Draft
9/30/98
AMBIENT AQUATIC LIFE WATER QUALITY CRITERIA
ATRAZINE
Prepared by
University of Wisconsin - Superior
Superior, Wisconsin 54880
and
Great Lakes Environmental Center
Traverse City, Michigan 49686
Prepared for
U. S. Environmental Protection Agency
Office of Water
Office of Science and Technology
Health and Ecological Effects Criteria Division
Washington, D.C.
Office of Research and Development
Environmental Research Laboratories
Duluth, Minnesota
Narragansett, Rhode Island
EPA Contract No. 68-C6-0036
Work Assignment No. B-05
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Draft
9/30/98
AMBIENT AQUATIC LIFE WATER QUALITY CRITERIA FOR
ATRAZINE
CAS Registry No. 1912-24-9
September 1998
U.S. ENVIRONMENTAL PROTECTION AGENCY
OFFICE OF WATER
OFFICE OF SCIENCE AND TECHNOLOGY
HEALTH AND ECOLOGICAL CRITERIA DIVISION
WASHINGTON D.C.
OFFICE OF RESEARCH AND DEVELOPMENT
ENVIRONMENTAL RESEARCH LABORATORIES
DULUTH, MINNESOTA
NARRAGANSETT, RHODE ISLAND
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NOTICES
This document has been reviewed by the Criteria and Standards Division, Office
of Water Regulations and Standards, U.S. Environmental Protection Agency, and
approved for publication.
Mention of trade names or commercial products does not constitute endorsement
or recommendation for use.
This document is available to the public through the National Technical
Information Service (NTIS), 5285 Port Royal Road, Springfield, VA 22161.
ii
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FOREWORD
Section 304(a)(l) of the Clean Water Act of 1977 (P.L. 95-217) requires
the Administrator of the Environmental Protection Agency to publish water
quality criteria that accurately reflect the latest scientific knowledge on
the kind and extent of all identifiable effects on health and welfare that
might be expected from the presence of pollutants in any body of water,
including ground water. This document is a revision of proposed criteria
based upon consideration of comments received from other federal agencies,
state agencies, special interest groups, and individual scientists. Criteria
contained in this document replace any previously published EPA aquatic life
criteria for the same pollutant(s).
The term "water quality criteria" is used in two sections of the Clean
Water Act, section 304(a)(l) and section 303(c){2). The term has a different
program impact in each section. In section 304, the term represents a non-
regulatory, scientific assessment of ecological effects. Criteria presented
in this document are such scientific assessments. If water quality criteria
associated with specific stream uses are adopted by a state as water quality
standards under section 303, they become enforceable maximum acceptable
pollutant concentrations in ambient waters within that state. Water quality
criteria adopted in state water quality standards could have the same
numerical values as criteria developed under section 304. However, in many
situations states might want to adjust water quality criteria developed under
section 304 to reflect local environmental conditions and human exposure
patterns. Alternatively, states may use different data and assumptions than
EPA in deriving numeric criteria that are scientifically defensible and
protective of designated uses. It is not until their adoption as part of
state water quality standards that criteria become regulatory. Guidelines to
assist the states and Indian tribes in modifying the criteria presented in
this document are contained in the Water Quality Standards Handbook (U.S. EPA,
1994). This handbook and additional guidance on the development of water
quality standards and other water-related programs of this Agency have been
developed by the Office of Water.
This final document is guidance only. It does not establish or affect
legal rights or obligations. It does not establish a binding norm and cannot
be finally determinative of the issues addressed. Agency decisions in any
particular situation will be made by applying the Clean Water Act and EPA
regulations on the basis of specific facts presented and scientific
information then available.
Tudor T. Davies
Director
Office of Science and Technology
iii
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ACKNOWLEDGMENTS
Daniel J. Call
(freshwater author)
University of Wisconsin-Superior
Superior, Wisconsin
iv
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CONTENTS
Page
Notices ii
Foreword iii
Acknowledgments iv
Tables v-i
Introduction 1
Acute Toxicity to Aquatic Animals 7
Chronic Toxicity to Aquatic Animals . 10
Toxicity to Aquatic Plants 16
Bioaccumulation 19
Other Data 20
Unused Data 42
Summary 44
National Criteria 47
Implementation 48
References 129
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TABLES
Page
1. Acute Toxicity of Atrazine to Aquatic Animals 51
2. Chronic Toxicity of Atrazine to Aquatic Animals 54
3. Ranked Genus Mean Acute Values with Species Mean Acute-Chronic
Ratios 56
4. Toxicity of Atrazine to Aquatic Plants 59
5. Bioaccumulation of Atrazine by Aquatic Organisms 67
6. Other Data on Effects of Atrazine on Aquatic Organisms 68
vi
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Tntroduet ion
Atrazine is an herbicide with the empirical formula CgH^CljNs and a
molecular weight of 215.7. It is a white, crystalline solid with a melting
point of 173-177°C, a boiling point of 279°C, and solubility in water of 33
mg/L at 25°C (Hunter et al. 1985; Farm Chemicals Handbook 1987). Atrazine has
an a-octanol-water partition coefficient (log P) of 2.82, a vapor pressure of
7.34 x 10~4 mm Hg, a Henry's Constant of 8.32 x 10"6 atm*m3/M, and a hydrolysis
half-life in excess of 1,000 days (Hunter et al. 1985). These physico-
chemical properties contribute to its environmental partitioning and degree of
persistence in the aquatic environment.
Atrazine is used extensively in the United States, Canada and other
countries for control of weeds in agricultural crops, especially in crops such
as corn, sorghum, wheat and soybeans. It is one of the most heavily used
pesticides in North America, generally being among the top few for total
pounds of herbicide used (Council on Environmental Quality 1984; Pike 1985;
Braden et al. 1989; Moxley 1989; Richards and Baker 1993; Ciba-Geigy 1994;
Burridge and Haya, 1988). Annual domestic usage during the past two decades
has been in the general range of 40-50 million kilograms applied to
approximately 25 million hectares of farm land in the U.S. (Eisler 1989). It
is also commonly used in other countries (Galassi et al. 1992,1993; Bester and
Huhnerfuss 1993; Hendriks and Stouten 1993; Lode et al. 1994; Bester et al.
1995; Caux and Kent 1998).
With this magnitude of application, atrazine has been commonly
detected in surface waters of agricultural watersheds where it is used. Being
relatively mobile from soil, atrazine surface water concentrations are highest
in field runoff, with concentration peaks generally following early major
1
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storm events within a few weeks of application (Muir et al. 1978; Triplett et
al. 1978; Wauchope 1978; Wauchope and Leonard 1980; Glotfelty et al. 1984).
Concentrations in the low mg/L range may be encountered in edge-of-field run-
off (Hall et al. 1972; Kadoum and Mock 1978; Roberts et al. 1979; Klaine et
al. 1988). Field run-off is diluted upon entering a stream or lake, resulting
in atrazine concentrations that are generally much lower (e.g., 1-10 ngfL
range) in such waters (Richard et al. 1975; Frank and Sirons 1979; Frank et
al. 1979; Roberts et al. 1979; Hu 1981; Richards and Baker 1993). Only trace
levels (i.e., <1.0-33 ng/L) were reported in a pesticide monitoring study in
California (Pereira et al. 1996). However, individual maximum concentrations
may be considerably higher. When considered over several years, maximum
concentrations reported in some creeks and rivers from midwestern agricultural
areas have ranged between 5 and 70 jug/L (Muir et al. 1978; Frank and Sirons
1979; Frank et al. 1979, 1982; Roberts et al. 1979; Illinois State Water
Survey 1990; Richards and Baker 1993; Ciba-Geigy 1992a,e, 1994).
Surface waters surrounded by agricultural lands may receive several
pulsed doses over the growing season corresponding to rainfall events (Herman
et al. 1986). Annual patterns of atrazine concentrations in Ohio streams show
peak time-weighted mean concentrations of about 6 ^ig/L in early June, with a
rapid increase between April and June followed by a rapid decrease between
June and August (Richards and Baker 1993). Time-weighted mean concentrations
between August and December are considerably lower, most frequently being less
than 1.0 Aig/I>. Atrazine concentrations are the lowest, and uniformly so,
between January and April. Also, smaller streams were shown to have higher
peak concentrations, but of shorter duration, than larger streams (Richards
and Baker 1993). The annual cycle is similar in southwestern Ontario, but
with the annual peak concentrations occurring several weeks later and peak
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concentrations being lower than in Ohio (Bodo 1991). Nonetheless, atrazine
concentrations in Ontario have regularly exceeded 2 ;ig/L, the Canadian water
quality guideline for aquatic life protection (Trotter et al. 1990).
Exceedances have similarly been reported in surface waters of Quebec (Caux and
Kent 1995).
Among the highest surface water concentrations of atrazine are those
in small reservoirs in southern Illinois. These are currently being
intensively monitored (Tierney et al. 1994a). Maximum concentrations as high
as 55 Aig/L have been reported from these reservoirs.
Similar seasonal trends in concentrations of atrazine to those in Ohio
streams have been observed in streams in Illinois (Illinois State Water Survey
1990; Ciba-Geigy 1992a), in Iowa (Ciba-Geigy 1994), and in other midwestern
states (Ciba-Geigy 1992e). In large rivers, such as the Mississippi, Missouri
and Ohio Rivers, peak concentrations have most commonly occurred in June, with
the means during the spring period being less than 5.0 pg/L (Ciba-Geigy
1992b). The maximum concentrations were generally between 2 and 8 ptg/L, with
.a single maximum as high as 17.25 pg/L (Ciba-Geigy 1992b,c). Atrazine
concentrations in the Mississippi River between Minneapolis, Minnesota, and
New Orleans, Louisiana, from July to August, 1991, ranged from 0.054 ug/L to
4.7 ug/L (Pereira and Hostetler 1993).
Atrazine residues in Illinois lakes tended to be lower than those in
the streams, with less pronounced peak values, but the lower concentrations
were sustained for longer durations (Ciba-Geigy 1992a). It should be noted
that the maximum observed atrazine concentration was less than 3.0 pg/L at 61
percent of 42 sites monitored over 6 years between 1975 and 1988 (Ciba-Geigy
1992a).
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Atrazine concentrations were considerably lower in Chesapeake Bay and
its tributaries (Ciba-Geigy 1992d). Here, the maximum observed concentration
in a tributary was 14.6 pg/L, and only 3 out of 600 samples analyzed between
1976 and 1991 exceeded 3.0 ^rg/L. The highest observed maxima in Upper and
V
Lower Chesapeake Bay were 1.7 and 0.38 ptg/L, respectively. Models for the
Great Lakes suggest that concentrations should be quite low, not likely to
exceed 0.13 A«g/L (Tieraey et al. 1994b). Individual measurements from Lake
Erie taken at Toledo, Ohio, have not exceeded 0.35 /jg/L, while concentrations
measured from samples collected in Lake Michigan at Michigan City, Indiana,
have been below 0.20 /jg/L (Ciba-Geigy 1992e).
In addition to field run-off, atrazine residues are also transported
by volatilization into the atmosphere and subsequent deposition. Atrazine has
been measured in fog (Glotfelty et al. 1987), and trace amounts have been
shown to be transported by the wind (Elling et al. 1987). Atrazine was
present year-round in rainwater samples in Maryland, with the highest
concentration of 2.2 ftg/L occurring in May (Hu 1981).
Atrazine has been shown to be enriched at the microsurface layer of
water (Wu et al. 1980; Wu 1981). This may be due to the presence of
microsurface films which tend to concentrate certain chemicals. Wu (1981)
suggested that atrazine enrichment in the microsurface layer was more likely a
source of atmospheric input rather than a result of atmospheric deposition,
and that the main source of atrazine at the site studied in Maryland was
agricultural runoff.
Studies of atrazine persistence in water have produced varying
results. Huckins et al. (1986) reported the loss of atrazine from water
within 4 days in a simulated prairie pond microcosm. In shallow artificial
streams, a 50% loss of atrazine occurred in 3.2 days (Kosinski 1984; Moorhead
4
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and Kosinski 1986). Lay et al. (1984) reported an 82% loss in 5 days and a
95% loss in 55 days. The half-life of atrazine in wetland mesocosms was from
8 to 14 days (Detenbeck et al. 1996). The half-life of "c-labeled atrazine
has been measured in estuarine water as 3 to 12 days, compared to 15 to 30
days in estuarine sediment and 330 to 385 days in agricultural soils (Kemp et
al., 1981; Jones et al., 1982). These rapid losses in small artificial
systems and in an estuarine environment are contrasted with reports of a 300-
day half-life in a larger lake system (Yoo and Solomon 1981), surface water
losses of only 33% in 120 days and 0% in 85 days in two separate 0.49 hectare
pond applications (Klaassen and Kadoum 1979), and a loss of only 40-50% in
pond water over a period of more than 5 months (Gunkel 1983). In two months
time, approximately 25-30% of single 20 and 500 ng/L atrazine applications to
a 0.045 hectare Kansas pond had disappeared from the water (deNoyelles et al.
1982). Approximately 25 percent of the initial applications remained after 12
months. The half-life of atrazine was approximately 3 months in Tasmanian
streams (Davies et al. 1994). Thus, the persistence of atrazine in water
appears highly variable, dependent perhaps upon both the nature of the aquatic
system into which it is introduced as well as the climatic conditions at the
exposure site.
Biodegradation is considered to be one of the most important processes
governing the environmental fate of atrazine (Radosevich et al. 1996).
Microbes isolated from aquatic ecosystems that are capable of degrading
atrazine have been reported. Mirgain and colleagues (1993) isolated a
Paeudomonaa putida/Xanthomonaa maltophilia. pair with atrazine-degrading
ability. Certain soil bacteria have also been shown to be capable of
degrading atrazine both aerobically and anaerabically (Behki et al. 1993;
Radosevich et al., 1995,1996). Some soil fungi also can degrade atrazine
5
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(Donnelly et al., 1993). The degradation products of atrazine were less toxic
to submerged aquatic vascular plants than the parent compound (Jones and
Winchell, 1984). In a salt marsh environment, the incorporation of atrazine
into the sediment appeared to be a prerequisite for its degradation (Meakins
et al. 1995). Very little degradation occurred in the water column.
The mode of atrazine"s toxic action toward plants is blockage of
electron transport within the Hill reaction of photosystem II, thereby
inhibiting photosynthesis (Moreland 1980). Vascular plants and algae are both
affected by this mode of action. In this way, atrazine has the demonstrated
capacity to reduce primary productivity in aquatic ecosystems (deNoyelles et
al. 1982; Kosinski and Merkle 1984; Dewey 1986; Herman et al. 1986; Pratt et
al. 1988).
Atrazine is also used in combination with other herbicides. These
include alachlor, ametryne, linuron, paraquat, propachlor, amitrole, and
cyanazine (Farm Chemicals Handbook 1987).
Several reviews exist on atrazine and its environmental impact (CCREM
1989; Eisler 1989; Huber 1993; deNoyelles et al. 1994; Solomon et al. 1996).
These reviews indicated that a few species of aquatic plants have been shown
to be slightly affected by atrazine at concentrations below 10 pg/L. The
review by deNoyelles et al. (1994) stated that herbicides have little direct
effects upon animals, and that they tend to produce ecosystem effects from the
bottom of the food chain upward, in contrast to insecticides which act in the
opposite direction. Huber (1993) and Solomon et al. (1996) stated that plants
readily recovered from the inhibitory effects of atrazine once the exposure
was reduced or eliminated.
An understanding of the "Guidelines for Deriving Numerical National
Water Quality Criteria for the Protection of Aquatic Organisms and Their Uses"
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(Stephan et al. 1985), hereafter referred to as the Guidelines, and the
response to public comment (U.S. EPA 1985a) is necessary to evaluate the
following text, tables, and calculations.
Whenever adequately justified, a national criterion may be replaced by
a site-specific criterion (U.S. EPA 1983a), which may include not only site-
specific criterion concentrations (U.S. EPA 19S3b), but also site-specific
durations of averaging periods and site-specific frequencies of allowed
excursions (U.S. EPA 1985b). The latest comprehensive literature search for
this document was conducted in January, 1997. Data in the files of the U.S.
EPA's Office of Pesticide Programs concerning the effects of atrazine on
aquatic organisms and their uses have been evaluated for use in the derivation
of aquatic life criteria. Some more recent information was also included.
Acute Taxi-City to Acruatic Animals
The data that are available according to the Guidelines concerning the
acute toxicity of atrazine are presented in Table 1. Acute toxicity data for
eight freshwater invertebrate species ranged from 720 /ug/L for first instar
larvae of a midge, Chlronomua tentanar (Macek et al. 1976) to >37,100 A/g/L for
an annelid, Lumbgieulua variegatua (Brooke 1990). A hydroid coelenterate
(fiXdca SP-) was the second most sensitive invertebrate tested, with an ECS0 of
3,000 ug/L (Brooke 1990). Stonefly (Acroneuria sp.) nymphs had an LC50 of
6,700 A/g/L and the amphipod, Hyalella azteca. had an LC50 of 14,700 A
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tested, a snail fPhyaa sp.) had an LC50 in excess of 34,100 ug/L (Brooke
1990).
The brook trout (Sa\velinus fontlnalia) was the most sensitive
freshwater vertebrate species tested, with an LC50 of 6,300 pg/L (Macek et al.
1976; Table 1). The fathead minnow (Pimephalea promegas) had a SMAV of 20,000
pg/L, while the LC50 for the brown trout (Salrno trutta) was 27,000 pg/L
(Grande et al. 1994). The LCSO's for the remaining four vertebrate species,
all fishes, were "greater than" values of 8,000, 10,000, 10,000, and 18,000
pg/L for the bluegill (Leppmla maeroehirua) (Macek et al. 1976), largemouth
bass (MipropteruB aalmoideg) (Jones 1962), channel catfish (letalurua
pimetatua) (Jones 1962), and coho salmon (Oncorhynchua kiauteh) (Lorz et al.
1979), respectively. The SMAV was based upon flow-through tests with measured
toxicant concentrations in the cases of Daphnia magna and the fathead minnow,
where other test results were also available.
Genus Mean Acute Values (Table 3) were identical to the SMAVs in all
cases. Of the 15 freshwater genera for which acute values are available, the
most sensitive genus, Chironomua. was over 50 times more sensitive than the
most tolerant, Lumbrieulua. Both the most sensitive and most tolerant were
invertebrates. The freshwater Final Acute Value for atrazine was calculated
to be 657.3 ug/L using the procedure described in the Guidelines and the Genus
Mean Acute Values for invertebrates and fish in Table 3. The Final Acute
Value is lower than all available freshwater Species Mean Acute Values.
The acute toxicity of atrazine to resident North American saltwater
animals has been determined with eight species of invertebrates and two
species of fish (Table 1). Although only two fish species were tested, fish
appear to have a similar sensitivity to atrazine as do invertebrates. The
acute values range from 1,000 t^gfL for mysids, Myaldopaia bahia (Ward and
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Ballantine, 1985) to >30,000 yug/L for the eastern oyster, CrasBostrea
virginlca (Ward and Ballantine, 1985). The copepod, Aeartia tonaa. had
similar LC50 values between a static unmeasured test (Ward and Ballantine,
1985) and two renewal tests (Thursby et al. 1990) with measured values of 94,
91.73 and 210.1 /ug/L, respectively. An additional flow-through measured test
(McNamara, 1991a) with the same species yielded an LC50 of 4,300 yug/L. It is
unclear why there is such a large difference between the flow-through measured
value and the other measured results. There was nothing unusual about the
variability of the chemistry data from the flow-through tests to indicate a
problem (coefficient of variations ranged from 2 to 15%). A possible
explanation is that the renewal, measured values were from tests conducted
with 70% technical grade atrazine (compared to 97.1% atrazine used in the
flow-through test). The "other 30%" may have contributed to the higher
toxicity. Because there is no obvious problem with the flow-through data set
for &. tonaa. the Guidelines state that the flow-through measured value must
be used. Therefore, the SMAV for this species is 4,300 /^g/L. LCSOs for the
copepod, Eurytemora affinia. were 500, 2,600 and 13,200 /ug/L at salinities of
5, 15 and 25 g/L, respectively (Hall et al. 1994a,b). The resultant SMAV was
2,579 /ug/L.
Genus Mean Acute Values (Table 3) were identical to the SMAVs in all
cases with the exception of Acartja where the two species tested had different
SMAVs. The four most sensitive saltwater genera to atrazine are all
crustacean genera. The saltwater Final Acute Value for atrazine, 611.7 ^g/L,
was calculated using the procedure described in the Guidelines and the Genus
Mean Acute Values in Table 3. This saltwater Final Acute Value is lower than
all available saltwater SMAVs.
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ChgQni.e foxi-city to Aquatic Animals
The available data concerning the chronic toxicity of atrazine that
are usable according to the Guidelines are presented in Table 2. Freshwater
tests have been completed with three invertebrate and three fish species.
The cladoceran, Ceriodaphnia dubla. was exposed to atrazine over its
entire life cycle in two 7-day tests (Oris et al. 1991). The end result was
identical in both tests, with chronic limits of 2,500 and 5,000 /ug/L, and a
calculated chronic value (geometric mean) of 3,500 pg/L. An accompanying
acute toxicity test resulted in an LC50 of >30,000 /jg/L. The resultant acute-
chronic ratio was >8.571.
In another 7-day life cycle exposure (Jop 1991d), atrazine did not
affect survival at any of the test concentrations (i.e., 290, 600, 1,200,
2,500 or 4,900 pg/L. However, reproduction was significantly reduced at the
two highest treatment levels. An average of 10 young per female were produced
at these two treatments compared to a mean of 23 for the pooled controls. The
chronic limits in this study were 1,200 and 2,500 pg/L, and the chronic value
was 1,732 /ug/L. An accompanying acute value of >4,900 pg/L resulted in an
acute-chronic ratio of >2.829.
The cladoceran, Daphnia magma, was continuously exposed to atrazine
over three generations for a total of 64 days (Hacek et al. 1976). Mean
measured concentrations of 250, 550 and 1,150 pg/L significantly reduced young
production in the first generation animals, while production at mean
concentrations of 60 and 140 pg/L was similar to controls. Variability in the
data for second and third generations precluded statistical significance of
generally reduced production with increased atrazine concentration. Chronic
limits based on young production by first generation daphnids were 140 and 250
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Aig/L, with a resultant chronic value (geometric mean) of 187 pg/L. A
corresponding acute value of 6,900 ^g/L (Macek et al. 1976) yielded an acute-
chronic ratio of 36.90.
The midge, Chironomus tentana, was continuously exposed to atrazine
for two generations in a life-cycle test (Macek et al. 1976). The test was
initiated by exposing first generation eggs through the various larval instar
stages, pupation and emergence. Eggs from first generation adults were then
continuously exposed in a similar fashion. Mean measured concentrations were
110, 230, 420, 780 and 1,330 pg/L. No significant differences between
controls and the lowest exposure (110 /ug/L) were noted in hatchability,
survival, pupation or emergence in first generation animals. Significant
reductions in the number of adults emerging in the first generation exposure
occurred at atrazine concentrations of 230 and 420 pg/l>- First generation
larvae exposed to higher concentrations experienced high mortality at the
early instar stages.
In the second generation, hatchability was reduced at 420 ^g/L, while
pupation and emergence were reduced at 230 and 420 Aig/L of atrazine. Exposure
to 110 Atg/L had no effect on growth or development of the chironomid larvae.
Based on these observations, the chronic limits were 110 and 230 Aig/L, and the
resultant chronic value (geometric mean) was 159 Aig/L. A corresponding acute
value of 720 fig/L (Macek et al. 1976) yielded an acute-chronic ratio of 4.528
for Chironomua tentans.
Yearling brook trout (Salvelinua fontinalia) and their offspring were
continuously exposed to atrazine for 306 days at mean measured concentrations
of 65, 120, 240, 450 and 720 pg/L (Macek et al. 1976). At 90 days,
significant reductions in weight and total length of first generation fish
occurred at concentrations of 240 A/g/L and above. At 306 days, weight and
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•total length of first generation fish were significantly less than controls at
atrazine exposures of 120 pg/L and above. Fish at these exposures also
appeared lethargic in comparison to the controls and fish at 65 pg/L.
Spawning activity and hatchability of second generation fry did not
appear to be affected, although considerable variability between replicates in
the parameters of total number of eggs spawned/ number of eggs per female,
percent fertilization and hatchability precluded statistical interpretation.
High replicate variability was also observed in morphological development of
the embryos. At 30 days of exposure, fry survival was similar for all
treatments, but was significantly reduced at concentrations of 240 A
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reproductive parameters of mean number of eggs produced per female and mean
number of eggs per spawn; or in hatchability, survival and growth of second
generation fish through 30 and 60 days. Based on a lack of any observed
adverse effect at the highest exposure of 213 /ug/L and an observation of 25
percent mortality in 3 to 5-day old fry after 96 hr of exposure at 870 ^/g/L,
the chronic limits were set at 213 and 870 Aig/L, with a resultant chronic
value (geometric mean) .of 430 Aig/L. A corresponding acute value of 15,000
pg/L (Macek et al. 1976) yielded an acute-chronic ratio of 34.88.
A fathead minnow full life-cycle chronic test that extended for 274
days was performed, with mean measured atrazine concentrations of 0, 150, 250,
460, 990 and 2,000 /jg/L (Dionne 1992). At 30 days, F0 larval length was
significantly reduced by concentrations >990 /ug/L, whereas at 60 days, length
was reduced at concentrations >460 pg/L. At 274 days, survival was
significantly reduced at 990 and 2,000 ^g/L of atrazine. There was no effect
upon the reproductive parameters of number of eggs per spawn, total number of
eggs produced, number of spawns per female, or number of eggs per female at
any treatment level. . Hatching success was slightly, but significantly,
reduced at concentrations of 250 ng/L and above. Ft larval growth (length and
weight) was significantly reduced at >460 A«g/L of atrazine. The chronic
limits were reported to be 250 and 460 i/g/L, based upon F0 and Ft larval
growth. This resulted in a chronic value of 339 pg/L. An accompanying acute
value of 20,000 A/g/L yielded an acute-chronic ratio of 59.00.
Bluegills (Lepomia maeroehirufl) were continuously exposed to atrazine
for 18 months, starting with 7-10 cm long fish, continuing through spawning,
and into a second generation for 60 days (Macek et al 1976). Mean measured
exposure concentrations were 8, 14, 25, 49 and 95 pg/L. Survival and growth
of first generation fish exposed to atrazine for 6 and 18 months were similar
13
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to the controls. Spawning activity was too sporadic to indicate any adverse
effects. Percent hatchability of eggs was similar to controls at
concentrations between 14 and 95 i/g/L. Low fry survival in the second
generation controls for the first 30 days precluded observations on survival
effects due to atrazine in this time interval. However, between 30 and 90
days, survival was near 100 percent in the controls and all atrazine
treatments. Total length of second generation fish through 90 days was
considered to be unaffected by any of the atrazine exposures. From a lack of
any adverse effect at concentrations as high as 95 Aig/L, and from an observed
lose of equilibrium in bluegills exposed to 500 /jg/L for 28 days, the chronic
limits were set at 95 and 500 Aig/L. The resultant chronic value was 218 ng/L.
A corresponding acute value of >8,000 pg/L (Macek et al. 1976) yielded an
acute-chronic ratio of >36.70.
The acute values for Paphnia magna. Chlronomua tentana. Salvelinus
fontinalla. Plmephalea promelaa and Lepomis maeroehiruB in tests reported by
Macek et al. (1976) were used in calculating acute-chronic ratios even though
the acute test concentrations were not measured. This was because of close
agreement between nominal and measured concentrations in the chronic tests.
For six chronic tests, the overall agreement between measured and nominal
concentrations was 94.4 percent. Therefore, it appeared likely that the
nominal concentrations presented for acute tests were also in good agreement
with actual concentrations.
The chronic toxicity of atrazine to saltwater species has been
determined in an 8-day test with the copepod, Euryfcemora affinia and in two
28-day tests; a life cycle test with the my a id, Myaidopaia fcahia/ and an early
life-stage test with the sheepshead minnow, Cyprinodon variegatua (Table 2).
Survival was the most sensitive endpoint in the 8-day chronic tests with
14
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gurytemora affinis. Tests were performed at salinity levels of 5, 15 and 25
g/L. At a salinity of 5 g/L, survival was significantly reduced to 37 percent
at 17,500 A16,000 ^g/L). Therefore the acute-chronic value was
>6.294.
15
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The species mean acute-chronic ratios for both freshwater and
saltwater differ by more than a factor of 10, and are not related to rank
order of acute sensitivity. For both freshwater and saltwater, separate
chronic values were calculated for fish and invertebrates using separate fish
and invertebrate Acute-Chronic Ratios. "Greater than" values were not used.
The freshwater Fish Chronic Value of 11.56 Aug/L, the lesser of the
two chronic values.
The saltwater Fish Chronic Value of 10.75 ^g/L is the quotient of the
Final Acute Value (611.7 A*g/L) and the Fish Final Acute-Chronic Ratio (56.88).
Likewise, the Invertebrate Chronic Value of 66.21 /^g/L is the quotient of the
Final Acute Value and the Invertebrate Final Acute-Chronic Ratio (9.239). The
Final Saltwater Chronic Value is 10.75 A
-------
Two species of freshwater green algae were exposed to atrazine in
studies in which the exposure duration was 4 days or longer, and the atrazine
concentrations were measured (Table 4). Chlamydomonaa reinhardtii cell
numbers were reduced 50 percent after 4 days of exposure to 51 ug/L, after 7
days of exposure to 21 ug/L, and after 10 days of exposure to 10.2 ug/L
(Schafer et al. 1993). The "no observable effect concentrations" (NOECs) were
3.4, 5.1 and 3.7 ^g/L at 4, 7 and 10 days, respectively (Schafer et al. 1994).
Selgnaatrum eaprieornutum had a 4-day EC50 of 4 ^g/L, based upon cell
numbers (University of Mississippi 1990). The EC50 for pheophytin A and
chlorophyll a. content was 20 and 150 pig/L, respectively. With the same
species and cell number as an endpoint, Gala and Giesy (1990) reported a 4-day
EC50 of 128.2 Aig/L, and Hoberg (1991) reported a 4-day EC50 of 130 pq/lL.
Hoberg (1993a) calculated a 5-day EC50 of 55 Aig/L. EC10 values at 4 and 5
days were 90 and 26 jug/L, whereas EC90 values at 4 and 5 days were 190 and 120
Aig/L, respectively (Hoberg 1991, 1993a).
Exposure of the duckweed, Lemna minor. to atrazine for 14 days
resulted in a NOEC of 10 A
-------
measured more often during the teat. In the first study, using frond number
as an endpoint, the EC10, BC50 and EC90 were 6.2, 37, and 220 A pibba to atrazine (Kirby and Sheahan 1994)
yielded ECSOs that were comparable to those of Hoberg et al. (1993b,c). ECSO
values of 56, 60 and 62 A*g/L were obtained based upon frond number, fresh
weight and chlorophyll content, respectively (Kirby and Sheahan 1994).
Elodea (Elodea eanadenaig) was exposed to atrazine both in the absence
•
and presence of sediment. In the absence of sediment, LOECs of 10 and 100
Aig/L were observed, based upon mature frond production and biomass,
respectively.(University of Mississippi 1990). With sediment present, the
biomass LOEC was 100 pg/L. Biomass ECSOs were 1,200 and 25,400 Aig/L when
sediment was absent and present, respectively, in the test systems. A
freshwater Final Plant Value was not calculated, as none of the species tested
met the Guidelines criteria for such a determination.
Information on the sensitivity of saltwater plants to atrazine is
available for five phytoplankton species, one seaweed and four vascular
plants, representing five phyla (Table 4). All of the plant effect
concentrations were less than the acute values for aquatic animals. Short-
term (two and three day) growth tests with phytoplankton resulted in ECSOs
ranging from 79 to 265 Mg/L (Mayer, 1987; Walsh 1983); a factor of only 3.4.
Two species of estuarine submerged vascular plants, Potamoye-han perfoliatua
and Myrlophyllum apleatum. exposed for 28-35 days to various concentrations of
18
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atrazine had ICSOs for growth and photosynthesis between 25 and 117 ug/L, with
the growth endpoint being more sensitive in both species (Kemp et al. 1982,
1985). The sago pondweed, Potamogeton paetlnatua. was tested for atrazine
toxicity for 28 days at three different salinities (1, 6 and 12 ppt) (Hall et
al., 1997). Dry weight was the most sensitive endpoint with chronic values of
21.2, 21.2 and 10.6 ug/L at salinities of 1, 6 and 12 ppt, respectively. A
two-way ANOVA yielded a chronic value of 5.3 ug/L of atrazine. Four separate
21-day exposures of the seagrass, Zoatera marina, resulted in LCSOs ranging
from 100 to 540 ug/L (Delistraty and Hershner 1984). A saltwater Final Plant
Value was not calculated, as none of the species tested met the Guidelines
criteria for such a determination.
Bioaceuimilation
Macek et al. (1976) analyzed muscle tissue or the eviscerated
carcasses of fish at the end of extended exposure periods. Brook trout
exposed to atrazine at 740 ^ig/L for 308 days contained less than 200 ug/kg of
atrazine in muscle tissue, resulting in a bioconcentration factor (BCF) of
<0.27 (Table 5). Bluegills exposed to 94 pg/L for 546 days also contained
less than 200 ug/kg in their muscle tissue, for a BCF of <2.1. Fathead
minnows exposed to atrazine at 210 pg/L for 301 days had less than 1,700 ug/kg
of atrazine in pooled samples of eviscerated carcasses, for a BCF of <8.1.
Dionne (1992) exposed fathead minnows to atrazine for up to 274 days.
Using "c-atrazine and measuring the radiolabel in fish tissue, the values
obtained would represent maximum possible BCFs. Regardless of the life-stage
or exposure duration, maximum BCFs were less than 8.5 in all cases.
19
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There is no U.S. Food and Drug Administration action level or any
other established maximum allowable concentration of chemical residues in
•tissue available for atrazine. Therefore, a Final Residue Value cannot be
determined.
Other Data
Many testa with atrazine and various freshwater or saltwater organisms
have been conducted either for a different duration or by different protocols
than those specified in the Guidelines for inclusion in Tables 1, 2, 4 and 5.
For example, plant tests were included in Table 6 rather than Table 4 if the
test duration was less than 4 days or the exposure concentrations were not
measured. Tests with animals were included in Table 6 for a number of
reasons, including considerations of test duration, type of test, and test
endpoints other than those of toxicity or bioaccumulation. These test results
are presented in Table 6.
Mixed nitrifying bacteria were unaffected regarding ammonium oxidation
at 28-day exposures up to 2,000 fjg/L (Gadkari 1988). Cell growth in the
bacterium, Paeudomonaa putIda, was not inhibited following a 16 hr exposure at
10,000 pg/L (Bringmann and Kuhn 1976, 1977). The cyanobacterium, Microeyatia
aeruginoaa. exhibited the onset of cell growth inhibition at a concentration •
of 3 fjg/l> in an 8-day exposure (Bringmann and Kuhn 1976; 1978a,b). After 5
days of exposure, cell numbers were significantly reduced at 108 £ig/L, and the
minimum algistatic concentration was 440 pg/L (Parrish 1978). Kallqvist and
Romstad (1994) obtained a 6-day EC50 of 630 A'g/L with M.. aeruginoaa.
Photosynthetic 14C uptake was highly reduced (84-96 percent) in H* aerupinoaa
following a 22 hr exposure to 2,667 ug/L of atrazine (Peterson et al. 1994).
20
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A 4-day EC50 of 90 pg/L was reported for an unidentified species of
Mieroeyatifl (Fairchild et al. 1994a; 1998). An EC50 of 130 vg/L was reported
for Syneehoeoeeua leopolienaia (Kallqvist and Romstad 1994).
Two different species of cyanobacteria, Anabaena inaequalia and
Anabaena Yarii^bllj.Pr had highly different ECSOs of 30 and 4,000 pg/L,
respectively after 14 days (Stratton 1984). Stratton (1984) obtained a 12-14
day EC50 of 1,200 pg/L for Anabaena eylindriea. while Larsen et al. (1986)
reported ECSOs of 253, 178 and 182 pg/L for this species.
A number of tests have been performed with the cyanobacterium,
Anabaena flos-aquae (Table 6). Hughes (1986) reported an EC50 of 230 pg/L
following a 5-day exposure. A concentration of 40 jug/L non-radiolabeled
atrazine reduced 14C uptake by approximately 50 percent after 1 to 3 days of
exposure, after which the reduction was less (Abou-Waly et al. 1991a).
Chlorophyll a content was reduced by atrazine, followed by recovery. The 3-
day EC50 was 58 /ig/L, while the 7-day EC50 was 766 ^g/L (Abou-Waly 1991b).
Anabaena floa-aquae had a 4-day EC50 that exceeded 3,000 pg/L in a study by
Fairchild et al. (1994a; 1998). Anabaena inaequalia and Pseudoanabaena sp.
exhibited reduced photosynthetic uptake of HC in the amounts of 65 and 91
percent, respectively, following a 22 hr exposure to 2,667 ug/L (Peterson et
al. 1994).
Toxicity studies of atrazine toward several other species of
cyanobacteria have been reported. A 31-day exposure of Pletrtonema boryanum to
10,000 pg/L resulted in a 69 percent decrease in cell numbers (Mallison and
Cannon 1984). A 5-day exposure of Svnechoeeua leopolenaia yielded an EC50 of
130 pg/L (Kallqvist and Romstad 1994). Aphanizomeonon floa-aquae and
Oaelllatorla sp. exhibited highly reduced photosynthetic uptake of 14C with a
22-hr exposure to 2,667 ug/L of atrazine (Peterson et al. 1994).
21
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The green alga, Chloralla pyrenoldoaa. had 70-95 percent reduced
growth following a 2-week exposure of 500 to 10,000 ngfL of atrazine (Virmani
et al. 1975). Photosynthesis by £. pyrenoldoaa was inhibited by approximately
64 percent following an 8 hr exposure to 10 pg/L atrazine (Valentine and
Bingham 1976). Stratton (1984) obtained an EC50 of 300 pg/L following a 12-14
day exposure. A 30 percent reduction in growth and 40 percent reduction in
chlorophyll & was observed in a 10-day exposure to 53.9 fig/L (Gonzalez-Muruaa
et al. 1985). A 110 hr exposure to 49.6 jug/L reduced chlorophyll by 39
percent (Hiranpradit and Foy 1992). Photosynthetic CO2 uptake was inhibited
by more than 80 percent in £. pyrenoldoaa following a 50-minute exposure to
125 ug/L (Hannan 1995).
Chlorella vulgaris had 24 hr ECSOs of 325, 305 and 293. ^g/L in three
separate tests based upon 14C uptake (Larson et al. 1986). Following 7 days
of exposure to 250 to 5,000 pg/L (only 2.3 to 4.7 percent remained on day 7),
dry weight of £. vulgaria was reduced from 31 to 62 percent (Veber et al.
1981). This same species had an EC50 of 94 ug/L based upon chlorophyll
concentration after 96 hr of exposure (Fairchild et al. 1998).
Chlorella fuaca cell numbers were reduced by atrazine, and an EC50 of
26 Aig/L was calculated following a 24 hr exposure (Altenburger et al. 1990).
Faust et al. (1993) obtained an EC50 of 15 Mg/L for this species. In
undefined species of Chlorella. a 72-96 hr atrazine exposure at 52 M9/L
resulted in a 31 percent inhibition of growth and a 39 percent reduction in
chlorophyll (Foy and Hiranpradit 1977). Higher exposures generally resulted
in larger adverse effects. A 2-3 day atrazine exposure of 21.6 yg/L reduced
the growth rate by 55 percent (Hersh and Crumpton 1987). Chlorella ap.
exhibited very rapid responses to atrazine with ECSOs of 35-41 pg/L based upon
photosynthetic oxygen evolution following a 2-minute exposure (Hersh and
22
-------
Crumpton 1989). Fairchild at al. (1994) reported a 4-day EC50 (biomass) of 92
Aig/L for Chlorella sp.
The green alga, cm amydomonaa relnhardtll. exhibited approximately a
32 percent inhibition of photosynthesis in an 8-hr exposure to 10 fig/L
(Valentine and Bingham 1976), and a 50 percent reduction in photosyntnetic
activity ("c uptake) in 24-hr exposures to 19-48 ^g/L (Larsen et al. 1986).
Atrazine-^sensitive and atrazine-resistant strains of £. reinhardtjl responded
to 2-minute exposures by a difference of approximately an order of magnitude
in their respective EC50 values of 45 and 484 ^g/L (Hersh and Crumpton 1989).
A 65-hr exposure to 49.6 Aig/L resulted in a 13 percent reduction of
chlorophyll (Hiranpradit and Foy 1992). Fairchild et al. (1998) obtained a
96-hr EC50 of 176 ug/L for fi. reinhardi.
Chlamydomonaa noctigama had a 3-day EC50 of 330 A*g/L (Kallqvist and
Romstad 1994). C- aeitleri had a similar level of sensitivity after a 1-hr
exposure, with an EC50 of 311 pg/L (Francois and Robinson 1990). Foy and
Hiranpradit (1977) exposed Chlamydomonaa sp. to various concentrations of
atrazine for 72-96 hr. A concentration of 50-52 Aig/L inhibited growth by 84.9
percent and reduced chlorophyll by 12.8 percent. Slight additional increases
in growth inhibition were observed with increased atrazine concentrations up
to 832 Aig/L. Fairchild et al. (1994) obtained a 4-day EC50 of 176 pg/L.
The green alga, Scenedeamua quadrieauda. had photosynthesis inhibited
by approximately 42 percent after 8 hr at an atrazine exposure'of 10 pg/L
(Valentine and Bingham 1976). Bringmann and Kuhn (1977; 1978a,b) found 30
pig/L to cause the onset of cell multiplication inhibition after 8 days of
exposure with this species, fi. cruadrieauda had a 12 to 14-day EC50 of 100
^ig/L (Stratton 1984). Bogacka et al. (1990) studied photosynthesis reductions
at various concentrations after 8 days of exposure, and observed a gradation
23
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from 4.5 percent reduction at 4 i*g/L to a 99.3 percent reduction at 337 pg/L.
Photoeynthetic "c uptake waa highly inhibited (96 percent) after 22 hr at
2,667 ug/L (Peterson et al. 1994). This species had a 96-hr EC50 of 169 ug/L,
based upon chlorophyll concentration (Fairchild et al. 1998).
In three tests with Seenedeamua obliquua the 24 hr ECSOs for UC uptake
were between 38 and 57 fjg/L (Larson et al. 1986). £. aubapieatua had a 4-day
EC50 of 110 fig/L (Geyer et al. 1985). Schafer et al. (1994) found 37 pg/L to
inhibit the effective photosynthetic rate by 57.4 percent. Kirby and Sheahan
(1994) reported a 48-hr EC50 of 21 Mg/L for fi. aubapicatua. Reinold et al.
(1994) observed a 50 percent reduction in dry mass at 21.5 Mg/L. Exposure of
an unidentified species of Scenedeamua for 72-96 hr at 50 pg/L resulted in
60.2 percent growth inhibition (Foy and Hiranpradit 1977). Increased
concentrations resulted in increased growth inhibition. Fairchild et al.
(1994) obtained a 4-day EC50 of 169 pg/L.
The green alga, Selenaatrum eapricornutum. exhibited a reduction in
cell numbers following a 5-day exposure to 54 nq/I* of atrazine (Parrish 1978).
Chlorophyll a. was reduced in increasing amounts at increasing concentrations
between 32 and 200 /jg/L. The minimum algistatic concentration was determined
to be 200 A
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content and in "c uptake occurred at 130 pg/L in 1- to 7-day exposures (Abou-
Waly et al. 1991a). ECSOs were 283, 218 and 214 j/g/L for chlorophyll a.
content at 3, 5, and 7 days, respectively (Abou-Waly et al. 1991b). Fairchild
et al. (1994a; 1998) reported a 4-day EC50 of 117 pg/L, while Kallqvist and
Romstad (1994) obtained 3-day ECSOs of 200 and 110 ^g/L. Photosynthetic UC
uptake was nearly completely inhibited (99 percent) at an exposure of 2,667
ug/L (Peterson et al. 1994). A 96-hr EC50 of 147 ^g/L was reported by Gaggi
et al. 1995. Additional ECSOs ranging from 26 to 359 ng/'L were reported for
72- to 96-hr exposures by Radetski et al. 1995, Caux et al. 1996, Van der
Heever and Grobbelaar 1996, and Fairchild et al. 1997, respectively.
The green alga, Ankiatrodeaimia braunii. had an 11-day EC50 of 60 pg/L
(Burrell et al. 1985). "c uptake ECSOs of 72 and 61 Aig/L resulted from 24-hr
exposures of Ankiatrodeamua sp. (Larsen et al. 1986). Two tests with
Stigeoelonlum tenue yielded 24-hr ECSOs of 127 and 224 /jg/L, while a test with
Ulothrix aubeonatrlc-fca yielded an EC50 of 88 pg/L (Larsen et al. 1986).
Virmani et al. (1975) observed reduced growth of Chlorococcum hypnosporum
following 2-week exposures to 5,000 and 10,000 pig/L. Similarly, a high test
concentration (2,157 /jg/L) inhibited calcification in Gloetaenium
loitleabergarianum (Prasad and Chowdary 1981). Short exposures (2 minutes) of
Franeala sp. yielded ECSOs between 430 and 774 pg/L, measured as
photosynthetic oxygen evolution (Harsh and Crumpton 1989).
Several diatom species have been tested for their sensitivities to
atrazine. Cyclotella meneghiniana yielded 7-minute ECSOs based upon
photosynthesis between 99 and 243 pg/L (Millie and Hersh 1987). A 22-hr
exposure to 2,667 ug/L inhibited photosynthetic 14C uptake by 97 percent
(Peterson et al. 1994). A 6-day EC50 of 430 ptg/L was obtained by Kallqvist
and Romstad (1994). Hughes (1986; 1988) determined several endpoints in S-day
25
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exposures of Navleula pell tculoaa. including a 5-day EC50 of 60 ug/L.
Photosynthesis was almost completely inhibited (99 percent) in Nltzaehia sp.
by a 22-hr exposure to 2,667 ug/L of atrazine (Peterson et al. 1994). The
EC50 was 60 fjg/L. Using a 9-day recovery period following the 5-day exposure,
the algistatic and algicidal concentrations were 1,730 and >3,200 /*g/L,
respectively. The crypt omonad, Crypt omonag pyrinoidifera. had a 6-day EC50 of
500 jig/L (Kallgvist and Romatad 1994).
Tha duckweed, Lemna minor, when exposed to 20 pg/L of atrazine for 20
days did not exhibit any adverse effects, but reduced growth occurred at
concentrations between 50 and 1,000 pig/L (Beaumont et al. 1976, a, b,c; Grenier
et al. 1979). Biochemical and ultrastructural changes in the chloroplasts of
Lemna minor were observed at an exposure of 248 iig/L (Grenier et al. 1987;
1989; Simard et al. 1990). Growth was inhibited 95 percent by a 7-day
exposure to 2,667 ug/L (Peterson et al. 1994). Four-day ECSOs of 92 and 153
l/g/L were reported for L. minor with biomass as the endpoint (Fairchild et al.
1994a; 1997; 1998). Hughes (1986; 1998) exposed a different species of
duckweed, Lemna gJJQba, to atrazine for 5 days, and obtained an EC50 of 170
A«g/L. Using a 9-day recovery period, the phytostatic and phytocidal
concentrations were 1,720 and >3,200. Aig/L, respectively.
Exposure of wild rice, Zizania aguatlea. to 50 Mg/L of atrazine for 83
days resulted in a visible state of senescence and a 75 percent reduction in
chlorophyll a in the leaves (Detenbeck et al. 1996). Wildcelery, Vallianerla
. had reduced leaf growth and whole plant biomass at an exposure of 8
pg/L and had reduced over-wintering success of tubers at 4 Aig/L (Cohn 1985).
A 14-day EC50 of 22 pg/L was reported for coontail, Cer-atophyllum sp.
(Fairchild et al. 1994; 1998). Stem elongation occurred at 50 Mg/L (Detenbeck
et al. 1996). Cattails, Typha latifolia. were unaffected at 25
26
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(Detenbeck et al. 1996). Eurasian watermilfoil, Myrlophyllum apieatum. had a
28-day EC50 of 1,104 Aig/L (Davis 1980; Forney and Davis 1981) and a 14-day
EC50 of 132 fjg/L (Fairchild et al. 1994a; 1998). M. apieatum exhibited a 30
percent increase in net photosynthetic rate at 10 ug/L (Hoffmann and Winkler
1990), and a 50 percent reduction in branch number at 3,700 ug/L (Bird 1993).
Sago pondweed, Potamogefcon peetlnatua. had reduced biomass after 28 days at
100 /ug/L (Fleming et al. 1991), and bushy pondweed, Najaa sp., had a 14-day
EC50 of 24 ug/L (Fairchild et al. 1994a; 1998). The 14-day EC50 was <38 /ug/L
for Egerla sp. (Fairchild et al. 1994a). Blodea eanadenaia had ECSOs of 80
and 109 /jg/L in exposures of 21 to 28 days (Davis 1980; Forney and Davis
1981). In a 20-day exposure to 10 ug/L, the dark respiration rate exceeded
the net photosynthetic rate (Hoffmann and Winkler 1990). Its growth was
unaffected at 75 A50,000 and
27
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118,500 Aig/L, respectively (Huber et al. 1991; Roberts et al. 1990). Schafer
et al. (1994) reported a 48 hr EC50 of 96,000 pg/L for T. pvriformis.
In representatives from higher animal phyla, relatively high
concentrations were required to produce notably adverse responses. A
concentration of 5,000 pg/L reduced the budding rate in Hvdra viridis (Benson
and Boush 1983). Two species of leeches, Glossiphonia comolanata and
Helobdella stactnalis. had LCSOs of 6,300 and 9,900 pg/L, respectively, after a
27-28 day exposure (Streit and Peter 1978). Snail (Lvmnaea palustris) growth,
fecundity and tissue glycogen content were unaffected at concentrations up to
125 Mg/L (Baturo et al. 1995), but the activities of benzo(a]pyrene and
glutathione-s-transferase enzymes were inhibited at 5 pg/L (Baturo and Lagadic
1996). The LC50 was greater than 60,000 pg/L for larval and juvenile mussels
(Anadonta imbeeilis) (Johnson et al. 1993). The rotifer, Brachionus
calvciflorus. had an LC50 of 7,840 Mg/L (Crisinel et al. 1994).
The anostracan crustacean, Streotocephalus texanus. had a 24-hr LC50
>30,000 Mg/L (Crisinel et al. 1994). The cladoceran, Ceriodaphnia dubia. had
maximum acceptable toxicant concentrations (MATCs) of 7,100 and 14,100 pg/L in
two 4-day tests (Oris et al. 1991). A 26-hr LC50 of 3,600 pg/L was reported
for Daphnia maana (Frear and Boyd 1967). In 48 hr exposures of D. maona to a
nominal atrazine concentration of 10 pg/L, whole body residues were only 4.4
and 2.2 times greater than the nominal concentration in water (Ellgehausen et
al. 1980). Young production was reduced in D. maana at 2,000'pg/L (Kaushik et
al. 1985). After 96 hr of exposure, Bogacka et al. (1990) observed 30 percent
mortality in D. maona at 16,900 pg/L, and 60 percent mortality at 48,300 pg/L.
Johnson et al. (1993) reported a 48-hr LC50 of 9,400 Mg/L> while Crisinel et
al. (1994) obtained a 24-hr EC50 of >30,000 Mg/L. Detenbeck et al. 1996)
observed a significant decrease in D. maona survival at 25 Mg/L, but not at 50
28
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. Exposures of Daphnia pulex for 28 to approximately 70 days resulted in
decreased survival and reproduction at concentrations between 1,000 and 20,000
A/g/L, with reproduction affected more greatly than survival (Schober and
Lamport 1977). Food consumption was reduced by 10 percent at 350 fig/I, and by
50 percent at 1,600 Aig/L in Q. pulex after 10 minutes (Pott 1980).
The 3-hr LC50 was in excess of 40,000 Aig/L for the cladoceran, Moina
maerocopa (Nishiuchi and Hashimoto 1967, 1969). A concentration of 1,000 pg/L
caused 40 percent mortality and reduced population growth in M- maeroeopa
(Scherban 1972a,b).
The amphipod, Cammarua f aaeia-fctia. had a 48-hr LC50 of 5,700 pg/L
(Macek et al. 1976). For the midge, Chironomus ripariua. a 10-day exposure
yielded.an LC50 of 18,900 A/g/L (Taylor et al. 1991), while a 4-day exposure of
£. tentana did not kill 50 percent of the test animals at 28,000 pg/L
(McNamara 1991b).
Rainbow trout, Qneorhynchua mykiss, embryos and sac fry exposed
continuously for 23 and 27 days had LCSOs between 696 and 888 A/g/L (Birge et
al. 1979). Water hardness did not have any appreciable effect. A
concentration of 4,020 Aig/L was required to produce over 60 percent teratic
larvae. Pluta (1989) reported a 48-hr LC50 of 5,660 pg/L. Changes in the
ultrastructure of trout renal corpuscles and tubules were observed following
28-day exposures to 5-10 Aig/L of atrazine (Fischer-Scher1 et al. 1991).
Twenty-eight day exposures resulted in slight ultrastructural changes in trout
renal corpuscles at 5 A, in slight histopathological changes in the liver
and increased ultrastructural changes in renal corpuscles at 10 pg/l>, and in
further changes in renal corpuscles and liver cells at 20 Aig/L (Schwaiger et
al. 1991). A 14-day exposure to 10 pg/L of atrazine did not affect survival,
body weight, liver weight or liver enzyme activity (Egaas et al. 1993).
29
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Concentrations of 3.0 and 50 ngfL .for 10 days were reported to reduce plasma
protein in rainbow trout (Davies et al. 1994b). Oulmi et al. (1995) observed
kidney changes at the cellular level in the proximal tubules at 12.4 ^g/L, and
in both the proximal and distal tubules at 24.0 ^g/L.
The 48 hr LC50 for the common carp, Cyprlnua earplo. was >10,000 ng/L
(Nishiuchi and Hashimoto 1967, 1969). Short-term exposures of from 4 to 24 hr
to lesser concentrations between 100 and 1,000 Atg/L resulted in increased
serum cortisol and serum glucose (Hanke et al. 1983; Gluth and Hanke 1984).
Serum acetylcholinesterase first increased and then decreased with time of
exposure. Changes were also noted in gill ATPase activity. Juvenile carp
yielded a 48-hr LC50 of 16,100 pg/L (Pluta 1989), and a 96-hr LC50, in which
the fish were fed, of 18,800 /jg/L (Neskovic et al. 1993). Biochemical changes
in the serum, heart, liver and kidneys of carp were observed after 14 days of
exposure to 1,500 pg/L, as well as hyperplasia of gill epithelial cells
(Neskovic et al. 1993). Goldfish, Caraaalua auratua. had a 48-hr LC50 of
>10,000 pg/L (Nishiuchi and Hashimoto 1967, 1969). Jop (1991b) reported the
•no observed effect concentration" (NOEC) to be in excess of 4,900 Aig/L for
fathead minnows exposed to atrazine for 7 days. Survival and.growth were
unaffected in fathead minnows, Pimephalea promelaa. exposed to 75 /ug/L
(Detenbeck et al. 1996).
Channel catfish f Itrfcalurua punetatuai embryos and sac fry had LCSOs
between 176 and 272 /ug/L after exposures of either 4.5 or 8.5 days (Birge et
al. 1979). Concentrations of approximately 340 A
-------
A/g/L were reported for the guppy (Poeeilia retieulata) after exposures of 48
and 72 hr, respectively (Tscheu-Schluter 1976). Mortalities of 40 and 53.2
percent were observed at 96 hr exposures of 28,600 and 37,200 pg/L,
respectively (Bogacka et al. 1990). Exposure of the Mozambique tilapia,
Tllapla moaBamblea. to 1,100 Aig/L of atrazine for 30 to 90 days affected blood
composition, oxygen consumption, water content, and the biochemistry of the
brain and liver (Prasad et al. 1991a,b; Srinivas et al. 1991). It also
resulted in increased serum sodium and potassium, and decreased serum calcium,
magnesium and bicarbonate (Prasad and Reddy 1994).
The embryo and larval stages of several amphibian species were exposed
to atrazine (Birge et al 1980). LCSOs for continuous exposure of embryos and
larvae through 4 days post-hatch were 410 A>g/I> for the bullfrog (Rana
cateabiana) . 7,680 t^q/'L for the leopard frog (Rana pipiena) . 17,960 pg/L for
the pickerel frog (Rana paluatria)f and >48,000 ^g/L for the American toad
(Bli£fl ameT-leanuai. Concentrations of atrazine in excess of 5,000 ng/1> were
required to cause an incidence of teratic larvae in excess of 7 percent.
Survival and growth of £. pipena tadpoles were unaffected after 41 days of
exposure to 25 A
-------
severe population density reductions in several species, and total destruction!
of the green alga, cladophora glomerata (Kosinski 1984). The extreme toxicity
to £. ylomerata is notable because of the dominant role that it often plays in
structuring a benthic community. By contrast, no effects were observed upon
stream macroinvertebrate community structure, periphyton production or
biomass, and the community photosynthesis/respiration ratio following a 30-day
exposure at 25 pg/L (Lynch et al. 1985).
Malanchuk and Kollig (1985) observed chemical changes in an
experimental stream community consisting of microscopic autotrophs and
heterotrophs following the introduction of atrazine at a nominal concentration
of 100 pg/L for a 2-week exposure period, followed by its removal from the
ecosystem. They observed decreased diurnal fluctuations in pH and dissolved
oxygen concentrations, as well as lower mean values for these parameters while
atrazine treatment was on-going. Nitrate nitrogen levels were increased.
Following the cessation of atrazine treatment, there was a rapid recovery for
each of these parameters back to control levels.
Moorhead and Kosinski (1986) observed reduced net primary productivity
at 100 £ig/L. Biomass reductions were noted in a stream Aufwuchs community
exposed to 24 or 134 pg/L of atrazine for 12 days (Krieger et al. 1988). A
24-hr exposure of 77.5 pg/L had no effect upon algal cell numbers or biomass
in a natural stream periphyton community (Jurgenson and Hoagland 1990). An
exposure of approximately 0.5 pg/L for 6 months resulted in an initial
decrease in phytoplankton species followed by a recovery (Lakshminarayana et
al. 1992). In contrast, Gruessner and Watzin (1996) did not observe any
effect upon a stream community of attached algae and benthic invertebrates at
5 A
-------
by the periphyton community of an artificial stream following exposure of 100
Mg/L of atrazine for 30 days.
In a static pond microcosm (1 L beaker), Brockway et al. (1984) found
that a 7-day exposure to 5.0 /jg/L had no effect upon diurnal oxygen
production, a measure of photosynthesis, by the various species of green and
blue-green algae present. A 50 jug/L exposure for 12 days resulted in a 25-30
percent reduction in diurnal oxygen production, while 7-12 day exposures at
100 to 5,000 pg/L further decreased oxygen production. Exposure of a
freshwater microcosm to 5.1 A
-------
(approximately 60-90 percent) in the ratio throughout most of the study.
Higher exposures (nominal concentrations of 100 to 500 Aig/L) caused further
reductions in this ratio, but not as large a difference as between controls
and the lowest exposure.
Experimental ponds in Kansas that were exposed for several years to
single annual applications of atrazine at nominal concentrations of 20 ^/g/L or
more exhibited reductions in the production and biomass of phytoplankton, in
macrophyte populations and in populations of benthic insect grazers, bullfrog
(Rana eateabiana) tadpoles, grass carp (Ctenopharyngodon idella) that had been
introduced, and bluegills (deNoyelles et al. 1982, 1989, 1994). Initial
nominal concentrations of 20, 100, 200 and 500 /jg/L depressed phytoplankton
growth within a few days in the ponds. However, after 3 weeks, phytoplankton
production and biomass were similar to controls. deNoyelles and Kettle (1985)
observed reduced photosynthesis of 40 percent or more in short-term (24-hr)
bioassays at these same atrazine concentrations, but longer-term bioassays (20
days) and the experimental pond studies showed a recovery from this initial
reduction.
Benthic insect community structure was studied in the same Kansas
experimental ponds following two single annual treatments at 20, 100 and 500
pg/L (Dewey 1986; Dewey and deNoyelles, 1994). Significant reductions of both
species richness and total abundance of emerging insects was observed at even
the lowest exposure of 20 Aig/L. Abundances of the herbivorous, non-predatory
insects were reduced at 20 pg/L, but not abundances of the predatory species.
This indicated that the observed loss of total insects was a secondary effect
due to feeding habit and loss of plant life, rather than a direct toxic
effect. Loss of insect habitat, particularly in the form of macrophytes, also
34
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likely had some effect upon the insect community. These effects tended to
destabilize the ecosystem (Dewey and deNoyelles 1994).
Species composition of macrophytes was altered in a pond mesocosm
community following an 8-week exposure to 50 ^g/L of atrazine (Fairchild et
al. 1994a). However, functional parameters were unaffected, indicating
functioning redundancy within the ecosystem. Juttner et al. (1995) did not
observe any effects upon the plankton community of a pond mesocosm following a
2-month exposure to 5 ^g/L, but did observe decreased oxygen production, pH
and conductivity at 10 f*g/L, and decreased phytoplankton populations at 182
/ug/L. At 318 Mg/L, reproduction was affected in Daphnia longiapina and a
population of rotifers, Polyarthra sp., was eliminated.
In a laboratory microcosm using a naturally derived microorganism
community, Pratt et al. (1988) observed that a 21-day exposure to a mean
measured concentration of 10 /jg/L of atrazine did not affect the dissolved
oxygen, a measure of photosynthetic function, but that a concentration of 32.0
pg/L caused significant reductions in this parameter. This resulted in a
calculated maximum acceptable toxicant concentration (MATC) of 17.9 /jg/L based
upon this functional endpoint. Several other endpoints, such as protozoan
colonization, biomass protein, chlorophyll a and potassium levels, were less
sensitive than dissolved oxygen, and had a calculated MATC of 193 pg/L.
Stay et al. (1989) studied atrazine effects in 1 L laboratory
microcosms containing mixed phyto- and zooplankton cultured from three Oregon
lakes and one pond. A 42-day exposure of approximately 15 pg/L atrazine did
not affect net primary productivity, the P/R ratio, or pH, but these
parameters were significantly reduced from controls at a mean measured
concentration of approximately 84
35
-------
Larson at al. (1986) measured photosynthetic 14C -uptake in a 3 L Taub
microcosm community at different time intervals for up to 373 days after
treatment with atrazine. ECSOs ranged from 24 /jg/L at 177 days to 131 pg/L at
43 days after atrazine treatment.
A 50 m2 pond community'exposed to atrazine for 4 months at a
concentration between 60 and 120 pg/L eliminated a population of duckweed,
Lamna minor, within 27 days (Gunkel 1983). Gunkel also observed a rapid
succession of algal species and a reduced rate of reproduction in Daphnla
ptillearla. Treatments of a pond mesocosm community with 20, 100 and 300 pg/L
of atrazine caused decreases in cell numbers of green algae and of cladoceran
populations, but increased numbers of cryptomonads (Neugebauer et al. 1990).
In experimental ponds treated with 20 A3 hr) of pond algae to 10 /ug/L of atrazine was
observed to increase the rate of fluorence for photosystem II (Ruth 1996).
In two reports of studies conducted at the same site, a lake community
was enclosed with a limnocorral (5mx5mx5m deep) to which atrazine was
added. Both studies focused on the periphyton community. In the first study
(Herman et al. 1986), the limnocorrals received two nominal atrazine
applications of 100 ug/L, one on day 0 and another on day 35. After 34 days
of exposure to measured concentrations ranging between 80 and 140 Aig/L, a
reduction in periphyton ash-free dry weight was observed. Over a 9 week
period with the two atrazine applications, which resulted in measured
concentrations of approximately 80 to 140 ug/L after the first application and
36
-------
110 to 190 ug/L after the second application, reductions occurred in
chlorophyll A, organic matter and total periphyton algal biomass. In the
second study (Hamilton et al. 1987), a 230-day - exposure to a mean measured
atrazine concentration of 80 pg/L caused approximate reductions of 60 percent
in biomass, 22 percent in cell numbers and 32 percent in number of species.
The results were more pronounced in exposures to mean measured atrazine
concentrations of 140 and 1,560 pg/L. A shift in community structure occurred
from a chlorophyte-dominated community to a diatom-dominated community.
Aquatic enclosures exposed to a nominal atrazine application of 100
jjg/L on June 1 followed by a second application of the same concentration 35
days later, exhibited a gradual die-off of the phytoplankton, a. long period of
recovery for the green algal community, and a distinct shift in the taxonomic
composition of algae (Hamilton et al. 1988). Thirteen days after the first
application, significant declines occurred in populations of the green algal
species Elakatothirix gelatinoaa. Tetraedon minimum. Sphaeroeyatig achroeteri.
and Ooeyati's laeustria; and of the dinoflagellate, Gymnodinium spp. Seventy-
seven days after the second application, phytoplankton communities were still
distinctly different, and total fresh weight biomass was reduced. By 323 days
after the first application, the phytoplankton assemblages were again similar
between control and treated enclosures.
From day 1 to day 114, control enclosures had an average of five more
taxa than the atrazine-treated enclosures (Hamilton et al. 1988). During the
period between days 49 and 77, the green algal (Chlorophyta) biomass
represented <7 percent of that found in the controls. By the following spring
(day 323), the biomass had returned to control levels. The herbicide
treatment did not affect the rotifer or crustacean communities. In the same
exposures, Hamilton et al. (1989) observed that the atrazine-treated
37
-------
enclosures became clearer with increased Secchi disc readings, while readings
of dissolved oxygen, chlorophyll/ dissolved organic carbon, and particulate
organic carbon decreased.
Using 1.70 m2 enclosures in a moderately entrophic lake, Lamport et al.
(1989) observed decreased photosynthesis and decreased populations of certain
zooplankters at atrazine concentrations of 0.1 and 1.0 pg/L. At 0.1 Aig/L,
populations of Daphnla sp. were severely reduced by 15 days, and oxygen
concentrations were reduced after 10 days. At 1.0 pg/L, concentrations of
chlorophyll A and oxygen were reduced by 10 days as were populations of
Daphnla. Cyclops, and Boamina species, and nauplii larvae. At 0.1 pg/L, there
was an apparent recovery after about 25 days. Genoni (1992) observed a
decreased algal population density and a decreased "scope for change in
ascendency" in a microcosm community exposed to 250 /jg/L. The "scope for
change in ascendency" is a biological system response endpoint, considered to
be analagous to the "scope for growth" endpoint for individual organisms.
Gustavson and Wangberg (1995) observed some minor changes in species
composition of the phytoplankton community in a lake mesocosm community after
a 20-day exposure to 20 pg/L. ECSOs were 58 and 52 Mg/L for the phytoplankton
community, and 52 and 54 Mg/L for the periphyton community. Brown and Lean
(1995) found that a short-term exposure (3 hr) of lake phytoplankton to
atrazine resulted in a much lower EC50 based upon photosynthetic carbon
assimilation (i.e., 100 Mg/L), than when based upon phosphate or ammonium
assimilation (14,000 and >33,000 Mg/L, respectively). A stream periphyton
community exhibited a significant reduction in chlorophyll a. following a brief
exposure (< 4 hr) to 109 ug/L (Day 1993). Caux and Kent (1995) observed a
reduction in green algae in Quebec streams following the spring atrazine
runoff pulse, with a maximum stream concentration of approximately 40 ug/L.
38
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Detenbeck at al. (1996) observed a decrease in the gross productivity of a
wetland mesocosm community at an atrazine concentration of 15 Mg/L. There
also was an increase in the concentrations of dissolved nutrients in the
water.
From the various studies of ecosystem effects (i.e., microcosm,
mesocosm and limnocorral studies), the lowest concentrations of atrazine that
have resulted in temporary negative effects upon abundance of aquatic plants
(primary effect) and animals (secondary effect) have generally occurred at 15-
20 pg/L and above. Studies by Kosinski et al. (1983), Kosinski and Herkle
(1984), Lakshminarayana et al. (1992), and Lamport et al. (1989) have observed
effects at lower concentrations. It appears that for effects at
concentrations up to 15 A
-------
bushy pondweed and Elodea) EC50 values between 21 and 24 ug/L. Several
species of water moss (Pontlnalia sp.) exhibited reduced photosynthetic
activity at 10 ug/L, with one species affected at 2 ug/L. EC/LC 50 values for
protozoans, coelenterates, annelids, molluscs and rotifers were 27,480 ug/L.
Various crustaceans had LC50 values 25,700 ug/L. The most sensitive endpoints
among fish were rainbow trout plasma protein and kidney ultrastructural
changes at atrazine exposures of 3 and 3.5 ug/L, respectively. The lowest
LC50 values in fish were 176-272 ug/L for 4.5 to 8.5-day exposures with early
life-stages of channel catfish. Frog embryo and tadpole life-stages had LC50
values 2,410 ug/L. In most aquatic ecosystem studies, reductions in algal or
vascular plant biomass were observed at concentrations 215 ug/L. This
commonly resulted in the reduction of herbivore populations, as well. One
exception reported effects at much lower concentrations (as low as 0.1 ug/L).
From these freshwater "Other Data", most of the "effect" levels of
possible biological significance appear to be 2 15 ug/L. This concentration
is greater than the Final Acute Values and Final Chronic Values, and therefore
does not determine the Criterion Continuous Concentration.
Additional data are available for saltwater algae, kelp, submerged
vascular plants, emergent vascular plants, and aquatic animals (Table 6).
EC50 values for various green algal species ranged from 37 ug/L to 1,500 ug/L
(Walsh 1972; Hollister and Walsh 1973; Hughes 1986, 1988; Samson and Popovich
1988; Gaggi et al. 1995). A 48-hr exposure of the green alga, Dunaliella
bloeulata. to 216 ug/L of atrazine resulted in a growth reduction of
approximately 35 percent (Felix et al. 1988). Seven-day growth tests with the
green alga, Nannochlorlg oeulata. suggested that atrazine toxicity was
dependent on light and temperature (Karlander et al., 1983; Mayasich et al.,
40
-------
1986), although the effect was not dramatic. A concentration of 15 ug/L
changed the doubling time in H. oeulata (Mayasich et al. 1987).
Diatom species were similar to green algae in their sensitivities to
atrazine. EC50 values for exposures of various durations were generally
between 20 and 600 ug/L (Walsh 1972; Hollister and Walsh; Walsh et al. 1988).
Plumley and Davis (1980) observed reduced photosynthesis in Nitachia aigma in
a 7-day exposure to 220 ug/L.
The kelp, Laminaria aaeeharina. had a similar sensitivity. A two-day
exposure was sufficient to significantly reduce sexual reproduction at
concentrations 272.2 ug/L, with no effect at 33.2 ug/L (Thursby and Tagliabue
1990).
Inhibition concentrations of 77 to 120 ug/L for a 50% effect on
photosynthesis by vascular plants in short-term (2 to 4 hours) exposures to
atrazine (Jones and Winchell, 1984) were similar to the effects upon growth
and photosynthesis in longer exposures with several other species (Table 4).
Eelgrass, Zoatera marina, had reduced oxygen evolution at 100 ug/L (Kemp et
al. 1981), and complete inhibition of photosynthesis and growth at 1,000 (Kemp
et al. 1981) and 1,900 ug/L (Schwarzschild et al. 1994). The emergent salt-
marsh rush, Juncua roemerj.anpg. exhibited effects indicative of stress after a
35-day exposure to 30 ug/L (Lytle and Lytle 1998).
Values for LCSOs for the copepod, Acartia £anaa, at 24, 48 and 72
hours showed that the sensitivity to atrazine increased with increasing
duration of exposure (Tables 1 and 6). Adult fiddler crabs, Pea pugnax. were
not very sensitive to one-time applications of atrazine either in field or
laboratory exposures (Plumley et al., 1980). There was, however, a seasonal
effect on the sensitivity of this species even when the laboratory conditions
were the same. Animals collected in the summer were more sensitive to
41
-------
atrazine than those collected in either the spring or fall (Plumley et al.,
1980). Two other species of crabs, Seaarma cinereum and Panopeua sp., were
also insensitive to very high levels of atrazine (Plumley et al. 1980).
A mesocosm study of a mixed assemblage of marine phytoplankton species
demonstrated reduced photosynthesis and primary production at concentrations
of 0.12 and 0.56 ug/L (Bester et al 1995). This is much lower than effect
levels demonstrated from the other studies.
Unused Data
Data from some studies were not used in this document, as they did not
meet the criteria for inclusion as specified in the Guidelines (Stephan et
al., 1985). The reader is referred to the Guidelines for further information
regarding these criteria.
Some data on the effects of atrazine on aquatic organisms were not
used because the studies were conducted with species that are not resident in
North America or Hawaii (e.g., Portmann 1972; Gzhetotskii et al. 1977; Gunkel
and Kausch 1976; Juhnke and Luedemann 1978; Prasad et al. 1990, 1995; Nagel
1992; Hendriks and Stouten 1993; Hendriks and Stouten 1993; Lewis et al. 1993;
L'Haridon et al. 1993; Biagianti-Risbourg and Bastide 1995; Steinberg et al.
1995; Alazemi et al. 1996; Hussein et al. 1996). Results were not used if the
duration of the exposure was not specified or was unclear (e.g., Hopkin and
Kain 1968; Portmann 1972; Tellenbach et al. 1983; Sampson and Popovic 1988),
or if the procedures or test materials were not adequately described or
translated (e.g. Braginskii 1973; Shcherban 1973; Schmidt 1987; Mark and Solbe
1998).
42
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The acute toxicity data of Bathe et al. (1973,1975) were not used due
to an insufficient number of test organisms. A chronic study with Gammarua
faaelatua was not used due to low survival in the controls (Macek et al.
1976). Studies published only as abstracts of presentations were not used
(e.g. Palmstrom and Krieger 1983; Zora and Paladino 1986; Fairchild et al.
1994b). Secondary observations reported in a review were not used (Hurlbert
1975). Similarly, a paper by Pratt et al. (1993) was not used, as the data it
contained had been previously published. A study by Butler et al. (1975) was
not used since data from several algal taxa were grouped in the reporting of
results. Stratton and Giles (1990) expressed toxicity on the basis of cell
numbers.
Toxicity data from laboratory tests were generally not used if the
test material was a formulation and atrazine comprised less than 80 percent of
its weight (Walker 1964; Hiltibran 1967; Semov and losifov 1973; Pavlov 1976;
Antychowicz et al. 1979; Hartman and Martin 1985; Sreenivas and Rana 1991,
1994); if atrazine was a component of a pesticide mixture (Ort et al. 1994);
or if atrazine was dosed in the diet (Cossarini-Dunier et al. 1988). Toxicity
tests by Tubbing et al. (1993) and Schmitz et al. (1994) were not used because
the tests were performed in river water which was likely contaminated with
various other chemicals. Similarly, a cytopathological study of fish exposed
to a spill of atrazine plus other pesticides was not used (Spazier et al.
1992). Effects data were not used if the atrazine exposure was part of a soil
mixture (Jones and Estes 1984). HcBride and Richards (1975) exposed excised
tissue.
A study of atrazine accumulation by Bohn and Muller (1976) was not
used due to expression of results on a volume basis rather than a weight
basis. A bioconcentration study by Walsh and Ribelin (1973) was not used due
43
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to the use of nominal atrazine concentrations in the exposure water rather
than measured concentrations. Data were not used if the exposure was to
radiolabeled atrazine (Davis et al., 1979; Jones et al., 1982, 1986; McEnerney
and Davis, 1979; Pillai et al., 1977, 1979; Weeter et al. 1980; Neumann et al.
1987). Uptake and accumulation from exposures in flasks or microcosms were
not used if 137,100 Aig/L for an annelid, Lumbrieulus variegatua. Within this
overall range, SMAVs for seven fish species ranged from 6,300 ng/l> for the
brook trout, Salvellnua fontinalia. to 27,000 M9/L for the brown trout, Salmo
tjnitta. Genus Mean Acute Values for atrazine are available for eight genera
of saltwater animals and range from 1,000 to >30,000 /ug/L; a factor of greater
than 30. Acute values for the four most sensitive genera (three crustaceans
and one fish) differed by a factor of 8.5.
Chronic effects of atrazine exposure to aquatic animals have been
studied with six freshwater species, three of which are invertebrates and
three of which are fish. In three tests with Cerlodanhnia dubia. chronic
44
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values were 3,500, 3,500, and 1,732 pg/L. Reproduction was reduced in Daphnia
magna at 250 pg/L, but not at 140 pg/L. A chronic value of 187 fig/I, was
derived, and a corresponding acute-chronic ratio of 36.90. The growth of a
midge, Chironomua tentana, was retarded at 230 Aig/L of atrazihe, but not at
110 pg/L. A chronic value of 159 pg/L was calculated, and a corresponding
acute-chronic ratio of 4.528 was derived.
Brook trout, Salvelinus fohtinalla. had reduced growth at 120 Aig/L,
but not at 65 pg/I», in a chronic exposure. A chronic value of 88.3 pg/L and
an acute-chronic ratio of 71.35 were calculated. In two life-cycle tests with
the fathead minnow, Pimephalea promelaa. the chronic limits were set in the
first test at 210 and 870 pg/L based upon no adverse effects observed in a
chronic exposure at 210 pg/L and 25 percent mortality in 3 to 5-day old fry at
870 pg/L. The chronic value was 430 Aig/L, and the acute-chronic ratio was
34.88. In the second test, chronic limits were 250 and 460 ng/L, based upon
growth of larval fish, resulting in a chronic value of 339 pg/L and an acute-
chronic ratio of 59.00. The acute-chronic ratio for this species was
calculated at 45.36, the geometric mean. Bluegills, Lepomia macroehirua. were
unaffected in a chronic exposure to 95 pg/L, while an equilibrium loss
occurred in bluegills exposed to 500 pg/L. These were established as the
chronic limits, with a chronic value of 218 nq/l*. Since the acute value was a
"greater than" value, the acute-chronic ratio was >36.70.
SMAVs for 9 .saltwater species ranged from 1,000 ug/L for the mysid,
Myaidopaia bahia. to >30,000 ug/L for the eastern oyster, Craaaoatrea
virginlea. The chronic value for tf. bahia was 123.3 ^g/L, based on survival.
The chronic value for Cyprinodon varlegatua was 2,542 /ug/L, based on mortality
of juveniles. The acute-chronic ratio for tf. bafria was 8.110, while the
45
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acute-chronic ratio for £. variegatua was > 6.294. Effect concentrations for
plants were lower than the acute and chronic values for aquatic animals.
Atrazine toxicity to aquatic plants, both algae and macrophytes,
commonly occurs at concentrations of 15 pg/L and above, with several reports
of toxicity to specific plant taxa at concentrations below 10 pg/L. Effects
are thought to be algistatic rather than algicidal at these lower
concentrations, with recovery occurring once the atrazine is removed. The
lowest EC50 values for green algae with exposure durations of 4 days or longer
were 10.2 and 4 A
-------
The national criteria given below were determined on the basis of
atrazine toxicity to aquatic animals. The Criterion Maximum Concentrations
for freshwater and saltwater were'one-half of the respective Final Acute
Values, which were based upon Table 1 acute toxicity values for all
invertebrate and vertebrate species. The Criterion Continuous Concentrations
for freshwater and saltwater were based upon the Final Chronic Values for
fish. These were calculated by dividing the Final Fish Acute-Chronic Ratio
into the Final Acute Value in each case. Separate Final Acute-Chronic Ratios
were determined for fish and invertebrates due to the large differences in the
ratios for the two groups. The Fish Chronic Values became the Criterion
Continuous Concentrations, since there were no Final Plant or-Final Residue
Values; and the results from studies in the "Other Data" section did not
appear to warrant the establishment of a lower concentration at this time.
National Criteria
The procedures described in the "Guidelines for Deriving Numerical
National Water Quality Criteria for the Protection of Aquatic Organisms and
Their Uses" indicate that, except possibly where a locally important species
is very sensitive, freshwater aquatic animals and their uses should not be
directly affected unacceptably if the four-day average concentration of
atrazine does not exceed 12 pg/L more than once every three years on the
average and if the one-hour average concentration does not exceed 330 //g/L
more than once every three years on the average. The four-day average of 12
ug/L for the protection of freshwater animals should also be protective of
most freshwater plants.
-------
The procedures described in the "Guidelines for Deriving Numerical
National Water Quality for the Protection of Aquatic Organisms and Their Uses*
indicate that, except possibly where a locally important species is very
sensitive, saltwater aquatic organisms and their uses should not be affected
unacceptably if the four-day average concentration of atrazine does not exceed
11 Mg/L more than once every three years on the average and if the one-hour
average concentration does not exceed 310 pg/L more than once every three
years on the average. The four-day average of 11 ug/L for the protection of
saltwater animals should also be protective of most saltwater plants.
Implementation
As discussed in the Water Quality Standards Regulation (U.S. EPA 1983)
and the Foreword to this document, a water quality criterion for aquatic life
has regulatory impact only when it has been adopted in a state water quality
standard. Such a standard specifies a criterion for a pollutant that is
consistent with a particular designated use. With the concurrence of the U.S.
EPA, states designate one or more uses for each body of water or segment
thereof and adopt criteria that are consistent with the use(s) (U.S. EPA 1983,
1987, 1994). Water quality criteria adopted in state water quality standards
could have the same numerical values as criteria developed under Section 304,
of the Clean Water Act. However, in many situations states might want to
adjust water quality criteria developed under Section 304 to reflect local
environmental conditions and human exposure patterns. Alternatively, states
may use different data and assumptions than EPA in deriving numeric criteria
that are scientifically defensibly defensible and protective of designated
uses. State water quality standards include both numeric and narrative
48
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criteria. A state may adopt a numeric criterion within its water quality
standards and apply it either state-wide to all waters designed for the use
the criterion is designed to protect or to a specific site. A state may use
an indicator parameter or the national criterion, supplemented with other
relevant information, to interpret its narrative criteria within its water
quality standards when developing KPDES effluent limitations under 40 CRF
122.44
-------
of these criteria (U.S. EPA 1991), limited data or other considerations might
require the use of a steady-state model (U.S. EPA 1986).
Guidance on mixing zones and the design of monitoring programs is also
available (U.S. EPA 1987, 1991).
50
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Table 1. Acute Toxicity of Atrazine to Aquatic Animals
Species
Hydra,
Hvdra sp.
Annelid,
Lumbricuius variegatus
Snail (adult),
Phvsa sp.
Cladoceran (<12 hr),
Ceriodaphnia dubia
Cladoceran (<24 hr),
Ceriodaphnia dubia
w Cladoceran (<24 hr),
|-j Daphnla maana
Cladoceran (>24 hr),
Daphnla manna
Cladoceran,
Daphnia ma ana
Amphlpod,
Hvalella azteca
Stonefly (nymph),
Acroneuria sp.
Nidge (1st instar),
Chironomua tentans
Coho salmon (yearling),
Oncorhvnchus kisutch
Brown trout,
Sat mo trutta
Brook trout (juvenile),
Method*
R,M
F,M
R,N
S,M
S,H
S,U
S,U
F,H
F.M
F,M
S,U
R,M
R,U
F.U
Chemical
298. 5X
298.5X
298.5X
>99X
97X
94X
296X
79.6X
298. 5X
298. 5X
94X
2 BOX
-
94X
Hardness
(mg/L as
CflCOiL.
FRESHWATER SPECIES
48.9
67.3
48.9
57.1
52
-
250
170
67.4
67.4
-
101
11
-
LC50
or EC50
Cua/L)"
3,000
>37,100
>34,100
>30,000
>4,900
6,900
>39,000
49,000
14,700
6,700
720
> 18, 000
27,000
6,300
Species mean
Acute value
(ua/L)
3.000
>37,100
>34,100
>30.000
•
-
•
49.000
14,700
6,700
720
>18,000
27.000
6,300
References
Brooke 1990
Brooke 1990
Brooke 1990
Oris et al.
Jop 1991c
Nacek et al.
March ini et
Putt 1991
Brooke 1990
Brooke 1990
Macek et al.
Lorz et al.
Grande et a I
Macek et al.
1991
1976
al. 1988
1976
1979
. 1994
1976
Salvelinus font
-------
Table 1. (continued)
Species
Fathead minnow
Pimephales prometas
Fathead minnow (juvenile),
Pimephales promotes
Fathead minnow,
Plmephates prometas
Channel catfish (sac fry),
Ictalurus punctatus
Blueglll (juvenile).
Lepomis macrochlrus
Largemouth bass (fry).
in Ml crept erus salmoides
(0
Eastern oyster
(embryo/larval),
Crassostrea virginica
Copepod (adult),
Acartia clausii
Copepod (field),
Acartia tonsa
Copepod (adult),
Acartia fonsa
Copepod (adult),
Acartia tonsa
Copepod (adult),
Acartia tonsa
Copepod (nauplius),
Eurvtemora affinis
Method* chemical
R,U 94X
S,M 97X
F,M 97. IX
S.U SOX
F,U 94X
S,U SOX
S,U 97.4X
R,U 70X
S,U 97.4X
R,M 70X
R.M 70X
F,M 97. IX
S,M 97. IX
Hardness
(mg/L as
CaCO.)
52
20-40
78
-
78
SALTWATER SPECIES
16"
6"
20"
31-32"
31"
30-34"
5"
LC50
or EC50
(itg/L)
15,000
>4,900
20,000
>10,000
>8,000
>10,000
>30,000
7,925
94
210.1
91.73
4,300
500
Species Mean
Acute Value
(itn/L) • References
Macek et al. 1976
Jop 1991a
20,000 D tonne 1992
> 10, 000 Jones 1962
>8.000 Macek et al. 1976
> 10, 000 Jones 1962
>30,000 Ward * Bat lantine
7.925 Thursby et al. 1990
Ward t Ballantine,
1985
1985
Thursby et al., 1990
Thursby et al. 1990
4,300 McNamara, 1991
Hall et al. 1994a.b
-------
Table 1. (continued)
Species
Copepod (nauplius),
Eurytemora. afffnjs
Copepod (nauplius),
Eurytemora aff Inis
Mysid (lab),
Mysidopsis bah la
Pink shrimp (field),
Penaeus duorarim
Grass shrimp (field),
Pataemonetes puglo
Fiddler crab, (field).
Uca pug Ha tor
Ul
u Sheepshead minnow (lab),
Cyprinodon varlenatus
Sheepshead minnow (larva),
Cvprlnodon varieaatus
Sheepshead minnow (larva),
Cyprinodon variegatus
Sheepshead minnow (larva),
Cyprinodon yarlegatus
Spot (field),
Hfiihfid*
S.N
S,M
F,M
S.U
S,U
S.U
S.M
S.M
S.M
S.U
Chemjcat
97. IX
97. IX
97. «X
97. 4X
97.4X
97.4X
97.4X
97. IX
97. IX
97. 1X
97.4X
^
15
25
20
26
26
26
13
5
15
25
12
LC50
or EC50
tua/L)
2.600
13,200
1,000
6,900
9,000
>29.000
>16,000
16,200
2.300
2.000
8,500
Species Mean
Acute Value
(ua/L) References
Hall et al. 1994a,b
2,579 Hall et al. 1994a,b
1,000 Ward ft Ballantine, 1985
6,900 Ward A Ballantine, 1985
9,000 Ward ft Ballantine, 1985
>29,000 Ward ft Ballantine. 1985
Ward ft Ballantine, 1985
Hall et al. 1994a.b
Hall et al. 1994a,b
5,660 Hall et al. 1994a,b
8.500 Ward ft Ballantine, 1985
* S = static; R = renewal; F - flow-through; M = measured; U = unmeasured.
b Salinity expressed as g/L.
-------
Table 2. Chronic Toxicity of Atrazine to Aquatic Animals
Species
Cladoceran,
Ceriodaphnia dubia
Cladoceran,
Ceriodaphnia dubia
Cladoceran,
Ceriodaphnia dubia
Cladoceran,
Daphnia magna
Midge.
Chlronomus tentans
Brook trout,
J£ Salvelinus fontl nails
Fathead minnow,
Pimeohales promelas
Fathead minnow,
Pimephales promelas
Bluegitl,
Lepomis macrochlrus
Copepod,
Eurytemora aff inls
Copepod,
Eurvtemora afflnls
Copepod,
Eurvtemora afflnls
Mysid,
Hvsldopsls bah la
Sheepshead minnow,
Test*
LC
LC
LC
LC
LC
LC
LC
LC
LC
LC
LC
LC
LC
ELS
Chemical
>99X
>99X
97X
94X
94X
94X
94X
97. IX
94X
97. IX
97. IX
97. IX
97.4X
97. 4X
Hardness
(mg/L as
CaCO,)
FRESHWATER
57.1
57.1
52
32.2
43.0
35.7
36.2
24-36
33.9
SALTWATER
5
15
25
20
13
Chronic
Limits
lua/lf
SPECIES
2,500-5.000
2.500-5.000
1.200-2,500
140-250
110-230
65-120
213-870
250-460
95-500
SRECJfS
12.250-17,500
17,500-25.000
4.200-6,000
80-190
1,900-3,400
Chronic Value
3,500
3,500
1,732
187
159
88.3
430
339
218
14,600
20,900
5,010
123.3
2,542
References
OrIs et al. 1991
Oris et al. 1991
Jop 1991d
Macek et al. 1976
Macek et al. 1976
Macek et al. 1976
Macek et al. 1976
Dionne 1992
Macek et al. 1976
Hall et al. 1995
Hall et al. 1995
Hall et al. 1995
Ward ft Ballantine, 1985
Ward & Ballantine, 1985
-------
Table 2. (continued)
Acute-Chronic Ratios
Species
Cladoceran,
Ceriodaphnia dubia
Cladoceran,
Ceriodaphnia dubia
Cladoceran,
Ceriodaphnia dubia
Cladoceran,
Daphnia magna
Midge,
phlronomus tentans
tn Brook trout,
Salyelinus fontinalis
Fathead minnow,
Pimephales promelas
Fathead minnow,
Pimephales promelas
Bluegill,
Lepomis macrochirus
Copepod,
Eurvtemora aff inis
Copepod,
Eurvtemora aff inis,
Copepod,
Eurytemora aff inis
Mysid.
Hysidopsis bah la
Sheepshead minnow.
pyprjqodop ypflfiF^ftiS
Hardness
(mg/L as
CaCCsl
57.1
57.1
52
32.2
43.0
35.7
36.2
24-36
33.9
5°
15C
25C
20°
13C
Acute Value
fua/L)
>30,000
>30,000
>4,900
6,900
720
6.300
15,000
20,000
>8,000
500
2,600
13,200
1,000
5,660
Chronic Value
(ug/L>
3,500
3.500
1,732
187
159
88.3
430
339
218
14,600
20,900
5,010
123.3
2,542
Ratio
>8.571
>8.571
>2.829
36.90
4.528
71.35
34.88
59.00
>36.70
0.0342
0.1244
2.635
8.110
-
• 1C = Life-cycle or partial life-cycle; ELS =
b Results are based on measured concentrations
0 Salinity in g/L.
early life-stage.
of atrazine.
-------
Table 3. Ranked Genus Mean Acute Values with Species Nean Acute-Chronic Ratios
in
ank'
15
14
13
12
11
10
9
8
7
6
5
4
3
Genus Nean
Acute Value
(uo/L)
49,000
>37,100
>34,100
>30,000
27,000
20,000
>18,000
14,,700
>10,000
>10,000
>8,000
6,700
6,300
Species
FRESHWATER SPECIES
Cladoceran,
Daphnia magna
Annelid.
Lumbriculus varlegatus
Snail.
Physa sp.
Cladoceran
Ceriodaphnia dybja.
Brown trout,
Sal mo trutta
Fathead minnow,
Pimephajes promelas
Coho salmon.
Oncorhvnchus kisutch
Amphipod.
Hvalella azteca
Channel catfish,
Ictalurus punctatus
Largemouth bass,
Nicropterus sat mo ides
Bluegilt.
Lepomis macrochirus
Stonefly,
Acroneurja sp.
Brook trout,
Species Mean
Acute Value
49,000
>37,100
>34,100
>30,000
27,000
20.000
> 18, 000
14,700
>10,000
>10,000
>8,000
6,700
6,300
Species Nean
Acute-Chronic
Ratio"
36.90
-
-
>3.163
•
45.36
-
-
-
-
>36.70
-
71.35
SalveHnus fontlnalis
-------
Table 3 (continued)
in
Rank*
2
1
9
8
7
6
5
4
4
3
2
1
Genus Mean
Acute Value
(uo/LI
3,000
720
>30,000
> 29, 000
9,000
8,500
6,900
5.838
5,838
5,660
2,579
1,000
Species
Hydra,
Hvdra sp.
Midge,
Chironomus tentans
SALTWATER SPECIES
Eastern oyster,
Crassostrea virginica
Fiddler crab,
Uca pug U a tor
Grass shrimp,
Palaemonetes pugio
Spot,
Leiostomus xanthurus
Pink shrimp,
Penaeus duoranm
Copepod,
Acartia clausii
Copepod,
Acartia tonsa
Sheepshead minnow,
Cvprlnodon variegatus
Copepod,
Eurvtemora affinis
Mysid,
Mysidoosis bahia
Species Mean
Acute Value
fug/L)b
3,000
720
>30,000
>29,000
9,000
8,500
6,900
7,925
4,300
5,660
2,579
1,000
Species Mean
Acute-Chronic
Ratio0
-
-
•
'
-
-
-
-
>6.291
2.635
8.110
* Ranked from most resistant to most sensitive based on Genus Mean Acute Value. Inclusion of "greater than" value does not necessarily imply a
true ranking, but does allow use of all genera for which data are available so that the Final Acute Value is not unnecessarily lowered.
" From Table 1.
0 From Table 2.
-------
Table 3 (continued)
Fresh Water
Final Acute Value - 657.3 *g/L
Criterion Maximum Concentration » (657.3 {ig/D/2 = 328.6 ng/L
Final Fish Acute-Chronic Ratio = 56.88
Fish Chronic Value = 11.56 /tg/L
Final Invertebrate Acute-Chronic Ratio = 9.239
Invertebrate Chronic Value = 71.14
Salt Mater
Final Acute Value = 611.7
Criterion Maximum Concentration = (611.7 ^g/L)/2 = 305.8
w
CD
Final Fish Acute-Chronic Ratio = 56.88
Fish Chronic Value > 10.75 ng/\.
Final Invertebrate Acute-Chronic Ratio = 9.239
Invertebrate Chronic Value = 66.21
-------
Table 4. Toxfcity of Atrazine to Aquatic Plants
10
Hardness
(mg/L as
Sceclifl Chemical CaCO,)
Green alga,
Chlarnvdomonas reinhardtii
Green alga,
Chlamvdomonas reinhardtii
Green alga,
Chlamvdomonas relnhardt i i
Green alga,
Chlamvdomonas relnhardt fl
Green alga,
Chlamvdomonas relnhardt (1 •
Green alga,
Chlamvdomonaq reinhardtii
Green alga,
Chlamvdomonas reinhardtii
Green alga,
Chlamvdomonas reinhardtii
Green alga,
Chlamvdomonas relnhardt ij
Green alga,
Selenastrum capricornutun
Green alga,
Selenastrum capricornutum
Duration
(days)
FRESHWATER SPECIES
4
7
7
4
4
7
7
10
10
4
4
—
ECSO
(cell number)
ECSO
(cell number)
ECSO
(cell number)
NOEC
(growth
inhibition)
ECSO
(growth
inhibition)
NOEC
(growth
inhibition)
ECSO
(growth
inhibition)
NOEC
(growth
inhibition)
ECSO
(growth
inhibition)
NOEC
(cell number,
bi amass)
NOEC
(chorohyll a.,
pheophytin a)
Concentration
(ua/L)' Reference
51 Schafer et al. 1993,
1994
21 Schafer et al. 1993,
1994
10.2 Schafer et al. 1993,
1994
3.4 Schafer et al. 1994
51.0 Schafer et al. 1994
5.1 Schafer et al. 1994
21.0 Schafer et al. 1994
3.7 Schafer et al. 1994
10.2 Schafer et al. 1994
0.5 Untv of Mississippi
1990
10 Univ of Mississippi
1990
-------
Table 4. (cont.)
Hardness
(mg/L as
Species Chemical CaCO.)
Green alga,
Selenastrum caprlcornutum
Green alga,
Selenastrum caprlcornutum
Green alga,
Selenastrum caprlcornutum
Green alga,
Setenastrun caprlcornutum
Green alga,
Selenastrum caprlcornutum
Green alga, 99. IX
Selenastrtm caprlcornutum
Green alga, 97. OX
Selenastrum caprlcornutum
Green alga, 97.0X
Selenastrum capricornutum
Green alga, 97.0X
Selenastrum caprlcornutum
Green alga, 97.0X
Selenastrum caprlcornutum
Green alga, 97.0X
Selenastrum capHcornutun
Green alga, 97.0X
Selenastrum caprlcornutum
Green alga, 97.1X
Setenastrum capricornutum
Duration
(davs)
4
4
• 4
4
4
4
4
4
4
4
4
4
5
LOEC
(cell density,
biomass)
LOEC
(chlorophyll fl,
pheophytin a)
ECSO
(cell number)
ECSO
(pheophytin a)
ECSO
(chlorophyll a)
ECSO
(cell number)
NOEC
(cell number)
MATC
(cell number)
LOEC
(cell number)
EC10
(cell number)
ECSO
(cell number)
EC90
(cell number)
NOEC
(cell number)
Concentration
1.0
100
4
20
150
128.2
76
99
130
90
130
190
16
Reference
Univ of Mississippi
1990
Univ of Mississippi
1990
Univ of Mississippi
1990
Univ of Mississippi
1990
Univ of Mississippi
1990
Gala and Giesy 1990
Hoberg 1991
Hoberg 1991
Hoberg 1991
Hoberg 1991
Hoberg 1991
Hoberg 1991
Hoberg 1993a
-------
Table 4. (cont.)
Hardness
(mg/L as
Species Chemical CaCO.)
Green alga, 97. 1X
Green alga, 97. IX
Selenastrum caoricornutum
Green alga, 97. IX
Selenastrum capricornuturo
Green alga, 97. IX
Selenastrtm capricornutum
Duckweed,
Lemna minor
Duckweed,
Lemna minor
Duckweed,
Lemna minor
Duckweed,
Lemna minor
Duckweed, 97X
Lemna gibbq
Duckweed, 97. IX
Lemna gibba
Duckweed, 97. IX
Lemna gibba
Duckweed, 97. IX
Lemna gibba
Duckweed, . 97. IX
Lemna gibba
Duckweed. 97. IX
Lemna gibba
Duration
(davs)
5
5
5
5
14
14
14
14
7
14
14
14
14
14
Effect
EC10
(cell number)
LOEC
(cell number)
ECSO
(cell number)
EC90
(cell number)
NOEC
(biomass)
LOEC
(mature frond
production)
LOEC
(biomass)
ECSO
(biomass)
ECSO
(frond
production)
NOEC
(frond number)
LOEC
(frond number)
EC10
(frond number)
NOEC
(frond biomass)
EC10
(frond biomass)
Concentration
fug/Li
26
31
55
120
10
10
100
8,700
180
<3.4
3.4
6.2
7.7
12
Reference
Hoberg 1993a
Hoberg 1993a
Hoberg 1993a
Hoberg 1993a
Univ of Mississippi
1990
Univ of Mississippi
1990
Univ of Mississippi
1990
Uhiv of Mississippi
1990
Hoberg 1991b
Hoberg 1993b
Hoberg 1993b
Hoberg 1993b
Hoberg 1993b
Hoberg 19936
-------
Table 4. (cent.)
10
Sneciea
Duckweed,
Lemna gibba
Duckweed,
Lemna gibba
Duckweed,
Lemna gibba
Duckweed,
Lemna gibba
Duckweed,
Lemna gibba
Duckweed,
Lemna gibba
Duckweed,
Lemna gibba
Duckweed,
Lemna gibba
Duckweed,
Lemna gibba
Duckweed,
Lemna gibba
Duckweed,
Lemna gibba
Duckweed,
Lemna gibba
Duckweed,
Lemna gibba
Duckweed,
Lemna minor
Hardness
(mg/L as
Chemical CaCOQ
97. IX
97. IX
97. IX
97. IX
97. IX
97. 4X
97. 4X
97. 4X
97. 4X
" 97. 4X
97.4X
97.4X
97.4X
98X
Duration
(dava)
14
14
14
14
14
14
14
14
14
14
14
14
14
10
Effect
LOEC
(frond biomass)
ECSO
(frond number)
ECSO
(frond biomass)
EC90
(frond biomass)
EC90
(frond number)
EC10
(frond number)
EC10
(frond biomass)
NOEC
(frond number &
biomass)
LOEC
(frond number I
biomass)
ECSO
(frond biomass)
ECSO
(frond number)
EC90
(frond number)
EC90
(frond biomass)
ECSO
(frond number)
Concentration
(MO/L)
17
37
45
170
220
2.2"'
4.2"'
8.3b/
Itf"
22"'
50"
98b'
110"'
56
Reference
Hoberg 1993b
Hoberg 1993b
Hoberg 1993b
Hoberg 1993b
Hoberg 1993b
Hoberg 1993c
Hoberg 1993c
Hoberg 1993c
Hoberg 1993c
Hoberg 1993c
Hoberg 1993c
Hoberg 1993c
Hoberg 1993c
Kirby and Shei
1994
-------
Table 4. (cont.)
Spec tea
Duckweed,
Lenna minor
Duckweed,
Lenrva minor
Elodea,
El odea canadena i a
Elodea.
Elodea canadena i a
Elodea,
Elodea canadensia
S Elodea,
Elodea canadensis
Elodea,
Elodea canadena i a
Elodea,
Elodea canadensia
Diatom,
Skeletonema costatun
Green alga,
Platvmonas sp.
Green alga,
ChloreUa sp.
Green alga,
Meochloris sp.
Hardness
(mg/L as Duration
Chemical CaCO.l (days)
98X - 10
98X - 10
10
10
10
10
10
10
SALTWATER SPECIES
30' 2
99. 7X 30* 3
99.7X 30* 3
99. 7X 30' 3
Effect
ECSO
(fresh weight)
ECSO
(chlorophyll)
NOEC
(biomass)
1 DEC
(biomass)
LOEC
(mature frond
production)
ECSO
(biomass)
LOEC
(biomass)
ECtO
(biomass)
ECSO growth
ECSO growth
ECSO growth
ECSO growth
Concentration
(fta/L)
60
62
10C/
100°'
100/
1,200C/
100"
25,400"'
265
100
140
82
Reference
Kirby and Sheahan
1994
Kirby and Sheahan
1994
Univ of Mississippi
1990
Univ of Mississippi
1990
Univ of Mississippi
1990
Univ of Mississippi
1990
Univ of Mississippi
1990
Univ of Mississippi
1990
Walsh, 1983
Mayer, 1987
Mayer, 1987
Mayer, 1987
-------
Table 4. (cont.)
Ul
Species
Sago pondweed,
Potamogetqn. pectinatus
Sago pondweed,
Potamogeton pectinatus
Sago pondweed,
Potamogeton pectinatus
Sago pondweed,
potamogetoi) pectinatus
Sago pondweed,
potamogeton pectinatus
Sago pondweed,
Potamogeton pectinatus
Sago pondweed,
Potamogeton pectinatus
Sago pondweed,
Potamogeton pectinatus
Sago pondweed,
Potamogeton pectinatus
Sago pondweed,
Potamogeton pectinatus
Sago pondweed,
Potamogeton pectinatus
Sago pondweed,
Potamogeton pectinatus
Sago pondweed,
Potamogeton pectinatus
Sago pondweed,
Potamoaeton pectinatus
Sago pondweed,
Potamogeton pectinatus
Sago pondweed,
Potamogeton pectinatus
Chemical
97. IX
97. IX
97. IX
97. 1X
97. IX
97. IX
97. IX
97. IX
97. IX
97. IX
97. IX
97. IX
97. IX
97. IX
97. IX
97. IX
Salinity*
6
6
6
6
6
6
12
12
12
12
12
12
12
12
12
1-12
Duration
(davs)
28
28
28
28
28
28
28
28
28
28
28
28
28
28
28
28
Effect
Dry weight
LOEC
Wet weight
LOEC
Rhizome tip
Mass LOEC
Dry weight
Chronic value
Wet weight
Chronic value
Rhizome tip mass
Chronic value
Dry weight
NOEC
Wet weight
NOEC
Rhizome tip mass
NOEC
Dry weight
LOEC
Wet weight
LOEC
Rhizome tip
Mass LOEC
Dry weight
Chronic value
Wet weight
Chronic value
Rhizome tip mass
Chronic value
Dry weight
Chronic value
Concentration
flM/L)
30
30
300
21.2
21.2
94.9
7.5
15
30
15
30
300
10.6
21.2
94.9
5.3
Reference
Hall et al.,
Hall et al.,
Hall et al..
Hall et al.,
Hall et al..
Hall et al..
Hall et al.,
Hall et al.,
Hall et al.,
Hall et at.,
Hall et al.,
Hall et al..
Hall et al.,
Hall et al.,
Hall et al..
Hall et al.,
1997
1997
1997
1997
1997
1997
1997
1997
1997
1997
1997
1997
1997
1997
1997
1997
-------
Table 4. (cont.)
Species
Eurasian Material I foil,
Mvrlophvllum splcatmi
Eurasian uatermilfoll,
Myrlophyllin splcatun
Eelgrass,
Zostera marina
Eelgrass,
Zostera marina
Eelgrass,
Zostera marina
Eelgrass,
2v?fen p^rJpfl
Chemical Salinity*
96.4X 9
96.4X 9
22
20
20
19
Duration
(davs)
28
35
21
21
21
21
Effect
IC50
photosynthesis
IC50 growth
(final bl omasa)
LC50
LC50
LC50
LC50
Concentration
(ua/L)
117
25
540
100
365
367
Reference
Kemp et al., 1983;
Kemp et al., 1985
Kemp et al., 1983;
Kemp et al., 1985
Oelistraty &
Hershner, 1984
Delistraty I
Hershner, 1984
Oelistraty t
Hershner, 1984
Delistraty &
Hershner, 1984
* Effect concentrations are based upon measured concentrations of atrazlne during the exposure period.
" Effect concentration is based upon measured concentration of atrazine on the last day of exposure only.
° No sediment present.
01 d Sediment present.
* Salinity expressed as g/L.
-------
Table 5. Bioaccumulation of Atrazine by Aquatic Organisms
Chemical
Hardness
(mg/L as Concentration Duration
fCaCo,) in Water (ua/LI fdavs) Tissue
BCF or
Reference
FRESHWATER SPECIES
Brook trout, 94X 35.7 740
Salvelinus fontinalis
Bluegill, 94X 33.9 94
Lepomls inacrochirus
Fathead minnow, 94X 36.2 210
Pimephales promelaa
Fathead minnow F, larvae, 97. IX 24-36 2,000
Pimphales promelas
Fathead minnow adult males, 97. IX 24-36 2,000
Plmcphales promelas
Fathead minnow adult 97.1X 24-36 2,000
females,
Pimephales promelas
Fathead minnow F! embryos, 97. IX 24-36 2,000
Pimephales promelas
Fathead minnow 14 day old 97. IX 24-36 2,000
larvae,
Pimephales promelaa
Fathead minnow 30 day old 97. 1X 24-36 2,000
larvae,
Pimephales promelas
308 Muscle
546 Muscle
301 Eviscerated
carcass
60 Uhole body
274 Uhole body
274 Uhole body
3 Uhole body
composite
sample
14 Uhole body
30 Uhole body
<0.27 Macek
1976
<2.1 Macek
1976
<8.1 Macek
1976
6.5" Dionne
8.5" Dionne
8.5" Dionne
4.6" Dionne
3.3" Dionne
6.0" Dionne
et al..
et al.
et al.
1992
1992
1992
1992
1992
1992
" Based on "C measurements, and therefore represents a maximum possible bioconcentration factor.
-------
Table 6. Other Data on Effects of Atrazine on Aquatic Organisms
Species
Mixed nitrifying,
bacteria
Nixed nitrifying,
bacteria
Bacterium,
Pseudomonas put i da
Cyanobecteriun,
0\ Hicrocvstis aeruginosa
00
Cyanobacterium,
Microcystis aeruginosa
Cyanobacterium,
Microcvstls aeruginosa
Cyanobacterium,
Microcvstis aeruginosa
Cyanobacterium,
Microcvstis aeruginosa
Cyanobacterium,
Microcvstic aeruginosa
Cyanobacteriun),
Mlcrocvstlc aeruginosa
Hardness
(tng/L as
Chemical CaCO.) puratlon
FRESHWATER SPECIES
28 days
28 days
214 16 hr
214 8 days
97.4X • 5 days
97.4X - 5 days
6 days
6 days
Technical - 22 hr
or
analytical
Technical • 22 hr
or
analytical
Effect
Increased
nitrite
oxidation;
ammonium
oxidation
unaffected
Ammonium
oxidation
unaffected
Incipient
Inhibition
Incipient
inhibition
Reduced cell
numbers
Minimum algistatlc
concentration
EC50
(growth)
EC50
(microplate
method)
96X inhibition of
photosynthesis
("C uptake)
84X inhibition of
photosynthesis
(" C uptake)
Concentration
(ua/L)
1,000
2,000
>10,000
3
108
440
630
630
2,667
2,667
Reference
Gadkari 1988
Gadkari 1988
Bringmam and
Kuhn 1976, 1977
Bringmam and
Kuhn 1976;
1978a,b
Parrish 1978
Parrlsh 1978
Kallqvist and
Romstad 1994
Kallqvist and
Romstad 1994
Peterson et al.
1994
Peterson et al.
1994
-------
Table 6. (Continued)
VO
Species
Cyanobacterium,
Microcvstis sp.
Cyanobacterium,
Svnechococcus leopoUenaia
Cyanobacterium,
Anabaena inaequalis
Cyanobacterium,
Anabaena varlabltls
Cyanobacterium,
Anabaena cyllndrlca
Cyanobacterium,
Anabaena cylindrica
Cyanobacterium,
Anabena cvlindrica
Cyanobacterium,
Anabaena cvlindrica
Cyanobacterium,
Anabaena f los-aouae
Cyanobacterium,
Anabaena flos -aquae
Cyanobacterium,
Anabaena flos -aquae
Cyanobacterium,
Anabaena flos -aquae
Cyanobacterium,
Anabaena flos -aquae
Cyanobacterium,
Anabaena flos-aouae
Hardness
(mg/L as
Chemical CaCO.) Duration
Technical - 4 days
or
analytical
5 days
>95X - 12-14 days
>95X - 12-14 days
>95X - 12-14 days
24 hr
24 hr
24 hr
97X - 5 days
97X - 5 day exposure,
9 day recovery
97X - 5 day exposure,
9 day recovery
97X - 5 day exposure,
' 9 day recovery
99.9X - 1 day
99.9X - 3 days
Concentration
Effect (ua/L) Reference
EC50
(biomass)
EC50
(microplate
method)
EC50
(cell number)
EC50
(cell number)
ECSO
(cell number)
ECSO
("C uptake)
ECSO
("C uptake)
ECSO
("C uptake)
ECSO
(cell number)
NOEC
(cell number)
Algistatic
concentration
Algicidal
concentration
56.2X reduction
in "C uptake
50. OX reduction
in "C uptake
90
130
30
4,000
1,200
253*
178'
182"
230
<100
4,970
>3,200
40
40
Falrchild et al.
1998
Kallqyist and
Romstad 1994
Stratton 1984
Stratton 1984
Stratton 1984
Larsen et al.
1986
Larsen et al.
1986
Larsen et al.
1986
Hughes 1986,
1988
Hughes 1986,
1986
Hughes 1986,
1988
Hughes 1986,
1988
Abou-Ualy et al .
1991a
Abou-Ualy et al.
1991a
-------
Table 6. (Continued)
Species
Cyanobacteriun),
Anabaena floa-aauae
Cyanobacteriun,
Anabaena ftos-aquae
Cyanobacterium,
Anabaena flos-aquae
Cyanobacteriun,
Anabaena flos-aquae
Cyanobacteriun,
Anabaena flos-aquae
Cyanobacterium,
Anabaena flos-aquae
Cyanobacterium,
Anabaena flos-aquae
Cyanobacterium,
Anabaena flos-aouae
Cyanobacteriun,
Anabaena flos-aquae
i
Cyanobacteriun,
Anabaena inaequalia
Cyanobacteriun,
Pseudoanabaena sp.
Cyanobacteriun,
plectonema borvanum
Cyanobacteriun,
Svnechoccus leopolensis
Cyanobacteriun,
Aphanlzomenon ftos-aouae
Chemical
Hardness
(mg/L as
CaCO.) Duration
Concentration
Effect
Reference
99.9X
99.9X
99.9X
99.9X
99.9X
99.9X
99.9X
99.9X
92. 2X
Technical
or
analytical
Technical
or
analytical
-
-
Technical
or
analytical
5 days
1 day
3 days
5 days
7 days
3 days
5 days
7 days
4 days
22 hr
22 hr
31 days
5 days
22 hr
• ••• •• •
9.5X reduction
in "C uptake
49. OX reduction
in chlorophyll
2.0X reduction
in chlorophyll
21. 8X reduction
in chlorophyll
29. 9X reduction
in chlorophyll
EC50
(chlorophyll a.)
ECSO
(chlorophyll a)
ECSO
(chlorophyll a)
ECSO
(chlorophyll A)
65X inhibition of
photosynthesis
("C uptake)
91X inhibition of
photosynthesis
(HC uptake)
69X decrease
in cell number
ECSO
(growth)
97X inhibition of
photosynthesis
("C uptake)
40
100
100
100
100
58
469
766
>3,000
2,667
2,667
10,000
130
2,667
Abou-Ualy et al
1991 a
Abou-Ualy et al
1991a
Abou-Ualy et al
1991a
Abou-Ualy et al
1991a
Abou-Ualy et al
1991a
Abou-Uay et al.
1991b
Abou-Uay et al.
1991b
Abou-Uay et al.
1991b
Fairchild et at
1998
Peterson et al.
1994
Peterson et al.
1994
Hallison and
Cannon 1984
Kallqvist and
Romstad 1994
Peterson et al.
1994
-------
Table 6. (Continued)
Species
Cyanobacterlun,
Oscillatorla sp.
Green alga,
ChloreHa pvrenoldosa
Green alga,
Chlorella pvrenoldosa
Green alga,
Chlorella pvrenoldosa
Green alga,
Chlorella pvrenoldosa
Green alga,
Chlorella pvrenoldosa
-4 Green alga,
""" Chlorella pvrenoidosa
Green alga,
Chlorella pvrenoldosa
Green alga,
Chlorella pvrenoldosa
Green alga,
Chlorella pvrenoldosa
Green alga.
Hardness
(mg/L as
Chemical CaCfr.) Duration
Technical - 22 hr
or
analytical
2 weeks
2 weeks
2 weeks
8 hr
8 hr
>95X - 12- 14
10 days
10 days
110 hr
Analytical - <50 min
Effect
87X inhibition of
photosynthesis
("C uptake)
70X reduced
growth
95X reduced
growth
92X reduced
growth
~64X Inhibition
of photosynthesis
~96X inhibition of
photosynthesis
EC50
(cell number)
30X growth
inhibition; 40X
reduction in
chlorophyll a
65X growth
inhibition; 70X
reduction in
chlorophyll a
39X reduction
in chlorophyll
>80X inhibition of
Concentration
(ua/lt
2,667
500
2,500
10,000
100
1,000
300
53.9
107.8
49.6
125
Reference
Peterson et al.
1994.
Vinnanl et al.
1975
Vinnanl et al.
1975
Virmani et al.
1975
Valentine and
Bfngham 1976
Valentine and
Bingham 1976
Stratton 1984
Gonzalez-Nuruaa
et al. 1985
Gonzalez-Muruaa
et al. 1985
Hlranpradit and
Foy 1992
Herman 1995
Chlorella ovrenoldosa
Green alga,
Chlorella ovrenoldosa
Analytical
<50 min
photosynthetic CO]
uptake
100X inhibition of
photosynthetic C02
uptake
1,250
Herman 1995
-------
Table 6. (Continued)
Hardness
(mg/L as
-j
to
Concentration
(ua/L) Reference
Green alga,
Chtorella vulgar Is
Green alga,
Chtorella vulgar la
Green alga,
Chlorella vulgar is
Green alga,
Chlorella vulgar Is
Green alga,
Chlorella vulgarls
Green alga,
Chlorella vulgarls
Green alga,
Chi orel la vulgarls
Green alga,
Chlorella vulgarls
Green alga,
Chlorella fusca
Green alga,
Chlorella fusca
Green alga,
Chlorella fusca
Green alga,
Chlorella fusca
7 days
7 days
7 days
7 days
24 hr
24 hr
24 hr
92. 2X - 96 hr
99X - 15 mln
99X - 14 hr
99X - 24 hr
>98X - 24 hr
31. OX reduction in
dry wt.
43.6X reduction in
dry wt.
S6.4X reduction in
dry wt.
61. 8X reduction in
dry wt.
EC50
<"C uptake)
EC50
("C uptake)
EC50
("C uptake)
ECSO
(chlorophyll)
ECSO
(photosynthesis)
ECSO
(cell volume
growth)
ECSO
(cell
reproduction)
ECSO
(cell number)
250C/
500C/
2,500C/
5,000°'
325'
305'
293"
94
141
36
26
IS
Veber et al.
1981
Veber et al.
1981
Veber et al.
1981
Veber et al.
1981
Larsen et al.
1986
Larsen et al.
1986
Larsen et al.
1986
Fairchild et al
1998
Altenburger et
al. 1990
Altenburger et
al. 1990
Altenburger et
al. 1990
Faust it al.
1993
-------
Table 6. (Continued)
u
SpecIeg
Green alga,
Chlorella kessleri
Chemical
Hardness
(mg/L as
CaCOQ
Green alga,
Chlorella sp.
Green alga,
Chlorella sp.
Green alga,
Chlorella sp.
Green alga,
Chlorella sp.
Green alga,
Chlorellq sp.
Green alga,
Chlorella sp."
Green alga,
phi ore! I a sp."
Green alga,
Chlprella sp."
Duration
72 hr
Concentration
(ua/L) Reference
72-96 hr
72-96 hr
72-96 hr
72-96 hr
72-96 hr
1-2 days
2-3 days
2 min
30X growth
Inhibition and
photosynthetic 0,
evolution; 6.7X
reduction in
protein synthesis;
effects upon
lipids
31.OX growth
Inhibition";
38.8X reduction in
chlorophyll
45.3X growth
inhibition";
30.3X reduction in
chlorophyll
52.3X growth
inhibition";
83.7X reduction in
chlorophyll
59.2X growth
inhibition1";
93.5X reduction in
chlorophyll
53.7* growth
inhibition";
95.4X reduction in
chlorophyll
Growth rate
reduced by 86X
Growth rate
reduced by 55X
EC50
(photosynthetic
oxygen evolution)
1,078
52
104
208
416
832
216
21.6
36
El-Sheekh et al.
1994
Foy and
Hiranpradit 1977
Foy and
Hiranpradit 1977
Foy and
Hiranpradit 1977
Foy and
Hiranpradit 1977
Foy and
Hiranpradit 1977
Hersh and
Crumpton 1987
Hersh and
Crumpton 1987
Hersh and
Crimp ton 1989
-------
Table 6. (Continued)
Spectea
Green alga,
ChtoreUa sp.*'
Green alga,
Clorella sp."
Green alga,
Chtorella sp.
Green alga,
Chlamvdomonas
rcinhardtii
Green alga,
Chlamvdomonas
relnhardtH
Green alga,
Chlamvdomonaa
reinhardtli
Green alga,
Chlamvdomonas
retnhardtll
Green alga,
Chlamvdomonaa
retnhardtH
Green alga,
Chlamvdomonas
reinhardtii
Green alga,
Chlamvdomonaa
reinhardtii"
Green alga,
Chlamvdomonas
reinhardtii"'
Green alga,
Chlamvdononaa
reinhardtii"
Green alga,
Chlamvdomonaa reinhardtiih/
Green alga,
Chlamvdomonas reinhardtii
Chemical,
94X
94X
-
•
-
-
-
-
•
•
•
94X
94X
-
Hardness
(mg/L as
CaCO.1 Duration
2 min
2 min
4 days
8 hr
8 hr
8 hr
24 hr
24 hr
24 hr
1-2 days
1-2 days
2 min
2 min
65 hr
Effect
EC50
(photosynthetic
oxygen evolution)
EC50
(photosynthetic
oxygen evolution)
EC50
(biomass)
*32X inhibition
of photosyntheseis
-74X inhibition
of photosynthesis
-97X inhibition
of photosynthesis
ECSO
("C uptake)
EC50
("C uptake)
ECSO
("C uptake)
Growth rate
reduced by 100X
Growth rate
reduced by 13X
ECSO
(photosynthetic
oxygen evolution)
ECSO
(photosynthetic
oxygen evolution)
13X reduction in
chlorophyll
Concentration
(ua/L) Reference
41
35
92
10
100
1.000
48''
19"
44"
216
21.6
45
484
49.6
Hersh and
Crumpton 1989
Hersh and
Crumpton 1989
Fairchild et at
1994
Valentine and
Bingham 1976
Valentine and
Bingham 1976
Valentine and
Btngham 1976
Larsen et al.
1986
Larsen et al.
1986
Larsen et al.
1986
Hersh and
Crumpton 1987
Hersh and
Crumpton 1987
Hersh and
Crumpton 1989
Hersh and
Crumpton 1989
Hiranpradit and
Foy 1992
-------
Table 6. (Continued)
•j
ui
Spectea
Green alga,
Chlamvdomonas relnhardi
Green alga,
Chlamvdomonas noctigama
Green alga,
ChlBmvdomonas gelt(er| Ettl
Green alga,
Chlamvdomonas geitlert Ettl
Green alga,
Chlamvdomonas sp.
Green alga,
Chlamvdomonas sp.
Green alga,
Chlamvdomonas sp.
Green alga,
Chlamvdomonas sp.
Green alga,
Chlamydomonas sp.
Green alga,
Chtamydofnonas sp.
Green alga,
Scenedesmus ouadrfcfl
Chemical
92.2%
•
96.4X
96.4X
-
Hardness
(mg/L as
CaCO.l Duration
96 hr
72 hr
1 hr
1 hr
72-96 hr
EfffiCi
EC50
(chlorophyll)
EC50
(growth)
EC50
(CO, fixation)
EC50
(CO* fixation)
36.2X " and 84.9X]
Concentration
(uo/LI
176
330
311
194"
50-52
Reference
Falrchlld et al.
1998
Kallqvist and
Romstad 1994
Francois and
Robinson 1990
Francois and
Robinson 1990
Foy and
72-96 hr
72-96 hr
72-96 hr
72-96 hr
4 days
8 hrs
growth inhibition;
12.8X reduction in
chlorophyll
64.IX d and 93.3X1
growth inhibition;
32.4X reduction in
chlorophyll
77.SX d and 96.6X*
growth inhibition;
49.9X reduction in
chlorophyll
76.6X " and 100X1
growth inhibition;
84.2X reduction in
chlorophyll
78.6X growth
inhibition"; 90.5X
reduction in
chlorophyll
EC50
(biomass)
"42X inhibition
of photosynthesis
100-104
Hiranpradit 1977
Foy and
Hiranpradit 1977
200-208 Foy and
Hiranpradit 1977
400-416 Foy and
Hiranpradit 1977
832 Foy and
Hiranpradit 1977
176 Fairchild et al.
1994
10 Valentine and
Bingham 1976
-------
Table 6. (Continued)
Species
Green alga,
Scenedesmus quadricauda
Green alga,
Scenedesmus quadricauda
Green alga,
Scenedesmus ouadHcauda
Green alga,
Scenedesmus quadricauda
Green alga,
Scenedesmus quadricauda
Green alga,
Scenedesmus Quadricauda
Green alga,
Scenedesmus Quadricauda
Green alga,
Scenedesmus quadricauda
Green alga,
Scencdesmus quadrtcauda
Green alga,
Scenedesmus ouadricauda
Green alga,
Scenedesmus quadricauda
Green alga,
Scenedesmus obllquus
Green alga,
Scenedesmus obliouus
Green alga,
Scenedesmus obHouus
Chemical
>95X
Technical
or
analytical
92.2X
Hardness
(mg/L as
CaCQ.) Duration
8 hr
8 hr
214 8 days
12-14 days
8 days
8 days
8 days
8 days
8 days
22 hr
96 hr
24 hr
24 hr
24 hr
Concentration
Effect • lua/L) Reference
~84X inhibition
of photosynthesis
~98X inhibition
of photosynthesis
Incipient
inhibition
ECSO
(cell number)
4.5X reduction in
photosynthesis
9.9X reduction in
photosynthesis
18.5X reduction in
photosynthesis
68.1X reduction in
photosynthesis
99. 3X reduction in
photosynthesis
96X inhibition of
photosynthesis
(HC uptake)
ECSO
(chlorophyll)
ECSO
("C uptake)
ECSO
(HC uptake)
ECSO
("C uptake)
100
1,000
30
100
4
9
30
100
337
2,667
169
38
57
49
Valentine and
Bingham 1976
Valentine and
Bingham 1976
Bringmann and
Kuhn 1977;
1978a,b
Stratton 1984
Bogacka et al.
1990
Bogacka et al.
1990
Bogacka et al.
1990
Bogacka et al.
1990
Bogacka et al.
1990
Peterson et al.,
1994
Fairchild et
al., 1998
Larsen et al.
1986
Larsen et al.
1986
Larsen et al.
1986
-------
Table 6. (Continued)
Species
Chemical
Hardness
(mg/L as
CaCO.) Duration
ElffiCl
Concentration
Reference
Green alga,
Scenedesmus subsplcatus
Green alga,
Scenedesmus subsolcatus
Green alga,
Scenedesmus subsolcatus
Green alga,
Scenedesmus subsoicatus
Green alga,
Scenedesmua subsoicatus
Green alga,
Scenqdesmus, subsplcatus
Green alga,
Scenedesmus subspicatus,
Green alga,
Scenedesmus sp.
Green alga,
Scenedesmus sp.
Green alga,
Scenedesmus sp.
Green alga,
Scenedesmus sp.
Green alga,
Scenedesmus sp.
99. OX
98X
4 days
24 hr
EC50
(cell number)
24.8X inhibition
of effective
photosynthesis
rate
110 Geyer et al.
1985
12.3 Schafer et al.
1994
24 hr
24 hr
24 hr
2 days
24 hr
72-96 hr
72-96 hr
72-96 hr
72-96 hr
72-96 hr
57.4X inhibition
of effective
photosynthesis
rate
93.4X inhibition
of effective
photosynthesis
rate
100.0X Inhibition
of effective
photosynthesis
rate
EC50
(cell numbers)
SOX reduction in
dry mass
60. 2X growth
inhibition1
72.4X growth
inhibition1
81. 6X growth
inhibition1
84. 7X growth
inhibition1
83. 7X growth
inhibition1
37
111.1
333.3
21
"21.5
50
100
200
400
800f
Schafer et al.
1994
Schafer et al.
1994
Schafer et al.
1994
Klrby and
Sheahan 1994
Relnold et al.
1994
Foy and
Hiranpradit 1977
Foy and
Hiranpradit 1977
Foy and
Hiranpradit 1977
Foy and
Hiranpradit 1977
Foy and
Hirarwradit 1977
-------
Table 6. (Continued)
Species
Hardness
(mg/L as
Chemical CaCQ,) Duration
Concentration
(ua/L) Reference
Green alga,
Sccnedesinus sp.
Green alga,
Selenastrum capricornutum
Green alga,
Selenastrum caprlcornutum
Green alga,
Selenastrum caprlcornutum
Green alga,
Selenastrum capricornutum
Green alga,
Selenastrum capricornutum
vj
oo Green alga,
Selenastrum caprlcornutum
Green alga,
Selenastrum caprlcornutum
Green alga,
Green alga,
Selenastrum caprlcornutum
Green alga,
Selenastrum capricornutum
Green alga,
Selenastrum capricornutum
Green alga,
Selenastrun caprlcornutum
Green alga,
Selenastrum caprlcornutum
Green alga,
Selenastrun capricornutum
4 days
97. AX - 5 days
97. IX - 5 days
97. 4X - 5 days
97.4X - 5 days
97.4X - 5 days
97.4X - 5 days
97.4X - 5 days
85. 5X 47 7 days
85. 5X 47 7 days
85. 5X 47 7 days
24 hr
24 hr
24 hr
5 days
EC50
(blomass)
Significantly
reduced cell
numbers
Minimum algfstatic
concentration
12X chlorophyll a
reduction
42X chlorophyll a
reduction
76X chlorophyll a
reduction
92X chlorophyll a
reduction
96X chlorophyll a
reduction
13. 8X increased
blomass
36. 2X decreased
biomass
75. 9X decreased
biomass
EC50
<"C uptake)
EC50
("C uptake)
EC50
(HC uptake)
EC50
(cell number)
169
54
200
32
54
90
150
200
100'
1,000*
1,000'
53'
34*
42b
100
Fairchild et al
1994
Parrish 1978
Parrish 1978
Parrish 1978
Parrish 1978
Parrish 1978
Parrish 1978
Parrish 1978
Johnson 1986
Johnson 1986
Johnson 1986
Larson et al.
1986
Larsen et al.
1986
Larsen et al.
1986
Roberts et al.
1990
-------
Table 6. (Continued)
Species
Green alga,
Selenastrum caoricornutum
Chemical
Hardness
(mg/L as
CaCQ.) Duration
Concentration
lua/i) Reference
Green alga,
Selenastrum capricornutum
Green alga,
Selenaatrum capricornutum
Green alga,
Selenastrum eapricornutum
Green alga,
Selenastrum capricornutum
Green alga,
Selenastrum capricornutum
Green alga,
Selenastrum capricornutum
Green alga,
Selenastrum capricornutum
Green alga,
Selenastrum capricornutum
Green alga,
Selenastrum capricornutum
Green alga,
Selenastrum capricornutum
Green alga,
Selenastrum capricornutum
-
SOX
SOX
SOX
SOX
reagent
grade
reagent
grade
reagent
grade
99.9X
99.9X
99. 9X
5 days
21 days
21 days
24 hr
24 hr
171 30 min.
171 30 min.
171 4 days
1 day
3 days
5 days
ECSO
(cell number)
ECSO
(biomass)
ECSO
(biomass)
ECSO
(0, evolution)
ECSO
(Devolution)
ECSO
(CO, fixation)
ECSO
(02 generation)
ECSO
(cell number)
22.0X reduction in
chlorophyll; 69.3X
reduction in "C
uptake
53.2X reduction in
chlorophyll; 42.4X
reduction in "C
uptake
24. 5X reduction in
chlorophyll; 60.6X
95
sa.r
*10b
69. r
854°
100
380
SO
130
130
130
Roberts et al.
1990
Turbak et al.
1986
Turbak et al.
1986
Turbak et al.
1986
Turbak et al.
1986
Versteeg 1990
Versteeg 1990
Versteeg 1990
Abou-Waly et al
1991a
Abou-Waly et al
1991a
Abou-Waly et al
1991a
99.9X
7 days
reduction in HC
uptake
11.6X reduction in
chlorophyll; 31.5X
reduction in "C
uptake
130 Abou-Waly et al.
1991a
-------
Table 6. (Continued)
Species
Green alga,
Selenaatrum caprlcornutun
Green alga,
Selenastrum capricornutum
Green alga,
Selenastrtm capricornutum
Green alga,
Selenastrum capricornutum
Green alga.
Selenastrum caprlcornutum
Green alga,
Selenastrum caprlcornutun
Green alga.
§ Selenastrtm capricornutum
Green alga,
Selenastrum capricornutum
Green alga.
Selenastrum capricornutum
Green alga.
Selenastrum capricornutum
Green alga,
Selenastrum capricornutum
Green alga.
Selenastrum capricornutum
Green alga,
Selenastrum capricornutum
Hardness
(mg/L as
Chemical CaCO.) Duration
99. 9X - 3 days
99.9X - 5 days
99. 9X - 7 days
92.2% - 4 days
72 hr
72 hr
Technical • 22 hr
or
analytical
100 96 hr
72 hr
96 hr
96 hr
72 hr
72 hr
Effect
ECSO
(chlorophyll a)
ECSO
(chlorophyll a)
ECSO
(chlorophyll a)
ECSO
(chlorophyll)
ECSO
(growth)
ECSO
(growth)
99X inhibition of
photosynthesis
("C uptake)
ECSO
(chlorophyll a)
ECSO
LC50
ECSO
(cell numbers)
ECSO
(cell numbers)
ECSO
(chlorophyll a -
spectrophotometric
Concentration
(un/L)
283
218
214
117
200
110
2,667
147
118.2
26
26
359
902
Reference
Abou-Uay et al.
1991b
Abou-Uay et al.
1991b
Abou-Uay et al.
1991b
Fail-child et al.
1994a. 1998
Kallqvist and
Romstad 1994
Kallqvlst and
Romstad 1994
Peterson et al.
1994
Gaggi et al.
1995
Radetskl et al.
1995
Caux et al. 1991
Caux et al. 1991
Van der Heever
and Grobbelaar
1996
Van der Heever
and Grobbelaar
1996
measurement)
-------
Table 6. (Continued)
Species
Green alga,
Selenastrum capHcornuttm
Green alga,
Selenastrum caoricornutum
Green alga,
Selenaatrum caoricornutum
Green alga,
Selenastrum capricornutum
Green alga,
oo Selenastrum capricornutum
h1
Green alga,
Selenaatrum capricornutum
.Green alga,
Anklatrodesmus brauni 1
Green alga,
Ankistrodesmus sp.
Green alga,
Ankistrodesmus sp.
Green alga,
Stloeoc Ionium tenue
Green alga,
Stioeoclonium tenue
Green alga,
Ulothrlx subconstrlcta
Green alga,
Chlorococctm hvpnosporum
Hardness
(mg/L as
Chemical CaCO.) Duration
72 hr
96 hr
96 hr
Technical - 96 hr
grade
Technical • 96 hr
grade
Technical • 96 hr
grade
99.9X - 11
24 hr
24 hr
24 hr
24 hr
24 hr
2 weeks
Effect
, EC50
(chlorophyll • -
fluorometric
measurement)
EC50
(cell number;
free culture)
EC50
(cell number;
Immobilized
culture)
Biomass
NOEC
Biomass
LOEC
Biomass
EC50
EC50
(cell number)
EC50
("C uptake)
EC50
(HC uptake)
EC50
(HC uptake)
EC50
("C uptake)
EC50
(nC uptake)
75X reduced
growth
Concentration
(ua/L)
960
200
220
75
150
235
60
72'
61'
127'
224'
88*
5,000
Reference
Van der Heever
and Grobbelaar
1996
Abdel-Hamid 1996
Abdel-Hamld 1996
Fairchild et al.
1997
Fairchild et al.
1997
Fairchild et al.
1997
Burred et al.
1985
Larsen et al.
1986
Larsen et al.
1986
Larsen et al.
1986
Larsen et al.
1986
Larsen et al.
1986
Virmant et al.
1975
-------
Table 6. (Continued)
00
N>
Species
Green alga,
Chlorococcum hvpnosporum
Green alga,
Gloetaeniunj 1 o 1 1 1 esbergar i anum
Green alga,
f ranee la sp."
Green alga,
F ranee i a sp."
Green alga,
F ranee i a sp."
Green alga,
France la sp.f/
Green alga,
France la sp."
Diatom,
Cvclotella mcneahiniana
(Arizona race)
Diatom,
Cvclotelta meneohinlana
(Iowa race)
Diatom,
Cvclotella meneohiniana
Diatom,
Cvclotella sp.
Diatom,
Havicula petllculosa
Hardness
(mg/L as
Chemical CaCO,) Duration
2 weeks
96 hr
94X . 2 min
94X - 2 min
94X - 2 min
94X - 2 min
94X - 2 min
7 min.
7 min.
Technical - 22 hr
or
analytical
6 days
97X • 5 days
EfifiCt
92X reduced
growth
inhibition
of calcification
EC50
(photosynthetic
oxygen evolution)
ECSO
(photosynthetic
oxygen evolution)
ECSO
(photosynthetic
. oxygen evolution)
ECSO
(photosynthetic
oxygen evolution)
ECSO
(photosynthetic
oxygen evolution)
ECSO
(photosynthesis)
ECSO
(photosynthesis)
97X inhibition of
photosynthesis
("C uptake)
ECSO
(growth)
ECSO
(cell number)
Concentration
(ua/l)
10,000
2,157
466
774
710
430
720
99
105
2,667
430
60
Reference
Vermani et al.
1975
Prasad and
Chowdary 1981
Hersh and
Crumpton 1989
Hersh and
Crumpton 1989
Hersh and
Crumpton 1989
Hersh and
Crumpton 1989
Hersh and
Crumpton 1989
Millie and Hersh
1987
Millie and Hersh
1987
Peterson et al.
1994
Kallqvist and
Romstad 1994
Hughes 1986,
1988
-------
Table 6. (Continued)
oo
Ul
Species
Diatom,
Mavicula pelliculosa
Diatom,
Mavicula pelliculosa
Diatom,
Mavicula pelliculosa
Diatom,
Mitischiq sp.
Cryptomonad,
Cryptomonas pvrinoidifera
Duckweed,
Lemna minor
Chemical
97X
97X
97X
Technical
or
analytical
Hardness
(mg/L as
CaCO.) Duration
Duckweed,
Lemna minor
Duckweed,
Lemna minor
Effect
Concentration
20 days
20 days
soluble protein
content; Increased
photosynthesis,
increased
respiration
~12X reduced
growth;
increased water,
soluble protein
content; increased
photosynthesis and
respiration
-23X reduced
growth; increased
water and soluble
protein content;
increased
photosynthesis and
respiration
SO
100
Reference
5 day exposure,
9 day recover
5 day exposure,
9 day recovery
5 day exposure,
9 day recovery
22 hr
6 days
20 days
NOEC
Algistatic
concentration
Algicidal
concentration
99X inhibition of
photosynthesis •
("C uptake)
EC50
(growth)
No effect upon
growth; increased
<100
1,710
>3,200
2,667
500
20
Hughes 1986,
1988
Hughes 1986,
1988
Hughes 1986,
1988
Peterson et a I
1994
Kallqvlst and
Romstad 1994
Beaumont et a I
1976a.b,c
Beaumont et al.
1976a.b,c
Beaumont et al.
1976a,b,c
-------
Table 6. (Continued)
Species.
Duckweed,
Lemna minor
Chemical
Hardness
(mg/L as
CflCQ,)
Duration
15 days
Duckweed,
Lemna minor
20 days
Duckweed,
Lama miciflc
15 days
Duckweed,
Lemna minor
Duckweed,
Lemna mlftor
15 days
10 days
Effect
Increased total
fatty acid and a-
llnolenic acid
content; increased
monogalatosyldia-
cyl-glycerol
percentage
*74X reduced
growth; increased
water,
chlorophyll, and
soluble protein
content; increased
photosynthesis and
respiration
Increased total
fatty acid and or-
linolenic acid
content; decreased
linoleic acid
content; increased
monoga-
lactosyldiacyl-
glycerol
percentage
Increased amounts
of polar lipids in
chlorophylt-
protein complexes
of chloroplasts
Increased tucj-
acetate
incorporation into
chloroplast lipids
Concentration
fug/Li
100
Reference
Grenier et al.
1979
250
Beaumont et al.
1976a,b.c
1,000
Grenier et al.
1979
248
248
Grenier et al.
1987
Grenier et al.
1989
-------
Table 6. (Continued)
Species
Duckweed, •
Lemna minor
Duckweed,
Lemna. minor
Duckweed,
Lemna minor
Duckweed,
Lemna minor
Duckweed,
03 Lemna minor
01 mmumtm .,
Duckweed,
Lemna minor
Duckweed,
Lemna qibba
Duckweed,
Lemna qibba
Duckweed,
Lemna qibba
Duckweed,
Lemna gjbba
Uild rice,
jtizapiq aquatica
Chemical .
-
Technical
or
analytical
92.2%
Technical
Technical
Technical
97X
97X
97X
97X
85X
Hardness
(mg/L as
CaCO.) Duration
2 days
7 days
4 days
96 hr
96 hr
96 hr
5 days
5 day exposure
9 day recovery
5 day exposure
9 day recovery
5 day exposure
9 day recovery
83 days
Concentration
Effect (ufl/L) Reference
Changes in
chloroplast
ult restructure;
increased
chlorophyll
content
95X inhibition of
growth
ECSO
(frond production)
Biomass
NOEC
Biomass
LOEC
Biomass
ECSO
ECSO
(frond production)
NOEC
(frond production)
Phytostatic
concentration
Phytocidal
concentration
Visibly senescent;
248
2,667
92
75
150
153
170
<100
1,720
>3,200
SO
Simard et al.
1990
Peterson et al.
1994
Fairchild et al.
1998
Fairchild et al.
1997
Fairchild et al.
1997
Fairchild et al.
1997
Hughes 1986,
1988
Hughes 1986,
1988
Hughes 1986,
1988
Hughes 1986.
1988
Detenbeck et al.
Wildcelery.
Valllsnerla americana
42 days
75X reduction in
chlorophyll a in
leaves
ECSO
(total leaf
length)
163
1996
Davis 1980;
Forney and Davis
1981
-------
Table 6. (Continued)
Spec{eg
Chemical
Hardness
(mg/L as
CaCOQ Duration
Effect
Concentration
tua/L) Reference
Wildcelery,
Vallisneria. americana
Wildcelery,
Vallisneria americana
Coontaii,
Ceratophyllum sp.
Coontaii,
Ceratophyllum dermersum
Cattail,
Tvpha latifolia
Eurasiun watermilfoil.
00 Hyriophvllum spicatum
-------
Table 6. (Continued)
o>
Species
Elodea,
Elodea canadenais
Elodea,
Elodea canadensis
Elodea,
Elodea canadensis
Elodea,
Elodea canadensis
Water moss,
Fontinails antiovretica
Water moss,
Fontinalia squamosa
Water moss,
FontlnaHs hypnoides
Mixed macrophytes,
Ceratophvllum sp.
and Elodea sp.
Nfxed macrophytes,
Ceratophvllum sp.
and Elodea sp.
Mixed macrophytes,
Ceratophvllum sp.
and Elodea sp.
Protozoa,
Acanthamoeba castellan!i
Protozoa,
Acanthamoeba castellan!i
Chemical
85X
92.2% .
•
•
85. SX
85. SX
85. SX
-
-
Hardness
(mg/L as
CaCq.) Duration
21 days
20 days
19 days
14 days
20 days
24 hr
24 hr
47 30 days
47 30 days
47 30 days
6 days
6 days
Concentration
Effect (ua/L) Reference
EC50
(length)
Dark respiration
rate exceeded net
photosynthesis
rate
No effect upon
growth
EC50
(wet weight)
Dark respiration
rate exceeded net
photosynthesis
rate
20X reduction in
net photosynthesis
90X reduction in
net photosynthesis
18.3X increased
biomass
11. 6X decreased
biomass
47.6X decreased
biomass
SX population
decrease
14X population
decrease
109
10
75
21
10
10
2
10
100
1,000
100
1,000
Davis 1980;
Forney and Davis
1981
Hoffmann and
Winkler 1990
Detenbeck et al.
1996
Fairchild et al.
1998
Hoffmann and
Winkler 1990
Hoffmann and
Winkler 1990
Hoffmann and
Winkler 1990
Johnson 1986
Johnson 1986
Johnson 1986
Prescott et al.
1977
Prescott et al.
1977
-------
Table 6. (Continued)
00
Spectea
Chemical
Hardness
(mg/L as
CaCO.) Duration
Concentration
(ua/L) Reference
Protozoa,
Acanthamoeba castel lani i
Protozoa,
Acanthamoeba castel lani i
Protozoa,
Eualena aracilis
Protozoa,
Eualena aracllls
. Protozoa,
Eualena oraclHs
Protozoa,
Cqlpldfum campvlun
Protozoa,
Tetrahvmena pyriformis
Protozoa,
Tetrahymena pvrlformis
Hydra,
Hvdra viridjs
Leech,
Glossiphonia complanata
Leech,
Helobdella st agnails
Snail,
Lvmnaea palustrls '
Snail,
Lymnaea palustrls
Mussel (glochidia larva),
Apadontq imbecills
6 days
6 days
- 8 hr
8 hr
8 hr
24 hr
- - 24 hr
48 hr
21 days
99. 2X - 27-28 days
99.2X - 27-28 days
97.8X - 12 wks
97.8X - 12 wks
97.3X 40-50 24 hr
15X population
decrease
40X population
decrease
*11X inhibition of
photosynthesis
~28X inhibition of
photosynthesis
~83X inhibition of
phyot synthesis
EC50
(cell number)
EC50
EC50
(cell number)
Reduced budding
rate
LC50
LC50
No effect upon
growth, fecundity
or glycogen
metabolism
Inhibited BaPH and
GST enzyme
activities
LC50
4,000
10,000
10
100
1.000
>50,000
118,500
96.000
5,000
6,300
9,900
125
5
>60,000
Prescott et al.
1977
Prescott et al.
1977
Valentine and
Blngham 1976
Valentine and
Blngham 1976
Valentine and
Blngham 1976
Roberts et al.
1990
Huber et al.
1991
Schafer et al.
1994
Benson and Boush
1983
Streit and Peter
1978
Streit and Peter
1978
Baturo et al.
1995
Baturo and
Lagadic 1996
Johnson et al.
1993
-------
Table 6. (Continued)
Hardness
(mg/L as
CaCO.) Duration
Concentration
Reference
Mussel (1-2d old juvenile),
Anadonta jmbecitis
Mussel (7-10 d old juvenile),
Anadonta Imbecilis
Rotifer,
Brachionus calvclflorus
Anostracan,
Streptoceohatua texanus
Cladoceran,
Ceriodaphnia dub la
Cladoceran,
Ceriodaphnia dubla
Cladoceran ($26 h),
8 Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
paphnia magna
Cladoceran,
Daphnia magna
Cladoceran,
Daphnia magna
Cladoceran (<24 h),
Daphnia magna
Cladoceran,
Paphniq magnq
••••^••••AMhA ,*^*mt^**J^-^: A«B^^Mb*AM
97.3X 40-50 48 hr
97.3X 40-50 48 hr
24 hr
24 hr
>99X 57.1 4 days
>99X 57.1 4 days
26 hr
100 . 48 hr
100 48 hr
21 days
48 hr
96 hr
96 hr
97.3X 40-50 48 hr
- 24 hr
^h^_»^i^h^
LC50
LC50
LC50
LC50
MATC
MATC
LC50
BCF «4.4
BCF = 2.2
Reduced young
production
10X mortality
30X mortality
60X mortality
LC50
EC50
>60,000
>60,000
7,840
>30.000
7,100
14.100
3,600
10
10
2,000
22.000
16.900
48,300
9,4000/
>30,000
Johnson et al.
1993
Johnson et al.
1993
Crisinel et al.
1994
Crlsinel et al.
1994
Oris et al. 1991
Oris et al. 1991
Frear and Boyd
1967
Ellgehausen et
al. 1980
Ellgehausen et
al. 1980
Kaushlk et al.
1985
Bogacka et al.
1990
Bogacka et al.
1990 '
Bogacka et al.
1990
Johnson et al.
1993
Crisinel et al.
1994
-------
Table 6. (Continued)
Spec j eft
Cladoceran,
Oaphnia maona,
Cladoceran,
Daphnia magna,
Cladoceran,
Daphnia magna,
Cladoceran (adult),
Daphnia put ex
Cladoceran,
Oaphnja pulex
Cladoceran,
Q Daphnia pulex
Cladoceran,
Daphnia pulex
Cladoceran,
Daphnla pulen
Cladoceran,
Oaphnia put ex
Cladoceran,
Daphnia pulex
Cladoceran,
Daphnia pulex
Hardness
(mg/L as
Chemical CaCO.) Duration
48 hr
85X - 48 hr
85X - 48 hr
• - 3 hr
99. 2X - 28 days
99.2X - 28 days
99.2X • "70 days
99.2X - 28 days
99.2X - 28 days
99. 2X - 28 days
99. 2X - 70 days
Effect
EC50
Significantly
decreased survival
No effect upon
survival
LCSO
11. 7X decreased
survival and 28. 2X
decreased
reproduction
4.2X decreased
survival and 26. 8X
decreased
reproduction
41.7X decreased
reproduction
20. 2X decreased
survival and 45. SX
decreased
reproduction
9.6X decreased
survival and 48. 3X
decreased
reproduction
42X decreased
reproduction
48. 2X decreased
reproduction
Concentration
(ua/L)
>30,000
25
50
>40,000
1,000
2.000
2.000
3,000
4,000
5,000
5,000
Reference
Crisinel et al.
1994
Detenbeck et a I
1996
Detenbeck et al
1996
Nishiuchi and
Hashimoto 1967,
1969
Schober and
Lanpert 1977
Schober and
Lanpert 1977
Schober and
Lanpert 1977
Schober and
Lanpert 1977
Schober and
Lanpert 1977
Schober and
Lanpert 1977
Schober and
Lanpert 1977
-------
Table 6. (Continued)
Species
Cladoceran.
Daphla pulex
Cladoceran,
Daphnfa pujex
Cladoceran,
Daphnia pulex
Cladoceran,
Daphnla pulex
Cladoceran,
Dauhnla pulex
Cladoceran (adult),
Molna macrocopa
Cladoceran,
Nofna macrocopa
Amphlpod (1st fnstar),
Camnarua fasciatus
Nidge (2nd instar),
Chironomus H par lug .
Nidge CIO d),
Chlronomus tentans
Rainbow trout (embryo),
Oncorhvnchus mvkisa
Rainbow trout (embryo),
Oncorhvnchus mvkiss
Hardness
(mg/L as
Chemical CaCO.) Duration
99.2% . - 28 days
99. 2X • 70 days
99. 2X • 28 days
10 min.
10 min.
3 hr
4-6 weeks
94X • 48 hr
151 10 days
97. 1 42-44 96 hr
(fed)
80% 50 23 days
(at hatching)
SOX 200 23 days
(at hatching)
Effect
14.9X decreased
survival; 53. 9X
decreased
reproduction
62.6X decreased
reproduction
96. 5X decreased
reproduction
10X reduction in
food consumption
SOX reduction in
food consumption
LC50
40X mortality; 10X
increase in
potential
production;
reduced actual
population growth
LC50
LC50
LC50
LC50
LC50
Concentration
(ug/L)
10,000
10,000
20,000
350
1.600
>40,000
1,000
5,700
18,900
>28,000
736
888
Reference
Schober and
Lamport 1977
Schober and
Lampert 1977
Schober and
Lampert 1977
Pott 1980
Pott 1980
Nlshiuchl and
Hashinoto 1967,
1969
Shcherban
1972a,b
Nacek et al.
1976
Taylor et al.
1991
NcNamara 1991
Blrge et al.
1979
Blrge et al.
1979
-------
Table 6. (Continued)
10
to
Specjes
Rainbow trout (sac fry),
Oncorhvnchus mvkiss
Rainbow trout (sac fry),
Oncorhynchus
Rainbow trout (sac fry),
Oncorhvnchus mykiss.
Rainbow trout (sac fry),
Oncorhynchus
Rainbow trout (sac fry),
Oncorhynchus mvkiss
Rainbow trout (sac fry),
Oncorhynchus mvkiss
Rainbow trout (sac fry),
Oncorhvnchuts mykiss
Rainbow trout (sac fry),
Oncorhvnchuts mvkiss
Rainbow trout (sac fry),
Oncorhynchus mykiss
Rainbow trout (sac fry),
Oncorhvnchus mykjss^
Rainbow trout (sac fry),
Oncorhvnchus
Chemfpat
SOX
80%
SOX
SOX
SOX
SOX
SOX
BOX
SOX
SOX
SOX
Hardness
(mg/L as
CflCOxL
50
200
50
200 .
50
50
50
200
200
200
200
Duration Effect
27 days LC50
(4 days post-
hatch)
27 days LC50
(It days post-
hatch)
27 days LCI
(4 days post-
hatch)
27 days LCI
(4 days post-
hatch)
27 days 3X teratic larvae
(4 days post-
hatch)
27 days 6X teratic larvae
(4 days post-
hatch)
27 days 62X teratic larvae
(4 days post-
hatch)
27 days 2X teratic larvae
(4 days post-
hatch)
27 days 3X teratic larvae
(4 days post-
hatch)
.27 days 4X teratic larvae
(4 days post-
hatch)
27 days 65X teratic larvae
(4 days post-
hatch)
Concentration
fua/L) Reference
696
864
23.2
61.8
43.2
432
4,020
13.6
48.0
416
4.020
Bfrge et al
1979
Birge et ai
1979
Birge et al
1979
Birge et al
1979
Birge et al
1979
Birge et al
1979
Birge et al
1979
Birge et al
1979
Birge et al
1979
Birge et at
1979
Birge et al,
1979
-------
Table 6. (Continued)
10
Species
Rainbow trout (Juvenile),
Oncorhvnchus mvkiss
Rainbow trout (juvenile),
Qncorhvnchus mvkiss
Rainbow trout (juvenile),
Qncorhvnchus myfciss
Rainbow trout,
Oncorhvnchus mykiss
Rainbow trout,
Oncorhvnchus mvkiss
Rainbow trout,
Oncorhvnchus mvkiss
Rainbow trout (juvenile),
Oncorhvnchus mvJtisg
Rainbow trout (juvenile),
Oncorhvnchus mvkisq
Rainbow trout (juvenile),
Oncorhvnchus mvkjsq
Chemical
99.3%
Hardness
(mg/L as
CaCO,)
93.
298%
>98%
Duration
48 hr
28 days
28 days
28 days
28 days
28 days
14 days
10 days
10 days
Effect
LC50
Changes in renal
corpuscle
ultrestructure
Changes in renal
corpuscle and
tubule
ultrestructure
Slight
u(trestructure!
changes in renal
corpuscles
Slight
histopathological
changes in liver;
increased
ultrestructure!
changes in renal
corpuscles
Ultrestruetural
changes in renal
corpuscles and
histopathological
changes in liver
No effect upon
survival, body
weight, liver
weight, or liver
xenobiotic-
metabolizing
enzyme activities
Reduced plasma
protein
Reduced plasma
protein
Concentration <
(ua/L) Reference
5,660 Pluta, 1989
Fischer-Scherl
et at. 1991
10 Fischer-Scherl
et al. 1991
SchwaIger et al.
1991
10 Schwaiger et al.
1991
20
10
3.0
50
Schwaiger et al.
1991
Egaas et al.
1993
Oavies et al.
1994
Davies et al.
1994
-------
Table 6. (Continued)
Spec{63
Rainbow trout (juvenile),
Oncorhynchus mvkiss
Rainbow trout (Juvenile),
Oncorhvnchus myjsias
Common carp,
Cvprlnus
Hardness
(mg/L as
Chemfcql CaCQ,) Duration
Effect
Concentration
tua/L) Reference
Common carp (30-SOg),
Cvprinus carpio
Common carp (30-50g),
Cvprinus carpio
Common carp (30-SOg),
Cyprinus carpi o
Common carp (30-50g),
Cvprinus carpio
Common carp (30-SOg),
Cvprinus carpio
Common carp (30-SOg),
Cyprinus carpio
Common carp (30-50g),
Cvprinus carpio
Common carp (30-50g),
Cvprinus carpio
Common carp <30-50g).
Cvprinus carpi9
Common carp (30-SOg),
Cvprinus carpio
99X
99X
380
380
5 weeks
5 weeks
48 hr
12 hr
24 hr
6 hr
12 hr
24 hr
12 hr
24 hr
6 hr
12 hr
24 hr
infrastructure I
alterations in
kidney proximal
tubules
Ultrastructural
alterations in
kidney proximal
and distal tubules
LC50
"125X increased
serum cortisol
*300X increased
serin cortisol
~40X increased
serum cortisol
"60X increased
serum cortisol
~250X increased
serum cortisol
"60X increased
serum glucose
~35X increased
serum glucose
"15X increased
serum glucose
~40X increased
serum glucose
~70X increased
serum glucose
12.4
24.0
>10,000
100
100
500
500
500
100
100
500
500
500
Oulni et at.
1995
Oulmi et al.
1995
Nishluchl and
Hashimoto 1967,
1969
Hanke et al.
1983
Hanke et al.
1983
Hanke et al.
1983
Hanke et al.
1983
Hanke et al.
1983
Hanke et al.
1983
Hanke et al.
1983
Hanke et al.
1983
Hanke et al.
1983
Hanke et al.
1983
-------
Table 6. (Continued)
Spectea
Chemical
Hardness
(mg/L as
CaCQQ
Concentration
lua/L} Reference
vo
01
Cannon carp (30-50g),
Cvprinua carolo
Cannon carp (30-SOg),
Cvprinua carpio '
Common carp (30-509),
Cvprinua carpio
Comnon carp (30-50g),
Cvprinus carpio
Comnon carp (30-SOg),
Cvprinua carpiq
Common carp (30-50g),
Cvprinus
72 hr
4 hr
Comnon carp (30-SOg),
Cvprinua carpio
6 hr
12 hr
24 hr
4 hr
6 hr
,"180X increased 1,000 Hanke et al.
serum glucose; 1983
"40X decreased
liver glycogen
100 Hanke et al.
1983
"25X increase in
gill total ATPase
activity; "20X
increase in gill
Na-K dependent
ATPase
~10X increase In 100 Hanke et al.
gill total ATPase; 1983
~30X decrease In
gill Na-K
dependent ATPase
"40X decrease In 100 Hanke et al.
gill total ATPase; 1983
"30Xdecrease in
gill Na-K
dependent ATPase
~5X decrease in 100 Hanke et al.
gill total ATPase; 1983
"2SX decrease in
gill Na-K
dependent ATPase
~60X increase in 100 Hanke et al.
serum AChE 1983
"15X increase in 100 Hanke et al.
serum AChE 1983
Common carp (30-50g),
Cvprinua carpio
Comnon carp (30-SOg),
Cvprinus carpio
12 hr
24 hr
~35X increase in
serum AChE
~25X decrease in
serum AChE
100
100
Hanke et al.
1983
Hanke et al.
1983
-------
Table 6. (Continued)
u>
a\
Species,
Common carp,
Cvprlnus carplq
Cannon carp (juvenile),
Cvprlnus carplo
Common carp (juvenile),
Cyprinus carolo
Comnon carp (juvenile),
Cvprlnus carpio
Goldfish,
Carasslus auratus
Fathead minnow (s24h),
Pjmephales prpmelas
Fathead minnow (juvenile),
Pimephales promelas
Fathead minnow (larvae),
Plmephales promelas
Channel catfish.
Ictalurus punctatus
Chemical
99.3X
93. 7X
93. 7X
Hardness
(mg/L as
CaCQ,) Duration
72 hr
48 hr
141-223 96 hr
(fed)
141-223 14 days
Effect
Increased serin
glucose and
cor tf sol;
decreased liver
and muscle
glycogen;
decreased serum
protein and
cholesterol
LC50
LC50
Increased serum
alkaline
Concentration
fuo/L) Reference
100 Gluth and Hanke
1984, 1985
16,100 Pluta, 1989
18.800 Neskovic et al.
1993
1.500 Neskovic et al.
1993
phosphatase;
decreased alkaline
phosphatase In
heart, liver and
kidneys; increased
GPT in liver and
kidneys;
hyperptasia of
some gill
epithelial cells
97
85X
85X
SOX
48 hr
60 7 days
13 days
7
50 4.5 days
(at hatching)
LC50
NOEC
(biomass)
No effect upon
survival or growth
No effect upon
survival
LC50
>10,000
z4,900
75
75
272
Nishluchi and
Hashimoto 1967.
1969
Jop 1991b
Oetenbeck et
1996
Oetenbeck et
1996
Birge et al.
1979
al
al
-------
Table 6. (Continued)
Species
Channel catfish,
Ictalurus punctatua
Channel catfish (sac fry),
Ictalurus punctatus
Channel catfish,
Ictalurus punctatus
Channel catfish (sac fry),
Ictalurus punctatus
Channel catfish (sac fry),
Ictalurua punctatus
ID
Kj
Channel catfish (sac fry),
Ictalurua punctatus
Channel catfish (sac fry),
Ictalurus punctatus
Channel catfish (sac fry),
Ictalurus punctatus
Channel catfish (sac fry),
Ictalurus punctatus
Channel catfish (sac fry),
Ictalurus punctatus
Channel catfish (sac fry),
Ictalurus punctatua
Chemical
SOX
80%
BOX
80X
SOX
SOX
SOX
SOX
BOX
SOX
SOX
Hardness
(mg/L as
CaCQT)
200
50
200
SO
50
50
50
50
200
200
200
Concentration
Duration Effect (ua/L) Reference
4.5 days LC50 248
(at hatching)
8.5 days LC50 176
(4 days post-
hatch)
8.5 days LC50 192
(4 days post-
hatch)
8.5 days 1X teratic larvae 22.4
(4 days post-
hatch)
8.5 days 4X teratic larvae 47.2
(4 days post-
hatch)
8.5 days 13X teratic larvae 344
(4 days post-
hatch)
8.5 days 69X teratic larvae 3,864
(4 days post-
hatch)
8.5 days 100X teratic 37.360
(4 days post- larvae
hatch)
8.5 days IX teratic larvae 26.4
(4 days post-
hatch)
8.5 days 4X teratic larvae 43.2
• (4 days post-
hatch)
8.5 days 16X teratic larvae 336
(4 days post-
hatch)
Blrge et al
1979
Blrge et al
1979
Blrge et al
1979
Blrge et al
1979
Birge et al
1979
Birge et al
1979
Birge et al
1979
Birge et al
1979
Blrge et al
1979
Birge et al
1979
Birge et al
1979
-------
Table 6. (Continued)
vo
oo
Species
Channel catfish (sac fry),
Ictalurua nunctatus
Channel catfish (sac fry),
Ictaturus ounctatus
Mosquitofish,
Gambits I a affinis
Poecilia reticulata
Guppy,
Poeclllq retlcutata
Cuppy,
PoeclUa reticulata
Cuppy,
Poecilia reticulata
Mozambique tilapia,
Tl lapia mossambica
Mozambique tilapia,
T, jlapia mossamblca
Chemical
BOX
SOX
technical
-
-
• -
-
-
Hardness
(mg/L as
CaCO.) Duration
200 8.5 days
(4 days post-
hatch)
200 8.5 days
(4 days post-
hatch)
48 hr
48 hr
72 hr
96 hr
96 hr
90 days
Elffitt
47X teratfc larvae
86X teratfc larvae
no mortality
LC50
LC50
40X
mortality
53. 2X
mortality
Decrease in red
and white blood
Concentration
lua/L)
3,848
37,360
10.000
38,200
31,600
28,600
37,200
1,100
Reference
Birge et al.
1979
Birge et al.
1979
Daruazeh and
Mull a 1974
Tscheu-Schluter
1976
Tscheu-Schluter
1976
Bogacka et al.
1990
Bogacka et al.
1990
Prasad et al.
1991a
30 days
cell counts,
hemoglobin, packed
cell volume, mean
corpuscular
hemoglobin;
decreased whole
animal oxygen
consumption;
increases in mean
cell volume, blood
volume and blood
water content.
Changes in enzyme
activity and
levels of amino
acids, proteins,
ammonia, and urea
in brain and liver
1,100
Prasad et al.
1991b
-------
Table 6. (Continued)
ID
10
Species
Mozambique tilapia,
Tilapia inossemfaica
Chemical
Mozambique tilapia.
Tilapia Bossambicus
Bullfrog (embryo and tadpole),
Rana catesbeiana
Bullfrog (embryo and tadpole),
Rana catesbeiana
Bullfrog (embryo and tadpole),
Rana catesbeiana
Bullfrog (entryo and tadpole),
Rana catesbeiana
Bullfrog (embryo and tadpole),
Rana catesbeiana
Bullfrog (embryo and tadpole),
Rana catesbeiana
Bullfrog (embryo and tadpole),-
pana catesbeiana
Hardness
(fflg/L as
CaCO.)
Duration
30 days
Effect
Increases in
lipase activity,
free fatty acids,
acetoacetate
concentration, and
total cholesterol
in liver and
muscle; decreases
in total lipids,
glycerol and
phospholipids in
liver and muscle.
Concentration
1,100
Reference
Srlnivas et al.
1991
•
BOX
SOX
BOX
80X
SOX
SOX
SOX
90 days
113 8 days
. (4 days post-
hatch)
113 8 days
(4 days post-
hatch)
113 8 days
(4 days post-
hatch)
113 4 days
(to hatch)
113 4 days
(to hatch)
113 4 days
(to hatch)
113 4 days
(to hatch)
Increased body
weight, percent
water, serum Ma*
and serum K*;
decreased serin
Ca", Mg", and
HCOj"
LC1
1C 10
LC50
IX teratic
surviving larvae
3X teratic
surviving larvae
7X. teratic
surviving larvae
22X teratic
surviving larvae
1,100 Prasad and Ri
1994
7.4 Blrge et al.
1980
44.9 Birge et al.
1980
410 Birge et al.
1980
51 Birge et al.
1980
410 Birge et al.
1980
6,330 Blrge et al.
1980
14,800 Birge et al.
1980
-------
Table 6. (Continued)
Species
Bullfrog (embryo and tadpole),
Rana catesbeiana
Bullfrog (embryo and tadpole),
catesbeiana
Leopard frog (embryo and
Rana pi pi ens
Leopard frog (embryo and tadpole),
Rang pipiens
Leopard frog (embryo and tadpole),
Rana plpiens
Leopard frog (embryo and tadpole),
Rana pipiens
Leopard frog (embryo and tadpole),
Rana pipiens
Leopard frog (embryo and tadpole),
Rana plpiens
Leopard frog (embryo and tadpole),
Rana pipicns
Leopard frog (embryo and tadpole),
Rana plpiens
Leopard frog (embryo and tadpole).
Rana pipiens
Leopard frog (tadpole),
Rana pipiens
Pickerel frog (embryo and
tadpole),
Rana palustris
Chemical
BOX
SOX
80X
SOX
SOX
SOX
SOX
SOX
SOX
SOX
SOX
85X
SOX
Hardness
(mg/L as
CaCO.)
113
113
115
115
115
115
115
115
115
115
115
-
103
Duration
4 days
(to hatch)
4 days
(to hatch)
9 days
(4 days post-
hatch)
9 days
(4 days post-
hatch)
9 days
(4 days post-
hatch)
5 days
(to hatch)
5 days
(to hatch)
5 days
(to hatch)
5 days
(to hatch)
5 days
(to hatch)
5 days
(to hatch)
41 days
8 days
(4 days post-
hatch)
Concentration
47X teratic
surviving larvae
100X teratic
surviving larvae
LCI
LC10
LC50
2X teratic
surviving larvae
2X teratic
surviving larvae
5X teratic
surviving larvae
9X teratic
surviving larvae
13X teratic
surviving larvae
46X teratic
surviving larvae
No effect upon
growth or survival
LC50
26,400
45.800
32.6
378.9
Reference
Blrge et al.
1980
Birge et al.
1980
Birge et al.
1980
Birge et al.
1980
7,680 Birge et al.
1980
110 Birge et al.
1980
210 Birge et al.
1980
1,113 Birge et al.
1980
6,540 Birge et al.
1980
13.200 Birge et al.
1980
48.700 Birge et al.
1980;
25 Detenbeck et al.
1996
17,960 Birge et al.
1980
-------
Table 6. (Continued)
Species
Pickerel frog (embryo and
tadpole),
Rana palustris
Pickerel frog (embryo and
tadpole),
Rana palustrls
Pickerel frog (embryo and
tadpole),
Rana palustrls
American toad (embryo and
tadpole),
Bufo americanus
American toad (embryo and
tadpole),
Bufo americanus
American toad (embryo and
tadpole),
Bufo americanus
American toad (embryo and
tadpole),
Bufo americanus
American toad (embryo and
tadpole),
Bufo americanus
American toad (embryo and
tadpole), .
Bufo amerlcanus
African clawed frog
(embryo),
Xenopus laevia
African clawed frog
(embryo),
Xenoous laevis
Chemical
BOX .
SOX
SOX
SOX
SOX
SOX
SOX
SOX
SOX
Hardness
(mg/L as
CaCO.l Duration
103 4 days
(to hatch)
103 4 days
(to hatch)
103 4 days
(to hatch)
7 days
(4 days post
hatch)
3 days
(to hatch)
3 days
(to hatch)
3 days
(to hatch)
3 days
(to hatch)
3 days
(to hatch)
40. ex
40.8X
96 hr
96 hr
Effect
2X teratic
surviving larvae
5X teratic
surviving larvae
18X teratic
surviving larvae
LC50
2X teratic
surviving larvae
2X teratic
surviving larvae
3X teratic
surviving larvae
6X teratic
surviving larvae
17X teratic
surviving larvae
100X abnormal
embryos
LC50
Concentration
(ua/Ll Reference
10,400 Birge et al.
1980
20,600 Blrge et al.
1980
33,900 Birge et al.
1980
>48,000 Birge et al.
1980
490 Birge et al.
1980
5,560 Birge et al.
1980
10.800 Birge et al.
1980
24,800 Birge et al.
1980
48,200 Blrge et al.
1980
8,000
Morgan et al.
1996
126,000 Morgan et al.
1996
-------
Table 6. (Continued)
10
Species
African clawed frog
(embryo),
Xenopus, laevls
Stream mixed
algal species
Experimental stream
perphyton community
Chemical
40.8X
80X
Hardness
(mg/L as
CaCO.)
-
Duratjon
96 hr
1 day to 3
weeks
Effect
LOEC
(teratogenesls)
39-78X reduction
In gross
productivity
Concentration
(un/L)
1,100
10
Reference
Morgan et al.
1996
Kosinskl et al.
1983; Kosinskl
and Merkle 1984
SOX
14 days
Stream mixed
community
Technical
164-202 30 days
Experimental laboratory
stream community
96.5
2 weeks
Stream mixed
algal species
Stream Aufuuchs
community
80%
3 days
12 days
Severe population 1,000 KosIraki 1984
density reductions
in several
species; total
destruction of
Cladophora
glomerata
No effect upon -25 Lynch et al.
macroinvertebrate 1985
community
structure,
periphyton
production or
biomass, and
community P/R
ratio
Decreased diurnal 100 Malanchuk and
fluctuation and Kollig 1985
mean values for pH
and dissolved
oxygen; increased
nitrate nitrogen;
parameters rapidly
returned to
control levels
when treatment
ended
Reduced net
primary
productivity
100 Moorhead and
Kosinskl 1986
4X biomass 24 Krieger et al.
reduction at 10°C 1988
-------
Table 6. (Continued)
Species
Hardness
(mg/L as
Chemical CaCO.l Duration
Concentration
tua/Ll Reference
CJ
Stream Aufuuchs
community
Stream Aufwuchs
community
Stream Aufwuchs
community
Natural Stream Periphyton
community
Natural stream plankton
conmunity
Stream algal and benthic
invertebrate conmunity
98X
Commercial
product
90X
Artificial stream periphyton
conmunity
Pond microcosm,
(static system)
Pond microcosm,
(static system)
98. 2X
98.2X
12 days
12 days
12 days
24 hr
6 mo
14 days
24X biomass
reduction; 30X
chlorophyll a.
reduction at 25°C
47X biomass
reduction; 40X
chlorophyll a.
reduction at 10*C
31X biomass
reduction; 44X
chlorophyll a.
reduction at 2S*C
No effect upon
algal cell numbers
or biomass
Initial decrease
in phytoplankton
species (6 uks)
followed by a
recovery
No effect upon
attached algal
chlorophyll a
concentrations or
benthic
invertebrate
populations
24
134
134
Krleger et al.
1988
Krieger et al.
1988
Krleger et al.
1988
77.5 Jurgenson and
Hoagland 1990
"0.5 Lakshminarayana
et al. 1992
Gruessner and
Watzin 1996
30 days
7 days
12 days
Community •
photosynthesis
inhibited
No effect upon
diurnal oxygen
production
25-30X decreased
oxygen production
100
5.0
50
Pearson and
Crossland 1996
Brockway et al.
1984
Brockway et al.
1984
-------
Table 6. (Continued)
Hardness
(mg/L as
Species Chemical CaCq,) Duration
Pond microcosm, 98. 2X . - 7 days
(static system)
Pond microcosm, 98. 2X - 12 days
(static system)
Pond microcosm, 98. 2X - 12 days
(static system)
Freshwater microcosm - 7 wks
Periphyton-dominated microcosm 96. 5X - 1 day
Perlphyton-dominated microcosm 96. 5X - 14 days
Phy topi ank ton, zooplankton and - - 60 days
benthos microcosm
Phytoplankton, zooplankton and - 25 days
benthos microcosm
40-50X decreased
diurnal oxygen
production
90X decreased
diurnal oxygen
production
100X inhibition of
diurnal oxygen
production
No effects upon
species
composition of
phy topi ank ton,
zooplankton or
bent Me
macroinverte-
brates; slight
decrease in
photosynthetic
activity
77X decrease in
daily net
productivity
*75X decrease in
P/R ratio
Reduced "C
uptake/chlorophyl I
a ratio
Reduced net
primary
productivity
Concentration
(ua/L) Reference
100 Brockway et al.
1984
500 Brockway et al.
1984
5,000 Brockway et al.
1984
5.1 Van den Brink
1995
100 Kama (a and
Kollig 1985
100 Kama I a and
Kollig 1985
43.8 Stay et al. 1985
*50 Stay et al. 1985
-------
Table 6. (Continued)
Spectea
Pond mesocosn community
Chemical
Hardness
(mg/L as
CaCO.l
Duration
70 days
Pond mesocosn community
121 days
Pond mesocosm
community
41X
805 days
Pond mesocosm
community
41X
A years with
single annual
applications
Effect
Changes in
population
densities of
zooplankton
(rotifers,
crustaceans and
insect larvae)
Changes in
phytoplankton
community
composition;
increased rotifer
population
Reductions in
phytoplankton
production and
biomass,
macrophyte,
populations, and
populations of
benthic insect
grazers.
catesbiana
tadpoles, grass
carp and bluegills
Reduced
photosynthesis in
24 hr bioassays,
followed by
recovery in 20-day
bioassays and
long-term pond
studies
Concentration
tua/L)
200
Reference
Pelchl et al.
1984
10
20
Pelchl et al.
1985
deNoyelles et
al. 1982, 1989,
1994
20-500
deNoyelles and
Kettle 1985
-------
Table 6. (Continued)
Speclea
Pond nesocosm
community
Chemlca[
97X
Hardness
(mg/L as
CaCO.)
Duration
9-112 days
Pond mesocosm
community
97X
9-112 days
Effect
Significant
reductions of
herbivorous
benthic insect
species richness,
abundance, and
total insect
emergence (89X),
shift to earlier
emergence for some
herbivorous
species;
destabilization of
ecosystem
Significant
reductions of
herbivorous
benthic insect
species richness,
abundance, and
total insect
emergence (95X),
shift to earlier
emergence for some
herbivorous
species; reduced
species evenness;
destabilization of
ecosystem
Concentration
fun/Li
20"
Reference
Dewey 1986;
Dewey and
deNoyelles 1994;
100"
Dewey 1986;
Dewey and
deNoyelles 1994;
-------
Table 6. (Continued)
Speclea
Pond mesocosra
community
Chemical
97X
Hardness
(mg/L as
CaCO.1
Duration
9-112 days
Pond mesocosm community
40.8X
8 Hks
Pond mesocosm plankton community
Pond mesocosm plankton community
Pond mesocosm plankton community
Pond mesocosm plankton community
Effect
Significant
reductions of
herbivorous
benthic insect
species richness,
abundance, and
total insect
emergence (85X),
shift to earlier
emergence for some
herbivourous
species; reduced
species evenness;
destabillzation of
ecosystem
Altered macrophyte
community species
composition; no
effects upon
primary
productivity,
total plant
biomass,
zooplankton or
fish
Concentration
(ua/L) Reference
50CP Dewey 1986;
Dewey and de
Novellea 1994;
50 Fairchtld et al.
1994
2 mo
2 mo
2 mo
2 mo
No effect
Decreased 0,, pH
and conductivity
Decreased
phytoplankton
populations
Reduced peak egg
ratios in Daphnia
longispina and
elimination of
Polvarthra sp.
rotifers
5 Juttner et
1995
10 Juttner et
1995
182 Juttner et
1995
318 Juttner et
1995,
al.
al.
al.
al.
-------
Table 6. (Continued)
Species
Hardness
(mg/L as
Chemical CaCO.) Duration
Concentration
tua/l )
Reference
Pond microbial microcosm
community
Pond microbial microcosm
community
Pond microbial microcosm
community
Pond microbial microcosm
community
Pond microblel microcosm
community
Pond microbial microcosm
community
Phyto- and zooplankton
microcosm community
98.6X
98.6X
98.6X
98.6X
98.6X
98.6X
-70 21 days
•70 21 days
~70 21 days
'70 21 days
~70 21 days
"70 21 days
42 days
NOEC for 10
concentrations of
Mg, Ca and
dissolved oxygen
MATC for 17.9
concentrations of
Mg, Ca and
dissolved oxygen
LOEC for 32.0
concentrations of
Mg, Ca and
dissolved oxygen
NOEC for protozoan 110
colonization,
biomass protein,
chlorophyll a, and
potassium
concentration
MATC for protozoan 193
colonization,
biomass protein,
chlorophyll a, and .
potassium
concentration
LOEC 337
for protozoan
colonization,
biomass protein,
chlorophyll a and
potassium
concentration
No or little "15
effect upon net
primary
productivity, P/R
ratio, and pH
Pratt et al.
1988
Pratt et al.
1988
Pratt et al.
1988
Pratt et al.
1988
Pratt et al.
1988
Pratt et al.
1988
Stay et al. 1989
-------
Table 6. (Continued)
\D
Species
Phyto- and zooplankton
microcosm community
Experimental pond
community
Experimental pond
community
Experimental pond
comnunity
Experimental pond
community
Experimental pond
comnunity
Experimental pond
community
Experimental pond
community
Nixed pond community
Nixed pond community
Chemical
Hardness
(mg/L as
CaCO.l
99.2%
99. 2X
Duration
42 days
39 days after
treatment
43 days after
treatment
101 days after
treatment
177 days after
treatment
249 days after
treatment
259 days after
treatment
373 days after
treatment
4 months
4 months
Concentration
(ua/L) Reference
Reduced net
primary
productivity. P/R
ratio, and pH
EC50
<"C uptake)
EC50
("C uptake)
EC50
("C uptake)
EC50
("C uptake)
ECSO
("C uptake)
ECSO
("C uptake)
ECSO
("C uptake)
Elimination of
Lemna minor
population
Rapid succession
of algal species;
reduced
reproduction rate .
in Daphnia
Duticaria
•84
96
131
109
24
27
37
100
60-120
Stay et al.
Larsen et al
1986
Larsen et al
1986
Larsen et al
1986
Larsen et al
1986
Larsen et al,
1986
Larsen et al,
1986
Larsen et al,
1986
Gunkel 1983
60-120
Gunkel 1983
-------
Table 6. (Continued)
Soeciea
Pond mesocosm
community
Chemical
99X
Hardness
(mg/L as
CaCO.)
Duration
2yr
Pond mesocosm
community
99X
2yr
Pond mesocosm
conmunity
99X
2yr
Decreased green
algal species,
cell milters and
cladoceran
populations;
increased
cryptomonad cell
numbers
Decreased green
algal species,
cell numbers and
cladoceran
populations;
increased
cryptomonad cell
numbers
Decreased green
algal species,
cell numbers and
cladoceran
populations;
increased
cryptomonad cell
numbers
Concentration
lua/L) Reference
20 Neugebauer et
al. 1990
100
Neugebauer et
al. 1990
300
Neugebauer et
al. 1990
-------
Table 6. (Continued)
Spectea
Pond nesocosn
connuiity
Chemical
Reagent
grade
Hardness
(mg/L as
CaCO,)
Duration
2yr
Pond mesocosm
comnunity
Reagent
grade
2 yr
Effect
Atrazine applied
in Nay and June
each year resulted
in decreased
abundance of
Endochironomua
niaricans in June,
and of total
macroinverte-
brates in both Nay
and June, followed
by recovery in
July. Epiphytes
were decreased in
abundance in June,
followed by
recovery in July.
Detrltovore
abundance was
decreased in Nay,
followed by
recovery in June.
Generalists were
decreased in Nay
and June, followed
by recovery in
July.
Results were
similar to those
at 20 fig/L in Nay
and June. Caenis
sp. were signifi-
cantly increased
in July. In late
July, increases
occurred in
abundance of
CflfiOifi sp., total
macroinverte-
brates, detrito-
vores and
generalists.
Concentration
(ua/Lt
20
Reference
Muggins et al.
1994
100
Huggins et al.
1994
-------
Table 6. (Continued)
Species
Chemical
Hardness
(mg/L as
CaCO.)
Duration
Effect
Concentration
(ua/L) Reference
Pond mesocosra
community
Reagent
grade
2yr
K)
Nixed algae from pond
Lake limnocorral
community
Lake limnocorral
•community
Lake limnocorral
perlphyton community
Lake limnocorral
periphyton conmunity
80%
80%
BOX
BOX
>3 hr
34 days
9 weeks (2
applications 6
weeks apart)
SO days
230 days
Results were
similar to those
at 20 and 100 jtg/L
in Nay and June.
In early July,
Cfliota sp. were
significantly
reduced in abund-
ance, but not in
late July. In
late July, the
abundance of epi-
phytes decreased,
while the abund-
ance of total
macroinverte-
brates and
generalists
increased.
Increased
fluorescence rate
for photosystem II
Reduced periphyton
ash-free dry
weight
36-67X reduction
in chlorophyll a,
organic matter,
and total peri-
phyton algal
biomass
*50X reduction in
ash-free dry
weight
Reductions of ~60X
in biomass, ~22X
in cell nunbers,
and ~32X in number
of species
500 Huggins et at.
1994
10
Ruth 1996
80-HO Herman et al.
1986
80-140 Herman et al.
(first 1986
application);
'110-190
(second
'application)
80
80
Hamilton et al.
1987
Hamilton et al.
1987
-------
Table 6. (Continued)
Spectea
Lake limnocorral
periphyton community
Chemical
SOX
Hardness
(mg/L as
CflCQO.
Duratlon
56 days
Lake limnocorral
periphyton coimunlty
SOX
56 days
Lake limnocorral
connunity
SOX
Two exposures
35 days apart
Ul
Lake mesocosm plankton
conmunfty
18 days
Effect
Reductions of "SOX
In chlorophyll i,
~32X In blomass,
"14X In cell
numbers, and "33X
In number of
species
Reductions of ~55X
In chlorophyll a.,
~68X in blomass,
"19X in cell
numbers, and "48X
in number of
species
Different
phytoplankton
species assem-
blages for up to
114 days after
second applica-
tion; increased
Seechi disc
readings and
decreased levels
of dissolved
oxygen, chloro-
phyll, and organic
carbon; phyto-
plankton
communities were
similar by day
323.
Decreased
chlorphyll a,
dissolved oxygen,
nauplii, Daphnia,
Cyclops; increased
particutate organ-
ic carbon
Concentration
tua/L) Reference
140 Hamilton et at.
1987
1,560
Hamilton et al.
1987
100 (first
application);
155 (second
application)
Hamilton et al.
1988, 1989
Lampert et al.
1989
-------
Table 6. (Continued)
Specteg
Lake nesocosm plankton
comnunity
Chemical
Hardness
(rag/L as
CeflM
Duration
10 days47
Lake bacterial and algal species
in microcosm study
Lake mesocosm community
20 days
Lake mesocosm phytoplankton
community
Lake mesocosm phytoplankton
community
Lake mesocosm periphyton community
Lake mesocosm periphyton community
20 days
20 days
20 days
20 days
Effect
Decreased algal
ptiotosynthettc
production,
dissolved oxygen
and Oaohnia
population;
apparent recov-
eries after about
25 days
Decreased algal
population density
and decreased
"scope for change
In ascendance" of
community
No effect upon
tolerance to
atrazine by
phytoplankton and
periphyton
communities or
upon length of
Cladocera; minor
changes in species
composition,
POC/PON ratio and
chlorophyll
concentration
EC50
EC50
EC50
ECSO
Concentration
(ua/L) Reference
0.1
250
20
58
52
52
54
Lampert et al.
1989
Genoni 1992
Gustavson and
Uangberg 1995
Gustavson and
Uangberg 1995
Gustayson and
Uangberg 1995
Gustavson and
Uangberg 1995
Gustavson and
Uangberg 1995
-------
ui
Table 6. (Continued)
Specie?
Lake phytoplankton .
Lake phytoplankton
Lake phytoplankton
Stream periphyton community
Stream phytoplankton community
Wetland mesocosm community
Green alga,
Chlamvdomonas sp.
Green alga,
Chlorococcui) sp.
Green alga,
Chlorococcum sp.
Green alga,
Chlorococcui) sp.
Chemical
85.5X
85X
Technical
80. OX
Technical
Hardness
(mg/L as
CflCTJL
"
"
•
Duration
3 hr
3 hr
3 hr
< 4 hr
Spring season
9-27 days
Effect
EC50
(carbon
assimilation)
EC50
(phosphate
assimilation)
ECSO
(ammonium
assimilation)
LOEC
(chlorophyll a)
Reduction in
populations of
green algae
Decreased
periphyton gross
productivity;
increased
dissolved
nutrients
Concentration
Cwo/L)
. 100
14,000
>33,000
109
40.4
maximum
IS
Reference
Brown and Lean
1995
Brown and Lean
1995
Brown and Lean
1995
Day 1993
Caux and Kent
1995
Detenbeck et a I
1996
SALTWATER SPECIES,
30r
30
30
30
90 min
90 min
90 min
90 min
ECSO
(oxygen evolution)
ECSO
(oxygen evolution)
ECSO
(oxygen evolution)
EC100
60
100
400
400
Hoi lister &
Walsh, 1973
Walsh 1972
Walsh 1972
Walsh 1972
(oxygen evolution)
-------
Table 6. (Continued)
ON
•
Species
Green alga,
Chlorococcun sp.
Green alga,
Chlorococcun sp.
Green alga,
Chlorococcun sp.
Green alga,
Chlorococcun sp.
Green alga,
Chlorococcun sp.
Green alga,
Dunaliella tertolecta
Green alga,
Dunaliella tertolecta
Green alga,
Dunaliella tertolecta
Green alga,
Dunaliella tertolecta
Green alga,
Dunaliella tertolecta
Green alga,
Dunal iet la tertolecta
Green alga,
Dunaliella tertolecta
Green alga,
Dunaliella tertolecta
Green alga,
Dunaliella tertiolecta
Green alga,
Dunaliella tertiolecta
Chemical
80. OX
Technical
80.0
Technical
80. OX
Technical
80. OX
Technical
80.0X
Technical
80.0X
Technical
80.0X
-
97X
Hardness
(mg/L as
CaCO,)
30
30
30
30
30
30
30
30
30
30
30
30
30
30r
-
Duration
90 min
10 days
10 days
10 days
10 days
90 min
90 min
90 min
90 min
10 days
10 days
10 days
10 days
90 min
5 days
Effecl
EC 100
(oxygen evolution)
ECSO
(growth)
ECSO
(growth)
EC 100
(growth)
'EC100
(growth)
ECSO
(oxygen evolution)
ECSO
(oxygen evolution)
EC100
(oxygen evolution)
EC100
(oxygen evolution)
ECSO
(growth)
ECSO
(growth)
EC100
(growth)
EC100
(growth)
ECSO, oxygen
evolution
ECSO
(cell number)
Concentration
-------
Table 6. (Continued)
SPECIeft
Green alga,
Dunaliella tertiolecta
Green alga,
OunaUella tertiolecta
Green alga,
Dunallella. tertiolecta
Green alga,
DunaHella tertiolecta
Green alga,
Dunatiella tertiotecta
Green alga,
Dunaliella terfiole<;ta
Green alga,
Dunatiella bioculata
Green alga,
OunaUella biocutata
Green alga,
Dunaliella bioculata.
Green alga,
Platymonas, sp.
Green alga,
Chlorella sp.
Green al'ga,
MeochlorJB sp.
Green alga,
Chlorococcun sp.
Green alga,
Mannochlorta oculata
Chemical
97%
97%
97%
Technical
Technical
Technical
Hardness
(mg/L as
CaCO.) Duration
5 day exposure,
9 day recovery
5 day exposure,
9 day recovery
5 day exposure,
9 day recovery
15 min
15 min
96 hr
48 hr
48 hr
48 hr
30, 90 min
30r 90 min
30 90 min
30 90 min
15 7 days
Effejct
NOEC
(cell numbers)
Algistatic
concentration
Algicidal
concentration
EC50 (oxygen
evolution)
EC50
(complementary
area)
EC50
(cell number)
35% reduction in
growth
85% reduction In
growth
100% growth
inhibition
EC50, oxygen
evolution
EC50, oxygen
evolution
EC50, oxygen
evolution
EC50, oxygen
evolution
21% change in
doubling time
Concentration
(un/L)
< 100
1,450
> 3,200
270
37
132
216
3,240
21,570
102
143
82
80
50
Reference
Hughes 1986,
1988
Hughes 1986,
1988
Hughes 1986,
1988
Samson and
Popov Ic 1988
Samson and
Popov! c 1988
Gaggi et al.
1995
Felix et al.
1988
Felix et al.
1988
Felix et al.
1988
Hollister ft
Walsh, 1973
Hollister ft
Walsh, 1973
Hollister ft
Walsh, 1973
Hollister ft
Walsh, 1973
Ka lander et at,
1983- Mm/no «/-(.
et at.. 1986
-------
Table 6. (Continued)
00
Species
Green alga,
Mannochloris oculata
Green alga,
Mannochloris oculata
Green alga,
Mannochloris ocul-ata
Green alga,
Marmochloris oculata
Green alga,
Mannochloris oculata
Green atga,
Mannochloris oculata
Green alga,
Mannochloris oculata
Green alga,
Mannochloris
Green alga,
Mannochtorls oculata
Green alga,
Mannochloris oculata
Green alga,
Mannochlorls oculata
Chemical
Hardness
(mg/L as
CaCOil.
15
15
15
15
15
15
15
15
15
15
15
Duration
7 days
7 days
7 days
7 days
7 days
7 days
7 days
7 days
7 days
7 days
7 days
Effect
11X change in
doubling time
12X change in
doubling time
34X change in
doubling time
35X change in
doubling time
33X change in
doubling time
42X change in
doubling time
35X change in
doubling time
28X change in
doubling time
46X change in
doubling time
35X change in
doubling time
21X change in
doubling time
Concentration
fug/L)
50
50
50
50
50
50
50
50
100
100
100
Reference
Kalander et al.,
1983; Nayasich
et al., 1986
Kalander et al.,
1983; Nayasich
et al., 1986
(Calender et al.,
1983; Nayasich
et al., 1986
Kalander et al.,
1983; Nayasich
et al.. 1986
Kalander et al.,
1983; Nayasich
et al., 1986
Kalander et al.,
1983; Nayasich
et al., 1986
Kalander et al.,
1983; Nayasich
et al., 1986
Kalander et al.,
1983; Nayasich
et al., 1986
Kalander et at.,
1983; Nayasich
et al., 1986
Kalander et at.,
1983; Nayasich
et at., 1986
Kalander et al.,
1983; Nayasich
et al., 1986
-------
Table 6. (Continued)
Species
Green alga,
Nannochloris oculata
Green alga,
Mannochloris oculata
Green alga,
Mannochlorls oculata
Green alga,
Mannochloria oculata
Green alga,
Harmochlorls oculata
Green alga,
Mannochloris oculata
Green alga,
Mannochloris oculata
Diatom.
Thalassipsira fluviatilis
Diatom,
ThalassiesIra ftuviatilis
Diatom,
Thalassiosira fluviatiUq
Diatom,
Mitzschia sigma
Diatom,
Mitzschia sioma
Chemical
Hardness
(mg/L as
CaCO.)
15
15
IS
15
15
15
15
20
20
30
20
20
Duration
7 days
7 days
7 days
7 days
7 days
7 days
7 days
7 days
7 days
90 min
7 days
7 days
Effect
59X change in
doubling time
52% change in
doubling time
47X change in
doubling time
S7X change in
doubling time
56X change in
doubling time
54X change in
doubling time
change in doubling
time
Reduced
chlorophyll
Reduced cell
number and
photosynthesis
EC50, oxygen
evolution
Reduced
photosynthesis
Reduced
chlorophyll and
cell number
Concentration
fun/L)
100
100
100
100
100
100
15
220
2,200
110
220
2,200
Reference
(Calender et al.,
1983; Mayasich
et al., 1986
(Calender et al.,
1983; Mayasich
et al., 1986
(Calender et al.,
1983; Mayasich
et al., 1986
(Calender et al.,
1983; Mayasich
et al., 1986
(Calender et at.,
1983; Mayasich
et al., 1986
(Calender et al.,
9183; Nayaslch
et al., 1986
Mayasich et al.
1987
Plunley i Davis,
1980
Plunley I Davis,
1980
Hoi I liter t
Walsh, 1973
Plunley t Davis,
1980
Plunley ft Davis,
1980
-------
Table 6. (Continued)
M
to
O
Species
Diatom,
Mitischia cloflterium
Diatom,
Hltzschja (Ind. 684)
Diatom,
Mavicula Inserta
Diatom,
Amphora ex
-------
Table 6. (Continued)
Speclea
Diatom.
IsochrvBJs galbana
Of atom,
Isochrvsis galbana
Diatom,
Isochrvsis galbana
Diatom,
Isochrvsis galbana
Diatom,
Isochrvsis gatbana
Diatom,
Isochrvsis gaibana
Diatom,
Phaeodactyliin tricornutun
Diatom,
Phaeodactvlim tricornutun
Diatom,
PhaeodactylUM tricornutum
Diatom,
Phaeodactvlun tricornutun
Diatom,
Phaeodactvlum tricornutum
Diatom,
Phacodactvltm tricornuttm
Diatom,
Phaeodactvlum tricornutum
Diatom,
Phaeodactylum tricornutun
Red alga,
Porphvridium cruentum
Hardness
(mg/L as
Chemical
80. OX
Technical
80. OX
Technical
80.0X
-
Technical
80. OX
Technical
80. OX
Technical
80. OX
Technical
80.0X
.
CaCO.)
30
30
30
30
30
30
30
30
30
30
30
30
30
30
30
Duratlo)
90 min
10 days
10 days
10 days
10 days
90 min
90 min
90 min
90 min
90 min
10 days
10 days
10 days
10 days
90 min
Concentration
lua/L) Reference
EC100
(oxygen evolution)
ECSO
(growth)
EC50
(growth)
EC100
(growth)
EC100
(growth)
ECSO, oxygen
evolution
ECSO
(oxygen evolution)
ECSO
(oxygen evolution)
EC100
(oxygen evolution)
EC100
(oxygen evolution)
ECSO
(growth)
ECSO
(growth)
EC100
(growth)
EC100
(growth)
ECSO, oxygen
evolution
500
100
100
200
200
100
100
200
200
600
200
200
500
500
79
Walsh 1972
Walsh 1972
Walsh 1972
Walsh 1972
Walsh 1972
HoiI later ft
Walsh, 1973
Walsh 1972
Walsh 1972
Walsh 1972
Walsh 1972
Walsh 1972
Walsh 1972
Walsh 1972
Walsh 1972
Hoilister ft
Walsh, 1973
-------
Table 6. (Continued)
H
K>
to
SpecIeg
Kelp.
Lamlnarla hvperborea
Kelp,
Laminaria saccharine
Kelp,
Lamlnarla saccharina
Kelp.
Laminaria hvperborea
Redheadgrass pondweed,
Potamogeton perfoHatus
Redheadgrass pondweed,
Potamogeton perfollatua
Euraisian watermflfoil,
Mvrlophvtliin spicatun
Aquatic vascular plant,
zarmlchellla palustrls
Widgeon grass,
Ruppla maritima
Vallisneria,
Vallisneria amerlcana
Vallisneria,
Valllsneria americana
Vallisneria,
Vallisneria amerlcana
Hardness
(mg/L as
Chemical CaCO.) Duration
70X
70X
99.7X
Effect
Concentration
lua/L) Reference
-
30
30
-
10
8-12
8-12
8-12
8-12
5
3
6
28 days
2 days
2 days
24 hours
4 hours
2 hours
2 hours
2 hours
2 hours
47 days
42 days
42 days
LOEC growth of new
sporophytes
No effect on
sexual
reproduction
66X reduction in
fertilization
LOEC respiration
ICSO
photosynthesis
ICSO
photosynthesis
ICSO
photosynthesis
ICSO
photosynthesis
ICSO
photosynthesis
67X reduction in
leaf production I
76X reduction in
leaf area
47X decrease in
growth as length,
and 48X decrease
as dry weight
27X decrease in
growth as length,
and 30X decrease
10 Hopkins t Kain.
1971
33.2 Thursby ft
Tagllabue 1990
72.2 Thursby &
Tagliabue 1990
> 1,000 Hopkins & Kain,
1971
80 Jones et al.,
1986
77 Jones I
Winched, 1984
104 Jones t
Winchell, 1984
91 Jones I
Winchell, 1984
120 Jones t
Winchell, 1984
12 Cornell & Wu,
1982
100 Forney, 1980;
Forney & Davis,
1981
100 Forney, 1980;
Forney & Davis,
1981
as dry weight
-------
Table 6. (Continued)
H
K)
U
Spectea
vallisneria,
vallisneria amerlcana
Valtisnerla,
ValHsnerla americana
Eelgrass,
Zostera marina
Eelgrass,
Zostera marina
Eelgrass,
Zostera marina
Turtlegrass,
Thalassla testudinun
Salt-marsh grass,
Soartina alternlflora
Salt-march grass,
Spartina atterniflora
Salt-marsh rush,
juncus roemerlanua
Chemical
-
•
97. 2X
Technical,
99.7X
97. IX
97. IX
Hardness
(mg/L as
CaCO.l Duration
3 42 days
6 42 days
24 hours
24 hours
14 10 days
30 40 hours
35 days
35 days
flfsti
27X decreased in
growth as length,
and 41X decrease
as dry weight
32X decrease in
growth as length,
and 29X decrease
as dry weight
Reduced net oxygen
evolution
No net oxygen
evolution
100X growth
inhibition
EC50
(photosynthesis)
Increased
peroxidase
activity
No effect upon
shoot growth,
Concentration
(uo/L)
320
320
100
1,000
1,900
320
30
3,100
Reference
Forney, 1980;
Forney ft Davis,
1981
Forney, 1980;
Forney ft Davis,
1981
Kemp et at.,
1981
Kemp et al.,
1981
Schwarzschlld et
al. 1994
Walsh et al.,
1982
Lytle ft Lytle
1998
Lytle ft Lytle
1988
97. IX
35 days
lipid peroxidation
products or
chlorophyll
production.
Enhanced
peroxidase
activity
Reduced chlorphyll
a; Increased
peroxidase
activity and lipid
peroxidation
products
30 Lytle ft Lytle
1998
-------
Table 6. (Continued)
to
Species
Salt-marsh rush,
June us roemerianua
Eastern oyster (juvenile),
Crassostrea virainica
Copepod,
Acartia tonsa
Copepod,
Acartia tonsa
Copepod,
Acartia tonsa
Brown shrimp (juvenile),
Penaeua attecus
Brown shrimp,
Penaeus aitecus
Brown shrimp,
Penaeus aztecus
Spot (juvenile),
Leiostomas santhurua
Fiddler crab (field),
Uca puanax
Chemical
97. IX
Technical,
99.7X
97. IX
97. IX
97. IX
Technical,
99.7X
-.
-
Technical,
99.7X
SOX
Hardness
(mg/L as
CaCO.) Duration
35 days
28 96 hours
30-34 72 hours
30-34 48 hours
30-34 24 hours
30 48 hours
24 hours
48 hours
29 48 hours
70 days
Effect
Reduced shoot
growth,
chlorophyll a.
chlorophyll b;
increased lipid
peroxldation
products
EC50
(shell growth)
LC50
LC50
LC50
EC50
20X mortality
30X mortality
LC50
No effect on
number per m1
after a single
application
Concentration
tua/L)
3,800
>1,000
6.100
8.400
15,000
1,000
1,000
1,000
>1,000
1,000,000
Reference
Lytle I Lytle
1998
Butler, 1965;
Mayer, 1987
McNamara, 1991
McNamara, 1991
HcNamara, 1991
Mayer, 1987
Butler, 1965
Butler, 1965
Butler, 1965;
Mayer. 1987
Plumley et al.,
1980
Fiddler crab (field).
UcA puqnax
SOX
70 days
94X reduction in
nunfcer per m2
relative to
control after a
single application
10,000.000 Plumley et al.,
1980
-------
Table 6. (Continued)
Species
Hardness
(mg/L as
Chemical CaCO.) Duration
Effect
Concentration
(UQ/L> Reference
Fiddler crab.
llca puanax
(animals collected in August)
SOX
20
8 days
to
in
Fiddler crab,
Uca puanax
(animals collected in August
1977)
Fiddler crab,
Uca pugnax
(animals collected in November)
Fiddler crab,
Uca puonax
(animals collected in March)
Fiddler crab,
Uca puonax
(animals collected in August 1978)
Fiddler crab,
Uca puanax
(animals collected in August 1978)
Fiddler crab,
Uca puonax
(animals collected in August 1978)
Fiddler crab,
Uca ptianax
(animals collected in August 1978)
80X
80X
SOX
80X
80X
SOX
SOX
20 8 days
20
20
20
20
20
20
30 days
9 days
9 days
9 days
9 days
9 days
2SX mortality of
large males;
100X mortality of
large females;
100X mortality of
small males;
75X mortality of
small females
SOX mortality of
large males;
100X mortality of
large females;
7SX mortality of
small males,
SOX mortality of
small females
No effect on
survival of small
males
No effect on
survival of small
males
60X mortality
90X mortality
BOX mortality
90X mortality
100,000 Plunley et al.,
1980
1,000,000 Plunley et al.,
1980
1,000,000 Plunley et al.,
1980
1.000.000 Plunley et al.,
1980
100,000 Plunley et at.,
1980
180,000 Plunley et al.,
1980
320,000 Plunley et al.,
1980
560,000 Ptumley et al.,
1980
-------
Table 6. (Continued)
to
Species
Fiddler crab,
Uca puonax
(animals collected in August 1978)
Fiddler crab,
UCfl puanax
(animals collected in August 1978)
Drift line crab (field).
Sesarma clnereum
Hud crab (field).
panopeus sp.
Mesocosm,
Nixed marine phytoplankton
Chemical
BOX
80%
SOX
SOX
Residue
grade
Hardness
(mg/L as
CaOM
20
20
-
Duration
9 days
9 days
70 days
70 days
90X mortality
100X mortality
No effect on
number per m2
after a single
application
No effect on
number per of
after a single
application
Concentration
(ua/L)
1,000,000
10,000,000
10,000,000
10,000,000
Reference
Plunley et al.,
1980
Plumley et al.,
1980
Plumley et al.,
1980
Plumley et al.,
1980
15 days
Reduced pH,
particulate
carbohydrates,
chlorophyll,
photosynthesis,
primary
production;
increased
dissolved organic
phosphorus,
dissolved organic
nitrogen, and
dissolved amino
acids
0.12 Bester et al.
1995
-------
Table 6. (Continued)
Species
Mesocosn,
Mixed marine phytoplankton
Chemical
Residue
grade
Hardness
(mg/L as
CaCO.)
Duration
15 days
Mesocosm,
Nixed marine phytoplankton
Residue
grade
15 days
M
•-J
Effect
Reduced pH,
particulate
carbohydrates,
chlorophyll,
photosynthesis,
primary
production;
increased
dissolved organic
phosphorus,
dissolved organic
nitrogen, and
dissolved amino
acids
Reduced pH,
particulate
carbohydrates,
chlorophyll,
photosynthesis,
primary
production;
increased
dissolved organic
phosphorus,
dissolved organic
nitrogen, and
dissolved amino
acids
Concentration
fno/L) Reference
0.56
Bester et al.
1995
5.80
Bester et al.
1995
-------
Table 6. (Continued)
H
K>
CO
Species
Chemical
Hardness
(mg/L as
CaCO.)
Duration
Effect
Concentration
fuu/L) Reference
Test was run using a Taub and Dollar medium.
Test Has run using an algal assay medium (U.S. EPA 1971).
Only 2.3 to 4.7 percent of this concentration remained on day 7.
Nephelometric determination.
Cultured from sample collected in Osage Spring, Clayton County, Iowa.
Cultured from sample collected in Big Spring, Clayton County, Iowa.
Test performed with an atrazfne-sensitive strain.
Test performed uith an atrazine-resistant strain
Algae were pre-conditioned for 4 days uith 531 ng/i. of atrazine.
Cotorlmetric determination.
Test performed with water from microcosm 30 days after atrazine had been introduced.
Test performed directly with atrazine in water without a microcosm exposure.
EC50 obtained using an algal assay medium.
ECSO obtained using creek water as the test mediun.
Animals were fed at 24 hr.
Two single annual applications at nominal concentration indicated.
Atrazine concentrations were below detection after 10 days; however, the study continued for 42 days.
Salinity in g/L,
-------
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