrations. Effects were
primarily assessed as a function of a80
ctivity level of varying duration.
Zischke, J.A. and J.W. Arthur. 1987.
Effects of elevated ammonia levels on
the fingernail clam, Musculium
transversum, in outdoor experimental
streams. Arch. Environ. Contam.
Toxicol. 16(2):225-231.
Musculium
transversum
Normalized LOEC = 2.07
(survival)
This was a flow-through, measured
mesocosm experiment performed in
the field. The test concentrations
varied during the length of the
experiment.
136
-------
Appendix A
EPA Final Draft Position Statement on:
Acute Toxicity Tests using Freshwater Mussels
(dated 04-28-09)
137
-------
Aquatic Life Criteria Coordinating Committee 4-28-09
Acute Toxicity Tests using Freshwater Mussels
Position statement:
When water quality criteria for aquatic life are derived, results of 96-hr acute toxicity tests using juveniles
of freshwater mussels will be reviewed for acceptability in the same way that results of acute toxicity tests
using other aquatic animals are reviewed for acceptability. Results of acute toxicity tests using glochidia of
freshwater mussels will be reviewed for acceptability after USEPA's Aquatic Life Criteria Coordinating
Committee decides that it is possible to derive defensible species-specific approximations of the duration of
the free-living portion of the glochidia life stage of about 95% of the glochidia that attach to hosts.
Rationale:
For the purposes of deriving aquatic life criteria, acute toxicity tests should usually be performed with
young organisms because (i) they are often more acutely sensitive than adults of the same species and (ii)
the acute sensitivity of a species to a pollutant is most usefully determined using the most sensitive life
stage of the species. There are two young life stages of freshwater mussels: glochidia and juveniles. The
juvenile life stage of freshwater mussels lasts for at least several weeks and so 96-hr acute toxicity tests
with juvenile freshwater mussels are ordinary acute toxicity tests and will be reviewed for acceptability in
the same way that acute toxicity tests with other aquatic animals are reviewed for acceptability.
The situation is more complicated for the glochidia life stage because, after a glochidium becomes free-
living in the water column, it must attach to a host fish in order to develop into an encysted parasite. For
those glochidia that become encysted parasites, the glochidia life stage is free living in the water column
only from the time when it enters the water column until the time when it attaches to a host; the average
duration of the free-living portion of the glochidia life stage differs from one species of freshwater mussel
to another. Unfortunately, an LC50 determined using glochidia sometimes decreases substantially as the
duration of the test increases from, for example, 6 hr to 24 hr to 96 hr. The most defensible duration of the
glochidia test is based on the species-specific duration of the free-living portion of the glochidia life stage
of about 95% of the glochidia that attach to hosts. Such species-specific information is not available for
any species of freshwater mussel. Until defensible species-specific approximations of the duration of the
free-living portion of the glochidia life stage of about 95% of the glochidia that attach to hosts are obtained,
results of acute toxicity tests with glochidia will not be used in the derivation of water quality criteria for
aquatic life.
In order to facilitate use of results of acute toxicity tests with glochidia in the derivation of water quality
criteria for aquatic life, the Aquatic Life Criteria Coordinating Committee wants to obtain defensible
species-specific approximations of the duration of the free-living portion of the glochidia life stage of about
95% of the glochidia that attach to hosts. ASTM (2006) and Cope et al. (2008) have been cited as
providing useful information concerning toxicity tests with glochidia. All of the relevant information given
in ASTM Standard E 2455 - 06 (Standard Guide for Conducting Laboratory Toxicity Tests with
Freshwater Mussels) concerning appropriate species-specific durations for toxicity tests with glochidia is
contained in the following excerpts:
a. In Section 4.1.1 it says:
For most species, the duration of a toxicity test conducted with glochidia should be up to 24 h with
survival measured at 6 and 24 h. Control survival is typically >90 % at the end of 24-h toxicity
tests conducted with glochidia. Longer duration toxicity tests with glochidia (for example, 48 h)
138
-------
can be conducted as long as control survival >90 % is achieved. For example, toxicity tests
conducted for 48 h with glochidia might be used for species for which juvenile mussels are not
readily available for testing or for species with a life history where glochidia are released into the
water column and remain viable for days before attaching to a host (in contrast to species that
release glochidia in mucus strands or in conglutinates).
b. In Section 10.1.4 it says:
The successful transfer of mature glochidia to a suitable host constitutes a critical event in the life
cycle of most freshwater mussels. Various adaptations have evolved to facilitate this process.
High levels of mortality occur during the passage of glochidia from the female mussel to the host
fish due to the low incidence offish host contact. Once encysted in the gill, glochidia may be
relatively protected from in situ exposure [to] contaminants in water (Jacobson et al 1997). The
method of host infestation greatly varies among species. While some species simply broadcast
glochidia into the surrounding water to haphazardly come into contact with the appropriate host,
the process is more intricate and direct for other species. For example, females in the genus
Lampsilis have an extension of the mantle tissue that resembles a small fish or invertebrate
complete with eye spots and appendages. This lure is displayed outside the shell between the
valves and is twitched repetitively to attract a predaceous fish host. The host is infested while
attempting to eat the lure when the marsuplial gills of the female are ruptured (Kramer 1970,
Barnhart and Roberts 1997). Some species release conglutinates (small structures containing
glochidia) freely into the water. In many conglutinate-producing species (for example, Elliptic,
Fusconia, Pleurobema, Plethobasus, Cyprogenia, and Quadrula), conglutinates are released as
cohesive masses made up of unfertilized eggs that hold together mature glochidia. Conglutinates
of some species (for example, Ptychobranchus) are made up of gelatinous material that enclose
large numbers of glochidia (Hartfield and Hartfield 1996). Conglutinates may resemble prey
items of the host fish; the host fish are infested with glochidia when fish attempt to eat
conglutinates (Chamberlain 1934, Barnhart and Roberts 1997, Jones et al 2004).
c. Section Al .2.2 is almost identical to Section 4.1.1.
d. In Section Al.2.5 it says:
Toxicity tests with glochidia have been conducted for up to 144 h, but 24 and 48-h exposures are
most often used (Table Al. 1). The relatively short duration of toxicity tests with glochidia is
based on the relatively short duration between release of glochidia into the water column and
encystment on the host and is based on the relatively short survival times of glochidia after
isolation from the female mussel (Table A1.2). If the life history of a particular species in not
known (for example, the host required for encystment or how long glochidia released from a
female mussel can remain in the water column before encysting on a host), it might be appropriate
to conduct toxicity tests with glochidia for longer than 24 h as long as 90 % control survival can
be achieved at the end of the test.
e. In Section Al.2.6 it says:
The time between release of glochidia from the marsupium of the female mussel to attachment of
these glochidia on a host may take only a few seconds for some species (10.1.4), but hours are
required for the gill tissue of a fish to migrate to form a cyst around the glochidia. During that
time, the glochidia may be exposed to water-borne toxicants. Many anodontinae species release
glochidia into water column that remain viable for days before infesting a host fish. Therefore, a
prolonged glochidia test would have ecological relevance for these species. Other species release
glochidia in mucus strands that coat the bottom or remain suspended on vegetation, waiting for
their hosts to swim by and still other species release glochidia packaged in conglutinates that serve
as a lure to host fish. Hence, glochidia of these species may also be in water for extended periods
of time; however, it is not known how exposure to water-borne contaminants would be influenced
by the mucus or conglutinate surrounding the glochidia.
139
-------
All of the relevant information given in Cope et al. (2008, Differential exposure, duration, and sensitivity of
unionoidean bivalve life stages to environmental contaminants; J. N. Am. Benthol. Soc. 27(2):451-462)
concerning appropriate species-specific durations for toxicity tests with glochidia is contained in the
following excerpts:
a. "Toxicity tests with glochidia generally are conducted for 24 h (ASTM 2006). This test duration is
based largely on the presumed length of time glochidia are in the water between release from the
female and encystment onto a host fish and their survival time in water. A 24-h test duration ensures
90% survival in control treatments at the end of the test (required by ASTM protocols; ASTM 2006,
Ingersoll et al. 2007). The actual longevity of glochidia after release from the female and before
attachment onto a host fish varies with species and water temperature (Zimmerman and Neves 2002),
but can range from several days to several weeks (ASTM 2006; Ingersoll et al. 2007)."
b. "For example, we measured survival of glochidia ... More than 90% of the species tested had viable
glochidia for at least 24 h after release from female mussels (Fig 3 A,B)."
c. "However, the duration of a toxicity tests with glochidia may be adjusted to longer or shorter than 24
h, based on the life history of the particular species of interest (ASTM 2006). A portion of the
glochidia released from some species with mantle-flap lure display or other fish-attracting behaviors
might attach to host fish within seconds to hours (Ingersoll et al. 2007)."
d. "Moreover, many species of mussels snare or lure host fish and increase the probability of infestation
by releasing glochidia contained within mucus strands or conglutinate packets resembling prey items
offish (Walters 2007). Thus, glochidia of these species might remain in the water or on the sediment
surface for extended periods of time. No studies are available on the toxicity of waterborne or
sediment-associated contaminants to glochidia contained in these structures."
e. "Based on the available information for glochidia, the primary route of exposure for contaminants is
through surface water, and occurrence of the exposure can be when the larvae are free in the water or
packaged in mucus and conglutinates over the course of seconds to days."
USEPA's Aquatic Life Criteria Coordinating Committee has the following comments:
1. When water quality criteria for aquatic life are derived, USEPA does not automatically accept all
toxicity tests that are performed according to an ASTM standard or according to "Standard Methods".
USEPA reviews results of all aquatic toxicity tests for acceptability.
2. Aquatic species that are critical, keystone, threatened, endangered, of concern, unique, rare, and/or
imperiled can receive special consideration in the derivation of site-specific water quality criteria for
aquatic life, but not in the derivation of national water quality criteria for aquatic life.
3. There is no evidence that glochidia that are in mucus, in conglutinates, in lures, or attached to a host
are exposed to water-borne pollutants; such exposure is hypothetical. Most uptake of pollutants by
aquatic organisms occurs via gills and food.
4. Neither ASTM (2006) nor Cope et al. (2008) gives much defensible information concerning
appropriate species-specific durations for toxicity tests with glochidia.
5. ASTM (2006) says that a 24-hr toxicity test should be performed with glochidia and survival should be
measured at 6 and 24 hr, but it does not say how the 6-hr data and the 24-hr data should be used.
6. Figures 3 A and 3B in Cope et al. (2008) show that glochidia of about five species had more than 10%
mortality in less than 24 hr and a few more species had more than 10% mortality in less than 48 hr. It
appears that glochidia of several species would have less than 90% survival in a 24-hr test.
7. Studies of the viability of free-living glochidia provide upper limits on the duration of the free-living
portion of the glochidia life stage of glochidia that attach to hosts.
8. For glochidia that attach to hosts, there is a major difference between (i) glochidia that are in mucus,
conglutinates, and lures and (ii) glochidia that are broadcast.
140
-------
a. Glochidia are in mucus, conglutinates, and lures in order to facilitate rapid attachment to hosts;
attachment apparently often begins within seconds after the glochidia become free-living. It is
quite possible that the duration of the free-living portion of the glochidia life stage of about 95%
of the glochidia in mucus, conglutinates, and lures is substantially less than 6 hours.
b. Other than the upper limits from laboratory studies of the viability of free-living glochidia, it is
possible that, for species of freshwater mussels that broadcast glochidia, no defensible information
is available concerning the duration of the free-living portion of the glochidia life stage of
glochidia that attach to hosts.
141
-------
Appendix B
EPA Final Draft Position Statement on:
Toxicity Tests on Ammonia using Hyalella azteca
(dated 04-28-09)
142
-------
Aquatic Life Criteria Coordinating Committee 4-28-09
Toxicity Tests on Ammonia using Hyalella azteca
Position statement:
Neither a Species Mean Acute Value nor a Species Mean Chronic Value for H. azteca should be used in the
derivation of a freshwater aquatic life criterion for ammonia at this time.
Rationale:
Several laboratories have reported regular or intermittent difficulty obtaining acceptable survival and
growth of H. azteca during testing and culturing. Although some waters seem to be usually acceptable, it is
not known why some of these waters work and others don't. Studies are currently being conducted in an
attempt to develop waters and/or foods that will give improved survival, growth, and/or reproduction of this
species, but much uncertainty remains. Although several water quality characteristics might be important,
it seems reasonably certain that, at a minimum, chloride, and possibly bromide, are important to this
species, as discussed in the following paragraphs.
Any consideration of toxicity tests using H. azteca should take into account the information that is now
available concerning the possible importance of chloride to this species.
a. Smith et al. (1997) said that when they used KC1 as a reference toxicant for acute toxicity tests using
H. azteca, survival in the control treatments was never >70%, but survival in the lowest tested
concentration of KC1 was >80%. These tests used moderately hard reconstituted water, which
contained 2 mg Cl/L. When they used a reformulated moderately hard reconstituted water that
contained 34 mg Cl/L, it gave acceptable control survival in 96-hr tests. There is no indication that an
attempt was made to determine the minimum acceptable concentration of chloride and/or the optimum
concentration of chloride.
b. Soucek (2007) studied the effect of chloride on the toxicity of sulfate to H. azteca and Ceriodaphnia
dubia. With H. azteca, as the concentration of chloride increased from 5 to 25 mg/L, the LC50 for
sulfate increased substantially, but as the concentration of chloride increased from 100 to 500 mg/L,
the LC50 for sulfate decreased substantially. With C. dubia, as the concentration of chloride increased
from 5 to 25 mg/L, the LC50 for sulfate increased slightly, but as the concentration of chloride
increased from 100 to 500 mg/L, the LC50 for sulfate decreased substantially. The LCSOs for sulfate
at 100 mg Cl/L were slightly higher than at 25 mg Cl/L for both species, but no tests were performed
with either species at concentrations of chloride between 25 and 100 mg Cl/L. One possible
interpretation of these results is that (i) the healthiness of H. azteca increased as the concentration of
chloride increased from 5 to 25 mg/L and (ii) H. azteca was about as healthy at 100 mg Cl/L as at 25
mg Cl/L. It is interesting that the concentration of chloride in the Smith et al. (1997) reformulated
moderately hard reconstituted water is between 25 and 100 mg/L.
c. On page 357 of Borgmann (1996) it says "Survival was substantially improved by the addition of
NaCl, but was not improved further by the addition of KC1"; however, the NaCl addition raised the
concentration of chloride from 0 to 21.3 mg Cl/L, whereas the further addition of KC1 only raised the
concentration of chloride from 21.3 mg Cl/L to 22.7 mg Cl/L. This is not a valid test of the possible
usefulness of concentrations of chloride greater than 21.3 mg Cl/L.
d. The tap water that was successfully used by Borgmann (1996) contained 26 mg Cl/L and Borgmann's
recommended SAM-5S water contains 73 mg Cl/L, both of which are between 25 and 100 mg/L. The
143
-------
higher concentration of chloride in SAM-5S water is due to the use of CaCb as the source of calcium
because it is more soluble than CaSC>4 and CaCCb.
e. Lasier et al. (1997) reported that a toxicity test on sodium chloride using H. azteca produced a 96-hr
LC50 of 3947 mg Cl/L in moderately hard reconstituted water.
It appears that (i) H. azteca is not healthy in waters having low concentrations of chloride, (ii) low
concentrations of chloride increase the sensitivity of this species to sulfate, and (iii) the mitigating
concentrations of chloride are much lower than concentrations that are acutely toxic to H. azteca.
Further, any consideration of toxicity tests using H. azteca should take into account the information that is
now available concerning the possible importance of bromide to this species.
a. Borgmann (1996) said that H. azteca requires bromide and recommended 0.8 mg bromide/L. The
concentration of bromide was not measured in the tap water that was successfully used by Borgmann,
but the tap water is from Lake Ontario. Tiffany et al. (1969) reported that the concentration of bromide
was 0.047 mg/L in Lake Ontario water and 0.013 mg/L in Lake Superior water. Borgmann's
comparison of various concentrations of bromide used concentrations that differed by a factor often.
The concentration of bromide in the waters used by Smith et al. (1997) and Soucek (2007) is not
known.
b. Borgmann et al. (2005a) cultured H. azteca in dechlorinated Burlington City tap water and performed
acute toxicity tests with H. azteca in dechlorinated Burlington City tap water and in a mixture of 10%
dechlorinated tap water and 90% deionized water. Even though these two waters potentially contained
1/17 and 1/170 the concentration of bromide recommended by Borgmann (1996), Borgmann et al.
(2005a) apparently were comfortable using them for culturing and testing H. azteca.
c. Soucek (personal communication to C. Stephan) said that when he transferred H. azteca from a culture
in Smith et al. water to Borgmann water, the organisms did not do well. In contrast, when he slowly
changed the water from Smith et al. water to Borgmann water, the organisms survived, grew, and
reproduced.
d. Borgmann et al. (2005b) performed toxicity tests on copper using H. azteca in both artificial media and
in dechlorinated Burlington City tap water. It was reported that "CaBr2 was added to the artificial
media to give a constant ratio of 0.01 mole Br~ per mole of Ca2+ because Br is essential to Hyalella and
is required in combination with Ca". When Stephan asked Borgmann (via email) the justification for
"0.01 mole Br per mole of Ca", he replied (via email):
A 1:1000 ratio of Br to Ca is probably sufficient (see Fig. 2 in our 1996 paper), but we go with
1:100 just to be sure we have enough Br. We keep the Br to Ca ratio constant because Hyalella do
well in both Lake Ontario water and in 10% Lake Ontario Water + 90% distilled water, however,
they do not survive well in 10% Lake Ontario water if CaC12 is added to bring the Ca back to it's
original level (roughly 1 mM Ca, with Br estimated at 0.6/10 uM, for a Br to Ca ratio of about 0.6
to 10000). This suggests that either the Ca/Br ratio is critical, or that the Br/Cl ratio is important
(i.e., Cl might interfere with Br's role). Since Ca is usually added as CaCb, we need to beef up the
Br concentration whenever we add CaCb.
The information provided by Borgmann does not provide a valid basis for making a decision regarding the
possible importance of bromide to H. azteca.
Another possible complication is the range of surface waters inhabited by H. azteca and the diversity that
apparently exists within what is classified as "H. azteca" (Alcocer et al. 1998; Colburn 1988; France 1992;
Galat et al. 1988; Thomas et al. 1997; Wellborn and Cothran 2004; Wellborn et al. 2005; Witt et al. 2006;
Wollheim and Lovvorn 1995).
Seven documents report results of toxicity tests on ammonia using H. azteca:
144
-------
1. Sarda (1991) says that the tests were 96 hr in the text, but pages 178 and 179 only give survival after
48 hr. There is nothing to imply that the tests were renewal or flow-through, so they were probably
static. The test material was ammonium chloride. It is said that pH was altered but it does not say how
and no results are given for H. azteca at various values of pH. Temperature was measured daily
whereas pH was measured at the beginning and end of the tests. Total ammonia was measured using
an electrode but it doesn't say when the measurements were made. Tests were performed in two
waters (a reconstituted water and a creek water) that differed with respect to pH and hardness.
Hardness, alkalinity, and pH changed substantially during the tests. Control survival was acceptable.
The concentration of chloride in the creek water is not known. The formula for preparing the
reconstituted water is given in Appendix A; one of the ingredients is Perrier water and
www.usa.perrier.com says that the concentration of chloride in Perrier water is 26 mg/L. Because the
test material was ammonium chloride, the concentration of chloride differed from one treatment to
another. The results of these tests should not be used in the derivation of aquatic life criteria because,
among other things, hardness, alkalinity, and pH changed substantially during the tests and the
concentration of chloride changed from one treatment to another.
2. Borgmann (1994) performed a variety of toxicity tests, two of which were 10-week water-only life-
cycle toxicity tests in which the test solutions were renewed weekly. Ammonia was measured at the
beginning and end of each renewal; the measured concentrations were close to nominal and the
final/initial measured ammonia concentrations averaged 1.09. pH was measured three times per week.
Ten-week control survival averaged 66.3%. The test material was ammonium chloride and the dilution
water was dechlorinated tap water that contained 26 mg Cl/L. On the basis of the nominal
concentrations of total ammonia, the increase in the concentration of chloride at the lowest tested
concentration of ammonia was 3.5 mg Cl/L whereas the increase at the highest tested concentration of
ammonia was 64 mg Cl/L. Thus the concentration of chloride in the treatments ranged from about 30
mg Cl/L to about 90 mg Cl/L. This range is within the range of 25 to 100 mg Cl/L, but no data are
available concerning the effect of chloride in the range from 25 to 100 mg/L on H. azteca or on its
sensitivity to ammonia.
3. Ankley et al. (1995) performed 96-hr water-only toxicity tests in which the test solutions were renewed
daily. The test organisms were cultured in hardened Lake Superior water and tests were performed at
three values of pH in each of three waters (soft water = Lake Superior water; moderately-hard water =
hardened Lake Superior water; hard water = salts added to Millipore water). The test material was
ammonium chloride and HC1 was used to acidify some test solutions. Biesinger and Christensen
(1972) reported that the concentration of chloride in Lake Superior water was 1.2 mg/L and Tiffany et
al. (1969) reported that the concentration of chloride in Lake Superior was 1.4 mg/L. The
concentration of chloride in the hardened Lake Superior water is about 19 mg/L, based on information
in an SOP for culturing H. azteca at MED. The concentration of chloride in the hard water used in
these tests was probably near 4 mg Cl/L. The increase in the concentration of chloride due to
acidification is not known. On the basis of the nominal concentrations of total ammonia, the increase
in chloride at the lowest and highest reported LCSOs was 44 mg Cl/L and 516 mg Cl/L, but the range
within any one test would not be nearly this large. It is known that H. azteca does not do well in Lake
Superior water. In addition, one investigator found that fathead minnows and C. dubia do not do well
when a CO2-enriched atmosphere is used to maintain pH, which means that this technique might
adversely affect H. azteca.
4. Whiteman et al. (1996) compared the toxicity of ammonia in a spiked-sediment exposure versus a
water-only exposure. The water-only toxicity test was a flow-through 96-hr test and the test material
was ammonium chloride. The dilution water was dechlorinated tap water from Superior, WI, which is
taken from a well in a sandy area near Lake Superior, and so the concentration of chloride in this water
was probably less than 2 mg/L. Ammonia, temperature, and pH were measured sufficiently often. The
increase in the concentration of chloride due to the test material at the 96-hr LC50 was 23 mg Cl/L;
145
-------
thus the amount of increase in the concentration of chloride in some treatments would be less than 25
Cl/L in treatments below the LC50, but would be greater than 25 mg Cl/L in treatments above the
LC50. The results of these tests should not be used in the derivation of water quality criteria because
of the low concentration of chloride in Lake Superior water.
5. Borgmann and Borgmann (1997) performed water-only toxicity tests in which the test solutions were
renewed weekly. The test material was ammonium chloride and HC1 was used to acidify some
solutions. They reported that sodium and potassium affected the toxicity of ammonia to H. azteca and
that the effect of pH on the toxicity of ammonia to H. azteca depends on hardness and on the
concentrations of sodium and potassium. On the basis of some dilution tests, they concluded that
calcium, magnesium and anions did not affect the toxicity of ammonia, but they did not actually study
the effect of a series of closely-spaced concentrations of calcium, magnesium, or any anion on the
toxicity of ammonia.
6. Besser et al. (1998) performed 96-hr static toxicity tests on two sediments that were spiked with a
solution that was prepared by adding ammonium chloride to a 50-50 mixture of well water and
deionized water. One sediment was from Little Dixie Lake and the other was a formulated sediment.
The dilution water contained about 11 mg Cl/L and 0.2 mg Br/L (C. Ingersoll, personal communication
to C. Stephan on 4-28-09); it is possible that one or both of the sediments increased or decreased the
concentrations of chloride and/or bromide in the test solutions. The methodology used for these tests
makes the results unacceptable for use in the derivation of water quality criteria because the
concentration of ammonia in the pore water is not known. Nevertheless, these results are interesting
because "Ammonia toxicity to amphipods, expressed as either total ammonia or un-ionized ammonia,
was similar to results of other 96-h tests at comparable pH and hardness [4]," where reference 4 is
Ankley etal. (1995).
7. Wang et al. (2008) performed 48-h toxicity tests on ammonia at pH = 6.5, 7.5, 8.0, 8.5, and 9.0 using a
combination of ammonium chloride and ammonium hydroxide. The pH of some solutions was
adjusted using HC1. The dilution water was reconstituted hard water that contained 7.9 mg Cl/L. At
only two of the pHs were the concentrations of ammonia sufficiently high to kill more than 20% of the
H. azteca in any of the treatments, and in both of these tests the percent survival was higher at several
concentrations of ammonia that were higher than the concentration at which the percent survival was
lowest.
Data reported by Sarda (1991) and Besser et al. (1998) concerning the sensitivity of H. azteca to ammonia
should not be used in the derivation of an aquatic life criterion for ammonia. Data from the other
publications are very questionable because of concerns regarding the importance of chloride and bromide
to H. azteca, the possible effect of chloride and/or bromide on the toxicity of ammonia to H. azteca, the use
of ammonium chloride as the test material, the use of hydrochloric acid to acidify some test solutions, the
use of dilution waters that contained low concentrations of chloride in some of the tests, and other aspects
of the methodology used in some of the tests. Some of these issues are of much more concern in water-
only tests with this species than in sediment tests. It is not known how much of the wide range of ammonia
LCSOs obtained with H. azteca is due to water quality, the methodology used in some of the tests, and/or
the health of the organisms. It appears that some of the lowest acute values were obtained using dilution
waters that contained low concentrations of chloride.
Studies are currently under way that might provide additional information concerning the importance of
water quality to H. azteca. These studies might make it possible to perform one or more high quality
toxicity tests on ammonia using H. azteca in the near future and might make it possible to identify one or
more published results that are probably high quality in the near future.
146
-------
References
Alcocer, J, E Escobar, A Lugo, and L Peralta. 1998. Littoral Benthos of the Saline Crater Lakes of the Basin of
Oriental, Mexico. Internal. J. Salt Lake Res. 7:87-108.
Ankley, GT, MK Schubauer-Berigan, and PD Monson. 1995. Influence of pH and Hardness on Toxicity of
Ammonia to the Amphipod Hyalella azteca. Can. J. Fish. Aquat. Sci. 52:2078-2083.
Besser, JM, CG Ingersoll, EN Leonard, and DR Mount. 1998. Effect of Zeolite on Toxicity of Ammonia in
Freshwater Sediments: Implications for Toxicity Identification Evaluation Procedures. Environ. Toxicol.
Chem. 17(11):2310-2317.
Borgmann, U. 1994. Chronic Toxicity of Ammonia to the Amphipod Hyalella azteca: Importance of
Ammonium Ion and Water Hardness. Environ. Pollut. 86:329-335.
Borgmann, U. 1996. Systematic Analysis of Aqueous Ion Requirements of Hyalella azteca; A Standard
Artificial Medium Including the Essential Bromide Ion. Arch. Environ. Cont. Toxicol. 30:356-363.
Borgmann, U, and AI Borgmann. 1997. Control of Ammonia Toxicity to Hyalella azteca by Sodium,
Potassium and pH. Environ. Pollut. 95(3):325-331.
Borgmann, U, Y Couillard, P Doyle, and DG Dixon. 2005a. Toxicity of Sixty-three Metals and Metalloids to
Hyalella azteca at Two Levels of Water Hardness. Environ. Toxicol. Chem. 24(3):641-652.
Borgmann, U, M Nowierski, and DG Dixon. 2005b. Effect of Major Ions on the Toxicity of Copper to
Hyalella azteca and Implications for the Biotic Ligand Model. Aquatic Toxicol. 73:268-287.
Colburn, EA. 1988. Factors Influencing Species Diversity in Saline Waters of Death Valley, USA.
Hydrobiologia 158:215-226.
France, RL. 1992. Biogeographical Variation in Size-specific Fecundity of the Amphipod Hyalella azteca.
Crustaceana 62:240-248.
Galat, DL, M Coleman, and R Robinson. 1988. Experimental Effects of Elevated Salinity on Three Benthic
Invertebrates in Pyramid Lake, Nevada. Hydrobiologia 158:133-144.
Sarda, N. 1994. Spatial and Temporal Heterogeneity in Sediments with Respect to Pore Water Ammonia and
Toxicity of Ammonia to Ceriodaphnia dubia and Hyalella azteca. MS Thesis. Wright State University, Dayton,
OH.
Smith, ME, JM Lazorchak, LE Herrin, S Brewer-Swartz, and WT Thoeny. 1997. A Reformulated,
Reconstituted Water for Testing the Freshwater Amphipod, Hyalella azteca. Environ. Toxicol. Chem.
16(6): 1229-1233.
Soucek, DJ. 2007. Comparison of Hardness- and Chloride-Regulated Acute Effects of Sodium Sulfate on Two
Freshwater Crustaceans. Environ. Toxicol. Chem. 26(4):773-779.
147
-------
Thomas, PE, DW Blinn, and P Keim. 1997. Genetic and Behavioural Divergence among Desert Spring
Amphipod Populations. Freshwater Biology 38:137-143.
Tiffany, MA, JW Winchester, and RH Loucks. 1969. Natural and Pollution Sources of Iodine, Bromine, and
Chlorine in the Great Lakes. J. Wat. Pollut. Cont. Fed. 41(7): 1319-1329.
Wang, N, RJ Erickson, CG Ingersoll, CD Ivey, EL Brunson, T Augspurger, and MC Barnhart. 2008. Influence
of pH on the Acute Toxicity of Ammonia to Juvenile Freshwater Mussels (Fatmucket, Lampsilis siliquoidea).
Environ. Toxicol. Chem. 27:1141-1146.
Wellborn, GA, and RD Cothran. 2004. Phenotypic Similarity and Differentiation among Sympatric Cryptic
Species in a Freshwater Amphipod Species Complex. Freshwater Biology 49:1-13.
Wellborn, GA, R Cothran, and S Bartholf 2005. Life History and Allozyme Diversification in Regional
Ecomorphs of the Hyalella azteca (Crustacea: Amphipoda) Species Complex. Biol. J. Linnean Soc. 84:161-
175.
Whiteman, FW, GT Ankley, MD Kahl, DM Rau, and MD Balcer. 1996. Evaluation of Interstitial Water as a
Route of Exposure for Ammonia in Sediment Tests with Benthic Macroinvertebrates. Environ. Toxicol. Chem.
15(5):794-801.
Witt, JDS, DL Threloff, and PDN Hebert. 2006. DNA Barcoding Reveals Extraordinary Cryptic Diversity in
an Amphipod Genus: Implications for Desert Spring Conservation. Molecular Ecology 15:3073-3082.
Wollheim, WM, and JR Lovvorn. 1995. Salinity Effects on Macroinvertebrate Assemblages and Waterbird
Food Webs in Shallow Lakes of the Wyoming High Plains. Hydrobiologia 310:207-223.
148
-------
Appendix C
EPA Final Draft Position Statement on:
28-day Toxicity Tests using Juvenile Freshwater Mussels
(dated 04-28-09)
149
-------
Aquatic Life Criteria Coordinating Committee 4-28-09
28-day Toxicity Tests using Juvenile Freshwater Mussels
Position statement:
In accordance with the 1985 Guidelines, 28-d survival and growth tests using juvenile freshwater mussels
do not qualify as chronic toxicity tests for use in the derivation of aquatic life criteria. Nevertheless, a
concentration that causes a reduction in survival of 20% or more can be used as an upper limit on a Species
Mean Chronic Value if the test is otherwise acceptable. A concentration that causes a reduction in growth
cannot be similarly used at this time because of uncertainties concerning these data. Therefore, growth data
from 28-day toxicity tests with juvenile mussels should be included in a criteria document as "other data" if
the tests are otherwise acceptable.
Rationale:
The 1985 Guidelines describe three kinds of toxicity tests that can be used in the derivation of a Species
Mean Chronic Value: life-cycle tests, partial life-cycle tests, and early life-stage (ELS) tests with fishes.
The 28-d survival and growth test using juvenile freshwater mussels is neither a life-cycle test nor a partial
life-cycle test, and ELS tests are used as predictors of life-cycle tests only for fishes. Thus, as for any other
similarly tested species that is not a fish, the 28-d survival and growth test with juvenile mussels is not an
acceptable chronic toxicity test for use in the derivation of a Species Mean Chronic Value.
Because of the complexities in their life cycle, development of testing methods for freshwater mussels is
very challenging. Although standard procedures have been adopted by ASTM, current literature shows that
several aspects of juvenile mussel testing are still being evaluated; variables include the type and ration of
food provided, and the water renewal and exposure apparatus that will sustain juvenile mussels in good
health and provide a level of control growth reflective of an organism otherwise free of substantial
background stress. These issues are further complicated by the comparatively limited data from which to
establish minimum performance criteria for juvenile mussel tests across the diversity of mussel taxa,
particularly for growth.
Toxicity tests with invertebrates that cover less than the full life cycle are not used in the derivation of
Species Mean Chronic Values because of uncertainties regarding the relation of results of these shorter tests
to results that would be obtained in full life-cycle tests. The above methodological issues notwithstanding,
survival data from less than life-cycle tests can be used to establish an upper limit on a Species Mean
Chronic Value because death is not reversible and so effects on survival are expected to translate directly to
the outcome of a life-cycle chronic test if one were performed. Accordingly, reduction in survival in 28-d
juvenile mussel tests can be used to set an upper limit on a Species Mean Chronic Value if the test is
conducted in a manner consistent with the 1985 Guidelines, the control survival is adequate, and the
organisms appear to be healthly. The resulting Species Mean Chronic Value would be an inequality
indicating that the expected chronic value for that species is not more than the concentration of the
pollutant that reduced survival by 20% or more in the 28-d juvenile test.
In a previous criteria document, tests concerning growth of organisms in non-life-cycle tests with duration
less than 90 days were not used in the derivation of a Species Mean Chronic Value (see page 45 in the 1999
ammonia criteria document). The reason for this is the lack of direct comparisons between these shorter
tests and life-cycle tests (as exists for ELS tests with fish), and the accompanying uncertainties regarding
the quantitative relationship between growth reductions observed over shorter exposures of only certain life
150
-------
stages and the expected effect on growth in a life-cycle test. In addition, some growth effects, particularly
smaller reductions, might be transient during a longer exposure, and the 28-day exposure period represents
a relatively small percentage of the overall duration of the juvenile life stage of mussels. As such,
reduction in growth during a 28-d juvenile mussel test would be incorporated as "other data" (traditionally
Table 6 of criteria documents), just as would be done with short-term growth data for any other species (if
the test was otherwise acceptable), except for growth data that are used to determine the results of an ELS
test. This placement is not because growth of juvenile mussels lacks biological importance, but because of
the attendant uncertainties surrounding the methodologies used to generate the growth data and the
uncertainties in relating any observed reductions to results of life-cycle toxicity tests.
As stated in the 1985 Guidelines, test results that do not otherwise qualify as acceptable acute or chronic
toxicity data (typically compiled in Table 6) have the potential to influence an aquatic life criterion if the
data indicate that the criterion is not consistent with sound scientific evidence (see Section XII.B of the
1985 Guidelines). It is likely that a concentration of a pollutant that causes a reduction in growth can be
used as an upper limit on a Species Mean Chronic Value if, on a species-specific basis, the test is
sufficiently long to indicate that the reduction is not transient (e.g., is not due to initial shock), if the percent
reduction in growth is sufficiently great (i.e., the shorter the test, the larger a percent reduction must be in
order to be considered unacceptable), and if the test is otherwise acceptable.
C. Ingersoll (personal communication to C. Stephan on 6-11-08) thinks that it might be possible to perform
acceptable 90-d toxicity tests with juvenile freshwater mussels. If acceptable 90-d juvenile toxicity tests
can be performed, it would be possible to determine whether the percent reductions in survival and growth
in 90 days are greater than, less than, or the same as the percent reductions in survival and growth in 28
days. However, regardless of the relationship between 28-d and 90-d results, both the reduction in survival
and the reduction in growth in a 90-d toxicity test with juvenile freshwater mussels can be used in the
derivation of a SMCV, if the test is otherwise acceptable.
151
-------
Appendix D
Conversion of Acute Results of Toxicity Tests
152
-------
All of the ammonia acute values (LCSOs and ECS Os) in Table 1 of this document were converted to total ammonia
nitrogen acute values using the reported temperatures and pHs, and using the pK relationship from Emerson et al. (1975).
Conversions were dependent on the form of ammonia the acute values were expressed, e.g., un-ionized ammonia (UIA),
un-ionized ammonia expressed as nitrogen (UIA-N), total ammonia (TA) and total ammonia nitrogen (TAN). Once all
the acute values were converted to total ammonia nitrogen, these values were then adjusted to pH=8 using the pH
relationship developed in the 1999 criterion document. After the adjustment to pH 8, the total ammonia nitrogen acute
values were further normalized to atemperature of 25°C for invertebrates only, as per the recommendations in the 1999
criterion document. The conversion procedure is illustrated here using the data for the flatworm, Dendrocoelum lacteum,
which is the first species in Table 1 in the 1984/1985 criteria document and was the species chosen to illustrate the
conversion procedure in Appendix 3 of the 1999 criterion document:
Acute value (AV) = 1.40 mg un-ionized ammonia (UIA) or NH3/L
pH = 8.20
Temperature = 18.0°C
Step 1.
Equation 3 in the 1999 criterion document is used to calculate the pK at 18 °C:
pK = 9.464905
Step 2.
Equation 2 in the 1999 criterion document and the definitions pK = -logi0K and pH = -logi0[ET] are used to
obtain the following:
Total ammonia = [NH3] + [NH+4] = [NH3] + [NH3]/0.0543369
Step 3.
The AV in terms of total ammonia is calculated as:
= 0.0543369
= 27.1652 mg total ammonia/L
Step 4.
The AV in terms of total ammonia nitrogen (AVt) is calculated as follows:
AVt = (27.1652 mg total ammonia/L)(14/17)
= 22.3713 mgN/L.
Step 5.
The AV in terms of total ammonia nitrogen, or AVt, is converted from pH=8.2 to pH=8
using Equation 11 in the 1999 criterion document:
AVt>8 = (AVt)/(0.681546) = 32.8244 mg N/L
Step 6. (temperature adjustment for invertebrates only)
The AV in terms of total ammonia nitrogen at pH=8, or AVt 8, is converted from this concentration at test
temperature to a standard test temperature of 25°C using Equation 5 in the 1999 criterion document with the
invertebrate acute slope of-0.036:
log(AVt,8,25) = log(AVu) - [-0.036(18 °C -25 °Q]
= 18.3737 mgN/L.
Because this is the only species in this genus for which data are in Table 1 in the 1984/1985 criteria document, 18.37 mg
N/L is the GMAV given for the genus Dendrocoelum in Table 1 of this update document.
153
-------
Appendix E
Conversion of Chronic Results of Toxicity Tests
154
-------
As in the previous appendix with the acute results of toxicity tests, all of the ammonia chronic values (EC20s
and IC20s) in Table 3 of this document were converted to total ammonia nitrogen chronic values using the
reported temperatures and pHs, and using the pK relationship from Emerson et al. (1975). Conversions were
dependent on the form of ammonia the acute values were expressed. Once all the chronic values were
converted to total ammonia nitrogen, these values were then adjusted to pH=8 using the pH relationship
developed in the 1999 criterion document. After the adjustment to pH 8, the total ammonia nitrogen chronic
values were further normalized to a temperature of 25°C for invertebrates only, as per the recommendations in
the 1999 criterion document. The conversion procedure is illustrated here using the data for the wavy-rayed
lamp mussel, Lampsilis fasciola, which is one of the several species in the genus Lampsilis ranked third in
Table 3 in this update document and was the species chosen to illustrate the conversion procedure used in this
document and the 1999 criterion document:
Chronic value (CV) = EC20 of <0.3981 mg total ammonia nitrogen (TAN)/L
pH=8.20
Temperature = 20.0°C
Step 1 through 4
(unnecessary in this case as CV is already expressed in terms of TAN, for more details regarding these steps,
see Appendix C).
Step 5.
The CV in terms of total ammonia nitrogen, or CVt, is converted from pH=8.2 to pH=8
using Equation 12 in the 1999 criterion document:
CVt.8 = (CVt)/(0.736263) = <0.5407 mg N/L
Step 6. (temperature adjustment for invertebrates only)
The CV in terms of total ammonia nitrogen at pH=8, or CVt,g, is converted from this concentration at
test temperature to a standard test temperature of 25°C using Equation 5 in the 1999 criterion document
with the invertebrate chronic slope of-0.028:
log(CVt,8;25) = log(CVt,8) - [-0.028(20°C -25°C)]
= <0.3917mgN/L
Because this is one of two species in this genus for which data are in Table 3 of this document, the geometric
mean of this value (<0.3917 mg N/L) and <0.3027 mg N/L for Lampsilis siliquoidea is the GMCV given for the
genus Lampsilis (<0.34 mg N/L, rounded to two significant figures) in Table 3 of this update document.
155
-------
Appendix F
Results of the Regression Analyses of New Chronic Data
156
-------
WAVY-RAYED LAMP MUSSEL, 28-D EXPOSURE OF JUVENILES, WANG et al. (2007a)
co
03
O
CD
Q_
1.1
1.0'
.9
.8
.7
.6
.5
.4
.3
.2
.1
I
0
-1.4
-1.2 -1.0 -.8 -.6 -.4 -.2 0
Log (mg TAN/I pH 8 and 25oC)
.2
.4
157
-------
Parameter Summary (Piecewise Linear Regression Analysis)
Parameter
LogXSO
S
YO -Transformed
Untransformed
Guess
-0.20000
1.5000
1.2490
0.9000
FinalEst
-0.20000
1,5000
1.2490
0.9000
StdError
0.10810
0.6938
0.2432
95%LCL
-0.54402
-0.7080
0.4751
0.2093
"
95%UCL
0.14402
3.7080
2.0230
0.8091
Effect Concentration Summary
% Effect
50,0
20.0
10.0
5.0
Xp Est
0.6310
0.3981
0.3415
0.3162
95%LCL
0.2857
0.1476
0.1088
0.0926
95%UCL
1.3932
1,0737
1.0714
1.0795
Source
Total
Regression
Error
Regression Analysis of Variance
df SS MS F
5 1.4081 0.2816
2 1.2804 0.6402 15.0
3 0.1277 0.0425
Alpha
0.0273
Exposure
-1.3979
-0.8861
-0.4685
-0.3565
0.0086
0.2967
Data Summary
Obs Effects Pred Effects Residual
0.9990 0.9000 -0.0990
0.8300 0.9000 0.0700
0.7700 0.8125 0,0425
0.7300 0.6613 -00687
0.3000 0.1684 -0.1316
0.0000 0.0000 0.0000
Weight
1. ;
1.
1,
1.
1.
1.
Error Summary
No Errors
158
-------
COMMON CARP, 28-D EXPOSURE OF LARVAE, MALLET AND SIMS (1994)
.35 r
0
CO
CO
CD
o
co
-------
Parameter Summary (Piecewise Linear Regression Analysis)
Parameter
LogXSO
S
YO -Transformed
Untransformed
Guess
-0.40000
2.000
-0.52288
0.3000
Final Est
-0.37111
1.6850
-0.53024
0.2950
StdError
0.06920
0.5801
0.05838
95%LCL
-0.59133
-0.1610
-0.71603
0.1923
95%UCL
-0.15089
3,5311
-0.34445
0.4524
% Effect
50.0
20.0
10.0
5.0
Effect Concentration Summary
Xp Est 95%LCL
0.4255 0.2563
0.2824 0.1357
0.2463 0.1054
0.2301 0.0926
95%UCL
0.7065
0.5878
0.5756
0.5718
Regression Analysis of Variance
Source
Total
Regression
Error
df
5
2
3
SS
0.48289
0.47346
0.00943
MS
0.09658
0.23673
0.00314
F Alpha
75.3 0.0027
Exposure
-2.000
-0.959
-0.638
-0.456
-0.260
-0.180
Obs Effects
0.300
0.290
0.240
0.215
0.100
0.050
Data Summary
Pred Effects
0.295
0.295
0.280
0.190
0.092
0.053
Residual
-0.005
0.005
0.040
-0.025
-0.008
0.003
Weight
1.
1.
1.
1.
1.
1.
Error Summary
No Errors
160
-------
ONCORHYNCHUS CLARKIHENSHAWI, 103-D EXPOSURE OF FERTILIZED EMBRYOS, KOCH et al.
(1980)
05
~co
>
'>
^
ID
03
O
CD
Q_
.7
.6
.5
.4
.3
.2
.1
0
-3.0
-2.5 -2.0 -1.5 -1.0 -.5
Log (mg UIA of NH3/L mg/l)
.5
161
-------
Parameter Summary (Logistic Equation Regression Analysis)
Parameter
LogXSO
S
YO -Transformed
Untransformed
Guess
-0.49795
2.000
1.0357
0.7400
FinalEst
-0.29623
0.7945
0.9950
0.7036
StdError
0.11705
0.2612
0.0478
95%LCL
-1.78346
-2.5240
0.3879
0.1430
95%UCL
1.19099
4.1131
1.6022
0.9990
Effect Concentration Summary
% Effect Xp Est 95%LCL
50.0 0.5056 0.0165
20.0 0.18516 0.00047
10.0 0.10289 0.00003
5.0 0.05988 0.00000
95%UCL
15.5236
73.42458
351.30917
1676.94336
Regression Analysis of Variance
Source df SS MS
Total 3 0.17433 0.05811
Regression 2 0.17077 0.08538
Error 1 0.00356 0.00356
F Alpha
24.0 0.1429
Exposure
-3.000
-2.000
-0.772
-0.051
Obs Effects
0.740
0.660
0.580
0.220
Data Summary
Pred Effects
0.703
0.700
0.577
0.221
Residual
-0.037
0.040
-0.003
0.001
Weight
1.
1.
1.
1.
Error Summary
No Errors
162
-------
Appendix G
Unused (Non-influential) Acute and Chronic Studies for Freshwater Ammonia Criteria Development
Screened Out Studies with Code List (appears separately at end of appendix)
163
-------
Citation
ECOTOX or Other
Ref. No
Rejection Code(s)
Comment(s)
Academy of Natural Sciences. 1960. The Sensitivity of
Aquatic Life to Certain Chemicals Commonly Found in
Industrial Wastes. Final Report No.RG-3965(C2R1),
U.S.Public Health Service Grant, Academy of Natural
Sciences, Philadelphia, PA :89 p..
5683
AF
Alabaster, J.S., D.G. Shurben, and G. Knowles. 1979. The
Effect of Dissolved Oxygen and Salinity on the Toxicity of
Ammonia to Smolts of Salmon, Salmo salar L. J.Fish
Biol.15(6):705-712 (Personal Communication Used).
406
Dur-1d
Alabaster, J.S., D.G. Shurben, and M.J. Mallett. 1983. The
Acute Lethal Toxicity of Mixtures of Cyanide and Ammonia
to Smolts of Salmon, Salmo salar L. at Low Concentrations
of Dissolved Oxygen. J.Fish Biol. 22:215-222.
10252
Dur-1d
Alam, M., Frankel, T. L., and Alam, M. Gill ATPase Activities
of Silver Perch, Bidyanus bidyanus (Mitchell), and Golden
Perch, Macquaria ambigua (Richardson): Effects of
Environmental Salt and Ammonia. Aquaculture 251(1), 118-
133. 2006.
84839
Non-NA
Allan, I.R.H., D.W.M. Herbert, and J.S. Alabaster. 1958. A
Field and Laboratory Investigation of Fish in a Sewage
Effluent. Minist.Agric.Fish.Food, Fish.lnvest.Ser.1 6(2):76.
10316
AF, Pet
Alonso, A. and Camargo, J. A. Ammonia Toxicity to the
Freshwater Invertebrates Polycelis Felina (Planariidae,
Turbellaria) and Echinogammarus echinosetosus
(Gammaridae, Crustacea). Fresenius Environ.Bull. 15(12b),
1578-1583.2006.
Non-NA
Arillo, A., B. Uva, and M. Vallarino. 1981. Renin Activity in
Rainbow Trout (Salmo gairdneri Rich.) and Effects of
Environmental Ammonia. Comp.Biochem.Physiol.A
68(3):307-311.
5704
Dur - 2d
Armstrong, D.A.. 1978. Toxicity and Metabolism of Nitrogen
Compounds: Effects on Survival, Growth and
Osmoregulation of the Prawn, Macrobrachium rosenbergii.
Ph.D.Thesis, University of California, Davis, CA:92
p.(Personal Communication Used).
5620
Dur- 1d
Babu, T.R., P. Surendranath, and K.V. Ramana Rao. 1987.
Comparative Evaluation of DDT and Fenvalerate Toxicity on
Penaeus indicus (H. Milne Edwards). Mahasagar 20(4):249-
253.
15
AF, Dur
Bailey, H.C., C. DiGiorgio, K. Kroll, J.L Miller, D.E. Hinton,
and G. Starrett. 1996. Development of Procedures for
Identifying Pesticide Toxicity in Ambient Waters:
Carbofuran, Diazinon, Chlorpyrifos. Environ.Toxicol.Chem.
15(6):837-845.
16844
AF
Ball, I.R.. 1967. The Relative Susceptibilities of Some
Species of Fresh-Water Fish to Poisons-l. Ammonia. Water
Res. 1(11/12):767-775.
10000
Dur
Banerjee, S., and S. Bhattacharya. 1994. Histopathology of
Kidney of Channa punctatus Exposed to Chronic Nonlethal
Level of Elsan, Mercury, and Ammonia.
Ecotoxicol.Environ.Saf. 29(3):265-275.
13750
UEndp
164
-------
Citation
ECOTOX or Other
Ref. No
Rejection Code(s)
Comment(s)
Banerjee, S., and S. Bhattacharya. 1995. Histopathological
Changes Induced by Chronic Nonlethal Levels of Elsan,
Mercury, and Ammonia in the Small Intestine of Channa
punctatus (Bloch). Ecotoxicol.Environ.Saf. 31(1):62-68.
15256
UEndp
Banerjee, S., and S. Bhattacharya. 1997. Histopathological
Changes Induced by Chronic Nonlethal Levels of Elsan,
Mercury and Ammonia in the Liver of Channa punctatus
(Bloch). J.Environ.Biol. 18(2):141-148.
18229
UEndp
Banerjee, T.K., and V.I. Paul. 1993. Estimation of Acute
Toxicity of Ammonium Sulphate to the Fresh Water Catfish,
Heteropneustes fossilis II. A Histopathological Analysis of
the Epidermis. Biomed.Environ.Sci. 6(1):45-58.
13480
UEndp
Baskaran, P., and S. Palanichamy. 1990. Impact of
Agricultural Fertilizer (Ammonium Chloride) on Physiology
and Biochemistry of the Freshwater Teleost Fish
Oreochromis mossambicus. J.Ecobiol. 2(2):97-106.
11072
AF, UEndp
Bergerhouse, D.L.. 1989. Lethal Effects of Elevated pH and
Ammonia on Early Life Stages of Several Sportfish Species.
Ph.D.Thesis, Southern Illinois University, Carbondale, IL
:246p..
3822
UEndp, Pur - 8h
Bergerhouse, D.L.. 1992. Lethal Effects of Elevated pH and
Ammonia on Early Life Stages of Walleye.
N.Am.J. Fish. Manage. 12(2): 356-366.
6903
UEndp, Pur - 8h
Bergerhouse, D.L.. 1993. Lethal Effects of Elevated pH and
Ammonia on Early Life Stages of Hybrid Striped Bass.
J.Appl.Aquacult. 2(3/4):81-100.
4290
UEndp, Pur - 8h
Besser, J. M., Brumbaugh, W. G., Allert, A. L, Poulton, B.
C., Schmitt, C. J., and Ingersoll, C. G. Ecological Impacts of
Lead Mining on Ozark Streams: Toxicity of Sediment and
Pore Water. Ecotoxicology and Environmental Safety
[Ecotoxicol. Environ. Saf.]. Vol. 72, no. 2, pp. 516-526. Feb
2009. 2009.
Mix
Bhattacharya, T., S. Bhattacharya, A.K. Ray, and S. Dey.
1989. Influence of Industrial Pollutants on Thyroid Function
in Channa punctatus (Bloch). Indian J.Exp.Biol. 27(1):65-68.
3106
AF, UEndp, Pur- 1d
Bianchini, A., W. Wasielesky Jr., and K.C. Miranda Filho.
1996. Toxicity of Nitrogenous Compounds to Juveniles of
Flatfish Paralichthys orbignyanus.
BulI.Environ.Contam.Toxicol. 56(3):453-459.
16445
AF
Biswas, J. K., Sarkar, D., Chakraborty, P., Bhakta, J. N.,
and Jana, B. B. Density dependent ambient ammonium as
the key factor for optimization of stocking density of
common carp in small holding tanks. Aquaculture 261(3),
952-959. 2006-.
No Dose, VarExp
Only 1 exposure concentration
(naturally increased over time)
Blanco Saul, Romo Susana, Fernandez-Alaez Margarita,
and Becares Eloy. Response of Epiphytic Algae to Nutrient
Loading and Fish Density in a Shallow Lake: a Mesocosm
Experiment. Hydrobiologia [Hydrobiologia]. Vol. 600, no. 1,
pp. 65-76. Mar 2008. 2008.
Mix
Mesocosm; no ammonia
165
-------
Citation
ECOTOX or Other
Ref. No
Rejection Code(s)
Comment(s)
Boons, M. D. , Semlitsch, R. D., Little, E. E., and Doyle, M.
C. Multiple Stressors in Amphibian Communities: Effects of
Chemical Contamination, Bullfrogs, and Fish. Ecol.Appl.
17(1), 291-301.2007.
Mix
Brun, F. G., Olive(acute), I., Malta, E. J., Vergara, J. J.,
Herna(acute)ndez, I., and Pe(acute)rez-Llore(acute)ns, J. L.
Increased Vulnerability of Zostera Noltii to Stress Caused
by Low Light and Elevated Ammonium Levels Under
Phosphate Deficiency. Marine Ecology Progress Series,
365 (-) pp. 67-75, 2008 . 2008.
Mix
Buikema, A.L.Jr., J. Cairns Jr., and G.W. Sullivan. 1974.
Evaluation of Philodina acuticornis (Rotifera) as Bioassay
Organisms for Heavy Metals. Water Resour.Bull. 10(4):648-
661.
2019
Dur
Burrows, R.E.. 1964. Effects of Accumulated Excretory
Products on Hatchery-Reared Salmonids. U.S.Fish
Wildl.Serv., Res.Rep.No.66, Washington, DC :12.
10002
Uenpd
Byrne Maria, Oakes Diana J, Pollak John K, and Laginestra
Edwina. Toxicity of Landfill Leachate to Sea Urchin
Development With a Focus on Ammonia. Cell biology and
toxicology, 2008 Dec, 24(6):503-12. Epub: 2008 Aug 21 .
2008.
Mix
Cairns, J.Jr., and A. Scheier. 1959. The Relationship of
Bluegill Sunfish Body Size to Tolerance for Some Common
Chemicals. Proc.13th Ind.Waste Conf., Purdue
Univ.Eng.Bull 96:243-252.
930
AF
Cairns, J.Jr., B.R. Niederlehner, and J.R. Pratt. 1990.
Evaluation of Joint Toxicity of Chlorine and Ammonia to
Aquatic Communities. Aquat.Toxicol. 16(2):87-100.
3207
Ace; No Org
Camargo, Julio A. and Alonso, Ivaro. Ecological and
toxicological effects of inorganic nitrogen pollution in aquatic
ecosystems: A global assessment. Environment
International 32(6), 831-849. 2006.
Sec
Cao, Te, Xie, Ping, Ni, Leyi, Zhang, Meng, and Xu, Jun.
Carbon and nitrogen metabolism of an eutrophication
tolerative macrophyte, Potamogeton crispus, under NH4+
stress and low light availability. Environmental and
Experimental Botany In Press, Corrected Proof.
No Dose
Only 1 exposure concentration
Carr, R. S., Biedenbach, J. M., and Nipper, M. Influence of
Potentially Confounding Factors on Sea Urchin Porewater
Toxicity Tests. Archives of Environmental Contamination
and Toxicology [Arch. Environ. Contam. Toxicol.]. Vol. 51,
no. 4, pp. 573-579. Nov 2006. 2006.
Mix
Centeno, M.D.F., G. Persoone, and M.P. Goyvaerts. 1995.
Cyst-Based Toxicity Tests. IX. The Potential of
Thamnocephalus platyurus as Test Species in Comparison
with Streptocephalus proboscideus (Crustacea:
Branchiopoda: Anostraca). Environ.Toxicol.Water Qual.
10(4):275-282.
14017
AF, Dur-1d
Chetty, A.N., and K. Indira. 1994. Alterations in the Tissue
Lipid Profiles of Lamellidens marginalis Under Ambient
Ammonia Stress. Bull.Environ.Contam.Toxicol. 53(5):693-
698.
13744
Dur - 2d
166
-------
Citation
Colt, J.E.. 1978. The Effects of Ammonia on the Growth of
Channel Catfish, Ictalurus punctatus. Ph.D. Thesis, Univ.of
California, Davis, CA :185 p..
Corpron, K.E., and D.A. Armstrong. 1983. Removal of
Nitrogen by an Aquatic Plant, Elodea densa, in
Recirculating Macrobrachium Culture Systems. Aquaculture
32(3/4):347-360.
Costa, Luiza Dy, Miranda-Filho, KleberC., Severe, Marlon
P., and Sampaio, Luis A. Tolerance of juvenile pompano
Trachinotus marginatus to acute ammonia and nitrite
exposure at different salinity levels. Aquaculture 285(1-4),
270-272. 2008-.
Craig, G.R.. 1983. Interlaboratory Fish Toxicity Test
Comparison-Ammonia. Environ. Protection Service, Quality
Protection Section, Water Resour. Branch, Canada :7.
Cucchiari, E., Guerrini, F., Penna, A., Totti, C., and
Pistocchi, R. Effect of Salinity, Temperature, Organic and
Inorganic Nutrients on Growth of Cultured Fibrocapsa
Japonica (Raphidophyceae) From the Northern Adriatic
Sea. Harmful Algae [Harmful Algae]. Vol. 7, no. 4, pp. 405-
414. Jun 2008. 2008.
Dabrowska, H., and H. Sikora. 1986. Acute Toxicity of
Ammonia to Common Carp (Cyprinus carpio L).
Pol.Arch.Hydrobiol. 33(1):121-128.
Danecker, E.. 1964. The Jauche Poisoning of Fish - an
Ammonia Poisoning. Osterreichs Fischerei. 3/4:55-68 (ENG
TRANS L).
Daoust, P.Y., and H.W. Ferguson. 1984. The Pathology of
Chronic Ammonia Toxicity in Rainbow Trout, Salmo
gairdneri Richardson. J.Fish Dis. 7:199-205.
De Moor, I.J. 1984. The Toxic Concentration of Free
Ammonia to Brachionus calyciflorus Pallas, a Rotifer Pest
Species Found in High Rate Algal Ponds (HRAP'S).
J.Limnol.Soc.South Afr. 10(2):33-36.
Dendene, M.A., T. Rolland, M. Tremolieres, and R.
Carbiener. 1993. Effect of Ammonium Ions on the Net
Photosynthesis of Three Species of Elodea. Aquat.Bot.
46(3/4):301-315.
Dey, S., and S. Bhattacharya. 1989. Ovarian Damage to
Channa punctatus After Chronic Exposure to Low
Concentrations of Elsan, Mercury, andAmmonia.
Ecotoxicol. Environ. Saf. 17(2):247-257.
DeYoe Hudson R, Buskey Edward J, and Jochem Frank J.
Physiological Responses of Aureoumbra Lagunensis and
Synechococcus Sp. To Nitrogen Addition in a Mesocosm
Experiment. Harmful Algae [Harmful Algae]. Vol. 6, no. 1 ,
pp. 48-55. Jan 2007. 2007.
Diamond, J. M., Klaine, S. J., and Butcher, J. B.
Implications of Pulsed Chemical Exposures for Aquatic Life
Criteria and Wastewater Permit Limits. Environ. Sci.Technol.
40(16), 5132-5138. 2006.
Dowden, B.F., and H.J. Bennett. 1965. Toxicity of Selected
Chemicals to Certain Animals. J.Water Pollut. Control Fed.
37(9):1308-1316.
ECOTOX or Other
Ref. No
59792
15323
10259
12711
10305
10217
5433
4268
446
102216
915
Rejection Code(s)
AF
Uendp, Con
Non-NA
AF
Mix
Dur - 2d
AF, UEndp, Dur
UEndp
UEndp
Uendp, Plant
AF, Dur - 2d
No Dose
No Dose, Dur, VarExp
AF
Comment(s)
Plants do not drive criteria, and
therefore, are not included in
CWA review and approval of
ORWQS
Plants do not drive criteria, and
therefore, are not included in
CWA review and approval of
ORWQS
Only one exposure
concentration
Only 2 exposure
concentrations
167
-------
Citation
Dowden, B.F.. 1961. Cumulative Toxicities of Some
Inorganic Salts to Daphnia magna as Determined by
Median Tolerance Limits. Proc.La.Acad.Sci. 23:77-85.
Drath, M., Kloft, N., Batschauer, A., Marin, K., Novak, J.,
and Forchhammer, K. Ammonia Triggers Photodamage of
Photosystem li in the Cyanobacterium Synechocystis Sp.
Strain Pec 6803. Plant Physiology, 147 (1) pp. 206-215,
2008 . 2008.
D'Silva, C., and X.N. Verlencar. 1976. Relative Toxicity of
Two Ammonium Compounds Found in the Waste of
Fertilizer Plants. Mahasagar 9(1/2):41-44.
Egea-Serrano, A., Tejedo, M., and Torralva, M. Analysis of
the Avoidance of Nitrogen Fertilizers in the Water Column
by Juvenile Iberian Water Frog, Pelophylax perezi (Seoane,
1885), in Laboratory Conditions.
BulI.Environ.Contam.Toxicol. 80(2), 178-183. 2008.
Ewell, W.S., J.W. Gorsuch, R.O. Kringle, K.A. Robillard, and
R.C. Spiegel. 1986. Simultaneous Evaluation of the Acute
Effects of Chemicals on Seven Aquatic Species.
Environ.Toxicol.Chem. 5(9):831-840.
Fang, J. K. H., Wu, R. S. S., Chan, A. K. Y., Yip, C. K. M.,
and Shin, P. K. S. Influences of Ammonia-Nitrogen and
Dissolved Oxygen on Lysosomal Integrity in Green-Lipped
Mussel Perna Viridis: Laboratory Evaluation and Field
Validation in Victoria Harbour, Hong Kong. Marine Pollution
Bulletin [Mar. Pollut. Bull.]. Vol. 56, no. 12, pp. 2052-2058.
Dec 2008. 2008.
Fedorov, K.Y., and Z.V. Smirnova. 1978. Dynamics of
Ammonia Accumulation and its Effect on the Development
of the Pink Salmon, Oncorhynchus gorbuscha, in Closed
Circuit Incubation Systems. Vopr.lkhtiol. 19(2):320-328.
Flagg, R.M., and L.W. Hinck. 1978. Influence of Ammonia
on Aeromonad Susceptibility in Channel Catfish.
Proc.Annu.Conf.Southeast.Assoc.Fish Wildl.Agencies
32:415-419.
Flis, J.. 1963. Anatomicohistopathological Changes Induced
in Carp (Cyprinus carpio L.) by Ammonia Water. Part 1 .
Effects of Toxic Concentrations. (Zmiany. Acta Hydrobiol.
10(1/2):205-224.
Foss, Atle, Imsland, Albert K., Roth, Bj0rn, Schram,
Edward, and Stefansson, Sigurd O. Interactive effects of
oxygen saturation and ammonia on growth and blood
physiology in juvenile turbot. Aquaculture 271(1-4), 244-
251 . 2007-.
ECOTOX or Other
Ref. No
2465
6084
103070
11951
5478
10317
10005
Rejection Code(s)
AF
No Dose
Dur - 2d
Mix, No Dose
Con; Uendp
No Dose
UEndp
UEndp
UEndp, Dur-1d
No Dose
Comment(s)
Only 1 or 2 exposure
concentrations at a specific pH
Only one exposure
concentration
Aside from insufficient
controls, as determined by
ECOTOX reviewers, the
LCSOs reported for the several
aquatic organisms in this study
were all greater than values,
and more appropriate acute
data are available for these
species. pH was also varied
between 6.5 and 8.5 during the
exposure.
Only one exposure
concentration
Only 2 exposure
concentrations
168
-------
Citation
Golding, C., Krassoi, R., and Baker, E. The Development
and Application of a Marine Toxicity Identification Evaluation
(TIE) Protocol for Use with an Australian Bivalve.
Australas.J.Ecotoxicol. 12(1), 37-44. 2006.
Griffis-Kyle Kerry L and Ritchie Mark E. Amphibian Survival,
Growth and Development in Response to Mineral Nitrogen
Exposure and Predator Cues in the Field: an Experimental
Approach. Oecologia, 2007 Jul, 152(4):633-42. Epub: 2007
Mar 10. 2007.
Gyore, K., and J. Olah. 1980. Ammonia Tolerance of Moina
rectirostris Leydig (Cladocera). Aquacult.Hung.(Szarvas)
2:50-54.
Hanna, T.D.. 1992. The Effect of Oxygen Supplementation
on the Toxicity of Ammonia (NH3) in Rainbow Trout
Oncorhynchus mykiss (Richardson). M.S. Thesis, Montana
State University, Bozeman, MT :51 .
Harader, R.R.J., and G.H. Allen. 1983. Ammonia Toxicity to
Chinook Salmon Parr: Reduction in Saline Water.
Trans.Am.Fish.Soc. 112(6):834-837.
Hazel, R.H., C.E. Burkhead, and D.G. Muggins. 1982.
Development of Water Quality Criteria for Ammonia and
Total Residual Chlorine for the Protection of Aquatic Life in
Two Johnson County, Kansas Streams. In: J.G.Pearson,
R.B.Foster, and W.E.Bishop (Eds.), Proc.Sth
Annu.Symp. Aquatic Toxicology, ASTM STP 766,
Philadelphia, PA:381-388.
Healey, F.P.. 1977. Ammonium and Urea Uptake by Some
Freshwater Algae. Can.J.Bot. 55(1):61-69.
Hecnar, S.J.. 1995. Acute and Chronic Toxicity of
Ammonium Nitrate Fertilizer to Amphibians from Southern
Ontario. Environ.Toxicol.Chem. 14(12):2131-2137.
Hedtke, J.L., and LA. Norris. 1980. Effect of Ammonium
Chloride on Predatory Consumption Rates of Brook Trout
(Salvelinus fontinalis) on Juvenile Chinook Salmon
(Oncorhynchus tshawytscha) i.
BulI.Environ.Contam.Toxicol. 24(1):81-89.
Hemens, J.. 1966. The Toxicity of Ammonia Solutions to the
Mosquito Fish (Gambusia affinis Baird & Girard).
J.Proc.lnst.Sewage Purif. 3:265-271.
Henderson, C., Q.H. Pickering, and A.E. Lemke. 1961. The
Effect of Some Organic Cyanides (Nitriles) on Fish.
Proc.15th Ind.Waste Conf., Eng. Bull. Purdue Univ.,
Ser.No.106, 65(2): 120-1 30.
Herbert, D.W.M., and D.S. Shurben. 1963. A Preliminary
Study of the Effect of Physical Activity on the Resistance of
Rainbow Trout (Salmo gairdnerii Richardson) to Two
Poisons. Ann.Appl.Biol. 52:321-326
Herbert, D.W.M., and D.S. Shurben. 1964. The Toxicity to
Fish of Mixtures of Poisons I. Salts of Ammonia and Zinc.
Ann.Appl.Biol. 53:33-41.
ECOTOX or Other
Ref. No
108468
5708
7823
10510
13785
7486
16378
6216
10152
923
8005
8006
Rejection Code(s)
Mix, No Dose
Mix
Dur- 1d
UEndp, Dur
Dur-1d
AF
AF, Uendp
AF, UEndp
Uendp, Eff
Dur- 17h
AF
Dur-1d
Dur - 2d
Comment(s)
Only one exposure
concentration
Data provided in earlier report
Plants do not drive criteria, and
therefore, are not included in
CWA review and approval of
ORWQS
169
-------
Citation
ECOTOX or Other
Ref. No
Rejection Code(s)
Comment(s)
Herbert, D.W.M., and D.S. Shurben. 1965. The
Susceptibility of Salmonid Fish to Poisons Under Estuarine
Conditions-ll Ammonium Chloride. Int. J.Air Water Pollut.
9(1/2):89-91.
10318
Dur- 1d
Herbert, D.W.M., and J.M. Vandyke. 1964. The Toxicity to
Fish of Mixtures of Poisons. II. Copper-Ammonia and Zinc-
Phenol Mixtures. Ann.Appl.Biol. 53(3):415-421.
10193
Dur - 2d
Hernandez, C., M. Martin, G. Bodega, I. Suarez, J. Perez,
and B. Fernandez. 1999. Response of Carp Central
Nervous System to Hyperammonemic Conditions: An
Immunocytochemical Study of Glutamine Synthetase (GS),
Glial Fibrillary Acidic Protein (GFAP) and 70 kDa Heat-
Shock Protein (HSP70). Aquat.Toxicol. 45(2/3): 195-207.
19920
UEndp
Holland, G.A., J.E. Lasater, E.D. Neumann, and W.E.
Eldridge. 1960. Toxic Effects of Organic and Inorganic
Pollutants on Young Salmon and Trout. Res.Bull.No.5,
State of Washington Dept.Fish., Seattle, WA :263 p..
14397
Dur - 3d
Hong, M., Chen, L, Sun, X., Gu, S., Zhang, L, and Chen,
Y. Metabolic and Immune Responses in Chinese Mitten-
Handed Crab (Eriocheir sinensis) Juveniles Exposed to
Elevated Ambient Ammonia. Comp.Biochem.Physiol.C
145(3), 363-369. 2007.
Det
Dilution water not described;
Prior exposure?
Hued, A. C., Caruso, M. N., Wunderlin, D. A., and Bistoni,
M. A. *. Field and in Vitro Evaluation of Ammonia Toxicity
on Native Fish Species of the Central Region of Argentina.
Bulletin of Environmental Contamination and Toxicology
[Bull. Environ. Contam. Toxicol.]. Vol. 76, no. 6, pp. 984-
991. Jun 2006. 2006.
Non-NA
Hurlimann, J., and F. Schanz. 1993. The Effects of Artificial
Ammonium Enhancement on Riverine Periphytic Diatom
Communities. Aquat.Sci. 55(1):40-64.
4134
No Org
Plants do not drive criteria, and
therefore, are not included in
CWA review and approval of
ORWQS
Inman, R.C.. 1974. Acute Toxicity of Phos-Check (Trade
Name) 202 and Diammonium Phosphate to Fathead
Minnows. Environ.Health Lab., Kelly Air Force Base, TX :13
p.(U.S.NTISAD/A-006122).
6010
Tox
Ip, Y. K., Lee, S. M. L, Wong, W. P., and Chew, S. F.
Mechanisms of and Defense Against Acute Ammonia
Toxicity in the Aquatic Chinese Soft-Shelled Turtle,
Pelodiscus Sinensis. Aquatic Toxicology [Aquat. Toxicol.].
Vol. 86, no. 2, pp. 185-196. 31 Jan 2008. 2008.
Exp
Injected
Ishio, S.. 1965. Behavior of Fish Exposed to Toxic
Substances. In: O.Jaag (Ed.), Advances in Water Pollution
Research, Pergamon Press, NY : 19-40.
14092
AF, Dur - 6h, UEndp, No Org
James, R., K. Sampath, and M. Narayanan. 1993. Effect of
Sublethal Concentrations of Ammonia on Food Intake and
Growth in Mystus vittatus. J.Environ.Biol. 14(3):243-248.
8994
AF, UEndp
Jampeetong, Arunothai and Brix, Hans. Effects of NH4+
concentration on growth, morphology and NH4+ uptake
kinetics of Salvinia natans. Ecological Engineering In Press,
Corrected Proof.
VarExp
Concentration increased over
time
170
-------
Citation
Jensen, R.A.. 1978. A Simplified Bioassay Using Finfishfor
Estimating Potential Spill Damage. In: Proc. Control of
Hazardous Material Spills, Rockville, MD :104-108.
Jha, B.K., and B.S. Jha. 1995. Urea and Ammonium Sulfate
Induced Changes in the Stomach of the Fish
Heteropneustes fossilis. Environ. Ecol. 13(1):179-181.
Joy, K.P.. 1977. Ammonium Sulphate As a Thyroid Inhibitor
in the Freshwater Teleost Clarias batrachus (L). Curr.Sci.
46(1 9):671 -673.
Kawabata, Z., T. Yoshida, and H. Nakagawa. 1997. Effect
of Ammonia on the Survival of Zacco platypus (Temminck
and Schlegel) at Each Developmental Stage. Environ. Pollut.
95(2):213-218.
Khatami, S.H., D. Pascoe, and M.A. Learner. 1998. The
Acute Toxicity of Phenol and Unionized Ammonia,
Separately and Together, to the Ephemeropteran Baetis
rhodani (Pictet). Environ.Pollut. 99:379-387.
Kim, J. K., Kraemer, G. P., Neefus, C. D., Chung, I. K., and
Yarish, C. Effects of Temperature and Ammonium on
Growth, Pigment Production and Nitrogen Uptake by Four
Species of Porphyra (Bangiales, Rhodophyta) Native to the
New England Coast. Journal of Applied Phycology, 19 (5)
pp. 431-440, 2007.2007.
Kirk, R.S., and J.W. Lewis. 1993. An Evaluation of Pollutant
Induced Changes in the Gills of Rainbow Trout Using
Scanning Electron Microscopy. Environ. Technol. 14(6):577-
585.
Knepp, G.L., and G.F. Arkin. 1973. Ammonia Toxicity
Levels and Nitrate Tolerance of Channel Catfish. Prog. Fish-
Cult. 35(4): 22 1-224.
Krainara, T.. 1988. Effects of Ammonia on Walking Catfish,
Clarias batrachus (Linnaeus). Abstracts of Master of
Science Theses, Faculty of Fisheries, Kasetsart University,
Bangkok, Thailand 13:6.
Kulkarni, K.M., and S.V. Kamath. 1980. The Metabolic
Response of Paratelphusa jacquemontii to Some Pollutants.
Geobios 7(2):70-73 (Author Communication Used).
Lang, T., G. Peters, R. Hoffmann, and E. Meyer. 1987.
Experimental Investigations on the Toxicity of Ammonia:
Effects on Ventilation Frequency, Growth, Epidermal
Mucous Cells, and Gill Structure of. Dis.Aquat.Org. 3:159-
165.
Larson James H, Frost Paul C, and Lambert! Gary A.
Variable Toxicity of Ionic Liquid-Forming Chemicals to
Lemna Minor and the Influence of Dissolved Organic
Matter. Environmental Toxicology and Chemistry [Environ.
Toxicol. Chem.]. Vol. 27, no. 3, pp. 676-681. Mar 2008.
2008.
Lay, J.P., A. Peither, I. Juttner, and K. Weiss. 1993. In Situ
Pond Mesocosms for Ecotoxicological Long-Term Studies.
Chemosphere 26(6):1 137-1 150.
ECOTOX or Other
Ref. No
5773
17562
7513
17963
19651
4931
8606
17533
5036
4106
7048
Rejection Code(s)
AF, Dur-1d
AF, UEndp
AF, UEndp
UEndp, Dur
Dur-1d
XNoec
UEndp, Dur
Dur - 7d, Form
AF
AF, UEndp, Dur
UEndp
Mix
AF, UEndp, No Org
Comment(s)
Organic mixture
171
-------
Citation
Lazorchak, J. M. and Smith, M. E. Rainbow Trout
(Oncorhynchus mykiss ) and Brook Trout (Salvelinus
fontinalis ) 7-Day Survival and Growth Test Method.
Arch.Environ.Contam.Toxicol. 53(3), 397-405. 2007
Lee, D.R.. 1976. Development of an Invertebrate Bioassay
to Screen Petroleum Refinery Effluents Discharged into
Freshwater. Ph.D. Thesis, Virginia Polytechnic Inst.and
State University, Blacksburg, VA :108.
Lewis, J.W., A.N. Kay, and N.S. Hanna. 1995. Responses
of Electric Fish (Family Mormyridae) to Inorganic Nutrients
and Tributyltin Oxide. Chemosphere 31(7):3753-3769.
LI, W. E. I., ZHANG ZHAO, and JEPPESEN ERIK. The
Response of Vallisneria Spinulosa (Hydrocharitaceae) to
Different Loadings of Ammonia and Nitrate at Moderate
Phosphorus Concentration: a Mesocosm Approach.
Freshwater Biology [Freshw. Biol.]. Vol. 53, no. 11, pp.
2321-2330. Nov 2008. 2008.
Linton, T.K., I.J. Morgan, P.J. Walsh, and C.M. Wood. 1998.
Chronic Exposure of Rainbow Trout (Oncorhynchus mykiss)
to Simulated Climate Warming and Sublethal Ammonia: A
Year-Long Study of Their Appetite. Can. J. Fish. Aquat.Sci.
55(3):576-586.
Litav, M., and Y. Lehrer. 1978. The Effects of Ammonium in
Water on Potamogeton lucens. Aquat.Bot. 5(2):127-138.
Lloyd, R., and D.W.M. Herbert. 1960. The Influence of
Carbon Dioxide on the Toxicity of Un-lonized Ammonia to
Rainbow Trout (Salmo gairdnerii Richardson).
Ann.Appl.Biol. 48(2):399-404.
Lloyd, R., and L.D. Orr. 1969. The Diuretic Response by
Rainbow Trout to Sublethal Concentrations of Ammonia.
Water Res. 3(5):335-344.
Loong, A. M. , Tan, J. Y. L, Wong, W. P., Chew, S. F., and
Ip, Y. K. Defense Against Environmental Ammonia Toxicity
in the African Lungfish, Protopterus aethiopicus: Bimodal
Breathing, Skin Ammonia Permeability and Urea Synthesis.
Aquat.Toxicol. 85(1), 76-86. 2007.
Loppes, R.. 1970. Growth Inhibition by NH4+ Ions in
Arginine-Requiring Mutants of Chlamydomonas reinhardi.
Mol.Gen.Genet. 109(3):233-240.
Losso, Chiara, Novelli, Alessandra Arizzi, Picone, Marco,
Ghetti, Pier Francesco, and Ghirardini, Annamaria Volpi.
Porewater as a matrix in toxicity bioassays with sea urchins
and bivalves: Evaluation of applicability to the Venice
lagoon (Italy). Environment International 35(1), 118-126.
2009.
Ma, J., Wang, S., Wang, P., Ma, L, Chen, X., and Xu, R.
Toxicity Assessment of 40 Herbicides to the Green Alga
Raphidocelis Subcapitata. Ecotoxicology and Environmental
Safety [Ecotoxicol. Environ. Saf.]. Vol. 63, no. 3, pp. 456-
462. Mar 2006. 2006.
ECOTOX or Other
Ref. No
100026
3402
16156
19144
7093
10018
10019
9619
Rejection Code(s)
Det, AF
Det
UEndp, Dur
Mix
UEndp, Dur
AF, UEndp, Dur
Dur - 8h
UEndp, Dur-1d
Non-NA, No Dose
AF, UEndp, Dur
Mix
Unrel
Comment(s)
7-day tests (S,U) with
ammonia chloride. pH not
reported
This thesis appears to provide
appropriate 48 h LC50 data for
D. pulex, but the paper should
be secured to ensure
acceptability. This reference
was originally screened out
based on title alone.
Plants do not drive criteria, and
therefore, are not included in
CWA review and approval of
ORWQS
Only one exposure
concentration
Plants do not drive criteria, and
therefore, are not included in
CWA review and approval of
ORWQS
No ammonia
172
-------
Citation
ECOTOX or Other
Ref. No
Rejection Code(s)
Comment(s)
Magalhaes Bastos, J.A.. 1954. Importance of Ammonia As
an Ichthyotoxic Substance. (Importancia Da Amonia Como
Substacia Ictiotoxica.). No.159, Serv.Pisciculture,
Publ.Ser.1-C, Dep.Nacl.Onbras Contra Secas, Ministerio
Viacao E Onbras Publicas, Brazil :115-132.
10302
UEndp, Pur
Magallon Barajas Francisco, Villegas Rosalia Servin, Clark
Guillermo Portillo, Mosqueda Joaquin Garcia, and Moreno
Berenice Lopez. Daily Variation in Short-Term Static
Toxicity of Unionized Ammonia in Litopenaeus Vannamei
(Boone) Postlarvae. Aquaculture Research [Aquacult. Res.].
Vol. 37, no. 14, pp. 1406-1412. Oct 2006. 2006.
Dur
Magallon Barajas, F.J., R. S. Villegas, G.P. Clark and B.L.
Moreno. 2006. Litopenaeus vannamei (Boone) post-larval
survival related to age, temperature, pH and ammonium
concentration. Aquacult. Res. 37: 492-499.
No Dose
Only 1 exposure concentration
Malacea, I.. 1966. Studies on the Acclimation of Fish to
High Concentrations of Toxic Substances. Arch.Hydrobiol.
65(1):74-95 (GER) (ENG TRANSL) (1968).
10020
Dur
Malham, Shelagh K., Cotter, Elizabeth, O'Keeffe, Selena,
Lynch, Sharon, Culloty, Sarah C., King, Jonathan W.,
Latchford, John W., and Beaumont, Andy R. Summer
mortality of the Pacific oyster, Crassostrea gigas, in the Irish
Sea: The influence of temperature and nutrients on health
and survival. Aquaculture 287(1-2), 128-138. 2009-.
Mix
Manissery, J.K., and M.N. Madhyastha. 1993.
Haematological and Histopathological Effect of Ammonia at
Sublethal Levels on Fingerlings of Common Carp Cyprinus
carpio. Sci.Total Environ.(Suppl .):913-920.
4314
UEndp
McDonald, S.F., S.J. Hamilton, K.J. Buhl, and J.F.
Heisinger. 1997. Acute Toxicity of Fire-Retardant and
Foam-Suppressant Chemicals to Hyalella azteca
(Saussure). Environ.Toxicol.Chem. 16(7): 1370-1376.
18102
Tox
Also, H. azteca is sensitive to
chloride concentration. EPA
has decided to not use data for
this species until additional
tests are conducted.
Mclntyre, M. , Davis, M., and Shawl, A. The Effects of
Ammonia on the Development, Survival and Metamorphic
Success of Strom bus gigas veligers. 98th
Annu.Meet.Natl.Shellfish.Assoc., Monterery, CA , (ABS).
2006-.
Det
Abstract only
Meador, Michael R. and Carlisle, Daren M. Quantifying
tolerance indicator values for common stream fish species
of the United States. Ecological Indicators 7(2), 329-338.
2007.
Mix
Melching, C. S., Novotny, V., Schilling, J. B., Chen, J., and
Beck, M. B. (eds). Probabilistic Evaluation of Ammonia
Toxicity in Milwaukee's Outer Harbor. Alliance House 12
Caxton Street London SW1H OQS UK . 2006. IWA
Publishing.
Mix
Merkens, J.C., and K.M. Downing. 1957. The Effect of
Tension of Dissolved Oxygen on the Toxicity of Un-lonized
Ammonia to Several Species of Fish. Ann.Appl.Biol.
45(3):521-527.
10021
UEndp, Dur
173
-------
Citation
Merkens, J.C.. 1958. Studies on the Toxicity of Chlorine and
Chloramines to the Rainbow Trout. Water Waste Treat. J.
7:150-151.
Miron, Denise dos, Moraes, Bibiana, Becker, Alexssandro
G., Crestani, Marcia, Spanevello, Roselia, Loro, Vania L,
and Baldisserotto, Bernardo. Ammonia and pH effects on
some metabolic parameters and gill histology of silver
catfish, Rhamdia quelen (Heptapteridae). Aquaculture
277(3-4), 192-196. 2008- .
Mitchell, S.J.Jr.. 1983. Ammonia-Caused Gill Damage in
Channel Catfish (Ictalurus punctatus): Confounding Effects
of Residual Chlorine. Can.J.Fish.Aquat.Sci. 40(2):242-247.
Morgan, W.S.G., and P.C. Kuhn. 1974. A Method to Monitor
the Effects of Toxicants upon Breathing Rate of Largemouth
Bass (Micropterus salmoides Lacepede). Water Res.
8(1):67-77 (Author Communication Used).
Morgan, W.S.G.. 1976. Fishing for Toxicity: Biological
Automonitor for Continuous Water Quality Control. Effluent
Water Treat. J. 16(9):471-472, 474-475 (Author
Communication Used).
Morgan, W.S.G.. 1978. The Use of Fish as a Biological
Sensor for Toxic Compounds in Potable Water. Prog.Water
Technol. 10(1/2):395-398 (Author Communication Used).
Morgan, W.S.G.. 1979. Fish Locomotor Behavior Patterns
as a Monitoring Tool. J.Water Pollut. Control Fed. 51(3):580-
589.
Morris, J. M., Snyder-Conn, E., Foott, J. S., Holt, R. A.,
Suedkamp, M. J., Lease, H. M., Clearwater, S. J., and
Meyer, J. S. Survival of Lost River Suckers (Deltistes
luxatus) Challenged with Flavobacterium columnare During
Exposure to Sublethal Ammonia Concentrations at pH 9.5.
Arch.Environ.Contam.Toxicol. 50(2), 256-263. 2006.
Mosier, A.R.. 1978. Inhibition of Photosynthesis and
Nitrogen Fixation in Algae by Volatile Nitrogen Bases.
J.Environ.Qual. 7(2):237-240.
Mugnier, Chantal, Zipper, Etienne, Goarant, Cyrille, and
Lemonnier, Hugues. Combined effect of exposure to
ammonia and hypoxia on the blue shrimp Litopenaeus
stylirostris survival and physiological response in relation to
molt stage. Aquaculture 274(2-4), 398-407. 2008-.
Mukherjee, S., and S. Bhattacharya. 1974. Effects of Some
Industrial Pollutants on Fish Brain Cholinesterase Activity.
Environ.Physiol.Biochem. 4:226-231 .
Muturi Ephantus J, Jacob Benjamin G, Shililu Josephat, and
Novak Robert. Laboratory Studies on the Effect of Inorganic
Fertilizers on Survival and Development of Immature Culex
Quinquefasciatus (Diptera: Culicidae). Journal of vector
borne diseases, 2007 Dec, 44(4):259-65 . 2007.
ECOTOX or Other
Ref. No
7404
10543
15362
5462
11127
131
97379
15860
668
Rejection Code(s)
UEndp, Dur
Non-NA
UEndp, Dur
UEndp, Dur
UEndp, Dur-1d
UEndp, Dur-1d
UEndp, Dur-1d
Mix
Dur
Non-NA
Dur - 2d
Dilut
Comment(s)
Plants do not drive criteria, and
therefore, are not included in
CWA review and approval of
ORWQS
Deionized water
174
-------
Citation
ECOTOX or Other
Ref. No
Rejection Code(s)
Comment(s)
Nimptsch, J. and Pflugmacher, S. Ammonia Triggers the
Promotion of Oxidative Stress in the Aquatic Macrophyte
Myriophyllum mattogrossense. Chemosphere 66(4), 708-
714. 2007.
100651
Non-NA
Obiekezie, A.I., and P.O. Ajah. 1994. Chemotherapy of
Macrogyrodactylosis in the Culture of African Clariid
Catfishes Clarias gariepinus and Heterobranchus longifiliis.
J.Aquacult.Trop. 9(3):187-192.
16594
AF, UEndp, Pur
Ohmori, M., K. Ohmori, and H. Strotmann. 1977. Inhibition
of Nitrate Uptake by Ammonia in a Blue-Green Alga,
Anabaena cylindrica. Arch.Microbiol. 114(3):225-229.
7605
UEndp, Pur
Plants do not drive criteria, and
therefore, are not included in
CWA review and approval of
ORWQS
Okelsrud, A. and Pearson, R. G. Acute and Postexposure
Effects of Ammonia Toxicity on Juvenile Barramundi (Lates
calcarifer). Arch.Environ.Contam.Toxicol. 53(4), 624-631.
2007.
Non-NA
Olson, K.R., and P.O. Fromm. 1971. Excretion of Urea by
Two Teleosts Exposed to Pifferent Concentrations of
Ambient Ammonia. Comp.Biochem.Physiol.A 40:999-1007.
10243
AF, UEndp, Pur- 1d
Ortiz-Santaliestra, M. E., Marco, A., Fernandez, M. J., and
Lizana, M. Influence of Pevelopmental Stage on Sensitivity
to Ammonium Nitrate of Aquatic Stages of Amphibians.
Environ.Toxicol.Chem. 25(1), 105-111. 2006.
Non-NA
Ortiz-Santaliestra, M. E., Marco, A., Fernandez-Beneitez,
M. J., and Lizana, M. Effects of Ammonium Nitrate
Exposure and Water Acidification on the Pwarf Newt: The
Protective Effect of Oviposition Behaviour on Embryonic
Survival. Aquat.Toxicol. 85(4), 251-257. 2007.
Non-NA
Pagliarani, A., Bandiera, P., Ventrella, V., Trombetti, F.,
Manuzzi, M. P., Pirini, M., and Borgatti, A. R. Response of
Na+-Pependent ATPase Activities to the Contaminant
Ammonia Nitrogen in Tapes philippinarum: Possible
ATPase Involvement in Ammonium Transport.
Arch.Environ.Contam.Toxicol. 55(1), 49-56. 2008.
No Pose
Only 2 exposure
concentrations
Palanichamy, S., S. Arunachalam, and M.P.
Balasubramanian. 1985. Food Consumption of
Sarotherodon mossambicus (Trewaves) Exposed to
Sublethal Concentration of Piammonium Phosphate.
Hydrobiologia 128(3):233-237.
11516
AF, UEndp, Pur
Palanisamy, R., and G. Kalaiselvi. 1992. Acute Toxicity of
Agricultural Fertilizers to Fish Labeo rohita. Environ.Ecol.
10(4):869-873.
8278
AF, Pur
Paley, R.K., I.P. Twitchen, and F.B. Eddy. 1993. Ammonia,
Na+, K+ and C1- Levels in Rainbow Trout Yolk-Sac Fry in
Response to External Ammonia, y) :273-284.
7746
UEndp, Pur-1d
Passell, H. P., Pahm, C. N., and Bedrick, E. J. Ammonia
Modeling for Assessing Potential Toxicity to Fish Species in
the Rio Grande, 1989-2002. Ecological Applications [Ecol.
Appl.]. Vol. 17, no. 7, pp. 2087-2099. Oct 2007. 2007.
Mix
175
-------
Citation
ECOTOX or Other
Ref. No
Rejection Code(s)
Comment(s)
Patrick, R., J. Cairns Jr., and A. Scheier. 1968. The Relative
Sensitivity of Diatoms, Snails, and Fish to Twenty Common
Constituents of Industrial Wastes. Prog.Fish-Cult.
30(3):137-140 (Author Communication Used) (Publ in Part
As 2406).
949
AF
Paul, V.I., and T.K. Banerjee. 1995. Acute Toxicity of
Ammonium Sulphate to the Air-Breathing Organ of the Live
Fish Heteropneustes (Saccobranchus) fossilis (Bloch).
Curr.Sci. 68(8):845-849.
19532
UEndp, Pur
Penaz, M.. 1965. The Influence of Ammonia on the Eggs
and Young of the Common Trout, Salmo trutta var. fario.
Zool.Listy14(1):47-54.
10307
UEndp, Pur
Perez-Landa Victor, Belzunce Maria Jesus, and Franco
Javier. The Effect of Seasonality and Body Size on the
Sensitivity of Marine Amphipods to Toxicants. Bulletin of
environmental contamination and toxicology, 2008 Pec,
81(6):548-52. Epub: 2008 Sep 13 . 2008.
Non-NA
Phillips, B. M., Anderson, B. S., Hunt, J. W., Clark, S. L,
Voorhees, J. P., Tjeerdema, R. S., Casteline, J., and
Stewart, M. Evaluation of Phase li Toxicity Identification
Evaluation Methods for Freshwater Whole Sediment and
Interstitial Water. Chemosphere [Chemosphere]. Vol. 74,
no. 5, pp. 648-653. Feb 2009. 2009.
Mix
Puglis Holly J and Boone Michelle P. Effects of a Fertilizer,
an Insecticide, and a Pathogenic Fungus on Hatching and
Survival of Bullfrog (Rana Catesbeiana) Tadpoles.
Environmental Toxicology and Chemistry [Environ. Toxicol.
Chem.]. Vol. 26, no. 10, pp. 2198-2201. Oct 2007. 2007.
Mix
Ram, R., and A.G. Sathyanesan. 1987. Effect of Chronic
Exposure of Commercial Nitrogenous Fertilizer, Ammonium
Sulfate, on Testicular Pevelopment of a Teleost Channa
punctatus (Bloch). Indian J.Exp.Biol. 25(10):667-670.
24
Non Res, AF, UEndp, Pur
Ram, R.N., and A.G. Sathyanesan. 1986. Ammonium
Sulfate Induced Nuclear Changes in the Oocyte of the Fish,
Channa punctatus (Bl.). Bull.Environ.Contam.Toxicol.
36(6):871-875.
11793
AF, UEndp, Pur
Ram, R.N., and A.G. Sathyanesan. 1986. Inclusion Bodies:
Formation and Pegeneration of the Oocytes in the Fish
Channa punctatus (Bloch) in Response to Ammonium
Sulfate Treatment. Ecotoxicol.Environ.Saf. 11(3):272-276.
12428
AF, UEndp, Pur
Ram, R.N., and A.G. Sathyanesan. 1987. Histopathological
Changes in Liver and Thyroid of the Teleost Fish, Channa
punctatus (Bloch), in Response to Ammonium Sulfate
Fertilizer Treatment. Ecotoxicol.Environ.Saf. 13(2):185-190.
12684
AF, UEndp, Pur
Ram, R.N., and S.K. Singh. 1988. Long-Term Effect of
Ammonium Sulfate Fertilizer on Histophysiology of Adrenal
in the Teleost, Channa punctatus (Bloch).
Bull.Environ.Contam.Toxicol. 41(6):880-887.
2649
AF, UEndp, Pur
Ramachandran, V.. 1960. Observations on the Use of
Ammonia for the Eradication of Aquatic Vegetation.
J.Sci.lnd.Res.19C:284-285; Chem.Abstr.55: (1961).
626
AF, UEndp, Pur
Plants do not drive criteria, and
therefore, are not included in
CWA review and approval of
ORWQS
176
-------
Citation
ECOTOX or Other
Ref. No
Rejection Code(s)
Comment(s)
Rani, E.F., M. Elumalal, and M.P. Balasubramanian. 1998.
Toxic and Sublethal Effects of Ammonium Chloride on a
Freshwater Fish Oreochromis mossambicus. Water Air Soil
Pollut. 104(1/2):1-8.
19157
UChron
Rao, V.N.R., and G. Ragothaman. 1978. Studies on
Amphora coffeaeformis II. Inorganic and Organic Nitrogen
and Phosphorus Sources for Growth. Acta Bot.lndica
6(Suppl):146-154.
5449
AF, UEndp, Pur
Plants do not drive criteria, and
therefore, are not included in
CWA review and approval of
ORWQS
Reddy-Lopata, K., Auerswald, L, and Cook, P. Ammonia
Toxicity and Its Effect on the Growth of the South African
Abalone Haliotis midae Linnaeus. Aquaculture 261(2), 678-
687. 2006.
105390
Non-NA
Redner, B.D., and R.R. Stickney. 1979. Acclimation to
Ammonia by Tilapia aurea. Trans.Am.Fish.Soc. 108:383-
388.
2561
Dur - 3d
Redner, B.D., J.R. Tomasso, and B.A. Simco. 1980. Short
Term Alleviation of Ammonia Toxicity by Environmental
Sodium Chloride in Channel Catfish (Ictalurus punctatus).
J.Tenn.Acad.Sci. 55:54.
407
Dur - 2d
Reichenbach-Klinke, H.H.. 1967. Investigations on the
Influence of the Ammonia Content on the Fish Organism.
Arch.Fischereiwiss. 17(2):122-132 (GER) (ENG TRANSL).
10170
UEndp
Other data used from study
Remen, Mette, Imsland, Albert Kjartansson, Stefansson,
Sigurd O., Jonassen, Thor Magne, and Foss, Atle.
Interactive effects of ammonia and oxygen on growth and
physiological status of juvenile Atlantic cod (Gadus
morhua). Aquaculture 274(2-4), 292-299. 2008-.
No Dose
Only 2 exposure
concentrations
Rice, S.D., and R.M. Stokes. 1975. Acute Toxicity of
Ammonia to Several Developmental Stages of Rainbow
Trout, Salmo gairdneri. Fish.Bull. 73(1):207-211 (Personal
Communication Used).
667
Dur- 1d
Rippon, G.D., and R.V. Hyne. 1992. Purple Spotted
Gudgeon: Its Use as a Standard Toxicity Test Animal in
Tropical Northern Australia. Bull.Environ.Contam.Toxicol.
49(3):471-476.
5770
AF, Dur
Robinette, H.R.. 1976. Effects of Selected Sublethal Levels
of Ammonia on the Growth of Channel Catfish (Ictalurus
punctatus). Prog.Fish-Cult. 38(1):26-29.
524
Dur- 1d
Rodriguez-Ramos, Tania, Espinosa, Georgina, Hernandez-
Lopez, Jorge, Gollas-Galvan, Teresa, Marrero, Jeannette,
Borrell, Yaisel, Alonso, Maria E., Becquer, Ubaldo, and
Alonso, Maray. Effects of Echerichia coli
lipopolysaccharides and dissolved ammonia on immune
response in southern white shrimp Litopenaeus schmitti.
Aquaculture 274(1), 118-125. 2008-.
Non-NA
Romano, Nicholas and Zeng, Chaoshu. Ontogenetic
changes in tolerance to acute ammonia exposure and
associated gill histological alterations during early juvenile
development of the blue swimmer crab, Portunus pelagicus.
Aquaculture 266(1-4), 246-254. 2007-.
Non-NA
177
-------
Citation
Ronan Patrick J, Gaikowski Mark P, Hamilton Steven J,
Buhl KevinJ. , and Summers Cliff H. Ammonia Causes
Decreased Brain Monoamines in Fathead Minnows
(Pimephales Promelas). Brain research, 2007 May 25,
1147:184-91. Epub: 2007 Feb 17 . 2007.
Rose, A., Carruthers, A. M., Stauber, J., Lim, R., and
Blockwell, S. Development of an Acute Toxicity Test with
the Marine Copepod Acartia sinjiensis.
Australas.J.Ecotoxicol. 12(2), 73-81. 2006.
Rubin, A.J., and G.A. Elmaraghy. 1977. Studies on the
Toxicity of Ammonia, Nitrate and Their Mixtures to Guppy
Fry. Water Res. 1 1(10): 927-935.
Rushton, W.. 1921 . Biological Notes. Salmon Trout Mag.
25:101-117.
Saha, N., and B.K. Ratha. 1994. Induction of Ornithine-Urea
Cycle in a Freshwater Teleost, Heteropneustes fossilis,
Exposed to High Concentrations of Ammonium Chloride.
Comp.Biochem.Physiol.B 108(3): 31 5-325.
Salin, D., and P. Williot. 1991 . Acute Toxicity of Ammonia to
Siberian Sturgeon Acipenser baeri. In: P.Willot (Ed.),
Proc.lst Symposium on Sturgeon, Bordeaux (Gironde,
France), Oct.3-6, 1989 :153-167.
Samylin, A.F.. 1969. Effect of Ammonium Carbonate on
Early Stages of Development of Salmon.
Uch. Zap. Leningr.Gos.Pedagog.lnst.lm.A.I.Gertsena. 422:47-
62 (RUS) (ENG TRANSL).
Sarkar, S.K., and S.K. Konar. 1988. Dynamics of Abiotic-
Biotic Parameters of Water and Soil in Relation to Fish
Growth Exposed to Ammonium Sulfate. Environ. Ecol.
6(3):730-733.
Sarkar, S.K.. 1988. Influence of Ammonium Sulphate on the
Feeding Rate of Fish Under Multivariate Temperature.
Comp.Physiol.Ecol. 13(1):30-33.
Sarkar, S.K.. 1991. Dynamics of Aquatic Ecosystem in
Relation to Fish Growth Exposed to Ammonium Sulphate.
J.Environ.Biol. 12(1):37-43.
Sarkar, S.K.. 1991 . Toxicity Evaluation of Urea and
Ammonium Sulphate to Oreochromis mossambicus
(Peters). J.Ecobiol. 3(1):79-80.
Sathyanesan, A.G., K.P. Joy, and R.S. Kulkarni. 1978.
Endocrine Changes in Fishes in Response to Pollutants.
Q.J.Surg.Sci. 14(1/2):67-77.
Schipper, C. A., Dubbeldam, M., Feist, S. W., Rietjens
IMCM, and Murk, A. T. Cultivation of the Heart Urchin
Echinocardium Cordatum and Validation of Its Use in
Marine Toxicity Testing for Environmental Risk Assessment.
Journal of Experimental Marine Biology and Ecology [J.
Exp. Mar. Biol. Ecol.]. Vol. 364, no. 1, pp. 11-18. 12 Sep
2008. 2008.
Schubauer-Berigan, M.K., P.O. Monson, C.W. West, and
G.T. Ankley. 1995. Influence of pH on the Toxicity of
Ammonia to Chironomus tentans and Lumbriculus
variegatus. Environ. Toxicol.Chem. 14(4):713-717.
ECOTOX or Other
Ref. No
7635
11164
16783
7491
2606
804
3235
238
7535
10173
15119
Rejection Code(s)
Det
Non-NA
Dur - 3d
AF, UEndp, Dur
UEndp
Dur- 1d
UEndp, Dur
UEndp / No Org
AF, UEndp, Dur
WatQual, UEndp /No Org
Con
AF, UEndp
Det
UEndp/ Dur -10d/AF
Comment(s)
Other data used from study
Other data used from study
178
-------
Citation
ECOTOX or Other
Ref. No
Rejection Code(s)
Comment(s)
Schulze-Wiehenbrauck, H.. 1976. Effects of Sublethal
Ammonia Concentrations on Metabolism in Juvenile
Rainbow Trout (Salmo gairdneri Richardson).
Ber.Dtsch.Wiss.Kommn.Meeresforsch. 24:234-250.
2616
UEndp, Pur
Shedd, T.R., M.W. Widder, M.W. Toussaint, M.C. Sunkel,
and E. Hull. 1999. Evaluation of the Annual Killifish
Nothobranchius guentheri as a Tool for Rapid Acute
Toxicity Screening. Environ.Toxicol.Chem. 18(10):2258-
2261.
20487
Dur- 1d
Sheehan, R.J., andW.M. Lewis. 1986. Influence of pH and
Ammonia Salts on Ammonia Toxicity and Water Balance in
Young Channel Catfish. Trans.Am.Fish.Soc. 115(6):891-
899.
12194
Dur- 1d
Singh, S.B., S.C. Banerjee, and P.C. Chakrabarti. 1967.
Preliminary Observations on Response of Young Ones of
Chinese Carps to Various Physico-Chemical Factors of
Water. Proc.Nat.Acad.Sci., India 37(3B):320-324;
Biol.Abstr.51:5159(1970).
2629
UEndp, Dur
Slabbert, J.L., and J.P. Maree. 1986. Evaluation of
Interactive Toxic Effects of Chemicals in Water Using a
Tetrahymena pyriformis Toxicity Screening Test. Water S.A.
12(2):57-62.
12836
AF, UEndp, Dur
Slabbert, J.L, and W.S.G. Morgan. 1982. A Bioassay
Technique Using Tetrahymena pyriformis for the Rapid
Assessment of Toxicants in Water. Water Res. 16(5):517-
523.
11048
AF, UEndp, Dur
Smart, G.. 1976. The Effect of Ammonia Exposure on Gill
Structure of the Rainbow Trout (Salmo gairdneri). J.Fish
Biol. 8:471-475(Author Communication Used).
2631
UEndp / Dur
Smith, C.E., and R.G. Piper. 1975. Lesions Associated with
Chronic Exposure to Ammonia. In: W.E.Ribelin and
G.Migaki (Eds.), The Pathology of Fishes, University of
Wisconsin Press, Madison, Wl :497-514.
2636
Uenpd, Dur
Smith, C.E.. 1984. Hyperplastic Lesions of the Primitive
Meninx of Fathead Minnows, Pimephales promelas,
Induced by Ammonia: Species Potential for Carcinogen
Testing. In: K.L.Hoover (Ed.), Use of Small Fish Species in
Carcinogenicity Testing, Monogr.Ser.Natl.Cancer
lnst.No.65, NIH Publ.No.84-2653, U.S.Dep.Health Human
Serv., Natl.Cancer Inst., Bethesda, MD :119-125.
10254
UEndp
Snell, T.W., B.D. Moffat, C. Janssen, and G. Persoone.
1991. Acute Toxicity Tests Using Rotifers IV. Effects of
Cyst Age, Temperature, and Salinity on the Sensitivity of
Brachionus calyciflorus. Ecotoxicol.Environ.Saf. 21(3):308-
317(OECDG Data File).
9385
AF, Dur-1d
Data provided in earlier report
Soderberg, R.W., J.B. Flynn, and H.R. Schmittou. 1983.
Effects of Ammonia on Growth and Survival of Rainbow
Trout in Intensive Static-Water Culture. Trans.Am.Fish.Soc.
112(3): 448-451.
15728
AF, UEndp, Dur
Solomonson, L.P.. 1970. Effects of Ammonia and Some of
its Derivatives on Photosynthesis in the Blue-Green Alga,
Plectonema boryanum. Ph.D.Thesis, Univ.of Chicago,
Chicago, I L:68.
5443
UEndp, Dur
Plants do not drive criteria, and
therefore, are not included in
CWA review and approval of
ORWQS
179
-------
Citation
ECOTOX or Other
Ref. No
Rejection Code(s)
Comment(s)
Speare, D., and S. Backman. 1988. Ammonia and Nitrite
Waterborne Toxicity of Commercial Rainbow Trout.
Can.Vet.J. 29:666.
2958
AF, UEndp, Dur-2d
Spencer, P., Pollock, R., and Dube, M. Effects of Un-
ionized Ammonia on Histological, Endocrine, and Whole
Organism Endpoints in Slimy Sculpin (Cottus Cognatus).
Aquatic Toxicology [Aquat. Toxicol.]. Vol. 90, no. 4, pp. 300-
309. 11 Dec 2008. 2008.
Det
Dilution water not described
Stanley, R.A.. 1974. Toxicity of Heavy Metals and Salts to
Eurasian Watermilfoil (Myriophyllum spicatum L).
Arch.Environ.Contam.Toxicol. 2(4):331-341.
2262
AF
Plants do not drive criteria, and
therefore, are not included in
CWA review and approval of
ORWQS
Suski, C. D., Kieffer, J. D., Killen, S. S., and Tufts, B. L.
Sub-Lethal Ammonia Toxicity in Largemouth Bass.
Comparative Biochemistry and Physiology, Part A:
Molecular & Integrative Physiology [Comp. Biochem.
Physiol., A: Mol. Integr. Physiol.]. Vol. 146, no. 3, pp. 381-
389. Mar 2007. 2007.
No Dose, Pur
Only 2 exposure
concentrations
Tabata, K.. 1962. Toxicity of Ammonia to Aquatic Animals
with Reference to the Effect of pH and Carbonic Acid.
Bull.Tokai Reg.Fish.Res.Lab.(Tokai-ku Suisan Kenkyusho
Kenkyu Hokoku) 34:67-74 (ENG TRANSL).
14284
Dur- 1d
Tarazona, J.V., M. Munoz, J.A. Ortiz, M. Nunez, and J.A.
Camargo. 1987. Fish Mortality due to Acute Ammonia
Exposure. Aquacult.Fish.Manage. 18(2): 167-172.
12807
UEndp, Dur-1d
Taylor, J.E.. 1973. Water Quality and Bioassay Study from
Crawford National Fish Hatchery. Trans.Nebr.Acad.Sci.
2:176-181.
2531
UEndp, Dur - 2d
Thomas, J.D., M. Powles, and R. Lodge. 1976. The
Chemical Ecology of Biomphalaria glabrata: The Effects of
Ammonia on the Growth Rate of Juvenile Snails. Biol.Bull.
151(2):386-397.
15962
UEndp, Dur
Thomas, P.C., C. Turner, and D. Pascoe. 1991. An
Assessment of Field and Laboratory Methods for Evaluating
the Toxicity of Ammonia to Gammarus pulex L. - Effects of
Water Velocity. In: D.W.Jeffrey and B.Madden (Eds.),
Bioindic.Environ.Manage., 6th Symposium, Academic
Press, London, UK :353-363.
6276
UEndp, Dur-1d
Thumann, M.E.. 1950. The Effect of Ammonium Salt
Solutions on Rainbow and Brook Trout and Some Fish
Nutrient Animals. (Uber Die Wirkung Von
Ammoniumsalzlosungen Auf...). Abh.Fischerei.Lieferung
2:327-348.
2528
UEndp, Dur
Thurston, R.V., and R.C. Russo. 1981. Acute Toxicity of
Ammonia to Golden Trout (Salmo aguabonita) and Mottled
Sculpin (Cottus bairdi). Tech.Rep.No.81-1, Fisheries
Bioassay Laboratory, Montana State University, Bozeman,
MT:10.
10221
Dur
Other data used from study
Tilak, K. S. , Veeraiah, K., and Raju, J. M. P. Toxicity and
Effects of Ammonia, Nitrite, Nitrate and Histopathological
Changes in the Gill of Freshwater Fish Cyprinus carpio.
J.Ecotoxicol.Environ.Monit. 16(6), 527-532. 2006
105937
Det, AF, Dur
Detail (no pH, temp, etc.)
180
-------
Citation
ECOTOX or Other
Ref. No
Rejection Code(s)
Comment(s)
Tomasso, J.R., C.A. Goudie, B.A. Simco, and K.B. Davis.
1980. Effects of Environmental pH and Calcium on
Ammonia Toxicity in Channel Catfish. Trans.Am.Fish.Soc.
109(2):229-234 (Personal Communication Used).
410
Dur-1d
Tonapi, G.T., and G. Varghese. 1984. Cardiophysiological
Responses of the Crab, Berytelphusa cunnicularis
(Westwood), to Three Common Pollutants. Indian
J.Exp.Biol. 22(10):548-549.
12198
AF, UEndp, Pur
Tonapi, G.T., and G. Varghese. 1987. Cardio-Physiological
Responses of Some Selected Cladocerans to Three
Common Pollutants. Arch.Hydrobiol. 110(1):59-65.
2075
AF, UEndp, Pur
Tsai, C.F., and J.A. McKee. 1980. Acute Toxicity to Goldfish
of Mixtures of Chloramines, Copper, and Linear Alkylate
Sulfonate. Trans.Am.Fish.Soc. 109(1):132-141 (Personal
Communication Used).
5619
AF, UEndp
Twitchen, I.P., and F.B. Eddy. 1994. Effects of Ammonia on
Sodium Balance in Juvenile Rainbow Trout Oncorhynchus
mykissWalbaum. Aquat.Toxicol. 30(1):27-45.
14071
UEndp
Twitchen, I.P., and F.B. Eddy. 1994. Sublethal Effects of
Ammonia on Freshwater Fish. In: R.Muller and R.Lloyd
(Eds.), Sublethal and Chronic Effects of Pollutants on
Freshwater Fish, Chapter 12, Fishing News Books, London
: 135-147.
18512
UEndp, Pur - 2d
Van den Heuvel-Greve, M., Postma, J., Jol, J., Kooman, H,
Pubbeldam, M., Schipper, C., and Kater, B. A Chronic
Bioassay with the Estuarine Amphipod Corophium volutator:
Test Method Pescription and Confounding Factors.
Chemosphere 66(7), 1301-1309. 2007.
Exp
Sediment exposure
Van Per Heide, T., Smolders, A. J. P., Rijkens, B. G. A.,
Van Nes, E. H., VanKatwijk, M. M., and Roelofs, J. G. M.
Toxicity of Reduced Nitrogen in Eelgrass (Zostera Marina)
Is Highly Pependent on Shoot Pensity and Ph. Oecologia,
158 (3) pp. 411-419, 2008
VarExp
Substantial loss of ammonia;
Plant
Van Vuren, J.H.J.. 1986. The Effects of Toxicants on the
Haematology of Labeo umbratus (Teleostei: Cyprinidae).
Comp.Biochem.Physiol.C83(1):155-159.
11744
AF, UEndp, Pur
Vedel, N.E., B. Korsgaard, and F.B. Jensen. 1998. Isolated
and Combined Exposure to Ammonia and Nitrite in
Rainbow Trout (Oncorhynchus mykiss): Effects on
Electrolyte Status, Blood Respiratory. Aquat.Toxicol.
41(4):325-342.
19154
UEndp
Vijayavel, K., Rani, E. F., Anbuselvam, C., and
Balasubramanian, M. P. Interactive Effect of
Monocrotophos and Ammonium Chloride on the Freshwater
Fish Oreochromis mossambicus with Reference to
Lactate/Pyruvate Ratio. Pestic.Biochem.Physiol. 86(3), 157-
161.2006.
108153
Pet, AF
Petail (pH, temp, etc. not
reported)
Wallen, I.E., W.C. Greer, and R. Lasater. 1957. Toxicity to
Gambusia affinis of Certain Pure Chemicals in Turbid
Waters. Sewage Ind.Wastes 29(6):695-711.
508
Pur, Con, Uendp
181
-------
Citation
ECOTOX or Other
Ref. No
Rejection Code(s)
Comment(s)
Walsh, Patrick J., Veauvy, Clemence, and Weihrauch, Dirk.
Comparison of the mechanisms of ammonia tolerance in
ureotelic (toadfish) versus ammoniotelic (midshipman) fish.
Comparative Biochemistry and Physiology Part C:
Toxicology & Pharmacology 148(4), 464-465. 2008.
Det
Wang, C., Zhang, S. K, Wang, P. F., Hou, J., Li, W., and
Zhang, W. J. Metabolic Adaptations to Ammonia-Induced
Oxidative Stress in Leaves of the Submerged Macrophyte
Vallisneria natans (Lour.) Hara. Aquat.Toxicol. 87(2), 88-98.
2008.
Non-NA
Ward Sara, Augspurger, T. o. m., Dwyer FJames, Kane
Cindy, and Ingersoll Christopher G. Risk Assessment of
Water Quality in Three North Carolina, Usa, Streams
Supporting Federally Endangered Freshwater Mussels
(Unionidae). Environmental Toxicology and Chemistry
[Environ. Toxicol. Chem.]. Vol. 26, no. 10, pp. 2075-2085.
Oct2007. 2007.
Mix
Water Pollution Research Board. 1961. Effects of Pollution
on Fish: Toxicity of Gas Liquors. In: Water Pollution
Research 1960, Water Pollution Research Board, Dep.of
Scientific and Industrial Research, H.M.Stationery Office,
London, England :76-81.
2514
UEndp, Pur
Water Pollution Research Board. 1968. Effects of Pollution
on Fish: Chronic Toxicity of Ammonia to Rainbow Trout. In:
Water Pollution Research 1967, Water Pollution Research
Board, Dep.of Scientific and Industrial Research,
H.M.Stationery Office, London :56-65.
10185
AF, Pur - 2d / UEndp
Watt, P.J., and R.S. Oldham. 1995. The Effect of
Ammonium Nitrate on the Feeding and Development of
Larvae of the Smooth Newt, Triturus vulgaris (L), and on
the Behaviour of Its Food. Freshw.Biol. 33(2):319-324.
14883
UEndp
Watton, A.J. and Hawkes, H.A. 1984. The acute toxicity of
ammonia and copper to the gastropod Potamopyrgus
jenkinsi (Smith). Environ. Pollut. (Series A) 36:17-29.
Non Res
Wee, N. L. J., Tng, Y. Y. M., Cheng, H. T., Lee, S. M. L.,
Chew, S. F., and Ip, Y. K. Ammonia Toxicity and Tolerance
in the Brain of the African Sharptooth Catfish, Clarias
gariepinus. Aquat.Toxicol. 82(3), 204-213. 2007.
No Dose
Only 2 exposure
concentrations
Wickins, J.F.. 1976. The Tolerance of Warm-Water Prawns
to Recirculated Water. Aquaculture 9(1 ):19-37.
2320
AF, UEndp, Pur
Weltering, D.M., J.L. Hedtke, and L.J. Weber. 1978.
Predator-Prey Interactions of Fishes Under the Influence of
Ammonia. Trans.Am.Fish.Soc. 107(3):500-504.
7218
UEndp, Pur
Other data used from study
Wu Jinfeng, Chen Suwen, Chen Lixiong, Mai Yangshan, Lu
Yimin, and Gan Juli. Studies on Toxicity of Sulfide and
Ammonia to Spat of Coelomactra Antiquata. Journal of
tropical oceanograhy/Redai Haiyang Xuebao [J. Trap.
Oceanogr./Redai Haiyang Xuebao]. Vol. 25, no. 1, pp. 42-
46.2006. 2006.
Pet, Forgn
182
-------
Citation
ECOTOX or Other
Ref. No
Rejection Code(s)
Comment(s)
Xu, Q., and R.S. Oldham. 1997. Lethal and Sublethal
Effects of Nitrogen Fertilizer Ammonium Nitrate on Common
Toad (Bufo bufo) Tadpoles. Arch.Environ.Contam.Toxicol.
32(3):298-303.
17840
AF, UEndp, Pur
Corresponding Code List
ABIOTIC FACTOR
(AF)
ACELLULAR
(Ace)
BACTERIA
(Bact)
BIOMARKER
(Biom)
CONTROL
(Con)
DETAIL
(Det)
DURATION
(Dur)
EFFLUENT
(Efflu)
EFFECT
(Eff)
ENDPOINT
(UEndp)
FIELD
(Field)
FORMULATION
(Form)
IN VITRO
(InVit)
LETHAL TIME
(LT)
NO DOSE or CONG
(No Dose or Cone)
NOMINAL
(Norn)
NON-RESIDENT
(NonRes)
NO ORGANISM
(No Org)
PURITY
(Pur)
ROUTE OF EXPOSURE
(RouExp)
TOXICANT
(Tox)
Studies where an abiotic factor such as total water hardness, pH, or temperature are not
reported for a criteria for which this information is necessary to derive a Species Mean Acute or
Chronic Value, i.e., several freshwater metals, pentachlorophenol, ammonia.
Studies of acellular organisms (protozoa) and yeast.
Studies describing only the results on bacteria.
Studies reporting results for a biomarker having no reported association with a biologically
significant adverse effect (survival, growth, or reproduction of an individual or population) and an
exposure dose (or concentration).
Studies where control mortality is insufficient or unsatisfactory, i.e., where survival is less than
90% in acute tests or 80% in chronic tests; or where no control is used.
Insufficient detail regarding test methodology or statistical analysis.
Laboratory and field studies where duration of exposure is inappropriate (e.g., too short) for the
type of test (i.e., acute or chronic), or was not reported or could not be easily estimated.
Studies reporting only effects of effluent, sewage, or polluted runoff where individual pollutants
are not measured.
Studies where the biologically significant adverse effect was not survival, growth, or reproduction
of an individual or population.
Studies reported in ECOTOX where an endpoint (LC50, EC50, NOEC, LOEC, MATC, EC20,
etc.) was not provided, where none of the concentrations tested in a chronic test were
deleterious (no LOEC); or where all concentrations tested in a chronic test caused a statistically
significant adverse effect (no NOEC).
Chronic, long-term studies conducted in a field setting (stream segment, pond, etc.) where
source/dilution water is not characterized for other possible contaminants.
Studies where the chemical is a primary ingredient in a commercial formulation, e.g., biocide,
fertilizer, etc.
In vitro studies, including only exposure of the chemical to cell cultures and excised tissues and
not related to whole organism toxicity.
Laboratory studies reporting only lethal time to mortality, except under special conditions (no
other applicable information is available for species pivotal in making a finding).
Studies with too few concentrations to establish a dose-response, or no usable dose or
concentration reported in either primary or sister article(s), except under special conditions (no
other applicable information is available for species pivotal in making a finding).
Chronic studies where test concentrations were not measured.
Species that are not resident to North America, or where there is no reported evidence of their
reproducing naturally in North America.
Laboratory and field studies where no one organism is studied (e.g., periphyton community) or
where no scientific/common name is given in either a primary or sister article(s).
Studies where the chemical purity of the toxicant was less than 80% pure (active ingredient).
Dietary or un-natural exposure routes for aquatic chemicals, e.g., injection, spray, inhalation.
Inappropriate form of toxicant used or none identified in a laboratory or field study. Note:
Inappropriate form includes mixtures.
183
-------
UNACCEPTABLE CHRONIC
(UChron)
UNUSUAL DILUTION
WATER
(Dilut)
VARIABLE EXPOSURE
(VarExp)
WATER QUALITY
(WatQual)
Chronic studies which were not based on flow-through exposures (exception for cladocerans
and other small, planktonic organisms where test water is continuously renewed) and/or where
test concentrations were not measured.
Laboratory or field studies where the dilution water contained unusual amounts or ratios of
inorganic ions or was without addition of appropriate salts (i.e., distilled or de-ionized water).
Excessive variability in contaminant concentrations during the exposure period.
Studies where the measured test pH is below 6 or greater than 9, where dissolved oxygen was
less than 40% saturation for any length of time, or where total or dissolved organic carbon is
greater than 5 mg/L.
184
------- |