WATER POLLUTION CONTROL RESEARCH SERIES • 18050GWV05/71
Water Quality Criteria Data Book
Volume 3
Effects of Chemicals on Aquatic Life
ENVIRONMENTAL PROTECTION AGENCY RESEARCH AND MONITORING
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WATER POLLUTION CONTROL RESEARCH SERIES
The Water Pollution Control Research Series describes
the results and progress in the control and abatement
of pollution in our Nation's waters. They provide a
central source of information on the research, develop-
ment, and demonstration activities in the Environmental
Protection Agency, through inhouse research and grants
and contracts with Federal, State, and local agencies,
research institutions, and industrial organizations „
Inquiries pertaining to Water Pollution Control Research
Reports should be directed to the Chief, Publications
Branch, Research Information Division, R&M, Environmental
protection Agency, Washington, B.C. 20^60.
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Water Quality Criteria Data Book - Vol. 3
EFFECTS OF CHEMICALS ON AQUATIC LIFE
Selected Data From the Literature Through 1968
by
Battelle's Columbus Laboratories
for the
ENVIRONMENTAL PROTECTION AGENCY
Project No. 18050 GWV
Contract No. 68-01-0007
May 1971
For sale by the Superintendent of Documents, U.S. Government Printing Office, Washington, D.C. 20402 - Price $3.75
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EPA Review Notice
This report has been reviewed by the Environmental Protection Agency
and approved for publication. The data are listed as reported in the
literature without collaboration or evaluation of their validity. Therefore,
these data must and cannot be used indiscriminately for the establishment
of water quality criteria for the aquatic environment. These data should be
used only as a guideline for the base of action. Approval does not signify
that the contents necessarily reflect the views and policies of EPA, nor
does mention of trade names or commercial products constitute endorse-
ment or recommendation for use.
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ABSTRACT
Original data from more than 500 technical publications concerning the specific effects of
chemicals on individual species of aquatic biota were collected and summarized in uniform
format. Alphabetical assembly of the data by chemical allows rapid access to considerable
detailed information. A Species Index facilitates search for information on the toxicity of
chemicals to individual aquatic species.
The details of major procedures in laboratory bioassay and field assessment of chemical
toxicity in water are discussed. Freshwater and marine procedures are included. A total of
approximately 1000 references were utilized in preparing this report.
Recommendations include:
(1) Establishment of an information-analysis center on chemical water pollution based
to some extent on the report prepared.
(2) Preparation of a listing of chemical constituents of effluents and continued
up-dating of this list.
(3) Development of a pattern of bioassays for evaluating the effects of a chemical on
aquatic life. Data from these evaluations would be used in developing
mathematical models for predicting chemical toxicity in a wide range of
environmental circumstances.
(4) Development of in situ bioassay procedures for more realistic assessment of
chemical toxicity to aquatic life.
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TABLE OF CONTENTS
Section
I Introduction 1
II Objectives 4
III Literature Search and Bibliographies 5
IV Fish Bioassay 6
V Bioassay of Aquatic Organisms Other Than Fish 18
VI Biochemical Oxygen Demand (BOD) and Related Microbiological
Procedures 19
VII Marine Bioassay 25
VIII Field Assessment 26
IX Factors Affecting Chemical Toxicity in Water 43
X Industrial Wastes 55
XI Extracted Data - The Effect of Chemicals on Aquatic Biota 63
XII Summary and Conclusions 66
XIII Recommendations 69
XIV Bibliography 70
XV Appendices
A. Chemicals and Mixtures of Chemicals A-l
B. Commercial Chemical Products B-l
C. Species Index C-l
D. Identification of Commercial Chemicals D-l
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LIST OF FIGURES
Figure
1 Food Web in Western Lake Erie Leading to the Sheepshead Fish
Page
27
VI
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LIST OF TABLES
Table Page
1 Fish Used in Bioassays, Frequency of Use, and Type of Water
in Which They Occur 12
2 Laboratory Methods for Studying the Effect of Chemicals on
Fish Other Than Bioassay Lethality 15
3 A Partial Listing of References Using Freshwater Aquatic Organisms
Other Than Fish for Bioassay 18
4 Toxicity of Various Compounds as Determined by BOD 23
5 Collecting Equipment in Common Usage in Limnological Studies
and the General Purpose for Which Each is Used 34
6 Partial Listing of Organisms Commonly Associated With Pollution 35
7 Thermal Death Points of Fish Acclimized at the Indicated Tempera-
tures (Freshwater = F, Marine — Atlantic = A, Pacific = P) 45
8 Minimum Oxygen Values at Various Temperatures at Which Fish
Can Exist Under Laboratory Conditions 51
9 Usual Fisheries Hazards of 30 Common Types of Municipal and
Industrial Effluents 56
10 General Comments on Selected Industrial Effluents 57
Vll
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SECTION I
INTRODUCTION
The internal and external chemical environment of an organism determines whether that
organism will survive, grow, and perpetuate itself. Internal chemical balance is mediated by the
genetic makeup of the organism, the external chemical milieu in which it lives, and all other
environmental factors. The effect of chemicals on living organisms is an especially important
factor in aquatic environs where organisms are in intimate contact with chemicals in solution and
suspension. Water passes into and through the body of an organism primarily via the integument,
membranes, gills, or mouth. Toxic chemicals in the water may cause immediate lethality
although in many instances sublethal quantities of deleterious chemicals may be accumulated
within the body. In time, the chemical residues in an organism may cause drastic effects of
varying types, also including mortality. Complicating this situation is the effect of chemicals on
lower animal forms which provide part or all of the food chain leading to higher aquatic
organisms. Thus, sport fish may leave polluted areas not to avoid chemical pollutants or to
escape death but rather to seek food, for example, when bottom fauna upon which they feed are
obliterated. Low dissolved-oxygen concentrations in water caused by release of oxygen-
consuming chemicals can also have equally drastic impact on aquatic organisms.
This then is the basic problem today in water pollution and is the primary subject of this
report. A closely related problem, considering aquatic biota as indicators of chemical toxic
effect, is the consideration of whether or not such water is safe for use by humans. At the
moment fish bioassay appears to be the best method available for determining the toxic effect of
chemicals on aquatic life.
In a report section entitled "Recommendations for the Use of Bioassays and Application
Factors to Denote Safe Concentrations of Wastes in Receiving Streams", the National Technical
Advisory Committee (Interim Report, 1967), has made the following recommendations in part
for the use of bioassays:
"1. For the determination of acute toxicities, flow-through bioassay s are the first
choice. Methods for carrying out these flow-through tests have been described by
Surber and Thatcher, 1962; Lemke and Mount, 1963; Henderson and Pickering, 1963;
Jackson and Brungs, 1966; Mount and Warner, 1963; Mount and Brungs, 1965; and
Brungs and Mount, 1967. Flow-through bioassays should be used for unstable volatile
or highly toxic wastes and those having an oxygen demand. They also must be used
when several variables such as pH, DO, CO2 and other factors must be controlled.
2. When flow-through tests are not feasible, tests of a different type or duration must
be used. The kinds of local conditions affecting the procedure might be single
application of pesticides or lack of materials and equipment.
3. Acute static bioassays with fish for the determination of TLm values should be
carried out in accordance with Standard Methods for the Examination of Water and
Waste Water. Such tests should be used for the determination of TLm values only for
persistent, nonvolatile, highly soluble materials of low toxicity which do not have an
oxygen demand as it is necessary to use the amount added as the concentration to
which the test organisms are exposed.
4. When application factors are used with TLm values to determine safe concentrations
of a waste in a receiving water, the bioassay studies to determine TLm values should
1
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be made with the most sensitive local species and life stages of economic or ecological
importance and with dilution water taken from the receiving stream above the waste
outfall. In the absence of knowledge concerning the most sensitive of the important
local species or life stages or due to difficulty in providing them in sufficient numbers,
other species whose relative sensitivity is known can be used or tests may be carried
out using one species of diatom, one species of an invertebrate and two species of fish,
one of which should be a pan or game fish. Further, these bioassays must be
performed with environmental conditions at levels at which the waste is most toxic.
Tests should be repeated with one species at least monthly and when there are changes
in the character or volume of the waste.
5. Concentration of materials with noncumulative toxic effects should not exceed 1/10
of the 96-hour TLm value at any time or place. The 24-hour average of the concentra-
tion should not exceed 1/20 of the TLm value. For toxicants with cumulative effects,
the concentrations should not exceed 1/10 and 1/100 for the above respective values."
The need for water of better quality by improved pollution control has been chronicled
broadly with considerable justification in news media, scientific journals, and government reports.
The result of this attention has been the establishment of water quality criteria and federal
requirements for states, localities, and consequently industries to set minimum water standards
within certain time limits, and to enforce these standards. The basic Federal Water Pollution
Control Act (1956) was provided and later amended in 1961, by the Water Quality Act of 1965,
and by the Clean Water Restoration Act of 1966. In the years given, these amendments were
approved as public laws. Water quality requirements are becoming more stringent each year.
Carpenter (1968) has outlined federal policy and organization in regard to this problem. In Water
Quality Criteria (1968), the various problems of water pollution control are discussed in detail
and recommendations are made for measures to improve pollution management. Earlier, these
and related problems were discussed in publications by the National Research Council (1966),
the Department of Health, Education, and Welfare (Public Health Service Publication No.
999-WP-25, 1965), ORSANCO (Ohio River Valley Water Sanitation Commission, 1967), and the
Environmental Pollution Panel (1965). Establishment of water quality criteria in the U.S. has
been recently considered by the Aquatic Life Advisory Committee (1955, 1956, 1960), the
American Society for Testing Materials (Katz and Woelke, 1967; Woelke, 1967), Bartsh and
Ingram (1959, 1966), Carter (1968), Ettinger and Mount (1967), Okum (1968), Smith (1961),
Tarzwell (1957, 1959, 1962), Weston (1964), and Wilhm and Dorris (1968). The Manufacturing
Chemists Association (1967) listed the sources of information on water quality criteria. The
number of meetings increases each year as announced in such periodicals as Water and Sewage
Works. The problems of industrial water utilization and effluent management of chemical wastes
are generally discussed by Bower (1965), Cairns (1965, 1967), in Public Works (Anonymous,
1968), and in various texts, as well as briefly in the section of this report entitled "Industrial
Wastes". Engdahl and Croxton (1962) have discussed the economics of pollution, a matter
further treated in such journals as Chemical Week and Chemical and Engineering News.
Eutrophication of lakes is a special pollution problem that is not discussed in this report.
Excellent documents pertaining to eutrophication are by Fruh, et al (1966) and bibliographies
by the U.S. Public Health Service (Mackenthun, 1962, 1965). Similarly, thermal effluents were
not considered as a topic for this report, due primarily to the magnitude of research in this field.
Useful, extensive bibliographies have been recently published, including ones by the American
Society for Civil Engineering (1967), Kennedy and Mihurksy (1967), Raney and Menzel (1967),
and Wurtz and Renn (1965).
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Another special problem is pesticide contamination of the environment. This is discussed to
a considerable extent throughout this report, but especially in the section "Field Assessments".
Reviews or general references concerning the effect of pesticides in the environment or other
agricultural problems of this nature include an article in Environmental Sciences and Technology
(Anonymous, 1968); papers by Cottam (1961), Langer (1964), Moore (1967), and Robinson
(1967); and periodicals such as Residue Reviews (Springer-Verlag New York Inc., Vol 1+, 1962+)
and Pesticides Documentation Bulletin (U.S. Department of Agriculture, Vol 1+, 1965+).
Other useful reference sources on trends in water pollution control are the chemical
industry trade journals, Chemical Week and Chemical and Engineering News, and such publica-
tions as the Conservation Foundation Letter, and the Environmental Health Letter (Vol 1+,
1961+).
This is something of the background in which this report was prepared in late 1968 and
early 1969.
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SECTION H
OBJECTIVES
The objectives of this program were to:
(1) Collect and summarize in standardized format the available information from the
scientific literature concerning:
(a) The specific effects of chemicals on individual species of aquatic biota. (This
study was limited to studies of single chemicals or simple mixtures of
chemicals and does not include industrial effluents that contain highly
complex chemical mixtures.)
(b) Details of the procedures and environmental factors important in the
observation or the measurement of these effects.
(2) Review the existing information on aquatic life as it is applicable or related to the
study of water pollution.
(3) Review the methodology used in studying the effects of chemicals on aquatic life.
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SECTION III
LITERATURE SEARCH AND BIBLIOGRAPHIES
Some 3500 papers, mostly from the period 1950 through 1968, were screened and about
2000 obtained for direct examination. Foreign language publications were not included. About
500 contained original data, from which extracts were prepared (Appendices A and B). An
attempt was made to be comprehensive for the years 1958 through 1968 with only selected
references included preceding this period. Of these selected references, the majority were
published after 1950, with only a few being from the older literature.
The primary source for identifying the references used in this study were the literature
reviews published annually by the Water Pollution Control Federation Committee in the Journal
of the Water Pollution Control Federation (1958-1968), which proved to be excellent. The
reference list was checked against Chemical Abstracts, Biological Abstracts, Water Pollution
Abstracts, and numerous recent special subject bibliographies. Very few additional references
were added to the list from these other sources. Personal visits were made to selected govern-
mental and industrial organizations to secure pertinent data. Information was also requested from
the Science Information Exchange (Smithsonian Institution) and National Referral Center
(Library of Congress). Letter requests for publications not commonly available were sent to a
number of scientists in this field.
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SECTION IV
FISH BIOASSAY
Fish bioassay of industrial wastes and other potentially toxic materials has evolved in the
past 50 or so years from nonstandardized procedures by individual scientists to the present
where standardized assay procedures now are available to researchers in this field. Early work on
fish bioassays was done in Europe and Asia nearly 60 years ago. Pioneering work in the U.S. on
developing procedures and methods for bioassay of fish was conducted by Shelford, Bilding,
Carpenter, and Ellis. In 1945, Hart, Doudoroff, and Greenbank in a book now out of print
described a standardized fish bioassay procedure, which Doudoroff, et al (1951) recommended as
a standard method for use by industry, government agencies, and others. This method with
comparatively few modifications, e.g., continuous flow exposure of fish in addition to static
exposure, has been widely used and today is used more or less in its original form. The fish
bioassay procedure outlined in the 12th edition of Standard Methods (American Public Health
Association, 1967) is basically that described by Doudoroff, et al. Procedures developed by W. E.
Martin of the Pesticides Regulation Division and by Burdick (1960) at the N.Y. Conservation
Department are quite similar. A prepublication copy of fish bioassay procedures that is to appear
in the forthcoming 13th edition of Standard Methods (1971) was kindly provided by Professor
M. C. Rand. The following discussions are based primarily on this document.
Static Bioassay
Briefly, the static bioassay procedure can be described as follows:
(1) After determination of an approximate toxic range of a chemical or effluent,
appropriate concentrations are prepared on a logarithmic or geometric scale within
the toxic range.
(2) Small (5.0-7.5 cm) fish, which have been quarantined 10-30 days (min-max) to
assure no disease problems and acclimatized to the chosen assay water, are placed
in the chemical or effluent solutions prepared with dissolved oxygen in concentra-
tions not less than 4 mg/1 (warm water fish) and 5 mg/1 (cold water fish) at a
constant temperature. Temperatures of 25 ± 2 C and 15 ± 2 C are recommended
for warm water and cold water species, respectively.
(3) Observation and recording are made of dead fish which should be removed at 8,
24, 48, and 96 hours after the assay is initiated. Notation of other effects, such as
intoxication, distress, loss of equilibrium, and other abnormal behavior, should
also be-made.
(4) Calculation or estimation of a TLso or TLm for various time periods is made by
interpolation of the data plotted on semilogarithmic coordinate paper.
The TLm of a compound is not considered as representing the concentration of a chemical
or effluent that is safe in fish habitats. It is merely a relative measure of the acute, lethal
toxicity of the material to a certain fish under controlled environmental conditions and must be
used with a mathematical application factor to determine safe concentrations of effluents to be
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released. This has been discussed by Doudoroff (1951), Warren and Doudoroff (1958), and the
National Technical Advisory Committee (1967).
A further distinction between LDso, LCso, and ECso is made in the prepublication copy
of Standard Methods as follows:
"The expressions 'lethal dose' (LD) and 'lethal concentration' (LC) have also been
frequently used, the term 'lethal dose' often incorrectly. The expression 'lethal dose' is
not appropriate when designating a certain concentration in an external medium,
inasmuch as a dose, strictly speaking, is a measured quantity administered. Unlike
'lethal dose' and 'lethal concentration', the term 'tolerance limit' is universally
applicable in designating a level of any measurable lethal agent, including high and low
temperatures, pH, and the like. The expression 'effective concentration' (EC) applies to
concentrations only and is generally used in connection with effects other than death."
The APHA procedure describes in excellent detail the selection and preparation of fish and
diluent water, effluent samplings or preparation-dilution of test substances, use of aeration,
controls, etc.
Static, acute fish bioassay has been shown to be inadequate for estimating the effect of
chemicals on fish. Lack of reproducibility between laboratories is the rule rather than the
exception. Reasons for this include chemical and microbiological degradation of toxic com-
pounds, volatility of some compounds, utilization of oxygen by microorganisms as well as by
fish, water quality variability, accumulation of fish metabolic by-products in assay containers,
and uptake of toxicants by the test animals.
Periodic (daily or more often) renewal of test solutions is a variation of the static, acute
fish bioassay that can be utilized to overcome some of the objections of this type of evaluation.
Continuous test solution renewal must be used in long-term, chronic exposures of fish to
chemical solutions where sublethal effects are to be studied. This variation is recommended in
the Standard Method especially "when there is evidence or expectation of a rapid change of
toxicity of the test solution".
Also recommended in the procedure is the determination of temperature, DO, and pH of
the samples under evaluation at various times during the experiment as well as of the chemical
properties or dissolved mineral content of the diluent water. To quote, "A rather complete
mineral analysis of the water is advisable". Furthermore, chemical analysis for the toxicant under
study is suggested throughout the exposure period. Seldom is this type of information reported
in the literature as is shown and discussed in subsequent sections of this report.
The U.S. Fish and Wildlife Service, Circular 185 (1964) describes static bioassay procedures
in relation to piscicide studies being carried out by the U.S. Bureau of Sport Fisheries and
Wildlife. Freeman (1953) discussed use of standardized diluent water in static bioassay of fish
and aquatic invertebrates. Other authors have also discussed or used synthetic or defined water
for bioassays (Cairns and Scheier, 1955, 1958, 1963, 1968; Doudoroff, 1956; Dowden and
Bennett, 1965; Fitzgerald et al, 1952; Trama, 1955; and Whitley, 1968). Handling and
maintenance of bioassay fish was described by Hunn, et al (1968). A number of authors have
discussed mathematical treatment of fish toxicity data including Burdick (1957) and Henderson
and Tarzwell (1957). Excellent general discussions of static fish bioassays have been published by
Burdick (1960, 1967), Cairns (1957, 1966), McCall (1961), Tarzwell (1959), Wuhrmann and
Woker (1959), and Wuhrman (1955).
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Cope (1961) suggested standards for reporting fish toxicity tests which apparently have not
been accepted widely. Essentially his appeal dealt with correct identification, size, and condition
of the test fish; complete description of the procedure involved and of chemical, physical, and
biological factors; volume of water and number of fish for that volume; etc. Many of these data
are lacking in most of the papers reviewed in the present report.
Continuous Flow Bioassay
The majority of the factors discussed under static bioassay apply to the continuous flow
procedure with the added requirement of automatic intermittent or continual metering of the
test substance dissolved or suspended in diluent water into the test chambers and continuous
flow-through of water. Problems associated with dissolved oxygen and test chemical content in
static exposures can be obviated in the continuous flow technique since the water added contains
these materials in constant concentrations.
Briefly, a continuous flow system is composed of:
(1) Diluent water reservoir from which water flows into the
(2) Constant head diluent supply where the water is cooled or heated to the desired
temperature and then metered along with
(3) The effluent or toxicant (added with a chemical pump, Mariotte bottle, etc.) into
(4) The test container in which fish are exposed, and which
(5) Overflows into an appropriate drain.
An acclimatizing tank for test fish can also receive water from the reservoir and constant
head diluent supply. Water flow is by gravity and the recommended flow rate is equal to a
complete volume change of test containers in 6 hours.
Data are taken usually over a 5-day period and plotted as for the static bioassay. Five-day
supplies of water and toxicant are required.
The procedure as it is outlined allows ample latitude for assembling the apparatus according
to individual requirements. As guides, the work of Jackson and Brungs (1966), Surber and
Thatcher (1963), Lemke and Mount (1963), Mount and Warner (1965), and Mount and Brungs
(1967), and others are referred to. These reports deal in part with information concerning valve
control systems,, chemical metering pumps, serial dilution apparatus, and the proportional diluter
as utilized in various types of studies.
The earliest paper found on continuous flow bioassay was by Merkens (1957), a British
scientist, who devised an automatically controlled apparatus for monitoring and adjusting temper-
ature, pH, dissolved oxygen, and toxicant concentration in the test water added. This system was
ingenious for its time.
Alabaster and Abram (1965) have more recently described British continuous flow tech-
niques. Flow rate is adjusted to maintain an adequate level of dissolved oxygen. The apparatus
and treatment of data are described in considerable detail.
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Other recent procedures or innovations on the continuous flow technique have been
reported by Betts, et al (1967), Burke and Ferguson (1968), Grenier (1960), Hendersen and
Pickering (1963), and Solon, et al (1968).
The use of the continuous flow procedure in chronic exposures (Mount, 1962, 1968;
Mount and Stephan, 1967), piscicide development (Parker and Wurth, 1965), residue accumula-
tion (Holden, 1966), tracer studies (Holden, 1962), spawning (Mount and Stephan, 1967), and
avoidance (Foster, 1967; and Warner et al, 1966) is discussed in other sections of this report.
Burdick (1960, 1967) and Jackson and Brungs (1966) have thoroughly discussed the
continuous flow technique and its applicability to current water pollution problems. There can
be no doubt that continuous flow fish bioassay simulates the field situation more closely than
does static bioassay.
Fish Selection
The selection of fish for bioassay depends in part on the species of appropriate size
available for study that can be maintained in the laboratory and also on the native fish present
in the receiving water under study. Lennon (1967) has recommended development of inbred
strains of test fish for standard reference in much the same manner as inbred mouse strains are
used in mammalian toxicology. Cope (1966) has also made similar recommendations.
Small, preferably juvenile, fish are generally used so that sufficient numbers may be
accommodated in the laboratory. Mount (1968) has briefly listed fish species that might be used
as appropriate test organisms. This listing was prepared at the National Water Quality Labora-
tory, Duluth, Minnesota. The fish were selected on the basis of the following criteria:
(1) Sport, commercial or forage value
(2) Potential for exposure to pollution
(3) Geographical distribution and abundance
(4) Suitability for laboratory studies
(5) Existing knowledge in regard to toxicity.
The fish selected were:
Primary list — all pollutants
Threadfin shad (Dorosoma petenense)
Brook trout (Salvelinus fontinalis)
Rainbow trout (Salmo gairdneri)
Northern pike (Esox Indus)
Emerald shiner (Notropis atherinoides)
Fathead minnow (Pimephales promelas)
White sucker (Catostomus commersoni)
Channel catfish (Ictalurus punctatus)
White bass (Roccus chrysops)
Bluegill (Lepomis macrochirus)
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Largemouth bass (Micropterus salmoides)
Yellow perch (Perca flavescens)
Special list — for selected pollutants
Coho salmon (Oncorhynchus kisutch)
Lake trout (Salvelinus namaycush)
Mountain whitefish (Prosopium williamsoni)
American smelt (Osmerus mordax)
Smallmouth bass (Micropterus dolomieui)
Walleye (Stizostedion vitreum)
The goldfish (Carassius auratus) was the selected equivalent of the "white rat".
Hunn, et al (1968) list the bioassay species used by the Bureau of Sport Fisheries and
Wildlife as follows:
Rainbow trout (Salmo gairdneri)
Brown trout (Salmo trutta)
Brook trout (Salvelinus fontinalis)
Lake trout (Salvelinus namaycush)
Northern pike (Esox lucius)
Goldfish (Carassius auratus)
Carp (Cyprinus carpio)
Fathead minnow (Pimephales promelas)
White sucker (Catostomus commersoni)
Black bullhead (Ictalurus melas)
Channel catfish (Ictalurus punctatus)
Green sunfish (Lepomis cyanellus)
Bluegill (Lepomis macrochirus)
Smallmouth bass (Micropterus dolomieui)
Largemouth bass (Micropterus salmoides)
Yellow perch (Perca flavescens)
Walleye (Stizostedion vitreum)
Henderson and Pickering (1963) state that many species are suitable for bioassays,
including:
Guppy (Lebistes reticulatus)
Mosquito fish (Gambusia affinis)
Goldfish (Carassius auratus)
Fathead minnow (Pimephales promelas)
Bluegill (Lepomis macrochirus)
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On the basis of research usage as determined by the papers reviewed in the present study,
an even wider variety of fish has been used experimentally. These, along with their frequency of
use and type of water in which they may be found, are summarized in Table 1. Only those
found in more than one paper are listed.
Chronic Bioassay
Evaluation of sublethal concentrations of various chemicals in long-term fish exposures is
probably the most reliable bioassay method for determining safe levels at which chemicals may
be released into receiving water. The exposure may be either static in which periodic solution
renewal is required or continuous flow in which the concentration of the chemical is maintained
at a constant level. The latter is by far the method of choice. Both procedures have been
discussed in previous sections.
Chronic Static Exposure
A few recent papers serve to illustrate the variations that may be employed in conducting
this type of exposure. The long-term effect of a 2-hour exposure to Dieldrin on the reproduction
of guppies (Lebistes reticulatus) was studied by Hubble and Reiff (1967) over a 12-month
period. The fish were placed in a standardized water following the exposure. No harmful effect
on reproduction was observed.
Weiss and Gakstatter (1964) studied the long-term effect of various pesticides on acetyl-
cholinesterase activity of bluegill, golden shiner, and goldfish by daily replenishing the test
solutions over periods up to 30 days. The pesticides studied could be detected at concentration
levels down to 0.1 x 10~3 mg/1.
Test water containing subacute concentrations of copper or zinc was used by Grande (1967)
to expose trout eggs, fry, and fingerlings. The test solutions were renewed during 28-day periods
every second day in experiments with eggs and daily for young trout.
The effect of sublethal concentrations of Dieldrin on laboratory populations of guppies
(Poecilia reticulata) in aquaria was studied by Cairns, et al (1967). Weekly renewal of test
solutions over a 14-month period was employed.
Dugan (1967) studied the combined effects of sublethal concentrations of detergents and
pesticides on goldfish. The test water was cleaned by filtering periodically and the chemical
concentrations adjusted to desired levels. Four-month exposure periods to the surfactants and up
to 51-day exposure periods to Dieldrin were studied. Synthetic water and 100-gal epoxy-coated,
galvanized water tanks were used.
In a study of the effect of Diquat on bluegill and bluegill food organisms, Gilderhus (1967)
exposed the animals to the chemical during a 24-week period with varied frequencies of sublethal
concentrations.
None of these authors used the static, acute fish bioassay procedure outlined in Standard
Methods.
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TABLE 1. FISH USED IN B10ASSAYS, FREQUENCY OF USE, AND TYPE OF WATER
IN WHICH THEY OCCUR
(Freshwater = F; Marine - Atlantic = A, Pacific = P)
Scientific Name
Abramis brama
Ambloplites rupesnis
Ameiurus nebulosus
Brachydanio rerio
Campostoma anomalum
Carassius auratus*
C. carassius
Catastomus commersoni*
Cyprinodon variegatus
Cyprinus carpio*
Ericymba buccata
Esox lucius
Eucalia inconstans
Fundulus similis
Gambusia af finis*
Gasterosteus aculeatus*
Gobio gobio
Hyborhynchus notatus
Ictalurus melas*
I. natalis*
I. nebulosus*
I. punctatus*
Lagodon rhomboides
Lebistes reticulatus*
Leiostomus xanthurus
Lepomis auritus
L. cyanellus*
L. gibbosus*
L. macrochirus**
L. megffloris
L. microlophus*
Micropterus dolomieui*
M. salmoides*
Mugil cephalus
Notemigonus crysoleucas*
Notropis atherinoides
N. cornutus
N. hudsonius
N. lutrensis
N. stramineus
N. umbratilis
Oncorhyncus kisutch*
O. tshawytscha*
Perca flavescens*
Petromyion marinus*
Phoxinus phoxinus*
Pimeptwles notatus*
P. promelas**
Rhinichthys atratulus
Rurilus rurilus
Salmo gairdneri**
S. salar*
S. trutta*
Salvelinus fontinalis*
S. namaycush
Semotilus atromaculatus*
Sti2ostedion vitreum*
Common Name
Bream
Rock bass
Brown bullhead
Zebrafish
Stoneroller
Goldfish
European carp
White sucker
Longnose killifish
Carp
Silverjaw minnow
Northern pike
Brook stickleback
Striped mullet
Mosquitofish
Threespine stickleback
Gobie
Bluntnose minnow
Black bullhead
Yellow bullhead
Brown bullhead
Channel catfish
Pinfish
Guppy
Spot
Redbreast sunfish
Green sunfish
Pumpkinseed
Bluegill
Longear sunfish
Redear sunfish
Smallmouth bass
Largemouth bass
Striped mullet
Golden shiner
Emerald shiner
Common shiner
Spottail shiner
Red shiner
Sand shiner
Redfin shiner
Coho salmon
Chinook salmon
Yellow perch
Sea lamprey
Red-sided shiner
Bluntnose minnow
Fathead minnow
Blacknose dace
Roach
Rainbow trout
Atlantic salmon
Brown trout
Brook trout
Lake trout
Creek chub
Walleye
Occurrence
F
F
F
F
F
F
F
F
A
F
F
F
F
A
A-F
A-F-P
F
F
F
F
F
F
A
F
A
F
F
F
F
F
F
F
F
A
F
F
F
F
F
F
F
P-F
P-F
F
A-F
F
F
F
F
F
A-F-P
A-F
A-F
A-F
F
F
F
All species listed were lound in two or more papers.
•Found in more than 5 papers.
"The most common!) used species.
12
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Chronic Continuous Flow Exposure
Brown, et al (1968), Butler (1965, 1967), Cairns and Scheier (1963), Cope (1965), Jensen
and Gaufin (1966), Mount (1962, 1968), Mount and Stephan (1967), Olsen and Foster (1958),
Raymont and Shields (1964), Surber and Thatcher (1963), and Weiss (1965) have utilized
continuous flow techniques of their own creation for the study of a variety of aquatic organisms
in long-term, continuous flow exposure to a variety of chemicals. Exposure periods up to 11
months were employed in these studies. The reports cited above represent less than 5 percent of
the total number of papers from which data were extracted for Appendices A and B.
Generally, chemicals are toxic at lower concentrations in continuous flow exposures,
especially long-term ones, than in static exposures. Furthermore, nonlethal effects occur more
readily in continuous flow bioassays. For example, Mount (1968) reported for this type of
bioassay that the "safe concentration" was 3-7 percent of the 96-hour TLm (static exposure) in
studying the chronic toxicity of copper to fathead minnows. Furthermore, Mount and Stephan
(1967) have stated that the biologically safe concentrations for Malathion and butoxyethanol
ester of 2,4-D as determined in a continuous flow, chronic study are 1/45 and 1/9, respectively,
of the 96-hour TLm for each of these compounds as determined in static bioassay. However,
Cairns and Scheier (1963) found in a study of the acute and chronic effects of sodium alkyl
benzene sulfonate on sunfish that results from the two types of exposure at equivalent
concentrations of ABS were quite close although not identical.
As further requirements to improve water quality are imposed, the need for chronic
continuous flow data concerning the effects of sublethal concentrations of potential pollutants
on aquatic biota will increase.
In situ Bioassay
The need for standardizing fish bioassay laboratory procedures has led to environmental
laboratory conditions unlike those found in streams and lakes. Factors such as fluctuating
sunlight, temperature, DO, pH, pollutant and nutrient concentration, etc., cannot be taken into
account or compensated for in the laboratory. In situ evaluation of a chemical solution in the
stream or body of water in which it is to be released is a method of determining with an
improved degree of accuracy the concentration effects of a discharge released into that particular
body of water. Exposures to the chemical in question of native species of fish can be conducted
by means of portable live cars, cages, plastic pools, or raceways. Thus, the fish species of concern
for a given stream can be studied in conditions approaching their particular complex ecological
situation.
There is no standard procedure for this type of bioassay, but it has been employed to some
extent as briefly discussed later in the section, "Field Studies". Burdick (1967) has recom-
mended this approach and pointed out that automated water quality monitoring equipment now
available can provide continuous recording of physical and chemical changes in water conditions
which may allow correlation of bioassay data with ecological conditions. Raceways with
disposable vinyl liners are used in advanced evaluation of piscicides as well as 9-10-ft-diameter
vinyl wading pools with bottom soils of various types, pond or ground waters, aquatic plants and
invertebrates, fish, and amphibians, as required. Hawskley (1967) speculated on the advent of
"continuous bioassay" in which effluent and receiving water in varied ratios will be circulated
into and out of test containers and noted that this almost of necessity will have to be performed
at the plant site. Standard method fish bioassays are conducted in this laboratory in conjunction
13
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with routine chemical analyses and analyses with an atomic absorption spectrophotometer.
Hawkins stated that a mobile unit for conducting fish bioassays and chemical analyses at the
plant site was in the design stage in 1964. A mobile bioassay unit was used in developing
selective larvicides for control of sea lamprey (Howell and Marquette, 1963). Automatic water
quality monitors can provide continuous and depth-profile data acquisition for water tempera-
ture, dissolved oxygen, pH, conductance, dissolved chlorides, oxidation-reduction potential, and
turbidity. These parameters are indirect but excellent physical-chemical indicators of water
pollution. In conjunction with fish bioassays, they can provide data suitable for mathematical
modeling and simulation. More than 200 monitors of this type are now in operation in the
United States. The monitor can be housed in a trailer for portability. Weather data recording for
air temperature, solar radiation, wind speed and direction, and total precipitation can be
integrated into the continuous recorder.
Fish Responses Other Than Bioassay Lethality
Methods for laboratory study of fish response to chemicals in freshwater environments vary
nearly as much as the number of investigators in this field of research. These range from simple
observations (as suggested in Standard Methods and other sources); to sophisticated determina-
tions of chemical residues, ACHE blood content, etc.; to the highly sophisticated Conditioned
Avoidance Response Apparatus (CARA). These methods are identified in Table 2. One of these
procedures may become a "standard method" for aquatic laboratory studies, but this does not
appear likely to occur in the near future. Standard static and continuous flow fish bioassay
methods will probably remain the principal laboratory tools for developing toxicity data with
chronic exposures becoming more widely used. Some of the methods, notably, the avoidance,
life stage, fish tissue culture, and CARA techniques, may be very useful in determining more
precisely the "safe concentration" levels for chemical effluent release. Texts, such as those by
Brown (1957) describe physiological methods for studying fish. Some of these methods would be
highly applicable to the study of the effect of chemicals on aquatic life and could form the basis
for the development of new procedures.
14
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TABLE 2. LABORATORY METHODS FOR STUDYING THE EFFECT OF CHEMICALS
ON FISH OTHER THAN BIOASSAY LETHALITY
Type
Comments
References
Observations of abnormal
behavior
Autopsy and histology
Avoidance
Growth retardation
Residue analysis
Observations may be made on the following:
Quiescence, excitability, or irritability
Surfacing or sounding
Tetanic or flaccid movement
Swimming - erratic, convulsive, gyrating,
inverted on side, etc.
Changes in pigmentation
External mucosa — exudate, shedding, etc.
Integument hemorrhagia
Rate of respiration - slow, irregular, gulping,
etc.
Gill hemorrhaging or mucous discharge
Defecating or regurgitating mucous or other
material
Sensitivity to stimuli such as light, sound,
touch, electric probe, etc.
Moribundity — distended operculum,
opaque eyes, etc.
Recovery — complete, or not.
Tissue and organ pathology are studied by
appropriate methods. Decrease of glycogen
and RNA, tissue dissociation, necrosis,
lesions, and secretions may also be noted.
Raceways or similar laboratory structures are
generally used so that a chemical solution can
be metered into the bioassay water to estab-
lish a concentration gradient. Fish have been
trained to discriminate between very low con-
centrations of selected chemicals.
Chronic exposure was the most effective tech-
nique utilized.
Following exposure, organs of the fish are
removed and analyzed for specific chemical
content. This technique is used most often
in studies of pesticide accumulation, and is
also quite useful in field studies to show
previous exposure. Whole fish homogenates
have also been analyzed as well as animal
feeds and processed sea foods prepared
from various types of marine fish species.
Brown, et al (1968), Cairns,
etal( 1967), Cope (1966),
Fromm and Schiffman
(1958), Grindley (1946),
Mount (1962), and Olsen
and Foster (1958)
Blumenkratz (1956), Cairns
(1966), Cairns and Scheier
(1963), Cope (1965), Eng.
Science, Inc. (1964), Gilderhus
(1967), Herbert and Shurben
(1964), Mount (1964), Mount
and Stephen (1967), Van Valin,
et al (1968), and Warner, et al
(1966)
Cairns (1957), Costa (1965),
Hasler and Wisby (1949),
and Ishio (1965)
Crandall and Goodnight
(1962), Olsen and Foster
(1958), and Royer (1966)
Butler (1965,1967), Cope
(1965), Eisler (1967),
Gilderhus (1966,1967),
Godsil and Johnson (1968),
Holden (1966), Mahdi
(1956), Moubry, et al (1968),
Mount (1962), Mount and
Stephan (1967), Pagan and
Hageman (1950), Ullman,
etal (1961), Weiss (1965),
and Welch and Spindler
(1964)
15
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TABLE 2. (Continued)
Type
Comments
References
Acetylcholinesterase (ACHE)
activity of brain
Radiotracers
Effects on various life
stages offish
Spawning (reproductive
behavior)
Swimming or cruising speed
and oxygen consumption
while swimming
Chemical resistance offish
This method is used primarily in the study of
organophosphorus pesticides in both labora-
tory and field studies of freshwater and
marine types. The utility of this method is
somewhat limited because of its near
specificity for organophosphates.
This technique is used primarily in the study of
pesticides and metal ions where labelling can
be successfully accomplished. Tissue and
organ analyses of radiotracer accumulation
have been conducted. Among the radio-
isotopes used in fish studies are Ca^S, C^,
P32, and Zn35. Acetates, chlorides, Bayer
22408, DDT, Dieldrin, Dimethoate,
Lindane and Parathion are some of the com-
pounds studied in this manner. Wet com-
bustion of tissues and measurement of
C 14(32 release has also been employed.
Effects of chemicals on sperm, eggs, yearling,
and adult fish as well as fry are often studied
to determine the relative resistance of these
life stages to chemicals. Embryos from
fertilized eggs have also been studied with the
finding that fertilized egg membranes provide
some resistance to the effects of chemicals.
This may be studied in the laboratory by pro-
viding suitable objects, such as pieces of
cement-asbestos tile; and proper environ-
mental conditions, including a controlled
photoperiod, for this activity. Spawning in
several studies was shown to be affected by
concentrations of chemical much lower than
those for the TLm (96 hr). A "Laboratory
Fish Production Index" (LFPI) has been
proposed and is gaining acceptance.
Specifically designed raceways, cages, or
"current trays" are required to determine
rate of speed. Oxygen utilization can be
determined by means of an oxygen-
consumption chamber or respirometer. This
is a useful technique for studying fish larger
than fry. Current velocity can be controlled
and is an important factor in studying large
fish which require sufficient speed for
oxygen transfer in their gills.
After sublethal exposure, fish acquire specific
resistance to certain chemicals. This has been
demonstrated in the laboratory and the field
most frequently for pesticides and metals.
Butler (1965), Cope (1965),
Fromm and Schiffman
(1958), Weiss (1959,1961,
1964,1965), and Weiss and
Gakstatter(1964)
Butler (1965), Douglas and
Irwin (1963), Fujiya (1965),
Gakstatter and Weiss
(1967), Holden (1962),
Joyner (1961), Marchetti
(1965), Miller, etal (1966),
and Schmidt and Weidhaas
(1961)
Cairns and Scheier (1959),
Cope (1966), Crandall and
Goodnight (1962), Goodman
(1951), Grande (1967),
Hiltibran (1967), Marchetti
(1965), Mount (1968),
Piavis (1962), and Skidmore
(1966)
Cairns, et al (1967), Cohen,
etal (1961), Gilderhus
(1967), Holden (1966),
Hubble and Reiff( 1967),
Mount (1962, 1968), and
Mount and Stephan (1967)
Cairns and Scheier (1963),
Doudoroff and Warren
(1962), Herbert and Shurben
(1963), Mount (1962), and
Ogilvie and Anderson (1965)
Boyd and Ferguson (1964),
Darsie and Corriden (1959),
Fairchild (1955), Ferguson,
etal(1954, 1955), and
Mount (1968)
16
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TABLE 2. (Continued)
Type
Comments
References
Blood studies
Glucose transport
Fish tissue culture
Environmental stress
Thermal acclimatization
Fish taste
Conditioned avoidance
response apparatus (CARA)
Changes in erythrocyte count, hemoglobin,
sodium and calcium levels, microhematocrit,
and hematocrit have been used in a variety of
studies. The latter has been suggested as a
measure of the state of health of bioassay
fish prior to testing.
This is an in vitro type of study using dissected
fish gut.
Epithelial cells of fathead minnow cultured on
modified Eagle's MEM medium, were found
to have a reduced mitotic index at the calcu-
lated "safe concentration" of zinc. It was
concluded that one-tenth of the 96-hr TLm
is probably closer to the safe concentration.
Reduced DO or increased temperature caused
increased toxicity of various chemicals.
In studies of the effect of DDT on salmon, it
was found that DDT interferes with the
normal thermal acclimation mechanism.
Fish exposed to 10 ppm DDT and acclimated
to warm water were extremely sensitive to
cold water. Acclimatization also affected
chemical toxicity.
The taste of sport fish can be drastically
changed by chemical pollutants.
Toxicant-induced behavior of fish exposed to
sublethal concentrations of chemicals was
studied in raceways by means of photo-
graphing the fish at various intervals and
calculating response in terms of relative
position. A large mirror facilitated photog-
raphy. At concentration levels 1/2000 of
the 96-hr TLm value for tetraethyl pyro-
phosphate (TEPP), aberrant behavior of
goldfish was noted. A ratio of 1/25 was
obtained for Toxaphene.
Cairns and Scheier (1963),
Cope (1965,1966),
Gilderhus (1967), Hatch
(1957), and Hunn, et al
(1968)
Stokes and Fromm (1965)
Rachlin and Perlmutter
(1968)
Cairns (1957), Lloyd (1961),
and Pickering (1968)
Cope (1963, Keenleyside (1958),
and Greer and Paim (1968)
Hynes (1966) and Rachlin
and Perlmutter (1968)
Eng. Science, Inc. (1964) and
Warner, etal( 1966)
17
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SECTION V
BIOASSAY OF AQUATIC ORGANISMS OTHER THAN FISH
Surprisingly few aquatic orgamsms other than fish have been used as test organisms in
bioassays. The orgamsms most commonly used are numerous species of algae and the
crustaceans, Daphnia magna and D. pulex. Other freshwater mvertebrates used in bioassays
include protozoa (Paramecium and Tetrahymena), planaria (Planaria and ^>>™*^
(Gammarus), gastropods (Lymnaea and Physa). stonefly and mayfly naiads andI caddisfly and
midge larvae. Oysters and shrimp are the principal test animals other than fish in marine
bioassays. The oyster (Ostrea) are quite sensitive to low concentrations of some chemicals as
determined by retarded shell growth. The brown, pink, and white shrimp (Penaeus) are the most
commonly used Crustacea in seawater bioassays. Barnacles (Balanus) are also used. These are
discussed in the section, Marine Bioassay. Table 3 is a listing of references using various
organisms other than fish for freshwater bioassay studies.
Procedures developed by C. M. Palmer and T. E. Maloney (1955) at the Taft Engineering
Center in Cincinnati, Ohio, and by G. P. Fitzgerald, et al (1952, 1958, 1963) are widely used for
laboratory study of freshwater algae.
There are no generally accepted or standard procedures for bioassays using these other types
of organisms, although the procedures developed by Bertil Anderson (1944, 1945, 1948, 1960)
in his studies of D. magna are commonly used.
In evaluating papers from which data were extracted (Appendices A and B), it was evident
that a much broader spectrum of species are studied in the field than under laboratory conditions.
TABLE 3. A PARTIAL LISTING OF REFERENCES USING FRESHWATER AQUATIC ORGANISMS
OTHER THAN FISH FOR BIOASSAY
Type References
Algae: Abram (1967), Alabaster and Swain (1963), Beak (1958), Elson and
(Chlorella pyrenoidosa, Kerswffl (1967), Ganelin, et al (1964), Holden (1964), Hopkins,
Microcystis aeruginosa, et al (1966), Kallman, et al (1962), Kemp, et al (1966), Khan
and numerous other species) (1964), Merkens (1958), Nejedly (1967), Palmer and Maloney
(1955), and Sprague, et al (1965)
Invertebrates: Abram (1967), Anderson (1946), Burdick (1965), Cairns, et al (1965),
(Daphnia magna, D. pulex, Chadwick (1960), Clarke (1947), Fromm (1965), Gaufin (1961),
Gammarus pulex, Culex spp, Gaufin, et al (1961), Henderson, et al (1961), Ingols (1959), Kabler
etc.) (1957), Naylor (1965), Shaw and Grushkin (1967), Sprague (1965),
Tarzwell (1957), Tarzwell and Henderson (1960), Turnbull, et al
(1954), Weiss and Botts (1957), Wilber (1965), Williams (1964),
and Wood (1957)
Vertebrates: Cairns, et al (1965), Lackey (1957), Shaw and Grushkin (1967), and
(Raiw pipiens, R. catesbieana, Stroud (1967)
Bufo valliceps - sperm, eggs,
tadpoles, and adults)
18
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SECTION VI
BIOCHEMICAL OXYGEN DEMAND (BOD) AND RELATED
MICROBIOLOGICAL PROCEDURES
Biochemical Oxygen Demand
The biochemical oxygen demand (BOD) test is a test which is designed to determine the relative
oxygen requirement of a municipal and/or industrial effluent. The determination of BOD of an
effluent for the purpose of regulating the rate of discharge into a stream or sewerage system with
minimal adverse effects on the oxygen resources of the receiving water will be at best an analytical
starting point. BOD has several very limiting criteria which must be adequately understood for this
technique of possible waste dilution to be useful. The procedure for BOD determinations as de-
scribed in the 13th Edition of the Standard Methods for the Examination of Water and Waste Water
(American Public Health Association, 1967) provides the basis for this discussion. This procedure
has been essentially the same for more than 10 years with comparatively minor changes.
Although basically a simple bioassay to execute, the exceptions and precautions given in the
BOD procedure make it somewhat formidable to the uninitiated. Briefly without specific details,
the procedure consists of:
(1) Microbial seeding (if needed) of appropriate water dilutions of the chemical or
effluent and initial determination of the dissolved oxygen (DO) of the sample by
the iodometric method, azide modification. Sample dilutions are prepared with
distilled water saturated with dissolved oxygen and buffered at pH 7.2 with a
phosphate buffer solution.
(2) Incubation of the seeded samples at 20 C for 5 days and in darkness in standard
BOD bottles which are water-sealed to exclude oxygen.
(3) DO determination of the diluted samples after the 5-day incubation period. The
most reliable results are said to be for that dilution which shows a residual DO of
at least 1 mg/1 and a depletion of at least 2 mg/1. For toxic chemicals or
effluents, toxic effect is indicated by lack of oxygen utilization by the micro-
organisms. When the lag period for microbial growth is prolonged, incubation
periods of up to 20 days or longer may be employed.
(4) When substances are evaluated that are oxidizable by molecular oxygen, then an
immediate dissolved oxygen demand (IDOD) should be determined and taken into
consideration when calculating the BOD. The IDOD is a short-term assay in which
DO is determined 15 minutes after the sample is added to the dilution water.
Carbon compounds utilizable by aerobic microorganisms, oxidizable nitrogen compounds
utilizable by nitrogen bacteria, and certain chemical reducing compounds (ferrous iron, sulfites,
sulfides, and aldehydes) are the three main types of chemicals that influence oxygen demand.
The latter can be taken into consideration by the IDOD determination. Solubility and volatility
of chemicals must also be considered. Some organic wastes are not oxidizable and thus are not
amenable to the BOD bioassay. When such wastes are suspected, chemical oxygen demand (COD)
and total carbon (TC) analyses would be conducted for comparison with BOD results.
According to the procedure: "In many cases, particularly in food processing wastes, a
satisfactory seed may be obtained by using the supernatant liquor from domestic sewage which
19
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has been stored at 20 C for 24-36 hr", but it goes on to state that "acclimated" seed and
receiving water below a point (2-5 miles) of effluent discharge may be used since "many
industrial wastes contain compounds which are not amenable to oxidation by domestic-sewage
seed". If the concern is with dissolved oxygen depletion, then an "acclimated" seed would seem
most appropriate whether it is acclimated in the laboratory or collected downstream from a
discharge. If the concern is with the toxic level of an effluent, then both acclimated and
domestic-sewage seed evaluations might be made to establish a type of index for safe discharge.
In the event of evaluation of a new type of discharge, seed acclimated in the laboratory to that
particular discharge undoubtedly would be most desirable.
In regard to the amount of seed to be added, it is stated that, "Only past experience can
determine the actual amount of seed to be added per liter." It would be more precise to add
exact amounts of seed, e.g., Zintgraff, et al (1968) added 0.5-2.0 mg/1 of seed in their studies.
The BOD bioassay suffers as do most laboratory procedures from lack of correlation
between laboratory results and those obtained in the field. The need for a standardized
procedure is recognized, but many factors enter into the behavior of a chemical in the aquatic
environment that cannot be taken into account in the laboratory. Some of these objectionable
features are alluded to and briefly discussed in Standard Methods, but others are overlooked and
should be considered in attempting to apply the results of BOD determinations. The principal
uncontrolled variable in the BOD procedure is the nonstandardized microbial inoculum or
acclimated microbial seed as the case may be. Briefly, other factors include:
(1) Temperature and pH — seldom is the aquatic environment at precisely one
temperature or pH.
(2) Fluctuating solids and dissolved solids content in receiving water — these can
greatly influence the effect of a chemical on aquatic biota.
(3) Algae — although BOD determinations are conducted in a dark incubator, algae
can grow heterotrophically and utilize oxygen, as do bacteria and other micro-
organisms. Dead algal cells can also affect BOD. Wisniewski (1958) has dis-
cussed the effect of algae on BOD determinations and DO in streams.
(4) Protozoa — these are known to be present in domestic sewage seed, and according
to Bhatla, et al (1965) protozoa are responsible for approximately 30 percent of
the BOD exerted under normal seeding conditions in 5-day BOD tests.
(5) Total aquatic biomass — all plants and animals other than the ones discussed
above significantly influence the effect of chemicals on the aquatic environment.
(6) Mixed nutrient substrates — these are the rule rather than the exception in
receiving water.
(7) Mixed toxicants in sublethal concentrations already present in receiving water —
this problem has received comparatively little attention as judged by reports in
the literature. Exceptions in non-BOD studies are the pesticides where the effect
or accumulation of mixtures of these compounds and their decomposition
products on and in aquatic biota have been documented. Additive, antagonistic,
or synergistic effects probably do occur.
(8) Photochemical oxidation by ultraviolet from sunlight.
20
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(9) Mixing due to currents — the BOD laboratory assay is static and therefore no
mixing occurs.
(10) Other factors briefly mentioned in various papers as important in oxygen deple-
tion are reduction of nitrates, anaerobic microbial alteration of organic com-
pounds, secondary oxygen uptake, and decomposition of chemical intermediates.
All of these factors should be recognized by the analyst who should take them into account
when applying data from BOD determinations.
BOD can be utilized to advantage by an experienced researcher in determining the oxygen
depletion potential or the effect on microorganisms of an effluent containing toxic chemicals.
Both are important considerations in effluent management for minimal effect on receiving
waters.
On studying the various papers concerned with reporting BOD data, it was found that a
wide variety of methods for reporting the data are utilized. As examples, Ingols (1954, 1955,
1956) plotted BOD values to show oxygen depletion in percent of control BOD with increasing
concentrations of mercuric chloride, copper, zinc, etc., in ppm. Oberton and Stack (1957) using
acclimated seed in studying the BOD of acrolein, diethanolamine, and methyl vinyl ketone
reported their results as observed BOD in percentage of theoretical oxygen demand plotted with
days of incubation. Randall (1966) reports the effect of acclimated seed on the pesticides,
Malathion and Parathion, in terms of net oxygen utilization and time in hours. In an article
entitled "The BOD of Textile Chemicals, Updated List — 1966", the data presented on nearly
400 chemicals and commercial chemical products are given as percent of 5-day BOD (Anon.,
1966). In another paper (Anon., 1958), data for mercuric chloride, sulfuric acid, formaldehyde,
and phenol are presented as the median toxic concentration in mg/1, i.e., the concentration at
which 50 percent inhibition of oxygen utilization occurred; Zintgraff, et al (1968) reported BOD
data using acclimated and nonacclimated seed for potassium cyanide in molar concentrations
plotted against oxygen uptake in ppm or with time in hours. Rudolfs, et al (1950) reviewed the
literature in 1950 on toxic materials affecting sewage treatment processes, streams, and BOD
determinations and made general statements concerning this subject but with scant tabular
material.
Since such a variety of methods for presenting data are found in the BOD literature, no
attempt has been made to summarize BOD results in this report. The reader is referred to the
various articles cited for information pertinent to his own interests, and to the summaries of
chemical data shown in Appendixes A and B.
Herman (1959) proposed a toxicity index based on BOD data. Depending on the BOD
curves obtained (percent available oxygen utilized plotted against concentration in mg/1), a series
of "toxigrams" (Types 1 through 5) were devised, which were:
Toxigram Type 1 — simple poisons (the curve drops at toxic concentrations)
Toxigram Type 2 — no effect (the "curve" is flat)
Toxigram Type 3 — immediate dissolved oxygen demand (IDOD) by reducing
substances (the curve rises to 100 percent oxygen utilization at higher concentrations)
Toxigram Type 4 — oxygen demand at low concentrations, inhibition of oxygen
utilization at relatively high concentrations (the curve rises at low concentrations and
drops at toxic levels)
21
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Toxigram Type 5 - same as Type 4 except that at still higher concentrations oxygen
utilization rose to 100 percent again. The author noted that the rise in oxygen
utilization was due probably to simple chemical oxygen demand.
By designating the median toxic concentration (TCso) and indicating the appropriate
toxigram type, a convenient index for characterizing that particular chemical was obtained.
Despite its disadvantages, i.e., slowness, lack of correlation between the lab and the
receiving stream, empirical application, and lack of reproducibility between laboratories, the BOD
bioassay or some variation of it can be a useful tool in pollution control. An effort should be
made by those who depend on BOD determinations to arrive at a common method for reporting
results and possibly to develop a toxigram index similar to that proposed by Herman (1959).
Data for 33 chemicals from Herman's study are summarized in Table 4. This index approach
has not been widely adopted, but probably should be in view of the confusing data presentations
revealed in the present critique. Herman pointed out that toxic concentrations other than the
median, e.g., TCio, TC25, TC75, etc., can be chosen to suit individual industrial needs for release
of chemicals.
Correlations of BOD with other data have also been attempted with varying success as
follows:
Chemical data on phenols, heavy metals, etc. (Lloyd and Jordan, 1964)
Respirometric methods (Vernimmen, et al, 1967; Montgomery, 1967)
Aquatic biota (Burlington, 1962)
Coliforms (Burlington, 1962)
Hynes (1959) has diagramatically depicted the effect of an organic effluent on a river by
plotting the BOD rate from an effluent outfall downstream and its relationship to dissolved
oxygen, salt, suspended solids, concentration of nitrogen (NH4 and NOs) and phosphate (PO4),
and populations of algae, bacteria, sewage fungi, Cladophora, Protozoa, Tubificidae, Chironomus,
Asellus, and clean water fauna. These diagrams are quite general and Hynes pointed out that the
detailed relationship of the various parameters plotted varies with the type of effluent.
Short-Term Oxygen Demand
The short-term oxygen demand (STOD) bioassay is a variation of BOD which requires time
in the order of minutes or a few hours to conduct rather than 5 days or longer. The STOD
requires a relatively sophisticated respiration cell with an oxygen electrode, continuous recorder,
and ancillary equipment compared to that required for BOD determinations. However,
endogenous growth rate, effect of substrate addition, and oxygen demand to the point of
substrate exhaustion can be determined within 40 minutes for some types of compounds.
When oxygen is fully utilized, the system may be aerated and further oxygen utilization
followed. Vernimmen, et al (1967) reviewed previous research on this subject and described the
equipment, procedure, and some results on such chemicals as sodium acetate, formaldehyde,
methanol, isopropanol, isobutanol and phenol. In this study various types of acclimated and
domestic sewage seed were used. Vernimmen and co-workers suggest establishing a suitable
correlation factor between STOD and BOD for a given waste and predicting BOD by means of a
STOD/BOD ratio in the same manner as COD is used in predicting BOD. Although appealing
because of immediate results, the STOD bioassay has not received wide acceptance.
22
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TABLE 4. TOXICITY OF VARIOUS COMPOUNDS AS DETERMINED BY BOD (Herman, 1959)
Substance Tested
Simple Inorganic Poisons
Ammonium thiocyanate
Boric acid
Cadmium sulfate
Chromic sulfate
Cobalt chloride
Copper sulfate
Mercuric chloride
Potassium cyanide
Sulfuric acid
Inorganic Reducing Agents
under Certain Conditions
Ferrous sulfate
Oxalic acid
Sodium metaarsenite
Sodium nitrite
Sodium oxalate
Inorganic Oxidizing Agents
under Acid Conditions
Potassium dichromate
Sodium arsenate
Organic Acids and Derivatives
Acetanilide
Formic acid
Nitrobenzene
Salicylic acid
Sodium benzoate
Sodium o-benzoyl sulfimide
(soluble saccharin)
Tannic acid
Alcohols, Aldehydes, Ketones,
and Derivatives
Acetaldehyde
Acetone
Formaldehyde
Hexamethylenetetramine
Methanol
Phenols and Cresols
o-cresol
m-dihydroxybenzene
2,4-dinitrophenol
Phenol
Chlorinated Hydrocarbons
Chloroform
Reported As
NH4SCN
H3BO4
Cd++
Cr+3
CoCl2
CuS04
HgCl2
KCN
H2S04
FeS04
H2C204
NaAs02
NaN02
Na2C204
Cr+6
NasAsO4
C6HsNH-COCH3
H-C02H
C6H5N02
C02H-C6H4-OH
C6Hs-CO2Na-H20
CyH403NSNa-H20
(HO)3C6H2-CO
CHs-CHO
CH3-CO-CH3
H-CH:O
(CH2)6N4
CH3OH
CH3-C6H4-OH
C6H4(OH)2
(N02)2C6H3OH
C6H5OH
HCCls
TC5o, mg/1*
5000
1000
142
117
64
21
0.61
15
58
—
43
—
—
—
17
100
—
550
630
110
-
1000
—
230
—
740
—
—
940
—
100
1600
—
Toxigram Type
2
2
1
1
1
1
1
1
1
3
1
3
3
3
1
2
3
4
4
4
3
2
3
5
3
4
3
3
4
3
1
4
3
*TC5Q = Concentration at which oxygen utilization is reduced 50 percent.
23
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Related Microbiological Methods
Montgomery (1967) and Ludzack and Ettinger (1963) thoroughly reviewed respirometnc
methods for the determination of biochemical oxygen demand, including the STOD procedure,
Warburg respirometry, Barcroft differential manometry, Wilson six-unit recording respirometry,
electrolytic respirometry, the Sierp apparatus, the Nordell odeometer, the oxyutilometer, and
Sapromat A6 respirometry. Malaney, et al (1959) presented data on the toxic effects of metallic
ions on sewage microorganisms using the Warburg procedure.
Biodegradability of organic chemicals in the aquatic environment is another important
factor related to biochemical oxygen demand. This is of increasing concern because of the
accumulation of chemicals, especially pesticides and detergents, in the beds of rivers, lakes, and
estuaries. The behavior of organic chemicals in the aquatic environment was reported in a recent
study by Buzzell, et al (1968). At sublethal concentrations, the BOD, COD, total organic carbon
(TOC), and toxicity as determined by microbial and fish bioassay were all determined for a
selected group of 20 compounds representing a variety of types of chemicals. Bacterial enumera-
tion was used to indicate bacterial growth in biodegradation units. Theoretical oxygen demand
(TOD) for each compound was compared with 5-day and 20-day BOD results. The comparison
showed that seldom was TOD reached in the BOD determinations. Graphs showing all of the
data obtained were plotted. Each compound had its own characteristic set of curves for BOD,
COD, TOD, etc. A sound basis resulted from this study to further evaluate BOD and other
measures of chemical effect on aquatic organisms. This approach might well be used in the study
of chemical toxicity in the aquatic environment.
Earlier, Ludjack and Ettinger (1963) reviewed methods of estimating the biodegradability
and treatability of organic water pollutants and how various types of data from BOD,
respirometry, etc., procedures can be applied in practice to various contact treatment units.
Several excellent papers (Beak, 1957; Dobbins, 1964; Gannon, 1966; Nejedly, 1967; and
Smith, et al, 1962) discuss laboratory BOD determination in relation to receiving stream BOD
and the multiple factors that are involved in calculating or estimating downstream dissolved
oxygen drop. In particular, papers by Dobbins (1964), Gannon (1966), Goodman and Dobbins
(1966), and Smith, et al (1962) would be particularly useful in developing mathematical
modeling or simulation of stream problems associated with dissolved oxygen depletion.
Other microbiological techniques for study of various types of water pollution are described
in standard texts too numerous to mention here. Bacteria and other microorganisms are usually
studied as indicators of fecal pollution. Papers by Kabler (1957, 1961), Khan (1964), Bonde
(1966), Morrison and Fair (1966), O'Connell and Thomas (1965), Cooke and Bartsch (1959),
Burman (1966), and Bick (1963) describe studies in which enumerations were made of Escherichia
coli, coliforms, fecal streptococci, salmonellae, Aeromonas, Pseudomonas, Clostridia, microfungi,
actinomycetes, and algae. Bick (1963) extended this list of organisms to include protozoa and
other aquatic invertebrates in reviewing Central European ecological approaches in studying water
pollution. According to this approach, organisms characteristically occur in various "saprobic
zones" which are used to describe the degree of pollution. The procedures involved in the papers
cited above are concerned primarily with sewage pollution or taste and odor problems. Burman
(1966) reviewed the various procedures, media, equipment, etc., in bacteriological examination of
water and describes a technique in which Cl4-iabelled compounds are incubated, the d4O2
evolved is absorbed on barium hydroxide, and counts of radioactivity are used to quantitate
respiration. Since only 4 hours are required for completion, this technique might be a useful,
more rapid variation of the standard BOD assay. A similar technique, using Cl4c>2 in the study
of photosynthetic activity of algae in the field, is used to determine trophic levels in various
types of water (Butler, 1965).
24
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SECTION VII
MARINE BIOASSAY
Any report or critique to be made of the methods used in bioassaying the effects of
chemical pollutants on marine and estuarine forms can be presented concisely and to the point.
That is, those bioassay techniques in which the flowing-seawater method is not used fall short of
obtaining accurate tolerance limits, etc., for marine and estuarine species in regard to chemical
pollutants. The flowing-seawater technique for both acute and chronic toxicity studies developed
at the Bureau of Commercial Fisheries at Gulf Breeze, Florida, as described by Lowe (1964)
comes closely to providing the necessary data regarding chemical toxicants to marine and
estuarine forms.
In this technique, the chemical solution is contained in a stock solution bottle and is
metered by means of a stopcock into a slanted mixing trough which contains running fresh
sea water. The fresh seawater is kept in a holding tank at a constant level and is siphoned at a
constant rate into the trough. From the trough, the toxicant-containing water flows by gravity
over baffles into the chamber containing the test animals. A drain is situated at one end of the
chamber to allow overflow and maintenance of a constant level of toxicant-containing water. The
author states that this constant-flow system eliminated the need for aeration and that no attempt
was made to control temperature and salinity. A record of the latter two values was kept
however.
Data on marine studies are included in Appendixes A and B and may be identified by the
names of the marine species listed in the second (Organism) column. Further identification is
afforded by the Species Index (Appendix C).
Marine species most frequently used in bioassay include: :
Algae
Fish
Dunaliella euchlora
Platymonas sp
Crustacea
Anemia salina — brine shrimp
Callinectes sapidus — blue crab
Carcinus spp — decapod crab
Peneaus aztecus — brown shrimp
P. duorarium — pink shrimp
P. setiferus — white shrimp
Molluscs
Balanus spp — barnacle
Crassostrea virginica — oyster
Mercenia mercenia — hard clam
Mya spp — soft shell clam
Ostreet spp — oyster
References to marine studies are made throughout the various sections of this report. It is
of some interest to note that somewhat less than 10 percent of all papers reviewed were
concerned with studies on the effect of chemicals on the marine organisms.
Cyprinodon variegatus — sheepshead minnow
Fundulus similis — longnose killifish
Lagodon rhomboides — pinfish
Leiostomus xanthurus — spot
Mugil curema — white mullet
M. cephalus — striped mullet
Oncorynchus kisutch — coho salmon
Petromyzon marinus — sea lamprey
Salmo gairdneri — rainbow trout
S. solar — Atlantic salmon
S. trutta — brown trout
25
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SECTION VIII
FIELD ASSESSMENT
Many ecological parameters must be taken into consideration when field studies are
conducted. Even minor variations in most environmental factors such as temperature, rainfall,
pH, dissolved oxygen, and sunlight can significantly affect the toxicity of many chemical
compounds. Full discussion of these factors is presented in texts by Hutchinson (1957, 1967),
Welch (1952), Ruttner (1953), and Odum (1959). One consideration of major importance is the
food web. The introduction of toxic substances at any point in the web may interfere with the
reproduction and well-being of higher animal forms.
Study of Residues in Aquatic Animals
The transfer of food energy from plants (the producers) through various animal organisms
(the consumers) with repeated eating and being eaten is referred to as a food chain. The links in
the chain seldom number more than five and usually many chains are interconnected with one
another with the resulting pattern being called a food web. Figure 1 is a simplified diagram of a
food web in western Lake Erie leading to the sheepshead. This diagram, modified from Daiber
(1952) by Kendeigh (1961) shows the producers and consumers organized into nutritional or
trophic levels. The lowest level (P) is composed of the producers that are able to use solar energy
for the manufacture of food. At the second level (Cj) are the primary consumers or grazing
herbivores; at the third level (€2) the secondary consumers or small-size carnivores; and the
fourth level (€3) the larger carnivores. It is possible that additional consumers may be present
(€4). The consumer levels are not sharply defined because feeding behavior of some species may
involve them in more than one level. Generally, the farther removed from the producers an
organism is, the greater the likelihood it will feed on more than one level. Bacteria and fungi act
as transformers (T) or decomposers and break down dead organic matter into nutrients that may
be utilized by the producers (Ingols, 1959; Odum, 1959; Phillipson, 1966; and Welch, 1952).
Food webs are studied in a variety of ways including direct observation which is probably
the least reliable. Stomach analysis of higher animal forms has been widely used for a great many
years and has provided some useful information. When using this method, a major problem arises
when plant juices and soft tissues must be considered because these are rapidly digested and
practically impossible to identify. Precipitin tests have recently been used. An extract is made
from a prey organism and this is injected into a rabbit which produces antibodies against this
foreign protein. An extract is then made from a predator species and mixed with the rabbit
antibodies. If this predator organism has been feeding on the prey organism, a white precipitate
of antigen and antibody will be formed. In recent years, radioactive isotopes have also proven to
be a most valuable tool in the study of the transfer of energy through trophic levels (Fujiya,
1965; Gakstatter and Weiss, 1967; and Miller, et al, 1966).
Meeks (1968) studied food chain organisms and how chemical contaminants can accumulate
in the various trophic levels. A marsh adjacent to Lake Erie was treated with 3.9 millicuries of
chlorine-36, ring-labeled DDT at a rate of 0.2 Ib of technical DDT per acre. Radiolabeled DDT
residues were traced until 1 5 months after the application. In his discussion of the work, Meeks
stated that plankton and larger organisms rapidly removed the DDT from the water. Producer
organisms contained their maximum residues between 1-3 days and most invertebrates contained
their maximum residues several days later. These residues could have come directly from the
26
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Deep bottom
Open water
••••• Sheepshead •••••
Shallow bottom
• Greenside darter---*,
V
Fantail darter «J
•Log perch c
Crayfish
Beetle larvae-
• Gammarus
•• Baetinine mayflies-
Ephemera
• Caddisflies
Midge flies
Aquatic angiosperms-
Attached thallophytes<
•Detritus-
FIGURE 1. FOOD WEB IN WESTERN LAKE ERIE LEADING TO THE SHEEPSHEAD FISH
Species are separated into their different trophic levels (as modified from Daiber,
1952, by Kendeigh, 1961).
27
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water or could have been picked up through the food web. There are several factors that indicate
that the food web is the most important contributor. Herbivorous snails, at the second trophic level,
contained their maximum levels at the same time as most primary producers. Odonata naiads and
backswimmers, both carnivorous invertebrates occupying the third trophic level, reached their
peak accumulation at 1 week. The red leech was probably the invertebrate closest to a secondary
carnivore, fourth trophic level, and it had the latest and highest DDT levels of any invertebrate.
Most vertebrates attained their maximum DDT residues after the invertebrates had their highest
levels.
The DDT applied in this project would equal 0.07 ppm in water if all of the DDT had been
available at the same time. Meeks used this figure as a base level for determining magnitudes of
accumulation and recorded a sample of Cladophora collected at 3 days which exceeded this level
by a factor of 3125. For a tadpole at 4 hours and a northern water snake at 13 months
accumulation was over 500 times this base level. Concentrations ranging from 200 to 500 times
occurred in some duckweed and bladderwort samples during the first week as it did in samples
of carp and tadpole tissues. Most plant and invertebrate species exceeded the 0.07 ppm by a
factor of 50 during the first week and throughout the project, vertebrate tissue often con-
centrated DDT more than 50 times the base level.
Miller, et al (1966) noted that molluscs characteristically accumulate pesticidal compounds
at levels far above those present in the surrounding water. In laboratory experiments, Butler
(1966) showed that oysters exposed to one ppb of DDT in flowing seawater may store 25 ppm
in its tissues within 10 days. Terriere, et alj(1966) reported concentration factors from water to
plant of 500, water to aquatic animals other than fish of 1,000 to 2,000, and for rainbow trout,
10,000 to 20,000. Odum, et al (1969) found that suspended particulate organic matter may be a
reservoir of DDT and some particles may contain residues thousands of times greater than the
concentration occurring in the water. Fiddler crabs and other organisms that utilize plant detritus
for food concentrate the pesticide in their tissues.
Nicholson (1967) stated that any DDT which is not excreted or metabolized can accumu-
late in tissues to some degree. It may then be passed on to the next higher trophic level by way
of the food chain. Pesticides have been detected in aquatic animal tissues far removed from
where the chemicals were actually used. Sladen, et al (1966) cited examples of Adelie penguins
and a crabeater seal whose tissues contained DDT residues. These species reportedly do not leave
the Antarctic ice pack. The pathway to these animals is probably the marine crustaceans upon
which they feed.
Cade, et al (1968) reported finding high levels of pesticides in the eggs and tissues of
fish-eating peregrine falcons of the Yukon area of Alaska, and Enderson and Berge (1968)
reported similar findings in peregrines in northern Canada.
Hunt and Bischoff (1960) believed that ODD residues in fish caused the deaths of grebes in
Clear Lake, California. Investigations showed the following ODD concentrations in samples taken
13 months after application of the ODD: in plankton, 10 mg/kg; in fat from plankton-eating
fish, 902 mg/kg; in fat from carnivorous fish, 2690 mg/kg; and in fat from fish-eating birds,
2134 mg/kg (Nicholson, 1967). It is believed that grebes are unable to tolerate as high a level of
DDD as some species of fish.
Fay and Youatt (1967) concluded that various pesticide residues found in tissues of aquatic
birds in Lake Michigan did not appear to be an important factor in bird die-offs in this lake.
Studies by Keith (1966), however, suggest that unusual mortality of aquatic birds in California
was due to pesticide poisoning. Pesticides have also been linked with the declining population of
fish-eating ospreys in Connecticut (Ames, 1966).
-------
Within a given species there may be strains or populations in existence which are resistant
to, or have a greater tolerance for, a particular chemical and, therefore, will survive under
conditions that would normally prove fatal for this species. Populations of yellow bullhead,
golden shiner, green sunfish, and bluegill have been found that were resistant to Endrin
(Ferguson and Bingham, 1966), while some mosquito fish (Ferguson and Bingham, 1966;
Ferguson, et al, 1966; and Toohey, et al, 1965), and black bullhead (Ferguson, 1967) have been
found resistant to DDT. The resistance of fish to these chemicals appears to be genetic, i.e.,
passed on from one generation to the next. This resistance, however, may be lost unless the fish
are kept in continual contact with the chemical. While these populations are now geographically
limited, the possibility exists that eventually they could become widespread. Ferguson (1967)
concluded that although selection of a resistant fishery may permit fish exposed to toxic
chemicals to survive, it may ultimately produce a biological product dangerous to consumers of
all sort, including man himself.
In recent years, numerous investigations have been carried out on the accumulation of
chemicals in both vertebrates and invertebrates. Emphasis has been placed primarily on pesticides
(see Appendix B).
Field Methodology
Field assessment studies may be divided into two general types although a clear-cut
distinction is not always possible. The first type consists of field observations made on the
effects of chemicals on aquatic life with little prior manipulation or study of the environment by
the investigator. In many cases, the exact concentration of the chemical is unknown and may
not be fully identified but may be simply referred to as a pesticide, an eradicant, an industrial
pollutant, an organic pollutant, etc. These studies are usually made when a body of water
becomes polluted from a pesticide-spraying operation, effluents from an industrial site, or from
the application of chemicals directly into the body of water.
The effects of these chemicals are often expressed as a reduction in numbers of a particular
species or the total absence of a species or population. Dead organisms are sometimes identified
and counted, as in fish kills, or estimations made of percent mortality of a given population.
Effects may sometimes be expressed by noting the presence of particular organisms, usually
considered to be undesirable, such as Sphaerotilus, Chironomus, and tubificids. Sometimes
pre-pollution studies have been made or comparisons made between similar bodies of water. This
type of approach has been widely used in assessing the effect of thermal pollution on aquatic
life.
The second type of field assessment consists of actual toxicity studies of the effects of
known chemical concentrations on particular organisms. The studies are sometimes made in
conjunction with laboratory toxicity tests and implies some prior manipulation of the environ-
ment. Results are usually expressed in lethal concentrations of the chemical studied. Field
assessments of this type are conducted in various sizes and types of water bodies. The smallest
are simple pools or channels, such as man-made troughs or tanks. Ponds, man-made or natural,
are widely used for this type of assessment. Lakes and reservoirs are also used but allow the
minimum control in a lentic environment due to size. Streams are used, but less than lentic
bodies of water. The following discussion deals with the methods used in these toxicity studies.
Chemicals are applied to bodies of water for the purpose of assessing their effects on
aquatic organisms in several different ways. A uniform distribution is of primary concern and,
therefore, the size and depth of the body of water will be a major factor in determining which
29
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method to use. Cloth bags containing chemicals may be submerged at various depths and the
chemicals allowed to diffuse out into the water or the bags may be towed from a boat. A
common method is to pour or drip chemicals from the stern of a power boat into the wake
caused by the motor. Power sprayers are used from boats in smaller bodies of water or from the
shore. In the largest bodies of water, airplanes or helicopters are used.
Gjullin, et al (1949) studied the effects of DDT on trout, blackfly, and caddisfly larvae
from Alaskan streams using 6-ft-long galvanized metal troughs set up adjacent to a stream. Water
from the stream was pumped into the troughs and DDT was administered by a 1-gallon aspirator
bottle calibrated with a stopcock to deliver the desired concentration per minute. Darsie and
Corriden (1959) used bushel-sized galvanized tubs placed at various points along a stream filled
with stream water at that point. Fish from the stream were placed in the tubs and the entire
area was sprayed with Malathion by plane. Control tubs were covered during spraying and
mortality of fish in all tubs was recorded after 4 hours. A similar method using aquaria was used
by Schouwenberg and Jackson (1966). Snow (1963) treated pails of water from a stream with
Simazine and then bass fry were placed in the pails and mortality recorded over a 96-hour
period. Field studies were conducted on the toxicity of Lindane using 60 large fish tanks (1.5 m
x 1.5 m x 30 cm) made from corrugated metal sheets. Each contained 50 fish and a different
concentration of Lindane was used in each tank (Kok and Pathak, 1966). Gannon, et al (1966)
used an experimental outdoor channel 640 feet long for water pollution studies. The channel
consisted of 4-feet-long aluminum units that supported a waterproof plastic liner.
Attempts to approach more natural conditions in man-made devices have been made by
other investigators. Applegate, et al (1961) and Howell, et al (1964) used running water raceways
with an artificial stream bed constructed of materials from local streams, to test sea lamprey
larvicides. These raceways were 6 feet wide and over 60 feet long. Productivity studies using
artificial streams, supplied with water from an underground spring, were reported by Haydu
(1968). The streams were 4 feet wide and ranged up to 700 feet long. Yeo (1967) used plastic
pools (4 feet square by 2 feet deep) with a 2-inch layer of clay on the bottom. The pools held
180 gallons of water and aquatic plants, clams, and fish were added. A liter of natural pond
water was added to introduce naturally-occurring microorganisms. These pools were used to
study the influence of water hardness on dissipation and toxicity of Diquat. Parka and Worth
(1965) also used plastic pools (6 feet in diameter and 15 inches deep) to study the effects of
Trifluralin on fish. These pools were placed in form-fitting holes at the lowest point of a sloping
field to form a catch basin. The pools were stocked with fish and the field was sprayed with a
known quantity of Trifluralin. Over the next three days a sprinkler system soaked the field with
ten inches of water which resulted in Trifluralin being carried into the basin in runoff water.
A more direct method, and one commonly used is to take qualitative and quantitative data
on biota, apply the chemical to the body of water, and resample the populations. A control
body of water may or may not be used. Numerous researchers have used this general approach
with varied modifications (Eipper, 1959; Hoffman and Drooz, 1953; Hilsenhoff, 1966; and
Surber, 1943).
Some investigators desire more control over the organisms being used in field assessments,
and various methods are used to contain them. Live boxes or screened cages are commonly used.
Patterson and Von Windeguth (1964) confined fish in live boxes and placed these in three
shallow ponds that were sprayed with Baytex. Additional live boxes were placed in three control
ponds and mortality was recorded after 24 hours. Mulla, et al (1963) and Wollitz (1963) did
similar work in ponds using fish and frogs. The same technique has also been used in lakes
(Jackson, 1960; Johnson, 1966; and Kallman, et al, 1962) and streams (Davis, 1954; Elson and
Kerswill, 1967; Graham and Scott, 1958; Kerswill, 1967; Kerswill and Edwards, 1967;
Schoenthal, 1963; and Schouwenberg and Jackson, 1966).
30
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Another method used to restrict the movement of organisms is to enclose sections of the
body of water. Harp and Campbell (1964) studied benthos in a farm pond by using plastic
enclosures that divided the pond into sections measuring 12 by 18 feet. Different concentrations
of Silvex were used in each section. Walker (1964) studied the effects of Dichlobenil on fish and
aquatic plants in enclosures and open plots in selected farm ponds. Copeland and Woods (1969)
also studied herbicidal effects on aquatic plants and used plots staked out in shallow areas of a
lake. The plots were screened in with chicken wire to prevent plants from drifting away. Bonn
and Holbert (1961) blocked off entire coves in a Texas lake with one-inch mesh nylon net to
prevent movement of fish into and out of the cove. The coves were then treated with rotenone
products.
A unique method to assess industrial pollution in a stream was used by Tatum (1966). A
sampler, similar to the one designed by Hester and Dendy (1962) consisting of masonite plates,
was placed in a fertilized pond for about one month to accumulate a dense growth of
chironomid larvae (Diptera). These samplers were then placed in a river at stations above and
below the outfall of an industrial site. Counts of larvae were made on each sampler after 1 week
and comparisons were made between the average number of organisms on the samplers at
stations above the outfall and on the samplers below the outfall. Williams and Mount (1965)
measured the effect of zinc on periphytic communities by using a glass slide method. Periphyton
populations were monitored by allowing periphyton to accumulate on glass slides submerged in
running water canals for 2-week periods. One canal was used as a control and three other canals
were treated with different concentrations of zinc.
The effects of chemicals sprayed into streams have been studied by monitoring the rate of
downstream drifting of aquatic insects (Binns, 1967; Burdick, et al, 1960; Coutant, 1964; and
Reed, 1966). Insects were continuously collected by Surber .square-foot bottom samplers both
before and after spraying and also in control streams. In another assessment, the effects of DDT
sprayed in a stream were studied by determining the abundance of aquatic insects (Reed, 1966).
An index was developed for those benthic insects found attached on rocks measuring approxi-
mately 15.2 centimeters in diameter. Butler (1965) studied the toxicity of pesticides by
measuring primary productivity. By mixing known amounts of Cl4 with two suspensions of
phytoplankton, one of which contains a known concentration of pesticide, it is possible to
measure the interference of the pesticide with growth in a given period of time. Decreased
carbon fixation provides an index of productivity, from which the relative toxicities of various
pesticides may be compared. Other field methods used to detect the effects of chemicals on
aquatic life include the use of other more specific radioactive tracers, the measurement of the
effects of chemicals on the biochemical oxygen demand (BOD), and the fish brain cholinesterase
inactivation technique. All of these methods have been discussed previously.
Sampling Equipment
Quantitative population samples taken to determine the effects of external factors are
difficult to obtain. The effects of the external factors must be great enough to override the
natural changing of the population brought about by migration, temperature, availability of
dissolved oxygen, food supply, etc. Studies that require collecting organisms for evaluation also
face the problem of valid sampling techniques because by definition a sample must be representa-
tive. Dimond (1967) stated that sampling procedures for stream insects are crude, and so much
variation in the data results from their use that only major shifts in population size and structure
can be detected. Lauer, et al (1966) said it was difficult to collect water samples that are truly
representative of the concentration of the toxic agent to which the organism has been exposed.
31
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Ricker (1968) in reference to collecting fish for productivity studies said that four truisms
emerge: (1) most collecting methods are selective, with respect to species and size of individuals;
(2) soundness of collecting procedures has too often been assumed and has too seldom been
evaluated experimentally; (3) vast opportunities remain for discovering and developing new
methods; (4) there is no substitute for operation experience on the part of the collector.
Several books provide valuable information on equipment and collecting procedures.
Standard Methods for the Examination of Water and Wastewater (American Public Health
Association, 1967), Limnological Methods (Welch, 1948), and Ecological Methods (Southwood,
1966) provide detailed information on the physical and chemical examination of water, informa-
tion on equipment and methods for collecting biological material, and information on population
sampling in freshwater habitats. Books by Ricker (1968) and Bennett (1962) give techniques for
collecting and examining fish. The brief discussion that follows concerns only the most common
methods used in the studies previously considered.
Though a wide variety of devices exist for sampling stream and lake bottoms, the three
most widely used are the Ekman and Peterson dredges for lake bottoms, and the Surber
square-foot sampler for shallow streams. Dredges take relatively shallow samples which are
usually disturbed before they reach the surface and, therefore, the devices are not suitable for
use in stratification studies. After the material is brought to the surface it is washed through a
No. 30 mesh screen and the organisms sorted out. The screen collects only macroscopic bottom
fauna. The Ekman dredge relies on its own weight to sink, has a rather weak spring to close the
jaws and is, therefore, limited to use on bottoms which are soft and consist of finely divided
mud. Large bivalves, sticks, or small rocks interfere with the closing of the jaws. The Peterson
dredge is heavier, has additional attached weights, and can be used in sand and gravel. This
dredge is sufficiently heavy, however, that it must be raised by a hoist. The Surber square-foot
sampler is by far the most widely used stream sampler and is especially suitable for sampling on
rocky bottoms which are shallow and possess current enough to hold the net in an open
position. It has limited use in water deeper than three feet and again only macroscopic organisms
are collected (Libby, 1964; Mackenthun, 1966; Mackenthun and Ingram, 1967; Southwood
1966; and Welch, 1948).
Benthic and periphytic organisms are also collected by emplacement of a removable
substrate. According to Southwood (1966), this is one of the most accurate collection methods.
Collecting devices of this type are in various forms including building bricks (Elvins, 1962),
asbestos-cement plates (Southwood, 1966), Plexiglas substrata (King and Ball, 1967), glass slides
(Welch, 1948), and wire boxes containing rocks and sticks (Bull, 1968; Mason, et al, 1967; and
Scott, 1958). N. W. Britt (1955) used concrete blocks on a rubble and gravel bottom to collect
mayfly naiads. Unattended concrete block and Hester-Dendy multiple plate samplers are some-
times disturbed by anglers. This can be a problem when collecting devices must be left
unattended in areas where large numbers of people use the water for recreational purposes. An
additional problem encountered using this type of sampler especially in deep water, is that
organisms not firmly attached may be lost when the sampler is raised.
The Kemmerer water sampler is probably the most widely used water collecting device and
is also suitable for quantitative plankton samples. An advantage that the Kemmerer sampler has
over the Juday plankton trap is that nannoplankton as well as net plankton is collected A
possible disadvantage of the Kemmerer is that motile zooplankters may tend to avoid it. The
Juday plankton trap is a commonly used quantitative sampler which collects and removes the
plankton in one operation. When the trap is brought to the surface, the water drains out and
concentrates the plankters in a small net container. This collects only net plankton as the
nannoplankton are so small they pass through the bolting cloth filter. The Juday trap is bulky,
32
-------
awkward to handle, and usually must be raised with a hoist. Qualitative plankton samples may
also be collected with a bolting cloth tow net or with a plankton pump (Southwood, 1966; and
Welch, 1948).
Ricker (1968) states that the use of electricity for capturing fish is one of the least selective
of all active fishing methods. Too strong an electrical current, prolonged exposure, or contact
with the electrodes, however, can kill fish, or cause damage that later proves fatal, and is of
potential danger to the operators. Electrofishing can be done in both lakes and streams but water
resistivity, variations in fish size, shape, or species, temperature, and fish mortality factors all
have a bearing on the effectiveness of the shocker (Patten and Gillespie, 1966). Seining is the
most common way to collect fish but is limited to shallow waters and bottoms that have few
large boulders and few aquatic plants. Hoop and fyke nets are commonly used and according to
Ricker (1968) can be both strongly selective and differently efficient in collecting fish species.
For example, a net set parallel to the shoreline can be either more or less efficient than one
perpendicular to it, depending on the species. Gill and trammel nets tend to be more efficient in
capturing fishes adorned with external roughnesses, teeth, etc. Since these nets are stationary and
depend on the fish moving to them, the fishing success may depend on abrupt changes in
barometric pressure, wind-driven currents, water-level fluctuations, turbidity, and transmitted
light. In very large bodies of water, purse seining and trawling are the most practical collection
methods.
Table 5 shows the most commonly used items of collecting equipment, exclusive of dip nets
and simple seines, with the general purpose for each item indicated. Of course, the quantitative
samples may also be used to collect qualitative samples. The various traps and nets used for
collecting fish result in acquiring qualitative information only. For fish population studies, some
form of the capture-mark-recapture method must be used. There are many kinds of collecting
devices in use though no single one is suitable for all types of habitats; a fact which complicates
attempts to make comparative determinations (Anderson, 1962).
Indicator Organisms
Thieneman (Patrick, 1965) was the first to emphasize the fact that certain groups or
associations of species were characteristic of a given type of environment. This does not mean
however, that individual species are necessarily reliable indicators of environmental conditions in
a particular area. Various researchers (Beak, 1965; Beck, 1957; Brinkhurst, 1966; Gaufin and
Tarzwell, 1956; Lackey, 1957; Lackey, 1961; Mackay, 1969, Olson, 1957; Palmer, 1959; Palmer,
1963; Patrick, 1957; and Patrick, et al, 1967) have concluded that few individual species as
indicators of pollution exist, but when a number of kinds of organisms are used in conjunction
with chemical, physical, and bacteriological methods, the combination may be a reliable index.
Table 6 is a list of organisms that have been associated with pollution of various types. When
considering this table, it must be borne in mind that a number of ecological factors may
influence the presence or absence of an organism and, therefore, changes in distribution and
abundance of a species may not be related to pollution (Paine and Gaufin, 1956; Patrick, 1965;
Lackey, 1957). Lackey (1957) pointed out that a cause and effect relationship does not
necessarily exist simply because of abundance of an organism and occurrence of a defined
pollutant.
Beak (1965) proposed a biotic index of water pollution based on presence and density of
certain macrobenthic organisms. There were six stages in the index from normal fauna to total
absence of fauna corresponding to increasing degrees of pollution. In most cases organisms were
33
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TABLE 5 COLLECTING EQUIPMENT IN COMMON USAGE IN LIMNOLOGICAL STUDIES
AND THE GENERAL PURPOSE FOR WHICH EACH IS USED
(Bennett, 1962; Ricker, 1968; Southwood, 1966; and Welch, 1948)
Equipment
General Purpose
Ooze sucker
Ekman dredge
Peterson dredge
Triangle bottom dredge
Wilding square-foot sampler
Dendy inverting sampler
Surber square-foot sampler
Hess circular sampler
Hollow square-foot-sampler
Wisconsin trap
Kemmerer water sampler
Birge cone net
Wisconsin plankton net
Closing net
Juday plankton trap
Clarke-Bumpus sampler
Hoop and Fyke traps
Gill and tangle nets
Sunken trap nets
Electric shocker
Purse seine
Trawl
Benthos
Microfauna (qualitative) in uppermost layers
Macrofauna (qualitative) on soft bottoms
Macrofauna (quantitative) on hard bottoms
Macrofauna (quantitative) on smooth bottoms
Macrofauna (quantitative) on soft or hard bottoms
Macrofauna (quantitative) shallow moving streams
Macrofauna (quantitative) shallow moving streams
Macrofauna (quantitative) shallow moving streams
Periphyton
Macrofauna (qualitative) from hard objects having large areas
Macrofauna (qualitative) from plants in shallow water
Plankton
Net and nannoplankton (quantitative)
Net plankton (quantitative)
Net plankton (quantitative)
Net plankton (quantitative) from deep water verticle tows
Net plankton (quantitative)
Net plankton primarily deep water
Fish
Quiet shallow waters
Pelagic fish, various depths
Lower depths in relatively shallow waters
Shallow streams and lakes
Open water surface seining in large bodies of water
Bottom, surface, or midwater depths in large bodies of water
34
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TABLE 6. PARTIAL LISTING OF ORGANISMS COMMONLY ASSOCIATED WITH POLLUTION
Organism
Type of Pollution
References
Insects
Chironomus riparius
C. plumosus
Culex pipiens
C. tentans
Eristalis bastardi
E. tenax
Glyptotendipes spp
Oligochaetes
Limnodrilus spp
Tubifex spp
Fungi
Fusarium aquaeductum
Geotrichum candidum
Leptomities lacteus
Penicillium lUacinum
P. ochrochloron
Bacteria
Aerobacter aerogenes
A. cloacae
Escherichia coli
Sphaerotilus natans
Streptococcus durans
S. faecalis
S. liquefaciens
S. zymogenes
Bryozoa
Ctenostomata sp
Protozoa
Bodo caudatus
Caenomorpha medusula
Chaenea spp
Colpoda spp
Colpidium spp
Dimastigamoeba gruberi
Diplophrys archeri
Organic
Organic
Organic
51
))
,,
Copper
Fecal pollution
,,
))
Organic
Fecal pollution
Organic
Organic
Gaufin, 1957; Learner and Edwards,
1966; Paine and Gaufin, 1956
Ingram, 1957
Gaufin, 1957; Ingram, 1957; Paine
and Gaufin, 1956; and Gaufin, 1958
Gaufin and Tarzwell, 1952
Gaufin, 1957; Gaufin and Tarzwell,
1952; and Paine and Gaufin, 1956;
Gaufin, 1958
Ingram, 1957
Paine and Gaufin, 1956
Brinkhurst, 1966; Gaufin, 1957;
1958; and Shrivastava, 1962
Brinkhurst, 1966; Gaufin, 1957,
1958; and Gaufin and Tarzwell,
1952
Cooke, 1957
Kabler, 1957, 1961
Kabler, 1961
Kabler, 1957, 1961
Curtis, 1969; Herbert and Richards,
1963; and Patrick, 1968
Kabler, 1961
Lackey, 1961
Lackey, 1957
Lackey, 1961
Lackey, 1957
35
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TABLE 6. (Continued)
Organism
Type of Pollution
References
Protozoa (Continued)
Enchelyomorpha vermicularis
Glaucoma pyriformis
G. schintillans
Hexamitus spp
H. crassus
H. inflatus
Loxodes vorax
Mastigamoeba spp
Mastigella spp
Metopus spp
M. sigmoides
Opercularia spp
Paramecium putrinum
Pelomyxa palustris
Polytoma uvella
Poteriodendron petiolatum
Saprodinium putrinum
Spirostomum spp
Strombidium spp
Tetramttus spp
T. pyriformis
Tillina magna
Trachelocerca coluber
Trepomonas spp
Trigonomonas compressa
Trimyema compressa
Uahlkampfia guttalu
U. Umax
Urocentrum turbo
Uroleptus spp
Urophagus rostratus
Urotricha spp
Urozona butschlii
Organic
Lackey,
Lackey,
Lackey,
Lackey,
Lackey,
1957
1961
1957
1961
1957
Lackey, 1961
Lackey, 1957
Lackey,
Lackey,
Lackey,
Lackey,
1961
1957
1961
1957
Lackey, 1961
Lackey,
Lackey,
Lackey,
1957
1957,1961
1961
Lackey, 1957, 1961
Lackey, 1957
Lackey,
Lackey,
Lackey,
Lackey,
1957,1961
1961
1957
1961
Achanthes affinis
A. minutissima
Achnanthidium brevipes
var intermedia
Actinastrum hantzschii
Actinella spp
Agrnenellum quadriduplicatum
Amphora coffeiformis
A. ovalis
Anabaena constricta
Anacystis spp
A. montana
Anomoeoneis serians var.
brachipira
Arthrospira jinneri
Hydrogen sulfide
Calcium carbonate
Salt brine
(principally NaCl)
•>•>
High acidity
Organic
Salt brine (principally NaCl)
Paper mill wastes, salt brine, oil
Organic
Salt brine (principally NaCl)
Organic
Iron
Organic
Palmer, 1959
Patrick, 1965
Palmer, 1959
Palmer, 1959, and Patrick, 1957
Palmer, 1959
36
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TABLE 6. (Continued)
Organism
Type of Pollution
References
Algae (Continued)
Astasia spp
Asterionella formosa
Caloneis amphisbaena
Calothrix spp
C. braunii
Camphlodiscus spp
Carteria multifilis
Ceratoneis arcus
Chaetomorpha spp
Chlamydobotrys spp
Chlamydomonas spp
C. ehrenbergii
C. reinhardi
Chlorella pyrenoidosa
C. vulgaris
C. variegata
Chlorobrachis spp
C. gracillina
Chlorococcum botryoides
C. humicola
Chlorogonium euchlorum
Chromulina spp
C. ovalis
Closterium acerosum
Coccachloris elabens
(Aphanothece halophytica)
Cocconeis diminuta
C. pediculus
C. placentula
Cryptoglena pigra
Cryptomonas erosa
Cyclotella kiitzingiana
C. meneghiniana
Cymatopleura solea
Cymbella lacustris
C. naviculiformis
C. ventricosa
Diatoma elongatum
D. vulgare
Diploneis elliptica
Dunaliella salina
Enteromorpha intestinalis
E, prolifeia
Entophy salts deusta
(Aphanocapsa littoralis)
Euglena spp
E. acus
E. adhaerens
E. agilis
Organic
Copper
Paper mill wastes, hydrogen sulfide
Salt brine (principally NaCl)
Copper
Hydrogen sulfide
Organic
Phenolic wastes
Salt brine (principally NaCl)
Distillery wastes
High acidity
Salt brine
Organic
Iron
Organic
Distillery wastes
Copper
Organic
Distillery wastes, organic
Iron
High acidity
Chromium
Salt brine (principally NaCl)
Paper mill wastes
5)
Phenolic wastes
Organic
High acidity
Phenolic wastes
Hydrogen sulfide, salt brine
Phenolic wastes, paper mill wastes
Salt brine (principally NaCl)
Copper, phenolic wastes
Salt brine, paper mill wastes, copper,
hydrogen sulfide
Salt brine (principally NaCl)
Phenolic wastes, paper mill
Wastes, oil
Salt brine (principally NaCl)
Lackey, 1957
Palmer, 1959
Lackey, 1957
Palmer, 1959
Chromium
High acidity
Organic
37
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TABLE 6. (Continued)
Organism
Type of Pollution
References
Algae (Continued)
E. deses
E. gracilis
E. hiemalis
E. mutabilis
E. oxguris
E. polymorpha
E. sociabilis
E. stellata
E. tatrica
E. viridis
Eunotia spp
E. exigua
E. lunaris
E. trinacria
Fragilaria virescens
Frustulia rhomboides var
saxonica
Gomphonema spp
G. acuminatum
G. herculaneum
G. olivacuum
G. parvulum
Gyrosigma attenuatum
Hantzschia amphioxys
H. elongata
Lepocinclis ovum
L. text a
Lyngbya astuarii
L. digueti
Melosira arenaria
M. varians
Meridian circulars
Microcoleus chthonoplastic
Navicula anglica
N. atomus
N. cincta var heufleri
N. cryptocephala
N. gregaria
N. linearis
N. longirostris
N. minima
N. minuscula
N. palea
A', pygmaea
j\. radiosa
j\. salinamm
A', subtilissima
N. viridis
Organic
11
High acidity
Organic, chromium
Organic
Chromium
Chromium, high acidity
High acidity
Chromium, high acidity, organic
Iron, high acidity
High acidity
Phenolic wastes
Salt brine (principally NaCl)
Iron
Paper mill wastes, oil
Calcium
Phenolic wastes, organic
Salt brine (principally NaCl)
Hydrogen sulfide, organic
Salt brine (principally NaCl)
High acidity, organic
Organic
Salt brine (principally NaCl)
Organic
Salt brine (principally NaCl)
Oil, organic
Salt brine (principally NaCl)
Chromium
Salt brine (principally NaCl)
Salt brine, organic, phenolic wastes,
paper mill wastes
Salt brine (principally NaCl)
Chromium
Salt brine (principally NaCl)
Hydrogen sulfide
Salt brine (principally NaCl)
Chromium, organic
Salt brine (principally NaCl)
Paper mill wastes, oil
Salt brine (principally NaCl)
High acidity, salt brine
High acidity, copper
Palmer, 1959
Lackey, 1957; Palmer, 1959; and
Sundaresan, et al, 1965
Palmer, 1959
Lackey, 1959, and Palmer, 1959
Palmer, 1959
Lackey, 1959, and Palmer, 1959
Palmer, 1959, and Patrick, 1957
Lackey, 1957, and Palmer, 1959
Palmer, 1959
Patrick, 1965
Palmer, 1959
Lackey, 1957, and Palmer, 1959
Palmer, 1959
Palmer, 1959, and Patrick, 1957
Palmer, 1959
•>•>
Lackey, 1957, and Palmer, 1959
38
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TABLE 6. (Continued)
Organism
Type of Pollution
Reference
Algae (Continued)
Neidium bisulcatum
Nitzschia acicularis
N. apiculata
N. epithemaides
N. frustulum
N. ignorata
N. palea
N. trybliowella var debilis
Ochromonas spp
Oscillatoria spp
0. chalybea
0. chlorina
O. formosa
O. lauterbornii
0. limosa
O. princeps
O. putrida
0. tenuis
Pandorina spp
P. momm
Pediastrum spp
P. simples
Penium cucurbitinum
Phacus parvulus
P. pyrum
Phormidium autumnale
P. tenue
P. uncinatum
Pinnularia spp
P. borealis
P. subcapitata var helseana
Platymonas spp
Polytoma citri
P. uvella
Pyrobotrys gracilis
P. stellata
Scenedesmus spp
S. bijugatus
S. obliquus
S. quadricauda
Spirogyra communis
Spirulina subsalsa
Spondylomorum spp
Stauroneis anceps
S. phoenicentem
Stenopterobia intermedia
Stephanaptera gracilis
Stichococcus bacillaris
Copper
Organic
Salt brine (principally NaCl)
Hydrogen sulfide
Phenolic wastes, hydrogen sulfide,
salt brine
Hydrogen sulfide
High acidity
Paper mill wastes, salt brine
Organic
Paper mill wastes
Organic
Paper mill wastes
Salt brine (principally NaCl)
High acidity
Organic
Salt brine (principally NaCl)
Organic
High acidity, iron, salt brine
Phenolic wastes
Iron
Organic
Paper mill wastes
Salt brine (principally NaCl)
Copper
Organic
55
Salt brine (principally NaCl)
Paper mill wastes
High acidity
Iron
55
Salt brine (principally NaCl)
Organic
Palmer, 1959
Lackey, 1957, and Palmer, 1959
Palmer, 1959
Lackey, 1957, and Palmer, 1959
Palmer, 1959
Lackey, 1957
Lackey, 1957, and Palmer, 1959
Palmer, 1959
Lackey, 1957
5)
Lackey, 1957, and Palmer, 1959
))
Palmer, 1959
Lackey, 1957, and Palmer, 1959
Palmer, 1959
39
-------
TABLE 6. (Continued)
Organism
Type of Pollution
References
Algae (Continued)
Stigeoclonium tenue
Surinella delicatissima
S. linearis
S. ovata
S. ovata var salina
Symploca erecta
Synedra acus
S. affinis
S. pulchella
S. ulna
Tabellaria flocculasa
Tetraedron muticum
Tetraspora spp
Trachelomonas spp
T. hispida
Trichodesmium spp
Ulothrix spp
U. zonata
Vanheurckia rhomboides var
crassenervia
Xanthidium antilopaeum
Organic
Iron
Curtis, 1969, and Palmer, 1959
Palmer, 1959
Paper mill wastes, phenolic wastes,
organic
Paper mill wastes, phenolic wastes,
hydrogen sulfide, organic
Copper
Oil, salt brine
Salt brine (principally NaCl)
Paper mill wastes, salt brine
Paper mill wastes, phenolic wastes, oil Palmer, 1959
High acidity
Organic
Chromium
Salt brine (principally NaCl)
Iron
Salt brine (principally NaCl)
Salt brine, paper mill wastes
High acidity
Palmer, 1959, and Patrick, 1957
Lackey, 1957, and Palmer, 1959
Palmer, 1959
40
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identified only to Family and were grouped according to feeding type and sensitivity to
pollution.
In using groups of aquatic organisms as indicators of pollution, the absence or reduction in
numbers of "clean-water" species may be as important, if not more so, than the presence of
known pollutional forms (Anderson, 1962; Fremling, 1964; Gaufin, 1958, 1965; Gaufin and
Tarzwell, 1952; and Leonard, 1965). Aquatic organisms usually considered to be "clean-water"
organisms include mayflies, stoneflies, caddisflies, molluscs of the family Unionidae, and beetles
of the family Elmidae. The absence of these organisms and the presence of physid snails,
tubificids, Eristdis tenax, and Chironomus pipiens would indicate water highly degraded by
organic wastes (Hinshaw, 1967; Ingram, 1957; Paine and Gaufin, 1956; and Young, 1961).
Palmer (1959) lists over 40 species of algae that he considers "clean-water" forms. He also said
that blue-green algae and flagellates are the algal groups most frequently encountered in the
portion of a stream containing organic pollution. Palmer (1963) has compiled a listing of more
than 600 species that are said to be tolerant of pollution.
The presence of large number of tubificids usually indicates a high concentration of organic
matter. These worms can live in water low enough in oxygen that most other fauna will not
survive (Brinkhurst, 1966, and Curry, 1965). King and Ball (1964) used wet weight ratios of
tubificids to aquatic insects to indicate changes in water quality. Their results indicated that this
technique may be useful in measuring organic pollution. Among the mayflies, there seems to be
an order of sensitivity to organic waste and as pollution increases sensitivity declines in the
following order: Rhithrogena, Heptagenia, Ecdyonurus, Ephemerella, and Baetis. An amphipod,
Gammarus pulex, lives quite well even in badly polluted water as long as the oxygen content is
not greatly lowered (Hynes, 1959). Ingram (1957) in discussing clams and snails, said that not
enough is known about molluscan ecology to name any species a pollution indicator and though
species such as Psidium idanoensis, Physa Integra, P. heterosteopha, and Musculium transversum
are found associated with organic waste, they are also found in areas unpolluted by domestic
sewage or putrescible industrial waste.
Coliform bacteria are constantly present in alimentary discharges, are comparatively easy to
enumerate, have long been considered indicative of fecal pollution (Gilderhus, 1966; and Kabler,
1957, 1961). Owing to special nutritional requirements a few species of fungi have been
associated with certain types of pollution (Servizi, et al, 1966). Generally, however, there has
been little correlation found between pollution and populations of aquatic fungi (Cooke and
Bartsch, 1959).
Brinkhurst (1966) said that fish are not particularly easy to use as indicators because they
are relatively difficult to sample, and their mobility makes it possible for them to avoid those
parts of the environment which become intolerable for short periods of time. Katz and Gaufin
(1953) studied the effects of organic pollution on fish distribution in a small Ohio stream. No
species of fish were regarded as indicators of pollution although several were relatively tolerant
of unfavorable conditions. They concluded that the number of species present and their relative
abundance are the most important considerations when pollutional conditions are being
evaluated.
Williams (1964) concluded that the search for biota or communities of biota which might
be useful as indicators of water quality has been hampered by the lack of information on the
environmental requirements of the various species and their resistance to specific chemical
substances.
41
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Concluding Remarks
(Field Assessment)
The value of field studies lies in the fact that more natural conditions are approached in
the field than in the laboratory. This is important because the reaction of an organism to a
chemical in the laboratory is not necessarily the same as it would be in nature. A price is paid
for these natural conditions, however, because it is impossible to control or even to ascertain all
of the variables in a field study. To complicate this further, in most field work there is a
conspicuous lack of detailed water-quality data taken in support of the field observations. In this
report, for example, approximately 220 papers dealing with field projects were carefully studied
and evaluated. Of these, only about 50 contained definitive water quality information. It has
long been recognized that the toxicity of a compound may depend on a number of interrelated
factors, including temperature, pH, water hardness, dissolved oxygen content, and exposure time.
For example, Cairns (1957) showed that considerable increases in toxicity may result during
periods of low dissolved oxygen content, and that this may occur even when the oxygen supply
is not low enough to be directly harmful to the organism. Burdick (1967) states that toxicants
react with detritus, and organic or inorganic materials in the water or bottom sediments and that
bacterial decomposition may alter chemicals to substances of greater or less toxicity. He
concluded that even light penetration may have an effect. Only rarely are all or even a majority
of these factors taken into consideration in conducting field studies of water pollution.
42
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SECTION IX
FACTORS AFFECTING CHEMICAL TOXICITY IN WATER
Depending on the nature of a chemical, environmental factors influencing water quality may
also affect the inherent toxicity of that compound to aquatic biota. Similarly, water quality
itself can affect chemical toxicity. For these reasons, chemical-physical characterization of water
is important whether it is used in a bioassay or studied in the field. Experimentation may have
little significance without minimal characterization, that is, measurement of water temperature,
pH, dissolved oxygen (DO), conductivity, oxidation-reduction potential, dissolved chlorides, and
turbidity. Furthermore, when potentially toxic ions, e.g., heavy metals or halogens, are known or
suspected to be present, analysis for these should be made. Without such data for an aquatic
experiment, the toxicity of a chemical to an aquatic organism means only that for the conditions
of that experiment is the chemical toxic at the concentration level reported, i.e., the toxicity
data cannot be extended to any other type of water.
As pointed out previously in other sections of this report, this type of water characteriza-
tion data was seldom given in the publications reviewed. Use of an unspecified, "standard water"
throughout a bioassay study helps very little when an attempt is made to extrapolate from the
study and predict how a chemical may behave in an entirely different water. If there is to be a
serious attempt to employ multivariate analysis or mathematical modeling in predictive studies of
chemical pollution problems, then the suggested type of water data must be taken, or completely
standardized experimental conditions including chemically defined water must be employed. The
following discussions concern the more important water-quality factors that may affect the
toxicity of a chemical in aquatic environments.
Temperature
The biological significance of temperature in the aquatic environment has been recognized
for many years. It was once said that a limnologist could obtain more information about a body
of water with a thermometer than any other single instrument. Reid (1962) believes "from the
broad and basically ecological point of view, the thermal properties of water and the attending
relationships are doubtless the most important factors in maintaining the fitness of water as an
environment." In several limnology texts (Reid, 1961, Ruttner, 1953, and Welch, 1952),
accounts are given of thermal stratification, thermoclines, heat budgets, general thermal dynamics
of water bodies, and the effects these factors have on aquatic life. Hutchinson (1957) gives an
in-depth account of the thermal properties of lakes. In recent years as the use of streams and
lakes by industry has increased, more investigators have been concerned with the effects of
increased temperatures on aquatic organisms. There are several very recent, extensive
bibliographies (over 1500 references) available on heated effluents and their effects on aquatic
life (American Society of Civil Engineers, 1967; Kennedy and Mihursky, 1967; and Raney and
Menzel, 1967). A reference manual on thermal effects on aquatic organisms was prepared by
Wurtz and Renn (1965).
A great deal of attention has been placed on thermal effects on fish. Fish, like most aquatic
organisms, are poikilotherms and therefore lack the means of maintaining an independent body
temperature. Needless to say, water temperature is a critical factor in the life of a fish and in
fish production. Each species has a thermal zone in which it can function in a normal manner
with a higher and lower zone in which it can survive for certain lengths of time. The degree of
43
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success the fish will have in these less than optimal zones will depend on a multitude of factors
including the health of the fish, stage of development, sex, diet, season of the year, and various
water quality parameters (Alabaster, 1967; Alabaster and Welcomme, 1962; Brett, 1956; Hoar,
1956; Huet, 1965; Mihursky and Kennedy, 1967; Tarzwell, 1957; and Tyler, 1966).
A major factor affecting the ability of an organism to adapt to a new temperature is the
previous temperature to which it has been exposed. Prosser and Brown (1961) define acclimation
as the compensation by animals to persistent change in temperature, usually in the laboratory.
Though not all authors make the distinction between acclimation and acclimatization, Prosser
and Brown refer to acclimatization as compensations under field conditions which come about
more slowly. Upper lethal temperatures tend to be closer to the acclimation temperature than
lower lethal temperatures (Colton, 1959). Upper or lower lethal temperatures obviously have
more meaning when the acclimation temperature is indicated. Table 7 lists the thermal death
points of a number of species of freshwater and marine fish in relation to the acclimation
temperatures. The table is a summary of work conducted by Brett (1956) and Jones (1964).
Laboratory studies conducted on thermal death points of various organisms may be of two
basic types. These are acute or shock tests in which large temperature increases are usually
completed in a few hours, and the chronic tests in which temperature increase is only a degree
or two a day and the overall test lasts several months. Shock tests are of value in studying fish
movements or when thermal loading is confined to a limited area. In these situations fish are
likely to move rapidly from one temperature zone to another. Chronic tests are designed to
approximate a condition of gradual exposure over considerable periods of time (Cairns, 1955,
1956).
Generally, fish of temperate regions are able to tolerate temperatures from 0 C to 30 C but
resistance to the highest and lowest temperature varies with different species. Salmonids and
other cold water fishes do not tolerate higher temperatures while warm water forms, such as the
cyprinids, tolerate higher temperatures quite well. Marine species may be more sensitive to
temperature change than freshwater species and immatures of both types are more sensitive than
adults. In general, all abrupt changes in temperature can be harmful even if the changes are short
lived.
Temperature may affect the fish directly or it may have an indirect effect. A change may
be within the toleration limits of a fish but may alter the environment to the point where it is
more suitable for another species (Tarzwell, 1957). This may come about in a number of ways
including a reduction or an increase in food supply, interference with the spawning process, or
alteration of the dissolved oxygen content of the water. Though other factors are also involved,
fish only spawn when the water reaches a suitable temperature and this varies with different
species. Water temperature may affect growth. For example, carp growth is very good between
20 C and 28 C, average between 13 C and 20 C, poor between 15 C and 13 C, and non-existent
below 5 C (Alabaster, 1967; Colton, 1959; Fry, 1960; Huet, 1965; and Swift, 1965).
Though the physiological effects of heat on an organism are discussed in some detail by
Brown (1957) and Prosser and Brown (1961), the actual cause of death by either heat or cold is
not well understood. Various theories have been put forth concerning the mechanism of heat
death including coagulation of protoplasm, inactivation of enzyme systems, lack of oxygen due
to inactivation of the respiratory center, and the release of toxic materials from heat affected
cells (Brett, 1956; Brown, 1961; Cairns, 1955; and Jones, 1964). Though the exact causes of
death at high temperatures may not be clear, most investigators agree that multiple factors are
involved.
44
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TABLE 7. THERMAL DEATH POINTS OF FISH ACCLIMIZED AT THE INDICATED TEMPERATURES
(FRESHWATER = F, MARINE - ATLANTIC = A, PACIFIC = P)
(Brett, 1956; and Jones, 1964)
Fish
Atlantic salmon
Atlantic salmon (grilse)
Atlantic salmon (parr)
Blacknose dace
Blacknose dace
Bluegill
Bluegill
Bluegill
Bluntnose minnow
Brook stickleback
Brook trout
Brook trout
Brook trout
Brook trout
Brook trout
Brown bullhead
Brown bullhead
Brown bullhead
Brown trout
Brown trout (fry)
Brown trout (fry)
Brown trout (yearling)
Brown trout (parr)
Carp
Chinook salmon (fry)
Chinook salmon (fry)
Chum salmon (fry)
Chum salmon (fry)
Coho salmon (fry)
Coho salmon (fry)
Common shiner
Common shiner
Creek chub
Creek chub
Creek chub
Emerald shiner
Emerald shiner
Emerald shiner
Fathead minnow
Fathead minnow
Fathead minnow
Gizzard shad
Gizzard shad
Acclimation
Temperature, C
_
—
-
10
20
15
20
30
25
25-26
5
10
15
20
25
15
20
30
26
5-6
20
—
-
20
15
20
15
20
15
20
15
30
10
15
25
10
15
25
10
20
30
25
30
Thermal Death-
Point, C
29.5-30.5
32.5-33.8
29.8
28.8
29.3
30.7
31.5
33.8
33.3
30.6
23.7
24.4
25
25.3
25.3
31.8
33.4
36.5
26
22.5
23
25.9
29
31-34
25
25.1
23.1
23.7
24.3
25
30.3
31.0
27.3
29.3
30.3
26.7
28.9
30.7
28.2
31.7
33.2
34.3
35.9
Occurrence
A-F
F
F
F
F
F
F
F
F
F
A-F
A-F
A-F
A-F
A-F
F
F
F
A-F
F
F
A-F
A-F
F
F
F
F
F
F
F
F
F
F
F
F
F
F
F
F
F
F
A-F
A-F
45
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TABLE 7. (Continued)
Fish
Golden shiner
Golden shiner
Golden shiner
Goldfish
Goldfish
Goldfish
Guppy
Largemouth bass
Largemouth bass
Largemouth bass
Mosquito fish
Mosquito fish
Mosquito fish
Opaleye
Opaleye
Perch
Perch
Perch
Perch
Pink salmon (fry)
Pink salmon (fry)
Pink salmon (fry)
Pumpkinseed
Rainbow trout
Rainbow trout (Kamloops var)
Roach
Roach
Roach
Sockeye salmon (fry)
Sockeye salmon (fry)
Sockeye salmon (fry)
Tench
White sucker
Yellow Perch
Acclimation
Temperature, C
15
25
30
10
20
30
30
20
25
30
15
20
30
20
30
—
10
15
25
5
10
20
25-26
—
11
20
25
30
5
10
20
-
25
15
Thermal Death-
Point, C
30.5
33.2
34.7
30.8
34.8
38.6
34
32.5
34.5
36.4
35.4
37.3
37.3
31.4
31.4
23-25
25.0
27.7
29.7
21.3
22.5
23.9
34.5
28
24
29.5
30.5
31.5
22.9
23.4
24.8
29-30
29.3
27.7
Occurrence
F
F
F
F
F
F
F
F
F
F
A-F
A-F
A-F
P
P
F
F
F
F
F
F
F
F
A-F-P
P-F
F
F
F
F
F
F
F
F
F
46
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When the temperature goes beyond the thermal zone optimal for the organism, evidence
indicates the general resistance to other adverse conditions is reduced. Hynes (1959) stated that
several workers have shown that a rise of 10 C may halve the survival time of test animals. It has
been reported that an increase in temperature caused an increase in toxicity in fluorides
(Angelovic, et al, 1961), cyanide (Cairns and Scheier, 1963), sodium pentachlorophenate
(Crandall and Goodnight, 1959), phenol (Brown, et al, 1967), various pesticides (Mahdi, 1966,
and Macek, et al, 1969), as well as a possible reduction in resistance to disease (Cairns, 1955,
and Turnbull, et al, 1954). It has also been reported that anesthesia with alcohol was induced
more rapidly in fish when the temperature was increased. Though it may not appreciably affect
the toxic threshold, an increase in temperature may affect the length of time required for a given
concentration to kill an organism. Hester (1959) found that if 40 F tests were continued beyond
3 days, the kill of fish by the end of the twenty-first day was approximately the same as 70 F
tests conducted for 3 days. When all tests were run at 3 days, however, more rotenone was
required to kill fish at 40 F than at 70 F. Similar findings were reported by Lloyd (1965) and
Cairns and Scheier (1957). The rate of uptake of chemicals by aquatic organisms increases with
an increase in temperature (Das and Needham, 1961). This occurs probably because of the
increase in metabolic rate which accompanies the increase in temperature.
An interesting example of the effects of temperature on fish behavior was reported by
Loeb, et al (1966). Brown bullheads (Ictalurus nebulosus) were killed when exposed to 50 ppb
of 4-iodo-3-salicylanilide at temperatures of 5 C or 21 C. When bottom sediments were added,
the bullheads would bury themselves in the sediment at 5 C and thus escape the toxic chemical.
At 21 C, however, the fish would not bury themselves and were killed by the chemical.
Results of field studies conducted to determine the effects of increased temperatures on
aquatic life are usually recorded as a reduction in numbers of individual organisms, reduction in
species (with or without reduction in numbers of individuals), or the presence of indicator
organisms (Geen and Andres, 1961; Mann, 1965; Trembley, 1960; and Wurtz and Dolan, 1961).
Various types of organisms are useful in these studies. Trembley (1965) conducted a five year
study of heated discharges in a Pennsylvania river and outlined the types of useful organisms and
made some brief remarks about each group. The numbers of species of periphyton tended to be
reduced in high temperatures but individual species were often present in great numbers. Most
aquatic invertebrates tended to increase during winter months and undergo reduction in the
summer. Insect larvae of the family Tendipedidae were the most tolerant invertebrates in the
heated water areas. A rooted aquatic plant, Potomogeton, was found growing well in tempera-
tures ranging from 35 C to 37 C. Certain species of blue-green algae, primarily Oscillatoria, were
found to be the most heat-tolerant and were observed growing well in temperatures up to 45 C.
During the summer, fish left the heated-water zone and were apparently attracted to the heated
water areas during the winter months. Plankters drifted with the current and because of this
were not considered suitable organisms to work with in lotic environments.
The Aquatic Life Advisory Committee (1956) in discussing water quality requirements for
freshwater fish concluded that "any change in the temperature of the aquatic habitat will affect
the animals and plants living in it, even though the change remains within their ranges of thermal
tolerance. Because there is a relationship between temperature and the solubility, dissociation
and stability of the substances dissolved or suspended in water, a change in temperature will have
an indirect effect upon aquatic organisms, entirely apart from any direct effect, through
alteration of the physical and chemical characteristics of their environment. Since body tempera-
ture of a fish or lower aquatic organism is very close to that of the water, a change in
temperature will have direct effect by action upon the metabolic rate, growth, reproduction and
other vital processes. It should be pointed out further that, as a consequence of the temperature
effect upon one species, a change in temperature might alter the biotic environment of another
47
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species, thereby affecting the latter indirectly through an increase or decrease in food or shelter.
The complexity of the problem is increased by the fact that the nature and magnitude of the
effects upon aquatic organisms are related, not only to the temperature itself, but also to the
rate at which it is changed and to the duration of the altered level".
pH
The most frequently used index of hydrogen ion activity is pH. The pH of natural waters
may range from extremes of 1.7, found in an African lake, to 12.0 recorded from some Japanese
lakes. Normally however, surface water pH is between 6.0 and 9.0. Factors influencing pH in
unpolluted bodies of water are currents, which serve to keep the waters mixed; biological
processes such as photosynthesis and respiration; and the composition of the rocks and sediments
of the substrate (Jordan and Lloyd, 1964; National Technical Advisory Committee, 1968; and
Reid, 1961). Hutchinson (1957) states that in practically every case where the water is neither
very acid nor very alkaline, it may be assumed that the pH is regulated by the carbon
dioxide-bicarbonate-carbonate system.
Determination of pH is not a measure of total acidity or alkalinity in water. Many
compounds may be in water in unionized portions of weakly ionizing acids such as phosphoric,
carbonic, fatty acids, protein compounds, or as hydrolyzing salts such as ferrous or aluminum
sulfate. The latter are referred to as acid buffers. When acidity is measured by titration using a
dye like methyl orange with an end-point at pH 4.5, the value is termed "free acidity". If the
titration is carried by alkali addition to the end point of phenolphthalein at a pH of 8.3, the
value is called "total acidity" and will include the weak acids, acid salts, and with sufficient time
for reaction between alkali additions, some acidity due to slowly hydrolyzable compounds.
Alkalinity is usually imparted by the bicarbonate, carbonate, and hydroxide components of
a natural or treated water supply. These ions are the so-called alkali buffers. In determining
alkalinity, if the solution is titrated to the phenolphthalein end point of 8.3, the alkali fraction
measured is that contributed by the hydroxide and half of the carbonate. Indicators responding
in the pH range of 4-5 are used to measure the "total alkalinity" contributed by the hydroxide,
carbonate, and bicarbonate.
Alkaline buffering capacity of water in some limestone areas, for example, may partially
neutralize acidic components of an effluent. Where carbon dioxide content is high, alkali
components of a waste effluent may be partially neutralized. Total acidity and alkalinity are
features of water quality that are often overlooked in considering effluent release, and also in
conducting bioassay or field studies of chemical toxicity.
When pH is the only factor considered, the toleration limit of most organisms falls in the
range of 5.0 to 9.0 (Jones, 1964; Doudoroff and Katz, 1950; and Hynes, 1966). Fry (1960)
concluded that the general range for good fish production was 6.7 to 8.6. McKse and Wolf
(1963) state that of waters which support a good fish fauna, only 5 percent have a pH of less
than 6.7 and only 5 percent have a pH over 8.3. The permissible range for fish depends on
several factors including temperature, age, dissolved oxygen, prior acclimatization, and the
content of various anions and cations.
The exact cause of death of fish in low or high pH waters is unclear though Tarzwell
(1957) has stated that an unsuitable pH may interfere with oxygen uptake. It has been reported
(Jones, 1964, and Aquatic Life Com., 1955) that fish are killed in acid waters by precipitation
and coagulation of the mucous on the gills and by coagulation of the gill membranes themselves
48
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The pH of water may have considerable influence on the toxicity of certain chemicals. The
pH value will determine the degree of dissociation of weak acids and bases, some of which may
be more toxic in molecular than ionic form (McKee and Wolf, 1963; Hynes, 1966; and Cairns
and Scheier, 1963). Highly dissociated inorganic acids do not appear to be toxic at pH values
above 5.0 and highly dissociated inorganic alkalies do not appear to be toxic below 9.0 (Aquatic
life Com., 1955).
The effect of pH on the toxicity of specific compounds has been reported. An increase in
toxicity brought about by a decrease in pH was reported for pentachlorophenol and sodium
pentachlorophenate (Goodnight, 1942, and Crandall and Goodnight, 1959), nickel cyanide
(McKee and Wolfe, 1963), and sodium sulfide (McKee and Wolfe, 1963, and Tarzwell, 1957).
Within certain ranges, pH may have little or no effect on toxicity. Henderson, et al (1958, 1959)
reported no differences in toxicity for several chlorinated hydrocarbon insecticides when the pH
was varied from 7.4 to 8.2. Loeb, et al (1965) conducted studies on ergot derivatives on
surfacing behavior of fish, and found no change in response when pH was changed from 6.3 to
7.2. Marking and Hogan (1967) found little difference in toxicity of Bayer 73 to fish in a pH
range between 6.4 to 8.0. At a higher pH (10.0) and a lower pH (5.0), the toxicity of this
compound was reduced. Mount (1966) in a flow-through study showed that zinc was always
more toxic at a high pH than at a low pH, and further that water hardness was also an
important factor.
Dissolved Oxygen
The amount of dissolved oxygen (DO) present is one of the most significant chemical
parameters in the study of surface waters. The amount of oxygen that can be dissolved in water
at any one time is dependent upon (1) water temperature, (2) partial pressure of the oxygen in
the atmosphere in contact with the water, and (3) salinity.
Photosynthesis in algae and higher aquatic plants is one source of DO in natural waters. The
rate of photosynthesis depends on many factors but the major one is light. The depth that light
penetrates the water (euphotic zone) is determined by turbidity, color, and the absorptive effect
of the water itself. Another important source of oxygen is the atmosphere. Factors which will
influence the rate at which oxygen will dissolve into the water from the atmosphere include (1)
wave action, or other surface disturbances, (2) the difference in partial pressure between the
atmosphere and the water, and (3) the moisture content of the atmosphere.
There may be considerable diurnal and seasonal fluctuations in DO in a stream or lake
primarily due to changes in water temperature and photosynthetic rates. Water temperatures vary
from one season to another and deep lake water may vary considerably from the surface to the
bottom, e.g., during thermocline formation. Though photosynthesis does not occur at night,
aquatic plant respiration continues and oxygen is utilized. The amount of oxygen that is used in
aerobic biochemical action in the decomposition of organic matter (BOD) also causes extreme
fluctuations in DO available for aquatic organisms.
Oxygen requirements of fish and other aquatic organisms vary with the species and are
affected by age, degree of activity, size, prior acclimatization, and health of the organism.
Environmental factors influencing DO requirements or interfering with oxygen uptake are
temperature, pH, carbon dioxide, and dissolved solids. Temperature appears to be the major
factor because as the temperature increases, the metabolic rate of cold-blooded animals increases
along with oxygen uptake. At the same time, the solubility of oxygen in water decreases as
49
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temperature increases. This is discussed in excellent detail with a tabulation of the water
solubility of oxygen in Standard Methods (American Public Health Association, 1967).
Jones (1964) summarized the work of various investigators (Table 8) who conducted
laboratory studies on DO requirements of fish at various temperatures. Jones pointed out that
these figures were somewhat low compared with observations made in the field at similar
temperatures. It follows, however, that while fish may survive short periods of stress under
laboratory conditions, this does not mean they will be able to survive indefinitely, feed,
reproduce, grow, and compete with other organisms.
Doudoroff and Warren (1962) found that sublethal adverse effects of low DO on fish
included reduction in swimming speed and loss of weight. The gross efficiency of food conver-
sion was not greatly reduced in fish maintained on an unrestricted diet until the DO level
dropped below 4 ppm. The reduction in growth rate was attributed to loss of appetite. It was
also found that sac fry hatched from eggs in waters with a low DO content were small and weak.
A low level of DO may in itself be a lethal factor for various aquatic organisms and may
also cause an increased toxicity in a variety of chemicals. Several investigators have reported an
increase in the toxicity of chemicals due to decreased DO including various petroleum products
(Tagatz, 1961), unionized ammonia (Downing and Merkens, 1955), potassium dichromate
(Cairns, 1965), potassium cyanide (Downing, 1954; and Cairns, 1965) zinc, lead and copper salts
(Reiff, 1964), and various other inorganic salts (McKee and Wolf, 1963).
Suspended Solids and Turbidity
Turbidity may be defined as the degree of opaqueness produced in water by suspended
particulate matter. In much of the literature, turbidity and suspended solids (or suspensoids) are
used as synonyms. The particle size, shape, and refractive index have more influence on turbidity
than weight composition (American Public Health Association, 1967). The interplay of light on
the suspended material along with the reflection from the sky or bottom are also responsible for
the apparent color of the water. This is distinguished from true color which is derived from
substances in solution or in the colloidal state.
Turbidity is measured in Jackson turbidity units (JTU) which is the distance through a
column of water at which the image of a standard flame from a candle is no longer visible. The
standard unit is that condition produced by 1 ppm Fullers earth in distilled water. Turbidity has
a profound effect on natural light penetration which can be determined by the use of a
photronic cell or a Secchi disk. The measure of natural light penetration, however, is not a good
measure of turbidity because other factors affect light penetration including intensity, cloud
cover, water disturbance, and direction of the sunlight.
Suspended solids that occur naturally in water bodies include plankton, organic and
inorganic detritus, and silt. These suspended solids are augmented by a multitude of materials in
discharges from population centers, agricultural, and industrial sites. McKee and Wolfe (1963)
note that differentiation between suspended and settieable solids are often not clear because the
terms are sometimes confused in the literature. Until settled to the bottom, all settieable solids
are suspended solids and the rate of settling is dependent on quiescence, temperature, density,
flocculation, and otlier factors.
50
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TABLE 8. MINIMUM OXYGEN VALUES AT VARIOUS TEMPERATURES AT
WHICH FISH CAN EXIST UNDER LABORATORY CONDITIONS
(Jones, 1964)
Fish
Bleak
Blunt-nosed minnow
Brook trout
Brook trout
Brook trout
Brook trout
Brook trout
Brook trout
Brook trout
Brown bullhead
Brown trout
Brown trout
Brown trout
Brown trout
Brown trout
Brown trout
Brown trout
Carp
Carp (mirror)
Coho salmon
Coho salmon
Coho salmon
Dace
Eel
Goldfish
Goldfish
Goldfish
Perch
Rainbow trout
Rainbow trout
Rainbow trout
Rainbow trout
Roach
Salmon parr
Smallmouth bass
Steel-colored shiner
3-spined stickleback
Tench
Yellow perch
Yellow perch
Oxygen, ppm
0.68-1.44
2.25
2.0
2.2
2.5
1.52
2.4
2.5
1.35-2.35
0.3
1.13
1.16
2.13
2.8
1.28-1.6
1.64-2.48
2.9
1.1
0.59-2.5
1.3
1.4
2.0
0.57-1.1
1.0
0.5
0.6
0.7
1.1-1.3
2.4-3.7
2.5
0.83-1.42
1.05-2.06
0.67-0.69
2.0-2.2
0.63-0.98
2.25
0.25-0.50
0.35-0.52
2.25
0.37-0.88
Temperature, C
16
20-26
10
15
20
3.5
23
19-20
15.6
30
6.4
9.5-10
18
24
9.4
17.2
-
30
16
16
20
24
16
17
10
20
30
16
16
19-20
11.1
18.5
16
8
15-16
20-26
-
16
20-26
15.5
51
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Cairns (1967) described the adverse effects of suspended solids on aquatic biota and
acknowledged that the effects would vary with the species and stage of development. A brief
summary of this discussion follows:
(1) Reduction of light penetration - This may restrict the growth of photosynthetic
forms and, as they are the base of the food web, this could have widespread
effects on all other organisms.
(2) Mechanical or abrasive action - This is of particular importance to gill-breathing
organisms, such as fish and mussels, because gill impairment not only effects
respiration and excretion but may have other widespread metabolic effects.
(3) Blanketing action or sedimentation - This has a deleterious effect on fish
spawning sites and in fact may make large areas useless for spawning. Benthic
organisms which are a valuable food source for fish may be eradicated.
(4) Availability as a surface for growth of fungi and bacteria - The presence of
particulate matter may enable the environment to support substantially increased
populations of microorganisms.
(5) Adsorption and/or absorption of various chemicals — This may lead to a buildup
of toxic substances in a limited area with a possibility of sudden release.
(6) Reduction of temperature fluctuations — Probably of little importance since
particulate concentration would have to be extremely high.
Reduced light penetration will greatly influence productivity. Little plant or benthic
productivity can be expected when the turbidity exceeds 200 JTU (National Technical Advisory
Committee, 1968). Buck (Tarzwell, 1957) reported the average volume of net plankton in clear
ponds was eight times greater than from turbid ponds. Buck also stated (Fry, 1960) that
virtually no light is transmitted beyond three inches when suspended solids reach 150 ppm. Most
predacious fish feed by sight and in turbid waters have difficulty competing with such bottom-
feeder fish as carp, buffalo, and carpsuckers.
Heavier particles of suspended material will settle out and may in this way reduce benthic
production. Generally, benthic productivity increases with a change from fine to coarse
substrates. Only small amounts of sand and silt shifting in and around the gravel will eliminate
much of an area suitable for aquatic insects and other benthic organisms (Aquatic Life Advisory
Committee, 1956). Spawning sites for fish are greatly altered by silting, and fish eggs may not
receive enough oxygen when covered with fine sediments. A covering of silt may also prevent
metabolites from being washed away (Trama and Benoit, 1960).
Reviewing data from other investigations, Tarzwell (1957) stated that in order for
suspended solids to be directly harmful to fish the material must be present in very large
amounts. Herbert and Merkens (1961) exposed trout to suspensions of kaolin and diatomaceous
earth at concentrations of 270 ppm, and substantial numbers of the fish died. Concentrations of
90-100 ppm were less harmful and concentrations of 30 ppm had no observable effect. Wallen
(Aquatic Life Advisory Committee, 1956) reported that fish lived for at least short periods
(approximately a week) in silt concentrations of 100,000 ppm. The fish died in a few hours
when exposed to concentrations of 175,000 to 225,000 ppm.
52
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MacLeod and Smith (1966) found that the rate of metabolism and swimming endurance
were reduced in minnows exposed to sublethal concentrations (100-800 ppm) of suspended
wood fibers. Herbert and Richards (1963) reported reduced growth in trout kept in pulp
suspensions of 50 and 100 ppm for 40 weeks, but concluded that streams containing concentra-
tions of these suspended solids as high as 200 ppm and sometimes higher may support a
"reasonable" fish population. They also stated that a fishery is likely to be seriously harmed if
the average concentration is greater than 600 ppm.
Herbert, et al (1961) reported a reduction in numbers of trout in a stream polluted with
suspended solids (1000 ppm) which was the only polluting material in the stream. He attributed
trout reduction to effects on spawning sites, reduction in available food organisms, and some
harmful effects directly to the fish.
Smith, et al (1963, 1965, 1966) and Kramer and Smith (1966) have conducted a series of
studies on the effects of suspended material from industrial sites. They stated that fish in streams
receiving woodfiber wastes may suffer deleterious effects from exposure to sublethal concentra-
tions of suspended fibers. They further concluded that the effects of suspended fibers on fish
mortality would depend on the species of fish, type of wood fiber, processing method, DO,
concentration, and to a lesser degree, temperature.
When high concentrations of suspended solids are present, death of fish may be due to
clogging of the gills (Brown, 1957; Thompson, 1963; and McKee and Wolfe, 1935). Large
populations of planktonic organisms such as diatoms and protozoans may produce irritation of
fish gills, a condition referred to as sestonosis (Fry, 1960).
There is little information on the effect of turbidity on the toxicity of chemicals. Though
the effects of the turbidity are not known, many investigators acknowledge its importance and it
is often measured in both laboratory and field studies (see Appendices A and B). Wallen, et al
(1957) conducted toxicity studies on a variety of chemicals and carefully measured the turbidity
both before and after the tests. They concluded their paper by stating that it would be
important to determine if variations in turbidity would significantly affect the toxicity of
chemicals, especially those that react to reduce turbidity. Schoenthal (1963) found that
mortality in trout exposed to DDT was reduced when turbidity and alkalinity were increased.
This may have been due to adsorption of the DDT by the sediment. Brungs and Bailey (1966)
have shown that Endrin toxicity to fish is not greatly reduced unless a highly absorptive material
such as activated carbon is present.
Other Factors
Among other water quality factors affecting chemical toxicity in the aquatic environment,
water hardness and CO2 content are probably the most important.
Hardness of water is chiefly attributed to calcium and magnesium ions. Water containing
more than 40 ppm total hardness is generally considered hard water while less than this amount
indicates soft water. Hardness in natural water can also be correlated with dissolved solids, and
sometimes with alkalinity. Increased toxicity of the following chemicals has been reported for
hard water: antimony potassium tartrate (Tarzwell and Henderson, 1960), Dipterex (Henderson
and Pickering, 1968), and Fermate (Pickering and Henderson, 1966). Soft water increased the
toxicity of the following chemicals: Sarin (Pickering and Henderson, 1959), copper and zinc
(Sprague and Ramsay, 1965), fifteen metal compounds (Tarzwell and Henderson, 1960),
53
-------
hexavalent chromium (Trama and Benoit, 1960), methyl methacrylate, styrene and vinyl acetate
(Pickering and Henderson, 1966), zinc (Mount, 1966, and Cairns and Scheier, 1958), Cumate
(Pickering and Henderson, 1966), and copper sulfate (McKee and Wolfe, 1963). Water hardness
had little or no effect on the toxicity of the following chemicals: antimony trioxide (Tarzwell
and Henderson, 1960), ten organic phosphorus compounds (Henderson and Pickering, 1958,
1959), twelve petrochemicals (Pickering and Henderson, 1966), eight organic cyanides
(Henderson, et al, 1961), cyanide (Cairns and Scheier, 1963), and ten phosphorus and
chlorinated hydrocarbon pesticides (Pickering and Henderson, 1966).
Dissolved carbon dioxide is important in the aquatic environment, especially to plants.
Although a product of respiration, the amount of CO2 in the body of many animals determines
respiration rate. Its primary role in photosynthesis has long been known along with its
importance in the carbon-dioxide-bicarbonate system that determines the pH of many natural
bodies of water. Carbon dioxide can also affect the toxicity of chemicals in water. At concentra-
tions below 30 ppm, carbon dioxide is generally not toxic to fish. Above this level, it may be
limiting in various ways, or lethal at high concentrations depending on the fish species involved.
The effect of carbon dioxide on aquatic organisms is closely associated with DO and is mediated
largely by ambient water temperature. The significance of carbon dioxide in aquatic environs is
discussed fully by Brown, 1957; Doudoroff and Warren, 1962; Fry, 1960; Tarzwell, 1957; and in
Water Quality Criteria, 1968. No information was found on carbon dioxide enhancement of the
toxicity of chemicals, but when carbon dioxide is present in amounts sufficient to alter pH, this
is a distinct possibility.
Natural environmental factors that may affect chemical toxicity directly or indirectly by
contributing to water quality changes are:
(1) Air temperature - contributes to water temperature
(2) Solar irradiation and cloud cover — affects surface evaporation rate and water
temperature as well as varying incident ultraviolet which may photooxidize chemi-
cals in water
(3) Precipitation - diluting factor
(4) Wind speed and direction - affects atmospheric C>2 uptake of water by surface
roiling and also causes varied rates of mixing
(5) Solids and rock substrata - provide dissolved chemicals that primarily constitute
the chemical make-up of water
(6) Plant and animal detritus present in a body of water and from drainage areas -
provide suspended and dissolved solids and nutrients.
Another important part of the environment that may affect chemical toxicity but not one
created by nature, is the extremely wide diversity of water pollutants added to natural waters by
man. Synergistic or antagonistic effects can and do occur in dilute chemical concentrations.
Mixed pollutants are discussed briefly in the section Industrial Wastes.
54
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SECTION X
INDUSTRIAL WASTES
The problem of maintaining desirable water quality increases with advancing technological
development. One of the most serious water quality problems facing industry with respect to
effluent discharges is the effect of toxic wastes on aquatic life. The many substances carried in
solution and suspension determine whether water will be suitable for supporting aquatic
organisms. Chemical contents of some wastes may be freely soluble or miscible in water, such as
acids, alkalies, organic solvents, etc.; or nonsoluble, such as slurries from mining operations, soil
washings, or wood pulp fibers. Adverse effects may be direct and immediate or they may be
chronic and deleteriously affect the environment only gradually over a long period of time.
Mixed, the wastes may be synergistic or they may reduce the damaging effects each would have
individually (Garrett, 1957; Keup, et al, 1967; and Neel, 1963).
Complex wastes such as pulp mill effluents, wastes from oil refineries, and chemical plants
are neither constant in content nor in concentration and this further complicates tests to
determine their toxicities. Not only will a waste vary in toxicological and chemical characteristics
from day to day, but also within any given day variations will occur due to process changes, raw
materials, and end products. These wastes contain many known but often many unknown toxic
substances (Clemens and Clough, 1965; Keup, et al, 1967; and National Technical Advisory
Committee, 1968). Ellis in 1937 summarized the hazards of 30 common types of municipal and
industrial effluents. This list was republished 30 years later by Keup, et al (1967) as shown in
Table 9. No updating of this data summary or anything similar to it was found. For these
reasons, less emphasis was placed in the present study on acquiring mixed effluent data.
However, during the course of literature acquisition, considerable information on this subject
area was obtained. These are briefly abstracted in Table 10. Although merely a token selection of
papers on this subject, the abstracts serve to show the wide diversity of problems associated with
industrial waste effluents.
For research to be effective, the scientist must know the materials he works with. McKee
and Wolfe (1963) in their summaries of potential chemical pollutants discuss 39 chemicals as
originating from textile wastes, while another (Anon., 1966) listed 386 compounds. This type of
situation probably exists for most other industries. In all likelihood, even the latter listing is not
complete since some process changes have undoubtedly been made since 1966. One of the first
orders of business should be the establishment of listing of effluent components from industrial
plants. These listings should be continually updated.
55
-------
TABLE 9. USUAL FISHERIES HAZARDS OF 30 COMMON TYPES OF MUNICIPAL AND INDUSTRIAL EFFLUENTS(a) (ELLIS, 1937. FROM KFUP. ET AL. UUV7)
Changes in Water Affecting Fish
Hydrogen-Ion Concentration Increase in
Types of Wastes
Decrease in
Dissolved Oxygen
Increase in
Acidity
Increase in Specific
Alkalinity Conductance
Increase in
Turbidity
Increase in
Ammonia
Bottom Pollution Specilic Toxic
Blanket Action on Fishes
Mineral Wastes, Little Bacterial Action
I-rosion silt
Limestone sawmills
Asbestos works
Mine flotation
Coal- and iron-mine drains
(.rude oil
Salt water from oil wells
None
Possible
None
None
Possible
Critical
None
None
Possible
None
Possible
None
Moderate
None
Critical
Critical
None
None
Critical None
Possible
Possible to critical
Possible Possible
Possible to critical Possible to critical
None
Organic, Bacterial Action
Municipal sewage
Dairy industries
Packing plants
Canning factories
Breweries and distilleries
Beet sugar, pulp wastes
Paper pulp
Sawdust
Coal -gas wastes
Spent lubricants
Metal refineries
Laundries and wool washings
Steffens house waste
Sulphite pulp
Strawbound waste
Chemical works (1)
Chemical works (2)
Tanneries
Hye works
Bittern liquors
Tin-plate and wire mills
Starch factories
Cloth sizing
Critical
Possible to critical
Possible
None
Moderate
Moderate to critical
None
Possible
Moderate
Possible
None
None to possible
Possible to critical
Possible
Critical
Moderate
Critical
None to moderate
Critical
Possible
Possible
None
Possible
None
Critical
Possible to critical
None to moderate
Critical
Possible to critical
Possible
None
Possible
None to moderate
None
Possible
Chemical
Possible
None
Possible
Moderate to critical
Critical
Moderate to critical
Critical
None
Possible to critical
None to moderate
None
Possible
Moderate
Possible
Processes
Moderate
Possible
Moderate
Critical
Moderate
Critical
Moderate
Possible
Possible
Moderate
Possible
None
Possible
Moderate
1
Possible
None
Possible
None
None to possible
Possible
Moderate
Critical
Moderate
Critical
Possible
Critical
None
Possible
Moderate to critical
None
Possible
None
Possible to critical
None
Possible
Possible to critical Possible to critical
Possible
Critical
Possible to critical
Possible to critical
Critical Possible
Critical Critical
Possible to critical
Possible to critical Critical
Possible Possible
Critical
Possible to critical
None
Critical
Possible
None Possible to critical
Possible to critical
Possible
(a) Increases in both acidity and alkalinity are noted in some cases, due to the fact that two or more kinds of effluents are mixed,
in the stream after the effluent is added.
with one predominating at times, and to changes which take place
-------
TABLE 10. GENERAL COMMENTS ON SELECTED INDUSTRIAL EFFLUENTS
Type of Waste
Remarks
Reference
General
Industrial wastes
Organic wastes
Unspecified chemical
waste
Industrial wastes
Organic wastes
Industrial wastes
Organic wastes from
industrial sites
Industrial wastes
Industrial wastes
Various polluting
agents in rivers
A discussion of methods for studying toxicities of industrial wastes.
Bottom communities found in streams show characteristics reac-
tions to pollution, i.e., grossly polluted streams contain tubificid
and chironomids, etc. Various streams in New Zealand were
surveyed.
A complex chemical waste containing such toxicants as fluorides,
arsenic, copper, zinc, tin, lead, and S02 was shown to lower pH
and cause fish kill at a loading of about 0.5% of the waste in sea-
water at pH 5.5 and lower. Maximum toxicity occurred when
superphosphate was being produced.
Fifty percent reduction in photosynthesis in kelp resulted from
exposures to the following chemicals in four days:
Inorganic
Mercury 0.05 ppm
Copper 0.1 ppm
Nickel 2.0 ppm
Chromium 5.0 ppm
Chlorine 5.10 ppm
Zinc 10.0 ppm
Organic
Sodium pentachlorophenate 0.3 ppm
Zephiran chloride 1.0 ppm
Sodium dodecyl sulfate 5-10 ppm
Cresols 5-10 ppm
Phenol 10.0 ppm
Emulsified fuel oils 10-100 ppm
Evaluation was made of the various approaches to the problems of
organic pollution in tidal estuaries.
A summary of the ways in which industrial wastes may affect
aquatic life.
Stream had DO depletion for about a 45-mile stretch with heavy
loss of fish and plankton organisms.
Methods of studying industrial wastes are described.
An attempt is made to estimate future industrial discharges into
the Eems Estuary, The Netherlands.
A summary of problems arising from suspended solids, toxic
materials and nutrients from sewage pollution.
Heukelekian
(1948)
Hirsch
(1958)
Chanin and
Dempster
(1958)
Clendenning
and North
(1960)
Pyatt
(1964)
Neel
(1963)
George, et al
(1966)
Jackson and
B rungs
(1966)
Eggink
(1967)
Patrick
(1968)
57
-------
TABLE 10. (Continued)
Type of Waste
Remarks
Reference
Petroleum
Refinery wastes from:
Fractionation area
Cracking area
Lube oil treating area
Paraffin treating area
Acid plant area
Naphtha treating area
Fluid catalyst unit
Sulfuric acid alkylation
unit
Combination unit
Distillate tank drawoff
Oil field brine water
Oil field brine water
Oil field brine water
Petroleum products:
Gasoline
Diesel fuel oil
Bunker oil
Refinery effluent
Refinery effluent
(hydrogen sulfide
and phenolics)
Petroleum oil
Effects on bluegill, 24-hr TLm, % vol were: Turnbull, et al
Nontoxic: (1954>
31.0
Nontoxic:
37.0
3.1
75.0
3.1
0.4
29.0
12.0
Average number of aquatic species found in a stream with varying Clemens and
chloride concentrations was: Finnell
4-13,000-20,000 ppm (1957)
6 - 10,000-13,000 ppm
7- 8,000-10,000 ppm
8 - 4,000- 8,000 ppm
10- 1,000- 4,000 ppm
13- 1,000 ppm
The 24-hr TLm of fish at various concentrations of chlorides showed Wood
a marked reduction in deaths as the concentration neared 7,000 ppm. (1957)
One test at 7,000 ppm for 192 hr showed 90% survival.
Fundulus and Lagodon may survive salinities up to 2.7%. Leistomus Cole, et al
did well above 2.0%. (1958)
Effects on American shad, 48-hr TL^ (mg/1), were: Tagatz
91 (1961)
167
2417
Lethality increase was accompanied by low DO.
Based on 24-hr TLm, Lebistes reticulatus was most resistant fish of Bunting and
several tested. Irwing
(1965)
No correlation between sulfide concentration and lethal dosage to Clemens and
fish was found. For phenolics, the LDso for goldfish was 33.1%, Clough
LX>50 for red shiners was 18.8%, and LDso forDaphnia was (1965)
19.0% lower than that for red shiners.
Pollution resulted from an underground storage tank leak. At the McCauley
beginning, the concentration in the water was 221.3 ppm and (1966)
after one year, 1.4 ppm. Toxic effect was pronounced on micro-
fauna in sediments.
Note:
Further references on this general subject area includes papers by Copeland and Dorris (1964), Douglas, et al
(1960, 1962, 1963), Gould and Irwm (1965), Johnson (1968), Smith (1968), Tubb and Dorris (1965), Ward
and Irwin (1961), and Zobell (1964).
58
-------
TABLE 10. (Continued)
Type of Waste
Remarks
Reference
Pulp and Paper
Sulfite waste liquor
Sulfite waste
Kraft mill effluent
Sulphate waste liquor
Kraft mill effluent
Paper mill effluent
(chlorine)
Paper mill effluent
Sulphite waste liquor
Kraft mill effluent
Kraft mill effluent
Paper mill effluent
Sulfite waste
Pulp mill waste
Decrease in feeding rate in oysters was observed.
Marked avoidance by juvenile chinook salmon was observed with
little or no avoidance by juvenile coho salmon.
A 100% survival of young salmon was recorded in seawater with
effluent concentration under 4.8% with adequate oxygen.
Reduced DO in river water to 1.0 mg per liter was recorded.
Prawns and Apocryptes lanceolatus died in 3 minutes or less
when exposed to the waste liquor.
Live car bioassays showed wastes were lethal to game fish during
periods of high water temperature. In mid-July, pollution-
sensitive bottom fauna decreased from 54 to 17%.
A 13-hr TLm of 32% concentration of the effluent was obtained
for Salmo salar.
Silver salmon did not avoid sulfite liquor or kraft wastes in low
enough concentrations to be "safe". Toxicity data are too
numerous to summarize here.
In fluviarum experiments, avoidance reactions were exhibited
by Phoxinus phoxinus, Leuciscus rutilus, L. idbarus, Perca
fluviatilis, Coregonus nasus, Salmo salar, and Gasterosteus
aculeatus.
A significant decrease in Sphaerotilus natans growth was accom-
plished by the intermittent discharge of the waste using a five-
or six-day holding period with a one- or two-day release.
Induced spawning in mussels Mytilus edulis andM califomianus
was observed.
Maximum survival of walleye eggs above mill:
On bottom 1.2%; off bottom 49.1%
Maximum survival of walleye eggs below mill:
On bottom 1.2%; off bottom 3.5%.
The principal cause of mortality below the mill was Sphaerotilus
natans.
Regeneration studies of bisected planaria indicated:
At 550 ppm — no regeneration occurred
At 50 ppm - regeneration was 75% of control.
Histological examination of three species of fish showed decrease
in RNA, glycogen in liver, necrosis in kidney, and accelerated
secretion of mucus in gills. In bivalve livers, decrease in RNA
and glycogen occurred, and nuclei disappeared in kidney cells.
Galtsoff, et al
(1947)
Jones, et al
(1956)
Alderdice
and Brett
(1957)
Chowdhury
(1957)
Spindler and
Whitney
(1960)
Betts and
Wilson
(1966)
Holland, et al
(1960)
Hoeglund
(1961)
McKeown
(1962)
Breese, et al
(1963)
Smith and
Kramer
(1963)
Eng. Science,
Inc.
(1964)
Fujiya
(1965)
59
-------
TABLE 10. (Continued)
Type of Waste
Remarks
Reference
Pulp and Paper (Continued)
Sulfite wastes
Neutralized kraft
process effluents:
Brown stock screen-
ing and deckering
Recausticizing
Bleach plant
acid sewer
Bleach plant
caustic sewer
Neutralized whole
effluent
Unneutralized whole
effluent
Neutralized kraft pulp
bleach waste
Kraft effluent
Sewage
Sewage
Sewage
Sewage
Sewage
Sewage
Sewage
It was not clearly demonstrated that sulfite waste in the area
studied was the only cause of deaths of oysters, but it was con-
cluded that the amounts were sufficient to cause stresses which
may have long-term adverse effects.
Effects on guppies were: 96-hr TLm, % vol of effluent -
51.3
92.5
29.5
41.1
52.5
9.2
Reduced growth in sockeye and pink salmon alevins was found in
concentration of 1/10 to 1/20 the average 96-hr TLm.
A 75% concentration was required to kill 100% of Salmo salar in
less than lOhr.
This is a summary of the problems of toxic materials and nutrients
from sewage pollution.
A 10% concentration caused reduction on photosynthetic capacity
of kelp. A concentration of 1% gave no such indication.
Flagellates, protozoa, diatoms, and filamentous green algae showed
highest sensitivity to pollution while rotifers, Sarcodina, and
Volvocales were most tolerant.
A resume of sewage pollution of streams and beaches on Oahu.
Low surface productivity at point of discharge was observed.
Increase in productivity downstream in about 6 hr was recorded
with maximum values in about 10 hi. This was followed by a
decrease toward normal levels.
In samples of surface water from marine stations, the numbers of
Escherichia coli depended primarily on the amount of sewage
and direction of flow. Results varied enormously.
Woelke
(1965)
Howard and
Walden
(1965)
Servizi, et al
(1966)
Betts, et al
(1967)
Lackey
(1958)
Clendenning
and North
(1960)
Farmer
(1960)
Lam
(1964)
Calif. State
Water
Quality
Control
Board
(1965)
Bonde
(1967)
60
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TABLE 10. (Continued)
Type of Waste
Remarks
Reference
Suspended Solids
Suspended mineral
solids
China-clay
suspended waste
Suspended solids
Pulpwood fibers
Suspended conifer
groundwood
Suspended
groundwood
Conifer ground-
wood fiber
Suspended wood
fibers
Paper fiber sludge
Miscellaneous
Unspecified chem-
ical waste
Electroplating
wastes
Concentrations of 90 to 810 ppm made trout more susceptible to
other adverse factors in the environment.
Concentrations of 1000 ppm reduced abundance of brown trout
in an otherwise unpolluted stream. Suspensions of 60 ppm had
no observable adverse effects.
Laboratory experiments did not indicate that suspensions of
30 ppm kaolin and diatomaceous earth and suspensions of 50 ppm
wood fiber and coal-washery wastes make well-grown trout more
susceptible to disease.
Significant changes occurred in blood of fathead minnows exposed
to wood fibers. Increased hematocrit was highest for conifer
groundwood, followed by aspen groundwood, kraft conifer, and
sulfite conifer.
Survival of walleye fingerlings decreased when DO was reduced.
Rainbow and brown trout eggs survived in suspensions of 60,125,
and 200 ppm conifer groundwood. Trout alevins survival rate
decreased to a minimum of 0 in 250 ppm. The growth rate of
survivors was reduced.
Fathead minnows which were held for 96 hr in 0 to 2000 ppm
of aspen groundwood showed no effects to this exposure. A
similar series run in conifer groundwood showed increased
mortality at 738 and 2000 ppm.
Reduced growth was recorded for walleye fingerlings held in con-
centrations of 50 to 150 ppm.
Walleye eggs survived at concentrations of 250 ppm.
Low DO, high CO2, and presence of dissolved sulfides in streams
were recorded.
A complex chemical waste containing such toxicants as fluorides,
arsenic, copper, zinc, tin, lead, and S02 was shown to lower pH
and cause fish kill at a loading of about 0.5% of the waste in
seawater at pH 5.5 and lower. Maximum toxicity occurred
when superphosphate was being produced.
A midgefly, Cricotopus bicinctus, survived and matured in con-
centrations of chromium as great as 25 ppm, in copper at 2.2
ppm, and in cyanides at 3.2 ppm.
Herbert and
Merkens
(1961)
Herbert, et al
(1961)
Herbert and
Richards
(1963)
Smith, et al
(1965)
Smith and
Kramer
(1965)
Smith and
Kramer
(1965)
Smith, et al
(1966)
Kramer and
Smith
(1966)
Colby, et al
(1967)
Chanin and
Dempster
(1958)
Surber
(1959)
61
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TABLE 10. (Continued)
Type of Waste
Remarks
Reference
Miscellaneous (Continued)
Spent still liquors from
coal distillation
Smelter wastes
Acid mine drainage
Alkaline water
Lurgi process wastes
(bituminous coal)
Uranium mill wastes
Coal washer wastes
Uranium mine
Landfill pollution
Sulfuric acid water
Photographic wastes
Indications are that the toxicity of spent still liquors from the dis-
tillation of coal is mainly due to ammonia and monohydric phenols.
Near the smelter, the aquatic flora and productivity was greatly
reduced. Leptodictyum riparium and Eleocharis acicularis v.
submersa appeared to be the most tolerant organisms.
Twenty states have streams affected by acid mine drainage.
Pennsylvania has 2,906 miles of streams polluted with acid mine
drainage, Virginia has 1,150, and Kentucky has 590. The remain-
ing states have less than 300 each.
The pH of water passing through asbestos-cement pipeline was
increased to 9.5 with no immediate lethal effect on salmonids.
Treatment of effluent reduced permanganate value to less than
50 ppm and BOD to less than 25 ppm. The residual organic
matter had little direct toxic effect on fish.
The radioactive element in this study was radium; the nonradio-
active materials included sulfates, nitrates, chlorides, manganese,
iron, lead, arsenic, and various organics. These wastes were im-
portant in limiting aquatic biota below uranium mills. Changes
in composition of the wastes and water flow make it difficult to
calculate the radioactive and nonradioactive components of the
mill wastes.
As long as the coal washer wastes were intermittent, there was
little effect on biological productivity.
The effluent did not appear to have any adverse effect on plankton,
periphyton, benthos, and fish species other than trout (reduced
numbers).
Groundwater was polluted with CO2 from decomposing refuse
in a landfill.
Considerable reduction in survival percentage was found in
herring eggs and embryos at dilutions of 1:32,000.
Common chemicals found in these wastes are potassium ferri-
cyanide, sodium ferricyanide, boron, chromium, and sodium
thiosulfate. Release of this type of waste into streams and the
Los Angeles sewage system is discussed.
Herbert
(1962)
Gorham and
Gordon
(1963)
Kinney
(1964)
Sprague
(1964)
Cooke and
Graham
(1965)
Sigler, et al
(1966)
Charles
(1966)
Mitchum
and Moore
(1967)
Bishop, et al
(1967)
Kinne and
Rosenthal
(1967)
Hennessey and
Rosenberg
(1968)
62
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SECTION XI
EXTRACTED DATA - THE EFFECT OF
CHEMICALS ON AQUATIC BIOTA
Extracted information from originally published data are divided in two sections, both
alphabetically arranged by chemical name. One section (Appendix A) concerns listing by chemi-
cal name, and the other a similar listing by commercial designation (Appendix B). In all cases,
the chemical names and names (common or scientific) of organisms designated by the authors
were used in this compilation. None of the nomenclature was changed or corrected in any
manner, e.g., when authors used the common name of a fish, this and this alone was used. The
abbreviations and other designations are discussed later in this report section and described in
footnotes to the Appendices. In using the data compilations, care should be exercised in
searching varied alternative names for a given compound.
Since many papers contained large amounts of data, the most significant toxicity level was
chosen for inclusion in this compilation. In most cases, data presented at 96-hr TLm (designated
T4: T = TLm or TLso, and 4 = four days or 96 hours) were selected when available. With few
exceptions, the T value at 4 days was lower than the values for 1 or 2 days. The T4 value is
generally accepted as a realistic indication of toxic effect and the best one to use (lacking data
from chronic studies) in estimating safe levels for effluent release. Tl or T2 data were usually
not included unless these were the only data given. A and C following these designations indicate
acute or chronic bioassays, respectively. Since the data are presented as brief summaries, the
reader is referred to the original report for additional information. When ECso, LC5Q, and
LDSO*> were known or described as being concerned with lethal effects, these abbreviations were
judged to be essentially the same as TLm or TLso and designated as such (T) in the data
extracts for consistency. We acknowledge that this is not standard practice, and that there are
important differences in these designations.
The conditions noted by the researchers are designated by lower case letters. When the
conditions were controlled, these letters were underlined. In some cases, the authors briefly
referred to previous papers as a simple means for describing experimental conditions. No
underlines were made in these instances, although in all likelihood some conditions were
controlled.
Comments, in general, are brief, with the expectation that interested readers would consult
the original article for further information.
Since the chemical nature of most industrial effluents is very complex and seldom analyzed
or reported, there is little information on the effect of mixed effluents or mixtures of chemicals
in the data presented. For this reason, this document must be described merely as pertaining to
the effect of single chemicals or simple mixtures of chemicals on aquatic life.
There was no attempt to extract data from various reviews available, since these rarely
contained descriptive information concerning experimental conditions. Among others, the reader
is referred to:
*EC5o= median effective concentration, LCso = median lethal concentration, and LDso = median lethal dosage.
63
-------
American Public Health Assoc. (1960)
Anon.(1968)
Aquatic Life Advisory Committee (1955,
I960, 1967)
Averett and Brinck (1960)
Beak (1958)
Bick(1963)
Breidenback, et al (1967)
Breidenback and Lichtenberg (1963)
Brown (1961)
Burdick (1965)
Butcher (1959)
Butler (1966)
Buzzell, et al (1968)
Byrd (1960)
Carter (1962)
Cope (1963, 1965)
Cope and Springer (1958)
Cottam (1961)
Delaporte (1958)
Dewey (1958)
Doudoroff (1951)
Doudoroff and Katz (1950, 1953)
Faust and Aly (1964)
Ferguson (1967)
Ferguson, et al (1966)
Fromm (1965)
Fruh, et al (1966)
Ganelin, et al (1964)
George (1959)
Graham (1960)
Hawkes (1963)
Henderson and Tarzwell (1957)
Hirsch (1958)
Hoffman (1960)
Holden (1964, 1965)
Hughes and Davis (1967)
Hunt (1965)
Hynes(1966)
Ingram and Towne (1960)
Jackson (1966)
Johnson (1968)
Johnson, et al (1967)
Jones(1964)
Kerswill, et al (1960)
Keup, et al (1966, 1967)
King (1968)
Langer (1964)
Lawrence (1962)
Lloyd (1964, 1965)
MacMullen(1968)
Mackenthum and Ingram (1962, 1964)
Malina(1964)
McKee and Wolfe (1963)
McFarland (1959)
Moore (1967)
National Technical Advisory Committee
(1968)
Neel (1963)
Newsom (1967)
Nicholson (1959, 1967)
Nicholson, et al (1964)
Patrick (1968)
Powers (1918)
Reymonds (1962)
Rudolphs, et al (1950)
Ryckman, et al (1966)
Schoettger (1967)
Skidmore (1964)
Snow (1958)
Spiller (1961)
Sproul and Ryckman (1963)
Surber and Taft (1965)
Tarzwell (1959, 1962)
Water Pollution Control Federation
Research Committee (1958-1968)
Weaver, et al (1965)
Webb (1961)
Wilson (1968)
Doudoroff (1951) states that certain references with literature summaries are particularly
helpful in providing pertinent information published before 1954 on water pollutants toxic to
fish. These references are:
Redeke, H. C, "Report on the Pollution of Rivers and Its Relation to Fisheries",
Rapp. Conseil Permanent Intern. Exploration Mer, 43, 1 (1927).
Steinmann, P., "Toxikologie der Fische", Handbuch Binnenfischerei Mitteleuropas
(Germany), 6, 289 (1928).
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Heifer, H., "Giftwirkungen auf Fishe; ihre Ermittelung der Versuche und die
Bewertung der Ergebnisse", Kleine Mitt. Mitglied. Ver Wasser-Boden-u. Lufthyg., 12,
32 (1936).
Cole, A. E., "The Effects of Pollutional Wastes on Fish Life", in a Symposium on
Hydrobiology, University of Wisconsin Press, Madison, Wisconsin, 241 (1941).
Southgate, B. A., "Treatment and Disposal of Industrial Waste Water", Department of
Scientific and Industrial Research, London, England, 23 (1948).
Harnisch, O., "Hydrophysiologie der Tiere", in "Die Binnengewasser", Vol. 19, Ed. A.
Thienemann, Schweizerbart'sche, Erwin Nagele, Stuttgart, Germany (1951).
"Water Quality Criteria", California Water Pollution Control Board, Pub. No. 3,
Sacramento, California (1952). (Also, Addendum No. 1, 1954, and Pub. No. 3,
1963).
Not to demean past contributions from ecological investigators, but rather to suggest how
the data they develop in the future can be made more valuable for engineering application, it
may be stated that problems of interpretation encountered in this review would be minimized or
eliminated by the following:
• Positive identity of chemicals under test
• Precise description of test organisms
• Use of standard test methods, where applicable, or full details of procedure if
standard methods are not used
• Closer definition and control of test conditions.
Apparent differences in results among investigators of the same chemical on the same fish
species may have resulted from different methods of handling specimens prior to and during
tests, different stages in the life cycle of specimens, variations in physical and chemical properties
of the water, excursions in time-temperature pattern of exposures to the chemical, and different
methods of evaluating effects.
We believe the manner in which this report is compiled will serve the industrial community
and others as well. Since each reader will undoubtedly have a specific applied situation for using
the data, there was no attempt to summarize in narrative form the data for each compound. The
compilation gives pertinent data for each chemical for which information was found, tempered
by the comments on bioassay or field conditions, as well as providing a bibliography of the more
recent information available in the literature through 1968. Additionally, a Species Index is
presented in Appendix C and the chemical nature of commercial chemicals is given when
available in Appendix D.
In handling large numbers of references, an occasional document may be overlooked and
not included. The authors would sincerely appreciate being informed by the readers of such
omissions for the principal time period covered (1958-1968). An updating effort of this report is
now under consideration and will likely be completed by early 1972.
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SECTION XII
SUMMARY AND CONCLUSIONS
Fish, representing one of the highest trophic levels in the aquatic environment, are the
animals of choice in studying the toxicity of chemical effluents in natural waters. Their
importance is further emphasized since man may be the next highest trophic level where edible
fish are concerned. Furthermore, considering fish as indicator organisms, their presence probably
indicates that the water in which they survive is suitable for consumption or other uses by man,
except in some situations, for example, where a cumulatively toxic material is present in small
amounts and the fish develop resistance to that material.
With the magnitude of pollution problems today, standard fish bioassay procedures (par-
ticularly, flow-through) are adequate for the task at hand. This is especially true for evaluation
of chemicals that are acutely or immediately toxic although these procedures can also be used in
studying the chronic toxicity of chemicals at sublethal levels. These standard procedures must be
employed in conjunction with other evaluations, especially specific residue analyses, when a
chemical or ion causes a drastic problem such as a large-scale fish kill. The chronic continuous
flow exposure of fish is preferable for determining more precisely acceptable concentrations for
chemical release. TLm data should be a baseline for comparison of data from either type of
evaluation. Adequate reporting of data and experimental conditions, especially water quality
data, would greatly enhance the value of published information.
For field investigation of chemical toxicity in the aquatic environment, the in situ bioassay
is desirable. Exposure of native fish or highly sensitive fish from other sources would give a
better representation of the toxicity of a given chemical in a given situation. This should be
supplemented with chemical analysis of the effluent in question as well as a recording of
receiving water quality data. In situ evaluation of water from above and immediately below an
effluent addition could provide an elegant proof of lack of complicity in a fish kill by a
manufacturer.
With the present situation of gross pollution in many localities, study of fish responses
other than lethality are of little direct utility except in cases where a chemical has long-term,
sublethal effects, such as DDT and other chlorinated hydrocarbons. All such procedures would
be best employed in conjunction with standard bioassays so that appropriate comparisons can be
made. These procedures include:
(1) Observations of abnormal behavior
(2) Autopsy and histology
(3) Avoidance
(4) Growth retardation
(5) Radiotracers
(6) Effects on various life stages
(7) Spawning
(8) Swimming or cruising speed and oxygen consumption
(9) Blood studies
(10) Glucose transport
(11) Environment stress
(12) Thermal acclimitization
(13) Fish taste
(14) Conditioned avoidance response.
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ror a careful limnological approach in bioassay studies, several researchers have suggested
toxicity evaluations of aquatic organisms representing at least three trophic levels of the food
web. Fish would, of course, be one level. Another could be bioassay using D. magna and the
techniques described by Anderson (1944-1946, 1948, 1960). The third type of bioassay could be
with algae, using the technique of Palmer and Maloney (1955) or of Fitzgerald and Faust (1963).
BOD determination by the standard method (American Public Health Association, 1967) could
be another bioassay procedure. More rapid, alternative methods (e.g., STOD) are also available
for estimating BOD. BOD data alone can provide a useful index of toxicity or of oxygen
depletion in receiving water.
Marine bioassay utilizing various organisms primarily including fish, oyster, clams, and
shrimp in a flow-through type of system lags considerably behind reports of freshwater bioassays
in the amounts of data reported. The procedure is practical but could be improved upon by
maintenance of water temperature, DO, and other water factors. The sensitivity of shell regrowth
in bioassay and field studies of oyster (Crassostrea Virginia), clam (Mercenaria mercenaria), and
related marine mollusks to low concentrations of pesticides suggests that a bioassay using a
freshwater mollusc should be developed.
Reports on field studies of pollution problems include some of the classic examples of
disruption of the aquatic environment by polluting effluents and pesticide applications. Although
the results of such research are irrefutable in most instances, improvement is needed in recording
and reporting correlative data, e.g., water quality, weather, and other environmental factors.
Collecting devices are generally adequate for their designed purposes if used by experienced field
scientists, but some mechanical changes could improve collection and ease of manipulation in the
field.
Evaluation in the field in a given pollution situation can yield more realistic results than
evaluation by laboratory bioassay. Consider, for example, change in chemical toxicity due to
seasonal temperature change. This is the reason in situ bioassay (using live cars or wire cages and
plastic pools or raceways with suitable bioassay species in conjunction with automatic water
quality monitoring) appears to be the method of choice for an individual industry to evaluate
the effect of its particular effluent(s) on a given waterway.
The complex, highly interrelated factors in the aquatic environment may have profound
effect on the toxicity of a chemical. Of these, the most important are temperature, dissolved
oxygen, pH, turbidity (suspended solids), and water hardness. Their importance in aquatic studies
and their effect on chemical toxicity were discussed in some detail.
In addition to conclusions and comments made throughout this report, the following
remarks are made in direct response to the objectives outlined earlier in this report:
(1) Collect and summarize in standardized format the available information from the
scientific literature. The extracted data presented in Appendices A and B show
that there is a considerable lack of adequate reporting of experimental conditions
concerning the effect of chemicals on aquatic life. The complexity of factors in
both laboratory and field studies in aquatic biology is such that control or
description of them is most difficult. The specific effects of chemicals on
individual species of aquatic biota are voluminously shown in Appendices A and
B in a standardized format. A Species Index (Appendix C) facilitates assembling
all data for any given species. Procedural details and environmental factors
important in the observation or measurement of these effects are discussed in
appropriate sections of this report. Except for standard fish bioassays (static,
67
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continuous flow, and chronic exposures) and BOD, the wide variety of procedures
utilized for these studies were not discussed in detail. References are cited to
allow the individual reader to obtain these procedures when needed.
(2) Review the existing information on aquatic life as it is applicable or related to the
study of water pollution. The existing, more recent information on aquatic life as
it is applicable or related to the study of water pollution was reviewed. Discussion
of test species, lack of species variety identification, short-comings of procedural
details in reporting bioassay and field results, etc., is presented in various report
sections.
(3) Review the methodology used in studying the effects of chemicals on aquatic life.
Similarly, a review of the more important aspects of aquatic life methodology is
presented. Briefly, except for the standardized bioassays, experimental procedures
vary almost directly and specifically with the number of researchers reporting data
in the literature.
We believe the requirements described in the objectives for this study were fulfilled.
68
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SECTION XIII
RECOMMENDATIONS
We recommend:
(1) Establishment of a chemical pollution effect information-analysis center as a means of
continuously updating the information summarized here. This report has shown the large volume
of information available on the effects of chemicals on aquatic life. The amount of information
is unwieldy and difficult to work with. A computerized information-analysis center would be
capable of quickly identifying all pertinent data and would allow rapid preparation of reports
summarizing data on any chemical or group of chemicals in given situations for various aquatic
biota. Establishment of a prototype information center on analytical methodology related to the
aquatic environment is now in progress at Battelle's Columbus Laboratories. Bioassay data not
now published but held by individual manufacturers could be anonymously submitted for
inclusion into the information pool. Only data obtained by a standard procedure or a well-
described one would be included at the discretion of EPA and center personnel. We believe the
data base would be greatly expanded in this manner. The information content of this prototype
center is to be continually updated so that it would always be current as well as immediately
responsive as required.
As data are accumulated, the chances for predicting potential problems by mathematical
modeling and simulation of the effect of chemicals on aquatic life will be improved. This report
should provide a sound base for pursuing this approach.
(2) Preparation of listings of chemical constituents present in effluents by cooperative input
from the chemical industry. Data inputs could be submitted anonymously. The listings should be
continuously updated and made easily available to anyone who requests updated copies.
(3) Development of a standard pattern of laboratory evaluations, not limited to but
primarily based on fish bioassay, for estimating more accurately the effect of chemicals on
aquatic life. Data from such evaluations could then be used in mathematical modeling studies
which would be used for predicting chemical toxicity under widely varied environmental
conditions.
(4) Development of in situ field bioassay procedures for more realistic results than those
obtained from laboratory bioassays.
We suggest that researchers publishing in this field be encouraged to positively identify the
chemicals evaluated; to precisely describe test organisms; to use standard methods, if possible, or
to fully describe experimental procedures; and to more closely define and control experimental
conditions. This improved reporting would greatly enhance the utility of the data, and allow
more precise development of multivariate analyses and mathematical modeling for predictive
assessments of chemical pollution problems.
69
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SECTION XIV
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B.O.D. Part II. Water Sewage Works 105: 300-305.
Woelke, C. E. (1965). Bioassays of pulp mill wastes with
oysters. In: Biological problems in water pollution. Third
Seminar, 1962. U.S. Public Health Serv. Publ. No.
999-WP-25, pp. 67-77.
Woelke, C. E. (1967). Measurement of water quality with
the Pacific oyster embryo bioassay. In: Water quality
criteria. Philadelphia, Pa., Amer. Soc. Testing and Materials.
ASTM Spec. Tech. Publ. No. 416, pp. 112-120.
Wollitz, R. E. (1963). Effects of certain commercial fish
toxicants on the limnology of three cold-water ponds,
Montana. Proc. Montana Acad. Sci. 22: 54-81.
Wood, M. L. (1957). Biological aspects of stream pollution
control in Arkansas. Proc. 10th Ann. Conf., Southeast
Assoc. Game Fish Comm., pp. 136-138.
Woodwell, G. M., C. F. Wurster, and P. A. Isaacson. (1967),
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Workman, G. W. and J. M. Neuhold. (1963). Lethal concen-
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100
-------
SECTION XV
APPENDICES
A. EXTRACTED DATA FROM ORIGINAL PAPERS -
CHEMICALS AND MIXTURES OF CHEMICALS
B. EXTRACTED DATA FROM ORIGINAL PAPERS -
COMMERCIAL CHEMICAL PRODUCTS
C. SPECIES INDEX FOR APPENDICES A AND B
D. IDENTIFICATION OF COMMERCIAL CHEMICALS
-------
Note: Both scientific and common names should
be checked for complete retrieval of infor-
mation for a given organism.
-------
APPENDIX A
EXTRACTED DATA FROM ORIGINAL PAPERS -
CHEMICALS AND MIXTURES OF CHEMICALS
-------
Note: Names of chemicals and organisms are as given by the various authors. Readers should search for alternate, common, and/or scientific names of both
chemical and aquatic species; and refer to report section on Extracted Data for further discussion of this appendix.
Footnotes for Appendices A and B:
(1) Letters represent:
B = bioassay, used in combination with S = static, CF = continuous flow, A = acute, and CH = chronic.
L = laboratory bioassay.
BOD = biochemical oxygen demand.
F = field study, used in combination with R = river, stream, creek, etc., L = lake or pond, M = marine, E = estuarine, and O = other
(port facility, flooded area, etc.).
(2) Field location is indicated by abbreviation of the state or country.
(3) The number indicates ppm (mg/1), unless otherwise indicated by appropriate designations or (0). The letters within parentheses following indicate
T = TLm, K = kill, SB = sublethal effects, NTE = no toxic effect, or 0 = other. The number following these indicates the time in days at which
observations were made. ECso, LC5Q, and similar designations for 50 percent lethality were all considered as TLm and designated as such. The
numbers within parentheses following these designations indicate the time in days when the effect was observed.
(4) The following indicate (when underlined the variable was controlled):
a = water temperature
b = ambient air temperature
c = PH
d = alkalinity (total, phenolphthalein or caustic)
e = dissolved oxygen
f = hardness (total, carbonate, Mg, or CaO)
g = turbidity
h = oxidation-reduction potential
i = chloride as Cl
j = BOD, 5 day; (J) = BOD, short-term
k = COD
1 = nitrogen (as NO2 or NOs)
m = ammonia nitrogen as NH3
n = phosphate (total, ortho-, or poly)
o = solids (total, fixed, volatile, or suspended)
p = C02
-------
CHEMICALS
>
2
Q
X
H
3D
m
en
O
Tl
O
I
m
O
r-
3>
KJ
Chemical
Acetaldehyde
Acetaldehyde
Acetaldehyde
Acetaldehyde
Acetaldehyde
Acetaldehyde (al-
acetone (bl-
copper (c)-
acetic acid (d)
mixture
Acetamide
Acetanilide
Acetic
acid
Organism
Lagodon
rhomboides
Lagodon
rhomboides
Sewage
organisms
Lepomis
macrochirus
Nitzschia
linearis
Lepomis
macrochirus
Lepomis
macrochirus
Gambusia
affinis
Sewage
organisms
Daphnia
magna
Bioassay
or Field
BSA
BSA
BOD
BSA
BSA
BSA
BSA
BOD
BSA
Toxicity,
Active
Field Ingredient,
Location (2) ppm'3)
70.0 (T1 A)
70.0 (T1 A)
230 (TC5Q)
53.0 (T4A)
236.6-
249.1 (T5A)
53.0 (T4A)
(a) 5.2 (T4A)
(b) 5.2 (T4A)
(c) 1.04 (T4A)
(d) 26.0 (T4A)
26,300 (T2A)
(NTE)
150(0)
Experimental
Variables
Controlled
or Noted'4' Comments
a Aerated sea water was used.
— Experiments were conducted in aerated salt water.
a The purpose of this paper was to devise a toxicity index for
industrial wastes. Results are recorded as the toxic con-
centration producing 50 percent inhibition (TCsfj) of oxy-
gen utilization as compared to controls. Five toxigrams
depicting the effect of the chemicals on BOD were devised
and each chemical classified.
a c d e All fish were acclimatized for 2 weeks in a synthetic dilution
water.
ace The purpose of this experiment was to determine whether
there was a constant relationship between the responses of
these organisms. From the data presented, there was no
apparent relationship of this type. Therefore the authors
advise that bioassays on at least 3 components of the food
web be made in any situation.
a c d e All fish were acclimatized for 2 weeks in a synthetic
dilution water.
a c d e g The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
— The purpose of this paper was to devise a toxicity index for
industrial wastes. Results are recorded as the toxic con-
centration producing 50 percent inhibition (TCsg) of oxy-
gen utilization as compared to controls. Five toxigrams
depicting the effect of the chemicals on BOD were devised
and each chemical classified.
a e This paper deals with the toxicity thresholds of various sub-
stances found in industrial wastes as determined by the use
of D. magna, Centrifuged Lake Erie water was used as a
diluent in the bioassay. Threshold concentration was
defined as the highest concentration which would just fail
to immobilize the animals under prolonged (theoretically
infinite) exposure.
Reference
(Year)
Daugherty and
Garrett
(1951)
Garrett
(1957)
Hermann
(1959)
Cairns and
Scheier
(1968)
Patrick, et al
(1968)
Cairns and
Scheier
(1968)
Wallen, et al
(1957)
Hermann
(1959)
Anderson
(1944)
>
•o
m
z
__
X
>
-------
Acetic
acid
Acetic
acid
Acetic
acid
Acetic
acid
Acetic
acid
Acetic
acid
g
I
O
s
Acetic
acid
Acetic
acid
m
O)
Acetic acid (a)-
acetaldehyde (b)-
acetone (cl-
copper (d)-
mixture
Semotilus BSA
atromaculatus
Cylindrospermum L
lichen/forme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Gambusia BSA
affinis
Ictalurus BSA
punctatus
Channel BSA
catfish
(fingerlings)
Cu/ex sp BSA
(larvae)
Daphnia
magna
Lepomis
macrochirus
Lepomis BSA
macrochirus
Nitzschia BSA
linearis
Lepomis
macrochirus
Lepomis BSA
macrochirus
100 to 200 (CR)
2.0(0)
251 (T2A)
388 (T2A)
629 (K2)
446 (K1A)
1500 (T1A)
47 (T1A)
100 (T1A)
75 (T4A)
74 (T5A)
75 (T4A)
(a) 26.0 (T4A)
(b) 5.2 (T4A)
(c) 5.2 (T4A)
(d) 1.04 (T4A)
Test water used was freshly aerated Detroit River water. A
typical water analysis is given. Toxicity is expressed as the
"critical range" (CR), which was defined as that concentra-
tion in ppm below which the 4 test fish lived for 24 hr
and above which all test fish died. Additional data are
presented.
Observations were made on the 3rd, 7th, 14th, and 21st days
to give the following (T=toxic, NT=nontoxic, PT= partially
toxic with number of days in parentheses. No number
indicates observation is for entire test period of 21 days):
Cl -NT
Ma -NT
So -NT
Cv -NT
Gp-NT
Np-NT
a c d e g The effect of turbidity on the toxicity of the chemicals was
~~ studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
a c f i The experiment was conducted at 77 C.
Tap water was used. Considerable additional data are
presented.
"Standard reference water" was described and used as well
as lake water. Varied results were obtained when evalua-
tions were made in various types of water.
a c d e All fish were acclimatized for 2 weeks in a synthetic
dilution water.
ace The purpose of this experiment was to determine whether
there was a constant relationship between the responses of
these organisms. From the data presented, there was no
apparent relationship of this type. Therefore the authors
advise that bioassays on at least 3 components of the food
web be made in any situation.
a c d e All fish were acclimatized for 2 weeks in a synthetic
dilution water.
Gillette, et al
(1952)
Palmer and
Maloney
(1955)
Wallen, et al
(1957)
Clemens and
Sneed
(1958)
Clemens and
Sneed
(1959)
Dowden and
Bennett
(1965)
Cairns and
Scheier
(1968)
Patrick, et al
(1968)
Cairns and
Scheier
(1968)
m
z
O
-------
CHEMICALS
>
0
S
X
-i
3D
m
O
-n
O
m
3
o
r
^
Chemical
Acetone
Acetone
Acetone
Acetone
Acetone
Acetone
Acetone (al-
copper (bl-
acetic acid (c)-
acetaldehyde (d)-
mixture
Acetonitrile
2-acetylamino-
fluorene (AAF)
Organism
Daphnia
magna
Gambusia
af finis
Sewage
organisms
Daphnia
magna
Lepomis
macrochirus
Nitzschia
linearis
Lepomis
macrochirus
Lepomis
macrochirus
Pimephales
promelas
Lepomis
macrochirus
Lebistes
reticulatus
Zebrafish
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study'1' Location'2) ppm'3) or Noted'4'
BSA - 9280(0) ae
BSA - 1 3,000 (T2A) acdeg
BOD - (NTE) a
BSA - 10(T2A) ac
BSA - 8300 (T4A) a c d e
BSA - 1 1 ,493 to ace
11,727
(T5A)
8,300 (T4A)
BSA - (a) 5.2 (T4A) a c d e
(b) 1.04 (T4A)
(c) 26.0 (T4A)
(d) 5.2 (T4A)
BSA - (H+S) 1000 (T4A) cdef
(S) 1850IT4A)
(S) 1650 (T4A)
BSA - (0)
Comments
This paper deals with the toxicity thresholds of various sub-
stances found in industrial wastes as determined by the
use of D. magna. Centrifuged Lake Erie water was used as
a diluent in the bioassay. Threshold concentration was
defined as the highest concentration which would just fail
to immobilize the animals under prolonged (theoretically
infinite) exposure.
The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
The purpose of this paper was to devise a toxicity index for
industrial wastes. Results are recorded as the toxic concen-
tration producing 50 percent inhibition (TCsfj) of oxygen
utilization as compared to controls. Five toxigrams depict-
ing the effect of the chemicals on BOD were devised and
each chemical classified.
"Standard reference water" was described and used as well
as lake water. Varied results were obtained when evalua-
tions were made in various types of water.
All fish were acclimatized for 2 weeks in a synthetic
dilution water.
The purpose of this experiment was to determine whether
there was a constant relationship between the responses
of these organisms. From the data presented, there was
no apparent relationship of this type. Therefore the authors
advise that bioassays on at least 3 components of the food
web be made in any situation.
All fish were acclimatized for 2 weeks in a synthetic
dilution water.
(H) Value in hard water
(S) Value in soft water
The chemical caused no change in flavor of the cooked
bluegill.
The results of this investigation show that definite changes in
the concentration of RNA and glycogen accompany the cell-
ular disorganization in abnormal embryos induced by AAF.
In embryos treated with AAF, there was a consistent decrease
of RNA content of the liver, nervous tissue, sense organs, and
the mucosal lining of the digestive tract. In general, this only
occurred when concentrations of the chemical exceeded
O.O3 percent.
Reference
(Year)
Anderson
(1944)
Wallen, et al
(1957)
Hermann
(1959)
Dowden and
Bennett
(1965)
Cairns and
Scheier
(1968)
Patrick, et al
(1968)
Cairns and
Scheier
(1968)
Henderson, et al
(1960)
Hisaoka
(1958)
^
•o
m
g
^
-------
Acetyl phenyl-
hydrazine
Acrolein
Acrolein
Acrolein
Acrolein
Acrolein
Acrolein
Acrylaldehyde
(acrolein)
O
m
5
_l Acrylonitrile
C
30
m
O Acrylonitrile
-n
O
m
§
o
£
Microcystis
aeruginosa
Sewage
microorganisms
Oyster
Fundulus
similis
(juvenile)
Penaeus
aztecus
Crassostrea
virginica
Penaeus
aztecus
Fundulus
similis
Phytoplankton
Salmon
Potamogeton
modosus
Potamogeton
pectinatus
Elodea
canadensis
Lagodon
rhomboides
Lepomis
macrochirus
Pomoxis
annularis
BOD
BCF
BSA
BCFA&
BSA
BSA
BSA
BSA
BSA & CH
100 (K)
1.5(0)
0.055 (O)
0.24 (O)
0.19(0)
0.05 (O)
0.1 (O)
0.24 (T2CFA)
0.08 (T2A)
100(0)
100 (0)
100 (K4wk)
24.5(T1A)
0.05-0.1
(100%KS)
0.1-1.0
(100%KCH)
6.0-10.0
(100%KCH)
a, etc The chemical was tested on a 5-day algae culture, 1 x 106
~~ to 2 x 106 cells/ml, 75-ml total volume. Chu No. 10
medium was used.
— The chemical was studied as to how low levels (ppm) may
affect BOD in domestic sewage. The chemical was toxic
to sewage microorganisms at the level stated. To acclimated
organisms the toxicity was 1 8 ppm.
a The value reported is a 96-hr ECgrj (decreased shell growth).
a Water temperature was 21 C. The figure reported is a
48-hr EC50.
Toxicant chemicals were evaluated in seawater at tempera
tures averaging about 28 C. The values are for 24-hr
or enough to cause loss of equilibrium or mortality.
Seawater was pumped continuously into test aquaria.
Salinity, temperature, and plankton fluctuated with tide,
and ambient weather conditions. Some bioassays with
fish were static. Toxicity was reported for the following:
Oyster - 96-hr ECgrj — Cone, which decreased
shell growth.
Shrimp — 48-hr ECgrj — Cone, which killed or
paralyzed 50% of test animals.
Fish — 48-hr ECgg — Cone, which killed
50%.
Phytoplankton — Percent decrease of CO2 fixation to a
4-hr exposure at 1 .0 ppm chemical
concentration.
Data are given as
Experiments were conducted in standing water. Results
were rated on a scale of 0 to 10, 0 standing for no toxic
effect and 10 signifying a complete kill. Evaluation was
based on visual observation of the plant response at
weekly intervals for 4 weeks.
Injury rating of 8.3.
Injury rating of 9.6.
Aerated seawater was used.
Additional data are presented for less than 24 hr.
Fitzgerald, et al
(1952)
Oberton and
Stack
(1957)
Butler
(1965)
Butler
(1965)
Butler
(1965)
Butler
(1965)
Bohmont
(1967)
Frank, et al
(1961)
•o
m
D
X
Daugherty and
Garrett
(1951)
Renn
(1955)
-------
n
i
m
S
0
P Chemical
> Acrylonitrile
Z
O
S Acrylonitrile
X
C
3D
m
0
o Adipicacid
I
m
S
5
r- Adiponitrile
Alkyl aryl
bromide
!**
ON
Alkyl-dimethyl-
ammonium
chlorides
Alkyl
sulfate
Bioassay
or Field
Organism Study 11)
Lagodon BSA
rhomboides
Pimephales BSA
promelas
Lepomis
macrochirus
Lebistes
reticulatus
Lepomis BSA
macrochirus
Pimephales BSA
promelas
Lepomis
macrochirus
Lebistes
reticulatus
Cylindrospermum L
licheniforme (Cl)
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (Sol
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Cylindrospermum \_
licheniforme (Cl)
Gleocapsa
sp(G)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzchia
palea (Np)
Pimephales BSA
promelas
(juveniles)
Toxicity, Experimental
Active Variables
Field Ingredient, Controlled
Location^2) ppm<3) or Noted<4)
24.5(T1A)
(S) 18.1 (T4A) cdef
(H) 14.3 (T4A)
(S) 11.8 (T4A)
(S) 33.5 (T4A)
330 (T1A) a c
(S)1250(T4A) cdef
(H)820 (T4A)
(S) 720 (T4A)
(S) 775 (T4A)
2.0 (O) a_
2.0 (0) a_
- (5)5.1-5.9 acdf
(T1^A)
(H) 5.9-6.1
Comments
Experiments were conducted in aerated salt water.
(H) Value in hard water
(S) Value in soft water
The chemical did not change the flavor of the cooked
bluegill.
"Standard reference water" was described and used as
well as lake water. Varied results were obtained
when evaluations were made in various types of
water.
(H) Value in hardwater
(S) Value in softwater
The chemical produced no change in the flavor of the
cooked bluegill.
Observations were made on the 3rd, 7th, 14th, and 21st
days to give the following (T = toxic, NT = nontoxic,
PT = partially toxic with number of days in parentheses.
No number indicates observation is for entire test period
of 21 days):
Cl -NT
Ma -T
So - NT
Cv -NT
Gp- NT
Np-NT
Observations were made on the 3rd, 7th, 14th, and 21st
days to give the following (T = toxic, NT = nontoxic.
PT = partially toxic with number of days in parentheses.
No number indicates observation is for entire test period
of 21 days) :
Cl -PT(7)
G -NT
So - PT (7)
Cv - PT (3)
Gp- NT
Np - PT (3)
Syndets and soaps were of nearly equal toxicity in soft
water (S) but syndets were approximately 40X more
toxic than soap in hard water (H). The surfactant
Reference
(Year)
Garrett
(1957)
Henderson, et al
(1960)
Dowden and
Bennett
(1965)
Henderson, et al
(1960)
Palmer and
Maloney
(1955)
Palmer and
Maloney
(1955)
Henderson,
et al
(1959)
•o
m
Z
O
(T1-4A)
rather than the builder contained the toxicant.
Alkyl benzene sullste — See ABS in Appendix B.
-------
Aluminum
ammonium
sulfate
Aluminum
chloride
Aluminum
chloride
Aluminum
nitrate
Aluminum
potassium
sulfate
Daphnia
magna
BSA
190 (O)
Aluminum
sulfate
_ Aluminum
S sulfate
3D
O
•n
O
m
Gambusia
affinis
Daphnia
magna
Gasterosteus
aculeatus
Daphnia
magna
BSA
BSA
BSA
135IT2A)
<6.7 (S)
0.07 (K10)
BSA
206 (O)
Daphnia
magna
BSA
136(0)
Micropterus
salmoides
Lepomis
machrochirus
Goldfish
BSA
100(0)
100 (O)
100(0)
a e This paper deals with the toxicity thresholds of various Anderson
substances found in industrial wastes as determined by (1944)
the use of D. magna. Centrifuged Lake Erie water was
used as a diluent in the bioassay. Threshold concentration
was defined as the highest concentration which would
just fail to immobilize the animals under prolonged
(theoretically infinite) exposure.
a c d e g The effect of turbidity on the toxicity of the chemicals Wallen, et al
was studied. Test water was from a farm pond with (1957)
"high" turbidity. Additional data are presented.
a_ Lake Erie water was used as diluent. Toxicity given as Anderson
threshold concentration producing immobilization (1948)
for exposure periods of 64 hr.
— Solutions were made up in tap water. 3.0 to 5.0 cm Jones
stickleback fish were used as experimental animals. (1939)
This paper points out that there is a marked
relationship between the toxicity of the metals and
their solution pressures. Those with low solution
pressures were the most toxic.
a_ e This paper deals with the toxicity thresholds of various Anderson
substances found in industrial wastes as determined (1944)
by the use of D. magna. Centrifuged Lake Erie
water was used as a diluent in the bioassay.
Threshold concentration was defined as the highest
concentration which would just fail to immobilize
the animals under prolonged (theoretically infinite)
exposure.
a_ e This paper deals with the toxicity thresholds of various Anderson
substances found in industrial wastes as determined (1944)
by the use of D. magna. Centrifuged Lake Erie
water was used as a diluent in the bioassay. Threshold
concentration was defined as the highest concentration
which would just fail to immobilize the animals under
prolonged (theoretically infinite) exposure.
£ c f p i The disposal of cannery wastes frequently involves the Sanborn
use of chemicals for treatment purposes. Ferrous (1945)
sulphate, alum, and lime are used in chemical
coagulation ; sodium carbonate for acidity control in
biological filters; and sodium nitrate in lagoons for
odor control. Lye (sodium hydroxide) peeling of
certain fruits and vegetables is not uncommon.
These chemicals, in whole or part, are discharged
in most cases to a stream. The concentrations
listed permitted all fish to survive indefinitely.
I
m
O
-------
CHEMICALS
2
O
£
X
H
3)
m
C/)
O
•n
O
I
m
2
g
£i
^
oo
Chemical
Aluminum
sulfate
Aluminum
sulfate
p-aminodi-
ethylaniline
HCI
p-aminodi-
methylaniline
p-aminodi-
methylaniline
HCI
T?-(3-amino-
propyl)
rosinamine
D diacetate
(28 percent
active)
p-aminophenol
4-amino-m
toluene-
sulfonic
acid
Bioassay
or Field
Organism Study C"
Sewage BOD
organisms
Gambusia BSA
aff/nis
Microcystis L
aeruginosa
Microcystis L
aeruginosa
Microcystis L
aeruginosa
Cylindrospermum L
licheniforme (CD
Microcystis
aeruginosa (Mai
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Daphnia BSA
magna
Gambusia BSA
affinis
Toxicity,
Active
Field Ingredient,
Location'?) ppm(3)
18.0 (0)
240 (T2A)
100 (K)
100 (K)
100 (K)
2.0 (O)
2 (K2A)
- 410(T2A)
Experimental
Variables
Controlled
or Noted'4' Comments
— Various metal salts were studied in relation to how they
affected the BOD of both raw and treated sewage as
well as how they affected the processing of sewage
in the treatment plant. BOD was used as the
parameter to measure the effect of the chemical.
The chemical concentration cited is the ppm required
to reduce the BOD values by 50%. This chemical
was tested in an unbuffered system.
a c d e g The effect of turbidity on the toxicity on the chemicals
was studied. Test water was from a farm pond with
"high" turbidity. Additional data are presented.
a , etc The chemical was tested on a 5-day algae culture.
1 x 1Q6 to 2 x 10^ cells/ml, 75 ml total volume.
Chu No. 10 medium was used.
a , etc Comment same as above.
a , etc Comment same as above.
a Observations were made on the 3rd, 7th, 14th, and 21st
days to give the following (T = toxic, NT = nontoxic,
PT = partially toxic with number of days in parentheses.
No number indicates observation is for entire test period
of 21 days):
Cl -T(14)
Ma-T
So - PT
Cv -T(14)
Gp-T
Np-T
a An attempt was made to correlate the biological
action with the chemical reactivity of selected
chemical substances. Results indicated a considerable
correlation between the aquarium fish toxicity and
antiautocatalytic potency of the chemicals in marked
contrast to their toxicity on systemic administration.
a c d e g The effect of turbidity on the toxicity of the chemicals
was studied. Test water was from a farm pond with
"high" turbidity. Additional data are presented.
Reference
(Year)
Sheets
(1957)
Wallen, et al
(1957)
Fitzgerald, et al
(1952)
Fitzgerald, et al
(1952)
Fitzgerald, et al
(1952)
Palmer and
Maloney
(1955)
Sollman
(1949)
Wallen, et al
(1957)
^
TJ
m
Z
O
X
-------
Ammonia
Trout
BSA
(O)
Ammonia
Ammonia
(unionized)
Ammonia
Ammonia
Ammonia
m
Ammonia
X
C
•3)
m
o
m
2
9
Pimepha/es
promelas
Salmo
gairdnerii
Salmo
gairdnerii
Gambusia
affinis
BSA
BSA
(H) 8.2 (T4A)
(S) 5.9 (T4A)
0.4 (T1A)
cdef
a b c d e
BSA
100-200 (O)
a c e p
BSA
(O)
a cd i
Green
sunfish
Abramis
brama
Perca
fluviatillis
Flu til is
ru tilis
Scardinius
erythrophthalmus
Salmo
gairdnerii
BSA
(O)
BCF
0.41 (T7CF)
0.29 (T7CF)
0.35 (T5CF)
0.36 (T6CF)
0.41 (T2CF)
a cd e f
No quantitative data are reported. 30 ppm of
nitrogen was added as ammonium chloride.
Carbon dioxide in concentrations up to 30 ppm
reduced the toxicity of the ammonia by lowering
the pH of the water. Concentrations of 60 ppm of
CO2 were toxic but not lethal when the
concentration of dissolved oxygen was low. A
concentration of 240 ppm of CO2 was lethal to
trout in little more than one hour.
(H) Value in hardwater
(S) Value in softwater
Toxicity of ammonia or of ammonium salts was
increased by a rise in pH value from 7.0 to 8.2.
Toxicity of such solutions to fish apparently
depended upon the concentration of the un-
ionized ammonia molecule present. Variation
was attributed to the increase in the concen-
tration of free carbon dioxide at the gill surfaces.
The major factor determining the toxicity of ammonia
is the pH of the water. Temperature, dissolved oxygen,
and bicarbonate alkalinity are also important. Only
unionized ammonia was toxic to fish.
At a pH of 7.0 the threshold value for ammonia ranges
between 100 and 200 ppm (as N), depending on the
bicarbonate hardness.
The pH value and temperature had a marked effect
upon the toxicity of ammonia solutions. As the
pH was raised, the toxicity increased markedly.
The concentration of unionized ammonia present
in each test was calculated using the mean temper-
ature and the pH value. The absence of toxic action
by tests at a total ammonia concentration equivalent
to 120 mg/IN.
Ammonia or ammonium hydroxide was found to repel
fish at 8.5, 10, and 20 mg/l. At 1.7 mg/l no repellency
was noted. In concentrations of 10 and 22 mg/l,
ammonia killed the fish in repellent studies before they
had the opportunity to move out of the area containing
the substance.
The T at LC5Q values are asymptotic values of undissociated
ammonia (mgN/l). Additional data are presented.
Herbert
(1955)
Henderson, et al
(1960)
Lloyd and
Herbert
(1960)
Lloyd
(1961)
Hemens
(1966)
Summerfelt
and Lewis
(1967)
Ball
(1967)
-------
CHEMICALS
Z
0
5
X
C
3)
m
O
Tl
O
m
3
o
£
^>
,* .
0
Chemical
Ammonia
Ammonia
Ammonia
(unionized)
Ammonia
(unionized)
Ammonia plus
carbon
dioxide
Ammonium
acetate
Ammonium
borofluoride
Ammonium
carbonate
Organism
Salmo
gairdneri
Salmo
gairdneri
Salmo
gairdnerii
Salmo
gairdnerii
Perca
fluviatilis
Rutilus
rutilus
Gobio
gobio
Rainbow
trout
Gambusia
af finis
Sewage
organisms
Gambusia
affinis
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study!"1' Location(2) ppm*3) or Noted<4' Comments
BSA — (O) a c 1 m After 24-hr exposure the mean blood levels for total ammonia
showed a direct linear correlation with ambient ammonia
and ranged from 38 to 70 g/ml. Fish exposed to 0-1 g/ml
nonionic ammonia had mean blood levels which ranged
from 0.6 to 1 .3 g/ml. Ammonia in concentrations up to
10 g NH3/ml was found to have no significant effect on the
ability of hemoglobin to combine with oxygen in vitro.
BSA - 34-47 (T2A) acdefo The concentration killing a half batch of fish in 2 days pro-
vides a reasonable estimate of the threshold concentra-
tion. The lethality of this chemical depends upon all the
experimental variables listed and the concentration of
undissociated ammonia which is present.
FR Stevenage (O) acelm Survival of rainbow trout in concentrations of unionized
Herts. ammonia in the range of 0.86-1 .96 ppm of nitrogen in-
creased as the concentration of dissolved oxygen was
raised from 1 .5 to 8.5 ppm. The effect of dissolved oxy-
gen in increasing survival time was greater in the lower
concentrations of unionized ammonia.
BSA — (O) a c e o p The resistance to rapidly lethal concentrations of un-
ionized ammonia ranging from about 2.0 to 8.8 ppm
nitrogen was determined in tensions of dissolved oxygen
53.4 and 96.7% of air saturation value at 1 5.2 C.
Period of survival decreased with rise in concentration of
unionized ammonia. The effect of oxygen tension on
period of survival was greatest in the lowest concentra-
tions of unionized ammonia.
BSA — (O) a e m n The reduction of toxicity of ammonia solutions by the
addition of carbon dioxide, was due to lowering the
pH of the solution. 60-240 ppm CO2 in solution was
toxic within 1 2 hr. 30 ppm ammonia nitrogen was
toxic, but up to 30 ppm CO2 increased fish survival time.
BSA - 238 (T2A) a c d e g The effect of turbidity on the toxicity of the chemicals
was studied. Test water was from a farm pond with
"high" turbidity. Additional data are presented.
BOD — 87.0(0) — Various metal salts were studied in relation to how they
affected the BOD of both raw and treated sewage as well
as how they affected the processing of sewage in the
treatment plant. BOD was used as the parameter to mea-
sure the effect of the chemical. The chemical concentra-
tion cited is the ppm required to reduce the BOD values
by 50%. This chemical was tested in an unbuffered system.
BSA — 238 (T2A) a c d e g The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
Reference
(Year)
Fromm and
Gillette
(1968)
Brown
(1968)
Downing and
Merkens
(1955)
Markens and
Downing
(1957)
Alabaster and
Herbert
(1954)
Wallen.et al
(1957)
Sheets
(1957)
Wallen, et al
(1957)
^
•o
m
Z
g
X
j,,
-------
Ammonium
chloride
Ammonium
chloride
Ammonium
chloride
Ammonium
chloride
Ammonium
chloride
Ammonium
chloride
o
m
D
2
C
3D
w Ammonium
° chloride
O
m Ammonium
M chloride
Carass/us
carass/us
Daphnia
magna
BSA
BSA
Salmo
gairdnerii
BSA
Daphnia
magna
Lepomis
macrochirus
Daphnia
magna
BSA
BCFA
BSA
Gambusia
affinis
Lepomis
macrochirus
BSA
BSA
(O)
<134(O)
a e
(O) Tap water
1000 ppm —
27.3 min
1000 ppm —
52.5 min
50 ppm —
>1000 min
Distilled water
3000 ppm —
292 min
1000 ppm —
725 min
100 ppm >
4320 min
91 (S)
6.0 (T4A)
a c e f
a ce f
246,6 (O)
510 (T2A)
7.7 (T4A)
a cd e g
a cd e i
This old, lengthy paper discusses toxicity of many chem-
icals, possible mechanism of action of some, the effect of
temperature, effect of dissolved oxygen, the efficiency of
the goldfish as a test animal, compares this work with
earlier work, and lists an extensive bibliography.
In 0.224N solution, fish survived 99 minutes.
This paper deals with the toxicity thresholds of various
substances found in industrial wastes as determined by the
use of D. magna. Centrifuged Lake Erie water was used as
a diluent in the bioassay. Threshold concentration was de-
fined as the highest concentration which would just fail to
immobilize the animals under prolonged (theoretically
infinite) exposure.
Tap or distilled water used as diluent. Toxicity defined as
the average time when the fish lost equilibrium when
exposed to the test chemical (ppm ammonia).
Lake Erie water was used as diluent. Toxicity given as
threshold concentration producing immobilization for
exposure periods of 64 hr.
Test water was composed of distilled water with CP grade
chemicals and was aerated throughout the 96-hour
exposure period.
Toxicity was dependent upon the concentration of un-
dissociated NH4OH which is dependent upon pH. The
initial pH was 9.0 and after four days it was 7.5.
The primary aim of this study was to determine the effects
of lowered dissolved oxygen concentration upon an
aquatic invertebrate when exposed to solutions of in-
organic salts known to be present in various industrial
effluents. Analysis of data conclusively shows the
D. magna tested under lowered oxygen tension exhibited
lower threshold values for the chemicals studied than
when tested at atmospheric dissolved oxygen.
The effect of turbidity on the toxicity of the chemicals
was studied. Test water was from a farm pond with
"high" turbidity. Additional data are presented.
A "control" was prepared by adding required chemicals
to distilled water, and this was constantly aerated. Data
reported are for larger fish, 14.24 cm in length. Data
for smaller fish are also in the report.
Powers
(1918)
Anderson
(1944)
Grindley
(1946)
Anderson
(1948)
Cairns and
Scheier
(1955)
Fairchild
(1955)
Wallen,et al
(1957)
Cairns and
Scheier
(1959)
-------
CHEMICALS
>
0
s
x
c
3)
m
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O
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3
5
c;
j
Chemical
Ammonium
chloride
(as N)
Ammonium
chloride
(as N)
Ammonium
chloride
Ammonium
chromate
Ammonium
dichromate
Ammonium
hydroxide
Ammonium
hydroxide
Ammonium
hydroxide
(as ammonia)
Ammonium
hydroxide
Ammonium
hydroxide
Organism
Rainbow trout
Salmo
gairdnerii
Carassius
carassius
Daphnia
magna
Lepomis
macrochirus
Lymnaea sp
(eggs)
Gambusia
affinis
Gambusia
affinis
Daphnia
magna
Gasterosteus
aculeatus
Semotilus
atromaculatus
Gambusia
affinis
Fish
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study'1) Location'2) ppm'3) or Noted'4)
BSA - (O) acd
BSA - 24.6 (T2A) a c d f
BSA - 202 (T1 A) ac
161 (T2A)
50 (T4A)
139 (T4A)
725 (T1-4A)
241 (T1A)
173 (T2A)
70 (T4A)
BSA - 270 (T2A) a c d e g
BSA - 212IT2A) acd eg
BSA - <8.75 (O) a e
BSA - (O) ce
BSA - 5to15(CR) ae
BSA - 37 (T2A) a c d e g
BSA - 4.3 x 10'5 M (K) ac
Comments
The 48-hour LD$Q of ammonium chloride (as N) as interpo-
lated from three graphs may be 30, 24, or 12 ppm. The
effect of dissolved oxygen is also discussed.
A mathematical equation was derived to explain the com-
bined toxicities of this salt and zinc sulfate.
"Standard reference water" was described and used as well
as lake water. Varied results were obtained when evalua-
tions were made in various types of water.
The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
Comment same as above.
This paper deals with the toxicity thresholds of various
substances found in industrial wastes as determined by the
use of D. magna. Centrifuged Lake Erie water was used as
a diluent in the bioassay. Threshold concentration was
defined as the highest concentration which would just fail
to immobilize the animals under prolonged (theoretically
infinite) exposure.
Tap water was used to make up the solutions. The fish
avoided concentrations of 0.04 and 0.01 N, but seemed
attracted to concentrations of 0.001 and 0.0001 N.
Test water used was freshly aerated Detroit River water.
A typical water analysis is given. Toxicity is expressed as
the "critical range" (CR), which was defined as that con-
centration in ppm below which the 4 test fish lived for
24 hr and above which all test fish died. Additional
data are presented.
The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
Avoidance behavior of test fish to toxic chemicals is given.
Toxicity is given as the lowest lethal concentration (molar).
Ratios of avoidance and lowest lethal concentration are
presented and discussed.
Reference
(Year)
Herbert
(1961)
Herbert and
Shurben
(1964)
Dowden and
Bennett
(1965)
Wallen, et al
(1957)
Wallen, et al
(1957)
Anderson
(1944)
Jones
(1948)
Gillette, et al
(1952)
Wallen, et al
(1957)
Ishio
(1965)
^
•o
m
z
g
x
^
-------
Ammonium
hydroxide
Ammonium
nitrate
Ammonium
salt
Ammonium
salts
Ammonium
sulfate
Ammonium
2 sulfate
m
5
2
z
o
g Ammonium
JJ sulfate
C
3
m
w
O
-n
Daphnia
magna
Caress/us
carassius
Nitzschia
linearis
Physa
heterostropha
Lepomis
macrochirus
Salmo
gairdnerii
BSA
BSA
BSA
BSA
Daphna
magna
BSA
Daphnia
magna
BSA
Salmo
gairdnerii
BSA
60 (T1A)
32 (T2A)
20 (T4A)
(O)
420 (T5A)
90.0 (T4A)
3.4 (T4A)
(0)
<106(O)
288.5 (O)
(O) Tap water
1000 ppm —
29.8 min
Distilled water
3000 ppm —
318 min
1000 ppm —
847 min
100 ppm
>5760 min
a c e f
"Standard reference water" was described and used as well Dowden and
as lake water. Varied results were obtained when evalua- Bennett
tions were made in various types of water. (1965)
This old, lengthy paper discusses toxicity of many chem- Powers
icals, possible mechanism of action of some, the effect of (1918)
temperature, effect of dissolved oxygen, the efficiency of
the goldfish as a test animal, compares this work with
earlier work, and lists an extensive bibliography.
In 0.213N solution, fish survived 78 minutes.
The purpose of this experiment was to determine whether Patrick, et al
there was a constant relationship between the responses (1968)
of these organisms. From the data presented, there was
no apparent relationship of this type. Therefore the
authors advise that bioassays on at least 3 components of
the food web be made in any situation.
This is a study of the effect of varying dissolved oxygen Lloyd
concentrations on the toxicity of selected chemicals. (1961)
The toxicity of heavy metals, ammonia, and monohydric
phenols increased as the dissolved oxygen in water was
reduced. The most obvious reaction of fish to increase
the volume of water passed over the gills, and this may
increase the amount of poison reaching the surface of
the gill epithelium.
The concentration of the chemical in the water was not
specified.
This paper deals with the toxicity thresholds of various Anderson
substances found in industrial wastes as determined by (1944)
the use of D. magna. Centrifuged Lake Erie water was
used as a diluent in the bioassay. Threshold concentra-
tion was defined as the highest concentration which
would just fail to immobilize the animals under prolonged
(theoretically infinite) exposure.
The primary aim of this study was to determine the effects Fairchild
of lowered dissolved oxygen concentration upon an (1955)
aquatic invertebrate when exposed to solutions of inor-
ganic salts known to be present in various industrial
effluents. Analysis of data conclusively shows the
D. magna tested under lowered oxygen tension exhibited
lower threshold values for the chemicals studied than
when tested at atmospheric dissolved oxygen.
Tap or distilled water used as diluent. Toxicity defined as Grindley
the avg. time when the fish lost equilibrium when ex- (1946)
posed to the test chemical (ppm ammonia).
m
O
X
-------
CHEMICALS
2
O
5
X
c
-»1
JU
m
en
O
-n
O
m
S
O
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1
-f^
Chemical
Ammonium
sulfate
Ammonium
sulfate
Ammonium
sulphate
Ammonium
sulfide
Ammonium
sulfite
Ammonium
sulfite
Ammonium
thiocyanate
Amyl acetate
N-amyl-acetate
n-amyl alcohol
t-amyl alcohol
Aniline
Organism
Gambusia
affinis
Daphnia
magna
Biomorpholaria
a. alexandrina
Bulinus
truncatus
Gambusia
affinis
Gambusia
affinis
Daphnia
magna
Gambusia
affinis
Semotilus
atromaculatus
Gambusia
affinis
Semoti/us
atromaculatus
Semoti/us
atromaculatus
Daphnia
magna
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study'1' Location'2' ppm'3' or Noted'4'
BSA - 1 ,400 (T2A) a c d e g
BSA - 423 (T1 A) ac
433 (T2A)
292 (T4A)
BSA - 800 (K1 A) a
300 (K1A)
BSA - 248 (T2A) a c d e g
BSA - 240 (T2A) a c d e g
BSA - 299 (T1 A) ac
273 (T2A)
203 (T4A)
BSA - 420 (T2A) a c d e g
BSA - 50to120(CR) ae
BSA - 65 (T2A) acdeg
BSA - 350 to 500 (CR) a e
BSA — 1 ,300 to 2,000 a e
(CR)
BSA - 279 (O) a c
Comments
The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
"Standard reference water" was described and used as well
as lake water. Varied results were obtained when evalua-
tions were made in various types of water.
The degree of tolerance for vector snails of biharziasis chem-
icals is somewhat dependent upon temperature. The tem-
perature at which (K1 A) occurred was 28 C.
The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
Comment same as above.
"Standard reference water" was described and used as well
as lake water. Varied results were obtained when evalua-
tions were made in various types of water.
The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
Test water used was freshly aerated Detroit River water.
A typical water analysis is given. Toxicity is expressed as
the "critical range" (CR), which was defined as that con-
centration in ppm below which the 4 test fish lived for
24 hr and above which all test fish died. Additional data
are presented.
The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
Test water used was freshly aerated Detroit River water.
A typical water analysis is given. Toxicity is expressed as
the "critical range" (CR), which was defined as that con-
centration in ppm below which the 4 test fish lived for
24 hr and above which all test fish died. Additional data
are presented.
Comment same as above.
This paper deals with the toxicity thresholds of various sub-
stances found in industrial wastes as determined by the
use of D. magna. Centrifuged Lake Erie water was used
as a diluent in the bioassay. Threshold concentration was
defined as the highest concentration which would just
fail to immobilize the animals under prolonged (theoreti-
cally infinite) exposure.
Reference
(Year)
Wallen, et al
(1957)
Dowden and
Bennett
(1965)
Gohar and
EI-Gindy
(1961)
Wallen, et al
(1957)
Wallen, et al
(1957)
Dowden and
Bennett
(1965)
Wallen, et al
(1957)
Gillette, et al
(1952)
Wallen, et al
(1957)
Gillette, et al
(1952)
Gillette, et al
(1952)
Anderson
(1944)
>
TJ
m
z
D
X
>
-------
Aniline
Aniline
hydrochloride
° Barium
3 chloride
c
3)
in
O Barium
jrj chloride
Microcystis
aeruginosa
Daphnia
magna
BSA
Antimony
potassium
tartrate
Antimony
trichloride
Antimony
trichloride
Antimony
trioxide
, Arsenite
*
i
Barium
carbonate
Barium
;» chloride
Pimephales
promelas
Daphnia
magna
Pimephales
promelas
Pimephales
promelas
Lepomis
macrochirus
(eggs)
L. cyanellus
(eggs)
Micropterus
dolomieui
(eggs)
Gambusia
affinis
Carassius
carassius
BSA
BSA
BSA
BSA
BSA
BSA
Daphnia
magna
BSA
50 (K)
5.5 (K2)
12 (T4A) H
20 (T4A) S
37 (S)
17 (T4A) H
9 (T4A) S
>80 (T4A) H
>80 (T4A) S
15/7 (O),
8 (NTE)
15 (NTE),
8 (NTE)
15/6(O),
8 (NTE)
10,000 (T2A)
(O)
<83 (O)
Daphnia
magna
BSA
29(0)
a The chemical was tested on a 5-day algae culture, 1x10^
~~ to 2 x TO*3 cells/ml, 75 ml total volume. Chu No. 10
medium was used.
a An attempt was made to correlate the biological action with
the chemical reactivity of selected chemical substances.
Results indicated a considerable correlation between the
aquarium fish toxicity and antiautocatalytic potency of
the chemicals in marked contrast to their toxicity on
systemic administration.
a c d f Both hard (H) and soft (S) water were used.
a Lake Erie water was used as diluent. Toxicity given as
threshold concentration producing immobilization for
exposure periods of 64 hr.
a c d f Both hard (H) and soft (S) water were used.
acdf Comment same as above.
— Fertilized fish eggs of indicated species were placed in
1 liter of test solution and allowed to hatch. Toxicity
data are presented as concentration in ppm/number of
days survival. Maximum length of test was 8 days. No
food was added. Small bluegill were tested to find the
highest concentration of chemical which did not cause
death in 12 days (O).
a_C d e g The effect of turbidity on the toxicity of the chemicals
was studied. Test water was from a farm pond with
"high" turbidity. Additional data are presented.
a This old, lengthy paper discusses toxicity of many chemicals,
~~ possible mechanism of action of some, the effect of tem-
perature, effect of dissolved oxygen, the efficiency of the
goldfish as a test animal, compares this work with earlier
work, and lists an extensive bibliography.
In 0.172N solution, fish survived 169 minutes.
a c This paper deals with the toxicity thresholds of various
substances found in industrial wastes determined by the
use of D. magna. Centrif uged Lake Erie water was used
as a diluent in the bioassay. Threshold concentration was
defined as the highest concentration which would just fail
to immobilize the animals under prolonged (theoretically
infinite) exposure.
a_ Lake Erie water was used as diluent. Toxicity given as
threshold concentration producing immobilization for
exposure periods of 64 hr.
Fitzgerald, et al
(1952)
Sollman
(1949)
Tarzwell and
Henderson
(1960)
Anderson
(1948)
Tarzwell and
Henderson
(1960)
Tarzwell and
Henderson
(1960)
Hiltibran
(1967)
m
O
Wallen.et al
(1957)
Powers
(1918)
Anderson
(1944)
Anderson
(1948)
-------
CHEMICALS
2
O
s.
X
c
3)
m
Q
-n
O
X
m
•£
O
[n
£
Os
Chemical
Barium
chloride
Barium
chloride
Barium
nitrate
Benzanilide
Benzene
Benzene
Benzidine
Benzoic
acid
Benzoic
acid
Organism
Gambusia
af finis
Rana sp
(eggs)
Gasterosteus
aculeatus
Salmo
gairdnerii
Carassius
auratus
Gambusia
af finis
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Microcystis
aeruginosa
Carassius
auratus
Daphnia
magna
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study!1) Location'2) ppm<3)
BSA - 3,200 (T2A)
BSA - 24,430 K
BSA - 400 (K10)
BSA - (O)
BSA - 395 (T2A)
BSA - 31 (T4A)
22 (T4A)
32 (T4A)
L 50 (K)
BSA - 0.165(K)
BSA - 146(0)
Experimental
Variables
Controlled
or Noted!4' Comments
a c d e g The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
a c "Standard reference water" was described and used as well
~~ as lake water. Varied results were obtained when evaluations
were made in various types of water.
— Solutions were made up in tap water. 3.0 to 5.0 cm stickle-
back fish were used as experimental animals. This paper
points out that there is a marked relationship between the
toxicity of the metals and their solution pressures. Those
with low solution pressures were the most toxic.
a This paper deals with the relations between chemical struc-
~ tures of salicylanilides and benzanilides and their toxicity
to rainbow trout and goldfish. The chemical structure of
salicylanilides and benzanilides was related to toxicity
and selectivity to rainbow trout and goldfish. Salicylanilides
were more toxic than benzanilides to the fishes. The ortho
hydroxy substitution of salicylanilide accelerated biological
activity against fish. Meta nitro substitution on the
salicylanilides and benzanilides increased toxicity to fish.
Similar findings are reported for halogens and their rela-
tive position(s) in the molecule. At 10 ppm, there was no
toxicity to goldfish or trout.
a c d e g The effect of turbidity on the toxicity of the chemicals
~~ was studied. Test water was from a farm pond with
"high" turbidity. Additional data are presented.
a c d e f Most fish survived at test concentrations of about one
~~ half , or slightly more, of the TLm value. No attempt
was made to estimate 100 percent survival.
a, etc The chemical was tested on a 5-day algae culture, 1x10^
~ to 2 x 10^ cells/ml, 75 ml total volume. Chu No. 10
medium was used.
a Goldfish weighed between 2 and 4 g. Temperature was
~ maintained at 27.0 ±0.2 C.
a c This paper deals with the toxicity thresholds of various
substances found in industrial wastes determined by the
use of D. magna. Centrifuged Lake Erie water was used as
diluent in the bioassay. Threshold concentration was de-
fined as the highest concentration which would just fail to
immobilize the animals under prolonged (theoretically
infinite) exposure.
Reference
(Year)
Wallen, et al
(1957)
Dowden and
Bennett
(1965)
Jones
(1939)
Walker, et al
(1966)
Wallen, et al
(1957)
Pickering and
Henderson
(1966)
Fitzgerald, et al
(1952)
Gersdorff
(1943)
Anderson
(1944)
>
TJ
•o
m
z
o
-------
D
2
x
30
m
CO
O
-n
O
m
§
o
Benzole
acid
Benzonitrile
2-benzoyl-1,3-
dichloropropane
3-ben zy 1-5,5-
dimethyl-2-
imidazolinethione
bis-benzyl
ethylene
diamine
diacetate
Gambusia BSA
affinis
Pimephales BSA
promelas
Lepomis
macrochirus
Lebistes
reticu/atus
Cylindrospermum L
licheniforme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvu/um (Gp)
Nitzschia
palea (Np)
Microcystis L
aeruginosa
Semotilus BSA
atromaculatus
Beryllium
chloride
9
m
2 Beryllium
O nitrate
Beryllium
sulfate
Beryllium
sulfate plus
sodium
tartrate
Pimephales BSA
promelas
Pimephales BSA
promelas
Pimephales BSA
promelas
Lepomis
macrochirus
Goldfish BSA
Minnow
Snails
Water
plants
225 (T2A)
(S) 135.0 (T4A)
(H) 78.0 (T4A)
(S) 78.0 (T4A)
(S) 400.0 (T4A)
2.0 (O)
a c d e g The effect of turbidity on the toxicity of the chemicals Wallen, et al
~ was studied. Test water was from a farm pond with "high" (1957)
turbidity. Additional data are presented.
cdef (H) Value in softwater Henderson, et al
(S) Value in softwater (1960)
10.0 (K)
5 to 20 (CR)
(H)15(T4A)
(S)0.15 (T4A)
(H) 20 (T4A)
(S)0.15 (T4A)
(H)11 (T4A)
(S) 0.2 (T4A)
(H)12(T4A)
(S) 1.3 (T4A)
(O)
The chemical did not change the flavor of the cooked
bluegill.
Observations were made on the 3rd, 7th, 14th, and 21st days
to give the following (T = toxic, NT = nontoxic, PT = partially
toxic with number of days in parentheses. No number indi-
cates observation is for entire test period of 21 days):
Cl -T (7),PT (21)
Ma-T
So - PT (7)
Cv -T
Gp-T
Np-T
a, etc The chemical was tested on a 5-day algae culture, 1 x 10^
~ to 2 x 106 cells/ml, 75 ml total volume. Chu No. 10
medium was used.
a e Test water used was freshly aerated Detroit River water.
"~ A typical water analysis is given. Toxicity is expressed as
the "critical range" (CR), which was defined as that con-
centration in ppm below which the 4 test fish lived for 24 hr
and above which all test fish died. Additional data are
presented.
a c d f Both hard (H) and soft (S) water were used.
a c d f Comment same as above.
a c d f Comment same as above.
After 10 days of incremental additions of the chemicals to
the aquarium, the final concentrations were: beryllium —
28.5 ppm; sulfate — 302 ppm; sodium tartrate — 664 ppm.
No toxic effect to the animals or plants was observed after
10 days of exposure.
Palmer and
Maloney
(1955)
Fitzgerald, et al
(1952)
Gillette, et al
(1952)
Tarzwell and
Henderson
(1960)
Tarzwell and
Henderson
(1960)
Tarzwell and
Henderson
(1960)
Pomelee
(1953)
m
-------
CHEMICALS
>
0
s
X
c
3D
rn
co
O
O
I
m
S
o
r
\Ji
;>
, ' -
oo
Chemical
Boric acid
Boric acid
Boric acid
Bromine
3'-bromo-3,
5-dinitro-
benzanilide
4'-bromo-3,
5-dinitrobenz-
anilide
4'-bromo-2-
nitrobenz-
anilide
Organism
Sewage
organisms
Gambusia
af finis
Sewage
organisms
Chlore/la
pyreno/dosa
Salmo
gairdnerii
Carassius
auratus
Salmo
gairdnerii
Carassius
auratus
Salmo
gairdnerii
Carassius
auratus
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study<1' Location^) ppm'3) or NotedW Comments
BOD — 480(0) - Various metal salts were studied in relation to how they
affected the BOD of both raw and treated sewage as well
as how they affected the processing of sewage in the
treatment plant. BOD was used as the parameter to mea-
sure the effect of the chemical. The chemical concentra-
tion cited is the ppm required to reduce the BOD values
by 50%. This chemical was tested in an unbuffered system.
BSA — 10,500 (T2A) acdeg The effect of turbidity on the toxicity of the chemicals was
~ studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
BOD — >1000 (TCgrj) a The purpose of this paper was to devise a toxicity index for
industrial wastes. Results are recorded as the toxic con-
centration producing 50 percent inhibition (TC5g) of oxy-
gen utilization as compared to controls. Five toxigrams
depicting the effect of the chemicals on BOD were devised
and each chemical classified.
BSA - 0.18(0) At 0.18 ppm, 2,100 cells/mm3 remained at the end of 4 days
as compared with a count of 2,383 cells/mm3 in control.
0.42 (O) At 0.42 ppm, 270 cells/mm3 remained at the end of 4 days
as compared with 2,383 cells/mm3 in controls.
Bromine showed no inhibitory effect in the first 48 hr.
Experiments were carried out in seven-liter containers of
tap water.
By maintaining a constant level of 0.2 ppm of bromine, it
would be possible to kill algae in water.
BSA — (O) a This paper deals with the relations between chemical struc-
tures of salicylanilides and benzanilides and their toxicity
to rainbow trout and goldfish. The chemical structure of
salicylanilides and benzanilides was related to toxicity and
selectivity to rainbow trout and goldfish. Salicylanilides
were more toxic than benzanilides to the fishes. The ortho
hydroxy substitution of salicylanilide accelerated biolog-
ical activity against fish. Meta nitro substitution on the
salicylanilides and benzanilides increased toxicity to fish.
Similar findings are reported for halogens and their relative
position(s) in the molecule. At 1.0 ppm, this chemical was
toxic to 4 out of 10 trout; but at the concentrations (.1 ,
1.0, 10.0) there was no toxicity to goldfish.
BSA — (O) a Comment same as above except that at 10 ppm the chem-
ical was not toxic to trout or goldfish.
(0)
BSA — 10 (K2) a Comment same as above except that at 10.0 ppm, this chem-
ical was toxic to 2 out of 10 goldfish in 48 hours.
(0)
Reference
(Year)
Sheets
(1957)
Wallen, et al
(1957)
Hermann
(1959)
Kott, et al
(1966)
Walker, et al
(1966)
Walker, et al
(1966)
Walker, et al
(1966)
TJ
TJ
m
Z
D
-------
>•
— t
•o
o
X
m
5
K
z
o
5
^
c
30
m
in
O
Tl
o
X
m
2
£
£
2*-bromo-3-
nitrosalicyl-
anilide
3'-bromo-3-
nitrosalicyl-
anilide
4'-bromo-3-
nitrosalicyl-
aniline
4'-bromo-5-
nitrosalicyl-
anilide
3-bromo-4-
nitrophenol
(free phenol)
2-bromo-4-
nitro phenol
(free phenol)
2-bromo-4-
nitrophenol
(Na salt)
2-bromo-4-
nitrophenol
3-bromo-4-
nitrophenol
Sea lamprey
(larva)
Salmo
gairdneri
(fingerling)
Sea lamprey
(larva)
Salmo
gairdneri
(fingerling)
Sea lamprey
(larva)
Salmo
gairdneri
(fingerling)
Sea lamprey
(larva)
Salmo gairdneri
(fingerling)
Petromyzon
marinus
Lepomis
macrochirus
Salmo
gairdnerii
Petromyzon
marinus
Salmo
gairdnerii
S. trutta
Petromyzon
marinus
Salmo
gairdnerii
Petromyzon
marinus
(larvae)
Petromyzon
marinus
(embryos and
prolarvae)
(larvae)
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
1.0 (K)
0.3 (K)
(O)
0.3 (K)
(O)
0.5 (K)
(O)
5 (K 100%)
15 (K 10%)
11 (K 10%)
5(K 100%)
13 (K 10%)
11 (K 10%)
7 (K 100%)
15 (K 10%)
10 (K14)
10 (K5-18)
10(K2-4hr)
See
Applegate,
This paper deals with the comparative toxicity of halonitro- Starkey and
salicylanilides to sea lamprey and fingerling rainbow trout Howell
as a function of substituent loci. (1966)
Ditto
Comment same as above.
1.0 ppm killed 25%.
Comment same as above.
1.0 ppm killed 25%.
Comment same as above.
1.5 ppm killed 25%.
Mortality occurred in approximately 24 hr. This was a
study on controlling sea lamprey larvae.
Comment same as above.
Comment same as above.
Additional data are presented.
Comment same as above.
Starkey and
Howell
(1966)
Starkey and
Howell
(1966)
Starkey and
Howell
(1966)
Ball
(1966)
Ball
(1966)
Ball
(1966)
Piavis
(1962)
Piavis
(1962)
m
O
-------
CHEMICALS
2
O
s
X
c
3)
m
0
•n
O
m
S
o
>
£
>£*
0
Chemical
4'-bromo-3-
nitro-o-sali-
cylotoluidide
3'-bromo-3-
nitrosalicyl-
anilide
4'-bromo-3-
nitrosalicyl-
anilide
2-butanone
n-butyl
alcohol
t-butyl
alcohol
Butyric
acid
Cadmium
Organism
Sa/mo
gairdnerii
Carassius
auratus
Sa/mo
gairdnerii
Carassius
auratus
Salmo
gairdnerii
Carassius
auratus
Gambusia
affinis
Semotilus
atromaculatus
Semotilus
atromaculatus
Daphnia
magna
Lepomis
macrochirus
Lebistes
reticulatus
Bufo
valliceps
(tadpoles)
Daphnia
magna
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study'1) Location'?) ppm'3)
BSA - 1.0(K3hr)
1.0 (K2)
10.0 (K 3 hr)
BSA - 1.0(K3hr)
1.0 (K2)
10.0 (K 3hr)
BSA - 1.0(K3hr)
1.0 (K2)
10.0 (K 3hr)
BSA - 5,600 (T2A)
BSA - 1 ,000 to
1,400 (CR)
BSAq - 3,000 to
6,000 (CR)
BSA - 61 (T2A)
200 (T1A)
BSA - 1.0 (K)
1.0 (K)
0.01 (K)
Experimental
Variables
Controlled
or Noted'4) Comments
a This paper deals with the relations between chemical struc-
tures of salicylanilides and benzanilides and their toxicity to
rainbow trout and goldfish. The chemical structure of
salicylanilides and benzanilides was related to toxicity and
selectivity to rainbow trout and goldfish. Salicylanilides
were more toxic than benzanilides to the fishes. The ortho
hydroxy substitution of salicylanilide accelerated biological
activity against fish. Meta nitro substitution on the sali-
cylanilides and benzanilides increased toxicity to fish. Sim-
ilar findings are reported for halogens and their relative
position(s) in the molecule.
a Comment same as above.
—
a Comment same as above.
~
a c d e g The effect of turbidity on the toxicity of the chemicals was
~ studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
a e Test water used was freshly aerated Detroit River water.
~~ A typical water analysis is given. Toxicity is expressed as
the "critical range" (CR), which was defined as that con-
centration in ppm below which the 4 test fish lived for
24 hr and above which all test fish died. Additional data
are presented.
a e Comment same as above.
a c "Standard reference water" was described and used as well
as lake water. Varied results were obtained when evalua-
tions were made in various types of water.
ace It is assumed in this experiment that the cations considered
are toxic because they combine with an essential sulfhydryl
group attached to a key enzyme. This treatment indicates
that the metals which form the most insoluble sulfides are
the most toxic. The log of the concentration of the metal
ion is plotted against the log of the solubility product con-
stant of the metal sulfide — a treatment that does not lend
itself to tabulation. The cation toxicity cited is only an
approximate concentration interpolated from a graph.
Time of death was not specified.
Reference
(Year)
Walker, et al
(1966)
Walker, et al
(1966)
Walker, et al
(1966)
Wallen, et al
(1957)
Gillette, et al
(1952)
Gillette, et al
(1952)
Dowden and
Bennett
(1965)
Shaw and
Grushkin
(1967)
^
TJ
m
Z
O
X
^
-------
Cadmium
Cadmium
Cadmium
Cadmium
Cadmium
chloride
Cadmium
chloride
Cadmium
chloride
s
ni Cadmium
? chloride
O
>
W Cadmium
> chloride
X
3D
m
O Cadmium
_ cyanide
X complex
m
S
Salmo
gairdnerii
Lepomis
macrochirus
Ictalurus
nebulosus
Salmo
gairdnerii
Salmo
gairdnerii
Carassius
carassius
BCFA
(O)
BSCFCH
BCFA
BCFA
BSA
Daphnia
magna
Pimephales
promelas
Limnaea
palustris
(eggs)
Pimephales
promelas
Lepomis
macrochirus
Lebistes
reticulatus
Green
sunfish
Lepomis
macrochirus
(juveniles)
BSA
BSA
BSA
BSA
BSA
0.1-100.0
0.008-
0.01 (T7A)
30mg(T1A)
30(T1A)
(O)
<0.0026 (S)
5 (T4A) H
0.9 (T4A) S
•\
6x10-6m
(K1)
(S) 1.05(T4A)
(H) 72.6 (T4A)
(S) 1.94(T4A)
(S) 1.27(T4A)
(S) 2.84 (T4A)
(H) 66.0 (T4A)
0.64 (O)
— A small, cone-shaped, cadmium-plated metal screen was used
to cover a 2-inch pipe outlet. Recirculating 2,500 gallons of
water through the screen at the rate of 50 gallons per min-
ute killed 16-per-pound rainbow trout in 24 hours. Rainbow
trout placed in a 15-gallon tub of water, with recirculation
through the cadmium screen were dead within 10 hours.
a c d e f Fish were exposed to 8, 16, and 20 ppm of cadmium for
varying periods of time (up to 90 days). In living fish the
accumulation of cadmium never exceeded 130 /Jg/g of gill
tissue, based on dry weight. In fish that died of poisoning,
the accumulation of cadmium was a maximum of 634/Jg/g
of gill tissue. The authors state that high cadmium content
(3-400 fJglg) in the liver of a fish would indicate a past
history of exposure.
a b f The data show that even at high concentrations, the toxic
effect to the fish was very slow. Experiments were con-
ducted in hard water.
a b f A 7-day TLm may be between 0.008 and 0.01 ppm. Despite
this high toxicity, the response of the fish to the poison
was initially very slow, even at high concentrations.
£ This old, lengthy paper discusses toxicity of many chemi-
cals, possible mechanism of action of some, the effect of
temperature, effect of dissolved oxygen, the efficiency
of the goldfish as a test animal, compares this work with
earlier work, and lists an extensive bibliography.
In a 0.157N solution, fish survived 70 minutes; in a solu-
tion of 0.000000037N, they survived 442 minutes.
£ Lake Erie water was used as diluent. Toxicity given as
threshold concentration producing immobilization for
exposure periods of 64 hr.
a c d f Both hard (H) and soft (S) water were used.
£C Toxicity is given in molar concentrations for maximum
direct mortality (kill) in 4 hours.
c d e f (S) Soft water
(H) Hard water
Values are expressed as mg/l of metal.
a_c d f £ For the concentration given, the median resistance time
was 134 minutes.
Roberts
(1963)
Mount and
Stephan
(1967)
Ball
(1967)
Velsen and
Alderdice
(1967)
Powers
(1918)
I
m
O
X
Anderson
(1948)
Tarzwell and
Henderson
(1960)
Morrill
(1963)
Pickering and
Henderson
(1965)
Doudoroff,
etal
(1966)
-------
CHEMICALS
2
0
s
X
-1
c
3D
m
in
0
•71
O
m
S
o
P
to
j>
K)
to
Chemical
Cadmium cya-
nide complex.
sodium cya-
nide (439 ppm
CN), and cad-
mium sulfate
(528 ppm Cd)
Cadmium
nitrate
Cadmium
sulfate
Caffeine
Calcium
c Tbonate
Calcium
chloride
Calcium
chloride
Calcium
chloride
Organism
Pimephales
promelas
Gasterosteus
aculeatus
Sewage
organisms
Carassius
carassius
Gambusia
affinis
Carassius
carassius
Daphnia
magna
Daphnia
magna
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Studyd) Location<2) ppm(3) or Noted**) Comments
BSA — 0.17 (T4A) ac Synthetic soft water was used. Toxicity data given as number
~~ of test fish surviving after exposure at 24, 48, and 96 hr.
TLm values were estimated by straight-line graphical inter-
polation and given in ppm CN".
BSA — 0.2 (K10) — Solutions were made up in tap water. 3.0 to 5.0 cm stickle-
back fish were used as experimental animals. This paper
points out that there is a marked relationship between the
toxicity of the metals and their solution pressures. Those
with low solution pressures were the most toxic.
BOD — 142 (TCsfj) a The purpose of this paper was to devise a toxicity index for
~~ industrial wastes. Results are recorded as the toxic concen-
tration producing 50 percent inhibition (TCsfj) of oxygen
utilization as compared to controls. Five toxigrams de-
picting the effect of the chemicals on BOD were devised
and each chemical classified.
BSA — (O) a This old, lengthy paper discusses toxicity of many chemicals,
~~ possible mechanism of action of some, the effect of tem-
perature, effect of dissolved oxygen, the efficiency of the
goldfish as a test animal, compares this work with earlier
work, and lists an extensive bibliography.
In a concentration of 0.285 g/liter, fish survived 94 minutes.
BSA - 56,000 (T2A) a c d e g The effect of turbidity on the toxicity on the chemicals
was studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
BSA — (O) a This old, lengthy paper discusses toxicity of many chemicals.
possible mechanism of action of some, the effect of tem-
perature, effect of dissolved oxygen, the efficiency of the
goldfish as a test animal, compares this work with earlier
work, and lists an extensive bibliography.
In 0.249N solution, fish survived 174 minutes.
BSA — 1332(0) ac This paper deals with the toxicity thresholds of various sub-
stances found in industrial wastes as determined by the
use of D. magna. Centrifuged Lake Erie water was used as
diluent in the bioassay. Threshold concentration was de-
fined as the highest concentration which would just fail to
immobilize the animals under prolonged (theoretically
infinite) exposure.
BSA — 920 (S) a Lake Erie water was used as diluent. Toxicity given as
threshold concentration producing immobilization for
exposure periods of 64 hr.
Reference
(Year)
Doudoroff,
et al
(1956)
Jones
(1939)
Hermann
(1959)
Powers
(1918)
Wallen, et al
(1957)
Powers
(1918)
Anderson
(1944)
Anderson
(1948)
^
TJ
T)
m
z
D
X
^
-------
to
OJ
Calcium
chloride
Calcium
chloride
Calcium
chloride
Calcium
chloride
Calcium
chloride
Calcium
chloride
m
2
O
Calcium
chloride
Lepomis
macrochirus
Lepomis
macrochirus
Daphnia
magna
BSA
BCFA
BSA
Gambusia
affinis
Lepomis
macrochirus
Daphnia
magna
Lepomis
macrochirus
Lymnaea sp
(eggs)
Nitzschia
linearis
Lepomis
macrochirus
BSA
BSA
BSA
BSA
10,650 (T4A)
9,500 (T4A)
small
11,300 (T4f)
large
3,972 (O)
13,400 (T2A)
11,300 (T4A)
3,526 (T1 A)
3,005 (T2A)
8,350 (T1 A)
4,485 (T1A)
3,094 (T2A)
2,373 (T3A)
3,130 (T5A)
10,650 (T4A)
a d e f This paper reports the LDgg in 96 hours for 8 common in- Trama
organic salts. A synthetic dilution water of controlled (1954)
hardness was prepared for use in the experiments. Among
other variables, specific conductivity, as mhos at 20 C,
was measured. If this salt is toxic to fish, this experiment
did not demonstrate it.
a c e f Test water was composed of distilled water with CP grade Cairns and
chemicals and was aerated throughout the 96-hour ex- Scheier
posure period. (1955)
a c The primary aim of this study was to determine the effects Fairchild
of lowered dissolved oxygen concentration upon an (1955)
aquatic invertebrate when exposed to solutions of inor-
ganic salts known to be present in various industrial
effluents. Analysis of data conclusively shows the
D. magna tested under lowered oxygen tension exhibited
lower threshold values for the chemicals studied than
when tested at atmospheric dissolved oxygen.
£ c d e g The effect of turbidity on the toxicity on the chemicals Wallen, et al
was studied. Test water was from a farm pond with "high" (1957)
turbidity. Additional data are presented.
£5^-£_L ^ "control" was prepared by adding required chemicals to Cairns and
distilled water, and this was constantly aerated. Data Scheier
reported are for larger fish, app 14.24 cm in length. Data (1959)
for smaller fish are also in the report.
£C "Standard reference water" was described and used as well Dowden and
as lake water. Varied results were obtained when evalua- Bennett
tions were made in various types of water. (1965)
The purpose of this experiment was to determine whether Patrick, et al
there was a constant relationship between the responses (1968)
of these organisms. From the data presented, there was
no apparent relationship of this type. Therefore the
authors advise that bioassays on at least 3 components of
the food web be made in any situation.
I
m
a
x
o
5
3]
m
CO
o
-------
0
m
S
o
P Chemical
^ Calcium
O hydroxide
S
X
H
X
m
w
O
•n
O
m
2
5 Calcium
J* hydroxide
E>
Calcium
hydroxide
Calcium
^ hypochlorite
"i
to
.p..
Calcium
hypochlorite
Bioassay
or Field
Organism Study C"
Micropterus BSA
salmoides
Lepomis
machrochirus
Goldfish
Gambusia BSA
affinis
Biomorpholaria BSA
alexandrina
Bulinus
truncatus
Lymnaea
caillaudi
Cylindrospermum L
lichen/forme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Blue-green algae L
Cylindrospermum
Anabaena
Anacystis
Calothrix
Nostoc
Oscillatoria
Plectonema
Green algae
Ankistrodesmus
Chlorella
Closterium
Oocystis
Scenedesmus
Stigeoclonium
Zygnema
Toxicity,
Active
Field Ingredient,
Location (2) ppm(3)
100 (O)
100 (O)
100 (O)
220 (T2A)
300 (K1)
300 (K1)
300 (K1)
2.0 (O)
2.0 (0)
Experimental
Variables
Controlled Reference
or Noted*4* Comments (Year)
acfpi The disposal of cannery wastes frequently involves the use Sanborn
~~ of chemicals for treatment purposes. Ferrous sulphate, (1945)
alum, and lime are used in chemical coagulation; sodium
carbonate for acidity control in biological filters; and
sodium nitrate in lagoons for odor control. Lye (sodium
hydroxide) peeling of certain fruits and vegetables is not
uncommon. These chemicals, in whole or part, are dis-
charged in most cases to a stream.
The concentration listed permitted large mouth bass to sur-
vive 3 to 5 hours, bluegills to survive 2 to 4.5 hours, and
goldfish to survive 3 to 3.5 hours.
a c d e g The effect of turbidity on the toxicity of the chemicals was Wallen, et al
~ studied. Test water was from a farm pond with "high" (1957)
turbidity. Additional data are presented.
a The degree of tolerance for vector snails of bilharziasis to Gohar and
various chemicals is somewhat dependent upon tempera- EI-Gindy
ture. The temperature at which (K1) occurred was 28 C. (1961)
a Observations were made on the 3rd, 7th, 14th, and 21st days Palmer and
~~ to give the following (T = toxic, NT = nontoxic, PT = partially Maloney
toxic with number of days in parentheses. No number indi- (1955)
cates observation is for entire test period of 21 days):
Cl -T(3)
Ma - T (3)
So -T(3),PT(7)
Cv - T (3)
Gp-T(3)
Np - T (3)
— Ca(OCI)2 was toxic or partially toxic to all of the algae Kemp, et al
species at the indicated concentration for 28 days. (1966)
^
^0
m
Z
g
x
^
-------
;>
to
Calcium
nitrate
Calcium
nitrate
Calcium
nitrate
Calcium
nitrate
Calcium
sulfate
Calcium
sulfate
Calcium
sulphate
H Calcium
-------
n
I
m
S
o
£ Chemical
M
> Calcium
O sulphate
S
X
-t
c.
n
m
w Capric
0 ac.d
O
m
§
^ Caproic
r acid
w
Caprylic
acid
Carbon
chloroform
extract (CCE)
>
K)
ON
Carbon
chloroform
extract (CCE)/
carbon alcohol
extract (CAE)
1/1.48
Carbon
chloroform
extract (CCE)/
carbon alcohol
extract (CAE)
1/1.56
Organism
Nitischia
linearis
Lepomis
macrochirus
Lepomis
macrochirus
Lepomis
macrochirus
Lepomis
macrochirus
Trout
Golden
Shiner
Sunfish
Trout
Red
Shiner
Sunfish
Trout
Red
Shiner
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Studyd) Location^2) ppm<3> or Noted^
BSA - 3,200 (T5A) ace
2,980 (T4A)
BSA - (O)
BSA - 150-200IT1A) ac
BSA - (O)
BSA - 36(T1A) acdefim
32 (T2A)
28 (T4A)
24 (T5A)
59 (T1A)
52 (T2A)
39 (T4A)
33 (T5A)
56(T1A)
49 (T2A)
45 (T4A)
39 (T5A)
BSA - 130 (T1 A) acdefim
125IT2A)
95 (T4A)
82 (T5A)
No effect up
to 305 (T5A)
166 (T1A)
144IT2A)
1 1 5 (T4A)
103(T5A)
BSA - 138 (T1A) acdefim
130 (T2A)
96 (T4A)
92 (T5A)
No effect up
to 24O (T5A)
Comments
The purpose of this experiment was to determine whether
there was a constant relationship between the responses of
these organisms. From the data presented, there was no
apparent relationship of this type. Therefore the authors
advise that bioassays on at least 3 components of the food
web be made in any situation.
"Standard reference water" was described and used as well
as lake water. Varied results were obtained when evaluations
were made in various types of water.
Chemical is only slightly soluble in water. No toxicity data
were obtained.
"Standard reference water" was described and used as well
as lake water. Varied results were obtained when evaluations
were made in various types of water.
Comment same as above except that compound was very
insoluble in water. No toxicity data were obtained.
The objects of this investigation were the recovery of or-
ganic micropollutantsfrom subsurface and surface
Missouri waters, characterization and identification of these
substances, and evaluation of their toxic effects, both
acute and long-term, in order to develop methods for their
destruction or removal.
Comment same as above.
Comment same as above.
Reference
(Year)
Patrick, et al
(1968)
Dowden and
Bennett
(1965)
Dowden and
Bennett
(1965)
Dowden and
Bennett
(1965)
Smith and
Grigoropoulos
(1968)
Smith and
Grigoropoulos
(1968)
Smith and
Grigoropoulos
(1968)
5
•o
m
z
o
X
-------
Carbon
dioxide
Trout
BSA
(O)
Carbon
dioxide
plus
Carbon
disulfide
Carbonic
acid
m
w
m
Rainbow
trout
Gambusia
affinis
Fish
BSA
BSA
BSA
*l
to
— 3
S
m
2
O
£
>
z
O
5
X
Cetyldimethyl
ammonium
bromide plus
alkylate ether
alcohol
Cetylpyridinum-
bromide
Cetyltrimethyl-
ammonium
bromide
Chlorauric
acid
Cylindrospermum
lichen/forme (Cl)
Gleocapsa
sp(G)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Mlcrocystis
aeruginosa
Microcystis
aeruginosa
Gasterosteus
aculeatus
(O)
135 (T2A)
6.5 x 10'4M
(K)
2.0 (O)
a cd eg
Chloride plus
fluoride
Rainbow
trout
BSA
BSA
2.0 (K)
2.0 (K)
0.4 (K10)
(O)
a, etc
a, etc
No quantitative data are reported. 30 ppm of nitrogen was Herbert
added as ammonium chloride. Carbon dioxide in concen- (1955)
trations up to 30 ppm reduced the toxicity of the ammonia
by lowering the pH of the water. Concentrations of
60 ppm of CC-2 were toxic but not lethal when the concen-
tration of dissolved oxygen was low. A concentration of
240 ppm of CO2 was lethal to trout in little more than
one hour.
The reduction of toxicity of ammonia solutions by the addi- Alabaster and
tion of carbon dioxide was due to lowering the pH of the Herbert
solution. 60-240 ppm CC"2 in solution was toxic within (1954)
12 hr. 30 ppm ammonia nitrogen was toxic, but up to
30 ppm CO2 increased fish survival time.
The effect of turbidity on the toxicity of the chemicals was Wallen, et al
studied. Test water was from a farm pond with "high" (1957)
turbidity. Additional data are presented.
Avoidance behavior of test fish to toxic chemicals is given. Ishio
Toxicity is given as the lowest lethal concentration (molar). (1965)
Ratios of avoidance and lowest lethal concentration are
presented and discussed.
Observations were made on the 3rd, 7th, 14th, and 21st days Palmer and
to give the following (T = toxic, NT = nontoxic, PT = par- Maloney
tially toxic with number of days in parentheses. No num- (1955)
ber indicates observation is for entire test period of
21 days):
Cl -NT
G -NT
So -NT
Cv -NT
Gp-NT
Np-NT
The chemical was tested on a 5-day algae culture, 1 x 106 Fitzgerald, et al
to 2 x 106 cells/ml, 75ml total volume. Chu No. 10 (1952)
medium was used.
Comment same as above. Fitzgerald, et al
(1952)
Solutions were made up in tap water. 3.0 to 5.0 cm stickle- Jones
back fish were used as experimental animals. This paper (1939)
points out that there is a marked relationship between the
toxicity of the metals and their solution pressures. Those
with low solution pressures were the most toxic.
When trout were exposed to 30 ppm CI" for 48 hours and Neuhold and
then challenged with fluoride, the LC^Q of the fluoride was Sigler
6 ppm. No exposure to CI" resulted in an LCgo of (1962)
22 ppm Fl'.
m
O
-------
n
I
m
2
o
£ Chemical
V)
^ Chlorinated
O benzene
S
X
H
3)
m
en
O
Tl
O
m
S
> Chlorinated
[o camphene
(60 percent)
to
00 Chlorine
(from mono-
and di-
chloramines)
Chlorine
Chlorine
Toxicity,
Bioassay Active
or Field Field Ingredient,
Organism Study 'D Location^) ppm(3)
Cylindrospermum L — 2.0 (O)
lichen/forme ICII
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
varihgata (Cv)
Gomphoiiema
parvulum {^p)
Nitzschia
palea (Np)
Cylindrospermum L — 2.0 (O)
lichen/forme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Salmo BCFA - 0.08 (T7A)
gairdnerii
Naisspp BSA - 1.0 (K)
Chlorella BSA - 0.18(0)
pyrenoidosa
0.42 (O)
Experimental
Variables
Controlled
or Noted W Comments
a Observations were made on the 3rd, 7th, 14th, and 21st days
~~ to give the following (T = toxic, NT = nontoxic, PT = par-
tially toxic with number of days in parentheses. No num-
ber indicates observation is for entire test period of
21 days):
Cl -T
Ma -T
So -T (3),PT (21)
Cv -T
Gp-T
Np-T
a Comment same as above except that:
Cl - PT
Ma-T (14), PT (21)
So -PT (14), NT
Cv -PT
Gp-T (3)
Np-PT (7)
ace The purpose of this paper was to investigate the toxicity of
chlorine to the rainbow trout in solutions containing
ammonia. The toxicity of residual chlorine was dependent
upon the relative proportions of free chlorine and
chloramines.
a f All tests were conducted in hard water. At 1 .0 ppm of chlo-
rine, 95% of the worms were killed after 35 minutes. There
was considerable variation in chlorine tolerance below
2 ppm and contact times from 1-3 hours may be necessary
for a complete kill.
a c i At 0.18 ppm, 1,900 cells/mm^ remained at the end of 4 days
as compared with a count of 2,383 cells/mm^ in controls.
At 0.42 ppm, 500 cells/mm^ remained at the end of 4 days
as compared with a count of 2,383 cells/mm^ in controls.
Chlorine showed an inhibitory effect in 48 hr.
Experiments were carried out in seven-liter containers of
tap water.
By using 0.2 ppm of free chlorine, one might expect not to
reduce the numbers of algae appreciably but to keep the
population constant.
Reference
(Year)
Palmer and
Maloney
(1955)
Palmer and
Maloney
(1955)
Merkens
(1958)
Learner and
Edwards
(1963)
Kott, et al
(1966)
>
TJ
-g
m
Z
O
X
>
-------
30
m
w
o
3'-chloro-5-
acetamidosali-
cylanilide
p-chlorobenz-
anilide
Chlorobenzene
Chlorobenzilate
Chlorobenzilate
4'-chloro-2,5-
dihydroxy
diphenyl
sulphone
S 4 chlorohexyl-
fi 2,6-dinitro-
> phenol, tech.
E>
Sal mo
gairdnerii
Carassius
auratus
BSA
Salmo
gairdnerii
Carassius
auratus
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Daphnia
magna
Simocephalus
serrulatus
Daphnia
pulex
BSA
BSA
BSA
BSA
O
m
O
^
z
o
4'-chloro-5-
bromo-3-
nitrosalicyl-
anilide
Salmo
gairdnerii
Carassius
auratus
BSA
Daphnia
magna
Lymnaeid
snails
BSA
BSA
10.0 (K 3 hr)
10.0 (K2)
(O)
(O)
29 (T4A)
20 (T4A)
45 (T4A)
44 (T4A)
1.4(0)
0.550 (SB)
0.870 (SB)
0.1 (K2)
1.0 (K 3 hr)
1.0 (K2)
10.0 (K3hr)
a c d
28.9 (K2A)
(0)
This paper deals with the relations between chemical struc-
tures of salicylanilides and benzanilides and their toxicity to
rainbow trout and goldfish. The chemical structure of
salicylanilides and benzanilides was related to toxicity and
selectivity to rainbow trout and goldfish. Salicylanilides
were more toxic than benzanilides to the fishes. The ortho
hydroxy substitution of salicylanilide accelerated biological
activity against fish. Meta nitro substitution on the salicyl-
anilides and benzanilides increased toxicity to fish. Similar
findings are reported for halogens and their relative
position(s) in the molecule.
Comment same as above except that at 10 ppm this chemi-
cal was not toxic to trout or goldfish.
Most fish survived at test concentrations of about one half,
or slightly more, of the TLm value. No attempt was made
to estimate 100 percent survival.
Walker, et al
(1966)
.The indicated concentration immobilized Daphnia in
50 hours.
Concentration reported is for immobilization.
Time for immobilization was 48 hr.
Data cited are for 60 F, but assays were performed at varied
temperatures.
"Water Chemistry" (Unspecified) was "controlled" during
the assay period.
This paper deals with the relations between chemical struc-
tures of salicylanilides and benzanilides and their toxicity
to rainbow trout and goldfish. The chemical structure of
salicylanilides and benzanilides was related to toxicity and
selectivity to rainbow trout and goldfish. Salicylanilides
were more toxic than benzanilides to the fishes. The ortho
hydroxy substitution of salicylanilide accelerated biologi-
cal activity against fish. Meta nitro substitution on the
salicylanilides and benzanilides increased toxicity to fish.
Similar findings are reported for halogens and their relative
position(s) in the molecule.
An attempt was made to correlate the biological action with
the chemical reactivity of selected chemical substances.
Results indicated a considerable correlation between the
aquarium fish toxicity and antiautocatalytic potency of
the chemicals in marked contrast to their toxicity on
systemic administration.
Each test container, 500-ml beaker, was filled with ditch
water. 100% mortality occurred in concentrations of
1:400,000 and greater.
Walker, et al
(1966)
Pickering and
Henderson
(1966)
Anderson
(1960)
Sanders and
Cope
(1966)
Walker, et al
(1966)
o
X
Sollman
(1949)
Batte, et al
(1951)
-------
o
I
m
P
r- Chemical
^ 2'-chloro-5'-
O methyl-3-nitro-
2 salicylanilide
X
C
m 2'-chloro-3-
w nitrosalicyl-
^ anilide
O
I
m
§ 2'-chloro-5-
0 nitrosalicyl-
p anilide
3'-chloro-3-
nitrosalicyl-
anilide
3'-chloro-5-
-^ nitrosalicyl-
' anilide
O
4'-chloro-3-
nitrosalicyl-
anilide
4'-chloro-5-
nitrosalicyl-
anilide
m-chlorophenol
o-chlorophenol
Organism
Sea lamprey
(larva)
Salmo
gairdneri
(fingerling)
Sea lamprey
(larva)
Salmo
gairdneri
(fingerling)
Sea lamprey
(larva)
Salmo
gairdneri
(fingerling)
Sea lamprey
(larva)
Salmo
gairdneri
(fingerling)
Sea lamprey
(larva)
Salmo
gairdneri
(fingerling)
Sea lamprey
(larva)
Salmo
gairdneri
(fingerling)
Sea lamprey
(larva)
Salmo
gairdneri
(fingerling)
Carassius
auratus
Carassius
auratus
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study*1) Location<2) ppmO)
BSA - 0.7 (LD10rj)
1.0 (LD25)
BSA - 3.0 (K)
(0)
BSA - 0.9 (K)
(0)
BSA - 0.3 (K)
(0)
BSA - 15.0IK)
(0)
BSA - 0.3 (K)
(0)
BSA - 0.5 (K)
(0)
BSA - 70.5 to 219
(K8hr)
61.7 (O)
20.6 (O)
BSA - 142 to 311
(K8hr)
104 (O)
82.8 (O)
10.0 (O)
Experimental
Variables
Controlled
or Noted (4) Comments
See This paper deals with the comparative toxicity of halonitro-
Applegate, salicylanilides to sea lamprey and fingerling rainbow trout
et al as a function of substituent loci.
(1957-1958)
Ditto Comment same as above.
70 ppm killed 25%.
' Comment same as above.
3.0 ppm killed 25%.
' Comment same as above.
0.9 ppm killed 25%.
Comment same as above.
15.0 ppm killed 25%.
" Comment same as above.
0.7 ppm killed 25%.
" Comment same as above.
1.0 ppm killed 25%.
a Temperature in test containers was maintained at 27 ± 0.2 C.
~~ Goldfish tested weighed between 2 and 4 g.
m-chlorophenol, 61.7 mg per liter, killed 93% of the fish
in 8 hr; 20.6 mg per liter killed 62% in 8 hr.
a Comment same as above except that o-chlorophenol,
~ 104 mg per liter, killed 83% of the fish in 8 hr; 82.8 mg
per liter killed 64% in 8 hr; and 10.0 mg per liter
killed 20% in 8 hr.
Reference
(Year)
Starkey and
Howell
(1966)
Starkey and
Howell
(1966)
Starkey and
Howell
(1966)
Starkey and
Howell
(1966)
Starkey and
Howell
(1966)
Starkey and
Howell
(1966)
Starkey and
Howell
(1966)
Gersdorff and
Smith
(1940)
Gersdorff and
Smith
(1940)
>
•o
m
X
>
-------
p-chlorophenol
4'-chloro-2',
5'-dimethoxy-
3-nitrosali-
cylanilide
Carassius
auratus
Salmo
gairdnerii
Carassius
auratus
>
O
_1
O
m
5
g
J*
>
Z
O
2
*
c
3D
m
CO
O
T*
O
X
m
2
5'-chloro-3,
5-dinitro-2-
benzanilide
2'-chloro-3,
5-dinitro-
benzanilide
3'-chloro-3,
5-dinitro-
benzanilide
3'-chloro-3,5-
dinitro-o-
benzotoluidide
S'-chloro-3,
5-dinitro-p-
benzotoluidide
5'-chloro-3,
5-dinitro-3-
benzotoluidide
2'-chloro-3',
4'-dinitro-
salicylanilide
Chloroform
Salmo
gairdnerii
Carassius
auratus
Salmo
gairdnerii
Carassius
auratus
Salmo
gairdnerii
Carassius
auratus
Salmo
gairdnerii
Carassius
auratus
Salmo
gairdnerii
Carassius
auratus
Salmo
gairdnerii
Carassius
auratus
Salmo
gairdnerii
Carassius
auratus
Pygosteus
pungitius
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BCF
54.3 to 190
(KShr)
47.5 (O)
12.7 (O)
6.3 (O)
1.0 (KShr)
1.0 (K2)
10.0 (KShr)
(O)
(O)
(O)
(O)
(O)
(O)
10.0 (K 3 hr)
(O)
(O)
(O)
10.0 (K 3 hr)
(KSmin.)
(O)
1.0 (KShr)
1.0 K (K2)
10.0 (KShr)
(O)
Comment same as above except that p-chlorophenol, 47.5 mg Gersdorff and
per liter, killed 85% of the fish in 8 hr; 12.7 mg per liter Smith
killed 75% in 8 hr; and 6.3 mg per liter killed 54% in 8 hr. (1940)
This paper deals with the relations between chemical struc- Walker, et al
tures of salicylanilides and benzanilides and their toxicity to (1966)
rainbow trout and goldfish. The chemical structure of sali-
cylanilides and benzanilides was related to toxicity and
selectivity to rainbow trout and goldfish. Salicylanilides
were more toxic than benzanilides to the fishes. The ortho
hydroxy substitution of salicylanilide accelerated biological
activity against fish. Meta nitro substitution on the salicyl-
anilides and benzanilides increased toxicity to fish. Similar
findings are reported for halogens and their relative
position(s) in the molecule.
Comment same as above except that at 10 ppm the chemical Walker, et al
was not toxic to trout. At 1.0 ppm, 1 out of 10 goldfish (1966)
died. This may not be valid since at 10 ppm, no fish were
killed.
Comment same as above except that at 10 ppm this chemical Walker, et al
was not toxic to trout or goldfish. (1966)
Comment same as above except that at 10.0 ppm the chem- Walker, et al
ical was toxic to 7 out of 10 trout in 48 hours. No goldfish (1966)
were killed at this and lower concentrations.
Comment same as above except that at 10 ppm the chemical Walker, et al
was not toxic to goldfish. Precipitation occurred at 10 ppm. (1966)
Comment same as above except that at 10.0 ppm the chem- Walker, et al
ical was toxic to 2 out of 10 trout in 48 hours. The chem- (1966)
ical was not toxic to goldfish at 10.0 ppm.
Comments same as above except that at 10 ppm the chem- Walker, et al
ical was not toxic to goldfish. (1966)
Comment same as above except data cited. Walker, et al
(1966)
A 1/2000 solution anaesthetized or killed very rapidly. Jones
1/5000 and 1/10000 induced an avoidance reaction in (1947)
the fish.
m
-------
CHEMICALS
2
O
3
X
-i
c
3)
m
01
0
o
I
m
s
o
EJ
»•
j
\
Chemical
Chloroform
3'-chloro-
3-hydroxy-
benzanilide
4'-chloro-3-
hydroxybenz-
anilide
2'-chloro-2-
nitrobenz-
anilide
3'-chloro-2-
nitrobenz-
anilide
2'-chloro-3-
nitrobenz-
anilide
2'-chloro-4-
nitrobenz-
anilide
3'-chloro-3-
nitrobenz-
anilide
3'-chloro-4-
nitrobenz-
anilide
Organism
Sewage
organisms
Salmo
gairdnerii
Carassius
auratus
Salmo
gairdnerii
Carassius
auratus
Salmo
gairdnerii
Carassius
auratus
Salmo
gairdnerii
Carassius
auratus
Salmo
gairdnerii
Carassius
auratus
Salmo
gairdnerii
Carassius
auratus
Salmo
gairdnerii
Carassius
auratus
Salmo
gairdneri
Carassius
auratus
Toxicity,
Bioassay Active
or Field Field Ingredient,
Studyd) Location<2) ppm(3)
BOD - (NTE)
BSA - 10.0 (K2)
(0)
BSA - 10.0 (K2)
(0)
BSA - (O)
(0)
BSA - 10.0 (K2)
(O)
BSA - 10.0 (K2)
(0)
BSA - (O)
(0)
BSA - 10.0 (K 3 hr)
10.0 (K2)
BSA - (O)
(0)
Experimental
Variables
Controlled
or NotedW Comments
a The purpose of this paper was to devise a toxicity index for
~ industrial wastes. Results are recorded as the toxic concen-
tration producing 50 percent inhibition (TCsfj) of oxygen
utilization as compared to controls. Five toxigrams de-
picting the effect of the chemicals on BOD were devised
and each chemical classified.
a This paper deals with the relations between chemical struc-
~ tures of salicylanilides and benzanilides and their toxicity
to rainbow trout and goldfish. The chemical structure of
salicylanilides and benzanilides was related to toxicity and
selectivity to rainbow trout and goldfish. Salicylanilides
were more toxic than benzanilides to the fishes. The ortho
hydroxy substitution of salicylanilide accelerated biological
activity against fish. Meta nitro substitution on the salicyl-
anilides and benzanilides increased toxicity to fish. Similar
findings are reported for halogens and their relative
position(s) in the molecule. At 10.0 ppm, the chemical
was toxic to 7 out of 10 goldfish at 48 hours.
a Comment same as above except that at 10.0 ppm the chem-
ical was toxic to 2 out of 10 goldfish in 48 hours.
a Comment same as above except that this chemical was not
toxic to trout or goldfish at 10 ppm.
a Comment same as above except that at 10.0 ppm the chem-
~ ical was toxic to 6 out of 10 goldfish at 48 hours.
a Comment same as above except that at 10 ppm the chem-
ical was toxic to 1 out of 10 fish in 48 hours.
a Comment same as above except that at 1 0 ppm this chem-
ical was not toxic to trout or goldfish.
a Comment same as above except data cited.
a Comment same as above except that no fish were killed at
1 0 ppm.
Reference
(Year)
Hermann
(1959)
Walker, et al
(1966)
Walker, et al
(1966)
Walker, et al
(1966)
Walker, et al
Walker, et al
(1966)
Walker, et al
(1966)
Walker, et al
(1966)
Walker, et al
(1966)
^
•o
m
g
x
^
-------
OJ
2
O
•33
m
w
3
4'-chloro-2-
nitrobenz-
anilide
5'-chloro-4-
nitrobenz-
anilide
3'-chloro-3-
nitro-p-benzo-
toluidide
5'-chloro-2-
nitrophenol
(free phenol)
Chloronitro-
propane
5'-chloro-3-
nitro-o-sali-
sylanilide
2'-chloro-5-
nitrosalicyl-
anilide
3'-chloro-3-
nitrosalicyl-
anilide
4'-chloro-3-
nitrosalicyl-
anilide
Salmo
gairdnerii
Carassius
auratus
Salmo
gairdnerii
Carassius
auratus
Salmo
gairdnerii
Carassius
auratus
Petromyzon
marinus
Salmo
gairdnerii
S. trutta
Protococcus sp
Chlorella sp
Dunaliella
euchlora
Phaeodactylum
tricornutum
Monochrysis
lutheri
Salmo
gairdnerii
Carassius
auratus
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
Salmo
gairdnerii
Carassius
auratus
Salmo
gairdnerii
Carassius
auratus
Salmo
gairdnerii
Carassius
auratus
BSA
BSA
BSA
10.0 (K2)
10.0 (K2)
10.0 (K2)
(O)
(O)
(O)
3(K 100%)
5(K10%)
5(K 10%)
80 (K)
80 (K)
80 (K)
80 (K)
80 (K)
1.0 (K3A)
10.0IK3A)
10.0 (K 3 hr)
10.0(K3hr)
1.0 (K2)
10.0(K3hrs)
10.0 (K 3 hrs)
1.0(K2)
1.0(K3hr)
0.1 (K2)
1.0(K3hr)
Comment same as above except data cited.
Comment same as above except that at 10.0 ppm the chem-
ical was toxic to 6 out of 10 goldfish in 48 hours.
Comment same as above except that chemical precipitated
at 10 ppm, and the chemical was not toxic to trout. At
0.1 ppm the chemical was toxic to 1 out of 10 goldfish.
Mortality occurred in approximately 24 hr. This was a
study on controlling sea lamprey larvae.
This paper concerns the growth of pure cultures of marine
plankton in the presence of toxicants. Results were ex-
pressed as the ratio of optical density of growth in the
presence of toxicants to optical density in the basal
medium with no added toxicants.
This paper deals with the relations between chemical struc-
tures of salicylanilides and benzanilides and their toxicity
to rainbow trout and goldfish. The chemical structure of
salicylanilides and benzanilides was related to toxicity and
selectivity to rainbow trout and goldfish. Salicylanilides
were more toxic than benzanilides to the fishes. The ortho
hydroxy substitution of salicylanilide accelerated biological
activity against fish. Meta nitro substitution on the salicyl-
anilides and benzanilides increased toxicity to fish. Similar
findings are reported for halogen and their relative
position(s) in the molecule.
Comment same as above.
Comment same as above.
Comment same as above.
Walker, et al
(1966)
Walker, et al
(1966)
Walker, et al
(1966)
Ball
(1966)
Ukeles
(1962)
Walker, et al
(1966)
I
m
O
X
Walker, et al
(1966)
Walker, et al
(1966)
Walker, et al
(1966)
-------
o
I
m
S
o
£ Chemical
to .. ., .
^ 4'-chloro-5-
O nitrosalicyl-
2 anilide
X
H
c
3
m
O
-n
0
m
2
O 3'-chloro-2-
J* nitro-o-benz-
w otoluidide
3'-chloro-3-
nitro-o-
salicylotolu-
idide
6'-chloro-3-
nitro-o-sahcy-
5> lotoluidide
OJ
4'-chloro-3-
nitro-o-salicyl-
otoluidide
2'-chloro-3-
nitro-p-sa-
licylotoluidide
Chlorophenol
(meta)
o-chloro-
phenol
o-chloro-
phenol
Bioassay
or Field
Organism Study 'D
Salmo BSA
gairdnerii
Carassius
auratus
Salmo BSA
gairdnerii
Carassius
auratus
Salmo BSA
gairdnerii
Carassius
auratus
Salmo BSA
gairdnerii
Carassius
auratus
Salmo BSA
gairdnerii
Carassius
auratus
Salmo BSA
gairdnerii
Carassius
auratus
Minnows BSA
Lepomis BSA
macrochirus
Pimephales BSA
promelas
Lepomis
macrochirus
Carassius auratus
Lebistes
reticulatus
Toxicity,
Active
Field Ingredient,
Location'2) ppm '3)
1.0 (K2)
1.0 (K2)
10.0 (K 3 hr)
(0)
(0)
1.0 (K2)
10.0 (K 3hr)
10.0 (K2)
10.0 (K2)
(0)
1.0(K3hr)
10.0 (K 3 hr)
1.0(K3hr)
1.0 (K3hr)
18.0 (T1A)
8.1 (T2A)
12IT4A)
10 (T4A)
14 (T4A)
23 (T4A)
Experimental
Variables
Controlled
or Noted^) Comments
a This paper deals with the relations between chemical struc-
~ tures of salicylanilides and benzanilides and their toxicity
to rainbow trout and goldfish. The chemical structure of
salicylanilides and benzanilides was related to toxicity and
selectivity to rainbow trout and goldfish. Salicylanilides
were more toxic than benzanilides to the fishes. The ortho
hydroxy substitution of salicylanilide accelerated biological
activity against fish. Meta nitro substitution on the salicyl-
anilides and benzanilides increased toxicity to fish. Similar
findings are reported for halogens and their relative
position(s) in the molecule.
a Comment same as above except that this chemical was not
~ toxic to trout or goldfish at 10 ppm.
a Comment same as above except data cited.
a Comment same as above except that this chemical was not
toxic to goldfish at 10 ppm.
a Comment same as above except data cited.
a Comment same as above.
e In the halophenols, the ortho was less toxic than the meta
or para. All of the monohalophenols were less toxic than
the 2,4,6-trihalophenols. Some data on biodegradability of
halophenols were presented.
a c d e f g i o Assays are completely described and autopsy data are
reported.
a c d Most fish survived at test concentrations of about one half
or slightly more of the TLm value. No attempt was made
to estimate 100 percent survival.
Reference
(Year)
Walker, et al
(1966)
Walker, et al
(1966)
Walker, et al
(1966)
Walker, et al
(1966)
Walker, et al
(1966)
Walker, et al
(1966)
Ingols and
Gaffney
(1965)
Lammering and
Burbank
(1961)
Pickering and
Henderson
(1966)
j>
T)
m
z
0
X
J>
-------
Chlorophenol
(ortho)
p-chlorophenol
Chlorophenol
(para)
3-(p-chloro-
phenol)-1,1-
dimethyl-
urea
Bis (p-chloro-
phenoxy)
methane
P-chloro-
phenyl-p-
chloroben-
zenesulfamate
m
2
O
O 3-chloro-
2 propene
|
•X
m
OT
o
m
S
Minnows BSA
Hyborhynchus BSA
notatus
Minnows BSA
Cylindrospermum L
lichen/forme (Cl)
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Bluegill BSA
Cylindrospermum L
lichen/forme (Cl)
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Pimephales BSA
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
58 (T1A)
(O)
14 (T1A)
2.0 (O)
(0)
2.0 (O)
24 (T4A)
42 (T4A)
22 (T4A)
48 (T4A)
*c d
In the halophenols, the ortho was less toxic than the meta Ingols and
or para. All of the monohalophenols were less toxic than Gaffney
the 2,4,6-trihalophenols. Some data on biodegradability (1965)
of halophenols were presented.
Fish in aquaria were trained to detect and distinguish between Hasler and
phenol and p-chlorophenol at levels as low as 0.0005 ppm. Wisby
The fish could also distinguish o-chlorophenol from the two (1949)
other compounds. The training method is described.
In the halophenols, the ortho was less toxic than the meta Ingols and
or para. All of the monohalophenols were less toxic than Gaffney
the 2,4,6-trihalophenols. Some data on biodegradability (1965)
of halophenols were presented.
Observations were made on the 3rd, 7th, 14th, and 21st days Palmer and
to give the following (T = toxic, NT = nontoxic, PT = partially Maloney
toxic with number of days in parentheses. No number indi- (1955)
cates observation is for entire test period of 21 days):
Cl -PT (7),T (21)
Ma-T
So -T (7),PT (21)
Cv -T (3),PT (14)
Gp-T
Np-T
No mortality occurred at 0.05 ppm and very low mortality Linduska and
at 0.10 ppm. All fish died when the concentration was Surber
0.2 ppm. (1948)
Observations were made on the 3rd, 7th, 14th, and 21st days Palmer and
to give the following (T = toxic, NT = nontoxic, PT = partially Maloney
toxic with number of days in parentheses. No number indi- (1955)
cates observation is for entire test period of 21 days):
Cl - PT (3)
Ma-PT(14)
So - PT (7)
Cv -NT
Gp - PT (7)
Np-T (3)
Most fish survived at test concentrations of about one half, Pickering and
or slightly more, of the TLm value. No attempt was made Henderson
to estimate 100 percent survival. (1966)
•o
m
Z
O
X
-------
CHEMICALS
>
D
2
x
-1
3)
m
tn
O
-n
o
m
2
£
£
tjj
Chemical
4, chJoro-o-
toloxy-
acetic
acid
Chromic
acid
Chromic
chloride
Chromic
sulfate
Chromic
sulfate
Chromic
sulfate
Chromic
sulfate
Chromic
sulfate plus
sodium di-
chromate
Chromium,
hexavalent
Bioassay
or Field
Organism Study (D
Cylindrospermum L
lichen/forme (Cl)
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Daphnia BSA
magna
Daphnia BSA
magna
BOD L
Sewage BOD
organisms
Sewage BOD
organisms
Daphnia BSA
magna
Lymnaea sp BSA
(eggs)
Bluegill, F
pumpkinseed
sunfish, and
orangespots
Toxicity,
Active
Field Ingredient,
Location'2' ppm'3)
2.0 (0)
O.6 (0)
«3.6 (S)
1.0(0)
- (O)
117ITC50)
0.1 (T1A)
0.03 (T2A)
0.2 (T1A)
Wood- (O)
stock.
III.
Experimental
Variables
Controlled
or Noted'4' Comments
a Observations were made on the 3rd, 7th, 14th, and 21st days
~~ to give the following (T = toxic, NT = nontoxic, PT = partially
toxic with number of days in parentheses. No number indi-
cates observation is for entire test period of 21 days):
Cl -T(3)
Ma -NT
So -NT
Cv -NT
Gp-T(3)
Np - T (3)
a c This paper deals with the toxicity thresholds of various sub-
~ stances found in industrial wastes determined by the use
of D. magna. Centrifuged Lake Erie water was used as a
diluent in the bioassay. Threshold concentration was defined
as the highest concentration which would just fail to im-
mobilize the animals under prolonged (theoretically infinite)
exposure.
a Lake Erie water was used as diluent. Toxicity given as
~ threshold concentration producing immobilization for
exposure periods of 64 hr.
j "Toxicity" is expressed as 10 percent reduction in oxygen
utilization.
— Chromate ion is less toxic than chromic. 1 .0 ppm produced
a 10% oxygen depletion as compared to a control, and
10 ppm produced a 30% depletion.
a The purpose of this paper was to devise a toxicity index for
~ industrial wastes. Results are recorded as the toxic con-
centration producing 50 percent inhibition (TCsg) of
oxygen utilization as compared to controls. Five toxigrams
depicting the effect of the chemicals on BOD were devised
and each chemical classified.
a c "Standard reference water" was described and used as well
as lake water. Varied results were obtained when evaluations
were made in various types of water.
a c Comment same as above.
c At chromium concentrations above 50 ppm, the range of
survival was such that no general curve could be applied
to the data plotted on the chart.
Reference
(Year)
Palmer and
Maloney
(1955)
Anderson
(1944)
Anderson
(1948)
Ingols
(1955)
Ingols
(1954)
Hermann
(1959)
Dowden and
Bennett
(1965)
Dowden and
Bennett
(1965)
Klassen, et al
(1948)
^
•o
m
O
X
-------
Chromium
Chromium
(hexavalent)
Chromium
(hexavalent)
Chromium (as
chromate)
Chromium
Chromium
Chlorococcum
variegatus
C. humicola
Scenedesmus
obliquus
Lepocinclis
steinii
Sal mo
gairdnerii
Lepomis
macrochirus
Salmo
gairdnerii
Salmo
gairdnerii
Rainbow
trout
BSA
BSCH
6.4-16.0 (O)
3.2-6.4 (O)
3.2-6.4 (O)
0.32-1.6(0)
2.5 (O)
FR
110IT4A)
5(K15)*
10 (K15)**
12.5 (K15)*
* 40% kill
**80% kill
2.5 (O)
Scotland 20 (NTE)
a c d f q
a c e f I m
Chromium as dichromate was evaluated in two different Hervey
tests. The concentrations reported are a range which (1949)
completely inhibited growth for 56 days. Concentra-
tions as low as 0.0001 to 0.032 ppm stimulated growth
up to 33 days of C. humicola, S. obliquus, and L. steinii.
Data for a flagellate and two diatoms are also presented.
For accumulation studies, fish were exposed for periods up Knoll and
to 24 days. For elimination studies, fish were exposed for Fromm
12 days, then placed in fresh water from 5 to 25. Chro- (1960)
mium in the blood never exceeded the concentration of
the surrounding water. All other tissues except muscle
accumulated concentrations in excess of that in the water.
Chromium was eliminated rapidly from blood, liver,
stomach, pyloric caeca, and posterior gut. The spleen lost
little of its chromium even after being in fresh water for
25 days. The kidney lost about 50% of its chromium in
25 days of fresh water exposure.
Soft water was used. Alkalinity and hardness significantly Trama and
reduced the toxicity of hexavalent chromium. Benoit
(1960)
This study is concerned with the measurement of chromium Fromm and
in trout before and after exposure. Chromium uptake is Stokes
passive, and the amount accumulated is dependent on the (1962)
concentration in water and duration of exposure.
Trout were exposed to 2.5 ppm of chromium as chromate Stokes and
in tap water for one week. The in vitro glucose transport Fromm
by gut segments from these animals was compared to that (1965)
of segments from untreated fish. The values from the
treated animals was 40 percent lower than the controls.
This work represents an extension of laboratory studies of Herbert, et al
the toxicity of complex effluents to investigations of (1965)
= Chromium
O
O
30
m
O
m
o
Mixture:
Chromium (a)-
naphthenic acids
(b)-cyanide (c)
Mixture
Chromium
chloride
Gasterosteus
aculeatus
Lepomis
macrochirus
Sewage
organisms
BSA
BSA
BOD
1.0(0)
(a) 0.019 (T4A)
(b) 4.74 (T4A)
(c) 0.26 (T4A)
0.18(0)
ji^e This is a discussion of a bioassay method using stickleback
fish and spectrophotometric determinations of the chem-
icals evaluated. The number listed is said to be the
"toxic limit" for the fish.
a c d e All fish were acclimatized for 2 weeks in a synthetic dilu-
tion water.
Various metal salts were studied in relation to how they af-
fected the BOD of both raw and treated sewage as well as
how they affected the processing of sewage in the treatment
plant. BOD was used as the parameter to measure the effect
of the chemical. The chemical concentration cited is the
ppm required to reduce the BOD values by 50%. This chem-
ical was tested in an unbuffered system.
Hawksley
(1967)
Cairns and
Scheier
(1968)
Sheets
(1957)
-------
CHEMICALS
>
O
2
X
c
•33
m
en
o
-n
O
X
m
2
o
Ui
>
OJ
OO
Chemical
Chromium
chromate
Chromium
dichromate
Chromium
oxide
Chromium
potassium
sulfate
Chromium
sulfate
Citric
acid
Citric
acid
Cobalt
Organism
Lepomis
macrochirus
Lepomis
macrochirus
Sewage
organisms
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Gasterosteus
aculeatus
Daphnia
magna
Biomorpholaria
a. alexandrina
Bulinus
truncatus
L ymnaea
caillaudi
Lebistes
reticulatus
Bufo
valliceps
(tadpoles)
Daphnia
magna
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study<1' Location<2) ppm'3) or Noted'4'
BSA - 170 (T4A) acdfq
BSA - 113IT4A) acde
BOD - 4.0 (O)
BSA - (S) 5.07 (T4A) cdef
(H) 67.4 (T4A)
(S) 7.46 (T4A)
(H) 71.9 (T4A)
(S) 4.10 (T4A)
(S) 3.33 (T4A)
BSA - 1.2 (K10)
BSA - 153 (O) ac
BSA - 1200(K1A) a
1000 (K1A)
800 (K1A)
L - 100.0 (K) ace
100.0 (K)
50.0 (K)
Comments
Soft water was used. Alkalinity and hardness significantly
reduced the toxicity of this form of chromium.
All fish were acclimatized for 2 weeks in a synthetic dilution
water.
The purpose of this experiment was to determine whether
there was a constant relationship between the responses
of these organisms. From the data presented, there was no
apparent relationship of this type. Therefore the authors
advise that bioassays on at least 3 components of the food
web be made in any situation.
(S) Soft water
(H) Hard water
Values are expressed as mg/l of chromium.
Solutions were made up in tap water. 3.0 to 5.0 cm stickle-
back fish were used as experimental animals. This paper
points out that there is a marked relationship between the
toxicity of the metals and their solution pressures. Those
with low solution pressures were the most toxic.
This paper deals with the toxicity thresholds of various sub-
stances found in industrial wastes as determined by the use
of D. magna. Centrifuged Lake Erie water was used as a
diluent in the bioassay. Threshold concentration was de-
fined as the highest concentration which would just fail to
immobilize the animals under prolonged (theoretically
infinite) exposure.
The degree of tolerance for vector snails of biharziasis chem-
icals is somewhat dependent upon temperature. The tem-
perature at which (K1 A) occurred was 27 C for Bulinus and
Biornphalaria and 28 C for Lymnaea.
It is assumed in this experiment that the cations considered
are toxic because they combine with an essential sulfhydryl
group attached to a key enzyme. This treatment indicates
that the metals which form the most insoluble sulf ides are
the most toxic. The log of the concentration of the metal
ion is plotted against the log of the solubility product con-
stant of the metal sulfide — a treatment that does not lend
itself to tabulation. The cation toxicity cited is only an ap-
proximate concentration interpolated from a graph. Time
of death was not cpecified.
Reference
(Year)
Trama and
Benoit
(1960)
Cairns and
Scheier
(1968)
Sheets
(1957)
Pickering and
Henderson
(1965)
Jones
(1939)
Anderson
(1944)
Gohar and
EI-Gindy
(1961)
Shaw and
Grushkin
(1967)
TJ
m
Z
O
-------
vo
o
m
S
>
O
m
en
O
Tl
O
m
Cobalt
chloride
Cobalt
chloride
Cobalt
chloride
Cobaltous
chloride
Cobalt
nitrate
Copper
Cu
Copper ion
(copper
chloride and
copper
sulfate
Daphnia
magna
Sewage
organisms
Limnaea
palustris
BSA
BOD
Daphnia
magna
BSA
BSA
<3.1 (S)
64.0 (TC50)
4x 10-5 M (K1)
<26 (O)
a c
Gasterosteus
aculeatus
Carassius
carassius
BSA
BSA
10(K10)
(O)
Copper
Nemacheilus
barbatulus
Lepomis
macrochirus
Sewage
organisms
BCH
BCH
BSA
BOD
England
England
0.28 (K)
0.20-0.30 (K)
0.74 (T4A)
0.94 (T2A)
(O)
a c d e
Lake Erie water was used as diluent. Toxicity given as Anderson
threshold concentration producing immobilization for (1948)
exposure periods of 64 hr.
The purpose of this paper was to devise a toxicity index for Hermann
industrial wastes. Results are recorded as the toxic concen- (1959)
tration producing 50 percent inhibition (TCgo) of oxygen
utilization as compared to controls. Five toxigrams depict-
ing the effect of the chemicals on BOD were devised and
each chemical classified.
Toxicity is given in molar concentrations for maximum direct Morrill
mortality (kill) in 4 hours. (1963)
This paper deals with the toxicity thresholds of various sub- Anderson
stances found in industrial wastes as determined by the use (1944)
of D. magna. Centrifuged Lake Erie water was used as a
diluent in the bioassay. Threshold concentration was defined
as the highest concentration which would just fail to im-
mobilize the animals under prolonged (theoretically infinite)
exposure.
Solutions were made up in tap water. 3.0 to 5.0 cm stickle- Jones
back fish were used as experimental animals. This paper (1939)
points out that there is a marked relationship between the
toxicity of the metals and their solution pressures. Those
with low solution pressures were the most toxic.
This old, lengthy paper discusses toxicity of many chemicals. Powers
possible mechanism of action of some, the effect of tern- (1918)
perature, effect of dissolved oxygen, the efficiency of the
goldfish as a test animal, compares this work with earlier
work, and lists an extensive bibliography.
In water distilled from a copper still with block-tin leads, the
fish survived 352 to 597 minutes — perhaps the effect of
copper.
Fresh water input was through Cu pipes into an aquarium. Mackereth and
All fish died within 24 hours at concentrations of 0.20 ppm Smyly
and above. (1951)
Modified Chu 14 diluent made of distilled water was used Trama
with aeration toxicity of copper ion was found to be de- (1954)
pendent upon pH. Below pH 5.3, all copper is in solution,
above this the copper precipitates and is less toxic.
Copper was more toxic than zinc in all concentrations from Ingols
0.1 to 10.0 ppm. The presence of the element could result (1956)
in errors in BOD tests. At 1.0 ppm the oxygen demand in
percent of the control was 65%.
m
O
-------
0
m
S
o
P Chemical
2 Copper
O
S
X
-1
!j Copper
m
e/)
O
-n
O
m
5 Copper
O
r-
Copper
Copper
T
O Copper
Copper
Organism
Chlorella
vulgar is
Nereis sp
Carcinus
maenas
Leander
squi/la
Salmo
salar
Rainbow
trout
Gasterosteus
aculeatus
Orconectes
rusticus
Lebistes
reticulatus
Bufo
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study (1) Location)2) ppm<3)
L - (0)
BSA - 1.5(K2-3)
0.5 (K4)
(0)
(0)
BCFA - 0.034 (T1A)
FR Scotland 0.8 (T2)
BSA - 0.02 (0)
BCFA -
3.0 (T4A)
1.0 (T1A)
1.0(K6)(T6A)
1.0(T6)(T6A)
BSA - 1.0(K)
0.1 (K)
Experimental
Variables
Controlled
or Noted(4) Comments
ace This was a respiration study using a shake culture technique.
~~ 10~1 M copper sulfate was not inhibitory for 7-20 hours.
Concentrations of 10'3 M copper sulfate were toxic to un-
shaken cultures.
a The threshold of copper for Nereis worms was about 0.1 ppm.
The copper toxicity threshold for the shore crab was 1-2 ppm.
The copper toxicity threshold for prawns was below 0.5 ppm.
act The laboratory water in which the experiment was performed
~ contained 3 /Jg/liter of zinc, as judged by analyses over sev-
eral years, and 2 jug/liter of copper. Lethal concentrations
of mixtures activities or three times as fast as the metals
singly, a somewhat greater potentiation than was found in
the previous tests with salmon.
a c e f I m This work represents an extension of laboratory studies of
the toxicity of complex effluents to investigations of rivers.
ace This is a discussion of a bioassay method using stickleback
fish and spectrophotometric determinations of the chemi-
cals evaluated. The number listed is said to be the "toxic
limit" for the fish.
a c e f All experiments were conducted at 20 C.
~ ~ Crayfish in the intermolt adult stage.
Adult crayfish.
Juvenile crayfish.
Recently hatched young which remained clinging to pleopods
of the female during the first molt.
An acute toxicity threshold existed between 0.6 and
0.125 mg/l for newly hatched young. At a concentration
of 1 mg/l, 50% mortality among newly hatched young was
reached with an exposure time of 1/50th required for
adults.
ace It is assumed in this experiment that the cations considered
are toxic because they combine with an essential sulfhydryl
group attached to a key enzyme. This treatment indicates
Reference
(Year)
Hassall
(1962)
Raymont and
Shields
(1964)
Sprague
(1965)
Herbert, et al
(1965)
Hawksley
(1967)
Hubschman
(1967)
Shaw and
Grushkin
(1967)
•o
m
z
o
valliceps
(tadpoles)
Daphnia
magna
0.1 (K)
that the metals which form the most insoluble sulfides are the
most toxic. The log of the concentration of the metal ion is
plotted against the log of the solubility product constant of
the metal sulf ide — a treatment that does not lend itself to
tabulation. The cation toxicity cited is only an approximate
concentration interpolated from a graph. Time of death was
not specified.
-------
Copper
Copper
Copper
X
X
m
v>
Copper (a)-
acetic acid (b)-
acetaldehyde
(c)-acetone
(d) mixture
Copper para-
amino
benzoate
Copper
carbonate
(basic)
Copper
citrate
Copper
cyanide
complex
Copper
cyanide
complex
Sodium
cyanide
(533 ppm CN-)
and
Cupric sulfate
(427 ppm Cu)
Copper
disodium
versenate
Pimephales
promelas
Salmo
gairdnerii
Lepomis
macrochirus
Lepomis
macrochirus
Balanus
eberneus
Balanus
balanoides
Balanus
eberneus
Balanus
balanoides
Balanus
eberneus
Lepomis
macrochirus
(juveniles)
Pimephales
promelas
BCFCH
0.43 (T4A)
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
0.4 to
0.5 (T2A)
1.25(T4A)
(a) 1.04 (T4A)
(b) 26.0 (T4A)
(c) 5.2 (T4A)
(d) 5.2 (T4A)
0.9 (O)
0.41 (0)
0.28 (O)
0.60 (O)
0.55 (O)
4.0 (O)
1.5 (T4) CN-
1.2(T4) Cu
Channel
catfish
(fingerlings)
BSA
1881
(K25hr A)
a c d e f The paper discusses growth rate, number of spawnings, num-
ber of eggs produced and hatchability of eggs in water con-
taining 4.4 to 95 ppm copper. Results indicated that the
sublethal concentrations of copper affecting growth and
reproduction lies between 3 and 7 percent of the 96-hr
median tolerance limit.
a c d e f The concentration killing a half batch of fish in 2 days pro-
vides a reasonable estimate of the threshold concentration.
The lethality of this chemical depends upon the total
hardness and dissolved oxygen concentration.
a c d e All fish were acclimatized for 2 weeks in a synthetic dilution
water.
a c d e Comment same as above.
The concentration listed was lethal to 90% of adult barnacles
in 2 days.
The concentration listed was lethal to 90% of adult barnacles
in 2 days.
Comment same as above.
£ c d f p For the concentration given, the median resistance time was
~ ~~ 226 minutes.
Synthetic soft water was used. Toxicity data given as number
of test fish surviving after exposure at 24, 48, and 96 hr.
TLm values were estimated by straight-line graphical inter-
polation and given in ppm CN".
Tap water was used. Considerable additional data are
presented.
Mount
(1968)
Brown
(1968)
Cairns and
Scheier
(1968)
Cairns and
Scheier
(1968)
Clarke
(1947)
Clarke
(1947)
Clarke
(1947)
Doudoroff, et al
(1966)
Doudoroff, et al
(1956)
m
O
Clemens and
Sneed
(1959)
5
-------
Jf-
t J
o
I
m
5
o
i Chemical
in
5 Copper
O naphthenate
S
X
H
C
33
m
O
-n
n
m
3
0
•£ Copper
w nitrate
Copper
salicylate
Copper
salts
h
j
Copper salt
plus citrate
Copper
sodium
citrate
Toxicity,
Bioassay Active
or Field Field Ingredient,
Organism Study ^' Location^) ppmJ3)
Cylindrospermum L — 2.0 (O)
lichen/forme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Gasterosteus BSA - 1.0IT6.5A)
aculeatus
Balanus BSA - 0.90 (0)
eberneus
Salmo BSA - (0)
gairdnerii
Cylindrospermum L — 2.0 (0)
licheniforme (Cl)
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Artemia BSA - 0.005 (O)
salina
Acartia 0.01 (O)
clausi
Elminus 0.002 (O)
modestus
Experimental
Variables
Controlled
or Noted(4) Comments
a Observations were made on the 3rd, 7th, 14th. and 21st days
~ to give the following (T = toxic, NT = nontoxic, PT = par-
tially toxic with number of days in parentheses. No number
indicates observation is for entire test period of 21 days) :
Cl - PT (7)
Ma - T (3)
So - PT (3)
Cv - PT (3)
Gp-T (7),PT (14)
Np-NT
a c Death of the fish resulted from an interaction between the
metallic ion and the mucus secreted by the gills. Coagulated
mucus formed on the gill membranes and impaired respira-
tion to such a degree that the fish asphyxiated.
The concentration listed was lethal to 90% of adult barnacles
in 2 days.
a e This is a study of the effect of varying dissolved oxygen con-
centration on the toxicity of selected chemicals.
The toxicity of heavy metals, ammonia, and monohydric
phenols increased as the dissolved oxygen in water was
reduced. The most obvious reaction of fish to lowered oxy-
gen content is to increase the volume of water passed over
the gills, and this may increase the amount of poison reach-
ing the surface of the gill epithelium.
The concentration of the chemical in the water was not
specified.
a Observations were made on the 3rd, 7th, 14th, and 21st days
to give the following (T = toxic, NT = nontoxic, PT = par-
tially toxic with number of days in parentheses. No number
indicates observation is for entire test period of 21 days):
Cl - T (3)
Ma-T (3)
So - PT (7)
Cv - T (3)
Gp'- T (3)
Np-T(3)
a c All tests were conducted in seawater.
Toxicity values reported are relative to that of mercuric
chloride expressed as unity.
Mechanism of action is discussed, as well as synergistic action
of two poisons administered simultaneously.
Reference
(Year)
Palmer and
Maloney
(1955)
Jones
(1938)
Clarke
(1947)
Lloyd
(1961)
Palmer and
Maloney
(1955)
Corner and
Sparrow
(1956)
m
2
X
>
-------
Copper
tartrate
Copper
and zinc
Copper
and zinc
Copper
chloride
Copper
chloride
(tech)
Copper
chloride
Copper
sulfate
Balanus
balanoides
Atlantic
salmon
Salmo
salar
Carassius
carass/us
Bluegill
Nitzschia
linearis
Lepomis
macrochirus
Algae
zooplankton
BSA
FR
Canada
0.58 (O)
(O)
BSA
0.048 Cu (O)
0.600 Zn
BSA
(O)
BSA?
BSA
Lakes in
Wise.
0.980 (T4A)
0.795-0.815
(T5A)
1.25(T4A)
(O)
a e g I n
The concentration listed was lethal to 90% of adult barnacles Clarke
in 2 days. (1947)
"Toxicity index" for copper and zinc combined was de- Sprague
scribed in connection with disturbed salmon migration. (1964)
Toxicity index > 1.0 indicates lethality to "young salmon
after long exposure". A toxicity index of 0.15 or 15% of
lethal concentration of copper and zinc seemed to be the
maximum safe level for salmon migration.
The values given are for an ILL (incipient lethal level) and in Sigler, et al
this instance only in water of 20 mg/liter of hardness. (1966)
Concentrations above this are lethal in about one day. These
values were determined by bioassay. Salmon parr in the
laboratory avoided less than one tenth of incipient lethal
levels. Avoidance thresholds were 0.09 ILL of zinc, 0.05 ILL
of copper and 0.02 ILL of equitoxic mixtures. In equitoxic
mixtures of these compounds, the ILL was additive.
This old, lengthy paper discusses toxicity of many chemicals. Powers
possible mechanism of action of some, the effect of temper- (1918)
ature, effect of dissolved oxygen, the efficiency of the gold-
fish as a test animal, compares this work with earlier work,
and lists an extensive bibliography.
In a concentration of 0.66N, fish survived 78 minutes; at a
concentration of 0.0000011N, fish survived 300 minutes —
truly a very wide variation.
This is an estimated LCgg value at temperatures from 55 Cope
to 75 F. (1965)
The purpose of this experiment was to determine whether Patrick, et al
there was a constant relationship between the responses (1968)
of these organisms. From the data presented, there was no
apparent relationship of this type. Therefore the authors
advise that bioassays on at least 3 components of the food
web be made in any situation.
Copper sulfate was applied when deemed necessary to control Domogalla
algae (0.50 pounds of copper sulfate per million gallons of (1935)
water). Applications of copper sulfate were made as re-
quired over an eleven-year period. Zooplankton was not
effected by these applications. The spray applied for control
of algae also kept fish fungal diseases under control.
•33
m
O
m
5
9
u,
-------
CHEMICALS
>
Z
O
Z
X
H
3D
m
tn
o
-n
O
m
S
£
K
»
^
^
Chemical
Copper
sulfate
Copper
sulfate
Copper
sulfate
Copper
sulfate
Copper
sulfate
(anhydrous)
Organism
Morons
americana
Perca
flavescens
All fish
Mesocyclops
obsoletus
Macrobdella
decora
Nymphaea
Juncus
Pontederia
Scirpus
Eriocaulon
Potamogeton
Algae
Morone
americana
Perca
flavescens
All fish
Mesocyclops
obsoletus
Macrobdella
decora
Nymphaea
Juncus
Pontederia
Scirpus
Eriocaulon
Potamogeton
Algae
Smallmouth
black bass
Chara sp
Pygosteus
pungitius
Lymnaeid
snails
Toxicity,
Bioassay Active
or Field Field Ingredient,
StudyCH Location (2) ppm(3)
FL 4 lakes, 1 (K)
Nova
Scotia 1 (K)
3 (K)
3 (SB)
3 (SB)
3 (NTE)
3 (NTE)
3 (NTE)
3 (NTE)
3 (NTE)
3 (NTE)
3 (NTE)
FL 4 lakes, 1 (K)
Nova
Scotia 1 (K)
3(K)
3 (SB)
3 (SB)
3 (NTE)
3 (NTE)
3 (NTE)
3 (NTE)
3 (NTE)
3 (NTE)
3(K)
FL Leetown, 2.0 (O)
Va.
BCF - (O)
BSA - 1.0 (K1A)
Experimental
Variables
Controlled
or Noted'4) Comments
a c d f The work was undertaken to test the feasibility of utilizing
poisons as a direct means of studying the production of
fish in streams and lakes. Caution must be used to prevent
irreparable damage by indiscriminate poisoning.
a c d f Comment same as above.
d Treatment of a series of ponds resulted in control of Chara
spp but no or slight fish kill due to copper sulfate. Some
kill occurred because of suffocation caused by decaying
vegetation.
a c Fish were exposed to 0.1 , 0.04, and 0.01 N copper sulfate.
~~ pH of the solutions was 5.0, 5.4, and 5.8. Survival times
were 55, 62, and 75 minutes, respectively.
- Each test container (500-ml beaker) was filled with ditch
water.
Reference
(Year)
Smith
(1939)
Smith
(1939)
Surber and
Everhart
(1950)
Jones
(1947)
Batte, et al
(1951)
>
T)
-o
m
z
D
X
-------
Copper
sulfate
2
O
O
5
Copper
sulfate
Copper
sulfate
Copper
sulfate
Copper sulfate
(with stabi-
lizing agent)
Copper
sulfate
C
30
m
CO
o Copper
"" sulfate
O
Tendipes
plumosus
Pisidium
idahoense
and other
bottom-
dwelling
organisms
FL&
BSA
Wise.
(O)
BOD
Microcystis
aeruginosa
Cylindrospermum
lichen/forme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gpi
Nitzschia
palea (Np)
Cylindrospermum
licheniforme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Pimephales
promelas
Sewage
organisms
1.0(0)
100 (K)
2.0 (O)
2.0 (O)
BSA
BOD
0.18 (T4A)
0.4 (O)
The bottom muds of Lake Morona contained up to 480 milli- Mackenthun
grams of copper per kilogram of mud on a dry-weight basis. and Cooley
Lakes Nagawicka and Pewaukee contain up to 22 and 55, (1952)
respectively. All contained thriving populations of aquatic
organisms despite years of CuSO4 application for algal con-
trol. From laboratory bioassays of muds containing CuSO4,
it was concluded that 9,000 parts per million copper on a
dry-weight basis precipitated and accumulated in bottom
muds was toxic to bottom organisms. From the results of
these studies, it is indicated that differences occurring in the
population density of bottom organisms in the four lakes
studied are due to ecological variables within these separate
bodies of water.
"Toxicity" is expressed as 39 percent reduction in oxygen Ingols
utilization. (1955)
The chemical was tested on a 5-day algae culture, 1 x 106 to Fitzgerald, et al
2 x 106 cells/ml, 75 ml total volume. Chu No. 10 medium (1952)
was used.
Observations were made on the 3rd, 7th, 14th, and 21st days Palmer and
to give the following (T = toxic, NT = nontoxic, PT = partially Maloney
toxic with number of days in parentheses. No number indi- (1955)
cates observation is for entire test period of 21 days):
Cl -PT (7),T (14)
Ma - T (3)
So - PT (7)
Cv - T (3)
Gp - T (3)
Np-T(3)
Comment same as above except that
Cl - T (3)
Ma - T (3)
So - PT (3)
Cv - T (3)
Gp-T(3)
Np-T(3)
Palmer and
Maloney
(1955)
a c d e f Toxicity to 30 species of algae is also presented. CuSO4
was algicidal in the range 0.5 to 2.0 ppm.
— This is part of a report listing 27 anions and their toxicities
on a planarian. Mode of action of the anions is discussed.
Water distilled in glass was used to prepare the solutions.
The pH of this solution was 7.0. Solutions were renewed
every 12 hours.
Palmer and
Maloney
(1956)
Sheets
(1957)
m
O
X
-------
CHEMICALS
>
O
Z
X
c
3)
m
w
O
^
O
I
m
S
o
E
C/l
J
•pk
ON
Chemical
Copper
sulfate
Copper
sulphate
Copper
sulfate
Copper
sulfate
Copper
sulfate
Copper
sulfate
Copper
sulfate
Copper
sulfate
Organism
Gambusia
a1 'finis
Salmo
gairdneri
(fry)
Salvelinus
fontinalis x
Salmo trutta
Notemigonus
crysoleucas
Micropterus
salmoides
Lepomis
macrochirus
Sewage
organisms
Pimephales
promelas
Lepomis
macrochirus
Limnodrilus
hoffmeisteri
Cyraulus
circumstria tus
Physa
heterostropha
Tendipes
decorus
Rana
pipiens
Physa
heterostropha
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study<1> Location<2) ppm(3) or Noted<4>
BSA - 84 (T2A) acdeg
BSA - 3.8 (T1A) acefip
10(0)
FPA N.Y. 1.0(323) acd
1.0 (K)
1.0 (S23)
1.0 (S23)
BOD - 21 (TC50) a
BSA - (H)1.4(T4A) acdf
(S) 0.05 (T4A)
(H) 10 (T4A)
(S) 0.2 (T4A)
BSA — 0.40 (T4A) a c d i
0.425 (T4A)
0.27 (T4A)
1.0 (K60%)
0.032 (K 40%)
BSCH - 16 (K) ac
BSA - 0.56 (T1 A) acf
Comments
The effect of turbidity on the toxicity of the chemicals
was studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
Five hatchery troughs were employed with 6 Imperial
gallons (27.276 liters) of hatchery water. The water
used in the experiments was reportedly typical of
Inyanga Rhodesia trout streams and dams. Concentra-
tions of 10 ppm of copper sulphate caused 90-100%
mortality.
Conventional farm ponds were used having an average surface
area of 0.3 acre and a maximum depth of 7-9 ft. Toxicity
(in ppm) to fish as maximum safe concentration (S) for
23 days was determined. Concentration of 0.5 ppm was
required to control algae.
The purpose of this paper was to devise a toxicity index for
industrial wastes. Results are recorded as the toxic con-
centration producing 50 percent inhibition (TC5Q) of oxygen
utilization as compared to controls. Five toxigrams de-
picting the effect of the chemicals on BOD were devised
and each chemical classified.
Both hard (H) and soft (S) water were used.
Hard water only was used in this study for all but T. decorus
which was also studied in soft water.
CuSO4 was toxic to this frog at various temperatures in
concentrations >0.001 5 percent.
These tests were conducted in hard and soft water. Data
indicated small if any differences in toxicity of copper
sulfate due to water hardness.
Reference
(Year)
Wallen, et al
(1957)
Turnbull-Kemp
(1958)
Eipper
(1959)
Hermann
(1959)
Tarzwell and
Henderson
(1960)
Wurtz and
Bridges
(1961)
Kaplan and
Yoh
(1961)
Wurtz
(1962)
>
£
TJ
m
5J5
0
X
-------
Copper
sulfate
Copper
sulfate
Copper
sulfate
Copper
sulfate
(Algeeclear)
(Cuprose)
Copper
sulfate
Copper
(copper
sulfate)
O
X Copper
! sulfate
Copper
sulfate
•33
m
w Copper
O sulfate
S
m
Microcystis sp
Zooplankters
Copepods
Cladocerans
Rotifers
Chaoboridae
Ostracods
etc.
Nais spp
Chlorella
pyrenoidosa
Microcystis
aeroginosa
Chlorella
pyrenoidosa
Anabaena
circinalis
Gloeotrichia
echinulata
Phormodinium
inundatum
Gammarus
lacustris
Salmo
salar
Salmo
salar
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Carp
Tench
Ephemeropterae
larvae
Trichopterae
larvae
FL
Auburn,
Ala.
0.5-0.8 (O)
BSA
BSA
BCF
BSA
BSA
FR
France
1.0 (K)
20 (AS1)
(O)
af
1.5 (T4A)
0.048 (O)
(O)
(S) 0.025 (T4A)
(H) 1.76(T4A)
(S) 0.66 (T4A)
(S) 0.036 (T4A)
(S) 0.036 (T4A)
0.1 (75% K6)
0.2 (75% K6)
0.2 (100%K)
a c d e f
a c d e f
cdef
In a series of ponds, CuSC>4 at the indicated concentration Crance
range reduced the growth of Microcystis spp by as much (1963)
as 95 percent in 5-20 days. This reduction lasted for as
long as 30 days in some cases. According to the authors,
generally there was an inverse relation between the
abundance of Micrycystis and the number of zooplankters.
Around pH 7.0, copper was more toxic in soft than in hard Learner and
water. At 1.00 ppm the average median survival time for Edwards
the worms was reduced from 70 to 35 minutes. It is inter- (1963)
esting that copper is less toxic at a pH of 4.0 than at 7.0.
Describes a bioassay method to differentiate between an algi- Fitzgerald and
cide (AC) and an algistat (AS). The treated culture was sub- Faust
cultured as time progressed. Allen's medium was used. (1963)
Different sources of copper appeared to be equally effective Fitzgerald and
as toxic agents for algae. The medium in which toxicity tests Faust
are carried out had a great influence on the toxicity of cop- (1963)
per. It was pointed out that in copper compounds, the range
in toxic action can vary from algicidal activity at concentra-
tions of 0.05 to 0.4 ppm of CuSC>4, or algistatic activity at
2 to 24 ppm of CuSO4 with certain algae, to situations in
which the growth of algae is only slightly inhibited by a con-
centration of copper sulfate as high as 30 ppm.
Emulsible concentrates were prepared from technical grade Nebeker and
insecticides with acetone as the solvent. Gaufin
Symptoms prior to death were observed and recorded on (1964)
graphs.
The experiments were carried out in soft water. Values are Sprague
reported as micrograms of metal and toxicity as LTso- In (1964)
solutions containing copper and zinc, fish died twice as
fast as would occur if the two metals were simply additive
in their lethal action.
The ECso or the effective concentration that elicited as Sprague
avoidance reaction in the fish was 0.052 x the ILL (1965)
(incipient lethal level), or 0.052 x 44 jUg/L, or 2.28 /Ug/L.
(S) Soft water Pickering and
(H) Hard water Henderson
Values are expressed as mg/l of metal. (1965)
Field studies conducted. Two streams were studied; one Vivier and
was used for testing, the other for control. Trichopterae Nisbet
were not affected, i.e., they were active even at concentra- (1965)
tions of 0.30 ppm.
-------
CHEMICALS
>
O
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X
H
JO
m
w
O
Tl
O
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m
S
5
^
L
P*
SQ
Chemical
Copper
sulfate
Copper
sulfate
(tech)
Copper
sulfate
Copper
sulfate
Copper
sulfate
Toxicity,
Bioassay Active
or Field Field Ingredient,
Organism Study'1' Location (2) ppm (3)
Helix BSA - 0.01-0.1 (O)
pomatia
Bluegill BSA - 2.8 (T4A)
Blue-green algae L - 2.0-4.0 (0)
Cylindrospermum
Anabaena
Anacystis
Calothrix
Nostoc
Oscillator/a
Plectonema
Green algae
Ankistrodesmus
Chlorella
Closterium
Oocystis
Green algae
Scenedesmus
Stigeoclonium
Zygnema
Green flagellate and
yellow algae
Chlamydomonas
Pandorina
Tribonema
Gomphonema
Navicula
Nitzchia
Salmo BSA - 0.150(T2A)
gairdneri
Lepomis 2.800 (T2A)
macrochirus
Lepomis FL Various 13-140 (K)
macrochirus lakes.
Michigan
Experimental
Variables
Controlled Reference
or Noted*4' Comments (Year)
c This paper was concerned with the effect of the chemical on de Calventi
mucous secretion in the snail. (1965)
Snails exposed to the indicated copper sulfate solutions
showed severe signs of toxicity. There was an increase in
mucous secretion and the animals did not respond to
tactile stimuli.
a This is an estimated LC5Q value at temperatures from Cope
55 to 75 F (1965)
— CuSC>4 was generally toxic or partially toxic to blue- Kemp, et al
green algae for 28 days at the indicated concentrations. (1966)
At 2.0 ppm, it was similarly toxic to the green algae.
green flagellates, and yellow algae.
a This paper reports acute toxicity of a number of compounds. Cope
and discusses sub-acute mortality as well. Effects on repro- (1966)
duction and behavior are also discussed. Data presented as
EC50-
a d For controlling bluegill reproduction, copper sulfate crystals Beyerle and
were directed toward nests where eggs and fry were the Williams
primary target. The estimated copper sulfate concentrations (1967)
were estimated to be 13-140 ppm. All eggs and fry were
dead in some 200 samplings. Fish other than bluegill fry
apparently were not killed by this copper sulfate treatment.
Treatment throughout the 3-month spawning period was
required for significant reduction of the bluegill population.
•o
m
Z
O
-------
I
Copper
sulfate
(as Cu)
Copper sulfate
plus
zinc sulfate
(various
ratios)
Cresol
Cresol
Cresol
Ortho-
cresol
O-cresol
m O-cresol
£> O-cresol
3D
m
tn
O p-cresol
TI
O
m
2
9
Salmo
salar
S. trutta
S. Salmo
gairdnerii
Salmo
gairdnerii
Lepomis
macrochirus
Gambusia
affinis
Lepomis
macrochirus
Phoxinus
phoxinus
Sewage
organisms
Channel
catfish
(fingerlings)
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Fish
BSCH
0.06 (K)
cf
BSA
BCFA
BSA
BSA
BCFA
BOD
BSA
BSA
BSA
(O)
13.6 (T4A) small
10.9 (T4A) med.
10 (T4A) large
24 (T2A)
10.0 (T4A)
0.04% (K 13min)
a e p
a c e f
a c d e g
a cd e i
940 (TC50)
66.8
(K 69 hr A)
13 (T4A)
24 (T4A)
23 (T4A)
29 (T4A)
5.1 x 10-5 M (K)
a c d e f
The reported figure is a reported lethal concentrate as found Grande
in polluted lakes and streams in Norway. Organic matter (1967)
apparently has a masking effect that reduces toxicity. 50%
of rainbow trout eggs survived to hatch in 0.05 ppm of Cu.
Rainbow trout and Atlantic salmon acted similarly to the
chemical. Brown trout were slightly more resistant.
Both hard and soft water were used. Median period of sur- Lloyd
vival in hard water was 3 days — 3.5 ppm Zn, and 1.1 ppm Cu; (1961)
in soft water — 7 days, 0.56 ppm Zn and 0.044 ppm Cu.
Test water was composed of distilled water with CP grade
chemicals and was aerated throughout the 96-hour
exposure period.
The effect of turbidity on the toxicity of the chemicals
was studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
A "control" was prepared by adding required chemicals to
distilled water, and this was constantly aerated. Data
reported are for larger fish, app 14.24 cm in length. Data
for smaller fish are also in the report.
Tap water used as a diluent. The apparatus used was a 34 mm
diameter tube fitted to permit sharp vertical separation of
water and test solution. With this system, avoidance data
could be obtained. Toxicity is given as average survival
time of replicates. Fish avoided concentrations of 0.03 to
0.04%.
The purpose of this paper was to devise a toxicity index for
industrial wastes. Results are recorded as the toxic concen-
tration producing 50 percent inhibition (TCsfj) of oxygen
utilization as compared to controls. Five toxigrams depict-
ing the effect of the chemicals on BOD were devised and
each chemical classified.
Tap water was used. Considerable additional data are
presented.
Most fish survived at test concentrations of about one half,
or slightly more, of the TLm value. No attempt was made
to estimate 100 percent survival.
Avoidance behavior of test fish to toxic chemicals is given.
Toxicity is given as the lowest lethal concentration (molar).
Ratios of avoidance and lowest lethal concentration are
presented and discussed.
Cairns and
Scheier
(1955)
Wallen, et al
(1957)
Cairns and
Scheier
(1959)
Jones
(1951)
Hermann
(1959)
Clemens and
Sneed
(1959)
Pickering and
Henderson
(1966)
m
O
X
Ishio
(1965)
-------
o
I
m
S
D
f. Chemical
to
> Cryolite
0
S
X
H
C
3)
m Crystal violet
CO
O
-n
I Cumene
2 hydroperoxide
=
O
£
Cupric
•^ ammonium
<~n chloride
O
Cupric
chloride
Cupric
chloride
Cupric
citrate
Cupric
oxide
Cupric
sulfate
Bioassay
or Field
Organism Study'1'
Simocephalus BSA
serrulatus
Daphnia
pulex
Microcystis L
aeruginosa
Cylindrospermum L
lichen/forme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Daphnia BSA
magna
Daphnia BSA
magna
Daphnia BSA
magna
Mytilus BSA
edulis
Gambusia BSA
affinis
Daphnia BSA
magna
Toxicity,
Active
Field Ingredient,
Location'2' ppm<3)
10.0 (SB)
5.0 (SB)
100 (K)
2.0 (O)
0.039 (S)
0.08 (0)
0.027 (S)
0.55 (O)
56,000 (T2A)
0.1 (O)
Experimental
Variables
Controlled
or Noted'4' Comments
— Concentration reported is for immobilization.
Time for immobilization was 48 hr.
Data cited are for 60 F, but assays were performed at
varied temperatures. "Water Chemistry" (Unspecified)
was "controlled" during the assay period.
a, etc The chemical was tested on a 5-day algae culture, 1 x 10^
~~ to 2 x 10*> cells/ml, 75 ml total volume. Chu No. 10
medium was used.
a Observations were made on the 3rd, 7th, 14th, and 21st
~ days to give the following (T=toxic, NT=nontoxic, PT=
partially toxic with number of days in parentheses. No
number indicates observation is for entire test period of
21 days):
Cl - PT (7)
Ma-T (7)
So -NT
Cv - PT (7)
Gp - PT (7)
Np - T (7)
a Lake Erie water was used as diluent. Toxicity given as
~~ threshold concentration producing immobilization for
exposure periods of 64 hr.
a c This paper deals with the toxicity thresholds of various
substances found in industrial wastes as determined by
the use of D. magna. Centrifuged Lake Erie water was
used as a diluent in the bioassay. Threshold concentration
was defined as the highest concentration which would just
fail to immobilize the animals under prolonged (theoreti-
cally infinite) exposure.
a Lake Erie water was used as diluent. Toxicity given as
~ threshold concentration producing immobilization for
exposure periods of 64 hr.
— When the mussels were placed in the test solution for one
day, and then in fresh sea water, they died in 2, 3, and-
4 days.
a c d e g The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
a c This paper deals with the toxicity thresholds of various
~~ substances found in industrial wastes as determined by the
use of D. magna. Centrifuged Lake Erie water was used
as a diluent in the bioassay. Threshold concentration was
defined as the highest concentration which would just fail
to immobilize the animals under prolonged (theoretically
infinite) exposure.
Reference
(Year)
Sanders and
Cope
(1966)
Fitzgerald, et al
(1952)
Palmer and
Maloney
(1955)
Anderson
(1948)
Anderson
(1944)
Anderson
(1948)
Clarke
(1947)
Wallen, et al
(1957)
Anderson
(1944)
m
z
o
-------
Cyanide
Cyanide
Cyanide
Cyanide
Cyanide
O
m
£
£
>
o
s
X
in Cyanide
tn
O
Mayorella
palestinensis
(soil amoeba)
BSA
(O)
Lepomis
auritus
L. macrochirus
Micropterus
salmoides
Pomoxis
annularis
Brown trout
Small mouth bass
BSA & CF
BSA
BCF
BCF
Lepomis
macrochirus
Physa
heterostropha
Lepomis
macrochirus
Lebistes
reticulatus
BSA
BSA
BSA
0.06 (T1SA)
0.01-0.06
(T<1SA)
0.05-0.06
(T<1CFA)
0.06 (T<11SA)
0.05-0.07
(T<1SA)
0.02-0.04
(T<1CFA)
0.31-0.96 (O)
0.32-1.06(0)
0.175-1.98(0)
0.18(T4A)
0.432 (T4A)
0.18 (T4A)
(O)
The experiments were carried out in Warburg manometers Reich
at 27 C for 4 hr at a pH of 8.0. (1955)
Cyanide in concentrations up to 5 x 10'3 M were shown
to have lethal effects on the organism.
Results were compared with controls and expressed in per-
cent of respiration.
Compared with normal respiration, nonlethal concentrations
of cyanide increased the respiration of the organism in
glucose-containing solutions.
It was concluded that the respiration of the organism depends
on at least three enzyme systems, which may be distinguished
by their behavior toward cyanide.
Additional data for less than 24 hr are given and also for the Renn
disappearance and breakdown of cyanide in anaerobic soil (1955)
systems.
£ c d e The pH of the water varied from 7.5-8.28 in the test solu- Burdick, et al
~ ~~ tions. Dissolved oxygen was controlled by aeration. In the (1958)
report, time of death is plotted against cyanide concentra-
tion. In a continuous flow apparatus, a range of concentrations
from 0.32 to 1.06 ppm killed in 17-48 minutes and 4.2 to
15.2 minutes, respectively. In a static test, 0.31 to 0.96 ppm
killed in 33-230 and 6.0-18.7 minutes, respectively. These data
are for brown trout. For small mouth bass, in a continuous
flow apparatus, concentrations of 1.98 ppm down to 0.175 ppm
killed in 6-10 and 213-477 minutes respectively. The effect of
dissolved oxygen is discussed.
a c d e All fish were acclimatized for 2 weeks in a synthetic dilution Cairns and
water. Scheier
(1968)
ace The purpose of this experiment was to determine whether Patrick, et al
there was a constant relationship between the lesponses of (1968)
these organisms. From the data presented, there was no
apparent relationship of this type. Therefore the authors
advise that bioassays on at least 3 components of the food
web be made in any situation.
a c f n o A series of equations was devised to describe the toxicity of a Chen and
system containing two toxicants — zinc - zinc and cyanide. Selleck
Concentrations of cyanide, 0.42 ppm, 0.28 ppm, and (1968)
0.26 ppm, killed 50 percent of the animals in 20, 30, and
43 hours, respectively. Toxicity of the two-component
system was then determined using varying ratios of the two
components.
m
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CHEMICALS
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X
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3D
m
VI
0
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o
(n
^
*i
L/I
to
Chemical
Cyanide
Cyanide (al-
chromium (b)-
naphthenic acids
mixture
Cyanide (a)-
zinc (b)-
mixture
Cychohexane
Cyclohexane
1, cyano-1,3-
butadiene
1, cyano-1,3-
butadiene
Cymeme
thiocyanate
2,4-diamino-
phenol dihydro-
chloride
2,4-diamino-
phenol hydro-
chloride
Oiamylamine
Organism
Fish
(unidentified)
Lepomis
macrochirus
(c)
Lepomis
macrochirus
Gambusia
affinis
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Lagodon
rhomboides
Lagodon
rhomboides
Green
sunfish
Microcystis
aeruginosa
Daphnia
magna
Semotilus
atromaculatus
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study'1) Location'2) ppm'3) or Noted'4)
FR Dunreith, 0.05-0.1 (K)
Indiana
BSA - (a) 0.026 (T4A) a c d e
(b) 0.019 (T4A)
(c) 4.74 (T4A)
BSA - (a) 0.26 (T4A) a c d e
(b) 3.90 (T4A)
BSA - 1 5,500 (T2A) _acdeg
BSA - 30 (T4A) a c d e f
31 (T4A)
33 (T4A)
48 (T4A)
BSA - 71.5IT1A) a
BSA - 71.5IT1A)
BSA - (O)
L - 100 (K) a, etc
BSA - 80 (K2) a
BSA - 5 to 20 (CR) a e
Comments
Tests for cyanide pollution were made following a train-
car collision. Five tank cars carrying acetone cyanohydrin.
vinyl chloride, ethylene oxide, and methyl methacrylate
were involved.
All fish were acclimatized for 2 weeks in a synthetic
dilution water.
Comment same as above.
The effect of turbidity on the toxicity of the chemicals
was studied. Test water was from a farm pond with
"high" turbidity. Additional data are presented.
Most fish survived at test concentrations of about one
half, or slightly more, of the TLm value. No attempt was
made to estimate 100 percent survival.
Aerated seawater was used.
Experiments were conducted in aerated salt water.
Fish were moderately repelled at concentrations of
20 mg/l but the response to 10 mg/l was indifferent. The
chemical has apparent high toxicity.
The chemical was tested on a 5-day algae culture, 1 x 10^ to
2 x 106 cells/ml, 75 ml total volume. Chu No. 10 medium
was used.
An attempt was made to correlate the biological action
with the chemical reactivity of selected chemical sub-
stances. Results indicated a considerable correlation
between the aquarium fish toxicity and antiautocatalytic
potency of the chemicals in marked contrast to their
toxicity on systemic administration.
Test water used was freshly aerated Detroit River water. A
typical water analysis is given. Toxicity is expressed as the
"critical range" (CR), which was defined as that concentra-
tion in ppm below which the 4 test fish lived for 24 hr
and above which all test fish died. Additional data are
presented.
Reference
(Year)
Moore and
Kin
(1969)
Cairns and
Scheier
(1968)
Cairns and
Scheier
(1968)
Wallen, et al
(1957)
Pickering and
Henderson
(1966)
Daugherty and
Garrett
(1951)
Garrett
(1957)
Summerfelt and
Lewis
(1967)
Fitzgerald, et al
(1952)
Sollman
(1949)
Gillette, et al
(1952)
^
•o
m
z
g
X
^
-------
2',5'-dibromo-
3-nitrosalicyl-
anilide
Salmo
gairdnerii
Carassius
auratus
BSA
1.0 (K2)
10.0 (K 3 hr)
10.0 (K 3hr)
£
OJ
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^
m
S
o
to
^
Z
O
s
X
c
3D
in
CO
O
O
X
m
2
g
3,5-dinitro-
2',3'-benz-
oxylidide
4',5-dibromo-
3-nitrosalicyl-
anilide
Di-sec-
butylamine
Di-n-
butylamine
1,3-dibutyl-
thiourea
Orthodichloro-
benzene
2,6-dcchloro-
benzine
acid (tech)
2,4-dichloro-
benzyl-
nicotinium
chloride
1,2-dichloro-
ethane
3,6-dichloro-
2,5-dimethoxy-
benzoquinone
Salmo
gairdnerii
Carassius
auratus
Salmo
gairdnerii
Carassius
auratus
Semotilus
atromaculatus
Semotilus
atromaculatus
Semotilus
atromaculatus
Protococcus sp
Chlorella sp
Dunaliella
euchlora
Phaeodactylum
tricornutum
Monochrysis
lutheri
Rainbow
trout
Bluegill
Microcystis
aeruginosa
Lagodon
rhomboides
Microcystis
aeruginosa
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
(O)
(O)
1.0 (K2)
10.0 (K 3hr)
15to40(CR)
20 to 60 (CR)
30 to 100 (CR)
13 (NG)
13 (NG)
13 (NG)
13 (NG)
13 (NG)
140 (T4A)
120(T4A)
5.0 (K)
150-175(0)
75 (K)
This paper deals with the relations between chemical struc-
tures of salicylanilides and benzanilides and their toxicity to
rainbow trout and goldfish. The chemical structure of
salicylanilides and benzanilides was related to toxicity and
selectivity to rainbow trout and goldfish. Salicylanilides
were more toxic than benzanilides to the fishes. The ortho
hydroxy substitution of salicylanilide accelerated biological
activity against fish. Meta nitro substitution on the sali-
cylanilides and benzanilides increased toxicity to fish.
Similar findings are reported for halogens and their relative
position(s) in the molecule.
Comment same as above except that at 10.0 ppm the
chemical was toxic to 1 out of 10 trout in 48 hr. At 10 ppm
the chemical was not toxic to goldfish.
Comment same as above except data cited.
Test water used was freshly aerated Detroit River water. A
typical water analysis is given. Toxicity is expressed as the
"critical range" (CR), which was defined as that concentra-
tion in ppm below which the 4 test fish lived for 24 hr and
above which all test fish died. Additional data are presented.
Comment same as above.
Comment same as above.
This paper concerns the growth of pure cultures of marine
plankton in the presence of toxicants. Results were
expressed as the ratio of optical density of growth in the
presence of toxicants to optical density in the basal
medium with no added toxicants. NG=no growth, but
the organisms were viable.
Walker, et al
(1966)
This is an estimated
55 to 75 F.
ue at temperatures from
a, etc The chemical was tested on a 5-day algae culture, 1 x 10§ to
2 x 106 cells/ml, 75 ml total volume. Chu No. 10 medium
was used.
- Experiments were conducted in aerated salt water. Toxicity
range given as the concentrations which produced <1/2
deaths and >112 deaths.
£, etc The chemical was tested on a 5-day-old algae culture,
1 x 106 to 2 x 106 cells/ml, 75 ml total volume. Chu No. 10
medium was used.
Walker, et al
(1966)
Walker, et al
(1966)
Gillette, et al
(1952)
Gillette, et al
(1952)
Gillette, et al
(1952)
Ukeles
(1962)
z
O
Cope
(1965)
Fitzgerald, et al
(1952)
Garrett
(1 957)
Fitzgerald, et al
(1952)
-------
i Toxicity,
™ Bioassay Active
5 or Field Field Ingredient,
P Chemical Organism Study*D Location*?) ppm*3)
> 1,1-dichloro- Lagodon BSA - 250-275 (O)
O ethane rhomboides
S
^ 1,4-dichloro- Green BSA - 6.5 (T1A)
C 2-nitro- sunfish 4.5 (T2A)
m benzene
(/)
O
-n
O 4,4-dichloro- Cylindrospermum L - 2.0 (O)
m alpha- lichen/forme (CD
5 methyl- Microcystis
Q benzhydrol aeruginosa (Mai
r~ Scenedesmus
obliquus (Sot
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gpl
Nitzschia
palea (Np)
^ 2,3-dichloro- Fish: BSA - (0)
i naphtho- Pomoxis
f± quinone nigromaculatus
Notropis
antherinoides
Hyborhynchus
notatus
Ambloplites
rupestris
Hum
salmoides
Water Plants:
Ceratophyllum
Myrophyllum
Elodea
Invertebrates:
Snails
Daphnia
Rotifers
Experimental
Variables
Controlled Reference
or Noted*4) Comments (Year)
— Experiments were conducted in aerated salt water. Toxicity Garrett
range given as the concentrations which produced <1/2 (1957)
deaths and >1 12 deaths.
a e p The main purpose of this experiment was to determine the Summerfelt and
repellent characteristics of certain chemicals. Experiments Lewis
were conducted in a wooden trough. (1967)
The toxic action of this chemical appeared to involve
suffocation.
a Observations were made on the 3rd, 7th, 14th, and 21st days Palmer and
~~ to give the following (T = toxic, NT = nontoxic, PT = partially Maloney
toxic with number of days in parentheses. No number (1955)
indicates observation is for entire test period of 21 days):
Cl - PT (3)
Ma- NT
So -NT
Cv - NT
Gp-PT(14)
Np-NT
e Aerated spring water was used as the test medium. No effect Fitzgerald, et al
~ was observed on fish after 2 days of exposure, even with (1952)
excess solid dispersed in water. No effect was observed on
higher aquatic plants and green algae. At concentrations in
excess of saturation level (100 mg/l), no toxic effect was
observed. At algicidal concentrations, no toxic effect was
noted on any of the species studied.
^
*o
m
Z
g
^
-------
2,3-dichloro-
napthoqui-
none
2,3-dichloro-
naphtho-
quinone
2,5-dichloro-
4-nitrophenol
2,5-dichloro-
4-nitrophenol
(Na salt)
I> 2,5-dichloro-
(free phenol)
3',4'-dichloro-
3-nitrosalicyl-
anilide
O
m
S
£ Dichloro-
O phenoxy-
2 butyric
X acid
c
3D
m
v>
O
•n
O
m
Cylindrospermum
lichen/forme (Cl)
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Pimephales
promelas
Petromyzon
marinus
(larvae)
Petromyzon
marinus
Salmo
trutta
Petromyzon
marinus
Salmo
gairdnerii
S. trutta
Salmo
gairdnerii
Carassius
auratus
2.0 (O)
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
0.15(T4A)
10 (K<1)
5(K100%)
17 (K 10%)
3(K100%)
13 (K 10%)
7 (K 10%)
1.0(K3hr)
1.0 (K2)
10.0 (K3hr)
acdef
Pteronarcys sp
(nymphs)
BSA
15.0IT4A)
Observations were made on the 3rd, 7th, 14th, and 21st days Palmer and
to give the following (T = toxic, NT = nontoxic, PT = partially Maloney
toxic with number of days in parentheses. No number (1955)
indicates observation is for entire test period of 21 days):
Cl -PT(7)
Ma-T
So -NT
Cv - PT (7)
Gp-T(7), PT(14)
Np-T
Toxicity to 30 species of algae also presented. 2,3 DNQ
was algicidal in the range 0.5 to 2.5 ppm.
Additional data are presented.
Mortality occurred in approximately 24 hr. This was a
study on controlling sea lamprey larvae.
Comment same as above.
Maloney and
Palmer
(1956)
Piavis
(1962)
Ball
(1966)
Ball
(1966)
m
O
This paper deals with the relations between chemical struc- Walker, et al
tures of salicylanilides and benzanilides and their toxicity (1966)
to rainbow trout and goldfish. The chemical structure of
salicylanilides and benzanilides was related to toxicity and
selectivity to rainbow trout and goldfish. Salicylanilides
were more toxic than benzanilides to the fishes. The ortho
hydroxy substitution of salicylanilide accelerated biological
activity against fish. Meta nitro substitution on the salicyl-
anilides and benzanilides increased toxicity to fish. Similar
findings are reported for halogens and their relative posi-
tion (s) in the molecule.
Experiments were all conducted at 60 F in 1964. The values Cope
were listed as LC^rj. (1965)
9
U,
-------
CHEMICALS
>
O
s
*
-1
3
m
en
O
o
X
m
S
2
In
»
i
*N
Chemical
Di (p-chloro-
phenyl)
methyl
carbinol
Diethanol-
amine
Diethanol-
amine
Diethylamine
Diethylamino-
hydrochloride
2',5'-diethyl-
3,5-dinitro-
benzanilide
Diethylene
glycol
Bioassay
or Field
Organism Study (D
Cylindrospermum L
licheniforme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Gambusia BSA
af finis
Sewage BOD
microorganisms
Semotilus BSA
atromaculatus
Semotilus BSA
atromaculatus
Salmo BSA
gairdnerii
Carassius
auratus
Gambusia BSA
affinis
Toxicity, Experimental
Active Variables
Field Ingredient, Controlled
Location <2) ppm(3) or Noted^ Comments
— 2.0 (O) a Observations were made on the 3rd, 7th, 14th, and 21st days
~~ to give the following (T = toxic, NT= non toxic, PT = partially
toxic with number of days in parentheses. No number
indicates observation is for entire test period of 21 days) :
Cl -PT(7)
Ma -NT
So - T (3)
Cv - T (3)
Gp - T (3)
Np - T (3)
— 1,550 (T2A) acdeg The effect of turbidity on the toxicity of the chemicals was
~ studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
— (O) — The chemical was studied as to how low levels (ppm) may
affect the BOD in domestic sewage. This compound was
not toxic to sewage organisms, but responded readily to
acclimated seed and contributed to the biochemical oxy-
gen demand.
— 70 to 100 (CR) ae Test water used was freshly aerated Detroit River water. A
~ typical water analysis is given. Toxicity is expressed as the
"critical range" (CR), which was defined as that concentra-
tion in ppm below which the 4 test fish lived for 24 hr and
above which all test fish died. Additional data are presented.
— 4,000 to 6,000 a e Comment same as above.
(CR)
— (O) a This paper deals with the relations between chemical struc-
tures of salicylanilides and benzanilides and their toxicity
(0) to rainbow trout and goldfish. The chemical structure of
salicylanilides and benzanilides was related to toxicity and
selectivity to rainbow trout and goldfish. Salicylanilides
were more toxic than benzanilides to the fishes. The ortho
hydroxy substitution of salicylanilide accelerated biological
activity against fish. Meta nitro substitution on the salicyl-
anilides and benzanilides increased toxicity to fish. Similar
findings are reported for halogens and their relative posi-
tion(s) in the molecule. At 10 ppm the chemical was not
toxic to trout. At 10.0 ppm, the chemical was toxic to
1 out of 10 goldfish in 48 hours.
- 32,000 (T2A) acdeg The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
Reference
(Year)
Palmer and
Maloney
(1955)
Wallen, et al
(1957)
Oberton and
Stack
(1957)
Gillette, et al
(1952).
Gillette, et al
(1952)
Walker, et al
(1966)
Wallen, et al
(1957)
^
^0
m
O
X
-------
Diethyl-
ethanol-
amine
Diethyl
nitrosoamine
1,3-diethyl-
thiourea
Diglycolic
acid
m-dihydroxy-
benzene
Di-isobutyl-
Semotilus
atromaculatus
Semotilus
atromaculatus
Semotilus
atromaculatus
Lepomis
macrochirus
Sewage
organisms
Semotilus
atromaculatus
BSA
BSA
BSA
BSA
BOD
80 to 120 (CR)
900-1,100 (CR)
100to300(CR)
105 (T1A)
(NTE)
BSA
*•
on
O
m
s
>
en
^
z
O
5
x
H
c
3
m
CO
O
•n
O
I
m
S
Di-isopropyl-
amine
Dimethyl-
amine
Dimethylamino-
benzaldehyde
0,0-dimethyl
dithiophos-
phate (47.7 per-
cent)
4,5-dimentyl-
2-mercapto-
thiazole
Semotilus
atromaculatus
Semotilus
atromaculatus
Cylindrospermum
lichen/forme (Cl)
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Lymnaeid
snails
Daphnia
magna
BSA
BSA
L
BSA
BSA
20 to 40 (CR)
40 to 60 (CR)
30 to 50 (CR)
2.0 (O)
(O)
56 (K2)
Test water used was freshly aerated Detroit River water. A
typical water analysis is given. Toxicity is expressed as the
"critical range" (CR), which was defined as that concentra-
tion in ppm below which the 4 test fish lived for 24 hr and
above which all test fish died. Additional data are presented.
Comment same as above.
a e Comment same as above.
a b e This report is a simple and straightforward determination of
a median tolerable limit for a selected group of herbicides.
a The purpose of this paper was to devise a toxicity index for
~ industrial wastes. Results are recorded as the toxic con-
centration producing 50 percent inhibition (TCsg) of oxy-
gen utilization as compared to controls. Five toxigrams
depicting the effect of the chemicals on BOD were devised
and each chemical classified.
a e Test water used was freshly aerated Detroit River water. A
~ typical water analysis is given. Toxicity is expressed as the
"critical range" (CR), which was defined as that concentra-
tion in ppm below which the 4 test fish lived for 24 hr and
above which all test fish died. Additional data are presented.
a e Comment same as above.
Comment same as above.
Observations were made on the 3rd, 7th, 14th, and 21st days
to give the following (T = toxic, NT = nontoxic, PT = partially
toxic with number of days in parentheses. No number
indicates observation is for entire test period of 21 days):
Cl -NT
Ma-NT
So -NT
Cv -NT
Gp-NT
Np-NT
Each test container, 500-ml beaker, was filled with ditch
water. Less than 100% mortality occurred in concentra-
tions of 1:100,000.
An attempt was made to correlate the biological action with
the chemical reactivity of selected chemical substances.
Results indicated a considerable correlation between the
aquarium fish toxicity and antiautocatalytic potency of the
chemicals in marked contrast to their toxicity on systemic
administration.
Gillette, et al
(1952)
Gillette, et al
(1952)
Gillette, et al
(1952)
Hughes and
Davis
(1967)
Hermann
(1959)
Gillette, et al
(1952)
Gillette, et al
(1952)
Gillette, et al
(1952)
Palmer and
Maloney
(1955)
m
0
X
Batte, et al
(1951)
Sollman
(1949)
-------
CHEMICALS
>
O
3
X
H
(3
3J
m
o
o
I
tT\
3
o
r
CO
.J,.
tyi
00
Chemical
2',3'-dimethyl-
3-nitrosalicyl-
anilide
2',4'-dimethyl-
3-nitrosalicyl-
anilide
2',5'-dimethyl-
3-nitrosalicyl-
anilide
2',6'-dimethyl-
3-nitrosalicyl-
anilide
Dimethyl
sulphoxide
Dimethyl
su If oxide
Organism
Sea
lamprey
(larva)
Salmo
gairdneri
(fingerling)
Sea
lamprey
(larva)
Salmo
gairdneri
(fingerling)
Sea
lamprey
(larva)
Salmo
gairdneri
(fingerling)
Sea
lamprey
(larva)
Salmo
gairdneri
(fingerling)
Carassius
auratus
Hemigrammus
erythrozonus
Paracheinodon
innesi
Xiphophorus
maculatus
Pescilia
latipinna
Poecilia
reticulata
Brachydanio
rerio
Corydoras
paleatus
Toxicity,
Bioassay Active
or Field Field Ingredient,
StudyCI) Location(2) ppm*3)
BSA - 3.0(LD100>
5.0 (LD25)
BSA - 3.0 (LD-|00>
7.0 (LD25)
BSA - 1.0(LD100>
0.7 (LD25)
BSA - >10.0(LDioo>
>10.0(LD25)
BSA - (0)
BSA - (O)
Experimental
Variables
Controlled
or Noted<4)
See
Applegate,
et al
(1957-1958)
See
Applegate,
et al
(1957-1958)
See
Applegate,
et al
(1957-1958)
See
Applegate,
et al
(1957-1958)
af
ace
Comments
This paper deals with the comparative toxicity of halonitro-
salicylanilides to sea lamprey and fingerling rainbow trout
as a function of substituent loci.
Comment same as above.
Comment same as above.
Comment same as above.
At 32 ppt DMSO, five goldfish survived for 10 days without
exhibiting signs of respiratory stress or symptoms of toxic
reaction. In a similar concentration of acetone the median
period of survival was about 90 minutes.
According to the authors, the LD5Q concentration in 0-5 days
was found to be 1 .9% for P. innesi, H. erythrozonus.
P. reticulata, P. latipinna, and X. maculatus. B. rerio and
C. poleatus tolerated higher concentrations of DMSO for
longer periods of time.
Reference
(Year)
Starkey and
Howell
(1966)
Starkey and
Howell
(1966)
Starkey and
Howell
(1966)
Starkey and
Howell
(1966)
Ball
(1966)
Rabinowitz and
Myerson
(1966)
^
•o
"O
m
z
2
x
-------
Dimethyl
su If oxide
Dimethyl
su If oxide
1,3-dimethyl-
urea
3,5-dinitro-
benzanilide
O
m
I
O
s
X m-dinitro-
^ benzene
3) (tech)
m
M m-dinitro-
£fj benzene
O
m
Salmo
gairdneri
Salvellnus
fontinales
S. namaycush
Cyprinus
carpio
Ictalurus
me/as
I. punctatus
Lepomis
cyanellus
L. macrochirus
Perca
flavescens
Oncorhynchus
tshawytscha
O. nerka
O. kisutch
Salmo
gairdneri
Semotilus
atromacu/atus
Salmo
gairdnerii
Carassius
auratus
BSA
BSA
BSA
BSA
Lymnaeid
snails
Microcystis
aeruginosa
BSA
53,000
32,300
54,500
36,500
47,800
37,300
44,000
41,700
42,500
36,500
39,000
32,500
65,000
43,000
72,000
33,500
65,000
37,000
12 (L)
(T1A)
(T3A)
(T1A)
(T3A)
(T1A)
(T3A)
(T1A)
(T3A)
(T1A)
(T3A)
(T1A)
(T3A)
(T1A)
(T2A)
(T1A)
(T2A)
(T1A)
(T2A)
Water quality had little effect on toxicity of DMSO but
increased temperature increased the toxicity to rainbow
trout.
Willford
(1967)
7,000 to 15,000
-------
CHEMICALS
z
0
s
X
c
3)
m
en
0
Tl
O
m
2
o
EJ
i
ON
Chemical
3.5-dinitro-2',3'-
benzoxylidide
3,5-dinitro-o-
benzotoluidide
Dinitro-o-sec-
butylphenol
(tech)
Dinitro-o-sec-
butylphenol
2,6-dinitro-4-
chlorophenol
(tech)
Dinitrocresol
(tech)
3,5-dinitro-o-
cresol
(tech)
4,6-dinitro-o-
cresol acetate
(tech)
Bioassay
or Field
Organism Study'D
Salmo BSA
gairdnerii
Carassius
auratus
Salmo BSA
gairdnerii
Carassius
auratus
Lymnaeid BSA
snails
Cylindrospermum L
lichen/forme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cy)
Gomphonema
parvulum fGp)
Nitzschia
palea (Np)
Lymnaeid BSA
snails
Pteronarcys BSA
californica
(naiads)
Lymnaeid BSA
snails
Lymnaeid BSA
snails
Toxicity, Experimental
Active Variables
Field Ingredient, Controlled
Location'2) ppm(3) or Noted'4) Comments
— (O) a This paper deals with the relations between chemical struc-
tures of salicylanilides and benzanilides and their toxicity
(O) to rainbow trout and goldfish. The chemical structure of
salicylanilides and benzanilides was related to toxicity and
selectivity to rainbow trout and goldfish. Salicylanilides
were more toxic than benzanilides to the fishes. The ortho
hydroxy substitution of salicylanilide accelerated biological
activity against fish. Meta nitro substitution on the sali-
cylanilides and benzanilides increased toxicity to fish.
Similar findings are reported for halogens and their relative
position(s) in the molecule. At 10.0 ppm, the chemical was
toxic to 1 out of 10 trout in 48 hours. At 10 ppm the
chemical was not toxic to goldfish.
— 10.1 (K2) a Comment same as above except at 10.0 ppm, the chemical
~~ was toxic to 8 out of 10 goldfish at 48 hours.
(0)
— (O) — Comment same as above except 100% mortality occurred at
1 :200,000 and greater.
— 2.0 (O) a Observations were made on the 3rd, 7th, 14th, and 21st days
to give the following (T = toxic, NT = nontoxic, PT = partially
toxic with number of days in parentheses. No number
indicates observation is for entire test period of 21 days):
Cl -NT
Ma - NT
So - NT
Cv -NT
Gp-NT
Np-NT
— (0) — Each test container (500-ml beaker) was filled with ditch
water. Less than 100% mortality occurred in concentrations
of 1:100,000.
- 0.00032 (T4A) acdef Data reported as LC5Q at 15.5 C in 4 days.
— (CO — Each test container (500-ml beaker) was filled with ditch
water. Less than 100% mortality occurred in concentrations
of 1:100,000.
— (O) — Comment same as above.
Reference
(Year)
Walker, et al
(1966)
Walker, et al
(1966)
Batte, et al
(1951)
Palmer and
Maloney
(1955)
Batte, et al
(1951)
Sanders and
Cope
(1968)
Bane, et al
(1951)
Batte, et al
(1951)
^
^
m
Z
g
x
-------
4,6-dinitro-o-
cresol methyl
ether (tech)
Dinitro-o-cyclo-
hexylphenol
(38 percent)
Dinitro-o-cyclo-
hexylphenol, di-
cyclohexylamine
salt (tech)
Dinitro-o-cyclo-
hexylphenol
Dinitro-o-cyclo-
hexylphenol,
dicyclohexyl-
amine salt
(20 percent)
2,4-dinitro-
phenol
Lymnaeid
snails
Lymnaeid
snails
Lymnaeid
snails
Lymnaeid
snails
Lymnaeid
snails
Sewage
organisms
BSA
BSA
BSA
BSA
BSA
BOD
IN
O
m
S
>
CO
z
o
2
X
c
m
CO
O
-n
O
m
2
2,4-dinitro-
phenol (tech)
2,4-dinitro-
phenolhydrazine
(tech)
2,4-dinitro-
phenol.
sodium salt
(tech)
2,4-dinitro-
phenyl-
hydrazine
2,4-dinitro-
phenyl-
hydrazine
Lymnaeid
snails
Lymnaeid
snails
Lymnaeid
snails
Microcystis
aeruginosa
Cylindrospermum
licheniforme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (Sol
Chlorella
variegata (Cv)
Comphonema
parvulum (Gp)
Nitzschia
palea (Np)
BSA
BSA
BSA
(O)
(O)
(O)
1.0 (K1)
(O)
100(TC50)
(O)
(O)
(0)
100 (K)
2.0(0)
a, etc.
Comment same as above.
Comment same as above except 100% mortality occurred
in concentrations of 1:400,000 and greater.
Comment same as above except 100% mortality occurred
in concentrations of 1:200,000 and greater.
Each test container (500-ml beaker) was filled with ditch
water.
Comment same as above except 100% mortality occurred
in concentrations of 1:400,000 and greater.
The purpose of this paper was to devise a toxicity index for
industrial wastes. Results are recorded as the toxic con-
centration producing 50 percent inhibition (TC5fj) of
oxygen utilization as compared to controls. Five toxi-
grams depicting the effect of the chemicals on BOD were
devised and each chemical classified.
Each test container (500-ml beaker) was filled with ditch
water. Less than 100% mortality occurred in concentrations
of 1:100,000.
Comment same as above.
Comment same as above.
The chemical was tested on a 5-day algae culture, 1 x 10^
to 2 x 106 cells/ml, 75 ml total volume. Chu No. 10
medium was used.
Observations were made on the 3rd, 7th, 14th, and 21st days
to give the following (T = toxic, NT = nontoxic, PT =
partially toxic with number of days in parentheses. No
number indicates observation is for entire test period of
21 days):
Cl -NT
Ma -NT
So - NT PT (7)
Cv -NT
Gp -NT
Np -NT
Batte, et al
(1951)
Batte, et al
(1951)
Batte, et al
(1951)
Batte, et al
(1951)
Batte, et al
(1951)
Hermann
(1959)
Batte, et al
(1951)
Batte, et al
(1951)
Batte, et al
(1951)
Fitzgerald,
et al
(1952)
Palmer and
Maloney
(1955)
m
o
-------
CHEMICALS
z
O
s
X
-J
31
m
u>
O
-n
0
m
S
o
[o
>.
ON
NJ
Chemical
2',3-dimtro-m-
salicylanilide
2',3-dinitro-p-
salicylotoluidide
3,5-dinitro-o-
salicylotoluidide
2,4-dinitro-
thymol (tech)
2,4-dinitro-
toluene (tech)
Di-n-propylamine
Disodium copper
salt of ethylene
diamine-tetra
acetic acid
Bioassay
or Field
Organism Study'1 )
Salmo BSA
gairdnerii
Carassius
auratus
Salmo BSA
gairdnerii
Carassius
auratus
Salmo BSA
gairdnerii
Carassius
auratus
Lymnaeid BSA
snails
Lymnaeid BSA
snails
Semotilus BSA
atromaculatus
Cylindrospermum L
lichen/forme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Toxicity,
Active
Field Ingredient,
Location'2) ppm (3)
1.0 (K2)
10.0 (K 3 hr)
(0)
1.0 (K2)
10.0 (K 3hr)
10.0 (K 2)
10.0 (K 3 hr)
(0)
(0)
(0)
20 to 60 (CR)
2.0 (0)
Experimental
Variables
Controlled
or Noted'4) Comments
a This paper deals with the relations between chemical struct
~~ tures of salicylanilides and benzanilides and their toxicity
to rainbow trout and goldfish. The chemical structure of
salicylanilides and benzanilides was related to toxicity and
selectivity to rainbow trout and goldfish. Salicylanilides
were more toxic than benzanilides to the fishes. The ortho
hydroxy substitution of salicylanilide accelerated biological
activity against fish. Meta nitro substitution on the salicyl-
anilides and benzanilides increased toxicity to fish. Similar
findings are reported for halogens and their relative
position(s) in the molecule. At 10.0 ppm, the chemical
was not toxic to goldfish.
a Comment same as above except data cited.
a Comment same as above except that at 10.0 ppm, the chem-
~ ical was toxic to 9 out of 10 goldfish at 48 hr.
— Each test container (500-ml beaker) was filled with ditch
water. 100% mortality occurred in concentrations of
1 : 400,000 and greater.
— Comment same as above except less than 100% mortality
occurred in concentrations of 1:100,000.
a e Test water was freshly aerated Detroit River water. A
typical water analysis is given. Toxicity is expressed as
the "critical range" (CR), which was defined as that
concentration in ppm below which the 4 test fish lived
for 24 hr and above which all test fish died. Additional
data are presented.
a Observations were made on the 3rd, 7th, 14th, and 21st days
to give the following (T = toxic, NT = nontoxic, PT =
partially toxic with number of days in parentheses. No
number indicates observation is for entire test period of
21 days):
Cl -NT
Ma -PT (14)
So -NT
Cv -NT
Gp - NT
NP - NT
Reference
(Year)
Walker, et al
(1966)
Walker, et al
(1966)
Walker, et al
(1966)
Batte, et al
(1951)
Batte, et al
(1951)
Gillette, et al
(1952)
Palmer and
Maloney
(1955)
TJ
TJ
z
0
X
>
-------
fc
co
X
m
2
3J
m
CO
O
-n
O
m
2
Disodium
octoborate
tetrahydrate
Dodecylaceta-
mido-dimethyl
benzyl
ammonium
chloride
Disodium Cylindrospermum L
ethylene lichen/forme (Cl)
bisdithio- Microcystis
carbamate aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Salmo BSA
gairdnerii
Cyclindrospermum L
lichen/forme (Cl)
Gleocapsa
sp (GP)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Ethanol Lesbistes BSA
reticulatus
Carassius
auratus
Ethyl alcohol Carassius BSA
Carassius
Ethyl alcohol Daphnia BSA
magna
Ethyl alcohol Pygosteus BCF
pungitius
2.0 (O)
4200 (T1A)
2750 (T2A)
2.0 (O)
(O)
(O)
18,400 (O)
(O)
Comment same as above except that:
Cl -NT
Ma -PT (14)
So -NT
Cv - T (3)
Gp-T(3)
Np -T(3)
Palmer and
Maloney
(1955)
Most of the weed-killer formulations in this study consisted Alabaster
of more than one substance, i.e., oils, emulsifiers, stabilizers, (1956)
and other adjuvants.
Observations were made on the 3rd, 7th, 14th, and 21st days Palmer and
to give the following (T = toxic, NT = nontoxic, PT = Maloney
partially toxic with number of days in parentheses. No (1955)
number indicates observation is for entire test period of
21 days):
Cl - PT (7)
G -T(3), PT(14)
So -T
Cv -T
Gp -T
Np -T
The uptake of ethanol from buffered solution by guppies Hayton
has been studied. There was an apparent increase in the and Hall
rate of absorption with increasing pH. Experiments with (1968)
goldfish failed to show an increase in absorption rate as
the pH was increased.
This old, lengthy paper discusses toxicity of many chemicals. Powers
possible mechanism of action of some, the effect of tempera- (1918)
ture, effect of dissolved oxygen, the efficiency of the gold-
fish as a test animal, compares this work with earlier work,
and lists an extensive bibliography.
In a concentration of 16 cc per liter, fish survived 98 minutes.
This paper deals with the toxicity thresholds of various sub- Anderson
stances found in industrial wastes as determined by the use of (1944)
D. magna. Centrifuged Lake Erie water was used as a diluent
in the bioassay. Threshold concentration was defined as the
highest concentration which would just fail to immobilize
the animals under prolonged (theoretically infinite) exposure.
A concentration of 4 percent ethyl alcohol immediately intox- Jones
icated the fish, which recovered when placed in fresh water. (1949)
A 1 percent solution caused the fish to exhibit an avoidance
reaction.
D
X
-------
o
I
m
2
o
i Chemical
^ Ethyl alcohol
O
S
X
H
C
30
00 Ethyl benzene
O
O
I
m
S
O
>
Cj
Ethyldietha-
nolamine
Ethylene
diamine
Ethylene
thiourea
2,ethy 1-1,3-
hexanediol
1-(2-ethyl-
hexyl)-2-
undecyl-
1 ,4,5,6-
tetrahydro-
pyrimidine
Ethylmercuric
chloride
Organism
Semotilus
atromaculatus
Pimephales
promelas
Lepomis
macrochirus
Carassius
a u rat us
Lebistes
reticulatus
Semotilus
atromaculatus
Semotilus
atromaculatus
Semotilus
atromaculatus
Channel
catfish
(fingerlings)
Microcystis
aeruginosa
Artemia
salina
Acartia
clausi
Elminius
modestus
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study'D Location<2) ppm(3) or Noted^)
BSA - 7,000 to a e
9,000 (CR)
BSA - 40 (T4A) acdef
29 (T4A)
73 (T4A)
78 (T4A)
BSA - 160 to 200 (CR) ae
BSA - 30 to 60 (CR) ae
BSA - 6,000 to a e
8,000 (CR)
BSA - 624(K25hrA) a
L - 2.0 (K) a, etc
BSA - 24.0 (O) a c
2.0 (0)
4.4 (O)
Comments
Test water used was freshly aerated Detroit River water. A
typical water analysis is given. Toxicity is expressed as the
"critical range" (CR), which was defined as that concen-
tration in ppm below which the 4 test fish lived for 24 hrs.
and above which all test fish died. Additional data are
presented.
Most fish survived at test concentrations of about one half.
or slightly more, of the TLm value. No attempt was made
to estimate 100 percent survival.
Test water used was freshly aerated Detroit River water. A
typical water analysis is given. Toxicity is expressed as the
"critical range" (CR), which was defined as that concen-
tration in ppm below which the 4 test fish lived for 24 hr
and above which all test fish died. Additional data are
presented.
Comment same as above.
Comment same as above.
Tap water was used. Considerable additional data are
presented.
The chemical was tested on a 5-day algae culture, 1x10^
to 2 x 106 cells/ml, 75 ml total volume. Chu No. 10
medium was used.
All tests were conducted in seawater.
Toxicity values reported are relative to that of mercuric
chloride expressed as unity.
Mechanism of action is discussed, as well as synergistic
Reference
(Year)
Gillette, et al
(1952)
Pickering and
Henderson
(1966)
Gillette, et al
(1952)
Gillette, et al
(1952)
Gillette, et al
(1952)
Clemens and
Sneed
(1959)
Fitzgerald, et al
(1952)
Corner and
Sparrow
(1956)
^
TJ
TJ
m
Z
o
x
action of two poisons administered simultaneously.
-------
2'-ethyl-3-nitro-
salicylanilide
O-ethyl-s-
pentachloro-
phenyl
thiocarbamate
Ferric chloride
Ferric chloride
o
m
£
X
•33
m
en
Ferric chloride
Ferric chloride
Ferric chloride
Ferric chloride
Ferric sulfate
Salmo
gairdnerii
Carassius
a u rat us
BSA
(O)
Petromyzoh
marinus
(larvae)
Carassius
carassius
Daphnia
magna
Daphnia
magna
Gambusia
affinis
Biomorpholaria
alexandrina
Bulinus
truncatus
Daphnia
magna
Gambusia
affinis
BSA
BSA
10 (K<1)
(O)
BSA
130 (O)
BSA
BSA
BSA
BSA
BSA
74 (T2A)
200 (K1)
200 (K1)
36(71 A)
21 (T2A)
15(T4A)
133IT2A)
a c d e g
a c d eg
This paper deals with the relations between chemical struc- Walker, et al
tures of salicylanilides and benzanilides and their toxicity (1966)
to rainbow trout and goldfish. The chemical structure of
salicylanilides and benzanilides was related to toxicity and
selectivity to rainbow trout and goldfish. Salicylanilides
were more toxic than benzanilides to the fishes. The ortho
hydroxy substitution of salicylanilide accelerated biological
activity against fish. Meta nitro substitution on the salicyl-
anilides and benzanilides increased toxicity to fish. Similar
findings are reported for halogens and their relative position(s)
in the molecule. No affect occurred for rainbow trout or
goldfish at 0.1 and 1.0 ppm.
Additional data are presented. Piavis
(1962)
This old, lengthy paper discusses toxicity of many chemicals, Powers
possible mechanism of action of some, the effect of tern- (1918)
perature, effect of dissolved oxygen, the efficiency of the
goldfish as a test animal, compared this work with earlier
work, and lists an extensive bibliography.
In a concentration of 0.284N, fish survived 29 minutes; in a
concentration of 0.0000166N, they survived 1200 minutes.
This paper deals with the toxicity thresholds of various sub- Anderson
stances found in industrial wastes as determined by the use of (1944)
D. magna. Centrifuged Lake Erie water was used as a diluent
in the bioassay. Threshold concentration was defined as the
highest concentration which would just fail to immobilize
the animals under prolonged (theoretically infinite) exposure.
Lake Erie water was used as diluent. Toxicity given as Anderson
threshold concentration producing immobilization for (1944)
exposure periods of 64 hr.
The effect of turbidity on the toxicity of the chemicals was Wallen, et al
studied. Test water was from a farm pond with "high" (1957)
turbidity. Additional data are presented.
The degree of tolerance for vector snails of bilharziasis to Gohar and
various chemicals is somewhat dependent upon tempera- EI-Gindy
ture. The temperature at which (K1) occurred was 26 C. (1961)
"Standard reference water" was described and used as well Dowden and
as lake water. Varied results were obtained when evalua- Bennett
tions were made in various types of water. (1965)
The effect of turbidity on the toxicity of the chemicals was Wallen, et al
studied. Test water was from a farm pond with "high" (1957)
turbidity. Additional data are presented.
I
m
D
X
O
m
-------
CHEMICAL!
WJ
0
s
X
H
C
3D
m
en
O
Tl
o
i
m
5
O
r;
i/i
ON
ON
Chemical
Ferrocyanide
complex
Sodium
cyanide
(482 ppmCN-)
and
Ferrous sulfate
(193 ppm Fe++)
Ferrous
chloride
Ferrous
disodium
versenate
Ferrous oxide
Ferrous sulfate
Ferrous sulfate
Ferrous sulfate
Ferrous sulphate
Organism
Pimephales
promelas
Daphnia
magna
Channel
catfish
(fingerlings)
Gambusia
affinis
Daphnia
magna
Micropterus
salmoides
Lepomis
machrochirus
Goldfish
Sewage
organisms
Biomorph olaria
alexandrina
Bulinus
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Studydl Location(2) ppm(3) or Noted<4)
BSA - 10(K<48hr) ac
BSA - <38(S) a
BSA - >500 a
(K25hrA) ~~
BSA - 1 0,000 (T2A) acdeg
~
BSA - <152(O) ac
BSA - 100 (O) acfpi
100 (O)
100 (O)
BOD - (NTE) a
BSA - 900 (K1) a
900 (K1)
Comments
Synthetic soft water was used. Toxicity data given as
number of test fish surviving after exposure at 24, 48,
and 96 hr.
Lake Erie water was used as diluent. Toxicity given as
threshold concentration producing immobilization for
exposure periods of 64 hr.
Tap water was used. Considerable additional data are
presented.
The effect of turbidity on the toxicity of the chemicals
was studied. Test water was from a farm pond with
"high" turbidity. Additional data are presented.
This paper deals with the toxicity thresholds of various
substances found in industrial wastes as determined by the
use of D. magna. Centrifuged Lake Erie water was used
as a diluent in the bioassay. Threshold concentration
was defined as the highest concentration which would
just fail to immobilize the animals under prolonged
(theoretically infinite) exposure.
The disposal of cannery wastes frequently involves the use
of chemicals for treatment purposes. Ferrous sulphate,
alum, and lime are used in chemical coagulation; sodium
carbonate for acidity control in biological filters; and
sodium nitrate in lagoons for odor control. Lye (sodium
hydroxide) peeling of certain fruits and vegetables is not
uncommon. These chemicals, in whole or part, are dis-
charged in most cases to a stream.
The concentrations listed permitted large mouth bass to
survive 2.5 to 3.5 days, and goldfish to survive indefinitely.
The purpose of this paper was to devise a toxicity index
for industrial wastes. Results are recorded as the toxic
concentration producing 50 percent inhibition (TCsfj)
of oxygen utilization as compared to controls. Five
toxigrams depicting the effect of the chemicals on BOD
were devised and each chemical classified.
The degree of tolerance for vector snails of bilharziasis to
various chemicals is somewhat dependent upon tempera-
ture. The temperature at which (K1 ) occurred was 27 C.
Reference
(Year)
Doudoroff, et al
(1956)
Anderson
(1948)
Clemens
and Sneed
(1959)
Wallen, et al
(1957)
Anderson
(1944)
Sanborn
(1945)
Hermann
(1959)
Gohar and
EI-Gindy
(1961)
^
^
•o
m
X
truncatus
-------
I
Ferrous sulfide
Ferrous sulfite
Fluoride
Fluoride
2'-fluoro-3',5'-
dinitrobenz-
anilide
Gambusia
affinis
Gambusia
affinis
Salmo
gairdnerii
Chlorella
pyrenoidosa
Salmo
gairdnerii
Carassius
auratus
BSA
BSA
BSA
O
m
S
O
£/)
1
O
s
H
C
3)
m
O
Tl
5
m
2
o
3'-fluoro-5-
nitrosalicyl-
anilide
3'-fluoro-3-
nitrosalicyl-
anilide
2'-fluoro-3-
nitrosalicyl-
anilide
4'-fluoro-3-
nitrosalicyl-
anilide
Salmo
gairdnerii
Carassius
auratus
Sea
lamprey
(larva)
Salmo
gairdneri
(fingerling)
Sea
lamprey
(larva)
Salmo
gairdneri
(fingerling)
Sea
lamprey
(larva)
Salmo
gairdneri
(fingerling)
BSA
BSA
BSA
BSA
BSA
10,000 (T2A)
350 (T2A)
(H) 250 (K21)
(H) 150(90% K21)
(H) 100(NTE21)
(S)253(K21)
(S) 113(K21)
(S)75(NTE21)
(O)
ja c d eg
£cd eg
ad
10 (K2)
10 (K2)
1.0 (K2)
10.0 (K 3 hr)
10.0 (K2)
0.5 (K)
(O)
1.0 K
1.0 (K)
See
Applegate,
et al
(1957-1958)
See
Applegate,
et al
(1957-1958)
See
Applegate,
et al
(1957-1958)
The effect of turbidity on the toxicity of the chemicals
was studied. Test water was from a farm pond with
"high" turbidity. Additional data are presented.
Comment same as above.
Aerated lake and well water were used as diluents.
Toxicity data are given as percentage killed at various
concentrations of fluoride in both hard (320 ppm)
and soft water (45 ppm). Threshold for 50% mortality
was 8.5 ppm F in 504 hr (21 days).
Fluoride caused growth inhibition in cultures of Chlorella
pyrenoidosa. This antimetabolite had its greatest effect
at concentrations greater than 10"3 M. No proportionality
could be established between the concentrations of fluoride
and the percentages of inhibition occurring at these
concentrations.
This paper deals with the relations between chemical struc-
tures of salicylanilides and benzanilides and their toxicity
to rainbow trout and goldfish. The chemical structure of
salicylanilides and benzanilides was related to toxicity and
selectivity to rainbow trout and goldfish. Salicylanilides
were more toxic than benzanilides to the fishes. The ortho
hydroxy substitution of salicylanilide accelerated biological
activity against fish. Meta nitro substitution on the sali-
cylanilides and benzanilides increased toxicity to fish.
Similar findings are reported for halogens and their relative
position(s) in the molecule.
Comment same as above.
This paper deals with the comparative toxicity of halonitro-
salicylanilides to sea lamprey and fingerling rainbow trout
as a function of substituent loci.
0.9 ppm killed 25%.
Comment same as above.
3.0 ppm killed 25%.
Comment same as above.
3.0 ppm killed 25%.
Wallen, et al
(1957)
Wallen, et al
(1957)
Herbert and
Shurben
(1964)
Smith and
Woodson
(1965)
Walker, et al
(1966)
O
X
Walker, et al
(1966)
Starkey and
Howell
(1966)
Starkey and
Howell
(1966)
Starkey and
Howell
(1966)
-------
o
I
m
O
f£ Chemical Organism
^ 4-fluoro-5- Sea
U nitrosahcyl- lamprey
2 anilide (larva)
X
C Fluosilicic Sewage
^ acid organisms
c/)
O
Tt
O
I
i
Q Formaldehyde Pygosteus
r~ (40% soln) pungitius
Formaldehyde Sewage
organisms
Formaldehyde Daphnia
j> magna
O\
Formaldehyde Sa/mo
gairdneri
Sa/mo
trutta
Satvelinus
fontinalis
Salvelinus
namaycush
Ictalurus
punctatus
Lepomis
macrochirus
Formalin Ictalurus
punctatus
Formalin Channel
(by volume) catfish
(fingerlings)
Formalin Tadpoles
Various fish
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study!1' Location'?) ppm'3'
BSA - 3.0 (K)
BOD - 2.6 (O)
BCF - (O)
BOD - 740 (TC50)
BSA - 100
1000 (T1A)
BSA - 168(T2A)
185 (T2A)
157 (T2A)
167 (T2A)
96 (T2A)
140 (T2A)
BSA - 126(K2A)
87 (T2A)
BSA - 87
(K 25 hr A)
FL III. 25-30 (K)
Experimental
Variables
Controlled
or Noted'4' Comments
See This paper deals with the comparative toxicity of halonitro-
Applegate, salicylanilides to sea lamprey and f ingerling rainbow trout
et al as a function of substituent loci.
(1957-1958)
— Various metal salts were studied in relation to how they
affected the BOD of both raw and treated sewage as well as
how they affected the processing of sewage in the treatment
plant. BOD was used as the parameter to measure the effect
of the chemical. The chemical concentration cited is the
ppm required to reduce the BOD values by 50%. This chem-
ical was tested in an unbuffered system.
a Concentrations of 0.1 to 0.4 percent (v/v) caused the fish to
show a negative reaction and appear to be irritated.
a The purpose of this paper was to devise a toxicity index for
industrial wastes. Results are recorded as the toxic concen-
tration producing 50 percent inhibition (TCsfj) of oxygen
utilization as compared to controls. Five toxigrams depict-
ing the effect of the chemicals on BOD were devised and
each chemical classified.
a c "Standard reference water" was described and used as well as
lake water. Varied results were obtained when evaluations
were made in various types of water.
a f Variance and the 95-percent confidence interval (C.I.) were
also determined.
a c f i The experiment was conducted at 77 C.
a Tap water was used. Considerable additional data are
presented.
a c After preliminary tests in aquaria, nine pond treatments were
made in six different ponds ranging in size from 0.03 to
0.5 acre. Formalin treatments caused oxygen depletion.
which, in turn, resulted in a fish kill. The ponds were treated
with formalin at 25 to 30 ppm. The authors recommend that
when fish are present, not more than 3O ppm should be used
to kill tadpoles in ponds.
Reference
(Year)
Starkey and
Howell
(1966)
Sheets
(1957)
Jones
(1947)
Hermann
(1959)
Dowden and
Bennett
(1965)
Willford
(1966)
Clemens and
Sneed
(1958)
Clemens and
Sneed
(1959)
Helms
(1967)
>
T)
m
D
^
-------
Formalin
I
vo
Formic
acid
Formic
acid
Furfural
Glutaric
O acid
m
_ Heptane
> Hexamethylene-
tetramine
Rana
catesbeiana
R. pipiens
Bufo sp
Notemigonus
crysoleucas
Cyprinus
carpio
Ictalurus
me/as
Large mouth
bass
Lepomis
macrochirus
L. cyanel/us
Tilapia sp
Sewage
organisms
Lepomis
macrochirus
Gambusia
affinis
Lepomis
macrochirus
Gambusia
affinis
Sewage
organisms
BSA
c
•33
m
w Hydrochloric
O acid
Tl
O
I
m
2
Carassius
carassius
BOD
BSA
BSA
BSA
BSA
BOD
BSA
80 (K),
53 (L1)
30 (K),
22 (L1)
50 (K),
45 (L3)
87 (L1),
67 (L2),
62 (L3)
70 (L3)
70+(L1),
49 (L2),
45 (L3)
100(L3)
100+ (L2),
80 (L3)
90 (L3)
100(L3)
550 (TC5o>
175 (T1A)
24 (T2A)
330 (T1 A)
4,924 (T2A)
(NTE)
Data are reported as LDso, although TLm or LCgrj might have
been more appropriate. The (K) represents minimum con-
centration for 100 percent kill.
Helms
(1967)
(0)
o
>
u,
a The purpose of this paper was to devise a toxicity index for
~ industrial wastes. Results are recorded as the toxic concen-
tration producing 50 percent inhibition (TCgg) of oxygen
utilization as compared to controls. Five toxigrams depict-
ing the effect of the chemicals on BOD were devised and
each chemical classified.
£C "Standard reference water" was described and used as well as
lake water. Varied results were obtained when evaluations
were made in various types of water.
£ c d e g The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
£C "Standard reference water" was described and used as well as
lake water. Varied results were obtained when evaluations
were made in various types of water.
a c d e g The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
£ The purpose of this paper was to devise a toxicity index for
industrial wastes. Results are recorded as the toxic concen-
tration producing 50 percent inhibition (TC5fj) of oxygen
utilization as compared to controls. Five toxigrams depict-
ing the effect of the chemicals on BOD were devised and
each chemical classified.
a This old, lengthy paper discusses toxicity of many chemicals,
possible mechanism of action of some, the effect of tem-
perature, effect of dissolved oxygen, the efficiency of the
goldfish as a test animal, compares this work with earlier
work, and lists an extensive bibliography.
In 0.0000313N solution, fish survived 1200 minutes.
Hermann
(1959)
Dowden and
Bennett
(1965)
Wallen, et al
(1957)
Dowden and
Bennett
(1965)
Wallen, et al
(1957)
Hermann
(1959)
Powers
(1918)
fc
•o
m
Z
D
X
-------
CHEMICALS
>
O
2
X
H
c
m
O
o
I
m
2
o
C
i/j
j>
— i
0
Chemical
Hydrochloric
acid
Hydrochloric
acid
Hydrochloric
acid
Hydrochloric
acid
Hydrochloric
acid
Hydrocyanic
acid
Hydrogen
cyanide
Hydrogen
cyanide
HCN
Hydrogen
cyanide
Organism
Daphnia
magna
Semotilus
atromaculatus
Lepomis
macrochirus
Gambusia
a f fin is
Lepomis
macrochirus
Lagodon
rhomboides
Lagodon
rhomboides
Fish
Lepomis
macrochirus
(juveniles)
Salmo
gairdnerii
Bioassay
or Field
Study*1'
BSA
BSA
BCFA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
Toxicity, Experimental
Active Variables
Field Ingredient, Controlled
Location*2' ppm*3) or Noted*4'
62 (O) a c
- 60 to 80 (CR) ae
(O) acef
282 (T2A) a c d e g
3.5(pH,T4A) acdei
0.069 (T1 A) a
0.069 (T1 A)
- 7.7 x 10'6 M ac
(K)
0.16 (T3A) acdfp
- 0.07 (T2A) a c d e f o
Comments
This paper deals with the toxicity thresholds of various sub-
stances found in industrial wates as determined by the use
of D. magna. Centrifuged Lake Erie water was used as a
diluent in the bioassay. Threshold concentration was de-
fined as the highest concentration which would just fail to
immobilize the animals under prolonged (theoretically
infinite) exposure.
Test water used was freshly aerated Detroit River water. A
typical water analysis is given. Toxicity is expressed as the
"critical range" (CR), which was defined as that concentra-
tion in ppm below which the 4 test fish lived for 24 hr and
above which all test fish died. Additional data are presented.
Test water was composed of distilled water with CP grade
chemicals and was aerated throughout the 96-hour exposure
period.
Toxicity was dependent upon pH. At pH 3.90 to 4.05,
10 percent of the fish died after 2 days. At pH 3.65,
50 percent survived after 3 days.
The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
A "control" was prepared by adding required chemicals to
distilled water, and this was constantly aerated. Data re-
ported are for larger fish, app 14.24 cm in length. Data
for smaller fish are also in the report.
Aerated sea water was used.
Experiments were conducted in aerated salt water.
Avoidance behavior of test fish to toxic chemicals is given.
Toxicitv is given as the lowest lethal concentration (molar).
Ratios of avoidance and lowest lethal concentration are
presented and discussed.
The solutions were prepared with NaCN, but the data given
are calculated as free HCN.
The concentration killing a half batch of fish in 2 days pro-
vides a reasonable estimate of the threshold concentration.
The toxicity of cyanide is related to the concentration of
molecular hydrogen cyanide, and not of the cyanide ion
(CN~). The lower the pH value the greater the proportion
of molecular HCN.
Reference
(Year)
Anderson
(1944)
Gillette, et al
(1952)
Cairns and
Scheier
(1955)
Wallen, et al
(1957)
Cairns and
Scheier
(1959)
Daugherty and
Garrett
(1951)
Garrett
(1957)
Ishio
(1965)
Doudoroff, et al
(1966)
Brown
(1968)
•^
^
•o
m
Z
O
X
>
-------
H ion
Hydrogen
sulphide
Hydrogen
sulfide
Hydrogen
sulfide
(undissociated)
Hydrogen
sulfide
c
3D
m
CO
O
Hydrogen
sulfide
O
Hydroquinone
Hydroquinone
Fish
Oncorhyncus
tshawytscha
Oncorhyncus
kisutch
Sal mo clarkii
clarkii
Bull/a
(Gastropoda)
Fish
Ictalurus
punctatus
BSA
BSA
BSA
BSA
FL
1.0 x 10-5 M
(K)
1.0 (K5)
1.2(K5)
1.0 (K5)
(O)
1.9 x ID'5 M
(K)
Texas
Ictalurus
punctatus
Lepomis
macrochirus
BSA
(O)
Hydroquinone
diacetate
Microcystis
aeruginosa
Daphnia
magna
Microcystis
aeruginosa
BSA
100 (K)
0.287 (K2)
100 (K)
a c Avoidance behavior of test fish to toxic chemicals is given. Ishio
~ Toxicity is given as the lowest lethal concentration (molar). (1965)
Ratios of avoidance and lowest lethal concentration are
presented and discussed.
£ d e This chemical is one of a number that may be found in Haydu, et al
Kraft mill waste effluents. Data are expressed as minimum (1952)
lethal concentration for 5 days.
— No quantitative data are reported. H2& was bubbled through Brown
sea water. When animals of this species were exposed to the (1964)
H2S solution more than half an hour, they were killed.
Animals removed after 15 minutes, then placed in fresh
aerated sea water, recovered.
ac Avoidance behavior of test fish to toxic chemicals is given. Ishio
~ Toxicity is given as the lowest lethal concentration (molar). (1965)
Ratios of avoidance and lowest lethal concentration are
presented and discussed.
a c g One hundred cat fish were placed in a pen in one lake and in Bonn and
less than 48 hours, all the test fish fry were dead. Tests Follis
showed that total hydrogen sulfide to be 0.96 ppm and a (1967)
pH of less than 6.0. This gave an unionized H2S concentra-
tion of at least 0.797 ppm, which was lethal to the catfish.
Based on the results of extensive tests, it was evident that the
production of unionized H2$ was seasonal, and often very
erratic.
a c The quantity of total sulf ides necessary to produce a TLm of Bonn and
the test catfish varied from 1.82 to approximately 7.0 ppm, Follis
depending upon the pH of the water. Most of the catfish (1967)
fry died in approximately 10 minutes at the concentration
range given above.
At a pH of 7.0 the TLm of unionized hydrogen sulfide was
found to be 1.0 ppm for fingerling channel catfish, 1.3 for
advanced fingerlings and 1.4 for adult catfish. The finger-
lings died in approximately 20 minutes while the TLm for
advanced fingerlings and adults was attained after about
45 minutes.
No TLm was reached for bluegill in the fingerling tests.
a_, etc The chemical was tested on a 5-day algae culture, 1 x 106 Fitzgerald, et al
to 2 x 106 cells/ml, 75ml total volume. Chu No. 10 medium (1952)
was used.
£ An attempt was made to correlate the biological action with Sollman
the chemical reactivity of selected chemical substances. (1949)
Results indicated a considerable correlation between the
aquarium fish toxicity and antiautocatalytic potency of the
chemicals in marked contrast to their toxicity on systemic
administration.
£, etc The chemical was tested on a 5-day algae culture, 1 x 106 Fitzgerald, et al
to 2 x 106 cells/ml, 75 ml total volume. Chu No. 10 medium (1952)
was used.
I
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CHEMICALS
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Chemical
Hydroqumone
monobenzyl
ether
Hydroquinone
monomethyl
ether
Hydroxyl
ion
Hydroxyl
ion
Hydroxyl-
amine-
HCI
Hydroxyl-
ammonium
benzoate
Hydroxyl-
ammonium
chloride
Bioassay
or Field
Organism Study (1)
Daphnia BSA
magna
Daphnia BSA
magna
Fish BSA
Moroco L
steindachnerii
Pungtungia
herzi
Acheilognathous
limbata
Cyprinus
carpio
Zaccho
platypus
Sarcocheilichthys
variegratus
Lebistes
reticulatus
Carassius
auratus (wild)
Carassius
auratus
Gnathepogon
gracilis
Pimephalus
promelas
Lepomis
macrochirus
Microcystis L
aeruginosa
Microcystis L
aeruginosa
Microcystis L
aeruginosa
Toxicity, Experimental
Active Variables
Field Ingredient, Controlled
Location*2) ppm(3) or Noted^)
2.5 (K2) a
200 (K2) a
1.0 x ID'5 M a c
(K)
1 1.23 to 9. 74 (O)
10.62 to 9. 16 (O)
10.12 to 9.03 (O)
10.13 to 8.62 (O)
10.12 to 8.62 (O)
9.63 to 8.71 (O)
9.38 to 8.44 (O)
10.38 to 8.24 (O)
10.25 to 7.38 (O)
10.38 to 7.40 (0)
9.56 to 9.05 (O)
9.62 to 8.76 (O)
50 (K) a, etc
100 (K) a, etc
- 100 (K) a, etc
Comments
An attempt was made to correlate the biological action with
the chemical reactivity of selected chemical substances.
Results indicated a considerable correlation between the
aquarium fish toxicity and antiautocatalytic potency of
the chemicals in marked contrast to their toxicity on
systemic administration.
Comment same as above.
Avoidance behavior of test fish to toxic chemicals is given.
Toxicity is given as the lowest lethal concentration (molar).
Ratios of avoidance and lowest lethal concentration are
presented and discussed.
The values given are the pH range avoided by the fish.
The chemical was tested on a 5-day algae culture, 1x10^
to 2 x 106 cells/ml, 75 ml total volume. Chu No. 10 medium
was used.
Comment same as above.
Comment same as above.
Reference
(Year)
Sollman
(1949)
Sollman
(1949)
Ishio
(1965)
Ishio
(1965)
Fitzgerald, et al
(1952)
Fitzgerald, et al
(1952)
Fitzgerald, et al
(1952)
^
TJ
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m
g
X
>
-------
Hydroxyl-
ammonium
phosphate
Hydroxyl-
ammonium
sulfate
2'-hydroxy-
phenazine-1-
carboxylic
acid
o-hydroxybenzoic
acid
Microcystis
aeruginosa
Microcystis
aeruginosa
Microcystis
aeruginosa
Anabaena
flos-aquae
Notemogonous
crysoleucas
Carassius
a u rat us
L
L
L
L
B£
p-hydroxybenzoic Carassius
acid auratus
m-hydroxybenzoic Carassius
acid auratus
p-hydroxyphenyl-
glycine
Daphnia
magna
BSA
BSA
BSA
100 (K)
100 (K)
0.1 (O)
1.0(0)
0.254 (K)
0.0230 (K)
0.0363 (K)
20 (K2)
a, etc Comment same as above.
a, etc Comment same as above.
;>
U>
8-hydroxy-
quinoline
Imidazoline
lodoacetic
acid
O
m
S
O
j£
w
2
a
5
x
c
3]
m
C/l
O
O
I
m
5
$
Microcystis L
aeruginosa
Microcystis L
aeruginosa
Cylindrospermum L
lichen/forme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorel/a
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
pa/ea (Np)
100 (K)
2.0 (K)
2.0 (O)
Concentrations noted are for complete inhibition of
M. aeruginosa and A. flos-aquae. No harmful effects to
N. crysoleucas were noted at the concentrations evaluated.
Goldfish weighed between 2 and 4 g.
Temperature was maintained at 27.0 ± 0.2 C.
Comment same as above.
a Comment same as above.
a An attempt was made to correlate the biological action with
the chemical reactivity of selected chemical substances.
Results indicated a considerable correlation between the
aquarium fish toxicity and antiautocatalytic potency of
the chemicals in marked contrast to their toxicity on
systemic administration.
a The chemical was tested on a 5-day algae culture, 1 x 10"
to 2 x 106 cells/ml, 75 ml total volume. Chu No. 10 medium
was used.
a, etc Comment same as above.
j3 Observations were made on the 3rd, 7th, 14th, and 21st days
to give the following (T = toxic, NT = nontoxic, PT = par-
tially toxic with number of days in parentheses. No number
indicates observation is for entire test period of 21 days):
Cl - PT (7)
Ma - T (3)
So - T (3)
Cv -NT
Gp-PT (14)
Np-NT
Fitzgerald, et al
(1952)
Fitzgerald, et al
(1952)
Toohey, et al
(1965)
Gersdorff
(1943)
Gersdorff
(1943)
Gersdorff
(1943)
So 11 man
(1949)
Fitzgerald, et al
(1952)
Fitzgerald, et al
(1952)
Palmer and
Maloney
(1955)
-------
CHEMICALS
>
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0
I
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5
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>
1/5
i
^
Chemical
4'-iodo-3,5-
dinitrobenz-
anilide
2'-iodo-3-
nitrosalicyl-
anilide
2'-iodo-3-
nitrosalicyl-
anilide
3'-iodo-3-
nitrosalicyl-
anilide
3'-iodo-3-
nitrosalicyl-
anilide
4'-iodi-nitro-
salicylanilide
Organism
Salmo
gairdnerii
Carassius
auratus
Sea
lamprey
(larva)
Salmo
gairdneri
(fingerling)
Salmo
gairdnerii
Carassius
auratus
Salmo
gairdnerii
Carassius
auratus
Sea
lamprey
(larva)
Salmo
gairdneri
(fingerling)
Ictalurus
nebulosus
Toxicity,
Bioassay Active
or Field Field Ingredient,
StudyC" Location<2) ppm(3)
BSA - (O)
(0)
BSA - 1.0 (K)
(O)
BSA - 10.0 (K 3 hr)
1.0 (K23hr)
BSA - 1.0(K3hr)
1.0 (K2)
10.0 (K3hr)
BSA - 0.3 (K)
(0)
BSA - 0.005 (K)
0.0025 (SB)
at 47 and
71 F
Experimental
Variables
Controlled
or NotedW) Comments
a This paper deals with the relations between chemical struc-
~ tures of salicylanilides and benzanilides and their toxicity
to rainbow trout and goldfish. The chemical structure of
salicylanilides and benzanilides was related to toxicity and
selectivity to rainbow trout and goldfish. Salicylanilides
were more toxic than benzanilides to the fishes. The ortho
hydroxy substitution of salicylanilide accelerated biological
activity against fish. Meta nitro substitution on the salicyl-
anilides and benzanilides increased toxicity to fish. Similar
findings are reported for halogens and their relative posi-
tion(s) in the molecule. Precipitation occurred at 10 ppm.
At 10 ppm the chemical was not toxic to trout or goldfish.
See This paper deals with the comparative toxicity of halonitro-
Applegate, salicylanilides to sea lamprey and fingerling rainbow trout
et al as a function of substituent loci.
(1957-1958)
a This paper deals with the relations between chemical struc-
~ tures of salicylanilides and benzanilides and their toxicity
to rainbow trout and goldfish. The chemical structure of
salicylanilides and benzanilides was related to toxicity and
selectivity to rainbow trout and goldfish. Salicylanilides
were more toxic than benzanilides to the fishes. The ortho
hydroxy substitution of salicylanilide accelerated biological
activity against fish. Meta nitro substitution on the salicyl-
anilides and benzanilides increased toxicity to fish. Similar
findings are reported for halogens and their relative posi-
tion (s) in the molecule.
a Comment same as above.
See This paper deals with the comparative toxicity of halonitro-
Applegate, salicylanilides to sea lamprey and fingerling rainbow trout
et al as a function of substituent loci.
(1957-1958)
a c g The chemical was dissolved in dimethyl sulfoxide for test-
ting. Non-aerated, turbid and non-turbid test waters at
47 and 71 F were used. Lodging of the fish in sediment
increased survival.
Reference
(Year)
Walker, et al
(1966)
Starkey and
Howell
(1966)
Walker, et al
(1966)
Walker, et al
(1966)
Starkey and
Howell
(1966)
Loeb and
Starkey
(1966)
•o
m
Z
O
-------
4'-iodo-3-
nitrosalicyl-
anilide
4'-iodo-3-
nitrosalicyl-
anilide
o-iodophenol
S p-iodophenol
O
O
S Iron
C
m
O
-n
O
m
2
Sea
lamprey
(larva)
Salmo
gairdneri
(fingerling)
Salmo
gairdnerii
Carassius
auratus
BSA
4'-iodo-5-
nitrosalicyl-
anilide
4'-iodo-5-
nitrosalicyl-
anilide
m-iodophenol
Salmo
gairdnerii
Sea
lamprey
(larva)
Salmo
gairdneri
(fingerling)
Carassius
auratus
Carassius
auratus
Carassius
auratus
Daphnia
magna
BSA
BSA
BSA
BSA
BSA
BSA
0.3 (K)
(O)
1.0(K3hr)
1.0 (K3hr)
1.0 (K2)
10.0(K3hr)
0.5 (K)
(O)
51.7 to 155.0
(K 8 hr)
38.8 (O)
10.3 (O)
45.8 to 91.6
(K 8 hr)
36.6 (O)
26.2 (O)
12.5 to 100
(K8hr)
11.8 (O)
10.0(O)
7.5 (O)
100 (K)
See This paper deals with the comparative toxicity of halonitro- Star key and
Applegate, salicylanilides to sea lamprey and fingerling rainbow trout Howell
et al as a function of substituent loci. (1966)
(1957-1958) 0.7 ppm killed 25%.
£ This paper deals with the relations between chemical struc- Walker, et al
tures of salicylanilides and benzanilides and their toxicity (1966)
to rainbow trout and goldfish. The chemical structure of
salicylanilides and benzanilides was related to toxicity and
selectivity to rainbow trout and goldfish. Salicylanilides
were more toxic than benzanilides to the fishes. The ortho
hydroxy substitution of salicylanilide accelerated biological
activity against fish. Meta nitro substitution on the salicyl-
anilides and benzanilides increased toxicity to fish. Similar
findings are reported for halogens and their relative posi-
tion(s) in the molecule.
a Comment same as above. Walker, et al
(1966)
See This paper deals with the comparative toxicity of halonitro- Starkey and
Applegate, salicylanilides to sea lamprey and fingerling rainbow trout Howell
et al as a function of substituent loci. (1966)
(1957-1958) 1.0 ppm killed 25%.
Temperature in test containers was maintained at 27 ± 0.2 C. Gersdorff and
Goldfish tested weighed between 2 and 4 g. Smith
m-iodophenol, 38.8 ppm, killed 75% of the fish in 8 hr; (1940)
10.3 ppm killed 33% in 8 hr.
Comment same as above except that o-iodophenol, 36.6 Gersdorff and
ppm, killed 83% of the fish in 8 hr; 26.2 ppm killed 8% Smith
in 8 hr. (1940)
Comment same as above except that p-iodophenol, 11.8 Gersdorff and
ppm, killed 92% of the fish in 8 hr; 10.0 ppm killed 77% Smith
in 8 hr; and 7.5 ppm killed 46% in 8 hr. (1940)
It is assumed in this experiment that the cations considered Shaw and
are toxic because they combine with an essential sulfhydryl Grushkin
group attached to a key enzyme. This treatment indicates (1967)
that the metals which form the most insoluble sulfides are
the most toxic. The log of the concentration of the metal
ion is plotted against the log of the solubility product con-
stant of the metal sulfide — a treatment that does not lend
itself to tabulation. The cation toxicity cited is only an
approximate concentration interpolated from a graph.
Time of death was not specified.
m
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CHEMICALS
>
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Chemical
Iso-amyl
alcohol
Isoamyl
alcohols.
mixed
primary
Isobornyl
thiocyano-
acetate
Isobornyl
thiocyano-
acetate
Toxicity,
Bioassay Active
or Field Field Ingredient,
Organism Study (D Location^) ppm(3)
Daphnia BSA - 881 (O)
magna
Semotilus BSA — 400 to 600
atromaculatus (CR)
Green FL III. (O)
sunfish
Large mouth
bass
Black
bullhead
Golden
shiner
Mosquito
fish
Tadpoles
Crayfish
Bluegill
Channel
catfish
Redear
sunfish
White
crappie
BSA
Green 0.6 (O)
sunfish
Rainbow <0.7 (0)
trout
Golden 1.5(0)
shiner
Channel 1.5 (O)
catfish
Black >1.5(0)
bullhead
Bluegill 0.4 (O)
Experimental
Variables
Controlled Reference
or Noted(4) Comments (Year)
a c This paper deals with the toxicity thresholds of various sub- Anderson
stances found in industrial wastes as determined by the use (1944)
of D. magna. Centrifuged Lake Erie water was used as a
diluent in the bioassay. Threshold concentration was de-
fined as the highest concentration which would just fail to
immobilize the animals under prolonged (theoretically
infinite) exposure.
a e Test water used was freshly aerated Detroit River water. A Gillette, et al
~~ typical water analysis is given. Toxicity is expressed as the (1952)
"critical range" (CR), which was defined as that concen-
tration in ppm below which the 4 test fish lived for 24 hr
and above which all test fish died. Additional data are
presented.
a Ponds were treated with concentrations of 0.7, 0.8, and Lewis
1.5 ppm of the chemical. The ponds were drained or (1968)
poisoned after the removal of isobornyl thiocyanoacetate-
affected fish were removed. This was done to determine
the numbers of each species that had survived.
Water temperature in the ponds ranged from 50 to 87 F.
Pond sizes ranged from 0.1 to 455 acres.
Results were quite similar to the results obtained in bio-
assay studies.
Centrarchids were selectively killed in the presence of
ictalurids and cyprinids.
a Twenty liter-glass aquaria were employed for the experi- Lewis
~~ ments. Temperature was maintained at 20 to 23 C. (1968)
Results are recorded as 24-hr lethal minimum dose of the
chemical.
24-hr lethal minimum dose at 20 to 23 C.
24-hr lethal minimum dose at 1 1 C.
24-hr lethal minimum dose at 20 to 23 C.
24-hr lethal minimum dose at 20 to 23 C.
24-hr lethal minimum dose at 20 to 23 C.
24-hr lethal minimum dose at 2O to 23 C.
-0
•o
m
X
^
-------
Isobutyl
alcohol
Carassius
carassius
BSA
(O)
2
5
Isoprene
p-isopropoxy
diphenyl
p-isopropoxy
diphenylamine
^\ Isopropyl
^j alcohol
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Daphnia
magna
Daphnia
magna
Semotilus
atromaculatus
BSA
BSA
75 (T4A)
39 (T4A)
180IT4A)
140 (T4A)
5.7 (K2)
a cd e f
BSA
BSA
O
m
2
O
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2
X
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m
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1-isopropyl-2-
(8,11-hepta-
decadienyl)-
4,4-dimethyl-
2-imidazoline
1-isopropyl-
2-(S-hepta-
decenyl)-
4,4-dimethyl-
2-imidazoline
1-isopropyl-
2-nonyl-4,
4-dimethyl-
2-imidazoline
1-isopropyl-
2-undecyl-
4,4-dimethyl-
2-imidazoline
Microcystis
aeruginosa
Microcystis
aeruginosa
Microcystis
aeruginosa
Microcystis
aeruginosa
5.7 (K2)
900 to 1,100
(CR)
2.0 (K)
1.0 (K)
2.0
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O
£ Chemical
11
> Lactic
O acid
2
X
H
C
31
m
M
O Lactonitrile
O
I
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5 Lactonitrile
0
>
tn Lactonitrile
>
J Lactonitrile
D
Laurylisoquino-
linium
bromide
Bioassay
or Field
Organism Study 'D
Daphnia BSA
magna
Lagadon BSA
rhomboides
Lagadon BSA
rhomeboides
Lepomis BSA
auritus & CF
/_epo/T7/s
macrochirus
Pomoxis
annularis
Pimephales BSA
prome/as
Lepomis
macrochirus
Lebistes
reticulatus
Pimephalus
promelas
Cylindrospermum L
licheniforme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Toxicity, Experimental
Active Variables
Field Ingredient, Controlled
Location'2) ppm'3) or NotedW)
243 (O) a c
0.215 (T1A) a
0.215 (T1A)
0.06-0.1 a
(100% KCF)
0.03-0.1
(100% KS)
0.055-0.07
(100% KF)
0.075
(100% KS)
0.065-0.07
(100%KS)
(S) 0.90 (T4A) c d e f
(S) 0.90 (T4A)
(S) 1.37 (T4A)
(H) 0.90 (T4A)
2.0 (0) a
Comments
This paper deals with the toxicity thresholds of various sub-
stances found in industrial wastes as determined by the use
of D. magna. Centrif uged Lake Erie water was used as a
diluent in the bioassay. Threshold concentration was de-
fined as the highest concentration which would just fail to
immobilize the animals under prolonged (theoretically
infinite) exposure.
Aerated seawater was used.
Experiments were conducted in aerated salt water.
Additional data are presented for less than 24 hr.
(H) Value for hard water.
(S) Value for soft water.
The chemical did not change the flavor of the cooked bluegill.
Observations were made on the 3rd, 7th, 14th, and 21st days
to give the following (T = toxic, NT = nontoxic, PT = par-
tially toxic with number of days in parentheses. No number
indicates observation is for entire test period of 21 day's):
Cl -T(3)PT(7)
Ma -PT (14)
So - T (3)
Cv - PT (7)
Gp - PT (7)
Np-PT (7)
Reference
(Year)
Anderson
(1944)
Daugherty and
Garrett
(1951)
Garrett
(1957)
Renn
(1955)
Henderson, et al
(1960)
Palmer and
Maloney
(1955)
>
3
V
m
Z
X
>
-------
Lead
Lead
Lead
acetate
Lead
chloride
Lead
J> chloride
Lead
chloride
Lead
nitrate
Z Lead
° nitrate
c
30
m
CO
O
o
m
2
Lead
nitrate
Lead
nitrate
Lebistes
reticulatus
Bufo
valliceps
(tadpoles)
Daphnia
magna
Gasterosteus
aculeatus
Pimephales
promelas
Lepomis
macrochirus
Daphnia
magna
Pimephales
promelas
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Gasterosteus
aculeatus
Gasterosteus
aculeatus
Phoxinus
phoxinus
Gambusia
affinis
Lebistes
reticulatus
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSCH
1.0 (K)
100.0 (K)
10.0 (K)
0.1 (O)
(S) 7.48 (T4A)
1.25 (S)
(H) >75 (T4A)
(S) 2.4 (T4A)
(S) 5.58 (T4A)
(H) 482.0 (T4A)
(S) 23.8 (T4A)
(H) 442.0 (T4A)
(S) 31.5 (T4A)
(S) 20.6 (T4A)
0.3 (TL4-3/4A)
cdef
acdf
cdef
(O)
240 (T2A)
2.0 (27% K90)
a cd e g
a cd e
It is assumed in this experiment that the cations considered
are toxic because they combine with an essential sulfhydryl
group attached to a key enzyme. This treatment indicates
that the metals which form the most insoluble sulfides are
the most toxic. The log of the concentration of the metal
ion is plotted against the log of the solubility product con-
stant of the metal sulfide — a treatment that does not lend
itself to tabulation. The cation toxicity cited is only an
approximate concentration interpolated from a graph.
Time of death was not specified.
This is a discussion of a bioassay method using stickleback
fish and spectrophotometric determinations of the chem-
icals evaluated. The number listed is said to be the "toxic
limit" for the fish.
(S) Soft water.
Values are expressed as mg/l of lead.
Lake Erie water was used as diluent. Toxicity given as
threshold concentration producing immobilization for
exposure periods of 64 hr.
Both hard (H) and soft (S) water were used.
(S) Soft water.
(H) Hard water.
Values are expressed as mg/l of metal.
Shaw and
Grushkin
(1967)
Death of the fish resulted from an interaction between the
metallic ion and the mucus secreted by the gills. Coagu-
lated mucus formed on the gill membranes and impaired
respiration to such a degree that the fish asphyxiated.
The addition of 50 mg/l of calcium chloride to the tank
protected against the toxic effect of this metal salt.
Tap water was used to make up the solutions. The animals
were attracted to a solution 0.04N - a positive reaction, they
tended to swim into it. They tended to show avoidance
reactions at concentrations of 0.004N down to 0.00002N.
The minnow detected and avoided a 0.000004N solution.
P. phoxinus minnows were much more sensitive to this
chemical than G. aculeatus.
The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
Sublethal effects found were retarded growth, increased
mortality, and delayed sexual maturity.
Hawksley
(1967)
Pickering and
Henderson
(1965)
Anderson
(1948)
Tarzwell and
Henderson
(1960)
Pickering and
Henderson
(1965)
m
o
X
Jones
(1938)
Jones
(1948)
Wallen, et al
(1957)
Crandall and
Goodnight
(1962)
-------
o
I
m
3
o
p Chemical Organism
5 Lead Tubificid
O nitrate worms
S
X
H
C Lead Gambusia
m oxide affinis
0
~" Lead Salmo
^ salts gairdnerii
m
S
O
r
Lithium Carassius
chloride carassius
•j>
i
OO
o
Lithium Daphnia
chloride magna
D-lysergic Notemigonis
acid crysoleucas
Cyprinus
carp/o
Csrasm/s
aurafus
Rhinichthys
atratulus
Semotilus
atromaculatus
Notropis
comutus
Lepomis
gibbosus
Lebistes
reticulatus
Perca
flavescens
Catostomus
commersoni
Ameiurus
nabulosus
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study'1) Location (2) ppm(3) or Noted'4) Comments
BSA — 49.0 (T1 A) ac Knop's solution was used. TLm levels for various pHs were
27.5 (T1 A) determined for the tubificids and were found to be 5.8 to
9.7. Lead nitrate was more toxic at pH extremes of 6.5
and 8.5 than at 7.5.
BSA — 56,000 (T2A) acdeg The effect of turbidity on the toxicity on the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
BSA — (O) ae This is a study of the effect of varying dissolved oxygen con-
centrations on the toxicity of selected chemicals.
The toxicity of heavy metals, ammonia, and monohydric
phenols increased as the dissolved oxygen in water was
reduced. The most obvious reaction of fish to lowered
oxygen content is to increase the volume of water passed
over the gills, and this may increase the amount of poison
reaching the surface of the gill epithelium.
The concentration of the chemical in the water was not
specified.
BSA — (O) a This old, lengthy paper discusses toxicity of many chemicals,
~~ possible mechanism of action of some, the effect of tem-
perature, effect of dissolved oxygen, the efficiency of the
goldfish as a test animal, compares this work with earlier
work, and lists an extensive bibliography.
In 0.1 66N solution, fish survived 234 minutes.
BSA — <7.2 (S) a Lake Erie water was used as diluent. Toxicity given as
~ threshold concentration producing immobilization for
exposure periods of 64 hr.
BSA — (0) a Lysergic acid and 45 of its derivatives were tested on a wide
variety of aquatic animals. Various concentrations of the
chemicals were used, from 0.5 to as high as 12.0 ppm. In
nearly all cases, the chemical caused involuntary surfacing
of the fish with no mortality at the above concentrations.
Reference
(Year)
Whitley
(1968)
Wallen, et al
(1957)
Lloyd
(1961)
Powers
(1918)
Anderson
(1948)
Loeb, et al
(1965)
TJ
•o
m
Z
O
-------
Magnesium
chloride
Magnesium
chloride
Magnesium
chloride
Magnesium
chloride
oo
^- Magnesium
nitrate
Magnesium
nitrate
O
m
? Magnesium
j nitrate
Magnesium
sulfate
C Magnesium
•{> sulfate
to
O Magnesium
j£ sulfate
§
O
Sal mo
trutta
Cottus
cognatus
Boleosoma
nigrum
Rana
pipiens
Carassius
carassius
Daphnia
magna
Gambusia
affinis
Daphnia
magna
Carassius
carassius
Casterosteus
aculeatus
Biomorpholaria
a. alexandrina
Gambusia
affinis
Biomorpholaria
a. alexandrina
Bulinus
truncatus
Daphnia
magna
Lepomis
macrochirus
Lymnaea sp
(eggs)
BSA
(O)
BSA
BSA
BSA
BSA
740 (O)
17,750 (T2A)
3,391 (T1A)
3,489 (T4A)
(O)
BSA
BSA
BSA
BSA
BSA
300 (K10)
(O)
15,500 (T2A)
(0)
4000 (K1A)
3,803 (T4A)
19,000 (T1A)
10,530 (T1A)
a This old, lengthy paper discusses toxicity of many chemicals, Powers
~~ possible mechanism of action of some, the effect of tem- (1918)
perature, effect of dissolved oxygen, the efficiency of the
goldfish as a test animal, compares this work with earlier
work, and lists an extensive bibliography.
In 0.313N solution, fish survived 88 minutes.
a Lake Erie water was used as diluent. Toxicity given as Anderson
~~ threshold concentration producing immobilization for (1948)
exposure periods of 64 hr.
a c d e g The effect of turbidity on the toxicity of the chemicals was Wallen, et al
studied. Test water was from a farm pond with "high" (1957)
turbidity. Additional data are presented.
a c "Standard reference water" was described and used as well Dowden and
~~ as lake water. Varied results were obtained when evalu- Bennett
ations were made in various types of water. (1965)
a This old, lengthy paper discusses toxicity of many chemi- Powers
~~ cals, possible mechanism of action of some, the effect of (1918)
temperature, effect of dissolved oxygen, the efficiency of
the goldfish as a test animal, compares this work with
earlier work, and lists an extensive bibliography.
In 0.229N solution, fish survived 107 minutes.
— Solutions were made up in tap water 3.0 to 5.0 cm stickle- Jones
back fish were used as experimental animals. This paper (1939)
points out that there is a marked relationship between the
toxicity of the metals and their solution pressures. Those
with low solution pressures were the most toxic,
a The degree of tolerance for vector snails of biharziasis Gohar and
chemicals is somewhat dependent upon temperature. EI-Gindy
B. a. alexandrina tolerated a 24-hour exposure to 6200 ppm (1961)
at 20 C.
a c d e g The effect of turbidity on the toxicity of the chemicals Wallen, et al
was studied. Test water was from a farm pond with "high" (1957)
turbidity. Additional data are presented.
a The degree of tolerance for vector snails of biharziasis Gohar and
chemicals is somewhat dependent upon temperature. EI-Gindy
The temperature at which (K1A) occurred was 26 C for (1961)
Bulinus. The tolerance for Biomorpholaria was 6200 ppm.
£C "Standard reference water" was described and used as well Dowden and
as lake water. Varied results were obtained when evalu- Bennett
ations were made in various types of water. (1965)
*
•o
m
Z
O
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-------
CHEMICALS
2
O
£
X
c
3>
m
O
-n
O
m
—
j>
C)
>
0
j
Chemical
Malachite
green
Malachite
green
Malachite
green
(oxalate salt)
Malachite
green
Malachite
green
Malachite
green
Malachite
green
Maleic
anhydride
Maleic
hydrazide
Organism
Ictalurus
punctatus
Microcystis
aeruginosa
Channel
catfish
(fingerlings)
Micropterus
salmoides
(fry)
Lepomis
macrochirus
(fry)
Salmo
gairdnerii
Salmo
trutta
Salvelinus
f on final is
Salvelinus
namaycush
Ictalurus
punctatus
Lepomis
macrochirus
Salmo
gairdnerii
Rasbora
heteromorpha
Salmo
gairdnerii
Rasbora
heteromorpha
Gambusia
affinis
Salmo
gairdnerii
Toxicity,
Bioassay Active
or Field Field Ingredient,
StudyCl) Location<2) ppm(3)
BSA - 0.19 (K2)
0.14 (T2A)
L - 100 (K)
BSA - 0.14 (K1A)
BSA - 0.025 (SB3)
0.001 (SB3)
BSA - 0.39 (T2A)
0.34 (T2A)
0.26 (T2A)
0.40 (T2A)
0.20 (T2A)
0.11 (T2A)
BCFA - 0.04
(threshold)
BSA - (0)
(0)
BSA - 240 (T2A)
BSA - 85(T1A)
56 (T2A)
Experimental
Variables
Controlled
or NotedW) Comments
a c f i The experiment was conducted at 77 C.
a, etc The chemical was tested on a 5-day algae culture, 1x10°
~~ to 2 x 106 cells/ml, 75 ml total volume. Chu No. 10
medium was used.
a Tap water was used. Considerable additional data are
~ presented.
a c d e f p At least 90 percent of the fry survived for a period of
72 hours at the concentration listed.
f Variance and the 95-percent confidence interval (C.I.) were
also determined.
a d e Aerated hard water was used. Threshold concentrations
were examined by 4 methods.
1. Long term — survival related to concentration.
2. Short term — percentage kill in narrow range of
concentrations.
3. Comparison of survival times.
4. Extrapolation of short-term results by plotting
velocity of death against log of concentration.
f This report derives a mathematical equation for determining
a threshold concentration for a toxicant. A concentration
of 0.048 ppm of the compound will kill 50% of trout in
about 18 days. 0.122 ppm was lethal to 50% in two and
a half days.
a c d e g The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
a e Most of the weed-killer formulations in this study consisted
of more than one substance, i.e., oils, emulsif iers, stabilizers.
and other adjuvants.
Reference
(Year)
Clemens and
Sneed
(1958)
Fitzgerald, et al
(1952)
Clemens and
Sneed
(1959)
Jones
(1965)
Willford
(1966)
Abram
(1967)
Wallen, et al
(1957)
Alabaster
(1956)
m
z
o
X
>
-------
Malonic
acid
Manganese
OJ
Manganese
chloride
Manganese
chloride
Manganese
disodium
versenate
Manganese
nitrate
Lepomis
macrochirus
Lebistes
reticulatus
Bufo
valliceps
(tadpoles)
Daphnia
magna
Daphnia
magna
Limnaea
palustris
(eggs)
Channel
catfish
(fingerlings)
Gasterosteus
acu/eatus
BSA
BSA
BSA
BSA
BSA
CHEMICALS
z
o
2
X
~i
•33
m
CO
O
-n
O
^
Mercuric
acetate
Mercuric
chloride
Mercuric
chloride
Mercuric
chloride
Cylindrospermum
lichen/forme (Cl)
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
pa/ea (Np)
Gasterosteus
acu/eatus
Balanus
balanoides
Pygosteus
pungitius
150 (T1A)
10,000 (K)
10,000 (K)
1,000 (K)
50(0)
5x TO'5 M
(K1)
>500 (K1A)
40(K10)
2.0 (O)
BSA
BSA
BCF
0.008 (K10)
1.0(0)
(O)
"Standard reference water" was described and used as well Dowden and
as lake water. Varied results were obtained when evalu- Bennett
ations were made in various types of water. (1965)
It is assumed in this experiment that the cations considered Shaw and
are toxic because they combine with an essential sulfhydryl Grushkin
group attached to a key enzyme. This treatment indicates (1967)
that the metals which form the most insoluble sulfides are
the most toxic. The log of the concentration of the metal
ion is plotted against the log of the solubility product con-
stant of the metal sulf ide — a treatment that does not lend
itself to tabulation. The cation toxicity cited is only an
approximate concentration interpolated from a graph.
Time of death was not specified.
Lake Erie water was used as diluent. Toxicity given as Anderson
threshold concentration producing immobilization for (1948)
exposure periods of 64 hr.
Toxicity is given in molar concentrations for maximum direct Morrill
mortality (kill) in 4 hours. (1963)
Tap water was used. Considerable additional data are Clemens and
presented. Sneed
(1959)
Solutions were made up in tap water. 3.0 to 5.0 cm stickle- Jones
back fish were used as experimental animals. This paper (1939)
points out that there is a marked relationship between the
toxicity of the metals and their solution pressures. Those
with low solution pressures were the most toxic.
Observations were made on the 3rd, 7th, 14th, and 21st days Palmer and
to give the following (T = toxic, NT = nontoxic, PT = par- Maloney
tially toxic with number of days in parentheses. No number (1955)
indicates observation is for entire test period of 21 days):
Cl -T (3)
Ma-T (3)
So - T (3)
Cv - T (3)
Gp-T(3)
Np-T(3)
Solutions were made up in tap water. 3.0 to 5.0 cm stickle- Jones
back fish were used as experimental animals. This paper (1939)
points out that there is a marked relationship between the
toxicity of the metals and their solution pressures. Those
with low solution pressures were the most toxic.
The concentration listed was lethal to 90% of adult barnacles Clarke
in 2 days. (1947)
The fish were immersed in solutions of 0.003, 0.002, 0.0003, Jones
and 0.00004N mercuric chloride. Survival times in these (1947)
solutions were respectively, 14, 22, 31, and 100 minutes.
I
m
O
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-------
CHEMICALS
>
2
0
Z
3
c
3}
m
w
O
Tl
O
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m
S
o
>
c
>
2
Chemical
Mercuric
chloride
Mercuric
chloride
Mercuric
chloride
Mercuric
chloride
Mercuric
iodide
Mercury
Mercury
Mercury
compounds
Organism
Daphnia
magna
BOD
Sewage
organisms
Sewage
organisms
Anemia
salina
Acartia
clausi
Elminius
modestus
Lebistes
reticulatus
Bufo
valliceps
(tadpoles)
Daphnia
magna
Maia
squinado
Esox
leucius
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study*1) Location(2) ppm(3)
BSA - <0.006 (O)
L - 1.0 (O)
BOD - (O)
BOD - 0.61 (TC50)
BSA - 31.0IO)
1.7 (0)
2.6 (O)
BSA - 0.01 (K)
0.1 (K)
0.1 (K)
BSA - 10 (SB 28)
FL Denmark (O)
Experimental
Variables
Controlled
or Noted**) Comments
a Lake Erie water was used as diluent. Toxicity given as
threshold concentration producing immobilization for
exposure periods of 64 hr.
j "Toxicity is expressed as 80 percent reduction in oxygen
utilization.
— There was a slow increase in toxicity of mercury from 0.02
to 0.2 ppm. Beyond this there was a sharp rise in the
toxicity until at approximately 2.0 ppm there was com-
plete bacteriostasis or an absence of BOD at this
concentration.
a The purpose of this paper was to devise a toxicity index
~ for industrial wastes. Results are recorded as the toxic con-
centration producing 50 percent inhibition (TCsfj) of oxy-
gen utilization as compared to controls. Five toxigrams
depicting the effect of the chemicals on BOD were devised
and each chemical classified.
a c All tests were conducted in seawater.
Toxicity values reported are relative to that of mercuric
chloride expressed as unity.
Mechanism of action is discussed, as well as synergistic action
of two poisons administered simultaneously.
ace It is assumed in this experiment that the cations considered
are toxic because they combine with an essential sulfhydryl
group attached to a key enzyme. This treatment indicates
that the metals which form the most insoluble sulf ides are
the most toxic. The log of the concentration of the metal
ion is plotted against the log of the solubility product con-
stant of the metal sulfide — a treatment that does not lend
itself to tabulation. The cation toxicity cited is only an
approximate concentration interpolated from a graph.
Time of death was not specified.
— Results showed that the highest mercury concentrations oc-
curred in the gills and internal organs. Concentrations
were minute in the blood and there was none in the urine.
— Mercury may become a water contaminant from seed dress-
ings in agriculture, fungicides in pulp and paper mills, and
from the chlorine alkali industry. Pike was chosen as an
indicator organism, and many analyses were given for mer-
cury content of pike. In water with a mercury content of
0.07 ppb, pike were found with a concentration of 3000
times that concentration. Analyses were reported of pike
containing from 60 to 2500 ppb. One value as high as
8000 ppb was reported.
There are many organisms capable of accumulating mercury
from water.
Reference
(Year)
Anderson
(1948)
Ingols
(1955)
Ingols
(1954)
Hermann
(1959)
Corner and
Sparrow
(1956)
Shaw and
Grushkin
(1967)
Corner
(1959)
Johnels, et al
(1967)
>
^
TJ
m
Z
0
>
-------
Methanol
*>
oo
2'-methoxy-5'-
chloro-3-nitro-
salicylanilide
Methyl
alcohol
Methyl
alcohol
Methyl
alcohol
Methylamine
2 HCI
m
§
O p-methylamino-
> phenol
W
O
§
X 2'-methyl-3'-
^ chloro-3-nitro-
3) salicylanilide
m
W
O
•n
O
m
2
Sewage
organisms
Sea
lamprey
(larva)
Salmo
gairdneri
(fingerling)
Carassius
carassius
BOD
BSA
BSA
(NTE)
0.7 (LD100)
1.0(LD25)
(O)
See
Applegate,
et al
(1957-1958)
Daphnia
magna
BSA
32,000 (O)
Semotilus
atromaculatus
Microcystis
aeruginosa
Daphnia
magna
Sea
lamprey
(larva)
Salmo
gairdneri
(fingerling)
BSA
BSA
8,000 to
17,000 (CR)
100 (K)
0.5 (K2)
BSA
0.7 (LD100)
1.0(LD25)
See
Applegate,
et al
(1957-1958)
The purpose of this paper was to devise a toxicity index for Hermann
industrial wastes. Results are recorded as the toxic concen- (1959)
tration producing 50 percent inhibition (TCsfj) of oxygen
utilization as compared to controls. Five toxigrams depict-
ing the effect of the chemicals on BOD were devised and
each chemical classified.
This paper deals with the comparative toxicity of halonitro- Starkey and
salicylanilides to sea lamprey and fingerling rainbow trout Howell
as a function of substituent loci. (1966)
This old, lengthy paper discusses toxicity of many chemicals. Powers
possible mechanism of action of some, the effect of tern- (1918)
perature, effect of dissolved oxygen, the efficiency of the
goldfish as a test animal, compares this work with earlier
work, and lists an extensive bibliography.
In a concentration of 25 cc per liter, fish survived 206
minutes.
This paper deals with the toxicity thresholds of various sub- Anderson
stances found in industrial wastes as determined by the use (1944)
of D. magna. Centrifuged Lake Erie water was used as a
diluent in the bioassay. Threshold concentration was de-
fined as the highest concentration which would just fail to
immobilize the animals under prolonged (theoretically
infinite) exposure.
Test water used was freshly aerated Detroit River water. A Gillette, et al
typical water analysis is given. Toxicity is expressed as the (1952)
"critical range" (CR), which was defined as that concen-
tration in ppm below which the 4 test fish lived for 24 hr
and above which all test fish died. Additional data are
presented.
The chemical was tested on a 5-day algae culture, 1 x 106 to Fitzgerald, et al
2 x 106 cells/ml, 75 ml total volume. Chu No. 10 medium (1952)
was used.
An attempt was made to correlate the biological action with Sollman
the chemical reactivity of selected chemical substances. (1949)
Results indicated a considerable correlation between the
aquarium fish toxicity and antiautocatalytic potency of
the chemicals in marked contrast to their toxicity on
systemic administration.
This paper deals with the comparative toxicity of halonitro- Starkey and
salicylanilides to sea lamprey and fingerling rainbow trout Howell
as a function of substituent loci. (1966)
m
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CHEMICALS
>
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Chemical
2'-methyl-4'-
chloro-3-mtro-
5alicylanilide
2'-methyl-5'-
chloro-3-nitro-
sahcylanilide
Methyldodecyl-
benzyl trimethyl
ammonium
chloride
Methyl dodecyl
benzyl trimethyl
ammonium
chloride plus
tridecyl methyl
hydroxy ethyl
imidazolinium
chloride
1,T-methylenedi-
2-naphthol
[bis(2-hydroxy-
naphthyl)
methane]
Toxicity,
Bioassay Active
or Field Field Ingredient,
Organism Study'D Location(2) ppm(3)
Sea BSA - 0.5 (LD10o>
lamprey
(larva)
Salmo 0.7 (LD25)
gairdneri
(fingerling)
Sea BSA - 0.5 (LD-|0o)
lamprey
(larva)
Salmo 0.9 (LD25)
gairdneri
(fingerling)
Cylindrospermum L — 2.0 (O)
licheniforme (CD
Gleocapsa
sp(G)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Cylindrospermum L — 2.0 (0)
licheniforme (Cl)
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Ptychocheilus FR Idaho (O)
oregonensis
Experimental
Variables
Controlled
or Noted!4) Comments
See This paper deals with the comparative toxicity of halonitro-
Applegate, salicylanilides to sea lamprey and fingerling rainbow trout
et al as a function of substituent loci.
(1957-1958)
See Comment same as above.
Applegate,
et al
(1957-1958)
a Observations were made on the 3rd, 7th, 14th, and 21st days
to give the following (T = toxic, NT = nontoxic, PT = par-
tially toxic with number of days in parentheses. No number
indicates observation is for entire test period of 21 days):
Cl -T (3),PT (7)
G - PT (3)
So -T (14)
Cv - PT (7)
Gp-T (14)
Np-T (14)
a Comment same as above except that:
~ Cl - NT
Ma - NT
So -PT (14)
Cv -PT (14)
Gp-NT
Np - NT
a The creek was treated with 0.75 Ib of chemical. Surface tem-
perature remained at 61 F during the 3-hr treatment. The
inlet of the stream was treated with 0.05 ppm for 2 hr
after the lagoon was treated.
Four and one-half hours after the start of the treatment, four
northern squawf ish were found dead. The next morning
numerous dead squawf ish were observed on the bottom of
the lagoon.
No live squawf ish were seen and no dead fish of any other
species were observed.
Reference
(Year)
Starkey and
Howell
(1966)
Starkey and
Howell
(1966)
Palmer and
Maloney
(1955)
Palmer and
Maloney
(1955)
MacPhee and
Ruelle
(1968)
•o
m
Z
O
-------
;>
oo
1,1'-methylenedi-
2-naphthol
[bis(2-hydroxy-
naphthyl)
methane]
BSA
Ptychocheilus
oregonensis
Onchorhynchus
tshawytscha
Onchorhynchus
kisutch
Sal mo
gairdneri
Methylene blue — see Appendix B
Methyl
mercaptan
Methyl
mercury
chloride
Onchorlynchus
tshawytscha
Oncorhyncus
kisutch
Sal mo clarkii
clarkii
Venus
japonica
Hurmomya
mutabilis
BSA
Japan
0.006 (K4A)
0.008 (K4A)
0.010(K4A)
0.015 (K4A)
0.9 (K5)
1.75 (K5)
1.2IK5)
(0)
g
in
S
£
CO
z
0
c
3)
m
CO
O
Tl
o
X
m
2
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>
»™
Methyl
mercury
dicyandiamide
Methyl
methacrylate
2-methyl-
naphtho-
quinone
Procambarus
clarkii
(juvenile)
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Pomoxis
nigromaculatus
Notropis
atherinoides
atherinoides
Hyborhynchus
notatus
Ambloplites
rupestris
rupestris
Hum
salmoides
BSA
BSA
BSA
0.083 (T5A)
150IT4A)
250(T4A)
240 (T4A)
420(T4A)
0.3 to 0.6
(K1-2)
a e Experiments were conducted in vessels containing 10 liters
~~ of water.
Temperature was held at 65 F.
Temperature was held at 60 F.
Temperature was held at 55 F.
Temperature was held at 50 F.
This chemical had no toxic effect upon Chinook salmon,
Coho salmon or steelhead trout at the temperature and
concentration indicated for squawfish.
a_d e This chemical is one of a number that may be found in Kraft
mill waste effluents. Data are expressed as minimum lethal
concentration for 5 days.
— Human beings, cats, and waterfowl eating shellfish from
Minamata Bay all succumbed to a strange poisoning. At
autopsy, clinicopathological changes similar to those
induced in mercury poisoning, were found in the
cerebellum, and the cerebral cortices. The shellfish were
examined chemically and were found to contain as much
as 85 mg/kg. The mercury compound was identified and
found in the effluent waste from a chemical plant making
acetyldehyde. A treatment was found to eliminate the
pollutant.
a c d o The pesticides studied in this report are widely used in rice
culture in Louisiana and are toxic to crawfish.
ji c d e f Most fish survived at test concentrations of about one half,
or slightly more, of the TLm value. No attempt was made
to estimate 100 percent survival.
Aerated spring water was used as the test medium. Effective
algicidal concentrations were also toxic to fish.
McPhee and
Ruelle
(1968)
Haydu, et al
(1952)
Irukayama
(1966)
o
X
Hendrick and
Everett
(1965)
Pickering and
Henderson
(1966)
Fitzgerald, et al
(1952)
-------
CHEMICALS
>
jj
0
§
X
H
3)
m
VI
O
-n
O
I
m
S
O
>
£
;>
00
OO
Chemical
5'-methyl-o-
salicylanisidide
Methyl vinyl
ketone
Molybdic
anhydride
Monoamyl-
amine
Mono-n-
butylamine
Monoethyl-
ethanolamine
Mono-
isobutylamine
Mono-iso-
propylamine
Mono-
methylamine
Mono-n-
propylamine
Mono-sec-
butylamine
Naphthenic
acid
Organism
Sa/mo
gairdnerii
Carassius
a u rat us
Sewage
microorganisms
Pimephales
promelas
Semotilus
atromaculatus
Semotilus
atromaculatus
Semotilus
a tro macula tus
Semotilus
atromaculatus
Semotilus
atromaculatus
Semotilus
atromaculatus
Semotilus
a tro macula tus
Semotilus
atromaculatus
Lepomis
macrochirus
Bioassay
or Field
Study (1)
BSA
BOD
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
Toxicity, Experimental
Active Variables
Field Ingredient, Controlled
Location^) ppm<3) or Noted'4*
10 (K2) a
10 (K2)
1.5(O)
(H)370(T4A) acdf
(S) 70 (T4A)
30 to 50 (CR) ae
- 3(3 to 70 (CR) a e
40 to 70 (CR) a e
20 to 60 (CR) ae
40 to 80 (CR) ae
10 to 30 (CR) ae
40 to 60 (CR) ae
20 to 60 (CR) a e
5.6 (T4A) ace
Comments
This paper deals with the relations between chemical struc-
tures of salicylanilides and benzanilides and their toxicity
to rainbow trout and goldfish. The chemical structure of
salicylanilides and benzanilides was related to toxicity and
selectivity to rainbow trout and goldfish. Salicylanilides
were more toxic than benzanilides to the fishes. The ortho
hydroxy substitution of salicylanilide accelerated biological
activity against fish. Meta nitro substitution on the
salicylanilides and benzanilides increased toxicity to fish.
Similar findings are reported for halogens and their relative
position(s) in the molecule.
The chemical was studied as to how low levels (ppm) may
affect BOD in domestic sewage. The chemical was toxic
at the level stated.
Both hard (H) and soft (S) water were used.
Test water used was freshly aerated Detroit River water.
A typical water analysis is given. Toxicity is expressed as
the "critical range" (CR), which was defined as that con-
centration in ppm below which the 4 test fish lived for
24 hr and above which all test fish died. Additional data
are presented.
Comment same as above.
Comment same as above.
Comment same as above.
Comment same as above.
Comment same as above.
Comment same as above.
Comment same as above.
Increase in temperature seemed to increase toxicity of this
chemical. Low dissolved oxygen reduced toxicity of some
Reference
(Year)
Walker, et al
(1966)
Oberton and
Stack
(1957)
Tarzwell and
Henderson
(1960)
Gillette, et al
(1952)
Gillette, et al
(1952)
Gillette, et al
(1952)
Gillette, et al
(1952)
Gillette, et al
(1952)
Gillette, et al
(1952)
Gillette, et al
(1952)
Gillette, et al
(1952)
Cairns
(1957)
>
TJ
"O
m
z
o
X
>
chemicals in this study. Toxicity values may be 20%
higher in hard versus soft water.
-------
oo
Naphthenic
acid
Naphthenic
acid
Naphthenic
acid
Naphthenic
acids
Naphthenic
acids
Naphthenic
acids
Naphthenic
acid (a) -
cyanide (b) -
chromium (c)
mixture
5 Naphthalene
Q a-naphthol
S
25
C b-naphthol
OJ
m
J? 1,4-naphtho-
-n quinone
O
m
S
9
Lepomis
macrochirus
Physa
heterostropha
Lepomis
macrochirus
Physa
heterostropha
Nitzschia
linearis
Physa
heterostropha
Lepomis
macrochirus
Lepomis
macrochirus
Physa
heterostropha
Brachydanio
rerio
(adults)
(eggs)
Lepomis
macrochirus
Lepomis
macrochirus
Lepomis
macrochirus
Cambusia
affinis
Microcystis
aeruginosa
Microcystis
aeruginosa
Microcystis
aeruginosa
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
(N) 5.6 (T4A)
(L) 2.0 (T4A)
(N) 6.6-7.5
(T4A) N
(L) 2.0 (T4A) L
5.6 (T4A)
2.0 (T4A)
6.6-7.5 (T4A)
2.0 (T4A)
43.1 (T5A)
6.6-7.5 (T4A)
5.6 (T4A)
5.79 (T4A)
6.60 (T1A)
Modified Chu No. 14 test medium was used. Toxicity is given Cairns and
both for "normal" 02 (5-9 ppm), (N), and with "low" C>2 Scheier
(2 ppm DO), (L). High and low threshold concentration and (1958)
concentration percent of survival are also presented.
16.3 (T2A)
3.5 (T2A)
5.6 (T2A)
5.6 (T4A)
(a) 4.74 (T4A)
(b) .026 (T4A)
(c) 0.019 (T4A)
165(T2A)
100 (K)
100 (K)
100 (K)
a e Normal oxygen content in water.
Low oxygen content in water.
Normal oxygen content in water.
Low oxygen content in water.
ace The purpose of this experiment was to determine whether
there was a constant relationship between the responses of
these organisms. From the data presented, there was no
apparent relationship of this type. Therefore the authors
advise that bioassays on at least 3 components of the food
web be made in any situation.
££^L "*"n's cnerr|ical is a mixture of compounds with a general
formula of CnH2N-C>2, CnH2N-4C>2, or CnH2N-6C>2,
which are widely used in insecticidal formulations. The
experiments were conducted in a synthetic dilution water
of controlled chemical composition. In hard water, the
chemical was somewhat less toxic.
a.£.fL5JL The test dilutions were made up from distilled water and ACS
grade chemicals. Temperature was held at 24 C and the
solution was aerated to maintain a dissolved oxygen content
of 5-9 ppm.
a c d e All fish were acclimatized for 2 weeks in a synthetic dilution
water.
a c d e Comment same as above.
a c d e g The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
a_ The chemical was tested on a 5-day algae culture. 1 x 10^ to
2 x 106 cells/ml, 75 ml total volume. CHU No. 10 medium
was used.
a Comment same as above.
a, etc Comment same as above.
Cairns
(1965)
Patrick, et al
(1968)
Cairns and
Scheier
(1962)
Cairns, et al
(1965)
Cairns and
Scheier
(1968)
Cairns and
Scheier
(1968)
Wallen, et al
(1957)
Fitzgerald, et al
(1952)
Fitzgerald, et al
(1952)
Fitzgerald, et al
(1952)
•o
m
Z
D
X
-------
o
I
m
S
o
£ Chemical
tn
5 1,4-naphtho-
O quinone
S
X
-l
c
3)
m
en
O
Tl
O
g a-naphthylamine
O
>
Eo
b-naphtha-
quinoline
Nickel
Nickel
Bioassay
or Field
Organism Study '1'
Pomoxis BSA
n/gromaculatus
Notropis
atherinoides
Hyborhynchus
notatus
Ambloplites
rupestris
Huro
salmoides
Cylindrospermum L
lichen/forme (Cl)
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chi ore! la
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Cylindrospermum L
licheniforme (Cl)
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Rainbow FR
trout
Lebistes L
reticulatus
Bufo
valliceps
(tadpoles)
Daphnia
magna
Toxicity,
Active
Field Ingredient,
Location^) ppm<3)
0.3 to 0.6
(K1-2)
2.0(0)
2.0 (O)
Scotland 25 (T2)
10 (K)
100 (K)
10 (K)
Experimental
Variables
Controlled
or NotedW Comments
e Aerated spring water was used as the test medium. Effective
algicidal concentrations were also toxic to fish.
a Observations were made on the 3rd, 7th, 14th, and 21st
days to give the following (T = toxic, NT = nontoxic.
PT = partially toxic with number of days in parentheses.
No number indicates observation is for entire test period
of 21 days):
Cl -PT (7)
Ma -T
So -T (7)
Cv -T (7),PT (21)
Gp-T (7),PT (21)
Np -T (3),PT (7)
a Comment same as above except that
Cl -PT
Ma -NT
So -PT
Cv -PT (7)
Gp-T(7),PT(21)
Np-T (3),PT (7)
a c e f I m This work represents an extension of laboratory studies of
the toxicity of complex effluents to investigations of rivers.
ace It is assumed in this experiment that the cations considered
are toxic because they combine with an essential sulfhydryl
group attached to a key enzyme. This treatment indicates
that the metals which form the most insoluble sulfides are
the most toxic. The log of the concentration of the metal
ion is plotted against the log of the solubility product
constant of the metal sulfide — a treatment that does not
lend itself to tabulation. The cation toxicity cited is only
an approximate concentration interpolated from a graph.
Time of death was not specified.
Reference
(Year)
Fitzgerald, et al
(1952)
Palmer and
Maloney
(1955)
Palmer and
Maloney
(1955)
Herbert, et al
(1965)
Shaw and
Grushkin
(1967)
^
TJ
m
X
^
-------
Nickel
ammonium
sulfate
Nickel
chloride
Nickel
chloride
Nickelous
chloride
NickeJ
chloride
Nickel
chloride
S
O
O
S
X
Nickel-
cyanide
complex
Nickel cyanide
complex
[sodium
cyanide
(600 ppm CN-)
plus nickelous
sulfate
(355 ppm NO]
ni Nickel-
_ ferrocyanide
-n complex
O
m
2
o
Sewage
organisms
Daphnia
magna
Sewage
organisms
BOD
134(0)
BSA
BOD
Pimephales
promelas
LJmnaea
paJustris
(eggs)
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Lepomis
macrochirus
(juvenile)
Pimephales
promelas
BSA
BSA
BSA
BSA
BSA
Pimephales
promelas
BSA
<0.7 (O)
38(0)
(H) 24 (T4A)
(S) 4 (T4A)
8x 10-6M
acdf
(S) 5.18(T4A)
(H) 42.4 (T4A)
(S) 5.18 (T4A)
(H) 39.6 (T4A)
(S) 9.82 (T4A)
(S) 4.45 (T4A)
(O)
0.95 (T4A)
c d e f
a c d f p
a cd
1.0 ppm CN"
0.8 ppm Cu
0.4 ppm Fe
(non-toxic
after 4 days)
Various metal salts were studied in relation to how they
affected the BOD of both raw and treated sewage as well
as how they affected the processing of sewage in the treat-
ment plant. BOD was used as the parameter to measure the
effect of the chemical. The chemical concentration cited is
the ppm required to reduce the BOD values by 50%. This
chemical was tested in an unbuffered system.
Lake Erie water was used as diluent. Toxicity given as
threshold concentration producing immobilization for
exposure periods of 64 hr.
Various metal salts were studied in relation to how they
affected the BOD of both raw and treated sewage as well
as how they affected the processing of sewage in the treat-
ment plant. BOD was used as the parameter to measure the
effect of the chemical. The chemical concentration cited is
the ppm required to reduce the BOD values by 50%. This
chemical was tested in an unbuffered system.
Both hard (H) and soft (S) water were used.
Toxicity is given in molar concentrations for maximum
direct mortality (kill) in 4 hours.
(S) Soft water
(H) Hard water
Values are expressed as mg/l of metal.
Sheets
(1957)
Anderson
(1948)
Sheets
(1957)
Tarzwell and
Henderson
(1960)
Morrill
(1963)
Pickering and
Henderson
(1965)
In solution with a calculated CN content of 100 to 500 ppm, Doudoroff, et a\
the median resistance time was 143 to 540 min. There (1966)
was no apparent correlation between median resistance time
and concentration.
Synthetic soft water was used. Toxicity data given as number Doudoroff, et al
of test fish surviving after exposure at 24, 48, and 96 hr. TLm (1956)
values were estimated by straight-line graphical interpolation
and given in ppm CN". Additional toxicity data in which total
alkalinity was varied, 730 (T-4) with 192 ppm CaCOs
alkalinity.
Synthetic soft water was used. Toxicity data given as number Doudoroff, et al
of test fish surviving. (1956)
-------
CHEMICALS
2j
D
S
X
-I
c
m
O
o
m
S
O
r;
to
>
3
\
Chemical
Nickel
nitrate
Nickel
nitrate
Nickel
sulfate
Nickel
sulfate
Nitric
acid
Nitric
acid
3-nitro-4
acetoxybenzoic
acid
Bioassay
or Field
Organism Study^)
Gasterosteus BSA
aculeatus
Sewage BOD
organisms
Sewage BOD
organisms
Salmo BSA
gairdneri
Salmo
trutta
Salvelinus
fontina/is
Salvelinus
namaycush
Ictalurus
punctatus
Lepomis
macrochirus
Daphnia BSA
magna
Gambusia BSA
affinis
Cylindorspermum L
lichen/forme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus /So)
Chlorella
variegate (Cv)
Gomphonema
parvulum (Opt
Nitzschia
pa/ea (Nf>)
Toxicity,
Active
Field Ingredient,
Location(2) ppm(3)
0.8 (K10)
64 (0)
16 (O)
160(T2A)
270 (T2A)
242 (T2A)
75 (T2A)
165 (T2A)
495 (T2A)
107 (O)
75 (T2A)
2.0 (0)
Experimental
Variables
Controlled
or NotedW) Comments
— Solutions were made up in tap water. 3.0 to 5.0 cm stickle-
back fish were used as experimental animals. This paper
points out that there is a marked relationship between the
toxicity of the metals and their solution pressures. Those
with low solution pressures were the most toxic.
— Various metal salts were studied in relation to how they
affected the BOD of both raw and treated sewage as well
as how they affected the processing of sewage in the treat-
ment plant. BOD was used as the parameter to measure
the effect of the chemical. The chemical concentration
cited is the ppm required to reduce the BOD values by
50%. This chemical was tested in an unbuffered system.
— Comment same as above.
a f Variance and the 95-percent confidence interval (C.I.) were
also determined.
a c This paper deals with the toxicity thresholds of various
substances found in industrial wastes as determined
by the use of D. magna. Centrifuged Lake Erie water was
used as a diluent in the bioassay. Threshold concentration
was defined as the highest concentration which would just
fail to immobilize the animals under prolonged (theoretically
infinite) exposures.
a c d e g The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
a Observations were made on the 3rd, 7th, 14th, and 21st
days to give the following (T = toxic, NT = nontoxic.
PT = partially toxic with number of days in parentheses.
No number indicates observation is for entire test period
of 21 days):
Cl -NT
Ma - NT
So - NT
Cv -NT
Gp - NT
Np — NT
Reference
(Year)
Jones
(1939)
Sheets
(1957)
Sheets
(1957)
Willford
(1966)
Anderson
(1944)
Wallen, et al
(1957)
Palmer and
Maloney
(1955)
^
T3
•o
m
z
g
x
^
-------
3-nitrobenz-
anilide
c
30
m
O
m
Nitrobenzene
3-nitro-4-
methoxy-
benzoic
acid
4'-nitro-o-
salicylanisidide
O
m
§
O
o-nitro-
phenol
p-nitrophenyl-
hydrazine
hydrochloride
p-nitrophenyl-
hydrazine
Salmo
gairdnerii
Carassius
auratus
BSA
10 (K2)
10 (K2)
Sewage
organisms
Cylin drospermum
lichen/forme fCt)
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gpi
Nitzschia
palea (Np)
Salmo
gairdnerii
Carassius
auratus
BOD
630 (TC50)
2.0 (0)
BSA
10 (K 3 hr)
10 (K2)
Lepomis
macmchirus
Microcystis
aeruginosa
Microcystis
aeruginosa
BSA
46.3-51.6
(T2A)
50 (K)
100 (K)
a cd e f g i o
a, etc
a, etc
This paper deals with the relations between chemical struc-
tures of salicylanilides and benzanilides and their toxicity
to rainbow trout and goldfish. The chemical structure of
salicylanilides and benzanilides was related to toxicity and
selectivity to rainbow trout and goldfish. Salicylanilides
were more toxic than benzanilides to the fishes. The ortho
hydroxy substitution of salicylanilide accelerated biological
activity against fish. Meta nitro substitution on the
salicylanilides and benzanilides increased toxicity to fish.
Similar findings are reported for halogens and their rela-
tive position(s) in the molecule.
The purpose of this paper was to devise a toxicity index for
industrial wastes. Results are recorded as the toxic con-
centration producing 50 percent inhibition (TCsfj) of
oxygen utilization as compared to controls. Five toxi-
grams depicting the effect of the chemicals on BOD were
devised and each chemical classified.
Observations were made on the 3rd, 7th, 14th, and 21st
days to give the following (T = toxic, NT = nontoxic,
PT = partially toxic with number of days in parentheses.
No number indicates observation is for entire test period
of 21 days):
Cl - NT
Ma - PT (3)
So - PT (7)
Cv - PT (3)
Gp-T(3)
Np - NT
This paper deals with the relations between chemical struc-
tures of salicylanilides and benzanilides and their toxicity
to rainbow trout and goldfish. The chemical structure of
salicylanilides and benzanilides was related to toxicity and
selectivity to rainbow trout and goldfish. Salicylanilides
were more toxic than benzanilides to the fishes. The ortho
hydroxy substitution of salicylanilide accelerated biological
activity against fish. Meta nitro substitution on the
salicylanilides and benzanilides increased toxicity to fish.
Similar findings are reported for halogens and their rela-
tive position(s) in the molecule.
Assays are completely described and autopsy data are
reported.
The chemical was tested on a 5-day algae culture, 1 x 10^ to
2 x 10^ cells/ml, 75 ml total volume. Chu No. 10 medium
was used.
Comment same as above.
Walker, et al
(1966)
Hermann
(1959)
Palmer and
Maloney
(1955)
I
m
O
Walker, et al
(1966)
Lammering and
Burbank
(1961)
Fitzgerald, et al
(1952)
Fitzgerald, et al
(1952)
-------
COMMERCE
>•
0
i
m
S
O
-o
O
O
c
0
H
^
^C
-fc.
Chemical
2' nitro-p-
solicylanilide
3-nitro-2',6'-
sahcyloxylidide
3-nitrosah-
cylanilide
3-nitro-2'.3-
salicyloxylidide
3-nitro-2',5-
salicyloxyl-
idide
3-nitro-2',4'-
salicyloxyl-
idide
Organism
Salmo
gairdnerii
Carassius
auratus
Salmo
gairdnerii
Carassius
auratus
Salmo
gairdnerii
Carassius
auratus
Salmo
gairdnerii
Carassius
auratus
Salmo
gairdnerii
Carassius
auratus
Salmo
gairdnerii
Carassius
auratus
Toxicity,
Bioassay Active
or Field Field Ingredient,
Studyd) Location<2) ppm(3)
BSA - 10(K3hr)
10 (K 3hr)
BSA - 10 (K2)
10 (K2)
BSA - 10 (K2A)
10 (K2A)
BSA - 1.0 (K2A)
10.0 (K2A)
BSA - 10.0 (K 3 hr)
10.0 (K2)
BSA - 1.0 (K2)
10.0 (K 3 hr)
Experimental
Variables
Controlled
or NotedW Comments
a This paper deals with the relations between chemical
structures of salicylanilides and benzanilides and
their toxicity to rainbow trout and goldfish. The
chemical structure of salicylanilides and benzanilides
was related to toxicity and selectivity to rainbow
trout and goldfish. Salicylanilides were more toxic
than benzanilides to the fishes. The ortho hydroxy
substitution of salicylanilide accelerated biological
activity against fish. Meta nitro substitution on the
salicylanilides and benzanilides increased toxicity to
fish. Similar findings are reported for halogens and
their relative position (s) in the molecule.
a Comment same as above.
a Comment same as above.
a Comment same as above.
a Comment same as above.
a Comment same as above.
Reference
(Year)
Walker, et al
(1966)
Walker, et al
(1966)
Walker, et al
(1966)
Walker, et al
(1966)
Walker, et al
(1966)
Walker, et al
(1966)
1
m
Z
O
-------
Nonyl
phenol
ethoxylate
p-octyl
diphenylamine
Salmo
gairdnerii
(12 days
after
hatching)
(25 days
after
hatching.
fry)
(210 days
after
hatching,
fingerling)
Daphnia
magna
BCFA
Oxydipro-
pionitrile
Pimephales
promelas
Lepomis
macrochirus
Lebistes
reticulatus
BSA
BSA
13.5 (K)
3hr
5.2 (K)
6hr
4.4 (K)
3hr
2.3 (K)
6hr
8.0 (K)
3hr
5.2 (K)
6hr
>40 (K2)
a cd e i
(H) 3600 (T4A)
(S) 3900 (T4A)
(S) 4200 (T4A)
(S) 4450 (T4A)
cdef
Successive developmental stages of the organism showed
marked differences in resistance to the chemical.
Changes in resistance could not be correlated with
changes in respiratory activity of the fish but rather
with their water metabolism.
An attempt was made to correlate the biological action
with the chemical reactivity of selected chemical sub-
stances. Results indicated a considerable correlation
between the aquarium fish toxicity and antiautocatalytic
potency of the chemicals in marked contrast to their
toxicity on systemic administration.
(H) Value in hardwater
(S) Value in softwater
The chemical produced no change in flavor of the cooked
bluegill.
Marchetti
(1965)
Sollman
(1949)
Henderson,
et al
(1960)
I
m
Z
O
X
Oxalic
acid
8
2 Oxalic
3 acid
O
>
O
m
5
jj Pentachloro-
r" phenol
TJ
O
o
Daphnia
magna
BSA
95 (O)
Sewage
organisms
BOD
Green
sunfish
BSA
43 (TC50)
(O)
This paper deals with the toxicity thresholds of various Anderson
substances found in industrial wastes as determined by (1944)
the use of D. magna. Centrifuged Lake Erie water was
used as a diluent in the bioassay. Threshold concentra-
tion was defined as the highest concentration which
would just fail to immobilize the animals under prolonged
(theoretically infinite) exposure.
The purpose of this paper was to devise a toxicity index Hermann
for industrial wastes. Results are recorded as the toxic (1959)
concentration producing 50 percent inhibition (TCsfj)
of oxygen utilization as compared to controls. Five
toxigrams depicting the effect of the chemicals on BOD
were devised and each chemical classified.
Pentachlorophenol was repellent to the green sunfish at Summerfelt
20 mg/l but the fish were indifferent in response to and Lewis
5.0mg/l. (1967)
-------
£
ON
o
I
m
S
o
•£ Chemical
C/7 • — •
> PH
O
s
H pH
C
3J
m
O
Tl
O
X
m
S
o
•£
to
Phenanthra-
quinone
o-phenanthro-
line
Phenazine-1-
carboxylic
acid
Phenol
Phenol
Bioassay
or Field
Organism Study (1)
Gasterosteus BSA
aculeatus
Salmo BSA
gairdnerii
Pomoxis BSA
nigromacu/atus
Notropis
atherinoides
atherinoides
Hyborhynchus
no tat us
Ambloplites
rupestris
rupestris
Huro
salmoides
Microcystis L
aeruginosa
Anabaena L
f/os-aquae
Notemigonous
crysoleucas
Carassius BSA
carassius
Carassius BSA
auratus
Toxicity, Experimental
Active Variables
Field Ingredient, Controlled
Location*2) ppm (3) or Noted'4) Comments
— (O) c e Tap water was used to make up the solutions. The fish
avoided water more acid than a pH of 5.6 or one
more alkaline than 1 1 .4.
— (O) abcdefp The pH value at which acid solutions proved lethal to rainbow
trout within 1 day was unaffected by the pH value to which
the fish had been acclimatized (pH 6.5-8.4). Fifty percent
of a population of yearling rainbow trout were killed in
about 1 day at a pH value of 3.6 when little free CC>2 was
present; where in the presence of 50 ppm free CC>2, a pH
value of 5.6 killed 50 percent of a population of fingerling
trout in 15 days. In water of low free CC>2 content, the
relation between pH value and log median period of survival
was linear for survival times between about 3 hr and 15 days.
Exposure to pH values below 5.0 for about 3 months might
be harmful to rainbow trout when little free CC>2 is present
in the water.
— (O) e Aerated spring water was used as the test medium. No effect
was observed on fish after 2 days of exposure, even with
excess solid dispersed in water. At algicidal concentrations,
this compound was not toxic to the fish studied.
— 100 (K) a, etc The chemical was tested on a 5-day algae culture, 1 x 10*> to
~~ 2 x 106 cells/ml, 75 ml total volume. Chu No. 10 medium
was used.
— 100 (O) — Value given is concentration for complete inhibition of
A. flos-aquae. No harmful effect to N. crysoleucas was
0.1 to 10.0 (0) noted at the concentrations evaluated.
— (O) a This old, lengthy paper discusses toxicity of many chemicals.
possible mechanism of action of some, the effect of tempera-
ture, effect of dissolved oxygen, the efficiency of the gold-
fish as a test animal, compares this work with earlier work.
and lists an extensive bibliography.
In a concentration of 0.259 g/liter, fish survived 104 minutes.
— 125 to 372 a Temperature in test containers was maintained at 27 ± .2 C.
(K 8 hr) ~~ Goldfish tested weighed between 2 and 4 g.
83.2 (O) Phenol, 83.2 ppm (mg per liter), killed 86% of the fish in
41.6 (O) 8 hr; 41.6 (mg per liter) killed 67% in 8 hr.
Reference
(Year)
Jones
(1948)
Lloyd and
Jordan
(1964)
Fitzgerald, et al
(1952)
Fitzgerald, et al
(1952)
Toohey, et al
(1965)
Powers
(1918)
Gersdorff and
Smith
(1940)
•o
m
Z
O
-------
Phenol
Phenol
Phenol
Phenol
Phenol
Phenol
Phenol
2
o
o
s
3D
m
Phenol
Phenol
o
I Phenol
•m
§
o
Anopheles
quadrimacula tus
Goldfish
Shiner
minnows
Carassius
auratus
Daphnia
magna
BSA
(O)
BSA
BSA
0.103 (K)
94 (O)
Hyborhynchus
n ota tus
Daphnia
magna
Phoxinus
phoxinus
Semotilus
atromaculatus
Lepomis
macrochirus
Lepomis
macrochirus
Cambusia
affinis
BSA
BSA
28.9 (K2)
BCFA
BSA
0.04% (K 4 min)
0.01% (K 8 min)
0.004%
(K 24 min)
0.0004%
(K 40-50 hr)
10 to 20 (CR)
BSA
BCFA
BSA
20.5 (T4A)
19.3 (T2A)
11.5 (T4A)
56 (T2A)
— Under the conditions of this experiment, this chemical Knowles, et al
(diluted 1 to 30) applied at rates of 10 to 95 gallons per (1941)
acre was less effective than kerosene in controlling
mosquitos. In the laboratory, at the rate of 50 gallon
per acre, 100 percent of fish were killed but only 16 per-
cent of the larvae. Phenol did not appear to be a desirable
larvacide for general mosquito control.
a Goldfish weighed between 2 and 4 g. Temperature was Gersdorff
maintained at 27.0 ± 0.2 C. (1943)
a c This paper deals with the toxicity thresholds of various Anderson
~~ substances found in industrial wastes as determined by (1944)
the use of D. magna. Centrifuged Lake Erie water was
used as a diluent in the bioassay. Threshold concentration
was defined as the highest concentration which would just
fail to immobilize the animals under prolonged (theoretically
infinite) exposure.
— Fish in aquaria were trained to detect and distinguish between Hasler and
phenol and p-chlorophenol at levels as low as 0.0005 ppm. Wisby
The fish could also distinguish o-chlorophenol from the two (1949)
other compounds. The training method is described.
a An attempt was made to correlate the biological action with Sollman
the chemical reactivity of selected chemical substances. (1949)
Results indicated a considerable correlation between the
aquarium fish toxicity and antiautocatalytic potency of
the chemicals in marked contrast to their toxicity on
systemic administration.
ja c Tap water was used as diluent. The apparatus used was a Jones
34 mm diameter tube fitted to permit sharp vertical (1951)
separation of water and test solutions. With this system,
avoidance data could be obtained. Toxicity is given as
average survival time of replicates. Fish did not avoid
phenol in the <0.04% range.
^e Test water used was freshly aerated Detroit River water. A Gillette, et al
typical water analysis is given. Toxicity is expressed as (1952)
the "critical range" (CR), which was defined as that
concentration in ppm below which the 4 test fish lived
for 24 hr and above which all test fish died. Additional
data are presented.
£ c d e Chu No. 14 modified medium was used as dilution water. Trama
The fish were transferred each 24 hours into new test (1955)
solutions because of phenol loss due to aeration.
a c e f Test water was composed of distilled water with CP grade Cairns and
chemicals and was aerated throughout the 96-hour Scheier
exposure period. (1955)
The phenol concentration was kept constant during the
test period.
a c d e g The effect of turbidity on the toxicity of the chemicals Wallen, et al
was studied. Test water was from a farm pond with "high" (1957)
turbidity. Additional data are presented.
m
O
X
-------
r>
i
m
n
P Chemical
^ Phenol
O
§
X
H
C
33
m
w Phenol
O
Tl
0
m Phenol
5
o
(/i
Phenol
Phenols
(monohydric)
3
•j
Phenol
Organism
Sewage
organisms
Channel
catfish
(fingerlings)
Lepomis
macrochirus
Lepomis
macrochirus
Salmo
gairdnerii
Hydropsyche
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study(l) Location '2) ppm '3)
BOD - 1600 (TC5fj)
BSA - 16.7
(K 48 hr A)
BSA - 11.5IT4A)
BSA - 22.2 (T2A)
BSA - (O)
BSA - 30.0 (T2A)
Experimental
Variables
Controlled
or Noted'4* Comments
a The purpose of this paper was to devise a toxicity index for
~ industrial wastes. Results are recorded as the toxic con-
centration producing 50 percent inhibition (TC50) of
oxygen utilization as compared to controls. Five toxi-
grams depicting the effect of the chemicals on BOD were
devised and each chemical classified.
a Tap water was used. Considerable additional data are
~ presented.
a c d e i A "control" was prepared by adding required chemicals to
distilled water, and this was constantly aerated. Data
reported are for larger fish, app 14.24 cm in length. Data
for smaller fish are also in the report.
a c d e f g i o Assays are completely described, and autopsy data are
reported.
a e This is a study of the effect of varying dissolved oxygen
concentrations on the toxicity of selected chemicals.
The toxicity of heavy metals, ammonia, and monohydric
phenols increased as the dissolved oxygen in water was
reduced. The most obvious reaction of fish to lowered
oxygen content is to increase the volume of water passed
over the gills, and this may increase the amount of poison
reaching the surface of the gill epithelium.
The concentration of the chemical in the water was not
specified.
a Soft water used as diluent water.
Reference
(Year)
Hermann
(1959)
Clemens and
Sneed
(1959)
Cairns and
Scheier
(1969)
Lammering and
Burbank
(1961)
Lloyd
(1961)
Roback
^
•o
m
z
o
X
•J.,
Phenol
Phenol
Stenonema
Protococcus sp
Chlorella sp
Dunaliella
euchlora
Phaeodactylum
tricornutum
Monochrysis
lutheri
"Aquatic
flora and
fauna"
14.5 (T2A)
BSA - 500 (K)
500 (K)
500 (K)
100(NG)
100(NG)
FR Luxembourg 5.0-10.0(0)
This paper concerns the growth of pure cultures of marine
plankton in the presence of toxicants. Results were
expressed as the ratio of optical density of growth in the
presence of toxicants to optical density in the basal medium
with no added toxicants. NG = no growth, but the organisms
were viable.
Destruction of all flora and fauna of the river occurred in
highly polluted zone (10 ppm), slight affects occurred at
3.0-10 ppm, and practically no damage occurred at con-
centrations below 3.0 ppm.
(1965)
Ukeles
(1962)
Krombach and
Barthel
(1963)
-------
Phenol
Rasbora BSA
heteromorpha
6.0 (O)
Phenol
Phenol
>
MD
Phenol
O
m Phenols
2
Phenol
O
m
CO
O Phenol
Fish
Fish
BSA
FR
1.4x10-4M (K) ac
Ohio .016 (O)
Carassius
auratus
Rainbow
trout
Daphnia
magna (young)
Daphnia
magna (adult)
Lepomis
macrochirus
Mollienesia
latopinna
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
BCSA
(O)
FR
BSA
BSA
Scotland 4.4 (T2)
17 (T1A)
7 (T2A)
61 (T1A)
21 (T2A)
63 (T1A)
22 (T2A)
29 (T4A)
26 (T4A)
46 (T4A)
44 (T4A)
a c e f I m
a c d e f
For many toxins the rate of mortality is found to be a linear Abram
function of the logarithm of the concentration of the poison; (1964)
whereas the comparable relation between the logarithms of
the survival time and the concentration is nonlinear. The
linear function can be exploited to provide comparatively
simple methods of estimating long-term survival concentra-
tions. An application of this is suggested for defining realistic
standards of toxicity. At the concentration listed, there
was a 30 percent mortality in about 2 weeks.
Avoidance behavior of test fish to toxic chemicals is given. Ishio
Toxicity is given as the lowest lethal concentration (molar). (1965)
Ratios of avoidance and lowest lethal concentrations are
presented and discussed.
Following shut-down of steel mills due to a strike, phenols Krumholz and
were 3.0 ppb in the Ohio River during the shut-down as Minckley
compared to 16.0 ppb after the mills resumed operation. (1964)
Threshold odor intensity and dissolved-iron content were
2 to 8X greater after start-up of the mills than during the
shut-down period. Appearance or increased abundance of
such "clean-water fish" as big-eye chub, common sucker,
stoneroller, creek chub, sand shiner, mimic shiner, common
shiner, and bluntnose minnow occurred while mills were
shut down. Additionally, small minnows increased 20X
during this period. The authors note that these facts are
indicative of a marked betterment of the environment.
Further, they suggest that the faunal monotony of the
upper Ohio River is more closely related to industrial than
to domestic discharges.
A 5% solution of phenol in water was injected in the Boni
muscular masses of the fish tails at various levels. The (1965)
WILD (minimal lethal dose) of phenol was found to be
230 mg/kg.
Goldfish are unable to conjugate phenol, while showing a
high efficiency in excreting the drug unchanged.
This work represents an extension of laboratory studies Herbert, et al
of the toxicity of complex effluents to investigations (1965)
of rivers.
"Standard reference water" was described and used as Oowden and
well as lake water. Varied results were obtained when Bennett
evaluations were made in various types of water. (1965)
Most fish survived at test concentrations of about one half, Pickering and
or slightly more, of the TLm value. No attempt was made Henderson
to estimate 100 percent survival. (1966)
-------
o
rn
2
O
p Chemical
g Phenol
O
§
*j Phenol
C
3D
m
t«
o
•n Phenol
O
I
m
3
£
>*
E
w
Phenol
>
,!_ Phenol
O
O
Phenol
Phenylhydra-
zine hydro-
chloride
4'-phenylazo-
3-nitrosali-
cylanilide
Organism
Salmo
gairdnerii
Salmo
gairdnerii
Salmo
salar
Salmo
gairdnerii
Nitzschia
linearis
Physa
heterostropha
Lepomis
macrochirus
Salmo
gairdnerii
Salmo
gairdnerii
Microcystis
aeruginosa
Salmo
gairdnerii
Carassius
auratus
Toxicity,
Bioassay Active
or Field Field Ingredient,
Studyd) Location'2) ppm'3)
BSA - 1.5IT2A)
BSA - 5.2 (T2)
BSA - (O)
BSA - 258 (T5A)
94.0 (T4A)
13.5 (T4A)
BCFA - 7.5 (T2A)
BSA - 4.58 to 5.8
(T2A)
L - 100 (K)
BSA - 0.1 (K2A)
1.0 (K3hr)
1.0 (K2A)
10.0 (K2A)
Experimental
Variables
Controlled
or Noted(4) Comments
a c d e f Test solution used in this study was sea water collected from
~ ~~ the North Sea, then diluted with distilled water. Sensitivity
of fish to poisoning by phenol increased as salinity increased.
a c d e f Fish were acclimatized to 14 days in salt water.
a c d e f p Fish were acclimatized to the temperature of the test water
over a period of 24-36 hr and then held at the test temper-
ature without being fed for 24 hr before testing. Results
showed that the resistance to poisoning by phenol increases
with increase in temperature up to at least 18 C, at which
the L2 is almost twice that at 6 C. A similar relationship
exists with gas-liquor phenols. The response of test popula-
tions showed the least viability at 12 C.
ace The purpose of this experiment was to determine whether
there was a constant relationship between the responses of
these organisms. From the data presented, there was no
apparent relationship of this type. Therefore the authors
advise that bioassays on at least 3 components of the food
web be made in any situation.
acdef Phenol rapidly damaged the gills of trout. Experiments were
conducted at levels above and below the \-C$rj and for
varying periods of time. Even at the level which killed only
20% of the fish in 48 hours, sufficient damage was done
within one week to impair survival of the individual and
affect reproduction. (This concentration was not specified,
but was probably 6.5 ppm.)
a c d e f o The concentration killing a half batch of fish in 2 days
provides a reasonable estimate of the threshold concen-
tration. The lethality of this chemical depends upon the
temperature and concentration of dissolved oxygen.
a, etc The chemical was tested on a 5-day algae culture, 1 x 10^ to
~ 2 x 106 cells/ml, 75 ml total volume. Chu No. 10 medium
was used.
a This paper deals with the relations between chemical struc-
~~ tures of salicylanilides and benzanilides and their toxicity
to rainbow trout and goldfish. The chemical structure of
salicylanilides and benzanilides was related to toxicity and
selectivity to rainbow trout and goldfish. Salicylanilides
were more toxic than benzanilides to the fishes. The ortho
hydroxy substitution of salicylanilide accelerated biological
activity against fish. Meta nitro substitution on the
salicylanilides and benzanilides increased toxicity to fish.
Similar findings are reported for halogens and their rela-
tive position(s) in the molecule.
Reference
(Year)
Brown, et al
(1967)
Brown, et al
(1967)
Brown, et al
(1967)
Patrick, et al
(1968)
Mitrovic, et al
(1968)
Brown
(1968)
Fitzgerald, et al
(1952)
Walker, et al
(1966)
>
•o
•o
m
Z
X
>
-------
p-phenylene-
diamine
Phenylmercuric
acetate
(10%soln.)
Phenylmercuric
acetate
Phenylmercuric
hydroxide
>
o
Phenylmercuric
nitrate
£
£
Daphnia
magna
Ictalurus
punctatus
Channel
catfish
(fingerlings)
Cylindrospermum
licheniforme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegate (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Cylindrospermum
licheniforme (Cl)
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
BSA
n-phenyl-naphthyl- Daphnia
amine magna
Phenylthiourea
z
o
2
X
33
m
Microcystis
aeruginosa
Daphnia
magna
BSA
BSA
5.74 (K2)
2.30 (K2)
1.46(T2A)
4.1 (K1A)
2.0 (O)
2.0 (O)
a An attempt was made to correlate the biological action
with the chemical reactivity of selected chemical substances.
Results indicated a considerable correlation between the
aquarium fish toxicity and antiautocatalytic potency of
the chemicals in marked contrast to their toxicity on
systemic administration.
a c f i The experiment was conducted at 68 C.
Tap water was used. Considerable additional data are
presented.
Observations were made on the 3rd, 7th, 14th, and 21st
days to give the following (T = toxic, NT = nontoxic,
PT = partially toxic with number of days in parentheses.
No number indicates observation is for entire test period
of 21 days):
Cl -T (3)
Ma-T (3)
So - T (3)
Cv - T (3)
Gp-T(3)
Np-T(3)
Comment same as above, including data cited.
BSA
4.4 (K2)
BSA
50 (K)
630 (K2)
An attempt was made to correlate the biological action
with the chemical reactivity of selected chemical substances.
Results indicated a considerable correlation between the
aquarium fish toxicity and antiautocatalytic potency of
the chemicals in marked contrast to their toxicity on
systemic administration.
The chemical was tested on a 5-day algae culture, 1 x 10^ to
2 x 106 cells/ml, 75 ml total volume. Chu No. 10 medium
was used.
An attempt was made to correlate the biological action
with the chemical reactivity of selected chemical substances.
Results indicated a considerable correlation between the
aquarium fish toxicity and antiautocatalytic potency of
the chemicals in marked contrast to their toxicity on
systemic administration.
Sollman
(1949)
Clemens and
Sneed
(1958)
Clemens and
Sneed
(1959)
Palmer and
Maloney
(1955)
Palmer and
Maloney
(1955)
I
m
O
X
Sollman
(1949)
Fitzgerald, et al
(1952)
Sollman
(1949)
-------
n
I
m
£
o
>
£
>
2
o
S
X
~^
c
3D
m
in
O
-n
O
z
m
5
Q
>
K
>
i
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r j
Chemical
Phosphoric
acid
Phosphorus
o-phthalic
anhydride
Picric
acid
Polyethylene
glycol
Polyoxy-
ethylene
ester
Potassium
azide
Potassium
azide
Potassium
chloride
Bioassay
or Field
Organism Study'1'
Gambusia BSA
affinis
Lepomis BSA
macrochirus
Pimephales BSA
prome/as
Cylindrospermum L
lichen/forme (CI)
Microcystis
aeruginosa (Mai
Scenedesmus
obliquus (So)
Chlorella
variegata (Cvl
Gomphonema
parvulum (Gp)
Nitzschia
palea INp)
Sewage BOD
microorganisms
Pimephales BSA
promelas
(juveniles)
Procambarus BSA
clarki
Lepomis
macrochirus
Pteronarcys BSA
californica
(naiads)
Carassius BSA
carassius
Toxicity,
Active
Field Ingredient,
Location (2) ppm(3)
138IT2A)
0.105(T2A)
0.053 (T3A)
0.025 (T7A)
>56 (T4A)
2.0 (0)
(0)
(S) 37-42
(T1-4A)
(H) 38-56
(T1-4A)
1 (K1)*
2 (K1)**
<1.5 (T1A)*
<1.8 (T1A)**
'Technical
formulation
**Granular
0.008 (T4A)
(0)
Experimental
Variables
Controlled
or Noted'4' Comments
a c d e g The effect of turbidity on the toxicity of the chemicals
was studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
a c d e f Colloidal phosphorus compounds were removed by filtra-
lf h i j k tion, so that the effect of elemental phosphate toxicity
n o was studied.
a c d e f o-phthalic anhydride is very slightly soluble in water.
a Observations were made on the 3rd, 7th, 14th, and 21st
~ days to give the following (T = toxic, NT = nontoxic.
PT = partially toxic with number of days in parentheses.
No number indicates observation is for entire test period
of 21 days):
CI - NT
Ma -NT
So - NT
Cv -NT
Gp-NT
Np - NT
— The chemical was studied as to how low levels (ppm) may
affect BOD in domestic sewage. This compound was not
toxic to sewage microorganisms. No concentration of the
chemical was given. Apparently this glycol is bio-
chemically inert because it did not respond even to
acclimated seed.
a c d f Syndets and soaps were of nearly equal toxicity in soft
water (S) but syndets were approximately 40X more
toxic than soap in hard water (H).
a In general, when mud was added to the tank the toxicity of
the chemical decreased.
a c d e f Data reported as LCsg at 1 5.5 C in 4 days.
a This old, lengthy paper discusses toxicity of many chemicals,
~ possible mechanism of action of some, the effect of tem-
perature, effect of dissolved oxygen, the efficiency of the
goldfish as a test animal, compares this work with earlier
work, and lists an extensive bibliography.
In O.214N solution, fish survived 60 minutes.
Reference
(Year)
Wallen, et al
(1957)
Isom
(1960)
Pickering and
Henderson
(1966)
Palmer and
Maloney
(1955)
Oberton and
Stack
(1957)
Henderson, et al
(1959)
Hughes
(1966)
Sanders and
Cope
(1968)
Powers
(1918)
>
3
TJ
m
Z
o
X
>
-------
Potassium
chloride
Potassium
chloride
Potassium
chloride
Potassium
chloride
Potassium
chloride
i—" Potassium
C5 chloride
Potassium
chloride
m Potassium
? chromate
— Potassium
H chromate
C
3)
m
O
-n
s
m
S
Daphnia
magna
Daphnia
magna
Lepomis
macrochirus
Gambusia
affinis
Biomorph olaria
a. alexandrina
Bui in us
truncatus
Daphnia
magna
Lepomis
macrochirus
Lymnaea sp
Nitzschia
linearis
Lepomis
macrochirus
Physa
heterostropha
Salmo
gairdnerii
BSA
373 (O)
BSA
BSA
BSA
BSA
BSA
BSA
BSA
Potassium
chromate
Lepomis
macrochirus
Gambusia
affinis
BCFA
BSA
432 (O)
2,010 (T4A)
4,200 (T2A)
1800 (K1A)
1200 (K1A)
679 (T1A)
5,500 (T1A)
1,941 (T1A)
1,337 (T5A)
940 (T4A)
2,010 (T4A)
(O)
2000 ppm
(42.0 min)
1000 ppm
(79 min)
20 ppm
(3580 min)
450 (T4A)
small
630 (B4A)
medium
5.50 (T4A)
large
480 (T2A)
ac This paper deals with the toxicity thresholds of various Anderson
~~ substances found in industrial wastes as determined by (1944)
the use of D. magna. Centrifuged Lake Erie water was
used as a diluent in the bioassay. Threshold concentration
was defined as the highest concentration which would just
fail to immobilize the animals under prolonged (theoretically
infinite) exposure.
a Lake Erie water was used as diluent. Toxicity given as Anderson
~~ threshold concentration producing immobilization for (1948)
exposure periods of 64 hr.
a d e f This paper reports the LD5Q in 96 hours for 8 common Trama
inorganic salts. A synthetic dilution water of controlled (1954)
hardness was prepared for use in the experiments. Among
other variables, specific conductivity, as mhos at 20 C, was
measured.
a c d e f The effect of turbidity on the toxicity of the chemicals was Wallen, et al
studied. Test water was from a farm pond with "high" (1957)
turbidity. Additional data are presented.
a The degree of tolerance for vector snails of biharziasis Gohar and
chemicals is somewhat dependent upon temperature. EI-Gindy
The temperature at which (K1A) occurred was 26 C. (1961)
a c "Standard reference water" was described and used as well Dowden and
as lake water. Varied results were obtained when evaluations Bennett
were made in various types of water. (1965)
ace The purpose of this experiment was to determine whether Patrick, et al
there was a constant relationship between the responses (1968)
of these organisms. From the data presented, there was
no apparent relationship of this type. Therefore the
authors advise that bioassays on at least 3 components of
the food web be made in any situation.
acef Tap or distilled water used as diluent. Toxicity defined as the Grindley
~~ ~ avg. time when the fish lost equilibrium when exposed to (1946)
the test chemical (ppm Cr).
acef Test water was composed of distilled water with CP grade Cairns and
chemicals and was aerated throughout the 96-hour Scheier
exposure period. (1955)
Beginning pH was 7.9 to 8.6, pH after four days was 7.0
to 7.94.
a c d e g The effect of turbidity on the toxicity on the chemicals was Wallen, et al
studied. Test water was from a farm pond with "high" (1957)
turbidity. Additional data are presented.
m
O
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CHEMICALS
2
0
S
x
H
3)
m
O
-n
0
I
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S
n
U>
>
Chemical
Potassium
chromate
Potassium
chromate
Potassium
chromate
Potassium
chromate
Potassium
chromate
Potassium
chromate
Potassium
cuprocyanide
Potassium
cyanide
(asCN)
Potassium
cyanide
Potassium
cyanide
Organism
Sewage
organisms
Micropterus
salmoides
Lepomis
macrochirus
Salmo
gairdnerii
Pimephales
promelas
Nitzschia
linearis
Physa
heterostropha
Lepomis
macrochirus
Rhinichthys
a tratul us
Rainbow
trout
(yearling)
Microcystis
aeruginosa
Rainbow
trout
(yearling)
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study'D Location(2) ppm(3) or Noted (4 >
BOD - 10.5(0)
BSA - 195 (T2A) acde
_
BSA - 550 (T4A) a c d e i
BSA - 100 (T1) acdg
BSA - (S) 45.6 (T4A) c d e f
BSA - 7.8 (T5A) ace
16.8 (T4A)
168.8 (T4A)
BCFA — 0.38, 0.47 and ace
0.71 (T1A)
BCFA - 0.14 (K-160 min) ace
L - 90 (K) a
BSA - 0.105-0.155(0) ace
Comments
Various metal salts were studied in relation to how they
affected the BOD of both raw and treated sewage as well
as how they affected the processing of sewage in the treat-
ment plant. BOD was used as the parameter to measure
the effect of the chemical. The chemical concentration
cited is the ppm required to reduce the BOD values by 50%.
This chemical was tested in an unbuffered system.
The mechanism for poisoning is discussed. Exposure to
chromium caused severe pathological change in the
intestine immediately posterior to the pyloric caeca that
in all probability completely destroyed its digestive
function.
A "control" was prepared by adding required chemicals to
distilled water, and this was constantly aerated. Data
reported are for larger fish, app 14-24 cm in length. Data
for smaller fish are also in the report.
Trout exposed to 20 ppm chromium had a mean hematocrit
of 43.8, as compared to unexposed trout of 31.8. Addi-
tional data are presented.
(S) Soft water
Values are expressed as mg/l of chromium.
The purpose of this experiment was to determine whether
there was a constant relationship between the responses of
these organisms. From the data presented, there was no
apparent relationship of this type. Therefore the authors
advise that bioassays on at least 3 components of the food
web be made in any situation.
The three values given are for cyanide to copper ratios of
4.0, 3.7, and 3.0, respectively.
Toxicity was determined in terms of survival time.
Acclimatization of fish to test conditions and fish size
was studied.
The chemical was tested on a 5-day algae culture, 1 x 10^ to
2 x 10^ cells/ml, 75 ml total volume. Chu No. 10 medium
was used.
Tap water was used as diluent. Study related oxygen con-
centration effect to cyanide toxicity. As an example.
control fish in 1.11 ppm 62 were affected in 18 min; at
0.105 ppm CN~, fish survived only 3.3 min at 10% 02
concentration.
Reference
(Year)
Sheets
(1957)
Fromm and
Schiffman
(1958)
Cairns and
Scheier
(1959)
Schiffman and
Fromm
(1959)
Pickering and
Henderson
(1965)
Patrick, et al
(1968)
Lipschuetz and
Cooper
(1955)
Herbert and
Merkens
(1952)
Fitzgerald, et al
(1952)
Downing
(1954)
-g
•o
m
g
^
-------
£
o
Potassium
cyanide
Potassium
cyanide
Potassium
cyanide
Potassium
cyanide
Potassium
cyanide
Potassium
cyanide
Potassium
cyanide
2 Potassium
m cyanide
1 (as CN")
O
O
2 Potassium
rj cyanide
C
3
m
w Potassium
O cyanide
Tl
r>
m
Salmo
gairdnerii
Rhinichthys
atratulus
meleagris
Lepomis
macrochirus
Gambusia
affinis
Lepomis
macrochirus
Lepomis
macrochirus
Physa
heterostropha
Sewage
organisms
Brachydanio
rerio
(adults)
(eggs)
Lepomis
macrochirus
Lepomis
macrochirus
Physa
heterostropha
Lepomis
macrochirus
BCFA
BCFA
BCFA
BSA
BSA
BSA
BOD
BSA
BSA
BSA
(O)
0.22 (T1A)
0.55 (T46) small a c e f
0.45 (T46) medium
0.57 (T46) large
1.6 (T2A)
0.45 (T4A)
(N) 0.45
(T4A)
(L) 0.12
(T4A)
(N) 1.08
(T4A)
(L) 0.48
(T4A)
15 (TC50)
0.49 (T2A)
117 (T2A)
0.16(T2A)
0.45 (T4A)
0.12 (T4A)
1.08(T4A)
0.48 (T4A)
0.57 (T4A)
a cd e g
a cd ef
a c d e i
Time-survival curves are plotted for seven concentrations Herbert and
of cyanide, from 0.14 to 10 ppm. At 10 ppm, all fish Downing
died in less than 3 minutes. At 0.14 ppm all fish died in (1955)
165 minutes.
This report contains a comparison of the toxicities of KCN Lipschuetz and
and potassium cuprocyanide of three different composi- Cooper
tions. Four-hour median tolerance limits are also given. (1955)
Test water was composed of distilled water with CP grade Cairns and
chemicals and was aerated throughout the 96-hour Scheier
exposure period. (1955)
The cyanide ion concentration was controlled.
The effect of turbidity on the toxicity of the chemicals was Wallen, et al
studied. Test water was from a farm pond with "high" (1957)
turbidity. Additional data are presented.
Increase in temperature seemed to increase toxicity of this Cairns
chemical. Low dissolved oxygen reduced toxicity of some (1957)
chemicals in this study. Toxicity values may be 20%
higher in hard versus soft water.
Modified Chu No. 14 test medium was used. Toxicity is given Cairns and
both for "normal" 02 (5-9 ppm), (N), and with "low" 02 Scheier
(2 ppm DO), (L). High and low threshold concentration (1958)
and concentration percent of survival are also presented.
The purpose of this paper was to devise a toxicity index for Hermann
industrial wastes. Results are recorded as the toxic con- (1959)
centration producing 50 percent inhibition (TCsfj) of
oxygen utilization as compared to controls. Five toxi-
grams depicting the effect of the chemicals on BOD were
devised and each chemical classified.
The test dilutions were made up from distilled water and Cairns, et al
ACS grade chemicals. Temperature was held at 24 C and (1965)
the solution was aerated to maintain a dissolved oxygen
content of 5-9 ppm.
Normal oxygen content in water. Cairns
Low oxygen content in water. (1965)
Normal oxygen content in water
Low oxygen content in water.
A "control" was prepared by adding required chemicals to Cairns and
distilled water, and this was constantly aerated. Data Scheier
reported are for larger fish, app 14-24 cm in length. Data (1959)
for smaller fish are also in the report.
I
m
o
-------
CHEMICALS
Z
O
S
X
H
C
33
m
en
O
-n
O
I
m
n
>
[o
•jf.
j_
O
CN
Chemical
Potassium
cyanide
Potassium
cyanide
Potassium
cyanide
Potassium
cyanide
as (CM")
Potassium
dichromate
Potassium
dichromate
Organism
Lepomis
macrochirus
Rasbora
heteromorpha
Daphnia
magna
Lymnaea sp
(eggs)
Hydropsyche
Stenonema
Daphnia
magna
Salmo
gairdnerii
Toxicity,
Bioassay Active
or Field Field Ingredient,
Studyd) Location(2) ppm<3)
BSA - 0.43 (T4A)
BSA - 0.072 (O)
BSA - 2IT1A)
0.7 (T3A)
0.4 (T4A)
796 (T1A)
147 (T3A)
130 (T4A)
BSA - 2.0 (T2A)
0.5 (T2A)
BSA - <0.6 (O)
BSA - 2000 ppm -
23.8 min
1000 ppm —
Experimental
Variables
Controlled
or Noted'4) Comments
a c d e f The experiments were conducted in a water of controlled
chemical composition.
The TLm concentration of KCN was slightly affected bv
increased temperature (more toxic at 30 C than at 18 C),
but not by water hardness.
— For many toxins the rate of mortality is found to be a linear
function of the logarithm of the concentration of the poison;
whereas the comparable relation between the logarithms of
the survival time and the concentration is nonlinear. The
linear function can be exploited to provide comparatively
simple methods of estimating long-term survival concentra-
tions. An application of this is suggested for defining
realistic standards of toxicity. At the concentration re-
ported, there was a 20 percent mortality in 7 days.
a c "Standard reference water" was described and used as well as
lake water. Varied results were obtained when evaluations
were made in various types of water.
a Soft water used as diluent water.
a c This paper deals with the toxicity thresholds of various
~~ substances found in industrial wastes as determined by
the use of D. magna. Centrifuged Lake Erie water was
used as a diluent in the bioassay. Threshold concentra-
tion was defined as the highest concentration which would
just fail to immobilize the animals under prolonged
(theoretically infinite) exposure.
a c e f Tap or distilled water used as diluent. Toxicity defined as
the avg time when the fish lost equilibrium when exposed
to the test chemical (ppm Cr).
Reference
(Year)
Cairns and
Scheier
(1963)
Abram
(1964)
Dowden and
Bennett
(1965)
Roback
(1965)
Anderson
(1944)
Grindley
(1946)
Potassium
dichromate
Potassium
dichromate
Lepomis
macrochirus
Gambusia
affinis
BCFA
BSA
54.6 min
200 ppm -
188 min
20 ppm —
4342 min
320 (T4A)
320 (T2A)
a c e f Test water was composed of distilled water with CP grade Cairns and
chemicals and was aerated throughout the 96-hour Scheier
exposure period. (1958)
The pH of the test water was about 6.2, which was determined
by the concentration of the test chemical.
ac d e g The effect of turbidity on the toxicity of the chemicals was Wallen, at al
studied. Test water was from a farm pond with "high" (1957)
turbidity. Additional data are presented.
•o
•D
m
z
D
-------
Potassium
dichromate
Potassium
dichromate
Potassium
dichromate
Potassium
dichromate
Potassium
dichromate
Potassium
dichromate
Potassium
dichromate
Potassium
dichromate
•J Potassium
m
2 dichromate
O
c
z
° Potassium
^ dichromate
C
3D
m
en
O
£
o
Lepomis
macrochirus
Lepomis
macrochirus
Lepomis
macrochirus
Lepomis
macrochirus
Sewage
organisms
Hydropsyche
Stenonema
Lepomis
macrochirus
Carassius
carassius
Daphnia
magna
Lepomis
macrochirus
Brachydanio
rerio
(adults)
(eggs)
Lepomis
macrochirus
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
BSA
BSA
BSA
BSA
BOD
BSA
BSA
BSA
BSA
BSA
320 (T4A)
(N) 320
(T4A)
(L) 320
(T4A)
320-384
(T4A)
320 (T4A)
17.0(TC50)
28.0 (T2A)
3.5 (T2A)
320(T4A)
320(T4A)
705 (T1A)
0.4 (T4A)
739 (T1A)
180(T2A)
1500 (T2A)
440 (T2A)
(S) 17.6(T4A)
(H) 27.3 (T4A)
(S) 118.0 (T4A)
(H) 133.0 (T4A)
(S) 37.5 (T4A)
(S) 30.0 (T4A)
^jc e Increase in temperature seemed to increase toxicity of this Cairns
chemical. Low dissolved oxygen reduced toxicity of some (1957)
chemicals in this study. Toxicity values may be 20% higher
in hard versus soft water.
ji£ Modified Chu No. 14 test medium was used. Toxicity is given Cairns and
~ both for "normal" 02 (5-9 ppm), (N), and with "low" O2 Scheier
(2 ppm DO), (L). High and low threshold concentration (1958)
and concentration percent of survival are also presented.
^ c d e f The concentration of <2Cr2O7 which resulted in 50 percent Cairns and
kill in 96 hours was 320 ppm in soft water at both 18 and Scheier
30 C, 382 ppm in hard water at 18 C, and 369 ppm in (1959)
hard water at 30 C.
£c cl e i A "control" was prepared by adding required chemicals to Cairns and
~~ distilled water, and this was constantly aerated. Data Scheier
reported are for larger fish, app 14-24 cm in length. Data (1959)
for smaller fish are also in the report.
£ The purpose of this paper was to devise a toxicity index for Hermann
~ industrial wastes. Results are recorded as the toxic concen- (1959)
tration producing 50 percent inhibition (TCsfj) of oxygen
utilization as compared to controls. Five toxigrams depicting
the effect of the chemicals on BOD were devised and each
chemical classified.
a Soft water used as diluent water. Roback
(1965)
a e Normal oxygen content of water. Cairns
Low oxygen content of water. (1965)
a c "Standard reference water" was described and used as well as Dowden and
lake water. Varied results were obtained when evaluations Bennett
were made in various types of water. (1965)
— -- — L The test dilutions were made up from distilled water and ACS Cairns, et al
grade chemicals. Temperature was held at 24 C and the solu- (1965)
tion was aerated to maintain a dissolved oxygen content
of 5-9 ppm.
c d e f (S) Soft water Pickering and
(H) Hard water Henderson
Values are expressed as mg/l of chromium. (1965)
m
Z
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-------
o
oo
CHEMICALS
2
D
3
X
H
33
m
in
O
Tl
O
I
m
3
£
>
)
Chemical
Potassium
dichromate
Potassium
ferricyanide
Potassium
hydroxide
Potassium
hydroxide
Potassium
nitrate
Potassium
nitrate
Potassium
nitrate
Potassium
nitrate
Potassium
nitrate
Organism
Nitzschia
linearis
Physa
heterostropha
Lepomis
macrochirus
Daphnia
magna
Gambusia
af finis
Biomorpholaria
a. alexandrina
Bulinus
truncatus
L ymnaea
caillaudi
Carassius
carassius
Gasterosteus
aculeatus
Lepomis
macrochirus
Gambusia
af finis
Biomorpholaria
a. alexandrina
Bulinus
truncatus
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study'1' Location'2) ppm'3)
BSA - 0.208 (T4A)
17.3 (T4A)
113.0 (T4A)
BSA - 905 (T1A)
549 (T2A)
0.6 (T3A)
0.1 (T4A)
BSA - 80 (T2A)
BSA - 500 (K1A)
300 (K1A)
150 (K1A)
BSA - (0)
BSA - 50IK10)
BSA - 3,000 (T4A)
BSA - 224 (T2A)
BSA - 2600 (K1 A)
1800 (K1A)
Experimental
Variables
Controlled
or Noted'4) Comments
ace The purpose of this experiment was to determine whether
there was a constant relationship between the responses
of these organisms. From the data presented, there was no
apparent relationship of this type. Therefore the authors
advise that bioassays on at least 3 components of the food
web be made in any situation.
a c "Standard reference water" was described and used as well
as lake water. Varied results were obtained when evaluations
were made in various types of water.
a c d e g The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
a The degree of tolerance for vector snails of biharziasis to
chemicals is somewhat dependent upon temperature.
The temperature at which (K1 A) occurred was 27 C.
a This old, lengthy paper discusses toxicity of many chemicals,
possible mechanism of action of some, the effect of temper-
ature, effect of dissolved oxygen, the efficiency of the
goldfish as a test animal, compares this work with earlier
work, and lists an extensive bibliography.
In 0.00002N solution, fish survived 2135 minutes.
— Solutions were made up in tap water. 3.0 to 5.0 cm stickle-
back fish were used as experimental animals. This paper
points out that there is a marked relationship between the
toxicity of the metals and their solution pressures. Those
with low solution pressures were the most toxic.
a d e f This paper reports the LD5Q in 96 hours for 8 common
inorganic salts. A synthetic dilution water of controlled
hardness was prepared for use in the experiments. Among
other variables, specific conductivity, as mhos at 20 C,
was measured.
a c d e g The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
a The degree of tolerance for vector snails of biharziasis to
chemicals is somewhat dependent upon temperature.
The temperature at which (K1 A) occurred was 28 C
for Bulinus and 25 C for Biomorpholaria.
Reference
(Year)
Patrick, et al
(1968)
Dowden and
Bennett
(1965)
Wallen, et al
(1957)
Gohar and
EI-Gindy
(1961)
Powers
(1918)
Jones
(1939)
Trama
(1954)
Wallen, et al
(1957)
Gohar and
EI-Gindy
(1961)
•o
m
Z
D
-------
Potassium
nitrate
Potassium
permangante
Potassium
permanganate
Potassium
permanganate
Potassium
permanganate
O Potassium
permanganate
s
m
C
31
m
w
o
Potassium
phosphate
Daphnia
magna
Lepomis
macrochirus
Lymnaea sp
(eggs)
Daphnia
magna
BSA
BSA
900 (T4A)
5,500 (T1A)
1,941 (T1A)
0.63 (O)
Gambusia BSA
affinis
Channel BSA
catfish
(fingerlings)
Lepomis BSA
macrochirus
Semotilus
atromaculatus
Blue-green algae L
Cylindrospermum
Anabaena
Anacystis
Calothrix
Nostoc
Oscillatoria
Plectonema
Green algae
Ankistrodesmus
Chlorella
Closterium
Oocystis
Green algae
Scenedesmus
Stigeoclonium
Zygnema
Green flagellate and
yellow algae
Chalmydomonas
Pandorina
Tribonema
Gomphonema
Navicula
Nitzchia
12 (T2A)
<3.2 (K1A)
4.2(T1,2,4A)
3.7 (T4A)
4.0-8.0 (0)
a c d e g
Gambusia
affinis
BSA
750 (T2A)
a cd e g
"Standard reference water" was described and used as well Dowden and
as lake water. Varied results were obtained when evaluations Bennett
were made in various types of water. (1965)
This paper deals with the toxicity thresholds of various Anderson
substances found in industrial wastes as determined by the (1944)
use of D. magna. Centrifuged Lake Erie water was used as
a diluent in the bioassay. Threshold concentration was
defined as the highest concentration which would just fail
to immobilize the animals under prolonged (theoretically
infinite) exposure.
The effect of turbidity on the toxicity of the chemicals was Wallen, et al
studied. Test water was from a farm pond with "high" (1957)
turbidity. Additional data are presented.
Tap water was used. Considerable additional data are Clemens and
presented. Sneed
(1959)
The values given are for a laboratory study. However, when Kemp, et al
concentrations as high as 32 ppm were applied in a pond, (1966)
no fish deaths occurred.
KMnC>4 was toxic or partially toxic at the indicated concentra- Kemp, et al
tions to blue-green and green algae. A concentration of (1966)
8.0 ppm was usually required to control green, flagellate,
and yellow algae.
1
m
O
X
The effect of turbidity on the toxicity of the chemicals was Wallen, et al
studied. Test water was from a farm pond with "high" (1957)
turbidity. Additional data are presented.
-------
CHEMICALS
>
O
2
X
H
C
JJ
m
en
O
-n
O
I
m
S
O
£j
^>
,1-
o
Chemical
Potassium
sulfate
Potassium
tellurite
Propion-
hydroxamic
acid
Propionic
acid
n-propyl
alcohol
Propylene
phenoxetol
n-propyl-N,N-
di-n-propyl
thiol-carbamate
Organism
Lepomis
macrochirus
Carassius
auratus
Microcystis
aeruginosa
Culex sp
(larvae)
Daphnia
magna
Lepomis
macrochirus
Semotilus
atromacu/atus
P/euronectes
platessa
Elodea
canadensis
Potamogeton
nodosus
Potamogeton
pectinatus
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study'1) Location'2) ppm'3) or Noted'4)
BSA - 3,550 (T4A) a d e f
BSA - (O) ac
L - 100 (K) a, etc
~
BSA - 1000(T2A) ac
50 (T2A)
188 (T1A)
BSA - 200 to 500 (CR) ae
BSA - (0) a
BSA - a
5(0)
100 (O)
5(O)
100 (O)
5 (0)
10O (O)
Comments
This paper reports the LDso in 96 hours for 8 common
inorganic salts. A synthetic dilution water of controlled
hardness was prepared for use in the experiments. Among
other variables, specific conductivity, as mhos at 20 C,
was measured.
A 0.5% solution in water prolonged the mortality of sperm
for at least 5 minutes in all samples tested. A 0.5% solution
in frog Ringer's produced similar mortility patterns but
average activity was lower after 10 minutes than in water
solution.
The chemical was tested on a 5-day algae culture, 1 x 10° to
2 x 1Q6 cells/ml, 75 ml total volume. Chu No. 10 medium
was used.
"Standard reference water" was described and used as well
as lake water. Varied results were obtained when evaluations
were made in various types of water.
Test water used was freshly aerated Detroit River water. A
typical water analysis is given. Toxicity is expressed as the
"critical range" (CR), which was defined as that concen-
tration in ppm below which the 4 test fish lived for 24 hrs.
and above which all test fish died. Additional data are
presented.
Fish were tested at 6.5 C in aquariums of 3-liter capacity. At
0.05% solution, the fish were able to survive if removed to
fresh water within 1 hour after exposure.
At 15 C and 0.005% solution, the fish took 2 hours to become
completely anesthetized and were unable to recover after
3 hours of exposure.
At 15 C and 0.025% solution, the fish were not able to sur-
vive if not removed within 1 hour. The chemical can be
used as an anesthetic for periods of up to 1 hour when a
solution of 0.01-0.025% is used.
Experiments were conducted in standing water. Results were
rated on a scale of 0 to 10, 0 standing for no toxic effect
and 10 signifying a complete kill. Evaluation was based on
visual observation of the plant response at weekly intervals
for 4 weeks.
No toxic effect.
Injury rating of 9.4.
No toxic effect.
Injury rating of 7.4
No toxic effect.
Injury rating of 8.3
Reference
(Year)
Trama
(1954)
Fribourgh
(1965)
Fitzgerald, et al
(1952)
Dowden and
Bennett
(1965)
Gillette, et al
(1952)
Bagenal
(1963)
Frank, et al
(1961)
TJ
m
z
o
-------
Pyridine
Carass/us
carassius
BSA
(O)
Pyridine
Pyridine
Pyridyl-
mercuric
acetate
Pyridyl-
mercuric
acetate
(tech.)
Pyridyl-
mercuric
acetate
(80%
active)
Pyridyl-
mercuric
acetate
O
m
5
5
o
c
j3 Pyridyl-
w mercuric
O acetate
O Pyrocatechol
m
2
O
Gambusia
affinis
Daphnia
magna
Rainbow
trout
Salmo
gairdnerii
BSA
BSA
FL
BSA
Wash.
Ictalurus
punctatus
Channel
catfish
(fingerlings)
BSA
BSA
Channel
catfish
(fingerlings)
Daphnia
magna
BSA
BSA
1,350 (T2A)
2,114(T1A)
944 (T2A)
2.0 (O)
10 (K 17%-
1 hr) 47 F
10 (K50%-
1 hr) 56 F
5 (K 1-1/2%-
1 hr) 47 F
5 (K 18%-
1 hr) 56 F
2.5 (K 0% -
1 hr) 47 F
2.5 (K 1%-
1 hr) 56 F
5.0 (K2)
3.8 (T2A)
4.12 (T2A)
2.81
0.49
2.81 (T3A)
1.81
<37
2.43 (T4A)
<37
<37
3.8 (K1A)
14 (K2)
a c d e g
a c f i
This old, lengthy paper discusses toxicity of many chemicals,
possible mechanism of action of some, the effect of temper-
ature, effect of dissolved oxygen, the efficiency of the gold-
fish as a test animal, compares this work with earlier work,
and lists an extensive bibliography.
In a concentration of 3.187 cc per liter, fish survived 180
minutes.
The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
"Standard reference water" was described and used as well
as lake water. Varied results were obtained when evaluations
were made in various types of water.
After the first treatment with the chemical the ponds were
partially emptied, flushed, and refilled. After a second
treatment, one pond showed a "catastrophic mortality".
The authors were unable to explain this unusual phenomenon.
Temp concentration data presented on groups of 200
fingerlings. Brook and Brown trout not affected by the
test cone, of 10, 5, and 2.5 ppm at either 47 F or 56 F
for 1 hr.
Powers
(1918)
The experiment was conducted at 75 C.
The toxicity of this compound increased as the temperature
was increased. In the data shown, the values for each T
level is for temperatures of 10, 16.5 and 24 centigrade.
These values were selected from a table presenting con-
centrations for T levels from one to 153 hours. Fish of
different ages were also studied.
Tap water was used. Considerable additional data are
presented.
An attempt was made to correlate the biological action with
the chemical reactivity of selected chemical substances.
Results indicated a considerable correlation between the
aquarium fish toxicity and antiautocatalytic potency of
the chemicals in marked contrast to their toxicity on
systemic administration.
Wallen, et al
(1957)
Dowden and
Bennett
(1965)
Foster and
Olson
(1951)
Rodgers, et al
(1951)
Clemens and
Sneed
(1958)
Clemens and
Sneed
(1959)
Clemens and
Sneed
(1959)
Sollman
(1949)
-------
o
g Bioassay
n or Field
P Chemical Organism Study JD
^ Pyrogallol Daphnia BSA
O magna
S
-H
C
30
m
w Quinacrine Salmo BSA
O hydro- gairdneri
— chloride Salmo
I frufra
g Salvelinus
^ fontinalis
> Salvelinus
E) namaycush
Ictalurus
punctatus
Lepomis
macrochirus
Quinine Channel BSA
sulphate catfish
(fingerlings)
J> Quinhydrone Microcystis L
>L- aeruginosa
K>
Quinone Microcystis L
aerogr//7osa
Resorcinol Daphnia BSA
majna
Salicylaldehyde Cylindrospermum L
licheniforme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (Sol
Chlcrella
variegata (Cv)
Gomphonema
parvulum (Gpl
Nitzschia
palea (Np)
Toxicity,
Active
Field Ingredient,
Location(2) ppm'3)
18 (K2)
17.2IT2A)
230 (T2A)
230 (T2A)
21.0 (T2A)
70.0 (T2A)
79.0 (T2A)
42IK1A)
100 (K)
100 (K)
56.4 (K2)
2.0 (0)
Experimental
Variables
Controlled
or Noted (4) Comments
a An attempt was made to correlate the biological action with
the chemical reactivity of selected chemical substances.
Results indicated a considerable correlation between the
aquarium fish toxicity and antiautocatalytic potency of
the chemicals in marked contrast to their toxicity on
systemic administration.
a f Variance and the 95-percent confidence interval (C.I.) were
~~ also determined.
a Tap water was used. Considerable additional data are
presented.
a, etc The chemical was tested on a 5-day algae culture, 1 x 10^ to
~~ 2 x 106 cells/ml, 75 ml total volume. Chu No. 10 medium
was used.
a, etc Comment same as above.
a An attempt was made to correlate the biological action with
the chemical reactivity of selected chemical substances.
Results indicated a considerable correlation between the
aquarium fish toxicity and antiautocatalytic potency of
the chemicals in marked contrast to their toxicity on
systemic administration.
a Observations were made on the 3rd, 7th, 14th, and 21st
~~ days to give the following (T = toxic, NT = nontoxic.
PT = partially toxic with number of days in parentheses.
No number indicates observation is for entire test period
of 21 days):
Cl - PT (3)
Ma - PT (3)
So - PT (3)
Cv - PT (3)
Gp-T(3), PT(21)
Np-T (3),PT (21)
Reference
(Year)
Sollman
(1949)
Willford
(1966)
Clemens and
Sneed
(1959)
Fitzgerald, et al
(1952)
Fitzgerald, et al
(1952)
Sollman
(1949)
Palmer and
Maloney
(1955)
TJ
•o
m
2
a
x
-------
Salicylic
acid
Selenium
Silver,
colloidal
Silver, colloidal,
(33 percent
silver nitrate)
2
O
o
2
X
c
30
m
en
Sewage
organisms
Black
bullhead
Bluegill
Channel
catfish
Large mouth
bass
Rainbow
trout
White
crappie
Yellow
walleye
Cylindrospermum
lichen/forme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Cylindrospermum
lichen/forme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
BOD
110(TC50)
FL
Sweitzer
Lake,
Colo.
2.0 (O)
2.0 (0)
The purpose of this paper was to devise a toxicity index for Hermann
industrial wastes. Results are recorded as the toxic con- (1959)
centration producing 50 percent inhibition (TCgo) of oxy-
gen utilization as compared to controls. Five toxigrams
depicting the effect of the chemicals on BOD were devised
and each chemical classified.
It was tentatively concluded on the basis of the available Barnhart
data that fish kill probably resulted from the toxic effects (1958)
of selenium, possibly acting in synergism with other ions
such as uranium or zinc. Arsenic was also found in the
lake. Samples of flora and fauna of the lake were
analyzed and found to contain greater than 300 ppm
selenium. It was believed that selenium is passed up the
food chain to the fish which accumulated the element in
lethal concentrations.
Observations were made on the 3rd, 7th, 14th, and 21st Palmer and
days to give the following (T = toxic, NT = nontoxic, Maloney
PT = partially toxic with number of days in parentheses. (1955)
No number indicates observation is for entire test period
of 21 days):
Cl - PT (3)
Ma-PT (14)
So -NT
Cv -NT
Gp-NT
Np-NT
Comment same as above except that: Palmer and
Cl - T (3) Maloney
Ma-T(3) (1955)
So - T (3)
Cv - T (3)
Gp-T(3)
Np-T(3)
I
m
O
X
O
-------
CHEMICALS
2
O
£
X
-1
C
3J
m
in
O
-n
O
m
S
O
£
to
*•
X
Chemical
Silver
Silver-
cynaide
complex
Silver
nitrate
Silver
nitrate
Silver
nitrate
Silver
sulfate
Sodium
acetate
Sodium
acetate
Sodium
acetate
Sodium
aluminate
Organism
Lebistes
reticulatus
Bufo
val/iceps
(tadpoles)
Daphnia
magna
Lepomis
macrochirus
(juveniles)
Gasterosteus
aculeatus
Daphnia
magna
Sewage
organisms
Balanus
balanoides
Polycelis
nigra
Daphnia
magna
Lepomis
macrochirus
Culex sp.
(larvae)
Gambusia
af finis
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study*1 > Location<2) ppm(3)
BSA - 0.01 (K)
0.1 (K)
0.1 (K)
BSA - (K<1.0)
BSA - 0.003 (K10)
BSA - 0.0051 (0)
BOD - 0.3 (O)
BSA - 0.4 (0)
BSA - 0.15MIL2)
BSA - <5800 (O)
BSA - 5,000 (T1 A)
7,500 (T1A)
BSA - 126IT2A)
Experimental
Variables
Controlled
or NotedW Comments
ace It is assumed in this experiment that the cations considered
are toxic because they combine with an essential sulfhydryl
group attached to a key enzyme. This treatment indicates
that the metals which form the most insoluble sulf ides
are the most toxic. The log of the concentration of the
metal ion is plotted against the log of the solubility product
constant of the metal sulfide — a treatment that does not
lend itself to tabulation. The cation toxicity cited is only
an approximate concentration interpolated from a graph.
Time of death was not specified.
a c d f p With 10 ppm as cyanide content, the median resistance
time varied from 391 to 789 minutes.
— Solutions were made up in tap water. 3.0 to 5.0 cm stickle-
back fish were used as experimental animals. This paper
points out that there is a marked relationship between the
toxicity of the metals and their solution pressures. Those
with low solution pressures were the most toxic.
a Lake Erie water was used as diluent. Toxicity given as
threshold concentration producing immobilization for
exposure periods of 64 hours.
— This is part of a report listing 27 anions and their toxicities
on a planarian. Mode of action of the anions is discussed.
Water distilled in glass was used to prepare the solutions.
The pH of this solution was 6.6. Solutions were renewed
every 12 hours.
— The concentration listed was lethal to 90% of adult
barnacles in 2 days.
c This is part of a report listing 27 anions and their toxicities
on a planarian. Mode of action of the anions is discussed.
Water distilled in glass was used to prepare the solutions.
The pH of this solution was 7.2. Solutions were renewed
every 1 2 hours.
— This assay is based on concentration of the chemical required
to immobilize the test animal. Assays were conducted in
centrifuged Lake Erie water. This salt may be toxic only
when the concentration is great enough to exert an
unfavorable osmotic effect.
a c "Standard reference water" was described and used as well
as lake water. Varied results were obtained when evaluations
were made in various types of water.
a c d e g The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
Reference
(Year)
Shaw and
Grushkin
(1967)
Doudoroff , et al
(1966)
Jones
(1939)
Anderson
(1948)
Sheets
(1957)
Clarke
(1947)
Jones
(1941)
Anderson
(1946)
Dowden and
Bennett
(1965)
Wallen, et al
(1957)
^
TJ
TJ
m
X
>
-------
O
Sodium
anthra-
quinone
alpha-
sulfonate
Sodium
anthra-
quinone-
a-sulfonate
Sodium
arsenate
Sodium
arsenate
(as AS2O3)
m
5 Sodium
5
arsenate
O
H Sodium
S= arsenate
m
CO
Sodium
— arsenate
O
Daphnia
magna
Lymnaea sp
Daphnia
magna
Polycelis
nigra
Smallmouth
black bass
Largemouth
black bass
Bluegill
sunfish
White crappie
Potomogeton
crispus
P. foliosus
Najas
flexilis
Anarchis
canadensis
Nymphea sp
Scirpus
validus
Chara sp
Hydrodictyon sp
Oedogonium sp
Cladophora sp
Daphnia
magna
BSA
BSA
BSA
FL
Leetown,
Va.
12 (T1A)
186 (T1-4A)
(O)
0.0048 M (L2)
5.0 (O)
BSA
31 (O)
Phoxinus
phoxinus
Daphnia
magna
BSA
BSA
2970 ppm
(205 min)
820 ppm
(467 min)
234 ppm
(951 min)
<20 (O)
"Standard reference water" was described and used as well
as lake water. Varied results were obtained when evaluations
were made in various types of water.
Assay water was not characterized chemically or otherwise
described. The pH at 100 percent toxicity was 7.1. The
100-hr threshold was 12%, with 0 percent toxicity at 10%
and 100 percent toxicity at 30%.
This is part of a report listing 27 anions and their toxicities
on a planarian. Mode of action of the anions is discussed.
Water distilled in glass was used to prepare the solutions.
The pH of this solution was 7.2. Solutions were renewed
every 12 hours.
Treatment of a series of ponds resulted in control of P. crispus,
P. foliosus, N. flexilis, and A. canadensis. Nymphea sp,
S. validus, and Chara sp were not controlled. Scum algae
(Hydrodictyon sp, Oedogonium sp, and Cladophera sp) in
solid mats were effectively destroyed by the arsenate.
Decomposing vegetation stimulated growth of more
desirable algae. No fish mortality occurred due to toxic
effect of chemical, but some fish suffocated due to decay-
ing vegetation.
a c This paper deals with the toxicity thresholds of various
substances found in industrial wastes as determined by the
use of D. magna. Centrifuged Lake Erie water was used
as a diluent in the bioassay. Threshold concentration was
defined as the highest concentration which would just
fail to immobilize the animals under prolonged (theoretically
infinite) exposure.
jsce_f Tap or distilled water used as diluent. Toxicity defined as
the avg time when the fish lost equilibrium when exposed
to the test chemical (ppm As).
This assay is based on concentration of the chemical required
to immobilize the test animal. Assays were conducted in
centrifuged Lake Erie water. This salt may be toxic only
when the concentration is great enough to exert an un-
favorable osmotic effect.
Dowden and
Bennett
(1965)
Freeman
(1953)
Jones
(1941)
Surber and
Everhart
(1950)
•o
m
Z
O
Anderson
(1944)
Grindley
(1946)
Anderson
(1946)
-------
n
I
m
S
o
S Chemical
in
^ Sodium
O arsenate
£
x
-i
c
33
m
w Sodium
O arsenite or
arsenious
I oxide
m
s
o
>
&
£
in
ON
Sodium
arsenite
Sodium
arsenite
Sodium
arsenite
Bioassay
or Field
Organism Study '^
Sewage BOD
organisms
Caenis sp BSA
Callibaetis sp
Libellula sp
Ischnura
verticalis
Chironomidae
Asellus
communis
Hydracarina sp
Hyalella
knickerbockeri
Colpidium sp
Paramecium sp
Stylonichia sp
Spirogyra sp
Phoxinus BSA
phoxinus
Daphnia BSA
rt?a<7/ia
Notropsis BSA
hudsonius
Toxicity, Experimental
Active Variables
Field Ingredient, Controlled
Location^) ppm (3) or Noted'4)
>100(TC50) a
3.0 (K) a
4.0 (K)
14.0 (56%
survival)
11.2 (85%
survival)
2.96 (83%
survival)
21 (81%
survival)
10.5 (94%
survival)
5.88 (30%
survival)
3.5 (100%
survival)
1.75 (plasmolysis
but no kill)
— 953 ppm a c e f
(54.6 min) ~ ~
290 ppm
(186 min)
17.8 ppm
(2174 min)
9.1 (0)
45IT1A) acde
29 (T2A)
27 (T3A)
Comments
The purpose of this paper was to devise a toxicity index for
industrial wastes. Results are recorded as the toxic con-
centration producing 50 percent inhibition (TC50) of
oxygen utilization as compared to controls. Five toxi-
grams depicting the effect of the chemicals on BOD were
devised and each chemical classified.
River water was used as test media with room temperature
and natural sunlight as environmental conditions.
Considerable additional data are presented.
Tap or distilled water used as diluent. Toxicity defined as
the avg time when the fish lost equilibrium when
exposed to the test chemical (ppm As).
This assay is based on concentration of the chemical required
to immobilize the test animal. Assays were conducted in
centrifuged Lake Erie water. This salt may be toxic only
when the concentration is great enough to exert an un-
favorable osmotic effect.
Some of the fish were not killed in 72 hours by the higher
doses of arsenic (30-35 ppm), had extensive damage to the
fins, while others had scale damage, severe diarrhea, heavy
breathing and hemorrhaging of the body areas around the
caudal, dorsal, and ventral fins.
Reference
(Year)
Hermann
(1959)
Surber and
Meeham
(1931)
Grindley
(1946)
Anderson
(1946)
Boschetti and
McLoughlin
(1957)
>
TJ
TJ
m
Z
O
X
>
-------
Sodium
arsenite
Sodium
arsenite
Sodium
arsenite
Sodium
arsenite
Pithophora sp
Hydrodictyon sp
Bottom
organisms
Lepomis
macrochirus
Microcrustacea
Rotifers
FL
Ala.
ponds
Notemigonus
crysoleucas
Pimephales
promelas
Lepomis
macrochirus
Channel
catfish
(fingerlings)
Lepomis sp
FPCH
N.Y.
BSA
FL
Ponds in
Ala.
g
^
m
S
o
£j
>
z
O
2
X
"1
3)
0)
O
Tl
0
z
m
5
Sodium
arsenite
50-51
(sodium
arsenite)
50-52
(sodium
arsenite)
Sodium
arsenite
(tech.)
Calico
fish
Water Hyssop
Parrot's Feather
Bladderwort
Water Hyssop
Parrot's Feather
Bladderwort
Rainbow
trout
Bluegill
FL
FL
FL
BSA
N.Y.
Lakes in
Fla.
Lakes in
Fla.
4.0 (O)
4.0 (O)
4.0 (O)
4.0 (S23)
4.0 (S23)
4.0 (S23)
47.9 (K1A)
(O)
(0)
(O)
(O)
(O)
(O)
(O)
(O)
26 (T4A)
30 (T4A)
— The purpose of this experiment was to determine the effec- Lawrence
tiveness of sodium arsenite as a control agent for Pithophora (1958)
and to determine the effects of repeated applications of 4
and 8 ppm arsenious oxide as sodium arsenite on bottom
organisms and fish production in treated ponds. Pithophora
was controlled by one or more applications of sodium
arsenite at a concentration of 4.0 ppm arsenious oxide. Best
results were obtained when sodium arsenite was applied while
the alga was in an active growing stage. The alga Hydrodictyon
was also controlled at 4.0 ppm. The applications of 4 ppm
applied 1 month apart reduced the number of bottom
organisms an average of 34 percent and reduced bluegill pro-
duction an average of 42 percent as compared with those of
the controlled ponds.
a c d Conventional farm ponds were used having an average surface
area of 0.3 acre and a maximum depth of 7-9 ft. Toxicity
(in ppm) to fish as maximum safe concentration (S) for
23 days was determined. Concentration of 0.5 ppm was
required to control algae.
a Tap water was used. Considerable additional data are
~~ presented.
— * Fish from ponds treated with sodium arsenite were analyzed
for arsenic when the concentration in the water had declined
to less than 1.0 ppm arsenious oxide. Bluegill sunfish
analyzed for arsenic were recovered by seining when the
arsenious oxide concentration in the pond water had
declined to less than 1.0 ppm. Arsenic in the digestive tract
of bluegills from the ponds ranged from 2.1 to 6.6 ppm
arsenious oxide (wet weight). However, no detectible
arsenic or only a trace amount was found in the tissue of
the digestive tract, liver, or muscle.
— Fish were analyzed for arsenic, before and after the lakes Ullmann
were treated with this herbicide. No differences in residues (1961)
were noted.
Eipper
(1959)
Clemens and
Sneed
(1959)
Dupree
(1960)
I
m
O
A concentration of 10.0 ppm controlled the indicated species.
Comment same as above.
This is an estimated LCsg value at temperatures from 55 to
75 F.
Phillippy
(1961)
Phillippy
(1961)
Cope
(1965)
-------
o
I
m
S
o
r Chemical
5 Sodium
O arsenite
S
X
-j
33
m
O
Tl
O
m
S
o
to Sodium
arsenite
Sodium
arsenite
3 Sodium
arsenite
Sodium
arsenite
Sodium
arsenite
Bioassay
or Field
Organism Study H)
Filamentous algae FL
Cladophora
Spirogyra
Zygnema
Submerged plants
Chara
Potamogeton
Emergent plants
Alisma
Sagittaria
Zooplankton
Pteronarcys sp BSA
(nymphs)
Salmo FL
gairdnerii
Carassius
auratus
Lepomis
macrochirus
Daphnia BSA
magna
Rainbow
trout
Bluegill
Salmo BSA
gairdneri
Lepomis
macrochirus
Pteronarcys
californicus
Daphnia
pulex
Simocephalus
serrulatus
Simocephalus BSA
serrulatus
Daphnia
pulex
Toxicity,
Active
Field Ingredient,
Location^) ppm'3)
N.Y.
4(K)
4(K)
4(K)
(0)
(0)
(0)
(0)
(0)
- 45 (T4A)
La Cross, 25 (T4A)
Wis.
34 (T4A)
35 (T4A)
6.5 (5.7-7.3)
(0)
60(0)
60 (O)
44 (O)
36.5 (T2A)
44.0 (T2A)
80.0 (T2A)
1.8 (T2A)
1.4 (T2A)
1.4 (SB)
1.8 (SB)
Experimental
Variables
Controlled
or Noted(4> Comments
a c
Complete decomposition in about 2 weeks.
Complete decomposition in about 2 weeks.
Complete decomposition in about 2 weeks.
Sodium arsenite, 4 ppm, did not cause any kill.
Sodium arsenite, 4 ppm, caused 95% kill. Decomposition
occurred in about 1 month.
Sodium arsenite, 4 ppm, caused 15% kill.
Sodium arsenite, 4 ppm, did not cause any kill.
Applications of 4 ppm sodium arsenite produced significant
reduction.
a Experiments were all conducted at 60 F in 1964. The values
were listed as LCsQ.
a c f i m The herbicide used was a commercial formulation containing
40 percent sodium arsenite by weight. Substantial residues
of arsenic were found in the water, bottom soil, and
throughout the organs and flesh of the bluegills at the
termination of the experiment. Treatments totaling
4.0 ppm or more resulted in reduced numbers of bottom
fauna, and a concentration of 1.2 ppm of the chemical
controlled rotifers.
a c d i q Toxicity, in terms of median immobilization concentration
(IC5Q), is presented for Daphnia; median lethal concen-
tration (LCgfj) values for rainbow trout and bluegill are
reported.
a This paper reports acute toxicity of a number of com-
pounds, and discusses subacute mortality as well. Effects
on reproduction and behavior are also discussed. Data
presented as £€59.
— Concentration reported is for immobilization.
Time for immobilization was 64 hr.
Data cited are for 78 F, but assays were performed at varied
temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
Reference
(Year)
Cowell
(1965)
Cope
(1965)
Gilderhus
(1966)
Crosby and
Tucker
(1966)
Cope
(1966)
Sanders and
Cope
(1966)
^
•o
m
2
2
^
-------
Sodium
arsenite
Sodium
arsenite
Sodium
arsenite
(tech.)
Sodium
azide
o
m
£
Blue-green algae
Cylindrospermum
Anabaena
Anacystis
Calothrix
Nostoc
Oscillatoria
Plectonema
Green algae
Ankistrodesmus
Chlorella
Closterium
Oocystis
Green algae
Scenedesmus
Stigeoclonium
Zygnema
Green flagellate and
yellow algae
Chalmydomonas
Pandorina
Tribonema
Gomphonema
Navicula
Nitzchia
Lepomis
macrochirus
Pteronarcys
californica
(naiads)
Procambarus
clarki
Lepomis
macrochirus
2.0 (O)
BSA
BSA
BSA
2
O
£
X
c
3)
m
CO
O
•n
g
m
S
Sodium
azide
Sodium
benzenesulfonate
Sodium
benzoate
Pteronarcys
calif ornica
(naiads)
Daphnia
magna
Daphnia
magna
BSA
BSA
BSA
0.7 (T1A)
0.038 (T4A)
1.0 (KD*
1.0 (K1)**
1.5 (T1A)*
1.8(T1A)*»
"Technical
formulation
**Granular
0.0092 (T4A)
(O)
<650 (O)
a b e
a c d e f
a cd ef
NaAsC>2 was generally nontoxic or only partially toxic
briefly for all algae species. Growth of Cylindrospermum
and Nitzchia was apparently stimulated. This compound
was the least effective of four evaluated as algicides.
Kemp, et al
(1966)
This report is a simple and straightforward determination Hughes and
of a median tolerable limit for a selected group of herbicides. Davis
(1967)
•o
m
Z
O
Data reported as LC5Q at 15.5 C in 4 days.
In general, when mud was added to the tank the toxicity of
the chemical decreased.
Data reported as (-€50 at 15.5 C in 4 days.
Assay water was not characterized chemically or otherwise
described. The pH at 100 percent toxicity was 7.1. The
100-hr threshold was 2840%, with 0 percent toxicity at
1895% and 100 percent toxicity at 8000%.
This assay is based on concentration of the chemical
required to immobilize the test animal. Assays were
conducted in centrifuged Lake Erie water. This salt
may be toxic only when the concentration is great
enough to exert an unfavorable osmotic effect.
Sanders and
Cope
(1968)
Hughes
(1966)
Sanders and
Cope
(1968)
Freeman
(1953)
Anderson
(1946)
-------
CHEMICALS
2
0
s
>J
— {
c
3D
m
en
O
-r\
O
I
m
s
o
c
CO
;>
t
K)
O
Chemical
Sodium
benzoate
Sodium
o-benzoyl
sulfimide
(soluble
saccharin)
Sodium
bicarbonate
Sodium
bicarbonate
Sodium
bicarbonate
Sodium
bicarbonate
Sodium
bicarbonate
Sodium
bicarbonate
Sodium
bicarbonate
Organism
Sewage
organisms
Sewage
organisms
Polycelis
nigra
Daphnia
magna
Daphnia
magna
Lepomis
macrochirus
Gambusia
affinis
Lepomis
macrochirus
Culex sp
(larvae)
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
StudyC" Location<2) ppm<3) or Noted<4)
BOD - (NTE)
BOD - >1000(TC5fj) a
BSA - 0.085 M(L2) c
BSA - 4200 (O) a c
BSA - 2350 (0)
BCFA - 8,250 (T4A) acef
small
8,600 (T4A)
medium
9,000 (T4A)
large
BSA - 7,550 (T2A) a c d e g
BSA - 9000 (T4A) a c d e i
BSA - 2,000 (T1 A) ac
Comments
The purpose of this paper was to devise a toxicity index for
industrial wastes. Results are recorded as the toxic con-
centration producing 50 percent inhibition (TCsfj) of
oxygen utilization as compared to controls. Five toxi-
grams depicting the effect of the chemicals on BOD were
devised and each chemical classified.
Comment same as above.
This is part of a report listing 27 anions and their toxicities
on a plananan. Mode of action of the anions is discussed.
Water distilled in glass was used to prepare the solutions.
The pH of this solution was 6.4. Solutions were renewed
every 12 hours.
This paper deals with the toxicity thresholds of various
substances found in industrial wastes as determined by the
use of D. magna. Centrifuged Lake Erie water was used as
a diluent in the bioassay. Threshold concentration was
defined as the highest concentration which would just fail
to immobilize the animals under prolonged (theoretically
infinite) exposure.
This assay is based on concentration of the chemical required
to immobilize the test animal. Assays were conducted in
centrifuged Lake Erie water. This report toxic value may
be due to an unfavorable osmotic effect.
Test water was composed of distilled water through CP
grade chemicals and was aerated throughout the
96-hour exposure period.
At pH 7, the ratio of bicarbonate to carbonate was
2270:1.
The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
A "control" was prepared by adding required chemicals to
distilled water, and this was constantly aerated. Data
reported are for larger fish, app. 14.24 cm in length. Data
for smaller fish are also in the report.
"Standard reference water" was described and used as well
as lake water. Varied results were obtained when evaluations
were made in various types of water.
Reference
(Year)
Hermann
(1959)
Hermann
(1959)
Jones
(1941)
Anderson
(1944)
Anderson
(1946)
Cairns and
Scheier
(1955)
Wallen, et al
(1957)
Cairns and
Scheier
(1959)
Dowden and
Bennett
(1965)
•o
•o
m
Z
O
-------
C
•}>
_
O
X
m
Sodium
bicarbonate
Sodium
bisulfate
Sodium
bisulfate
Sodium
bisulfate
Sodium
J> bisulfite
i—»
i—• Sodium
bisulfite
Sodium
bisulfite-
Sodium
sulfate
Sodium
2 bisulfite-
nj Sodium
— carbonate
> Sodium
bisulfite-
> Sodium
O carbonate-
2 Sodium
~ chromate
Sodium
bisulfite-
Sodium
carbonate-
Sodium
...
silicate
Sodium
bisulfite-
Sodium
silicate
Nitzschia
linearis
Lepomis
macrochirus
Daphnia
magna
Daphnia
magna
BSA
Culex sp
(larvae)
Daphnia
magna
Daphnia
magna
Daphnia
magna
Daphnia
magna
Daphnia
magna
Daphnia
magna
Daphnia
magna
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
650 (T5A)
8,600 (T4A)
190 (O)
153.4 (O)
BSA
300 (T1 A)
<145(O)
102 (O)
82 (O)
3642 (O)
850 (O)
436 (O)
87 (O)
440 (O)
0.35 (O)
38(0)
194 (O)
92 (O)
177 (O)
427 (O)
The purpose of this experiment was to determine whether
there was a constant relationship between the responses of
these organisms. From the data presented, there was no
apparent relationship of this type. Therefore the authors
advise that bioassays on at least 3 components of the food
web be made in any situation.
This assay is based on concentration of the chemical required
to immobilize the test animal. Assays were conducted in
centrifuged Lake Erie water.
Toxic effect may be a result of lowering the pH below 6.0.
The primary aim of this study was to determine the effects
of lowered dissolved oxygen concentration upon an aquatic
invertebrate when exposed to solutions of inorganic salts
known to be present in various industrial effluents.
Analysis of data conclusively shows the D. magna tested
under lowered oxygen tension exhibited lower threshold
values for the chemicals studied than when tested at
atmospheric dissolved oxygen.
"Standard reference water" was described and used as well
as lake water. Varied results were obtained when evaluations
were made in various types of water.
This assay is based on concentration of the chemical required
to immobilize the test animal. Assays were conducted in
centrifuged Lake Erie water.
Standard reference water used. Toxicity threshold is defined
as that concentration which immobilizes 50 percent in a
100-hr exposure period.
Comment same as above.
Comment same as above.
Comment same as above.
Comment same as above.
Patrick, et al
(1968)
Anderson
(1946)
Fairchild
(1955)
Comment same as above.
Dowden and
Bennett
(1965)
Anderson
(1946)
F-'reeman and
Fowler
(1953)
Freeman and
Fowler
(1953)
Freeman and
Fowler
(1953)
Freeman and
Fowler
(1953)
Freeman and
Fowler
(1953)
Freeman and
Fowler
(1953)
O
X
-------
CHEMICALS
2
0
Z
X
c
XI
m
en
O
O
I
m
£
o
c;
^
K)
NJ
Chemical
Sodium
bisulfite-
Sodium
chromate
Sodium
bisulfite-
Sodium
silicate-
Sodium
sulfate
Sodium
bisulfite-
Sodium
chromate-
Sodium
silicate
Sodium
bisulfite-
Sodium
carbonate-
Sodium
sulfate
Sodium
bisulfite-
Sodium
chromate-
Sodium
sulfate
Sodium
bisulfite
Sodium
bisulfite
Sodium
bisulfite
Organism
Daphnia
magna
Daphnia
magna
Daphnia
magna
Daphnia
magna
Daphnia
magna
Daphnia
magna
Gambusia
af finis
Daphnia
magna
(young)
Daphnia
magna
(adult)
Dugesia sp
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study!1* Location!2) ppm(3)
BSA - 70 (O)
0.286 (0)
BSA - 52 (O)
126 (O)
2308 (0)
BSA - 144(O)
0.861 (O)
506 (0)
BSA - 58 (0)
295 (0)
2562 (O)
BSA - 75 (O)
0.306 (O)
3312 (O)
BSA - 61.4(0)
BSA - 240 (T2A)
BSA - 116IT2A)
102 (T4A)
179 (T4A)
Experimental
Variables
Controlled
or Noted!4) Comments
ac Standard reference water used. Toxicity threshold is defined
as that concentration which immobilizes 50 percent in a
100-hr exposure period.
a c Comment same as above.
a c Comment same as above.
a c Comment same as above.
a c Comment same as above.
a c The primary aim of this study was to determine the effects
of lowered dissolved oxygen concentration upon an aquatic
invertebrate when exposed to solutions of inorganic salts
known to be present in various industrial effluents.
Analysis of data conclusively shows the D. magna tested
under lowered oxygen tension exhibited lower threshold
values for the chemicals studied than when tested at
atmospheric dissolved oxygen.
a c d e g The effect of turbidity on the toxicity on the chemicals
was studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
a c "Standard reference water'' was described and used as well
as lake water. Varied results were obtained when evaluations
were made in various types of water.
Reference
(Year)
Freeman and
Fowler
(1953)
Freeman
(1953)
Freeman
(1953)
Freeman
(1953)
Freeman
(1953)
Fairchild
(1955)
Wallen, et al
(1957)
Dowden and
Bennett
(1965)
m
Z
g
x
-------
Lymnaea sp
Sodium
bisulfite plus
sodium
silicate
Mollienesia
latopinna
Daphnia
magna
;>
OJ
O
s
5
£
>
0
s
X
H
3D
m
V)
O
Tl
1.
m
2
E
Sodium
bisulfite plus
sodium
carbonate
Sodium
bisulfite plus
sodium
chromate
Sodium
bisulfite plus
sodium
sulfate
Sodium
bisulfite plus
sodium
carbonate and
sodium
chromate
Sodium
bisulfite plus
sodium
chromate
and sodium
sulfate
Sodium
bisulfite
plus sodium
carbonate
and sodium
silicate
Sodium
bisulfite
plus sodium
chromate
and sodium
silicate
Sodium
bisulfite
plus sodium
carbonate
and sodium
sulfate
Daphnia
magna
Daphnia
magna
Daphnia
magna
Daphnia
magna
Daphnia
magna
Daphnia
magna
Daphnia
magna
Daphnia
magna
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
179 (T1A)
241 (T1A)
950-14,210 (T1A)
785-11,723 (T2A)
15-22 (T4A)
436(T4A)
85(T4A)
68 (T4A)
0.278 (T4A)
82 (T4A)
3,654 (T4A)
86 (T4A)
441 (T4A)
0.354 (T4A)
78 (T4A)
0.32 (T4A)
3,443 (T4A)
39 (T4A)
198 (T4A)
93 (T4A)
224 (T4A)
0.086 (T4A)
506 (T4A)
57 (T4A)
296 (T4A)
2,869 (T4A)
"Standard reference water" was described and used as well
as lake water. Varied results were obtained when evaluations
were made in various types of water.
The two TLm values are the respective concentration of each
of the chemicals listed.
Comment same as above.
Comment same as above.
Comment same as above.
Comment same as above.
Comment same as above.
Comment same as above.
Comment same as above.
Comment same as above.
Dowden and
Bennett
(1965)
Dowden and
Bennett
(1965)
Dowden and
Bennett
(1965)
Dowden and
Bennett
(1965)
Dowden and
Bennett
(1965)
Dowden and
Bennett
(1965)
Dowden and
Bennett
(1965)
Dowden and
Bennett
(1965)
Dowden and
Bennett
(1965)
I
m
O
X
-------
CHEMICALS
2
0
£
X
H
an
m
tn
O
o
X
m
Z
0
r;
i/i
>•
j
^
Chemical
Sodium
bisulfite
plus sodium
silicate and
sodium
sulfate
Sodium
borate
Sodium
borate
Sodium
borate
(ore)
Sodium
borate
Sodium
bromate
Sodium
bromate
Sodium
bromide
Sodium
bromide
Sodium
p-bromo-
benzene-
sulfonate
Organism
Daphnia
magna
Polycelis
nigra
Daphnia
magna
Salmo
gairdnerii
Gambusia
af finis
Polycelis
nigra
Daphnia
magna
Polycelis
nigra
Daphnia
magna
Daphnia
magna
Bioassay
or Field
Study (1)
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
Toxicity,
Active
Field Ingredient,
Location'2) ppm'3)
52 (T4A)
126(T4A)
2,326 (T4A)
0.026 M (L2)
<240 (O)
2800 (T1 A)
1800(T2A)
8,200 (T2A)
- 0.020 M(L2)
210(0)
0.14 M(L2)
8200 (0)
843 (K)
Experimental
Variables
Controlled
or Noted (*) Comments
a c "Standard reference water" was described and used as well
~ as lake water. Varied results were obtained when evaluations
were made in various types of water.
Each of the three TLm values represents the concentration
of each of the chemicals, respectively.
c This is part of a report listing 27 anions and their toxicities
on a planarian. Mode of action of the anions is discussed.
Water distilled in glass was used to prepare the solutions.
The pH of this solution was 6.8. Solutions were renewed
every 12 hours.
— This assay is based on concentration of the chemical required
to immobilize the test animal. Assays were conducted in
centrifuged Lake Erie water. Threshold value may be only
half of that reported.
a e Most of the weed-killer formulations in this study consisted
of more than one substance, i.e., oils, emulsifiers,
stabilizers, and other adjuvants.
a c d e g The effect of turbidity on the toxicity of the chemicals was
~ studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
c This is part of a report listing 27 anions and their toxicities
on a planarian. Mode of action of the anions is discussed.
Water distilled in glass was used to prepare the solutions.
The pH of this solution was 6.6. Solutions were renewed
every 12 hours.
— This assay is based on concentration of the chemical required
to immobilize the test animal. Assays were conducted in
centrifuged Lake Erie water.
c This is part of a report listing 27 anions and their toxicities
on a planarian. Mode of action of the anions is discussed.
Water distilled in glass was used to prepare the solutions.
The pH of this solution was 6.6. Solutions were renewed
every 12 hours.
— This assay is based on concentration of the chemical required
to immobilize the test animal. Assays were conducted in
centrifuged Lake Erie water. This salt may show toxicity
when the concentration is high enough to exert unfavorable
osmotic effect.
a c Assay water was not characterized chemically or otherwise
described. The pH at 100 percent toxicity was 6.9.
Reference
(Year)
Dowden and
Bennett
(1965)
Jones-
(1941)
Anderson
(1946)
Alabaster
(1956)
Wallen, et al
(1957)
Jones
(1941)
Anderson
(1946)
Jones
(1941)
Anderson
(1946)
Freeman
(1953)
^
TJ
m
z
D
>
-------
Sodium
p-bromo-
benzene-
sulfonate
Sodium
n-butyl-
sulfonate
Sodium
butyl
sulfonate
Sodium
butyrate
Sodium
carbonate
;>
i— Sodium
h? carbonate
O
m Sodium
S carbonate
Sodium
carbonate
c
a
Jjj Sodium
carbonate
X Sodium
2 carbonate
O
Daphnia
magna
Lepomis
macrochirus
Lymnaea sp
(eggs)
Daphnia
magna
Daphnia
magna
Lepomis
macrochirus
Daphnia
magna
BSA
BSA
BSA
BSA
BSA
Micropterus
salmoides
Lepomis
macrochirus
Goldfish
BSA
Daphnia
magna
Oncorhyncus
tshawytscha
Oncorhyncus
kisutch
Salmo
clarkii
Daphnia
magna
Lepomis
macrochirus
BSA
BSA
BSA
BCFA
523(T4A)
1,560(T1A)
2,590 (T1-4A)
7,827 (K)
8,000 (T1A)
5,400 (T3A)
2,700 (T4A)
5,000 (T1A)
424 (O)
a c
500 (O)
500 (O)
500 (O)
a c f p i
<424 (O)
68 (K5)
70 (K5)
80 (K5)
524 (O)
300 (T4A)
a d e
a c e f
"Standard reference water" was described and used as well
as lake water. Varied results were obtained when evaluations
were made in various types of water.
Assay water was not characterized chemically or otherwise
described. The pH at 100 percent toxicity was 7.1.
"Standard reference water" was described and used as well
as lake water. Varied results were obtained when evaluations
were made in various types of water.
Comment same as above.
This paper deals with the toxicity thresholds of various
substances found in industrial wastes as determined by the
use of D. magna. Centrifuged Lake Erie water was used
as a diluent in the bioassay. Threshold concentration was
defined as the highest concentration which would just fail
to immobilize the animals under prolonged (theoretically
infinite) exposure.
The disposal of cannery wastes frequently involves the use
of chemicals for treatment purposes. Ferrous sulphate,
alum, and lime are used in chemical coagulation; sodium
carbonate for acidity control in biological filters; and
sodium nitrate in lagoons for odor control. Lye (sodium
hydroxide) peeling of certain fruits and vegetables is not
uncommon. These chemicals, in whole or part, are dis-
charged in most cases to a stream. The concentrations
listed permitted largemouth bass to survive 7 to 9 hours,
bluegills to survive 4.5 to 11 hours, and goldfish to survive
indefinitely.
This assay is based on concentration of the chemical required
to immobilize the test animal. Assays were conducted in
centrifuged Lake Erie water. Toxic effect may be due in
part to the rise in pH to 9.2.
This chemical is one of a number that may be found in
Kraft mill waste effluents. Data are expressed as minimum
lethal concentration for 5 days.
Standard reference water used. Toxicity threshold is defined
as that concentration which immobilizes 50 percent in a
100-hr exposure period.
Test water was composed of distilled water with CP grade
chemicals and was aerated throughout the 96-hr
exposure period. Toxicity was essentially determined
by pH. At pH 10 the carbonate to bicarbonate ratio
was 1:2.27.
Dowden and
Bennett
(1965)
Freeman
(1953)
Dowden and
Bennett
(1965)
Dowden and
Bennett
(1965)
Anderson
(1944)
Sanborn
(1945)
Anderson
(1946)
Haydu, et al
(1952)
Freeman and
Fowler
(1953)
Cairns and
Scheier
(1955)
O
X
-------
CHEMICALS
>
0
Z
X
H
C
3D
m
C/1
O
Tl
i
i
o
>
r
C/)
>
.1.
t j
G^
Chemical
Sodium
carbonate
Sodium
carbonate
Sodium
carbonate
Sodium
carbonate
Sodium
carbonate
Sodium
carbonate-
Sodium
chromate
Sodium
carbonate
plus sodium
chromate
Sodium
carbonate-
Sodium
silicate
Organism
Daphnia
magna
Gambusia
affinis
Lepomis
macrochirus
Amphipoda
Co/ex sp
(larvae)
Daphnia
magna
Dugesia sp
Lepomis
macrochirus
Lymnaea sp.
(eggs)
Mollienesia
latopinna
Nitzschia
linearis
Lepomis
macrochirus
Daphnia
magna
Daphnia
magna
Daphnia
magna
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study<1 > Location<2) ppm(3)
BSA - 552.4 (O)
BSA - 840 (T2A)
BSA - 300 (T4A)
BSA - 360 (Tl A)
1,820 (T1A)
347 (T1A)
607 (T1A)
384 (T1A)
385 (T1 A)
403 (T1A)
405 (T2A)
BSA - 242 (T5A)
320 (T4A)
BSA - 408 (0)
0.33 (0)
BSA - 420 (T4A)
0.34 (T4A)
BSA - 180(0)
85 (O)
Experimental
Variables
Controlled
or Noted(4) Comments
a c The primary aim of this study was to determine the effects
of lowered dissolved oxygen concentration upon an aquatic
invertebrate when exposed to solutions of inorganic salts
known to be present in various industrial effluents.
Analysis of data conclusively shows the D. magna tested
under lowered oxygen tension exhibited lower threshold
values for the chemicals studied than when tested at atmo-
spheric dissolved oxygen.
a c d e g The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
a c e d i A "control" was prepared by adding required chemicals to
~~ distilled water, and this was constantly aerated. Data
reported are for larger fish, app. 14.24 cm in length. Data
for smaller fish are also in the report.
a c "Standard reference water" was described and used as well
~ as lake water. Varied results were obtained when evaluations
were made in various types of water.
ace The purpose of this experiment was to determine whether
there was a constant relationship between the responses of
these organisms. From the data presented, there was no
apparent relationship of this type. Therefore the authors
advise that bioassays on at least 3 components of the food
web be made in any situation.
a c Standard reference water used. Toxicity threshold is defined
as that concentration which immobilizes 50 percent in a
100-hr exposure period.
a c "Standard reference water" was described and used as well
~ as lake water. Varied results were obtained when evaluations
were made in various types of water. Each value represents
the concentration of each respective chemical.
a c Standard reference water used. Toxicity threshold is defined
as that concentration which immobilizes 50 percent in a
100-hr exposure period.
Reference
(Year)
Fairchild
(1955)
Wallen, et al
(1957)
Cairns and
Scheier
(1959)
Dowden and
Bennett
(1965)
Patrick, et al
(1968)
Freeman and
Fowler
(1953)
Dowden and
Bennett
(1965)
Freeman and
Fowler
(1953)
m
Z
O
-------
to
-J
Sodium
carbonate
plus sodium
silicate
Sodium
carbonate-
Sodium
sulfate
Sodium
carbonate
plus sodium
sulfate
Sodium
carbonate-
Sodium
chro mate-
Sodium
silicate
Sodium
carbonate
plus sodium
chromate
and sodium
silicate
Sodium
carbonate-
Sodium
chromate-
Sodium
sulfate
O Sodium
j^ carbonate
2 plus sodium
O chromate
p and sodium
W sulfate
Z Sodium
° carbonate-
Is Sodium
>5 silicate-
C Sodium
j*j sulfate
_ Sodium
•n carbonate
O plus sodium
m silicate and
S sodium
O sulfate
Daphnia
magna
Daphnia
magna
Daphnia
magna
Daphnia
magna
Daphnia
magna
Daphnia
magna
Daphnia
magna
Daphnia
magna
Daphnia
magna
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
265 (T1 A)
130 (T1A)
221 (O)
1,918 (O)
198 (T1A)
666(T1A)
172(T2A)
577 (T2A)
66 (T3A)
222 (T3A)
182 (O)
0.146(0)
86(0)
187(T4A)
0.15 (T4A)
88 (T4A)
240 (O)
0.192 (O)
2079 (O)
240 (T4A)
0.19 (T4A)
2,078 (T4A)
155(O)
73(0)
1343 (O)
161(T4A)
76(T4A)
1,396(T4A)
"Standard reference water" was described and used as well Dowden and
as lake water. Varied results were obtained when evaluations Bennett
were made in various types of water. Each TLm value is (1965)
equal to the concentration of each respective chemical.
Standard reference water used. Toxicity threshold is defined Freeman and
as that concentration which immobilizes 50 percent in a Fowler
100-hr exposure period. (1953)
"Standard reference water" was described and used as well Dowden and
as lake water. Varied results were obtained when evaluations Bennett
were made in various types of water. Each TLm value is (1965)
equal to the concentration of each respective chemical.
Standard reference water used. Toxicity threshold is defined Freeman and
as that concentration which immobilizes 50 percent in a Fowler
100-hr exposure period. (1953)
"Standard reference water" was described and used as well Dowden and
as lake water. Varied results were obtained when evaluations Bennett
were made in various types of water. Each TLm value (1965)
represents the concentration of each respective chemical.
Standard reference water used. Toxicity threshold is defined Freeman and
as that concentration which immobilizes 50 percent in a Fowler
100-hr exposure period. (1953)
"Standard reference water" was described and used as well Dowden and
as lake water. Varied results were obtained when evaluations Bennett
were made in various types of water. Each TLm value (1965)
represents the concentration of each respective chemical.
Standard reference water used. Toxicity threshold is defined Freeman and
as that concentration which immobilizes 50 percent in a Fowler
100-hr exposure period. (1953)
"Standard reference water" was described and used as well Dowden and
as lake water. Varied results were obtained when evaluations Bennett
were made in various types of water. Each TLm value is (1965)
equal to the concentration of each respective chemical.
m
O
-------
to
00
CHEMICALS
2
0
3
x
c
3)
m
en
O
-n
O
m
S
o
>
In
j
)
Chemical
Sodium
carboxyethyl
rosin amine
Sodium
chlorate
Sodium
chlorate
Sodium
chlorate
Sodium
chloride
Sodium
chloride
Sodium
chloride
Toxicity,
Bioassay Active
or Field Field Ingredient,
Organism Study (^ Location^) ppm'3)
Cylindrospermum L — 2.0 (O)
licheniforme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Poly eel is BSA - 0.15M(L2)
nigra
Daphnia BSA - 4240 (0)
magna
Salmo BSA - 4200 (T1 A)
gairdnerii 2750 (T2A)
Carassius BSA - (O)
carassius
Polycelis BSA - 0.19 M(L2)
nigra
Daphnia BSA - 6143(O)
magna
Experimental
Variables
Controlled
or Noted(4) Comments
a Observations were made on the 3rd, 7th, 14th, and 21st
~ days to give the following (T = toxic, NT = nontoxic.
PT = partially toxic with number of days in parentheses.
No number indicates observation is for entire test period
of 21 days):
Cl -PT(14)
Ma-PT (14)
So - NT
Cv - NT
Gp-T(3)
Np- NT
c This is part of a report listing 27 anions and their toxicities
on a planarian. Mode of action of the anions is discussed.
Water distilled in glass was used to prepare the solutions.
The pH of this solution was 6.4. Solutions were renewed
every 12 hours.
— This assay is based on concentration of the chemical required
to immobilize the test animal. Assays were conducted in
centrifuged Lake Erie water.
a e Most of the weed-killer formulations in this study consisted
~ of more than one substance, i.e., oils, emulsifiers, stabilizers.
and other adjuvants.
a This old, lengthy paper discusses toxicity of many chemicals,
~ possible mechanism of action of some, the effect of temper-
ature, effect of dissolved oxygen, the efficiency of the gold-
fish as a test animal, compares this work with earlier work.
and lists an extensive bibliography.
In 0.27N solution, the fish survived 178 minutes.
c This is part of a report listing 27 anions and their toxicities
on a planarian. Mode of action of the anions is discussed.
Water distilled in glass was used to prepare the solutions.
The pH of this solution was 7.0. Solutions were renewed
every 1 2 hours.
a c This paper deals with the toxicity thresholds of various
substances found in industrial wastes as determined by the
use of D. magna. Centrifuged Lake Erie water was used
as a diluent in the bioassay. Threshold concentration was
defined as the highest concentration which would just fail
to immobilize the animals under prolonged (theoretically
infinite) exposure.
Reference
(Year)
Palmer and
Maloney
(1955)
Jones
(1941)
Anderson
(1946)
Alabaster
(1956)
Powers
(1918)
Jones
(1941)
Anderson
(1944)
m
O
-------
Sodium
chloride
Brook
trout
BSA
(O)
Sodium
chloride
Sodium
chloride
Sodium
chloride
Sodium
chloride
I Sodium
™ chloride
1
O
C
3D
rn
c/i
Q Sodium
~n chloride
X
m
5
o
Daphnia
magna
Daphnia
magna
Lepomis
macrochirus
BSA
BSA
BSA
<4200 (O)
3,680 (S)
12,946 (T4A)
Daphnia
magna
BSA
5,093 (O)
Cylindrospermum
lichen/forme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata ICv)
Gomphonema
parvulum (Gpi
Nitzschia
palea (Np)
Biomorpholaria
a. alexandrina
Bui in us
truncatus
Lymnaea
caillaudi
2.0 (O)
BSA
4100 (K1A)
2600 (K1A)
2600 (K1 A)
Fish were fed NaCI in gelatin capsules in amounts of 5.0 to
25.0 mg. Fish averaged 5.6 grams in weight. Physical effects
of the salt were exhibited rather than true toxicity. Fish
were also immersed in NaCI solution. Immersion in a 2.5%
solution produced no increase in blood salt concentration.
A 30-minute bath in 3.0% salt or a 10-minute bath in 5.0%
salt caused a rise in blood salinity that quickly returned to
normal when the fish were placed in fresh water. A 60-
minute bath in 3.0% salt resulted in a very high blood salt
level that required 48 hours to return to normal. A
15-minute bath in a 5.0% solution resulted in the loss of
the majority of the fish.
This assay is based on concentration of the chemical required
to immobilize the test animal. Assays were conducted in
centrifuged Lake Erie water.
Lake Erie water was used as diluent. Toxicity given as
threshold concentration producing immobilization for
exposure periods of 64 hours.
Phillips
(1944)
Anderson
(1946)
Anderson
(1948)
Trama
(1954)
a d e f This paper reports the LDsg in 96 hours for 8 common
inorganic salts. A synthetic dilution water of controlled
hardness was prepared for use in the experiments. Among
other variables, specific conductivity, as mhos at 20 C,
was measured. If this salt is toxic to fish, this experiment
did not demonstrate it. A saturated solution of 2,980 ppm
produced no significant mortalities.
ac The primary aim of this study was to determine the effects Fairchild
of lowered dissolved oxygen concentration upon an aquatic (1955)
invertebrate when exposed to solutions of inorganic salts
known to be present in various industrial effluents. Analysis
of data conclusively shows the D. magna tested under lowered
oxygen tension exhibited lower threshold values for the
chemicals studied than when tested at atmospheric dissolved
oxygen.
a_ Observations were made on the 3rd, 7th, 14th, and 21st days Palmer and
to give the following (T = toxic, NT = nontoxic, PT = Maloney
partially toxic with number of days in parentheses. No (1955)
number indicates observation is for entire test period of
21 days):
Cl -NT
Ma - NT
So -NT
Cv -NT
Gp -NT
Np -NT
a The degree of tolerance for vector snails of biharziasis chem- Gohar and
icals is somewhat dependent upon temperature. The tern- EI-Gindy
perature at which (K1 A) occurred was 26 C. (1961)
m
z
a
-------
CHEMICALS
z
o
Z
X
-\
c
DO
m
C/)
O
Tl
0
I
m
S
o
•^
t/i
i**
LO
0
Chemical
Sodium
chloride
Sodium
chloride
Sodium
chloride
Sodium
chloride
Sodium
chloride
Sodium
chloride
Bioassay
or Field
Organism Study'""
Gambusia BSA
af finis
Limnodrilus BSA
hoffmeisteri
Erpobdella
punctata
Helisoma
campanulata
Gyraulus
circumstriatus
Physa
heterostropha
Sphaerium
cf. tenue
Asellus
communis
Argia sp
Hydropsyche BSA
Stenonema
Cyprinidae BSA
Asellus sp
Hydropsyche sp
Dressenia sp
Calliriche sp
Helosciadium sp
Nodiflorum sp
f/uviatilis
Lemna
trisulca
Nais spp BSA
Potamogeton BSA
pectinatus
Toxicity, Experimental
Active Variables
Field Ingredient, Controlled
Location'2) ppm'3) or Noted'4)
18,100 (T2A) acdeg
6200 (T4A) a c d i
7500 (T4A)
6150 (T4A)
3200 (T4A)
3500 (T4A)
5100 (T4A)
6200 (T4A)
1100 (T4A)
1 1 50 (T4A)
8250 (T4A)
24,000 (T4A)
9,000 (T2A) a
2,500 (T2A)
10,000 (L10A) a
1 0,000 (L7 and
K4FA)
10,000 (L6and
K17A)
10,000 (L5A)
10,000 (K13A)
(0)
1.0%(T36min) af
(0)
Comments
The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
Most of the data developed was with hard water, but experi-
ments with soft water were also conducted. Additional
TLm data are presented.
Soft water used as diluent water.
L. trisulca was not affected at 10,000 ppm.
All tests were conducted in hard water. Time given is
median survival time of the worms.
Increasing NaCI solutions produced a proportional adverse
effect on vegetative growth and seed production, but a
Reference
(Year)
Wallen, et al
(1957)
Wurtz and
Bridges
(1961)
Roback
(1965)
Vivier and
Nisbet
(1965)
Learner and
Edwards
(1963)
Teeter
(1965)
m
Z
g
x
concentration of 3000 ppm stimulated the production and
growth of tubers. 9000 ppm completely inhibited the
growth of one-week-old plants. 15,000 ppm reduced
growth completely and was fatal to many plants.
-------
Sodium
chloride
Sodium
chloride
Carassius
carassius
Culex sp
(larvae)
Daphnia
magna
Lepomis
macrochirus
Lymnaea sp
(eggs)
Mollienesia
latopinna
Nitzschia
linearis
Lepomis
macrochirus
BSA
BSA
£>
t— *
OJ
£
m
8
Jo
^
0
s
X
c
3)
m
O)
O
/•v
5
m
§
Sodium p-
chlorobenzene
sulfonate
Sodium p-
chlorobenzene
sulfonate
Sodium 2-
chlorotoluene-
4-sulfonate
Sodium 2-
chlorotoluene-
5-sulfonate
Sodium
chromate
Sodium
chromate
Sodium
chromate
Daphnia
magna
Daphnia
magna
Lepomis
macrochirus
Lymnaea sp
(eggs)
Lepomis
macrochirus
Daphnia
magna
(young)
Daphnia
magna
(adult)
Lymnaea sp
(eggs)
Mollienesia
latopinna
Polycelis
nigra
Sewage
organisms
Daphnia
magna
BSA
BSA
BSA
BSA
BSA
BOD
BSA
13,750 (T1A)
10,500 (T1A)
6,447 (T1A)
14,125 (T1A)
3,412 (T1 A)
18,735 (T1A)
2,430 (T5A)
12,940 (T4A)
3,007 (K)
2,394 (T4A)
3,219 (T1A)
8,600 (T1 A)
1,374 (T1A)
0.8 (T1A)
3.3 (T1A)
30. (T1A)
115.2 (T1A)
0.0028M (L2)
1.0(0)
<0.32 (O)
"Standard reference water" was described and used as well
as lake water. Varied results were obtained when evalua-
tions were made in various types of water.
Dowden and
Bennett
(1965)
The purpose of this experiment was to determine whether
there was a constant relationship between the responses of
these organisms. From the data presented, there was no
apparent relationship of this type. Therefore the authors
advise that bioassays on at least 3 components of the food
web be made in any situation.
Assay water was not characterized chemically or otherwise
described. The pH at 100 percent toxicity was 7.1.
"Standard reference water" was described and used as well
as lake water. Varied results were obtained when evalua-
tions were made in various types of water.
Comment same as above.
Comment same as above.
This is part of a report listing 27 anions and their toxicities
on a planarian. Mode of action of the anions is discussed.
Water distilled in glass was used to prepare the solutions.
The pH of this solution was 7.2. Solutions were renewed
every 12 hours.
"Toxicity" is expressed as 10 percent reduction in oxygen
utilization.
This assay is based on concentration of the chemical required
to immobilize the test animal. Assays were conducted in
centrifuged Lake Erie water.
Patrick, et al
(1968)
Freeman
(1953)
Dowden and
Bennett
(1956)
Dowden and
Bennett
(1965)
Dowden and
Bennett
(1965)
m
2
O
Jones
(1941)
Ingols
(1955)
Anderson
(1946)
-------
CHEMICALS
>
z
0
3
3
c
33
m
C/)
O
Tl
O
I
m
S
£
r:
1/3
>
t—t
U>
(0
Chemical
Sodium
chromate
Sodium
chromate
Sodium
chromate
Sodium
chromate
Sodium
chromate
Sodium
chromate
Sodium
chro mate-
Sodium
silicate-
Sodium
sulfate
Sodium
chro mate-
Sodium
sulfate
Sodium
chromate-
Sodium
silicate
Organism
Daphnia
magna
Sewage
organisms
Daphnia
magna
Gambusia
af finis
Escherichia
coli
Saccharomyces
ellipsoides
Nereis sp
Card n us
maenas
Leander
squilla
Daphnia
magna
Daphnia
magna
Daphnia
magna
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study'1' Location'2) ppm'3)
BSA - 0.42 (O)
BOD - (O)
BSA - 0.51 (O)
BSA - 500 (T2A)
L - (0)
BSA - 0.5 (SB 21)
1.0 (SB 21)
60.0 (T12A)
50.0 (SB 12)
5.0 (SB 35)
BSA - 0.201 (0)
119 (O)
2180 (O)
BSA - 0.276 (O)
2984 (O)
BSA - 0.159(O)
93 (O)
Experimental
Variables
Controlled
or Noted'4' Comments
a c Standard reference water used. Toxicity threshold is defined
as that concentration which immobilizes 50 percent in a
100-hr exposure period.
— A concentration of 1.0 ppm produced an oxygen depletion in
percent of the control of 90%. It required 10.0 ppm to pro-
duce 38% oxygen depletion. There is an apparent relation-
ship between toxicity of chromium and the organic matter
concentration in that higher amounts of organic matter com-
plex with the chromium thus reducing its apparent toxicity.
a c The primary aim of this study was to determine the effects of
lowered dissolved oxygen concentration upon an aquatic
invertebrate when exposed to solutions of inorganic salts
known to be present in various industrial effluents. Anal-
ysis of data conclusively shows the D. magna tested under
lowered oxygen tension exhibited lower threshold values
for the chemicals studied than when tested at atmospheric
dissolved oxygen.
a c d e g The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
— This study suggests that the chromates have an effect on
microbial genetic expression. Toxicity appeared to be in
the range of 100 to 500 mg/l.
a The threshold toxicity for shore crabs was in the range of
40 to 60 ppm for a 12-day period of exposure.
The threshold toxicity for prawns was a little less than
10 ppm in adults and 5 ppm in young.
ac Standard reference water used. Toxicity threshold is defined
as that concentration which immobilizes 50 percent in a
100-hr exposure period.
a c Comment same as above.
a c Comment same as above.
Reference
(Year)
Freeman and
Fowler
(1953)
Ingols
(1954)
Fairchild
(1955)
Wallen, et al
(1957)
Ingols and
Fetner
(1961)
Raymont and
Shields
(1964)
Freeman and
Fowler
(1953)
Freeman and
Fowler
(1953)
Freeman and
Fowler
(1953)
>
•o
•o
m
Z
O
X
>
-------
Sodium
chromate
plus sodium
silicate
Sodium
chromate
plus sodium
sulfate
Sodium
chromate
plus sodium
silicate
and sodium
sulfate
Sodium
citrate
Sodium
citrate
Sodium
cyanide
Sodium
cyanide
Sodium
cyanide
^ Sodium
OT cyanide
>
D
2
3
•{j Sodium
w cyanide
O
-n
s
OJ
Daphnia
magna
Daphnia
magna
Daphnia
magna
Polycelis
nigra
Daphnia
magna
Polycelis
nigra
Daphnia
magna
Pimephales
promelas
Sewage
organisms
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BOD
0.21 (T4A)
130IT4A)
0.28 (T4A)
3,044 (T4A)
0.28 (T4A)
122 (T4A)
2,255 (T4A)
0.015M (L2)
825 (O)
0.0006M (L2)
<3.4 (0)
0.23 (T4A)
3.6 (O)
"Standard reference water" was described and used as well
as lake water. Varied results were obtained when evalua-
tions were made in various types of water.
Each TLm value is equal to the concentration of each
respective chemical.
Comment same as above.
Comment same as above.
Lepomis
cyanellus
FL
Carbon- 1.0 (K1)
dale. III.
This is part of a report listing 27 anions and their toxicities
on a planarian. Mode of action of the anions is discussed.
Water distilled in glass was used to prepare the solutions.
The pH of this solution was 6.6. Solutions were renewed
every 12 hours.
This assay is based on concentration of the chemical required
to immobilize the test animal. Assays were conducted in
centrifuged Lake Erie water.
This is part of a report listing 27 anions and their toxicities
on a planarian. Mode of action of the anions is discussed.
Water distilled in glass was used to prepare the solutions.
The pH of this solution was 4.8. Solutions were renewed
every 12 hours.
This assay is based on concentration of the chemical required
to immobilize the test animal. Assays were conducted in
centrifuged Lake Erie water.
Synthetic soft water was used. Toxicity data given as number
of test fish surviving after exposure at 24, 48, and 96 hr.
TLm values were estimated by straight-line graphical in-
terpolation and given in ppm CN~.
Various metal salts were studied in relation to how they
affected the BOD of both raw and treated sewage as well
as how they affected the processing of sewage in the treat-
ment plant. BOD was used as the parameter to measure the
effect of the chemical. The chemical concentration cited
is the ppm required to reduce the BOD values by 50%.
This chemical was tested in an unbuffered system.
Green sunfish placed in cages in ponds 1 and 2 days after
application of the chemical suffered 100 percent mortality
at 1.0 ppm.
Toxicity seemed to be less in waters exhibiting high pH or
low temperature.
Dowden and
Bennett
(1965)
Dowden and
Bennett
(1965)
Dowden and
Bennett
(1965)
Jones
(1941)
Anderson
(1946)
Jones
(1941)
I
m
Z
D
X
Anderson
(1946)
Doudoroff, et al
(1956)
Sheets
(1957)
Bridges
(1958)
-------
CHEMICALS
>
O
S
X
H
jj
m
O
-n
O
I
m
S
o
£
>
i
oj
"^
Chemical
Sodium
cyanide
Sodium
cyanide
Sodium
cyanide
Sodium
cyanide
Sodium
cyanide
Sodium
cyanide
Sodium 2,5-
dichloro-
benzene-
sulfonate
Organism
Lepisosteus
osseus
Carassius
auratus
Cyprinus
carpio
Ictalurus
natal is
Micropterus
salmoides
Lepomis
cyanellus
Pimephales
promelas
Lepomis
macrochirus
Gasterosteus
aculeatus
Anguilla
anguilla
Phoxinus
phoxinus
Salmo
trutta
Carassius
auratus
Gammarus
pu/ex
Rana
temporaria
Green
sunfish
Daphnia
magna
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study*1) Location<2) ppm*3) or Noted*4)
BSA - 1.0(K<1) ace
BSA - (H)0.35(T4A) cdef
(S) 0.23 (T4A)
(H)0.15 (T4A)
BSA - 0.49 (K 8 hr) ace
0.49 (K 12 hr)
0.49 (K 6hr)
0.49 (K 2 hr)
4.9 (K 12 hr)
BCFA - (O) ace
BCFA - (O) ae
BSA and Okla. (O) -
FL
BSA - 3,890 (K) a c
Comments
After application of 1 ppm of the chemical to small farm
ponds, fish began to surface within 5 to 30 minutes.
At concentrations of 1 ppm and at a variety of temperature
and pH conditions, effective kills of a number of different
species of warm-water fishes were produced.
Concentrations of 1 ppm produced complete kill of all
species of fish within 8 hr.
(H) Value in hardwater.
(S) Value in softwater.
This rather long paper deals more with behavior (avoidance
reaction time, etc.) than other aspects of toxicity. However,
interpolation from several curves resulted in the concentra-
tions quoted. Avoidance occurred at concentrations as low
as 10-°N.
Temperature and pH were important factors determining the
behavior and reaction time of Gammarus during exposure
to solutions of this chemical. Most of the data were de-
scribing behavioral responses. However, in a solution of
0.00005N, the fish survived 1-1/2 hours. Gammarus were
somewhat more resistant to sodium cyanide than fish.
This report deals more with behavioral aspects than strict
toxicity. The response limit for frog tadpoles is about
0.49 ppm. Increased temperature, a higher pH, and the
amount of dissolved oxygen were critical. The response
limit for tadpoles was 0.00001 N. The tadpoles were less
sensitive than fish but more sensitive than Gammarus.
Sodium cyanide was found to be moderately effective as a
repellent at 5 mg/l and to produce an avoidance response
at 1 .0 mg/l. No response was noted at or below 0.5 mg/l.
Assay water was not characterized chemically or otherwise
described. The pH at 100 percent toxicity was 7.1.
Reference
(Year)
Bridges
(1958)
Henderson, et al
(1959)
Costa
(1965)
Costa
(1965)
Costa
(1965)
Summerfelt
and Lewis
(1967)
Freeman
(1953)
•o
m
z
o
-------
Sodium 2,5-
dichloro-
benzene
sulfonate
Sodium
dichromate
Sodium
dichromate
Sodium
dinitrophenate
Sodium
ferrocyanide
m
S
O
>
W
Sodium
fluoride
Sodium
fluoride
Sodium
fluoride
30
m
M Sodium
° fluoride
9
m Sodium
— formate
Daphnia
magna
Lepomis
macrochirus
Lymnaea sp
(eggs)
Gambusia
affinis
Daphnia
magna
Phoxinus
phoxinus
Polycelis
nigra
Sodium
ferrocyanide
Sodium
fluoride
Daphnia
magna
Polycelis
nigra
Daphnia
magna
Gambusia
affinis
Rainbow
trout
Homarus
americanus
Daphnia
magna
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
1,468 (T4A)
3,750 (T4A)
4,513 (T4A)
420 (T2A)
22 (T1A)
250 ppm
(17.7 min)
100 ppm
(61.0 min)
50 ppm
(209.0 min)
0.0008M (L2)
<600 (O)
0.0011M (L2)
504 (O)
925 (T2A)
5.9-7.5
(T2A)*
2.6-6.0
(T2A)**
*45 F
*55 F
0.9-4.5
(SB10)
<5200 (O)
"Standard reference water" was described and used as well
as lake water. Varied results were obtained when evalua-
tions were made in various types of water.
£ c d e g The effect of turbidity on the toxicity of the chemicals was
~~ studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
a_ c "Standard reference water" was described and used as well
~~ as lake water. Varied results were obtained when evalua-
tions were made in various types of water.
Tap or distilled water used as diluent. Toxicity defined as
theavg time when the fish lost equilibrium when exposed
to the test chemical (ppm dinitrophenate).
c This is part of a report listing 27 anions and their toxicities
on a planarian. Mode of action of the anions is discussed.
Water distilled in glass was used to prepare the solutions.
The pH of this solution was 6.4. Solutions were renewed
every 12 hours.
— This assay is based on concentration of the chemical required
to immobilize the test animal. Assays were conducted in
centrifuged Lake Erie water.
c This is part of a report listing 27 anions and their toxicities
on a planarian. Mode of action of the anions is discussed.
Water distilled in glass was used to prepare the solutions.
The pH of this solution was 7.2. Solutions were renewed
every 12 hours.
— This assay is based on concentration of the chemical required
to immobilize the test animal. Assays were conducted in
centrifuged Lake Erie water.
£ c d e g The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
a_ This study postulates that temperature affects the toxicity
of fluoride concentration because of its effect on the
metabolic rate of the fish. TLm values are given as
Fluoride was not toxic even at levels five times those gen-
erally used in municipal water supplies. The lobsters
employed weighed 500 grams.
This assay is based on concentration of the chemical required
to immobilize the test animal. Assays were conducted in
centrifuged Lake Erie water. Toxic effect may be a result
of unfavorable osmotic effect.
Dowden and
Bennett
(1965)
Wallen, et al
(1957)
Dowden and
Bennett
(1965)
Grindley
(1946)
Jones
(1941)
Anderson
(1946)
Jones
(1941)
Anderson
(1946)
Wallen, et al
(1957)
Anonymous
(1966)
Stewart and
Cormick
(1964)
Anderson
(1946)
m
O
X
-------
CHEMICALS
2
O
s
X
c
JO
m
en
O
-n
O
m
§
O
E)
^
J
\
Chemical
Sodium
formate
Sodium
hydrosulfide
Sodium
hydrosulfide
Sodium
hydroxide
Sodium
hydroxide
Sodium
hydroxide
Sodium
hydroxide
Sodium
hydroxide
Sodium
hydroxide
Bioassay
or Field
Organism Study (1)
Lepomis BSA
macrochirus
Gambusia BSA
at 'finis
Semotilus BSA
atromaculatus
Polycelis BSA
n/gra
Daphnia BSA
magna
Micropterus BSA
sa/moides
(large mouth
bass)
Lepomis
macrochirus
Goldfish
Daphnia BSA
magna
Oncorhyncus BSA
tshawytscha
Oncorhyncus
kisutch
Salmo clarkii
clarkii
Semotilus BSA
Atromaculatus
Toxicity,
Active
Field Ingredient,
Location (2) ppm '3)
5,000 (T1 A)
206 (T2A)
4to10(CR)
0.000004M
(L2)
240 (O)
50 (0)
50(0)
50(0)
156(0)
48 (K5)
20 (K5)
35 (K5)
20 to 40 (CR)
Experimental
Variables
Controlled
or Noted(4) Comments
a c "Standard reference water" was described and used as well
~ as lake water. Varied results were obtained when evalua-
tions were made in various types of water.
a c d e g The effect of turbidity on the toxicity of the chemicals
~ was studied. Test water was from a farm pond with
"high" turbidity. Additional data are presented.
a e Test water used was freshly aerated Detroit River water. A
typical water analysis is given. Toxicity is expressed as the
"critical range" (CR), which was defined as that concentra-
tion in ppm below which the 4 test fish lived for 24 hr and
above which all test fish died. Additional data are presented.
c This is part of a report listing 27 anions and their toxicities
on a planarian. Mode of action of the anions is discussed.
Water distilled in glass was used to prepare the solutions.
The pH of this solution was 7.8. Solutions were renewed
every 12 hours.
a c This paper deals with the toxicity thresholds of various sub-
stances found in industrial wastes as determined by the use
of D. magna. Centrifuged Lake Erie water was used as a
diluent in the bioassay. Threshold concentration was
defined as the highest concentration which would just fail
to immobilize the animals under prolonged (theoretically
infinite) exposure.
a c f p i The disposal of cannery wastes frequently involves the use of
~~ chemicals for treatment purposes. Ferrous sulphate, alum,
and lime are used in chemical coagulation; sodium carbonate
for acidity control in biological filters; and sodium nitrate in
lagoons for odor control. Lye (sodium hydroxide) peeling
of certain fruits and vegetables is not uncommon. These
chemicals, in whole or part, are discharged in most cases to
a stream. The concentrations listed permitted fish to survive
indefinitely.
— This assay is based on concentration of the chemical required
to immobilize the test animal. Assays were conducted in
centrifuged Lake Erie water. Toxic effect may be due to
the rise in pH to 9.1-9.5.
a d e This chemical is one of a number that may be found in Kraft
~ mill waste effluents. Data are expressed as minimum lethal
concentration for 5 days.
a e Test water used was freshly aerated Detroit River water. A
typical water analysis is given. Toxicity is expressed as the
"critical range" (CR), which was defined as that concentra-
tion in ppm below which the 4 test fish lived for 24 hr and
above which all test fish died. Additional data are presanted-
Reference
(Year)
Dowden and
Bennett
(1965)
Wallen, et al
(1957)
Copeland and
Woods
(1959)
Jones
(1941)
Anderson
(1944)
Sanborn
(1945)
Anderson
(1946)
Haydu, et al
(1952)
Gillette, et al
(1952)
•o
m
Z
O
-------
Sodium
hydroxide
Sodium
hydroxide
Sodium
hydroxide
Sodium
hydroxide
Sodium
hydroxide
Sodium
hydroxide
Sodium
iodate
s
m Sodium
_ iodide
Sodium
to iodide
Sodium
iodate
Sodium
metaarsenite
£
X
3D
m
ui
O
Tl
O
"i Sodium
— mono-
Lepomis
macrochirus
Lepomis
gibbosus
Lepomis
gibbosus
Gambusia
affinis
Lepomis
macrochirus
Biomorpholaria
a. alexandrina
Bulinus
truncatus
Lymnaea
caillaudi
Polycelis
nigra
Polycelis
nigra
Daphnia
magna
Daphnia
magna
Sewage
organisms
Daphnia
magna
BCFA
BSA
FL
BSA
BSA
BSA
Durham,
N. H.
BSA
BSA
BSA
BSA
BOD
(O)
5 (K 3-5 min)
5 (K 3-5 min)
125 (T2A)
9.9 (pH, T4A)
450 (K1 A)
150 (K1A)
150 (K1A)
0.0013M (L2)
0.044M (L2)
3.3 (O)
<158(0)
(NTE)
BSA
hydrogen
phosphate
1,154(T1A)
1,089 (T2A)
426 (T4A)
a c e f Test water was composed of distilled water with CP grade Cairns and
chemicals and was aerated throughout the 96-hour Scheier
exposure period. (1955)
At pH 9.8, all fish survived. At pH 9.9 to 10.1 after 4 days,
only one-half survived. At pH 10.41 to 10.50, only
10 percent survived after 3 days.
c The author suggests placing pellets of sodium hydroxide Jackson
in the nests of the sunfish when eggs or fry are present. (1956)
This method for controlling sunfish was developed first
in the laboratory in petri dishes and later conducted in
the field.
a The chemical must be applied after spawning begins and Jackson
before the fry leave the nest. The author suggests placing (1956)
pellets of sodium hydroxide in the nest of the sunfish
when eggs or fry are present.
£ c d e g The effect of turbidity on the toxicity of the chemicals Wallen, et al
~~ was studied. Test water was from a farm pond with (1957)
"high" turbidity. Additional data are presented.
a c d e i A "control" was prepared by adding required chemicals to Cairns and
distilled water, and this was constantly aerated. Data Scheier
reported are for larger fish, approximately 14.24 cm in (1959)
length. Data for smaller fish are also in the report.
a The degree of tolerance for vector snails of biharziasis to Goharand
chemicals is somewhat dependent upon temperature. EI-Gindy
The temperature at which (K1A) occurred was 27 C. (1961)
This is part of a report listing 27 anions and their toxicities Jones
on a planarian. Mode of action of the anions is discussed. (1941)
Water distilled in glass was used to prepare the solutions.
The pH of this solution was 8.0. Solutions were renewed
every 12 hours.
Comment same as above. Jones
(1941)
This assay is based on concentration of the chemical required Anderson
to immobilize the test animal. Assays were conducted in (1946)
centrifuged Lake Erie water.
Comment same as above except value may be only half of Anderson
that reported. (1946)
The purpose of this paper was to devise a toxicity index for Hermann
industrial wastes. Results are recorded as the toxic con- (1959)
centration producing 50 percent inhibition (TCsfj) of
oxygen utilization as compared to controls. Five toxi-
grams depicting the effect of the chemicals on BOD were
devised and each chemical classified.
"Standard reference water" was described and used as well Dowden and
as lake water. Varied results were obtained when evalua- Bennett
tions were made in various types of water. (1965)
m
O
X
-------
o
I
m
S
o
r~
cn
O
s
X
H
C
3)
m
o
Tl
o
i
m
S
O
£
1
Chemical
Sodium
mono-
hydrogen
phosphate
plus sodium
pyrophosphate
Sodium
napthalene
B-sulfonate
Sodium
nitrate
Sodium
nitrate
Sodium
nitrate
Sodium
nitrate
Sodium
nitrate
Sodium
nitrate
Organism
Daphnia
magna
Lymnaea sp
(eggs)
Daphnia
magna
Carassius
carassius
Gasterosteus
aculeatus
Polycelis
nigra
Daphnia
magna
Micropterus
salmoides
Lepomis
macrochirus
Goldfish
Daphnia
magna
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study'1) Location'2) ppm'3)
BSA - 3,580 (T1 A)
433 (T1A)
2,685 (T1A)
63 (T1A)
BSA - 308 (K)
BSA - (O)
BSA - 500 (K10)
BSA - 0.043M (L2)
BSA - 8,500 (0)
BSA - 4,000 (0)
2,000 (O)
2,000 (0)
BSA - 5,000 (0)
Experimental
Variables
Controlled
or Noted'4) Comments
a c "Standard reference water" was described and used as well
~~ as lake water. Varied results were obtained when evalua-
tions were made in various types of water.
Each TLm value is equal to the concentration of each re-
spective chemical.
a c Assay water was not characterizied chemically or otherwise
~~ described. The pH at 100 percent toxicity was 7.1.
a This old, lengthy paper discusses toxicity of many chemicals,
possible mechanism of action of some, the effect of tem-
perature, effect of dissolved oxygen, the efficiency of the
goldfish as a test animal, compares this work with earlier
work, and lists an extensive bibliography.
In 0.220N solution, fish survived 171 minutes.
— Solutions were made up in tap water. 3.0 to 5.0 cm stickle-
back fish were used as experimental animals. This paper
points out that there is a marked relationship between the
toxicity of the metals and their solution pressures. Those
with low solution pressures were the most toxic.
c This is part of a report listing 27 anions and their toxicities
on a planarian. Mode of action of the anions is discussed.
Water distilled in glass was used to prepare the solutions.
The pH of this solution was 7.2. Solutions were renewed
every 12 hours.
a c This paper deals with the toxicity thresholds of various sub-
stances found in industrial wastes as determined by the use
of D. magna. Centrifuged Lake Erie water was used as a
diluent in the bioassay. Threshold concentration was
defined as the highest concentration which would just fail
to immobilize the animals under prolonged (theoretically
infinite) exposure.
a c f p i The disposal of cannery wastes frequently involves the use of
chemicals for treatment purposes. Ferrous sulphate, alum.
and lime are used in chemical coagulation; sodium carbonate
for acidity control in biological filters; and sodium nitrate in
lagoons for odor control. Lye (sodium hydroxide) peeling
of certain fruits and vegetables is not uncommon. These
chemicals, in whole or part, are discharged in most cases to
a stream. The concentrations listed permitted large mouth
bass to survive indefinitely, bluegills to survive 3 days to
indefinitely, and goldfish to survive 4 days.
— This assay is based on concentration of the chemical required
to immobilize the test animal. Assays were conducted in
centrifuged Lake Erie water. Toxic effect may be caused
when the chemical concentration is high enough to exert
unfavorable osmotic effect.
Reference
(Year)
Dowden and
Bennett
(1965)
Freeman
(1953)
Powers
(1918)
Jones
(1939)
Jones
(1941)
Anderson
(1944)
Sanborn
(1945)
Anderson
(1946)
>
TJ
m
Z
D
X
>
-------
\o
Sodium
nitrate
Sodium
nitrate
Sodium
nitrate
Sodium
nitrate
Sodium
nitrite
Sodium
nitrate
Sodium
nitrate
o
m
jj Sodium
JJj nitrite
>
O
— Sodium
H nitrite
C
3)
m
CO
Lepomis
macrochirus
Lepomis
macrochirus
Gambusia
affinis
Lepomis
macrochirus
Sewage
organisms
Biomorpholaria
a. alexandrina
Bulinus
truncatus
Carassius
carassius
Daphnia
magna
Lepomis
macrochirus
Lymnaea sp
(eggs)
Polycelis
nigra
Daphnia
magna
BSA
BCFA
BSA
BSA
BOD
BSA
BSA
BSA
BSA
12,000 (T4A)
9,500 (T4A)
10,000 (T2A)
9,000 (T4A)
(NTE)
6,000 (K1A)
3,100 (K1A)
12,150 (T1A)
4,206 (T4A)
12,800 (T1A)
6,375 (T1A)
5,950 (T2A)
3,251 (T4A)
0.0006M (L2)
<20 (O)
a d e f This paper reports the LDgQ in 96 hours for 8 common
inorganic salts. A synthetic dilution water of controlled
hardness was prepared for use in the experiments. Among
other variables, specific conductivity, as mhos at 20 C, was
measured. If this salt is toxic to fish, this experiment did
not demonstrate it.
a c e f Test water was composed of distilled water with CP grade
chemicals and was aerated throughout the 96-hour
exposure period.
£ c d e g The effect of turbidity on the toxicity on the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
!L——^.l. A "control" was prepared by adding required chemicals to
distilled water, and this was constantly aerated. Data re-
ported are for larger fish, approximately 14.24 cm in
length. Data for smaller fish are also in the report.
— The purpose of this paper was to devise a toxicity index for
industrial wastes. Results are recorded as the toxic con-
centration producing 50 percent inhibition (TC5Q) of
oxygen utilization as compared to controls. Five toxi-
grams depicting the effect of the chemicals on BOD were
devised and each chemical classified.
a The degree of tolerance for vector snails of biharziasis to
chemicals is somewhat dependent upon temperature.
The temperature at which (K1 A) occurred was 28 C for
Bulinus and 26 C for Biomophalaria.
a_c "Standard reference water" was described and used as well
as lake water. Varied results were obtained when evalua-
tions were made in various types of water.
This is part of a report listing 27 anions and their toxicities
on a planarian. Mode of action of the anions is discussed.
Water distilled in glass was used to prepare the solutions.
The pH of this solution was 6.0. Solutions were renewed
every 12 hours.
This assay is based on concentration of the chemical required
to immobilize the test animal. Assays were conducted in
entrifuged Lake Erie water.
Trama
(1954)
Cairns and
Scheier
(1955)
Wallen, et al
(1957)
Cairns and
Scheier
(1959)
Hermann
(1959)
Gohar and
EI-Gindy
(1961)
Dowden and
Bennett
(1965)
m
D
Jones
(1941)
Anderson
(1946)
O
m
-------
CHEMICALS
>
O
g
X
H
C
JD
m
0
Tt
O
I
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£
O
E>
^>
J-
o
Chemical
Sodium
nitrite
Sodium
nitrite
Sodium m-
nitrobenzene
sulfonate
Sodium m-
nitrobenzene
sulfonate
Sodium 4-
nitrochloro-
benzene-2-
sulfonate
Sodium 4-
nitrochloro-
benzene-2-
sulfonate
Sodium
nitroprusside
Sodium
nitroprusside
Sodium 4-
nitrotoluene-
2-sulfonate
Sodium
oxalate
Organism
Semotilus
atromaculatus
Gambusia
af finis
Daphnia
magna
Lepomis
macrochirus
Daphnia
magna
Daphnia
magna
Lepomis
macrochirus
Lymnaea sp
(eggs)
Daphnia
magna
Polycelis
nigra
Daphnia
magna
Lepomis
macrochirus
Polycelis
nigra
Toxicity,
Bioassay Active
or Field Field Ingredient,
StudyCO Location*2* ppm<3)
BSA - 400 to 2000
(CR)
BSA - 7.5 (T2A)
BSA - 2,235 (T4A)
1,350 (T1A)
BSA - 5,61 8 (K)
BSA - 1 ,474 (T4A)
6,375 (T4A)
3,532 (T1A)
3,208 (T2A)
BSA - 3,187 (K)
BSA - 0.0008M (L2)
BSA - <210 (O)
BSA - 1,440(T1A)
BSA - 0.011m(L2)
Experimental
Variables
Controlled
or Noted (4) Comments
a e Test water used was freshly aerated Detroit River water. A
~ typical water analysis is given. Toxicity is expressed as the
"critical range" (CR), which was defined as that concentra-
tion in ppm below which the 4 test fish lived for 24 hr and
above which all test fish died. Additional data are presented.
a c d e g The effect of turbidity on the toxicity of the chemicals was
~~ studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
a c "Standard reference water'' was described and used as well
~~ as lake water. Varied results were obtained when evalua-
tions were made in various types of water.
a c Assay water was not characterized chemically or otherwise
~ described. The pH at 100 percent toxicity was 8.6.
a c "Standard reference water" was described and used as well
~~ as lake water. Varied results were obtained when evalua-
tions were made in various types of water.
a c Assay water was not characterized chemically or otherwise
described. The pH at 100 percent toxicity was 6.9.
c This is part of a report listing 27 anions and their toxicities
on a planarian. Mode of action of the anions is discussed.
Water distilled in glass was used to prepare the solutions.
The pH of this solution was 6.0. Solutions were renewed
every 12 hours.
— This assay is based on concentration of the chemical re-
quired to immobilize the test animal. Assays were con-
ducted in centrifuged Lake Erie water. Value may be
half of that reported.
a c "Standard reference water" was described and used as well
as lake water. Varied results were obtained when evalua-
tions were made in various types of water.
c This is part of a report listing 27 anions and their toxicities
on a planarian. Mode of action of the anions is discussed.
Water distilled in glass was used to prepare the solutions.
The pH of this solution was 7.2. Solutions were renewed
every 12 hours.
Reference
(Year)
Gillette, et al
(1952)
Wallen, et al
(1957)
Dowden and
Bennett
(1965)
Freeman
(1953)
Dowden and
Bennett
(1965)
Freeman
(1953)
Jones
(1941)
Anderson
(1946)
Dowden and
Bennett
(1965)
Jones
(1941)
j^
•o
m
g
x
^
-------
Sodium
oxalate
Sodium
oxalate
Sodium
oxalate
Sodium
oxalate
Sodium
pentachloro-
phenate
O
m
Q Sodium
> pentachloro-
E> phenate
> (88 percent)
O
Z
X
c
30
m
en
Daphnia BSA
magna
Gambusia BSA
affinis
Sewage BOD
organisms
Lepomis BSA
macrochirus
Erisymba BSA
buccata (EB)
Notropis
umbratilis (NU>
Pimephales
notatus (PN)
Campostoma
anomalum
Notropis
whipplii
-------
CHEMICALS
Z
D
s
X
H
33
m
O
""
O
m
2
o
•£
en
>
Chemical
Sodium
pentachloro-
phenate
Sodium
pentachloro-
phenate
Sodium
pentachloro-
phenate
Sodium
pentachloro-
phenolate
Sodium
pentachloro-
phenate
Sodium
pentachloro-
phenate
Sodium
pentachloro-
phenate
Bioassay
or Field
Organism Study 0)
Cylindrospermum L
lichen/forme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gpl
Nitzschia
palea (Np)
Lebistes BSA
reticulatus
Pimephales BSA
promelas
Channel BSA
catfish
(fingerlings)
Lebistes BSCH
reticulatus
Oncorhynchus BSA
kisutch
Tubificid BSA
worms
Toxicity,
Active
Field Ingredient,
Location^) ppm(3)
2.0 (O)
2 (K 94%-
1440 min)
4 (K 100%-
300 min)
8 (K 100%-
90 min)
15(K 100%-
40 min)
25 (K 100%-
25 min)
0.32-0.35
(T1A)
0.46 (K1A)
0.5 (44.6%
K90)
3.0 (0)
0.31 (T1A)
Experimental
Variables
Controlled
or Noted(4) Comments
a Observations were made on the 3rd, 7th, 14th, and 21st days
~~ to give the following (T = toxic, NT = nontoxic, PT =
partially toxic with number of days in parentheses. No
number indicates observation is for entire test period of
21 days):
Cl -T(3)
Ma -T (3)
So - PT (7)
Cv -NT
Gp -PT (7)
Np -T (3)
— Standard curves are developed for use in determining concen-
trations for molluscicidal use in field conditions.
a c d f Temperature and pH were studied as variables. The lower the
pH, the more toxic the chemical was to the fish. As tem-
perature was increased the toxicity rose proportionately.
a Tap water was used. Considerable additional data are
presented.
a c d e Sublethal effects found were retarded growth.
a e The value reported is obtained by a complex mathematical
treatment and is for "median resistance times" of juvenile
salmon with varying levels of salinity, temperature, and
dissolved oxygen. At 3.0 mg/l pentachlorophenate, the
maximum response (toxicity) was calculated to be 17.68%
salt concentration, 4.86 c, and 7.66 mg/l of dissolved oxygen.
a c Knop's solution was used. TLm levels for various pH's were
determined. This compound was more toxic at the lower
pH levels studied.
Reference
(Year)
Palmer and
Maloney
(1955)
Klock
(1956)
Crandall and
Goodnight
(1959)
Clemens and
Sneed
(1959)
Crandall and
Goodnight
(1962)
Alderdice
(1963)
Whitley
(1968)
^
•o
m
X
^
-------
>
L
>
O
m
1
^
Z
O
2
X
^
X
m
CO
O
•n
O
m
§
o
Sodium
pentachloro-
phenate
plus sodium
salts of other
phenols
Sodium
perborate
Sodium p-
phenol
sulfonate
Sodium p-
phenol
sulfonate
Sodium
phosphate
Sodium
phosphate
Sodium
phosphate
Sodium
picrate
Sodium
propionate
Sodium
pyrophosphate
Cylindrospermum
lichen/forme (CD
Microcystis
aeruginosa {Ma)
Scenedesmus
obliquus (Sol
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Daphnia
magna
Daphnia
magna
Daphnia
magna
Lepomis
macrochirus
Lymnaea sp
(eggs)
Polycelis
nigra
Gambusia
af finis
Daphnia
magna
Phoxinus
phoxinus
Culex sp
(larvae)
Lepomis
macrochirus
Gambusia
affinis
2.0 (O)
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
<5.2 (O)
5,623 (K)
1,471 (T4A)
19,616 (T4A)
8,828 (T4A)
0.026M (L2)
720 (T2A)
237 (T1A)
177 (T2A)
126(T3A)
2000 ppm
(192 min)
1000 ppm
(369 min)
200 ppm
(1563 min)
2,320 (T2A)
5,000 (T1A)
1,380 (T2A)
a cd e g
a c e f
a cd e g
Observations were made on the 3rd, 7th, 14th, and 21st days Palmer and
to give the following (T = toxic, NT = nontoxic, PT = Maloney
partially toxic with number of days in parentheses. No (1955)
number indicates observation is for entire test period of
21 days):
Cl -PT
Ma -PT (14), NT (21)
So -PT (14), NT (21)
Cv -NT
Gp - PT (7)
Np -T(3)
This assay is based on concentration of the chemical required Anderson
to immobilize the test animal. Assays were conducted in (1946)
centrif uged Lake Erie water.
Assay water was not characterized chemically or otherwise Freeman
described. The pH at 100 percent toxicity was 6.7. (1953)
"Standard reference water" was described and used as well Dowden and
as lake water. Varied results were obtained when evalua- Bennett
tions were made in various types of water. (1965)
This is part of a report listing 27 anions and their toxicities Jones
on a planarian. Mode of action of the anions is discussed. (1941)
Water distilled in glass was used to prepare the solutions.
The pH of this solution was 6.6. Solutions were renewed
every 12 hours.
The effect of turbidity on the toxicity of the chemicals was Wallen, et al
studied. Test water was from a farm pond with "high" (1957)
turbidity. Additional data are presented.
"Standard reference water" was described and used as well Dowden and
as lake water. Varied results were obtained when evalua- Bennett
tions were made in various types of water. (1965)
Tap or distilled water used as diluent. Toxicity defined as Grindley
the average time when the fish lost equilibrium when (1946)
exposed to the test chemical (ppm picrate).
"Standard reference water" was described and used as well Dowden and
as lake water. Varied results were obtained when evalua- Bennett
tions were made in various types of water. (1965)
The effect of turbidity on the toxicity of the chemicals Wallen, et al
was studied. Test water was from a farm pond with "high" (1957)
turbidity. Additional data are presented.
m
Z
O
G;
-------
CHEMICALS
2
0
S
3
c
m
w
O
Tl
O
I
m
S
>
&
^
5
Chemical
Sodium
pyrophosphate
Sodium
salicylate
Sodium
silicate
Sodium
silicate
Sodium
silicate
Sodium
silicate-
Sodium
sulfate
Sodium
stearate
Sodium
sulfate
Sodium
sulfate
Sodium
sulfate
Organism
Daphnia
magna
Daphnia
magna
Daphnia
magna
Gambusia
al 'finis
Amphipoda
Daphnia
magna
Lymnaea sp
(eggs)
Daphnia
magna
Pimephales
promelas
(juveniles)
Polycelis
nigra
Daphnia
magna
Daphnia
magna
Toxicity,
Bioassay Active
or Field Field Ingredient,
Studyd) Location(2) ppm.(3)
BSA - 433 (T1 A)
BSA - 1,450(O)
BSA - 2.47 (O)
BSA - 2,400 (T2A)
BSA - 895 (T1A)
263 (T2A)
160 (T4A)
247 (T4A)
630 (T1-4A)
BSA - 158(O)
2,899 (O)
BSA - (S) 200
(T1-4A)
(H) 1,800
(T1-4A)
BSA - 0.048M (L2)
BSA - 7,1 05 (O)
BSA - 5,960 (O)
Experimental
Variables
Controlled
or Noted (4) Comments
a c "Standard reference water" was described and used as well
~ as lake water. Varied results were obtained when evalua-
tions were made in various types of water.
— This assay is based on concentration of the chemical required
to immobilize the test animal. Assays were conducted in
centrifuged Lake Erie water.
a c Standard reference water used. Toxicity threshold is defined
as that concentration which immobilizes 50 percent in a
100-hr exposure period.
a c d e g The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
a c "Standard reference water" was described and used as well
~ as lake water. Varied results were obtained when evalua-
tions were made in various types of water.
a c Standard reference water used. Toxicity threshold is defined
as that concentration which immobilizes 50 percent in a
100-hr exposure period.
a c d f Syndets and soaps were of nearly equal toxicity in soft water
(S) but syndets were approximately 40X more toxic than
soap in hard water (H). Pure compound was less toxic than
packaged soap products.
c This is part of a report listing 27 anions and their toxicities
on a planarian. Mode of action of the anions is discussed.
Water distilled in glass was used to prepare the solutions.
The pH of this solution was 6.6. Solutions were renewed
every 12 hours.
a c This paper deals with the toxicity thresholds of various sub-
stances found in industrial wastes as determined by the use
of D. magna. Centrifuged Lake Erie water was used as a
diluent in the bioassay. Threshold concentration was defined
as the highest concentration which would just fail to
immobilize the animals under prolonged (theoretically
infinite) exposure.
— This assay is based on concentration of the chemical required
to immobilize the test animal. Assays were conducted in
centrifuged Lake Erie water. This salt may be innocuous
until the concentration exerts an unfavorable osmotic effect.
Reference
(Year)
Dowden and
Bennett
(1965)
Anderson
(1946)
Freeman and
Fowler
(1953)
Wallen, et al
(1957)
Dowden and
Bennett
(1965)
Freeman and
Fowler
(1953)
Henderson, et al
(1959)
Jones
(1941)
Anderson
(1944)
Anderson
(1946)
j,
^
m
z
O
X
•p
-------
Sodium
sulphate
Sodium
sulfate
Sodium
sulfate
Sodium
sulfate
Sodium
sulfate
Sodium
sulfate
Sodium
sulfate
O
nj Sodium
— sulphate
>
O
? Sodium
JJ sulfate
C
3)
m
c/>
Oncorhyncus
kisutch
Sal mo clarkii
clarkii
Lepomis
macrochirus
Lepomis
macrochirus
Daphnia
magna
BSA
BSA
BCFA
BSA
Gambusia
affinis
Lepomis
macrochirus
Pimephales
promelas
(juveniles)
Biomorpholaria
a. alexandrina
Bui in us
truncatus
Lymnaea
caillaudi
Hydro psychidae
Stenonema
ares
S. heterotarsale
BSA
BSA
BSA
BSA
BCFA
16,500 (K5A)
6,700 (K5A)
13,500 (T4A)
12,500 (T4A)
5,514 (O)
17,500 (T2A)
12,500 (T4A)
(S) 9,000-
13,000
(T1-4A)
(H) 13,500-
14,000
(T1-4A)
4,800 (K1 A)
900(K1A)
1,000 (K1A)
320
(K 15%-4da)
320
(K50%-4da)
320
(K30%-4da)
^d e This chemical is one of a number that may be found in Kraft
~~ mill waste effluents. Data are expressed as minimum lethal
concentration for 5 days.
a d e f This paper reports the \-D$Q in 96 hours for 8 common
inorganic salts. A synthetic dilution water of controlled
hardness was prepared for use in the experiments. Among
other variables, specific conductivity, as mhos at 20 C, was
measured.
a c e f Test water was composed of distilled water with CP grade
chemicals and was aerated.
a c The primary aim of this study was to determine the effects
of lowered dissolved oxygen concentration upon an aquatic
invertebrate when exposed to solutions of inorganic salts
known to be present in various industrial effluents. Analysis
of data conclusively shows the D. magna tested under
lowered oxygen tension exhibited lower threshold values
for the chemicals studied than when tested at atmospheric
dissolved oxygen.
£ c d e g The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
a c d e i A "control" was prepared by adding required chemicals to
distilled water, and this was constantly aerated. Data
reported are for larger fish, approximately 14.24 cm in
length. Data for smaller fish are also in the report.
a c d f Syndets and soaps were of nearly equal toxicity in soft water
(S) but syndets were approximately 40X more toxic than
soap in hard water (H). The surfactant rather than the
builder contained the toxicant.
The degree of tolerance for vector snails of biharziasis to
chemicals is somewhat dependent upon temperature. The
temperatures at which (K1 A) occurred was 27 C for Bulinus
and Lymnaea and 26 C for Biomorpholaria.
a c d e Soft water used as diluent. Additional data are presented.
Haydu, et al
(1952)
Trama
(1954)
Cairns and
Scheier
(1955)
Fairchild
(1955)
Wallen, et al
(1957)
Cairns and
Scheier
(1959)
Henderson, et al
(1960)
Gohar and
EI-Gindy
(1961)
Surber and
Thatcher
(1963)
I
m
D
o
m
§
o
-------
ON
CHEMICALS
>
O
s
X
-1
c
3)
m
in
0
TJ
O
m
S
o
Ci
^
Chemical
Sodium
sulfate
Sodium
sulfate
Sodium
sulfhydrate
Sodium
sulfide
Sodium
sulfide
Sodium
sulphide
Sodium
sulfide
Bioassay
or Field
Organism Study (D
Amphipoda BSA
Culex sp
(larvae)
Daphnia
magna (adult)
Daphnia
magna (young)
Lepomis
macrochirus
Lymnaea sp
(eggs)
Mollienesia
latopinna
Nitzschia BSA
linearis
Lepomis
macrochirus
Oncorhyncus BSA
tshawytscha
Oncorhyncus
kisutch
Salmo clarkii
clarkii
Daphnia BSA
magna
Gasterosteus BSA
aculeatus
Oncorhyncus BSA
tshawytscha
Oncorhyncus
kisutch
Salmo clarkii
clarkii
Gambusia BSA
a f fin is
Toxicity,
Active
Field Ingredient,
Location(2) ppm<3)
- 2,380 (T1A)
1,110 (T2A)
880 (T4A)
11,430 (T1A)
4,547 (T4A)
6,800 (T1A)
17,500 (T1A)
5,401 (T1A)
3,553 (T4A)
20,000 (T1A)
15,996 (T2A)
1,900(T5A)
1 3,500 (T4A)
3.3 (K5)
3.5 (K5)
1.8IK5)
9.4 (O)
(0)
3.5 (K5)
3.1 (K5)
3.0 (K5)
750 (T2A)
Experimental
Variables
Controlled
or Noted(4) Comments
a c "Standard reference water" was described and used as well
~ as lake water. Varied results were obtained when evalua-
tions were made in various types of water.
ace The purpose of this experiment was to determine whether
there was a constant relationship between the responses
of these organisms. From the data presented, there was
no apparent relationship of this type. Therefore the authors
advise that bioassays on at least 3 components of the food
web be made in any situation.
a d e This chemical is one of a number that may be found in Kraft
mill waste effluents. Data are expressed as minimum lethal
concentration for 5 days.
— This assay is based on concentration of the chemical required
to immobilize the test animal. Assays were conducted in
centrifuged Lake Erie water.
c e Tap water was used to make up the solutions, which made up
a pH of 6.8 with sulfuric acid. At a concentration of
0.0007N, the fish displayed much distress. At 0.00008N,
the animal showed very little reaction. The test animal
survived 72 hours in a solution of 0.0003N.
a d e This chemical is one of a number that may be found in Kraft
mill waste effluents. Data are expressed as minimum lethal
concentration for 5 days.
a c d e g The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
Reference
(Year)
Dowden and
Bennett
(1965)
Patrick, et al
(1968)
Haydu, et al
(1952)
Anderson
(1946)
Jones
(1948)
Haydu, et al
(1952)
Wallen, et al
(1957)
>
T)
m
_
X
>
-------
Sodium
sulfide
Rasbora
heteromorpha
BSA
3.0 (O)
O
c
30
m
w
O
m
Sodium
sulfide
Sodium
sulfite
Sodium
sulfite
Sodium
sulfite
Sodium
sulfite
Sodium
O sulfite
— Sodium
5 tartrate
Sodium
tartrate
Sodium
thiocyanate
Sodium
thiocyanate
Daphnia
magna
Polycelis
nigra
Daphnia
magna
Daphnia
magna
Gambusia
affinis
Daphnia
magna
Polycelis
nigra
Daphnia
magna
Polycelis
nigra
Daphnia
magna
BSA
BSA
BSA
16 (T1A)
13 (T2A)
9 (T4A)
0.048M (L2)
3,784 (O)
BSA
BSA
BSA
BSA
BSA
BSA
BSA
440 (O)
2,600 (T2A)
299 (T1A)
273 (T2A)
203 (T4A)
0.065M (L2)
<3,500 (O)
0.012M (L2)
a c d e g
For many toxins the rate of mortality is found to be a linear Abram
function of the logarithm of the concentration of the (1964)
poison; whereas the comparable relation between the
logarithms of the survival time and the concentration is
nonlinear. The linear function can be exploited to provide
comparatively simple methods of estimating long-term
survival concentrations. An application of this is suggested
for defining realistic standards of toxicity. At the concen-
tration listed for the chemical, the mean survival time was
was 173 minutes.
"Standard reference water" was described and used as well Dowden and
as lake water. Varied results were obtained when evalua- Bennett
tions were made in various types of water. (1965)
This is part of a report listing 27 anions and their toxicities Jones
on a planarian. Mode of action of the anions is discussed. (1941)
Water distilled in glass was used to prepare the solutions.
The pH of this solution was 6.8. Solutions were renewed
every 12 hours.
This paper deals with the toxicity thresholds of various sub- Anderson
stances found in industrial wastes as determined by the use (1944)
of D. magna. Centrifuged Lake Erie water was used as a
diluent in the bioassay. Threshold concentration was
defined as the highest concentration which would just fail
to immobilize the animals under prolonged (theoretically
infinite) exposure.
This assay is based on concentration of the chemical required Anderson
to immobilize the test animal. Assays.were conducted in (1946)
centrifuged Lake Erie water.
The effect of turbidity on the toxicity of the chemicals was Wallen, et al
studied. Test water was from a farm pond with "high" (1957)
turbidity. Additional data are presented.
"Standard reference water" was described and used as well Dowden and
as lake water. Varied results were obtained when evalua- Bennett
tions were made in various types of water. (1965)
This is part of a report listing 27 anions and their toxicities Jones
on a planarian. Mode of action of the anions is discussed. (1941)
Water distilled in glass was used to prepare the solutions.
The pH of this solution was 7.4 Solutions were renewed
every 12 hours.
This assay is based on concentration of the chemical required Anderson
to immobilize the test animal. Assays were conducted in (1946)
centrifuged Lake Erie water.
This is part of a report listing 27 anions and their toxicities Jones
on a planarian. Mode of action of the anions is discussed. (1941)
Water distilled in glass was used to prepare the solutions.
The pH of this solution was 9.6. Solutions were renewed
every 12 hours.
This assay is based on concentration of the chemical required Anderson
to immobilize the test animal. Assays were conducted in (1946)
centrifuged Lake Erie water.
z
O
X
-------
CHEMICALS
z
0
S
X
H
C
3)
m
tn
O
O
I
m
S
O
Cj
i
^
00
Chemical
Sodium
thiosulfate
Sodium
thiosulfate
Sodium
thiosulfate
Sodium
thiosulfate
Sodium
dibasic
phosphate
Sodium
tribasic
phosphate
Sodium
triphosphate
Sodium
tripoly-
phosphate
Sodium
valerate
Stannic
chloride
Stannous
chloride
Strontium
chloride
Organism
Polycelis
nigra
Daphnia
magna
Gambusia
af finis
Daphnia
magna
Daphnia
magna
Daphnia
magna
Gambusia
affinis
Pimephales
promelas
(juveniles)
Lepomis
macrochirus
Daphnia
magna
Daphnia
magna
Carassius
carassius
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study'1 ) Location*2) ppm<3)
BSA - 0.053M (L2)
BSA - <520 (0)
BSA - 26,000 (T2A)
BSA - 2,245 (T1 A)
1,223 (T2A)
805 (T4A)
BSA - <59 (O)
BSA - <52 (O)
BSA - 467 (T2A)
BSA - (S) 400
(T1-4A)
(H) 1,300-
1,350
(T1-4A)
BSA - 5,000 (T1A)
BSA - 146 (O)
BSA - <25 (0)
BSA - (O)
Experimental
Variables
Controlled
or Noted*4) Comments
c This is part of a report listing 27 anions and their toxicities
on a planarian. Mode of action of the anions is discussed.
Water distilled in glass was used to prepare the solutions.
The pH of this solution was 6.4. Solutions were renewed
every 12 hours.
— This assay is based on concentration of the chemical required
to immobilize the test animal. Assays were conducted in
centrifuged Lake Erie water. Value may be only half of
that reported.
a c d e g The effect of turbidity on the toxicity of the chemicals was
~ studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
a c "Standard reference water" was described and used as well
as lake water. Varied results were obtained when evalua-
tions were made in various types of water.
— This assay is based on concentration of the chemical required
to immobilize the test animal. Assays were conducted in
centrifuged Lake Erie water. Value may be only half of
that reported.
— Comment same as above.
Toxic effect may be the result of the precipitate formed
which may obstruct the straining mechanism of the Daphnia.
a c d e g The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
a c d f Syndets and soaps were of nearly equal toxicity in soft
water (S) but syndets were approximately 40X more toxic
than soap in hard ware (H). The surfactant rather than the
builder contained the toxicant. Additional data are given.
a c "Standard reference water" was described and used as well
as lake water. Varied results were obtained when evalua-
tions were made in various types of water.
a Lake Erie water was used as diluent. Toxicity given as
threshold concentration producing immobilization for
exposure periods of 64 hours.
a Comment same as above.
a This old, lengthy paper discusses toxicity of many chemicals.
possible mechanism of action of some, the effect of tem-
perature, effect of dissolved oxygen, the efficiency of the
goldfish as a test animal, compares this work with earlier
work, and lists an extensive bibliography.
In O.237N solution, fish survived 168 minutes.
Reference
(Year)
Jones
(1941)
Anderson
(1946)
Wallen, et al
(1957)
Dowden and
Bennett
(1965)
Anderson
(1946)
Anderson
(1946)
Wallen, et al
(1957)
Henderson, et al
(1959)
Dowden and
Bennett
(1965)
Anderson
(1948)
Anderson
(1948)
Powers
(1918)
=5
•o
rn
Z
O
X
J,
-------
Strontium
chloride
Strontium
nitrate
Strontium
nitrate
Styrene
>> 4-styryl-
^ pyridine
VO
Sulfide
Sulfoxide
X
m
§
> Sulfur
Sulfur
(colloidal)
O
5
X Sulfur,
C lime
33
m
CO
O
m
2
Daphnia
magna
Carassius
carassius
Gasterosteus
aculeatus
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Petromyzon
marinus
(larvae)
Polycelis
nigra
Pimephales
promelas
Gambusia
affinis
Carassius
carassius
Simocephalus
serrulatus
Daphnia
pu/ex
BSA
BSA
114(0)
(O)
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
0.2 (K10)
51 (T4A)
22 (T4A)
68 (T4A)
68 (T4A)
10 (NTE)
0.00045M (L2)
0.74 (T4A)
10,000 (T2A)
(O)
11.0 (SB)
10.0 (SB)
a c d e f
a cd f g
a cd e g
Lake Erie water was used as diluent. Toxicity given as
threshold concentration producing immobilization for
exposure periods of 64 hours.
This old, lengthy paper discusses toxicity of many chemicals,
possible mechanism of action of some, the effect of tem-
perature, effect of dissolved oxygen, the efficiency of the
goldfish as a test animal, compares this work with earlier
work, and lists an extensive bibliography.
In 0.165N solution, fish survived 300 minutes.
Solutions were made up in tap water. 3.0 to 5.0-cm stickle-
back fish were used as experimental animals. This paper
points out that there is a marked relationship between the
toxicity of the metals and their solution pressures. Those
with low solution pressures were the most toxic.
Most fish survived at test concentrations of about one half,
or slightly more, of the TLm value. No attempt was made
to estimate 100 percent survival.
Additional data are presented.
This is part of a report listing 27 anions and their toxicities
on a planarian. Mode of action of the anions is discussed.
Water distilled in glass was used to prepare the solutions.
The pH of this solution was 6.6. Solutions were renewed
every 12 hours.
Test water was spring water diluted with distilled water.
Removal of toxic chemicals by carbon adsorption, chlorine
and chlorine dioxide treatment, and alum coagulation was
studied. The most effective method to remove fish poisons
was by use of activated charcoal adsorption.
The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
Sulfur concentrations were toxic from 0.016 to 0.210 per-
cent. Survival time is reported in minutes, from 45 to 315.
Concentration reported is for immobilization.
Time for immobilization was 48 hours.
Data cited are for 60 F, but assays were performed at
varied temperatures. "Water Chemistry" (unspecified)
was "controlled" during the assay period.
Anderson
(1948)
Powers
(1918)
Jones
(1939)
Pickering and
Henderson
(1966)
Piavis
(1962)
Jones
(1941)
Cohen, et al
(1961)
Wallen, et al
Harukawa
(1922-23)
Sanders and
Cope
(1966)
m
O
-------
CHEMICALS
2
D
S
X
H
3J
m
O
0
I
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Chemical
Sulfuric
acid
Sulfuric
acid
Sulfuric
acid
Tannic
acid
Tannic
acid
Tannic
acid
Tartaric
acid
Toxicity,
Bioassay Active
or Field Field Ingredient,
Organism Study!"1) Location(2) ppm(3)
Daphnia BSA - 88 (O)
magna
Gambusia BSA - 42 (T2A)
af finis
Sewage BOD - 58 (TCsg)
organisms
Daphnia BSA - <26 (0)
magna
Gambusia BSA - 41 (T2A)
affinis
Sewage BOD - (NTE)
organisms
Daphnia BSA - 135 (0)
magna
Experimental
Variables
Controlled
or Noted!4) Comments
a c This paper deals with the toxicity thresholds of various sub-
~~ stances found in industrial wastes as determined by the use
of D. magna. Centrifuged Lake Erie water was used as a
diluent in the bioassay. Threshold concentration was defined
as the highest concentration which would just fail to
immobilize the animals under prolonged (theoretically
infinite) exposure.
a c d e g The effect of turbidity on the toxicity of the chemicals was
~~ studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
a The purpose of this paper was to devise a toxicity index for
~~ industrial wastes. Results are recorded as the toxic concen-
tration producing 50 percent inhibition (TCgrj) of oxygen
utilization as compared to controls. Five toxigrams depicting
the effect of the chemicals on BOD were devised and each
chemical classified.
a c This paper deals with the toxicity thresholds of various sub-
stances found in industrial wastes as determined by the use
of D. magna. Centrifuged Lake Erie water was used as a
diluent in the bioassay. Threshold concentration was defined
as the highest concentration which would just fail to
immobilize the animals under prolonged (theoretically
infinite) exposure.
a c d e g The effect of turbidity on the toxicity of the chemicals was
studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
— The purpose of this paper was to devise a toxicity index for
industrial wastes. Results are recorded as the toxic concen-
tration producing 50 percent inhibition (TCso) of oxygen
utilization as compared to controls. Five toxigrams depicting
the effect of the chemicals on BOD were devised and each
chemical classified.
a c This paper deals with the toxicity thresholds of various sub-
stances found in industrial wastes as determined by the use
of D. magna. Centrifuged Lake Erie water was used as a
diluent in the bioassay. Threshold concentration was defined
as the highest concentration which would just fail to
immobilize the animals under prolonged (theoretically
infinite) exposure.
Reference
(Year)
Anderson
(1944)
Wallen, et al
(1957)
Hermann
(1959)
Anderson
(1944)
Wallen, et al
(1957)
Hermann
(1959)
Anderson
(1944)
^
*Q
•o
Z
O
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-------
o
m
jj
30
m
Terpine
alcohol
(85 percent
pine oil)
2-tertiary-butyl-
4,6 dinitro-
phenol
1,2,3,4-tetra-
chlorobenzene
Tetrachloro-
hydroquinone
Tetramethyl-p-
phenylene-
diamine
hydrochloride
2',3',4'-5-tetra-
nitrobenz-
anilide
Cylindrospermum
lichen/forme (CD
Mfcrocystis
aeruginosa (Ma)
Scenedesmus
ob/iquus (Sol
Chlorella
variegata ICv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Cylindrospermum
licheniforme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
ob/iquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Australorbis
glabratus
Microcystis
aeruginosa
Microcystis
aeruginosa
Sa/mo
gairdnerii
Carassius
auratus
2.0 (O)
2.0 (O)
BSA and
FL
BSA
Puerto Failed
Rico
100 (K)
100 (K)
10 (K2)
(O)
a, etc
a, etc
Observations were made on the 3rd, 7th, 14th, and 21st days
to give the following (T = toxic, NT = nontoxic, PT = partially
toxic with numbers of days in parentheses. No number indi-
cates observation is for entire test period of 21 days):
Cl -T(3)
Ma -PT(14)
So -NT
Cv - T (3)
Gp-T(3)
Np -NT
Comment same as above except
Cl -NT
Ma -NT
So -NT
Cv - PT (7)
Gp -NT
Np -PT
Seven of the tested compounds failed to meet acceptability
criteria — that is, complete kill after 6-hr exposure to
10ppm. They were not used in field tests. Field tests
showed WL 8008 to be highly effective.
The chemical was tested on a 5-day-old algae culture,
1 x 106 to 2 x 106 cells/ml, 75 ml total volume, Chu
No. 10 medium was used.
Comment same as above.
Palmer and
Maloney
(1955)
Palmer and
Maloney
(1955)
This paper deals with the relations between chemical struc-
tures of salicylanilides and benzanilides and their toxicity
to rainbow trout and goldfish. The chemical structure of
salicylanilides and benzanilides was related to toxicity and
selectivity to rainbow trout and goldfish. Salicylanilides
were more toxic than benzanilides to the fishes. The ortho
hydroxy substitution of salicylanilide accelerated biological
activity against fish. Meta nitro substitution on the salicyl-
anilides and benzanilides increased toxicity to fish. Similar
findings are reported for halogens and their relative position(s)
in the molecule.
At 10 ppm the chemical was not toxic to goldfish.
Seiffer
and Schoof
(1967)
Fitzgerald,
et al
(1952)
Fitzgerald,
etal
(1952)
Walker, et al
(1966)
I
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-------
CHEMICALS
>
0
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X
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3D
m
en
O
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S
O
£
1
1
Chemical
Thiocarbamide
Titanium
sulfate
Toluene
Toluene
Tribromo-
phenol
Tri-n-
butylamine
Tri-n-
butyltin
acetate
bis-(tri-n-
butyltin)
oxide
Bioassay
or Field
Organism Study*""
Cylindrospermum L
lichen/forme (CD
Microcystis
aeruginosa (Mai
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvu/um (Gp)
Nitzschia
pa/ea (Np)
Pimephales BSA
promelas
Pimephales BSA
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Gambusia BSA
al 'finis
Bacteria BSA
(sewage)
Semotilus BSA
a tromaculatus
Australorbis BSA and
glabratus FL
Australorbis BSA and
glabratus F L
Toxicity,
Active
Field Ingredient,
Location^) ppm(3)
2.0 (0)
(H) 120 (T4AI
(S) 8.2 (T4A)
44 (T4A)
24 (T4A)
62 (T4A)
66 (T4A)
1,260(T2A)
97 (0)
20 to 40 (CR)
Puerto Failed
Rico
Puerto 0.41-0.84 (L)
Rico
Experimental
Variables
Controlled
or Noted'*) Comments
a Observations were made on the 3rd, 7th, 14th, and 21st days
to give the following (T = toxic, NT = nontoxic, PT = partially
toxic with number of days in parentheses. No number indi-
cates observation is for entire test period of 21 days):
Cl -NT
Ma -PT (14)
So -PT (14)
Cv -PT (14)
Gp - PT (7)
Np - PT (7)
a c d f Both hard (H) and soft (S) water were used.
a c d e f Most fish survived at test concentrations of about one half.
~~ or slightly more, of the TLm value. No attempt was made
to estimate 100 percent survival.
a c d e g The effect of turbidity on the toxicity of the chemicals was
"~ studied. Test water was from a farm pond with "high"
turbidity. Additional data are presented.
e In the halophenols, the ortho was less toxic than the meta or
para. All of the monohalophenols were less toxic than the
2,4,6-trihalophenols. Some data on biodegradability of
halophenols were presented. The figure reported is for a
TLm value for cumulative gas production for 7 days.
ae Test water used was freshly aerated Detroit River water. A
typical water analysis is given. Toxicity is expressed as the
"critical range" (CR), which was defined as that concentra-
tion in ppm below which the 4 test fish lived for 24 hours
and above which all test fish died. Additional data are
presented.
c Seven of the tested compounds failed to meet acceptability
criteria — that is, complete kill after 6-hr exposure to
10 ppm. They were not used in field tests. Field tests
showed WL 8008 to be highly effective.
c Comment same as above.
Reference
(Year)
Palmer and
Maloney
(1955)
Tarzwell and
Henderson
(1960)
Pickering and
Henderson
(1966)
Wallen, et al
(1957)
Ingols and
Gaffney
(1956)
Gillette, et al
(1952)
Seiffer and
Schoof
(1967)
Seiffer and
Schoof
(1967)
2
•o
m
z
2
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-------
1,2.4-trichloro-
benzene
BSA
OJ
1,1,1-trichloro-
ethane
1,1,2-trichloro-
ethane
Trichloro-
phenol
Trichloro-
toluene
O
m
o
3,4,6-trichloro-
2-nitrophenol
(free phenol)
3,4,6-trichloro-
2-nitrophenol
Elodea
canadensis
Potamogeton
nodosus
Potamogeton
pectinatus
Lagodon
rhomboides
Lagodon
rhomboides
Bacteria
(sewage)
Elodea
canadensis
Potamogeton
nodosus
Potamogeton
pectinatus
Petromyzon
marinus
Salmo
gairdnerii
S. trutta
Petromyzon
marinus
(prolarvae)
(larvae)
BSA
BSA
BSA
BSA
BSA
BSA
5(0)
100 (O)
5(0)
100 (O)
5(0)
100 (O)
75-100 (O)
150-175(0)
60(0)
5 (K4wk)
100(K4wk)
5(0)
100(O)
5(0)
100 (O)
5 (K 100%)
17 (K 10%)
15 (K 10%)
10(K15)
10 (K1)
Experiments were conducted in standing water. Results were
rated on a scale of 0 to 10, 0 standing for no toxic effect and
10 signifying a complete kill. Evaluation was based on visual
observation of the plant response at weekly intervals for
4 weeks.
No toxic effect.
Injury rating of 9.5.
No toxic effect.
Injury rating of 9.8.
No toxic effect.
Injury rating of 9.8.
Experiments were conducted in aerated salt water. Toxicity
range given as the concentrations which produced < 1/2
deaths and > 1/2 deaths.
Comment same as above.
In the halophenols, the ortho was less toxic than the meta or
para. All of the monohalophenols were less toxic than the
2,4,6-trihalophenols. Some data on biodegradability of
halophenols were presented. The figure reported is for a
TL|\/| value for cumulative gas production for 7 days.
Experiments were conducted in standing water. Results were
rated on a scale of 0 to 10, 0 standing for no toxic effect and
10 signifying a complete kill. Evaluation was based on visual
observation of the plant response at weekly intervals for
4 weeks.
Injury rating of 8.4.
Injury rating of 9.1.
Injury rating of 8.5.
Injury rating of 9.5.
Mortality occurred in approximately 24 hours. This was a
study on controlling sea lamprey larvae.
Additional data are presented.
Frank, et al
(1961)
Garrett
(1957)
Garrett
(1957)
Ingols and
Gaffney
(1965)
Frank, et al
(1961)
m
z
O
Ball
(1966)
Piavis
(1962)
X
3)
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-------
o
I
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3
O
£ Chemical
2 3,4,6-trichloro-
O 2-nitrophenol
S (Nasalt)
X
H
C
3)
m
en
O
-n
O
I
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S
O
Ej
i
2',4',6'-tri-
chloro-3-
nitrosali-
cylanilide
Triethylamine
Organism
Petromyzon
mar in us
(larvae)
Salmo
gairdnerii
(fingerlings)
S. trutta
Sa/velinus
fontinalis
Amb/oplites
rupestris
Lepomis
gibbosus
Coesius
plumbeus
Semotilus
atromaculatus
Percina
caprodes
Cambarus spp
Aquatic
larvae
Catostomus
commersoni
Ictalurus
me/as
1. nebulosus
Perca
flavescens
Salmo
gairdnerii
Carassius
auratus
Semotilus
atromaculatus
Bioassay
or Field
Study d)
BSA
FS
BSA
FS
FS
FS
FS
FS
FS
FS
FS
FS
FS
FS
FS
FS
FS
BSA
BSA
Toxicity,
Active
Field Ingredient,
Location^) ppm(3)
13 (K 100%)
Mich. 12 (K 100%)
23 (K 10%)
40 (NTE)
40 (NTE)
40 (NTE)
40 (NTE)
40 (NTE)
40 (NTE)
40 (NTE)
40 (NTE)
40 (NTE)
40 (NTE)
32 (NTE)
20 (K)
32 (NTE)
10(K3hr)
10 (K2)
- 50 to 80 (CR)
Experimental
Variables
Controlled Reference
or Noted'4) Comments (Year)
a Mortality occurred in approximately 24 hours. This was a Applegate
~~ study on controlling sea lamprey larvae. The "field" study (1958)
involved use of simulated lake water in large raceways.
a This paper deals with the relations between chemical struc- Walker, et al
tures of salicylanilides and benzanilides and their toxicity (1966)
to rainbow trout and goldfish. The chemical structure of
salicylanilides and benzanilides was related to toxicity and
selectivity to rainbow trout and goldfish. Salicylanilides
were more toxic than benzanilides to the fishes. The ortho
hydroxy substitution of salicylanilide accelerated biological
activity against fish. Meta nitro substitution on the salicyl-
anilides and benzanilides increased toxicity to fish. Similar
findings are reported for halogens and their relative position(s)
in the molecule.
a e Test water used was freshly aerated Detroit River water. A Gillette, et al
typical water analysis is given. Toxicity is expressed as the (1952)
"critical range" (CR), which was defined as that concentra-
tion in ppm below which the 4 test fish lived for 24 hours
and above which all test fish died. Additional data are
presented.
O
X
-------
30
m
CO
_
m
3-trifluoro-
methyl-4-
nitrophenol
3-trifluoro-
methyl-4-
nitrophenol
a,a,a-trifluoro-
4-nitro-m-
cresol
Triiodophenol
2,2,4-tri methyl
(/3-phenyliso-
propyl)-1,2-
dihydro-
quinoline
Trimethyl and
trimethyl-
octadecadienyl
ammonium
chlorides
S 3,3',5-tri-
S nitrobenz-
O anilide
O
£
Trinitro-
toluene
2,3,5-tri-
phenyltetra-
zolium
chloride
Petromyzon BSA
marinus
Salmo
gairdnerii
Petromyzon BSA
marinus
(larvae)
Salmo BSA
gairdnerii
S. trutta BSA
Bacteria BSA
(sewage)
Daphnia BSA
magna
Cylindrospermum L
licheniforme (CD
Gleocapsa
sp(C)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Salmo BSA
gairdnerii
Carassius
au rat us
2 (K 100%)
7 (K 10%)
10 (K 1-2 hr)
9 (K 10%)
7 (K 19%)
83(0)
1.8 (K2)
2.0 (O)
10(K3hr)
(O)
Microcystis
aeruginosa
Microcystis
aeruginosa
100 (K)
2.5 (K)
a, etc
a, etc
Mortality occurred in approximately 24 hours. This was a
study on controlling sea lamprey larvae.
Additional data are presented.
Mortality occurred in approximately 24 hours.
In the halophenols, the ortho was less toxic than the meta or
para. All of the monohalophenols were less toxic than the
2,4,6-trihalophenols. Some data on biodegradability of
halophenols were presented. The figure reported is for a
] value for cumulative gas production for 7 days.
Applegate
(1958)
Piavis
(1962)
Applegate
(1958)
Ingols and
Gaffney
(1965)
An attempt was made to correlate the biological action with Sollman
the chemical reactivity of selected chemical substances. (1949)
Results indicated a considerable correlation between the
aquarium fish toxicity and antiautocatalytic potency of
the chemicals in marked contrast to their toxicity on
systemic administration.
Observations were made on the 3rd, 7th, 14th, and 21st days Palmer and
to give the following (T = toxic, NT = nontoxic, PT = partially Maloney
toxic with number of days in parentheses. No number indi- (1955)
cates observation is for entire test period of 21 days):
Cl -NT
G -NT
So -PT
Cv -NT
Gp -NT
Np -NT
This paper deals with the relations between chemical struc- Walker, et al
tures of salicylanilides and benzanilides and their toxicity (1966)
to rainbow trout and goldfish. The chemical structure of
salicylanilides and benzanilides was related to toxicity and
selectivity to rainbow trout and goldfish. Salicylanilides
were more toxic than benzanilides to the fishes. The ortho
hydroxy substitution of salicylanilide accelerated biological
activity against fish. Meta nitro substitution on the salicyl-
anilides and benzanilides increased toxicity to fish. Similar
findings are reported for halogens and their relative position(s)
in the molecule. At 10 ppm the chemical was not toxic to
goldfish.
The chemical was tested on a 5-day algae culture, 1 x 106 to Fitzgerald, et al
2 x 106 cells/ml, 75-ml total volume. Chu No. 10 medium (1952)
was used.
Comment same as above. Fitzgerald, et al
(1952)
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CHEMICALS
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o
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X
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3D
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C/l
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5
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Chemical
Triphenyltin
acetate
Triphenyltin
chloride
Tri-n-pro-
pylamine
Tri-n-propyltin
oxide
Trypaflavine
(acriflavine
neutral)
Uranyl
acetate
Uranyl
nitrate
Uranyl
sulfate
Urea
Valeric
acid
Vanadium
pentoxide
Vanadyt
sulfate
Organism
Australorbis
glabratus
Australorbis
glabratus
Semotilus
atromaculatus
Australorbis
glabratus
Ictalurus
punctatus
Pimephales
promelas
Pimephales
promelas
Pimephales
promelas
Semotilus
atromaculatus
Daphnia
magna
Pimephales
promelas
Pimephales
promelas
Lepomis
macrochirus
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study'1) Location (2) ppm'3) or Noted'4)
BSA Puerto (O) c
Rico
BSA Puerto (O) c
Rico
BSA - 30 to 70 (CR) ae
BSA Puerto (0) c
Rico
BSA - 17.9 (K2) acfi
11.5 (T2A)
BSA - (S) 3.7 (T4A) acdf
BSA - (S) 3.1 (T4A) acdf
BSA - (H)135(T4A) acdf
(S) 2.8 (T4A)
BSA - 1 6,000 to 30,000 a e
BSA - 45 (T2A) a c
BSA - (H)55(T4A) acdf
(S) 13(T4A)
BSA - (H) 30 (T4A) acdf
(S) 4.8 (T4A)
(H) 55 (T4A)
(S) 6 (T4A)
Comments
Seven of the tested compounds failed to meet acceptability
criteria — that is, complete kill after 6-hr exposure to
10 ppm. They were not used in field tests. Field tests
showed WL 8008 to be highly effective.
Comment same as above.
Test water used was freshly aerated Detroit River water. A
typical water analysis is given. Toxicity is expressed as the
"critical range" (CR), which was defined as that concentra-
tion in ppm below which the 4 test fish lived for 24 hours
and above which all test fish died. Additional data are
presented.
Seven of the tested compounds failed to meet acceptability
criteria — that is, complete kill after 6-hr exposure to
10 ppm. They were not used in field tests. Field tests
showed WL 8008 to be highly effective.
The experiment was conducted at 66 C.
Both hard (H) and soft (S) water were used.
Comment same as above.
Comment same as above.
Test water used was freshly aerated Detroit River water. A
typical water analysis is given. Toxicity is expressed as the
"critical range" (CR), which was defined as that concentra-
tion in ppm below which the 4 test fish lived for 24 hours
and above which all test fish died. Additional data are
presented.
"Standard reference water" was described and used as well
as lake water. Varied results were obtained when evalua-
tions were made in various types of water.
Both hard (H) and soft (S) water were used.
Comment same as above.
Reference
(Year)
Seiffer and
Schoof
(1967)
Seiffer and
Schoof
(1967)
Gillette, et al
(1952)
Seiffer and
Schoof
(1967)
Clemens and
Sneed
(1958)
Tarzwell and
Henderson
(1960)
Tarzwell and
Henderson
(1960)
Tarzwell and
Henderson
(1960)
Gillette, et al
(1952)
Dowden and
Bennett
(1965)
Tarzwell and
Henderson
(1960)
Tarzwell and
Henderson
(196O)
^
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Vanillin
Vinyl
acetate
Xanthic
acid, ethyl
sodium salt
Xylene
n
m
S Xylene
9
£
£
X
3)
5
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Zinc
Zinc
Cylmdrospermum L
lichen/forme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum IGp)
Nitzschia
palea INp)
Pimephales BSA
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Cy/indrospermum L
licheniforme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (Sol
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Daphnia BSA
magna
Pimephales BSA
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Salmo BSA
gairdnerii
Sewage BOD
organisms
2.0 (O)
22 (T4A)
18 (T4A)
42 (T4A)
26 (T4A)
2.0 (O)
a c d e f
100
1000 (T1A)
21 (T4A)
22 (T4A)
24 (T4A)
39 (T4A)
6(K2)
(O)
a cd e f
Observations were made on the 3rd, 7th, 14th, and 21st days Palmer and
to give the following (T = toxic, NT = nontoxic, PT = partially Maloney
toxic with number of days in parentheses. No number indi- (1955)
cates observation is for entire test period of 21 days):
Cl -NT
Ma -NT
So - PT (3)
Cv - PT (3)
Gp -T (3), PT (21)
Np -PT(7)
Most fish survived at test concentrations of about one half, Pickering and
or slightly more, of the TLm value. No attempt was made Henderson
to estimate 100 percent survival. (1966)
Observations were made on the 3rd, 7th, 14th, and 21st days
to give the following (T = toxic, NT = nontoxic, PT = partially
toxic with number of days in parentheses. No number indi-
cates observation is for entire test period of 21 days):
Cl -NT
Ma - PT (7)
So -NT
Cv - PT (7)
Gp-NT
Np-NT
"Standard reference water" was described and used as well as
lake water. Varied results were obtained when evaluations
were made in various types of water.
Most fish survived at test concentrations of about one half, or
slightly more, of the TLm value. No attempt was made to
estimate 100 percent survival.
The concentration given was fatal to fingerlings. Young fish
2 and 4 weeks old could not tolerate concentrations of
4 ppm, but with increasing age showed a tendency to de-
velop a tolerance to solutions of this concentration.
Zinc was toxic to sewage organisms in concentrations as low
as 0.001 ppm. This could result in errors in BOD tests.
At 1.0 ppm, the oxygen demand in percent of the control
was 83%.
Palmer and
Maloney
(1955)
I
m
O
X
Dowden and
Bennett
(1965)
Pickering and
Henderson
(1966)
Goodman
(1951)
Ingols
(1956)
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—
>
E5
Zinc
x
1
3
Zinc
Organism
Lepomis
macrochirus
(adult)
Salmo
salar
Lepomis
macrochirus
Lepisosteus
osseus
Dorosoma
petenense
Dorosoma
cepedianum
Alosa
chrysochloris
Cyprinus
carpio
Carassius
auratus
Lepomis
macrochirus
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study!"") Location<2) ppm(3)
BSA - 18 C
(H) 10.1-
12.5 (T4A)
(S) 2.9-
3.8 (T4A)
30 C
(H) 10.2-
12.2 (T4A)
(S) 1.9-
3.6 (T4A)
BCFA - 0.042 (T1 A)
BCFA - 0.0-5.0(0)
BSA - 2.86-3.78 (O)
Experimental
Variables
Controlled
or IMoted(4) Comments
a c d e f i n g The results of these experiments indicated that in dilution
~~ water of the same quality there was little difference in
toxicity at 18 C and 30 C. A considerable difference in
toxicity was apparent between hard (H) and soft (S)
water. A greater amount of zinc in solution was required
in hard water than in soft water. Hardness of the dilution
water had a greater effect upon the toxicity of zinc than
did temperature.
a c f The laboratory water in which the experiment was per-
formed contained 3 jU I/liter of zinc, as judged by analysis
over several years, and 2 jUg/liter of copper. Lethal concen-
trations of mixtures acted two or three times as fast as the
metals singly, a somewhat greater potentiation than was
found in the previous tests with salmon.
a c f An autopsy method for acute zinc toxicity in fish was devel-
oped. Thirty to 90-day exposures to sublethal concentra-
tions indicated that the opercular bone accumulates zinc
at the same rate as gill tissue. By using the ratio of zinc in
the gill to zinc in the bone a reasonably constant value was
obtained by nonlethal exposures. This value increased up
to a hundredfold in acute exposures.
a f At the given concentration 50% survival occurred at 18 C
in soft water.
Reference
(Year)
Cairns and
Scheier
(1958)
Schoenthal
(1963)
Mount
(1964)
Cairns
(1965)
•o
m
Z
O
Zinc
Rainbow
trout
FR
Scotland
0.90-2.10 (O)
6.60-9.47 (O)
6.18-9.50 (O)
3.9 (T2)
a c efIm
At the given concentration 50% survival occurred at 30 C
in soft water.
At the given concentration 50% survival occurred at 18 C
in hard water.
At the given concentration 50% survival occurred at 30 C
in hard water.
This work represents an extension of laboratory studies of
the toxicity of complex effluents to investigations of rivers.
Herbert, et al
(1965)
-------
Zinc
Pimephales
promelas
BSA
(O)
Zinc
Fathead
minnow
BCFA
4.9 to 32.3
(T4A)
^
~ Zinc
Zinc
2
O
" Zinc
O
f
2 Zinc
C
3D
m
O
-n
m
S
Fundulus
heteroclitus
Lebistes
reticulatus
Bufo
va/liceps
(tadpoles)
Daphnia
magna
Gasterosteus
aculeatus
Lebistes
reticulatus
(guppy)
BSA
BSA
BSA
157-180 (K)
10.CHK)
10.0 (K)
1.0 (K)
0.1 (O)
(O)
a c d Zinc sulfate was added to tap water for the experiments. Pickering and
TLm values for minnow eggs: Vigor
1 day - 3.95 ppm (1965)
2 day — 2.55 ppm
4 day — 1.83 ppm
7 day — 1.71 ppm
12 day - 1.63 ppm
TLm values for minnow fry:
1 day — 0.95 ppm
2 day - 0.95 ppm
4 day — 0.87 ppm
7 day — 0.87 ppm
From the experimental data, it appeared that animals ex-
posed to a dilute zinc solution developed a tolerance to
this metal. The duration of the tolerance was not
investigated.
a c d e Zinc was most toxic at a pH of 8.0 and a water hardness of Mount
50 ppm and least toxic at pH 6.0 and a hardness of 200 ppm. (1966)
At any given hardness, zinc was always more toxic at a high
pH than at a low pH. The results are in disagreement with
most published work possibly because a flow-through system
would keep any precipitated zinc in suspension. The first
value reported is for a pH of 8.0 and a hardness of 50, and
the second for a pH of 6.0 and a hardness of 200.
acei Fish subjected to the concentration reported died in 24 to Eisler
48 hours. The dead fish contained 7 and 8 times more zinc (1967)
in the whole fish and in the gill arch than untreated control
fish.
ace It is assumed in this experiment that the cations considered Shaw and
are toxic because they combine with an essential sulfhydryl Grushkin
group attached to a key enzyme. This treatment indicates (1967)
that the metals which form the most insoluble sulfides are
the most toxic. The log of the concentration of the metal
ion is plotted against the log of the solubility product con-
stant of the metal sulfide — a treatment that does not lend
itself to tabulation. The cation toxicity cited is only an
approximate concentration interpolated from a graph.
Time of death was not specified.
£££ This is a discussion of a bioassay method using stickleback Hawksley
fish and spectrophotometric determinations of the chem- (1967)
icals evaluated. The number listed is said to be the "toxic
limit" for the fish.
a c f n o A series of equations was devised to describe the toxicity of Chen and
a system containing two toxicants — zinc and cyanide. Selleck
A concentration of 1 ppm of Zn killed 50% of the fish in (1968)
32 hours. 0.75 ppm killed 50% in 63 hours, and 0.56 ppm
killed 50% in 96 hours. Toxicity of the two-component
system was then determined using varying ratios of the
two components.
m
O
-------
o
I
m
S
o
P Chemical
5 Zinc
D
S
X
-1
C
33
m
° Zinc
O
T
m
S
> Zinc
C
Zinc
(Zn++)
Zinc and
copper
\
j
Zinc and
copper
Zinc
acetate
Zinc boro-
fluoride
Organism
Lepomis
macrochirus
Salmo
gairdnerii
Oncorhynchus
kisutch
Lepomis
macrochirus
Atlantic
salmon
Salmo
salar
Pimephales
promelas
Sewage
organisms
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
StudyCO Location (2) ppm(3) or Noted^
BCFA - 7.2-12.0 acdef
(T20CF)
BSA - 2.8-3.5 (T4A) a c d e f o
BSA - (O) a c
BSA - 4.2 (T4A) a c d e
FR Canada (O) f
BSA - 0.048 Cu (O) a
0.600 Zn
BSA - (S) 0.88 (T4A) c d e f
BOD - 55 (O)
Comments
The toxicity of zinc was largely dependent upon the dis-
solved oxygen in the water. Bluegills showed an increased
mortality to zinc as a result of an environmental stress of
low dissolved oxygen concentration. The lowest toxic zinc
concentration was for a system containing 1.8 mg/l of
dissolved oxygen, and the highest for a system containing
5.6 mg/l.
The concentration killing a half batch of fish in 2 days pro-
vides a reasonable estimate of the threshold concentration.
The lethality of this chemical depends upon the total hard-
ness of the water and the dissolved oxygen concentration.
Zinc uptake and distribution in the developing coho salmon
egg was measured using radioisotope tracer techniques.
About 70% of the total accumulated zinc was bound rather
firmly to the chorion, 26% was found in the perivitelline
fluid, 2% in the yolk, and 1% in the embryo.
All fish were acclimatized for 2 weeks in a synthetic dilution
water.
"Toxicity index" for zinc and copper combined was de-
scribed in connection with disturbed salmon migration.
Toxicity index >1.0 indicates lethality to "young salmon
after long exposure" A toxicity index of 0.15 or 15% of
the lethal concentration of zinc and copper seems to be
the maximum safe level for migration.
The values given are for an I LL (incipient lethal level) and in
this instance only in water of 20 mg/liter of hardness.
Concentrations above this are lethal in about one day.
These values were determined by bioassay. Salmon parr
in the laboratory avoided less than one tenth of incipient
lethal levels. Avoidance thresholds were 0.09 ILL of zinc,
0.05 ILL of copper and 0.02 ILL of equitoxic mixtures.
In equitoxic mixtures of these compounds, the ILL was
additive.
(S) Soft water.
Values are expressed as mg/l of metal.
Various metal salts were studied in relation to how they
affected the BOD of both raw and treated sewage as well
Reference
(Year)
Pickering
(1968)
Brown
(1968)
Wedemeyer
(1968)
Cairns and
Scheier
(1968)
Sprague
(1964)
Sigler, et al
(1966)
Pickering and
Henderson
(1965)
Sheets
(1957)
•o
m
Z
O
as how they affected the processing of sewage in the treat-
ment plant. BOD was used as the parameter to measure
the effect of the chemical. The chemical concentration
cited is the ppm required to reduce the BOD values by 50%.
This chemical was tested in an unbuffered system.
-------
O
Zinc
chloride
Zinc
chloride
Zinc
chloride
Zinc
chloride
(as Zn++)
Zinc
chloride
Zinc
chloride
(tagged with
zinc 35)
Zinc
chloride
(as Zn++)
Zinc
chloride
n Zinc
chloride
Daphnia
magna
Lepomis
macrochirus
Lepomis
macrochirus
Lepomis
macrochirus
Lepomis
macrochirus
Ictalurus
nebulosus
BSA
BCFA
BSA
BSA
BSA
BS
«0.15 (S)
6.91 (T4A)
20(T4A)
(N) 8.02
(T4A) N
(L) 4.9
(T4A) L
6.91 (T4A)
(O)
Brachydanio
rerio
(adults)
(eggs)
Lepomis
macrochirus
Lepomis
macrochirus
Nitzschia
linearis
Physa
heterostropha
Lepomis
macrochirus
BSA
BSA
BSA
28(T2A)
105(T2A)
5.2 (T2A)
(S) 5.37 (T4A)
4.3 (T5A)
0.79-1.27 (T4A)
2.86-3.78 (T4A)
£ Lake Erie water was used as diluent. Toxicity given as
~ threshold concentration producing immobilization for
exposure periods of 64 hours.
a c e f Test water was composed of distilled water with CP grade
chemicals and was aerated throughout the 96-hour ex-
posure period.
ace Increase in temperature seemed to increase toxicity of this
chemical. Low dissolved oxygen reduced toxicity of some
chemicals in this study. Toxicity values may be 20% higher
in hard versus soft water.
££ Modified Chu No. 14 test medium was used. Toxicity is given
both for "normal" 02 (5-9 ppm), (N), and with "low" C"2
(2 ppm DO), (L). High and low threshold concentration
percent of survival are also presented.
a c d e i A "control" was prepared by adding required chemicals to
distilled water, and this was constantly aerated. Data
reported are for larger fish, approximately 14.24 cm in
length. Data for smaller fish are also in the report.
c d f i I Bullheads showed an initial rapid uptake of zinc for the first
several hours followed by a short period of decline. Z-35
was used to measure zinc uptake. The fish exposed to
6.0 ppm of zinc for 96 hours, when placed in flowing, fresh
water, lost 43 percent of their total accumulated zinc after
1 day. Fish exposed to 12 ppm of zinc for 14 days all
survived.
The test dilutions were made up from distilled water and
ACS grade chemicals. Temperature was held at 24 C and
the solution was aerated to maintain a dissolved oxygen
content of 5-9 ppm.
c d e f (S) Soft water.
Values are expressed as mg/l of metal.
ace The purpose of this experiment was to determine whether
there was a constant relationship between the responses of
these organisms. From the data presented, there was no
apparent relationship of this type. Therefore the authors
advise that bioassays on at least 3 components of the food
web be made in any situation.
Anderson
(1948)
Cairns and
Scheier
(1955)
Cairns
(1957)
Cairns and
Scheier
(1958)
Cairns and
Scheier
(1959)
Joyner
(1961)
Cairns, et al
(1964)
Pickering and
Henderson
(1965)
Patrick, et al
(1968)
I
m
Z
D
X
c
30
m
C/J
m
2
-------
CHEMICALS
>
O
s
X
H
C
33
m
en
O
T
O
m
5
O
en
i
ON
KJ
Chemical
Zinc-copper-
cyanide
complex
Zinc
cyanide
Zinc
cyanide
complex
Zinc (a)-
cyanide (b)
mixture
Zinc
cyanide
complex
(sodium
cyanide
(564 ppm CN-)
and
zinc sulfate
(394 ppm Zn)]
Zinc
dimethyl-
dithio-
carbamate
Bioassay
or Field
Organism Study'D
Pimephales BSA
promelas
Sewage BOD
organisms
Lepomis BSA
macrochirus
(juveniles)
Lepomis BSA
macrochirus
Pimephales BSA
promelas
Cylindrospermum L
lichen/forme (CD
Microcystis
aeruginosa (Ma)
Toxicity, Experimental
Active Variables
Field Ingredient, Controlled
Location'2) ppm'3) or Noted'4)
— 1.0 ppm Zn ac
0.025 ppm Cu ~
0.05 ppm CN
(non-toxic
4 days)
1.0 ppm Zn
0.25 ppm Cu
0.33 ppm CN
(non-toxic
4 days)
1.0 ppm Zn
0.025 ppm Cu
(K<14 hr)
0.75 (O)
0.4 (O) acdfp
(a) 3.90 (T4A) a c d e
(b) 0.26 (T4A)
0.18 (T4A) ac
2.0 (0) a
Comments
Synthetic soft water used.
Various metal salts were studied in relation to how they
affected the BOD of both raw and treated sewage as well
as how they affected the processing of sewage in the treat-
ment plant. BOD was used as the parameter to measure
the effect of the chemical. The chemical concentration
cited is the ppm required to reduce the BOD values by 50%.
This chemical was tested in an unbuffered system.
For the concentration given, the median resistance time in
minutes was 256.
All fish were acclimatized for 2 weeks in a synthetic dilution
water.
Synthetic soft water was used. Toxicity data given as number
of test fish surviving after exposure at 24, 48, and 96 hr.
TLm values were estimated by straight-line graphical inter-
polation and given in ppm CN"
Observations were made on the 3rd, 7th, 14th, and 21st days
to give the following (T = toxic, NT = nontoxic, PT = partially
toxic with number of days in parentheses. No number indi-
cates observation is for entire test period of 21 days):
Reference
(Year)
Doudoroff, et al
(1956)
Sheets
(1957)
Doudoroff, et al
(1966)
Cairns and
Scheier
(1968)
Doudoroff, et al
(1956)
Palmer and
Maloney
(1955)
^
•o
m
z
g
x
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gpi
Nitzschia
palsa (Npl
Cl - PT (7)
Ma-T (7),PT (14)
So -NT
Cv -PT (14)
Gp-T (14)
Np - T (3)
-------
Zinc
dimethyl-
dithio-
carbamate
(100 percent)
Zinc
ion
c
30
m
CO
o
I
Zinc
stearate
Cylindrospermum
lichen/forme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Physa
heterostropha
2.0 (O)
BSA
"l
ON
W
S
m
S
O
r~
Zinc
ion
Zinc-nickel
cyanide
complex
Zinc
nitrate
Zinc
salts
Zinc
salts
Fish
Pimephales
promelas
Balanus
balanoides
Diatoms
Platyhelminths
Many insects
Salmo
gairdnerii
BSA
BSA
BSA
FR
BSA
Ystwyth,
Wales
Lepomis
macrochirus
BSA
20 C
(S) 0.79-
1.27 (T4A)
(H) 2.66-
5.57 (T4A)
30 C
(S) 0.62-
0.78 (T4A)
(H) 2.36-
6.36 (T4A)
1.5x 10'4M (K)
1.0 ppm CM"
0.6 ppm Zn
(K<16hr)
0.13 ppm Ni
32.0 (O)
0.2-0.7 (O)
(O)
(O)
Comment same as above except that:
Cl -T(3)
Ma-T (3)
So - T (3)
Cv - T (3)
Gp-T(3)
Np-T(3)
Palmer and
Maloney
(1955)
a c d e q The objective of these experiments was to determine the
~~ ~ effects of water temperature and hardness on the toxicity
of zinc ion to pond snails. (H) = hard water, (S) = soft
water.
Avoidance behavior of test fish to toxic chemicals is given.
Toxicity is given as the lowest lethal concentration (molar).
Ratios of avoidance and lowest lethal concentration are
presented and discussed.
Synthetic soft water was used. Toxicity data given as number
of test fish surviving.
The concentration listed was lethal to 90% of adult barnacles
in 2 days.
Zinc salts were from mine drainage. The flora above the mines
was rich, but below the sources of pollution was poor in
quantity and variety of lithophilous insects.
This is a study of the effect of varying dissolved oxygen con-
centrations on the toxicity of selected chemicals.
The toxicity of heavy metals, ammonia, and monohydric
phenols increased as the dissolved oxygen in water was
reduced. The most obvious reaction of fish to lowered oxy-
gen content is to increase the volume of water passed over
the gills, and this may increase the amount of poison reach-
ing the surface of the gill epithelium.
The concentration of the chemical in the water was not
specified.
"Standard reference water" was described and used as well as
lake water. Varied results were obtained when evaluations
were made in various types of water.
Compound is very slightly soluble in water. No toxicity data
given.
Cairns and
Scheier
(1958)
Ishio
(1965)
Doudoroff, et al X
(1956) >
Clarke
(1947)
Jones
(1958)
Lloyd
(1961)
Dowden and
Bennett
(1965)
-------
CHEMICALS
>
O
s
X
-H
35
m
co
O
o
I
m
O
>
w
^
j^
ON
•^
Chemical
Zinc
sulfate
Zinc
sulfate
Zinc
sulfate
Zinc
sulfate
Zinc
sulfate
Zinc
sulfate
Zinc
sulfate
(as Zn)
Zinc
sulfate
Zinc
sulfate
Organism
Gasterosteus
aculeatus
Daphnia
magna
Salmo
gairdnerii
Pygosteus
pungitius
Sewage
organisms
Salmo
gairdnerii
Rainbow
trout
Tendipes
decorus
Limnodrilus
hoffmeisteri
Physa
heterostropha
Asellus
communis
Argia sp
Lebistes
reticulatus
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study (D Location<2> ppm<3> or Noted W
BSA - 0.7 (TL4y3A) a c
BSA - <48 (O) a c
BSA - 25 ppm a c e f
(0, 133 ~ ~
min)
BCF - (O) ac
BOD - 920 (O) -
BSA - (O) a c
BSA - (O) a c d
BSA - 56 (K 40%) a c d i
10 (T4A)
14 (T4A)
38.5 (T4A)
56 (T4A)
BSCH - 5.0 (41% K 90) acde
Comments
Death of the fish resulted from an interaction between the
metallic ion and the mucus secreted by the gills. Coagulated
mucus formed on the gill membranes and impaired respira-
tion to such a degree that the fish asphyxiated.
The addition of 50 mg/l of calcium chloride to the tank pro-
tected against the toxic effect of this metal salt.
This paper deals with the toxicity thresholds of various sub-
stances found in industrial wastes as determined by the use
of D. magna. Centrifuged Lake Erie water was used as a
diluent in the bioassay. Threshold concentration was defined
as the highest concentration which would just fail to im-
mobilize the animals under prolonged (theoretically infinite)
exposure.
Tap or distilled water used as diluent. Toxicity defined as
the average time when the fish lost equilibrium when exposed
to the test chemical (ppm Zn).
Fish were exposed to 0.04, 0.003, 0.0003, and 0.0001 N zinc
sulfate. Survival times at these concentrations were, re-
spectively: 85 minutes, 190 minutes, 7 hr, and 15 hr.
Various metal salts were studied in relation to how they
affected the BOD of both raw and treated sewage as well as
how they affected the processing of sewage in the treatment
plant. BOD was used as the parameter to measure the effect
of the chemical. The chemical concentration cited is the
ppm required to reduce the BOD values by 50%. This chem-
ical was tested in an unbuffered system.
Zinc sulfate was less toxic in hard water than in soft water;
more toxic in hard water with increased temperature; and
more toxic when DO decreased. Survival curves are
presented.
The 48-hour LDsg as interpolated from a graph was 4 ppm.
A method for prediction of toxicity of spent liquor from
a coke oven before and after biological treatment is briefly
discussed.
Kill data for T. decorus is presented on other concentrations
in either hard or soft water.
Sublethal effects found were retarded growth, increased
mortality, and delayed sexual maturity.
Reference
(Year)
Jones
(1939)
Anderson
(1944)
Grindley
(1946)
Jones
(1947)
Sheets
(1957)
Lloyd
(1960)
Herbert
(1961)
Wurtz and
Bridges
(1961)
Crandall and
Goodnight
•o
m
O
(1962)
-------
Zinc
sulfate
Zinc
sulfate
Zinc
(zinc
sulfate)
Zinc
sulfate
(as Zn)
Zinc
sulfate
Zinc
sulphate
Zinc
sulfate
O
m Zinc
? sulfate
O
to Zinc
> sulfate
D
C Zinc
3) sulfate
co (as Zn)
O
m
Physa
heterostropha
Helisoma
companulata
Salmo
salar
Salmo
salar
Salmo
gairdnerii
Periphyton
Brachydanio
rerio
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Brachydanio
rerio
(embryos)
Brachydanio
rerio
Salmo
salar
S. trutta
S. gairdnerii
S. trutta
S. gairdnerii
BSA
BSA
BCF
BSA
FL
BSA
BSA
Newtown,
Ohio
BSCH
BSA
BSCH
4.2 (T1A)*
1.9 (T2A)
1.9 (T3A)
1.9 (T4A)
49.0 (T1A)
49.0 (T2A)
13.4 (T3A)
13.4 (T4A)
(O)
0.6 (O)
3.86 (T2A)
1.1-6.5 (O)
(0)
(S) 0.96 (T4A)
(H) 33.4 (T4A)
(S) 5.46 (T4A)
(H) 40.9 (T4A)
(S) 6.44 (T4A)
(H) 1.27 (T4A)
20 (K 15 hr)
20 (K1)
0.1 (K)
(0)
(O)
(O)
(O)
a c d e f
a cd ef
acdf
acdf
a c e f
cdef
a c d e
cf
These tests were conducted in hard and soft water at varied
temperatures. Generally, this chemical was more toxic in
soft water. At temperatures up to 90 F, zinc sulfate was
less toxic than at 51 F for P. heterostropha.
The ECgrj °r the effective concentration that produced an
avoidance response in 50% of the fish was 0.092 x the ILL
(incipient lethal level), or 0.092 x 580 |Ug/l,or 53.3jUg/l.
The experiments were carried out in soft water. Values are
reported as micrograms of metal and toxicity as LTsg.
In solutions containing copper and zinc, fish died twice as
fast as would occur if the 2 metals were simply additive in
their lethal action.
A mathematical equation was derived to explain the com-
bined toxicities of this salt and ammonium chloride.
Fungi and slime-forming bacteria grew abundantly in the
high Zn concentrations, apparently due to nutrient release
from decaying periphyton.
Survival time for adult fish (aged 40 days) in 168 hours was
10 ppm. The chemical was more toxic to newly hatched
fish.
(S) Soft water.
(H) Hard water.
Values are expressed as mg/l of metal.
Wurtz
(1962)
Embryos with the outer membranes removed survived longer
than natural embryos — the action of zinc sulfate on mem-
branes is unknown. Additional data are presented.
Data are given for several concentrations of zinc. The authors
also measured oxygen uptake of the fish plotting this value
against the dry weight of the fish. Toxicity of zinc to fish
of different ages was also measured. An equation was de-
rived to express toxicity of zinc to these fish.
The reported figure is a reported lethal concentrate as found
in polluted lakes and streams in Norway. Apparently organic
matter has a masking effect that reduces toxicity. Rainbow
trout and Atlantic salmon reacted similarly to the chemical.
Brown trout was only slightly more tolerant. The value given
is for a 21-day median survival period. 50% of brown trout
eggs survived to hatch in 0.3 ppm Zn. Eggs of rainbow trout
behaved similarly.
Sprague
(1964)
Sprague
(1964)
Herbert and
Shurben
(1964)
Williams and
Mount
(1965)
Skidmore
(1965)
Pickering and
Henderson
(1965)
m
O
X
Skidmore
(1966)
Skidmore
(1967)
Grande
(1967)
-------
CHEMICALS
z
o
5
X
H
c
33
m
en
O
~n
O
I
m
S
O
£
;>
>i-
ON
ON
Chemical
Zinc
sulfate
Zinc
sulphate
(hydrated)
Zinc
sulfate
Zinc
sulfate
plus
copper
sulfate (vari-
ous ratios)
Zinc
sulfate
plus alkyl-
benzene
sulfonate
Zirconium
oxychloride
Zirconium
sulfate
Organism
Salmo
gairdnerii
Perca
fluviatilis
Rutilus
rutilus
Gobio
gobio
Abramis
brama
Salmo
gairdnerii
Perca
fluviatilis
Rutilus
rutilus
Gobio
gobio
Abramis
brama
Tubificid
worms
Salmo
gairdnerii
Salmo
gairdnerii
Pimephales
promelas
Lepomis
macrochirus
Pimephales
promelas
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study'1) Location'2) ppm'3) or Noted*4*
BSA - 4.6 (T4A) c e
16.0 (T5A)
17.3 (T5A)
8.4 (T7A)
14.3 (T5A)
BCFA - 3.8-5.5 (K5)
14.8-17.3 (K5) ace
15.4-19.4 (K5)
9-15 (K5)
12.5-16.3 (K5)
BSA - 46.0 (T1 A) ac
BSA - - a e p
BCFCH - 0.3* (T4A) abcdef
& A *ABS +
0.8 ppm Zn
BSA - (H)240(T4A) acdf
(S) 18IT4A)
(H) 270 (T4A)
(S) 15 (T4A)
BSA - (H)145(T4A) acdf
(S) 14IT4A)
Comments
Data given as LC5fj which was taken as equivalent to TLm.
Additional data for other exposure periods are presented.
Data confirmed that experiments of short duration are not
necessarily reliable for ranking the ultimate sensitivities
of several species of fish to a given poison.
Knop's solution was used. TLm levels for various pHs were
determined for the tubificids and were found to be 5.8 to
9.7. Zinc sulfate was more toxic at pH extremes of 6.5
and 8.5 than at 7.5.
Both hard and soft water were used. Median period of sur-
vival in hard water was 3 days — 3.5 ppm Zn, and 1.1 ppm
Cu; in soft water 7 days, 0.56 ppm Zn and 0.044 ppm Cu.
For a concentration of 0.45 ppm of alkyl benzene sulfonate
alone, the median tolerance limit was recorded in 4 days.
The zinc concentration was 0.08 ppm in the combined
zinc-detergent solution. The ABS appeared to block devel-
opment of resistance to Zn in the trout in chronic studies.
Both hard (H) and soft (S) water were used.
Comment same as above.
Reference
(Year)
Ball
(1967)
Ball
(1967)
Whitley
(1968)
Lloyd
(1961)
Brown, et al
(1968)
Tarzwell and
Henderson
(1960)
Tarzwell and
Henderson
(1960)
•o
m
Z
a
-------
APPENDIX B
EXTRACTED DATA FROM ORIGINAL PAPERS
COMMERCIAL CHEMICAL PRODUCTS
-------
Note: Names of chemicals and organisms are as given by the various authors. Readers should search for alternate, common, and/or scientific names of both
chemical and aquatic species; and refer to report section on Extracted Data for further discussion of this appendix.
Footnotes for Appendices A and B:
(1) Letters represent:
B = bioassay, used in combination with S = static, CF = continuous flow, A = acute, and CH = chronic.
L = laboratory bioassay.
BOD = biochemical oxygen demand.
F = field study, used in combination with R = river, stream, creek, etc., L = lake or pond, M = marine, E = estuarine, and O = other
(port facility, flooded area, etc.).
(2) Field location is indicated by abbreviation of the state or country.
(3) The number indicates ppm (mg/1), unless otherwise indicated by appropriate designations or (0). The letters within parentheses following indicate
T = TLm, K = kill, SB = sublethal effects, NTE = no toxic effect, or O = other. The number following these indicates the time in days at which
observations were made. EC$Q, LC$Q, and similar designations for 50 percent lethality were all considered as TLm and designated as such. The
numbers within parentheses following these designations indicate the time in days when the effect was observed.
(4) The following indicate (when underlined the variable was controlled):
a = water temperature
b = ambient air temperature
td C = PH
~ d = alkalinity (total, phenolphthalein or caustic)
e = dissolved oxygen
f = hardness (total, carbonate, Mg, or CaO)
g = turbidity
h = oxidation-reduction potential
i = chloride as Cl
j = BOD, 5 day; (J) = BOD, short-term
k = COD
1 = nitrogen (as N02 or NOs)
m = ammonia nitrogen as NH3
n = phosphate (total, ortho-, or poly)
o = solids (total, fixed, volatile, or suspended)
p = C02
-------
o
o
2
2
m
o Chemical
"~ 2389
2 1 1 0%)
m
2
o
> Abate
1
3)
O
O
C
q
M
Abate
(Am.Cy.52,
160)
CO
t-o
Abate
Abate
Abate
Alky! benzene
sulphonate
(ABS)
Sodium
alkvlaryl
sutfonate
Organism
Chlorella
pyrenoidosa
Prosimulum spp
Cnephia spp
Simulium spp
(larvae)
Micropterus
salmoides
Lepomis
macrochirus
Gambusia
af finis
Lebistes
reticulatus
Paleomonetes
paludosus
Hyalella
azteca
Plankton
(Euglena,
Coleps)
Rotifers
Callinectes
sapidus
Microp terus
salmoides
Pteronarcys
ca/ifornica
(naiads)
Cladophora
glomerata
Eurhynchium
ruse/forme
Ranunculus
pseudofluitans
Potamogeton
pectinatus
P. densus
Rainbow
trout
(frv)
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study!"!' Location'2) ppm'3) or Noted^)
L - 100 (AC 1/2 hr)
LCFA - 4.0 (O) a
BSA - 200+ (L1 A) a
200+ (L1A)
200+ (L1A)
200+ (L1A)
1.0 (L1A)
0.65 (L1A)
50.0 (K2)
50.0 (K2)
BCFCH - 0.01 (K) a
BSA - 5.0 (T 1 hr) ae
5.0 (K 2 hr)
BSA - 0.01 (T4A) acd ef
BSA - 10(K21A)
10 (K21A)
2.5 (K14)
2-3 (SB 14)
2.5 (SB14)
BSA - 3.0-5.0 (T1 A) acde
Comments
Describes a bioassay method to differentiate between an
algicide (AC) and an algistat (AS). The treated culture
was subcultured as time progressed. Allen's medium
was used.
Stones heavily populated with larvae were placed in troughs
of running water containing the toxicant. When the larvae
became detached from the rocks and floated away, they
were assumed to have undergone lethal intoxication. The
larvae were exposed to the toxicant for 5 minutes, then in
clean water for 24 hours. At that time the number detached
amounted to 56 percent.
Abate was toxic to fish at a dosage rate necessary to control
the larvae of the chironomid midge.
Little or no information was given about test procedures
and further results.
Experiments were carried out in plastic tubs lined with saran
plastic. Fish weights averaged 217 grams.
Data reported as LCso at 1 5.5 C in 4 days.
Within the range of reduction of ABS detergent concentration
which has been achieved by the Luton experiment there
was very little biological effect on the river.
The 24-hr TLm was very near the highest concentration
that was nonlethal in 6 hr. Additional data are
discussed.
Reference
(Year)
Fitzgerald and
Faust
(1963)
Jamnback and
Frempong-
Boadu
(1966)
Von Windeguth
and Patterson
(1966)
Butler and
Johnson
(1967)
Mulla, et al
(1967)
Sanders and
Cope
(1968)
Hynes and
Roberts
(1962)
Vivier and
Nisbet
(1965)
TJ
•o
m
z
o
CD
-------
Sodium
alkyl
benzene
sulfonate
ABS
Alkyl benzene
sulfonate
(25 percent)
ABS
C8
OJ
Lepomis
macrochirus
L. gibbosus
Lepomis
macrochirus
Hydropsychidae
Stenonema sp
S. ares
S. heterotarsale
Isonychia
bicolor
Orconectes
rusticus
Coniobasis sp
Lepomis
gibbosus
BSA and
CFCH
BCF
BCFACR
BSCHA
8
s
m
3)
O
>
r~
0
2
o
>
-o
3)
O
O
c
0
Alkyl
benzene
sulfonate
(54.8%)
Sodium
alkyl
benzene
sulfonate
Nitzchia
linearis
Navicula
seminulum
Physa
heterostropha
Lepomis
macrochirus
and
Lepomis
gibbosus
Ictalurus
natal is
BSA
BSCH
17.4 (T4A)
17.4 (T4CF)
21.9 (T4A)
19.7 (T1A)
18.1 (T4A)
17.3(T30A)
32 (60% K)
16 (K)
16 (K)
16 (K)
4.0 (K)
32 (K)
32 (K)
12(0)
a c d e
(S) 10 (T5)
(S) 5.6 (T5)
(H) 39.4 (T5)
(S) 34.2 (T5)
(H) 35.8 (T5)
5.6-18.0
(survived, but
extensive gill
damage
occurred)
0.5 (SB1CH)
a c d e f q
a cd e
acdf
Both hard and soft water were used. Data from both were
similar. TLm for 24 and 48 hr are given. Gill damage
occurred at 5-6 ppm after 3 months of exposure. Data on
cruising speed and active oxygen consumption are also
presented in addition to erythrocyte count and histological
examination of gills. Similar gill damage for L. macrochirus
occurred in acute and chronic studies.
Toxicities are recorded as an average for 3 tests. Test fish
exhibited some degree of acclimation to the chemical after
exposure to sublethal concentrations.
Concentration, time and percent survival are given. Con-
siderable additional data are also presented.
Fish were exposed to the ABS solution for two weeks, and
subsequently to a sublethal concentration of ZnCl2 (2.4
ppm). Limited tests indicated that exposure to ABS in
excess of 5.6 ppm caused marked gill damage but produced
no gross changes in zinc tolerance. Other fish were exposed
to ABS as above, then in dilution water alone, and the
temperature was raised to 35 for 96 hours. Exposure to
ABS apparently caused no changes in the tolerance of the
fish to the higher temperature.
Effects in hard (H) and soft (S) waters were compared. Two
compositions of ABS were used. TLm is given in ppm of
ABS composition.
At 0.5 ppm, bullhead chemoreceptor damage occurred.
Detergent concentration was monitored by the
methylene-blue technique.
Cairns and
Scheier
(1963)
Lemke and
Mount
(1963)
Surberand
Thatcher
(1963)
Cairns and
Scheier
(1964)
Cairns, et al
(1964)
Bennett
(1962)
m
D
X
oo
-------
n
o
S
2
m
o Chemical
£ ABS
o
I
m
S
O
r~
5 ABS
g (54.8%
C active)
q
en
Alkyl benzene
sulfonate
j^
^
ABS
Organism
Brachydanio
rerio
(adults)
(eggs)
Lepomis
macrochirus
Lepomis
gibbosus
Vaucheria
Cladophora
Chlorella
pyrenoidosa
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study <1> Location*2) ppm(3)
BSA
42.0 (T2A)
75.0 (T2A)
17.4 (T2A)
BSCH - 18 (O)
BSA - (O)
L - 0-20 mg/l
increased
growth
Experimental
Variables
Controlled
or Noted'4) Comments
a c d e f The test dilutions were made up from distilled water and
ACS grade chemicals. Temperature was held at 24 C and
the solution was aerated to maintain a dissolved oxygen
content of 5-9 ppm.
a c d e i Chloride content of the water was adjusted to 60 ppm — and
the fish were exposed to the test solution for 21 days. At
this time, the chloride content was raised to 6500 ppm, and
the test was continued another 21 days. ABS generally
damaged the gill structure. Since salt exchange as well as
oxygen exchange takes place here, it would not be surprising
that gill damage would correlate with chloride content of the
blood. However, there was little difference in the blood
chloride in control and experimental animals.
afiln Experiments were conducted in five 1 -gal. containers. Algal
~~ communities were subsampled and the samples were placed
in 60-ml bottles at 4 time periods: 12 hr, 24 hr, 48 hr,
and 96 hr.
Results showed that ABS has a negative effect on C14 uptake
for both algae communities, the communities appear to partly
recover their ability to assimilate C14 at extended exposures
to high concentrations, and a slight stimulation of C14 uptake
appears to occur at abbreviated exposures to low
concentrations.
a c e p Growth rates of the Chlorella were followed when supplied
synthetic detergents as the phosphorus source. Sodium
triphosphate was responsible for increased growth.
Reference
(Year)
Cairns, et al
(1965)
Cairns and
Scheier
(1966)
Hicks and
Neuhold
(1966)
Maloney
(1966)
^
TJ
m
z
O
X
ABS
ABS
(54.8%)
Pimephales
pro met as
(eggs)
Jordanella
floridae
ABS
ABS
Lepomis
gibbosus
Notropis
antherinoides
Pimephales
notatus
Lepomis
macrochirus
BCF
BSCH
BSA
BCFA
BCFA
BCFA
rate
6.4 (T9)
10 to 65
(NTE)
(0)
7.4 (T4A)
7.7 (T4A)
8.2 (T4A)
a c d e f Mortality range is given for exposure (days 1 -9) with various Pickering
concentrations and controls. Additional data are presented. (1966)
— Aquaria were prepared containing 0, 10, 28, 42, 56, 65 ppm Foster, et al
of ABS. The major effect found was on the feeding habits (1966)
of the fish. Apparently the chemical made worms in the
aquaria unpalatable. Time required for the consumption of
the worms varied with the concentration of the chemical.
£e_ Gill damage in pumpkinseed sunfish resulting from 24-hr Scheier and
exposure to 18 ppm of this chemical was not reversible, Cairns
even after the test fish were removed to fresh dilution water (1967)
for an eight-week period.
a c d e f Differences in sensitivity to ABS between closely related Thatcher
species was studied. Since bluntnose and fathead minnows (1966)
are closely related phylogenetically and ecologically, one
might expect them to be very similar in their response to a
given toxicant. However, from the data in this report, this
is not necessarily true since the two species were significantly
different in ABS sensitivity. The differences between several
species of Notropis also illustrate this.
-------
Alkyl benzene
sulfonate
ABS
(54.8%)
Alkyl benzene
sulfonate
plus zinc
sulfate
Campostoma
anomalum
Notropis
stramineus
Ericymba
buccata
Notropis
ardens
Pimephales
promelas
Notropis
cornutus
Cyprinus
carpio
Ictalurus
me/as
Lepomis
macrochirus
Pimephalus
promelas
Ictalurus
melas
Notropis
atherinoides
Notropis
cornutus
Nitzschia
linearis
Physa
heterostropha
Lepomis
macrochirus
Sal mo
gairdnerii
BCFA
BCFA
BCFA
BCFA
BCFA
BCFA
BCFA
BCFA
BSA
BSA
BCFC
8
I AC-5727
f (15 percent
S EC)
'n AC-5727
I
m
2
o
3D
O
O
Gambusia
affinis
Salmo
gairdnerii
(one wk old
sac fry)
(one mo old
feeding fry)
FL
BSA
Ponds -
Bakers-
field,
Calif.
8.9 (T4A)
9.0 (T4A)
9.2 (T4A)
9.5 (T4A)
11.3(T4A)
17.0 (T4A)
18.0 (T4A)
22.0 (T4A)
8.2 (T4A)
11.3IT4A)
22.0 (T4A)
7.4 (T4A)
17.0 (T4A)
10.0 (T5A)
34.2 (T4A)
17.44 (T4A)
0.3* (T4A)
*ABS +
0.8 ppm Zn
(O)
0.5 (K 0%)
5.0 (K 0%)
0.5 (K 0%)
5.0 (K 0%)
a c d e
a b c d e f
In all of these tests, the LAS stock powder contained 60.8%
LAS. The values reported were calculated on a basis of
pure LAS.
The purpose of this experiment was to determine whether
there was a constant relationship between the responses of
these organisms. From the data presented, there was no
apparent relationship of this type. Therefore the authors
advise that bioassays on at least 3 components of the food
web be made in any situation.
For a concentration of 0.45 ppm of alkyl benzene sulfonate
alone, the median tolerance limit was recorded in 4 days.
The zinc concentration was 0.08 ppm in the combined
zinc-detergent solution. The ABS appeared to block
development of resistance to Zn in the trout in chronic
studies.
At 0.2 Ib/acre, 2 percent mortality occurred in 24 hours.
At 0.8 Ib/acre, 20 percent mortality occurred in 24 hours.
The experiments were conducted in cages placed in the
ponds.
Results are averages of triplicate tests. Toxicity is reported
as percent mortality (K %).
Thatcher and
Santner
(1967)
Patrick, et al
(1968)
Brown, et al
(1968)
Mulla and
Isaak
(1961)
Lewallen and
Wilder
(1962)
1
m
z
o
X
00
-------
COMMERCE
>»
r~
O
X
rn
S
0
r~
•o
O
Q
C
o
C/l
ON
Chemical
American
Cyanamid
12009
(tech)
American
Cyanamid
43,913
AC^3913
AC-47031
(EC4)
AC-47921
(EC4)
AC-47921
(EC4)
Amer. Cyan-
amid 52,160
Amer. Cyan.
52160
ACP-M-569
ACP
(a-chloroaceto*
phenone)
Acriflavin
Organism
Pimephales
promelas
Lepomis
macrochirus
Lebistes
reticulatus
Leiostomus
xanthurus
(juvenile)
Oyster
Australorbis
glabratus
Gambusia
affinis
Gambusia
affinis
Rana
catesbeiana
Gambusia
affinis
Oyster
Oyster
Leiostomus
xanthurus
(juvenile)
Rainbow
trout
Onchorynchus
tshawytscha
Green
sunfish
Microcystis
aeruginosa
Bioassay
or Field
Study (D
BSA
BSA
BCF
BSA and
FL
FL
FL
FL
BCF
BCF
BSA
-
BSA
BSA and
FL
L
Toxicity,
Active
Field Ingredient,
Location(2) ppm(3)
0.32 (T4A)
0.075 (T4A)
0.010 (T4A)
(0)
0.20 (0)
Puerto Rico (O)
Cal. 0.5 (K1)
Cal. 0.4 (O)
(0)
Cal. 0.1 (K1)
0.042 (O)
(0)
(0)
1 .0 (T4A)
185 (T1A)
155 (T2A)
Okla. 1.1 (T1A)
1.05 (T2A)
1.0 (K)
Experimental
Variables
Controlled
or Noted (4) Comments
a c d e f The toxicity of this substance was not influenced by the
quality of the water (pH, hardness, alkalinity).
a Water temperature was 13 C. 20% mortality at 1.0 ppm
occurred.
The value reported is a 96-hr ECsg (decreased shell growth).
c Seven of the tested compounds failed to meet acceptability
criteria — that is, complete kill after 6-hr exposure to
10 ppm. They were not used in field tests. Field tests
showed WL 8008 to be highly effective. All others failed.
— Toxicity value is in Ib/acre.
- At a concentration of 0.4 Ib/acre, 96% mortality of the fish
occurred in 24 hours. No mortality in tadpoles of
R. catesbeiana occurred during an exposure period of one
week. Toxicity value is in Ib/acre.
— Toxicity value is in Ib/acre.
a The value reported is a 96-hr ECgg (decreased shell growth).
Exposure to a concentration of 1 ppm caused a 35.0%
decrease in shell growth.
Water temperature was 13 C. Fish showed irritation at
1 .0 ppm.
— The values reported are given as LC5Q.
a c d e Concentrations were based on percent active ingredient.
a e p The main purpose of this experiment was to determine the
repellent characteristics of certain chemicals. Tests were
conducted at 22 C to 23 C. BSA experiments were made
in a wooden trough.
a , etc The chemical was tested on a 5-day algae culture, 1 x 10^
to 2 x 106 cells/ml, 75 ml total volume. Chu No. 10
medium was used.
Reference
(Year)
Pickering and
Henderson
(1966)
Butler
(1965)
Seiffer and
Schoof
(1967)
Mulla
(1966)
Mulla
(1966)
Mulla
(1966)
Butler
(1965)
Cope
(1965)
Bond.et al
(1960)
Summerfelt
and Lewis
(1967)
Fitzgerald.et al
(1952)
•o
Z
O
X
DO
-------
Acriffavine
Acriflavine
i
Acrylaldehyde
(acrolein)
Acti-dione
Aerosporin-
Q Polymyxin
B (sulfate)
m
a>
O
o
I
m
5
O
-o
3)
O
o
c
Aldrin (hexa-
chloro-
hexahydro-
dimeth-
anonaphthalene,
48 percent)
tctalurus
punctatus
(fry)
Lepomis
macrochirus
(fry)
Sal mo
gairdnerii
Sal mo
trutta
Salvelinus
fontinalis
Salvelinus
namaycush
Ictalurus
punctatus
Lepomis
macrochirus
BSA
BSA
5.0 (SB3)
5.0 (SB3)
19.9 (T2A)
27.0 (T2A)
14.8 (T2A)
28.0 (T2A)
33.2 (T2A)
13.5 (T2A)
a c d e f At least 90 percent of the fry survived for a period of
p 72 hours at the concentration listed.
a f Variance and the 95-percent confidence interval (C.I.)
~~ were also determined.
BSA
Cylindrospermum
licheniforme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Oomph onema
parvulum (Gp)
Nitzschia
pa lea (Np)
Cylindrospermum
licheniforme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (Sol
Chlorella
variegata (Cv)
Gomph onema
parvulum (Gp)
Nitzschia
palea (Np)
Lymnaeid
snails
2.0 (O)
2.0 (0)
BSA
(O)
Jones
(1965)
Willford
(1966)
Experiments were conducted in standing water. Results were Frank, etal
rated on a scale of 0 to 10,0 standing for no toxic effect and (1961)
10 signifying a complete kill. Evaluation was based on visual
observation of the plant response at weekly intervals for
4 weeks.
Observations were made on the 3rd, 7th, 14th, and 21st days Palmer and
to give the following (T = toxic, NT = nontoxic, PT «= partially Maloney
toxic with number of days in parentheses. No number indi- (1955)
cates observation is for entire test period of 21 days):
Cl - PT (7)
Ma- NT
So -T
Cv - PT (7)
Gp-T
Np-T
Comment same as above except that: Palmer and
Cl - T Maloney
Ma-T (1955)
So -T (14)
Cv -T
Gp-T
Np-T
Each test container (500-ml beaker) was filled with ditch Batte, et al
water. 100% mortality occurred at 1:100,000 and greater. (1951)
m
z
o
X
00
-------
o
o
2
S
m
o Chemical
Q Aldrin
m
S
O
f-
•o
3J
O
O
C
5 Aldrin
en
Aldrin
Aldrin
(88.4%)
rt
U
O
Aldrin
Aldrin
(dust)
Aldrin
Aldrin
Organism
Fathead
minnow
Bluegill
Goldfish
Guppy
Fathead
minnow
Pimephales
promelas
Lepomis
macrochirus
Carassius
auraws
Lebistes
reticulatus
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Pimephales
promelas
Lepomis
macrochirus
Tilapia
melanopleura
Daphnia
magna
Oncorh ynchus
kisutch
Oncorhynchus
tshawytscha
Sal mo
gairdnerii
Gast«n»tsus
acuteatuv
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study'1) Location'2) ppm'3) or Noted'4*
BSA - 0.033 (T4A) a
~
0.013 (T4A)
0.028 (T4A)
0.033 (T4A)
BSA - 0.028 (T4A) a
BSA - 0.03 (T4A) adef
0.01 (T4A)
0.03 (T4A)
0.03 (T4A)
BSA - 0.032 (T4A) a b e c d f
0.015 (T4A)
0.032 (T4A)
0.037 (T4A)
BSA - 0.033 (T4A) a
0.013(T4A)
FLCH Tangan- 1.0lb(3.3%K)
yika 5.0 Ib (3.3% K -
3wks)
10.0lb (60.0% K-
3wks)
BSA - 0.0292 (0) a
BSA - 45.9 (T4A) acde
7.5 (T4A)
17.7 (T4A)
39.8 (T4A)
Comments
It was the authors opinion that pH, alkalinity and hardness,
within the usual range in natural waters, had little effect on
the toxic effect of the compounds studied. The values given
are from Henderson, Pickering, and Tarzwell, "The Relative
Toxicity of Ten Chlorinated Hydrocarbon Insecticides to
Four Species of Fish". It is interesting that the different
tables from the above book (as reported in this paper) report
widely different values for the same compounds.
Comments same as above except that the experiment was
performed in hard water.
Concentrations were based on percent active ingredient.
Dilution water was usually soft although some studies were
conducted with hard water.
Bioassay investigations of the new insecticides indicate that
in general the organic phosphorus compounds are not as
toxic to fish as are the chlorinated hydrocarbons. The
toxicity of most of these materials was not significantly
influenced by water quality. Therefore it is to be expected
that the toxicity of these materials will not differ significantly
in different streams.
Trial periods were for 20 weeks. Sublethal effects such as
impaired breeding, retarded growth, or altered taste
were not detected. Dosages are given as Ib/acre of surface
water.
The indicated concentration immobilized Daphnia in
50 hours.
Chemical dissolved in acetone. TLm expressed in ppb.
Reference
(Year)
Tarzwell
(1959)
Henderson, et al
(1959)
Henderson, et al
(1959)
Tarzwell
(1959)
Webbe and
Shute
(1959)
Anderson
(1960)
Katz
(1961)
>
TJ
m
2
g
x
00
-------
Aldrin
Aldrin
(EC 2)
Aldrin
Aldrin
m
3)
o
o
i
m
S
O
TJ
3J
O
O
Gammarus
lacustris
lacustris
Gambusia
affinis
Rana
catesbeiana
(tadpoles)
Lepomis
macrochirus
Salmo
gairdneri
Aquatic insects:
Ephemeroptera
Trichoptera
Chironomidae
Fish:
Moxostoma
erythrurum
Hypentelium
nigricans
Catostomus
commersoni
Pimephales
notatus
Notropis
chrysocephalus
Semotilus
atromaculatus
Campostoma
anomalum
Ericymba
buccata
Etheostoma
zonale
Hybopsis
biguttata
Percina
maculata
Notropis
spilopterus
N. stramineus
N. volucellus
Etheostoma
caeruleum
Notropis
umbratilis
BSA
(O)
FL
Cal.
0.5 (O)
BSA
FR
10 (T1A)
6 (T2A)
(O)
a e p The mortality might have been partially due to the suscepti-
bility of the organism to higher temperatures, toxicity from
extended exposure to copper electrodes (used to shock the
organism to determine death), or the increase of COj.
Results were expressed as LTso; for example, at 0.5 ppm,
50 percent of the shrimp were killed in 200 (±35) min.
a c Mixed populations of the indicated test species contained in
cages were exposed to various insecticidal chemicals
applied as dilute sprays to ponds 1/16 acre in size. The
indicated toxicant concentration is in Ib/acre, and resulted
in a 90 percent mortality for the fish, and a 80 percent
mortality for the tadpoles in 24 hours.
a The experiment was conducted at 65 F.
Dosage application rate was 2 Ib aldrin/acre. After initial
application a great number of fish and insects of indicated
species were killed. A collection, made 7 months later,
showed this stream contained a diversity of insect species
and sizes of fish.
McDonald
(1962)
Mulla, etal
(1963)
Cope
(1963)
Moye and
Luckmann
(1964)
I
m
O
X
00
-------
o
o
s
s
m
o Chemical
r-
O Aldrin
m
5
o
n Aldnn
•o
O
a
c
o
H
Aldnn
Aldnn
Aldrin
QO
!— '
O
Aldrin
Aldrin
Aldrin
Aldrin
(tech)
Organism
Bluegill
Notemigonus
crysoleucas
Lepomis
macrochirus
L. cyanel/us
Gammarus
lacustris
Gambusia
affinis
affinis
Pa/eomonetes
kadiakensis
Acroneuria
pacifica
Ephemerella
grandis
Gammarus
lacustris
Pteronarcys
californica
Procambarus
clarkii
(juvenile)
(adult)
Gambusia
affinis
Icta/urus
melas
Rainbow
trout
Bluegill
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study*1) Location<2) ppm*3* or Noted*4*
BSA - 0.01 3 (T4A) a
BSA - (B) 0.080 (T 1.5) a c f
(A) 4.750 (T 1.5)
(B) 0.038 (T 1.5)
(A) 3.0 (T 1.5)
(B) 0.062 (T 1.5)
(A) 3.25 (T 1.5)
BSA - 38.5 (T4A) a e
BSA - 0.05 to 2.1 (O) a
BSA - (N) 85 (TT/jA) a cf
(TB) 185 (TV/2 A)
BSA - 0.143IT4A) ac
0.009 (T4A)
38.5 (T4A)
0.18 (T4A)
BSA - a c d o
0.038 (T5A)
0.60 (T5A)
BSA - 0.02-0.06 (T3A) a c d e
0.013-0.185 (T3A)
BSA - 0.031 (T4A) -
0.0052 (T4A)
Comments
Assays were conducted in soft water at 25 C. Decrease
in brain cholinesterase was measured in fish exposed to
the toxicant.
Chemical was dissolved in acetone. Final concentration of
acetone was <2 ml/l. Data shows TLm ppb for
insecticide-resistant (A) and insecticide non-resistant (B)
strains of the test fish.
Emulsible concentrates were prepared from technical grade
insecticides with acetone as the solvent. Symptoms
prior to death were observed and recorded on graphs.
The lower value is for fish that had never been exposed to
the toxicant, and the higher value was obtained with fish
that had been exposed to a sublethal dose in the past.
Apparently such an exposure produces a resistance that
can be retained when they are exposed later.
Test organisms were collected from 2 locations, Twin Bayou
(TB), Sunflower Co., Miss. (Agricultural area) and Noxubee
National Wildlife Refuge (N), Noxubee Co., Miss, (non-
agricultural area) and evaluated in laboratory bioassays.
The Twin Bayou shrimp were more resistant.
Additional TLm data are given.
The pesticides studied in this report are widely used in
rice culture in Louisiana and are toxic to crawfish.
Test fish were collected from 8 different locations of the
Mississippi River. The 3-day TLm values were made to
determine if a resistance gradient existed. The data indi-
cated that there was none.
The values reported are given as LC^Q.
Reference
(Year)
Weiss
(1964)
Ferguson, et al
(1964)
Nebeker and
Gaufin
(1964)
Boyd and
Ferguson
(1964)
Ferguson, et al
(1965)
Gaufin, et al
(1965)
Hendrick and
Everett
(1965)
Ferguson, et al
(1965)
Cope
(1965)
^
-o
TJ
O
X
CO
-------
Aldrin
Aldrin
(tech,
93 percent
active in
acetone)
Aldrin
Aldrin
Aldrin
Aldrin
3)
O
O Aldrin
I
m
§
9
3}
O
O
Pteronarcys
californica
Acroneuria
pacifica
Ephemerella
grandis
Daphnia
magna
Gammarus
lacustris
Pteronarcys
californica
(naiad)
Acroneuria
pacifica
(naiad)
Bluegill
BSA
Acroneuria
pacifica
Pteronarcys
californica
Procambarus
clarkii
Daphnia
magna
Notropis
umbra til is
N. umbratilis
(2 in.)
N. cornutus
BSA
BSA
BSA & CFCH
FO
Crowley,
La.
BSA
BSA
0.18 (T4A)
0.1 (T4A)
0.009 (T4A)
0.03 (T 50 hr A)
38.5 (T4A)
0.180 (T4A)
0.143 (T4A)
9.7 (T4A)
7.7 (T4A)
6.2 (T4A)
5.6 (T4A)
0.143 (T4A)
0.022 (T30CH)
0.180 (T4A)
0.0025 (T30CH)
(0)
0.030 (SB)
0.02-0.08
(T4A)
0.4 (T4A)
0.02-0.08
(T4A)
Unspecified chemical characteristics of assay water were
determined by standard methods. General comments were
made concerning "standardized" conditions, use of "soft"
water, and use of emulsifying agents. Additional data are
presented.
Gaufin, et al
(1965)
c d e f A. pacifica was much more sensitive to chlorinated hydro-
carbons and to organic phosphate insecticides than
P. californica.
a These experiments were performed to demonstrate that at
~~ increased temperatures the toxic effect of most chemicals
is increased.
For the toxicant concentrations listed, the temperatures were
respectively, 45, 55, 65, 75, and 85 F. Data on the effect
of time as well as temperature was also reported. The
experimental animals all were approximately one gram in
weight.
a c d e Additional data are presented.
c d e p Experiments were conducted in a flooded rice field. Area
was divided into 4 blocks with a fence, restricting crawfish
to desired areas. The rearing of crawfish in rice fields is of
considerable commercial importance in Louisiana. No
untoward effect on the crawfish occurred. Aldrin was used
on the rice seed at the rate of 0.25 lb/100 Ib seed. Even
with the addition of carbonyl solution 0.8 Ib/acre showed
no more effect.
— Concentration reported is for immobilization.
Time for immobilization was 64 hr.
Data cited are for 78 F, but assays were performed at
varied temperatures. Water chemistry (unspecified) was
"controlled" during the assay period.
acd£ Aerated pond water was used as diluent. Both aquarium
and a "boat" were used as test vessels. Other experiments
with oxygen concentration variations are reported.
Jensen and
Gaufin
(1964)
Cope
(1965)
Jensen and
Gaufin
(1966)
Hendrick,et al
(1966)
I
m
O
X
CD
Sanders and
Cope
(1966)
Proffitt
(1966)
(continued)
-------
o
0
2
m
o Chemical
r-
0
I
m
2
O
>
TJ
33
O
O
c
5
en
a
j
Aldrin
Aldrin
Organism
/V. blennius
(2 in.)
Spotfins
(2 in.)
(3 in.)
Lepomis
macrochirus
(<1-1/2 in.)
(1-1/2 in.)
(2 in.)
L. cyanellus
(1-1/2 in.)
(3 in.)
Microptera
salmoides
(2-1/2 in.)
Fundalus
no tat us
(1-1/2 in.)
Etheostoma
flabellare
(2 in.)
Noturus
miurus
Etheostoma
nigrum
(2 in.)
£. caeruleum
(2 in.)
£. blennioides
(2-1/2 in.)
Campostoma
anomalum
(5 in.)
Hypentelium
nigricans
(5-1/2 in.)
Ericymba
buccata
Hypognathus
nuchalis
Simocephalus
serrulatus
Daphnia
pulex
Catfish
Buffalo fish
Perch
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study'1' Location'2' ppm'3'
0.6 (T6A)
0.6 (T6A)
0.6 (T8A)
0.2 (T2A)
0.4 (T4A)
0.6 (T6A)
0.4 (T4A)
0.6 (T6A)
0.4 (T4A)
0.6 (T8A)
0.6 (T8A)
0.6 (T8A)
0.8 (T10A)
0.8 (T10A)
0.8 (T10A)
0.8 (NTE)
0.8 (NTE)
0.21 (K2A)
0.25 (K2A)
BSA - 0.023 (SB)
0.028 (SB)
L - (0)
Experimental
Variables
Controlled Reference
or Noted'4' Comments (Year)
^
^
TJ
m
z
g
X1"
03
— Concentration reported is for immobilization. Sanders and
Time for immobilization was 48 hr. Cope
Data cited are for 60 F, but assays were performed at (1966)
varied temperatures. Water chemistry (unspecified) was
"controlled" during the assay period.
— The chemical was found from O.02 to 0.21 ppm as residues Sparr, et al
in catfish, and O.O1 to O.O4 in buffalo fish — after a soil (1966)
treatment nearby of 5 Ib/acre.
-------
Aldrin
Aldrin
Aldrin
Aldrin
Aldrin
14C-Aldrin
Aldrin
Algeeclear
m
3D
O
^ Algibiol
r
o
2
5
•o
3J
O
o
Oyster
Daphnia
carinata
Mya
arenaria
Crassostrea
virginica
Corbicula
manillensis
Mercenaria
mercenaria
Rangia
cuneata
Oyster
Lamps/Us
siliquoidea
L. ventricosa
Anodonta
grandis
Carassius
auratus
(Linnaeus)
Pteronarcys
californica
(naiads)
Chlorella
pyrenoidosa
Phoxinus
phoxinus
BCF
BSA
BCFCH
0.001 (SB4)
1.0 (SB4)
0.0040 (SB)
(O)
FE
Gal vest on (O)
Bay,
Texas
Red Cedar (O)
River,
Mich.
BSA
0.05 (SB)
BSA
BSA
0.0013 (T4A)
20 (AS 1)
25 (K2A)
20 (T1A)
a c d e f
a cd e
Seawater was employed in this experiment.
Concentration reported is for immobilization.
Time for immobilization was 64 hr.
Data cited are for 78 F, but assays were performed at
varied temperatures. Water chemistry (unspecified) was
"controlled" during the assay period.
Results are recorded as a range of uptake of the chemical
by 5 species of aquatic mollusks. An uptake or concentra-
tion of 350-4500X resulted.
Oysters from the area were found to contain from none
to 0.03 ppm.
The mussels listed were analyzed for the toxicant and its
metabolites. Mussels may be used as detectors for this
toxicant, because they tend to concentrate the chemical
in much higher concentrations than it is ever found in the
water. The amount of chemical applied as a spray was
not specified.
Immediately after 8-hr exposure ^4C-Dieldrin was detected
in various tissues; percentages increased with time until
at 32 days they were 93.9% or more except for visceral
fat; 50 and 100% of the residues were Dieldrin within
2.5-5.4 and 31.5-92.4 days, respectively; in visceral fat
the corresponding times were 46.9 and 14,733 days.
Data reported as LC^Q at 15.5 C in 4 days.
Describes a bioassay method to differentiate between an
algicide (AC) and an algistat (AS). The treated culture
was subcultured as time progressed. Allen's medium
was used.
The assays were conducted in a dual aquarium with aeration.
The highest dilution that was nonletal was 7.5 ppm.
Butler
(1966)
Sanders and
Cope
(1966)
Butler
(1967)
Casper
(1967)
Bedford
(1968)
Gakstatter
(1968)
Sanders and
Cope
(1968)
Fitzgerald and
Faust
(1963)
Vivier and
Nisbet
(1965)
•o
m
O
X
CD
-------
COMMERCE
>»
r~
O
m
S
O
>
r~
3)
O
0
c
o
tn
£
-P>.
Chemical
Algimaster
Algimycin
(MT-4)
Algimycin
200
Allethrin
Allethrin
(tech)
Allethrin
Allethrin
Allethrin
Altacide
2,4-D
p-ammophenol
Organism
Chlorella
pyrenoidosa
Chlorella
pyrenoidosa
Chlorella
pyrenoidosa
Pteronarcys so
(nymphs)
Rainbow
trout
Simocephalus
serrulatus
Daphnia
pulex
Prosimulum spp
Cnephia spp
Simulium spp
(larvae)
Pteronarcys
californica
(naiads)
Spatterdock
Daphnia
magna
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study'1) Location(2) ppm(3) Or Noted'4'
L - 3.0 (AC<1/2)
L - 3.0 (AC < 1/10)
L - 3.0 (AC < 1/2)
BSA - 0.0021 (T4A) a
BSA - 0.019 (T4A)
BSA - 0.056 (SB)
0.021 (SB)
LCFA - 0.4 (O) a
BSA - 0.0021 (T4A) a c d e f
FL Fla. (O)
BSA - 2 (K2A) a
Comments
Describes a bioassay method to differentiate between an
algicide (AC) and an algistat (AS). The treated culture was
subcultured as time progressed. Allen's medium was used.
Comment same as above.
Comment same as above.
Experiments were all conducted at 60 F in 1964. The values
were listed as LCgQ.
The values reported are given as LCso-
Concentration reported is for immobilization.
Time for immobilization was 48 hr.
Data cited are for 60 F, but assays were performed at varied
temperatures.
Water chemistry (unspecified) was "controlled" during the
assay period.
Stones heavily populated with larvae were placed in troughs
of running water containing the toxicant. When the larvae
became detached from the rocks and floated away, they
were assumed to have undergone lethal intoxication. The
larvae were exposed to the toxicant for 5 minutes, then
in clean water for 24 hours. At that time the number
detached amounted to 67 percent.
Data reported as LC^rj at 1 5.5 C in 4 days.
At 10.0 Ib/acre, 2 percent control of spatterdock was
obtained.
An attempt was made to correlate the biological action
with the chemical reactivity of selected chemical sub-
stances. Results indicated a considerable correlation
between the aquarium fish toxicity and antiautocatalytic
potency of the chemicals in marked contrast to their
toxicity on systemic administration.
Reference
(Year)
Fitzgerald and
Faust
(1963)
Fitzgerald and
Faust
(1963)
Fitzgerald and
Faust
(1963)
Cope
(1965)
Cope
(1965)
Sanders and
Cope
(1966)
Jamnback and
Frempong-
Boadu
(1966)
Sanders and
Cope
(1968)
Copeland and
Woods
(1959)
Sollman
(1949)
>>
^
•o
m
Z
O
X
-------
Ami ton
oxalate
Amitrol-T
Ametryne
Ametryne
Aminotriazol
Aminotriazole
8
? Aminotriazole
30
O
Amitrole
O
2 Amitrole
•3)
O
O
Carassius
auratus
Lepomis
macrochirus
Lepomis
macrochirus
Crassostrea
virginica
Penaeus
aztecus
Leiostomus
xanthurus
Phytoplankton
Penaeus
aztecus
Oyster
Leiostomus
xanthurus
(juvenile)
Panicum
hemitomum
Oncorhynchus
kisutch
Micropterus
salmoides
Salmon
Daphnia
magna
Lepomis
macrochirus
(eggs)
L. cyanellus
(eggs)
Micropterus
dolomieui
(eggs)
BSCH
BSA
BCFA&
BSA
BCF
BSA
FL
BSA and
CF
BSA
BSA
Fla.
10 (O)*
10
-------
8
m
n Chemical
i-
i
m
£
-o Amitrole T
3D
o
O
c
O Ammate
W
Ammate
Amopyroquin
to
K—
o\
Antimycin A
Antimycin A
Organism
Erimyzon
sucetta
(eggs)
L. macrochirus
(fry)
Daphnia
magna
Althernanthera
philoxeroides
Typha
la ti folia
Channel
catfish
(fingerlings)
Salmo
gairdneri
Salmo
trutta
Salvelinus
f on final is
Salvelinus
namaycush
Ictalurus
punctatus
Lepomis
macrochirus
Salmo
gairdneri
Dorosoma
cepedianum
Salmo
gairdneri
S.
trutta
Esox
leucius
Compostoma
anomalum
Carassius
auratus
Notemigonus
crysoleucas
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
StudyCU Location <2* ppm<3) or NotedW
50 (NTE)
25 (S)
BSA - 40(14.3- acdiq
112.0) (O)
FL Fla. (O)
BSA - 259 (K1A) a
BSA - 35.3 (T2A)
36 (T2A)
40 (T2A)
14 (T2A)
12.5 (T2A)
18.5 (T2A)
BSA - 0.25 (T18 hr) a
BSA - 800 (K1A) adefil
100 (K4A) mp
600 (K1A)
80 (K4A)
400 (K1A)
80 (K4A)
800 (K1A)
1,000 (K1A)
100,000 (K1A)
2,000 (K4A)
2,000 (K1 A)
6OO (K4A)
Comments
Toxicity, in terms of median immobilization concentration
(IC5o), is presented.
At 76 and 120 Ib/acre, respectively, 1 percent control of
alligator weed was obtained while 80 percent control of
cattail was obtained with the higher application rate.
Tap water was used. Considerable additional data are
presented.
Variance and the 95-percent confidence interval (C.I.)
were also determined.
The experiment was conducted at 55 F. Fish were 2-3 in.
long.
Results were reported at 12 C. All fish were killed in 24 hr
by 40 ppm at 22 C.
Results were reported at 12 C.
Results were reported at 12 C.
Results were reported at 12 C. All fish were killed in 24 hr
by 200 ppm at 17 C; by 100 ppm at 22 C.
Results were reported at 12 C. All fish were killed in 24 hr
by 4,000 ppm at 22 C.
Results were reported at 12 C. All fish were killed in 24 hr
by 500 ppm at 22 C.
Reference
(Year)
Crosby and
Tucker
(1966)
Copeland and
Woods
(1959)
Clemens and
Sneed
(1959)
Willford
(1966)
Cope
(1963)
Walker, et al
(1964)
^
•o
m
Z
X
00
-------
8
3 Antimycin A
O
O
Aquaherb
(2,4-D ester)
2 Aqualin
O (acrolein)
O
I
Pimephales
promelas
Catostomus
commersoni
Ictiobus
cyprinellus
Ictalurus
me/as
I.
natalis
I.
punctatus
Eucalia
inconstant
Lepomis
cyanellus
L.
gibbosus
L.
macrochirus
L.
megalotis
Micropterus
salmo/des
Poxomis
annularis
Etheostoma
exile
Perca
flavescens
Stizostedion
vitreum
Cyprinus
carpio
Salmo
gairdneri
S.
trutta
Althernanthera
philoxeroides
Salmo
trutta
Lepomis
machrochirus
FL
FL
BCFA
Wise.
Fla.
2,000 (K1A)
400 (K4A)
220 (K4A)
400 (K4A)
120,000 (K1A)
80,000 (K4A)
80,000 (K1A)
20,000 (K1A)
5,000 (K1A)
2,000 (K1A)
800 (K4A)
2,000 (K1A)
200 (K4A)
1,000 (K1A)
400 (K4A)
2,000 (K1A)
400 (K4A)
6,000 (K1A)
800 (K4A)
2,000 (K1 A)
660 (K1A)
660 (K1A)
660 (K1A)
2,000 (K1A)
600 (K4)
600 (K1A)
80 (K4A)
400 (K1A)
80 (K4A)
(O)
0.046 (T1CFA)
0.079 (T1CFA)
a cd g
Results were reported at 12 C. All fish were killed in 24 hr
by 800 ppm at 22 C.
Results were reported at 12 C.
Results were reported at 12 C.
Results were reported at 12 C. All fish were killed in 24 hr
by 40,000 ppm at 22 C.
Results were reported at 12 C.
Results were reported at 12 C. All fish were killed in 124 hr
by 6,000 ppm at 22 C.
Results were reported at 12 C.
Results were reported at 12 C. All fish were killed in 24 hr
by 800 ppm at 22 C.
Results were reported at 12 C. All fish were killed in 24 hr
by 200 ppm at 22 C.
Results were reported at 12 C. All fish were killed in 24 hr
by 200 ppm at 22 C.
Results were reported at 12 C. All fish were killed in 24 hr
by 4,000 ppm at 22 C.
Results were reported at 12 C.
Results were reported at 12 C.
Results were reported at 12 C.
Results were reported at 12 C. All fish were killed in 24 hr
by 660 ppm at 22 C.
Results were reported at 12 C.
Results were reported at 12 C.
Results were recorded at 12 C. All fish were killed in 24 hr Walker, et al
by 80 ppm at 17 C. (1964)
Results were recorded at 12 C. All fish were killed in 24 hr
by 60 ppm at 17 C.
At 14.2 pounds per acre, only 1-2 percent control of alligator Copeland and
weed was obtained. Woods
(1959)
Spring water was used as dilution water. The chemical was Burdick.etal
found to be toxic to the test fish at concentrations below (1964)
that recommended to control aquatic vegetation.
m
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COMMERCI
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—
OO
Chemical
Aqualm
Aqualin
Aqua San
Aquasan
(colloidal Ag)
Aqua San
2,4-D
Aquathol
Aquatic
Aramite -chloro-
ethyl, -(P-tertiary-
butylphenoxy)
methty -ethyl
sulfite, 15 percent
Aramite
(15%)
Aramite
(tech)
Organism
Carassius
auratus
Carassius
auratus
Ictalurus
nebulosus
Pestia
stratiotes
Microcystis
aeruginosa
Pestia
stratiotes
Spatterdock
Gammarus
lacustris
Richardsonius
balteatus
hydroflox
Lymnaeid
snails
Channel
catfish
(fingerlings)
Rainbow
trout
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study'1* Location'2) ppm(3) or Noted'4)
BSA - 1.0-2.0 (K 3 hr) a
FL California 3.0 (K1) ace
2.0 (K 18 hr)
1.0 (K1)
2.0 (K 18 hr)
FL Fla. (0)
L - 100 (K) a_
FL Fla. (O)
BSA - >320 ae
(T4A)
BSA - 83(T1A) acdef
75 (T2A)
75 (T4A)
BSA - (O)
BSA - >100(K1A) a.
BSA? 0.320 (T4A)
Comments
Fiber glass tanks were used as test containers. Goldfish
were acclimated to the tank habitat for 2 weeks before
testing. Detoxification of the tank occurred within 43
hours when a concentration of 3.0 ppm was applied.
The chemical was applied to Big Bear Lake at 3 ppm.
Within 24 hours all fish in the area died.
Fish were placed in Mentone pond in 3 live cars.
An area between 2 dams separate from Big Bear Lake
was tested. This area was made up of 26 acre-feet of
water at a surface temperature of 72 F between the two
dams. At 1 .0 ppm distress of fish was evident in 1 hour
and most visible fish died in 2 hours. In 1 day, all fish
in live cars were dead.
Fish were placed in Mentone pond in 3 live cars.
At 32.0 Ib/acre, 2 percent control of water lettuce was
obtained.
The chemical was tested on a 5-day algae culture, 1x10^
to 2 x 106 cells/ml, 75 ml total volume. Chu No. 10
medium was used.
At 20.0 and 25.0 Ib/acre, respectively, 8 percent control of
water lettuce was obtained while spatterdock was not
controlled at the higher rate.
Emulsible concentrates were prepared from technical grade
insecticides with acetone as the solvent.
Symptoms prior to death were observed and recorded on
graphs.
Results given were in soft water. Results in hard water were
as follows: 57 (T1 A), 83 (T2A), and 78 (T4A).
Each test container, 500-ml beaker, was filled with ditch
water. Less than 100% mortality occurred in concentrations
of 1:100,000.
Tap water was used. Considerable additional data are
presented.
The values reported are given as LC5g.
Reference
(Year)
St. Amant,
et al
(1964)
St. Amant,
et al
(1964)
Copeland and
Woods
(1959)
Fitzgerald, et al
(1952)
Copeland and
Woods
(1959)
Nebeker and
Gaufin
(1964)
Webb
(1961)
Batte, et al
(1951)
Clemens and
Sneed
(1959)
Cope
(1965)
>
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Aramite
Armazide
ATA (3 amine-
1,2,3, trizole
as the active
ingredient)
A ta brine
Ata brine
Atlas "A"
Atlas 1901
8
3)
O
O
m
2
Atlox
2082 A
(spray
emulsifier
for DDT)
Atrazine
Simocephalus
serrulatus
Daphnia
pulex
Chlorella
pyrenoidosa
Richardsonius
ba/teatus
hydroflox
Microcystis
aeruginosa
Channel
catfish
(fingerlings)
Najas
quadalupensis
Pandalus
montagni
Crangon
crangon
Carcinus
maenas
Card/urn
edule
Oncorhyncus
kisutch
Micropterus
salmoides
(fry)
Ictalurus
punctatus
(fry)
Lepomis
macrochirus
(fry)
BSA
BSA
BSA
FL
BSA
Fla.
BSA
BSA
0.180 (SB)
0.160 (SB)
3.0 (AC 1)
1330(T1A)
1163.3(T2A)
983.3 (T4A)
100 (K)
0.93 (K1A)
(O)
87.2 (T2A)
120.0 (T2A)
150.0 (T2A)
48.5 (T2A)
20.7 (T2A)
5.0 (SB3)
10 (SB3)
10 (SB3)
— Concentration reported is for immobilization. Time for
immobilization was 48 hr.
Data cited are for 60 F, but assays were performed at
varied temperatures. Water chemistry (unspecified) was
"controlled" during the assay period.
— Describes a bioassay method to differentiate between an
algicide (AC) and an algistat (AS). The treated culture
was subcultured as time progressed. Allen's medium was
used.
a c d e f Results given were in soft water.
Results in hard water were as follows: >3600 (T1 A),
>3600 (T2A),and 1370 (T4A).
£ The chemical was tested on a 5-day algae culture, 1 x 106
to 2 x 10^ cells/ml, 75 ml total volume. Chu No. 10
medium was used.
a_ Tap water was used. Considerable additional data are
presented.
At 50.3 Ib/acre, N. quadalupensis was not affected.
Experiments were conducted in tanks holding 10 liters of
seawater at 15 C.
It was shown that the toxicity of this solvent emulsifier
decreased with time, due to evaporation of the solvent.
Atlas 1901 at a concentration of 33.3 ppm killed 95% of
Crangon crangon larvae in 3 hr.
The figure cited is calculated from the data. The compound
is an alkyl sulfonate.
a c d e f p At least 90 percent of the fry survived for a period of 72
hours at the concentration listed.
Sanders and
Cope
(1966)
Fitzgerald and
Faust
(1963)
Webb
(1961)
Fitzgerald, et al
(1952)
Clemens and
Sneed
(1959)
Copeland and
Woods
(1959)
Portmann and
Connor
(1968)
Alderdice and
Worthington
(1959)
Jones
(1965)
3)
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I- Atrazine
O
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m
— Atrazine
> (gesaprime)
r~
TJ
•E Atrazine
O
C
£)
CO
Atrazine
tH
N)
O
Atrazine
(WP)
Atrazine
(granular)
Organism
Phoxinus
phoxinus
Phoxinus
phoxinus
Leiostomus
xanthurus
(juvenile)
Oyster
Crassostrea
virginica
Penaeus
a2tecus
Leiostomus
Phytoplankton
Lepomis
macrochirus
(eggs)
Micropterus
dolomieui
(eggs)
Erimyzon
sucetta
(eggs)
L. macrochirus
(fry)
Lepomis
macrochirus
(eggs)
L. cyanellus
(eggs)
L. macrochirus
Toxicity,
Bioassay Active
or Field Field Ingredient,
StudyCI) Location<2) ppm<3)
BSA - 5.0 (K2A)
1.25 (K2A)
BSA - 10IK2A)
BSA - (O)
BCF - (O)
BCFA & - 1.0 (NTE)
BSA
1.0 (NTE)
L - (0)
10/3(O)
10 (NTE)
5.0 (S)
L - 10 (NTE)
10 (NTE)
10 (S)
Experimental
Variables
Controlled
or Noted^) Comments
a c d e The assays were conducted in a dual aquarium with aeration.
The chemical was still toxic to minnows at 2.5 and 5.0 ppm
in the presence of plants. Kill occurred between 8-15 days.
a d c e The maximum nonlethal dose in 48 hours was 2.5 ppm.
a Water temperature was 28 C. No effect was noticed on
exposure to 1.0 ppm.
a No effect on exposure to the chemical at 1.0 ppm.
— Seawater was pumped continuously into test aquaria.
Salinity, temperature, and plankton fluctuated with
tide, and ambient weather conditions. Some bioassays
with fish were static. Toxicity was reported for the
following:
Oyster — 96-hr EC$Q — Cone, which decreased
shell growth.
Shrimp — 48-hr EC$Q — Cone, which killed or
paralyzed 50% of test animals.
Fish - 48-hr EC^Q ~ Cone, which killed
50%.
Phytoplankton - Percent decrease of CO2 fixation to a
4-hr exposure at 1 .0 ppm chemical
concentration.
— Fertilized fish eggs of indicated species were placed in
1 liter of test solution and allowed to hatch. Toxicity
data are presented as concentration in ppm/number of
days survival. Maximum length of test was 8 days. No food
was added. Small bluegill were tested to find the highest
concentration of chemical which did not cause death in
12 days (S).
— Comment same as above.
Reference
(Year)
Vivier and
Nisbet
(1965)
Vivier and
Nisbet
(1965)
Butler
(1965)
Butler
(1965)
Butler
(1965)
Hiltibran
(1967)
Hiltibrsn
(1967)
g
x
DO
(fry)
-------
Azide
Mayorella
patestinensis
soil amoeba
BSA
(O)
w
to
Bayer 29493
(Baytex)
Banvel D
Baron
Baron
Bay 73
(WP71)
Bay 73
(WP71)
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5
Procambarus
simulans
simulans
Lepomis
macrochirus
Onchorynchus
tshawytscha
Micropterus
salmoides
Channel
catfish
(fingerlings)
Micropterus
salmoides
Micropterus
salmoides
Cyprinus
carpio
FL
Texas
BSA
BSA
BSA
BSA
FL
0.25 (K2)
0.37 (K2)
0.50 (K2)
(L)410(T2A)
(G) 20 (T2A)*
(G) 67.5 (T2A)**
*vermiculite
**attapulgite
2.62 (T1 A)
2.3 (T2A)
4.6 (T1A)
7.2 (K1A)
0.05 (O)
0.10 (K1)
Chino 0.10(0)
Fishery 0.25 (K2)
bass pond, 0.10(O)
Ca|. 0.25 (O)
<± c_ The experiments were carried out in Warburg manometers at
27 C for 4 hr as a pH of 8.0
Azide in concentrations up to 2 x 10"3 M were shown to have
lethal effects on the organism.
Results were compared with controls and expressed in percent
of respiration.
Compared with normal respiration, nonlethal concentrations
of azide increased the respiration of the organism in glucose-
containing solutions.
It was concluded that the respiration of the organism depends
on at least three enzyme systems, which may be distinguished
by their behavior toward azide.
a c d p Bluegills held in wire boxes were not affected at the indi-
cated concentrations. Water temperature was 58 F at the
time of treatment, 49 F at drainage.
Largemouth bass showed distress and some crappies died in
waters treated with 0.33 ppm at 85 F. No deaths were
noted in waters at 80 F.
£ c d e g Toxicity data for 24 and 48 hours are presented for liquid
(L) and granular (G) formulations. Various commercial
formulations were tested. The liquid formulations were
almost invariably more toxic than the granular ones.
a c d e Concentrations were based on percent active ingredient.
Tap water was used. Considerable additional data are
presented.
At 0.05 ppm, 12 percent mortality occurred in 1 day.
Experiments were carried out in fiber glass tubs filled
with well water. Fish weights ranged from 2 to 6 pounds.
For bass:
At 0.10 ppm, no mortality occurred in 1 day.
At 0.25 ppm, 50 percent mortality occurred in 1 day,
and 100 percent occurred in 2 days.
For carp:
At 0.10 and 0.25 ppm, 10 percent mortality occurred.
Reich
(1955)
Lowman
(1965)
Hughes and
Davis
(1965)
Bond, et al
(1960)
Clemens and
Sneed
(1959)
Mulla, et al
(1967)
Mulla, et al
(1967)
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r- Bayer 73
O
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2
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Bayer 73
(tech)
Bayer 73
(WP 71%)
Bayer 73
(tech)
Bayer
4731
Baver 9O18
tttch)
Organism
Sal mo
gairdnerii
Salvelinus
fontinalis
Carassius
auratus
Cyprinus
carpio
Pimephales
prome/as
Catastomus
commersoni
Ictiobus
cyprinellus
Ictalurus
me/as
1. punctatus
Pylodictis
olivaris
Lepomis
cyanel/us
L. macrochirus
L. microlophus
Micropterus
dolomieui
M. salmoides
Perca
flavescens
Talapia
mossambica
1. nebuilosus
Rainbow
trout
Gambusia
af finis
Pteronanys
californica
(naiads)
Leiostomus
xan th urus
(juvenile)
Rainbow
trout
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study*1) Location*2) ppm*3>
BSA - 0.052 (T2A)*
0.016 (T2A)*
0.279 (T2A)
0.139 (T2A)*
0.148 (T2A)
0.103IT2A)
0.081 (T2A)*
0.064 (T2A)
0.096 (T2A)*
0.084 (T2A)
0.043 (T2A)
0.115 (T2A)
0.098 (T2A)*
0.082 (T2A)
0.153(T2A)
0.089 (T2A)
0.097 (T2A)
0.081 (T2A)*
0.150(T2A)
0.071 (T2A)
*12C, other
data at 1 7 C
BSA - 0.320 (T4A)
FL Cal. 1.0 (K1)
BSA - 0.0002 (T4A)
BSA - 0.032 (O)
BSA - 0.320 (T4A)
Experimental
Variables
Controlled Reference
or Noted*4) Comments (Year)
ac Various temperatures (12 and 17 C) and water qualities in Marking and
static bioassays did not influence the toxicity greatly, but Hogan
pH variations in chemically buffered solutions did. (1967)
— The values reported are given as LCso- Cope
(1965)
— Toxicity value is in Ib/acre. Mulla
(1966)
£5.^.11 Data reported as LCso at 15.5 C in 4 days. Sanders and
Cope
(1968)
a Water temperature was 13 C. The figure reported is a Butler
48-hr EC50. (1965)
— The values reported are given as LCso. Cope
(1966)
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Bayer
22408
Bayer
22408
(EC2)
Bayer
25198
(50 percent EC)
Bayer
25141
(50 percent EC)
Bayer
25141
(tech)
Bayer
29492
(EC2)
Bayer
29493
(Baytex)
Bayer
29493
Anopheles
quadrimacula tus
Gambusia
affinis
Rana
catesbeiana
Gambusia
affinis
Gambusia
affinis
Lepomis
macrochirus
Gambusia
affinis
Carassius
auratus
Lepomis
macrochirus
Notemigonus
crysoleugus
Gammarus
lacustris
0
s
m
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Bayer
29493
(tech, 93
percent active
in acetone)
Bayer
29493
(25 percent
EC)
Pteronarcys
californica
(naiad)
Acroneuria
pacifica
(naiad)
Gambusia
affinis
BSA
FL
FL
FL
BSA
FL
BSCH
0.04
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COMMERCIA
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Chemical
Bayer
29493
Bayer
29493
(tech)
Bayer
29493
(Baytex)
Bayer
29493
Bayer
29493
Bayer
29493
Bayer
29493
(Baytex)
Bayer
29952
(EC2)
Bayer
30749
(EC4)
Organism
Chaoborus
as tic to pus
Lepomis
macrochirus
Rainbow
trout
Procambarus
simu/ans
simulans
Pteronarcys
californica
Acroneuria
pacifica
Ephemeral/a
grandis
Gammarus
lacustris
Acroneuria
pacifica
Ephemere/la
grandis
Gammarus
lacustris
Pteronarchys
californica
Acroneuria
pacifica
Pteronarcys
californica
Pimephales
promelas
Lepomis
macrochirus
Lebistes
reticulatus
Gambusia
affinis
Rana
catesbeiana
Gambusia
affinis
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study*1) Location<2) ppm(3) or Noted<4>
BSA - (0) a
BSA - 0.760 (T4A)
BSA - 0.18 (K1A) ac d
BSA - 0.03 (T4A) a
0.005 (T4A)
0.02 (T4A)
0.01 (T4A)
BSA - 0.005 (T4A) a c
0.025 (T4A)
0.014 (T4A)
0.026 (T4A)
BSA & - 0.0051 (T4A) a c d e
CFCH 0.00064 (T30A)
0.00265 (T4A)
0.00360 (T30A)
BSA - 3.3 (T4A) a c d e f
3.1 (T4A)
3.1 (T4A)
FL Ponds in (O)
III.
FL Ponds in (O) -
III.
Comments
Tests were conducted on bluegill sunfish, C. astictopus first
instar larvae, and fourth instar larvae, results on larvae were
as follows:
Fourth instar 0.007 (T1A)
First instar 0.0043 (T1A)
The values reported are given as LC5Q.
Bioassays showed that concentrations to 5.6 ppm in 96 hr
did not kill fingerling channel fish, largemouth bass, and
redear sunfish.
Unspecified chemical characteristics of assay water were
determined by standard methods. General comments were
made concerning "standardized" conditions, use of "soft"
water, and use of emulsifying agents. Additional data are
presented.
Additional TLm data are given.
Additional data are presented.
The toxicity of this substance was not influenced by the
quality of the water (pH, hardness, and alkalinity).
When applied at 0.025 pound/acre active ingredient.
100 percent fish mortality occurred in 1 day.
When applied at 0.4 pound/acre, 5 percent bullfrog
mortality occurred in 1 day.
When applied at 0.8 pound/acre active ingredient, 100
percent fish mortality occurred in 1 day.
Reference
(Year)
Hazeltine
(1963)
Cope
(1965)
Lowman
(1965)
Gaufin, et al
(1965)
Gaufin, et al
(1965)
Jensen and
Gaufin
(1966)
Pickering and
Henderson
(1966)
Mulla, et al
(1963)
Mulla, et al
(1963)
>
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Bayer
34O42
(EC4)
Bayer
37289
(EC4)
Bayer
37289
Bayer
37289
Bayer
37289
(tech)
Bayer
37289
Bayer
37342
(EC4)
Bayer
37343
(EC2)
Bayer
37344
(tech)
Bayer
37344
Bayer
37344
Bayer
38156
(50 per-
cent EC)
Bayer
38156
Gambusia
affinis
Rana
Catesbeiana
Gambusia
affinis
Bufo
boreas
Scophiopus
hammondi
Pteronarcys sp
(nymphs)
Leiostomus
xanthurus
(juvenile)
Rainbow
trout
Pteronarcys
californica
(naiads)
Gambusia
affinis
Gambusia
affinis
Rainbow
trout
Pteronarcys sp
(nymphs)
Pteronarcys
californica
(naiads)
Gambusia
affinis
Leiostromus
xanthurus
Cyprinodon
variegatus
Mugil
cephalus
FL
FL
BSA
BSA
BSA
BSA
FL
FL
BSA
BSA
BSA
FL
BCFCH
Ponds in (O)
III.
Ponds in (O)
III.
0.0001 (T4A)
0.32 (O)
0.240 (T4A)
0.0001 (T4A)
Ponds in (O)
III.
Ponds in (O)
III.
0.640 (T4A)
0.0054 (T4A)
0.0054 (T4A)
Ponds- 0.1 (K1)
Bakers- 0.4 (K1)
field.
Cal.
0.001 (O)
0.001 (0)
0.001 (O)
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r~ Bayer
0 38819
S (tech)
- Bayer
> 38920
•" (EC4)
"O
3D
O
O Bayer
£5 41831
H (EC4)
Bayer
41831
Bayer
41831
(tech)
Bayer
41831
Bayer
CjD 41831
K)
Bayer
46676
(EC2)
Baygon
Baygon
Baytex
Organism
Rainbow
trout
Gambusia
af finis
Rana
catesbeiana
Gambusia
af finis
Rana
catesbeiana
Pteronarcys sp
(nymphs)
Rainbow
trout
Cyprinodon
variegatus
(juvenile)
Pteronarcys
californica
(naiads)
Gambusia
af finis
Prosimulum spp
Cnephia spp
Simulium spp
(larvae)
Pteronarcys
californica
(naiads)
Salmo
gairdnerii
(one wk old
sac fry)
(one mo old
feeding fry)
Toxicity,
Bioassay Active
or Field Field Ingredient,
Studyd) Location<2) ppm(3)
BSA - 0.450 (T4A)
FL Ponds in (O)
III.
FL Ponds in (O)
III.
BSA - 0.0038 (T4A)
BSA - 0.700 (T4A)
BSA - (O)
BSA - 0.004 (T4A)
FL Cal. 0.2 (K1)
LCFA - 0.4(0)
BSA - 0.01 3 (T4A)
BSA - 0.2 (K. 0%)
2.0 (K0%)
0.2 (K0%)
2.0 (K 0%)
Experimental
Variables
Controlled
or IMotedW Comments
— The values reported are given as LC5Q.
— When applied at 0.5 pound per acre active ingredient, 100
percent mortality of both species occurred in 1 day.
- When applied at 1 .6 pounds per acre active ingredients, 44
percent fish mortality occurred in 1 day.
No bullfrog mortality occurred at 0.8 pound per acre in
1 day.
a Experiments were all conducted at 60 F in 1964. The values
were listed as LC5Q.
— The values reported are given as LC5Q-
a Water temperature was 9 C. Fish showed irritation at 1.0
ppm.
a c d e f Data reported as LCso at 15.5 C in 4 days.
— Toxicity value is in Ib/acre.
a Stones heavily populated with larvae were placed in troughs
of running water containing the toxicant. When the larvae
became detached from the rocks and floated away, they
assumed to have undergone lethal intoxication. The larvae
were exposed to the toxicant for 5 minutes, then in clean
water for 24 hours. At that time the number detached
amounted to 83 percent.
a c d e f Data reported as LC^rj at 1 5.5 C in 4 days.
_a.e Results are averages of triplicate tests. Toxicity is reported
as percent mortality (K %).
Reference
(Year)
Cope
(1965)
Mulla, et al
(1963)
Mulla
(1963)
Cope
(1965)
Cope
(1965)
Butler
(1965)
Sanders and
Cope
(1968)
Mulla
(1966)
Jamnback and
Frempong-
Boadu
(1966)
Sanders and
Cope
(1968)
Lewallen and
Wilder
(1962)
-
*O
m
Z
g
X
CD
-------
Baytex
Baytex
Baytex
Baytex
Baytex
8
30
O
O
O
O
§
en
Ben Venue
35 (tech)
Ben Venue
3835 (tech)
Ben Venue
54 (tech)
Benzene
hexachloride
a-benzene
hexachloride
Culex pip/ens
quadrimaculatus
Pteronarcys sp
(nymphs)
Gambusia
affinis
Fundulus
chrysotus
Lepomis
macrochirus
Lepomis
microlophus
Chaenobryttus
gulosus
Oyster
Simocephalus
serrulatus
Daphnia
pulex
Rainbow
trout
Rainbow
trout
Rainbow
trout
Bluegill
Microcystis
aeruginosa
BSA
BSA
BSA &
FL
BCF
BSA
BSA
BSA
BSA
BSA
Benzene hexa- Lymnaeid
chloride snails
(various isomers,
tech)
Benzene hexa- Lymnaeid
chloride snails
(gamma-isomer,
5 percent)
BSA
BSA
(O)
0.0044 (T4A)
Not affected
5(K2)
5(K2>
5(K2)
5(K2)
1.0 (SB4)
0.00092 (SB)
0.00080 (SB)
3.0 (T4A)
0.380 (T4A)
0.480 (T4A)
0.45 (SB)
50 (K)
(0)
(O)
(O)
Tests were conducted in tap water and artificially polluted
tap water. The values reported are the concentration range
for an LC90, 0.0015 to 0.0080 ppm in polluted and 0.0060
to 0.0160 in tap water.
Experiments were all conducted at 60 F in 1964. The values
were listed as
Lewallen and
Wilder
(1963)
Cope
(1965)
Patten and
Gillaspie
(1966)
Butler
(1966)
Sanders and
Cope
(1966)
None of the fish showed overt symptoms of Baytex poisoning
at a concentration of 0.025 ppm which is the equivalent of
an application rate of 0.2 pound per acre. Some mortality
occurred at 2.5 ppm concentration after 48 hours. There
was little danger of acute poisoning to these species of fish
when it was applied at 0.2 pound per acre. Long range effects
of the chemical on other aquatic organisms were studied in
plastic-lined ponds of 300 gallon capacity. Baytex was
applied at 0.2 pound (tech) per acre. All of the Cladocera
and chironomid population at 0.2 pound per acre were almost
completely eliminated in the treated pond within a week.
Copepods, ostracods, hydra, and annelid worms exhibited no
noticeable population change.
Seawater was employed in this experiment.
Concentration reported is for immobilization.
Time for immobilization was 48 hr.
Data cited are for 60 F, but assays were performed at varied
temperatures.
Water chemistry (unspecified) was "controlled" during the
assay period.
The values reported are given as LCsg. Cope
(1965)
Comment same as above. Cope
(1965)
Comment same as above. Cope
(1965)
Bluegills tolerated concentrations of 0.45 ppm. A field study Linduska and
is also described. Surber
(1948)
The chemical was tested on a 5-day algae culture, 1 x 10^ to Fitzgerald, et al
2 x 106 cells/ml, 75 ml total volume. Chu No. 10 medium (1952)
was used.
Each test container (500-ml beaker) was filled with ditch Batte, et al
water. Less than 100% mortality occurred in concentra- (1951)
tions of 1:100,000.
Each test container (500 ml-beaker) was filled with ditch Batte, et al
water. 100% mortality occurred in concentrations of (1951)
1:600,000 and greater.
1
m
O
X
TO
-------
o
o
2
S
m
n Chemical
3> • • '
r~ Benzene hexa-
O chloride
m (99.8 percent
? isomer)
O
> Benzene hexa-
*"" chloride
X
0
o
c
q
en
Benzene hexa-
chloride (alpha
isomer)
0
j
D
Benzene hexa-
chloride (beta
isomer)
Toxicity,
Bioassay Active
or Field Field Ingredient,
Organism Study'1' Location'2* ppm'3)
Lymnaeid BSA - (O)
snails
Oncorhynchus FL Sproat (O)
kisutch Lake,
(fry) Canada
Cylindrospermum L — 2.0 (0)
lichen/forme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (Sol
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
pa/ea (Np)
Cylindrospermum L — 2.0 (O)
licheniforme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Experimental
Variables
Controlled Reference
or NotedW) Comments (Year)
— Each test container (500 ml-beaker) was filled with ditch Batte, et al
water. 100% mortality occurred in concentrations of (1951)
1 :600,000 and greater.
— Tests were in fresh water and seawater. No difference in Jackson
toxicity was observed due to water type. The chemical (1960)
was sprayed as an emulsion from a plane, at the rate of
1 2.3 Ib per 34,848 sq ft. The fish were exposed in boxes
submerged in the water. At a concentration of 1 .38 ppn,,
5 of 15 fish survived 15 minutes; at 0.36 ppm 3 of 15 sur-
vived 32 minutes; at 0.031 ppm, 3 of 15 survived 105
minutes; at 0.034 ppm all fish were dead in 10 hours. The
calculated initial concentration of 6.0 ppm had decreased
to 1.38 in 15 minutes, and to 0.081 in 105 minutes, and
0.34 ppm in 10 hours. It is interesting that fish held more
than a foot below the surface were unharmed.
a Observations were made on the 3rd, 7th, 14th, and 21st days Palmer and
to give the following (T = toxic, NT = nontoxic, PT = Maloney
partially toxic with number of days in parentheses. No (1955)
number indicates observation is for entire test period of
21 days):
Cl - NT
Ma -NT
So - NT
Cv - NT
Gp- NT
Np-NT
a Comment same as above except that: Palmer and
Cl - PT (7) Maloney
Ma-PT(7) (1955)
So -NT
Cv -NT
Gp-NT
Np-NT
£
TO
T3
m
Z
g
x
00
-------
Benzene hexa-
chloride
(delta
isomer)
Benzene hexa-
chloride
(gamma
isomer)
Cylindrospermum
lichen/forme (Cll
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Black fly
(larvae)
Rainbow
trout
Caddisfly
2.0 (O)
FR
Alaskan 0.5 (O)
streams 10 (O)
10(0)
3
J
3
8
5
m
30
O
r
o
m
5
9
Benzene hexa-
chloride
(gamma
isomer)
Benzene hexa-
chloride
(gamma
isomer)
Benzene hexa-
chloride
(gamma
isomer, tech)
Lepomis
macrochirus
Micropterus
salmoides
Cylindrospermum
licheniforme (Cl)
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
Variegata (Cv)
Gomphonema
parvulum (Gp)
NiKschia
palea (Np)
Cylindrospermum
licheniforme (Cl)
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
NiKschia
palea (Np)
B
F
L
L
Auburn,
Ala.
0.1 to 2.0 (K.)
0.1 to 0.2 (K)
2.0 (O)
2.0 (O)
TJ
30
O
O
Comment same as above except that:
Cl — NT
Ma - PT (7)
So - PT (7)
Cv -NT
Gp-T
Np-PT (14)
Palmer and
Maloney
(1955)
The chemical was applied for control of black flies, and
because the acetone solution was most effective, only that
data is reported here. The figures reported are for minimum
effective dosages for black fly larvae and maximum nonlethal
dosages for rainbow trout and caddisfly larvae. The value
given for black flies was the highest dosage tested and was
ineffective.
Aquarium test.
In an earthen pond, 0.18 ppm failed to kill bluegill, bass,
golden shiner and several species of minnows.
Observations were made on the 3rd, 7th, 14th, and 21st days
to give the following (T = toxic, NT = nontoxic, PT =
partially toxic with number of days in parentheses. No
number indicates observation is for entire test period of
21 days):
Cl -NT
Ma-NT
So - NT
Cv - NT
Gp-NT
Np- NT
Gjulian, et al
(1949)
Lawrence
(1950)
Palmer and
Maloney
(1955)
S
m
O
X
00
Comment same as above except that:
Cl - NT
Ma-PT
So - PT (14)
Cv - NT
Gp-PT
Np- NT
Palmer and
Maloney
(1955)
-------
CO
w
o
o
0
s
2
m
o Chemical
I- BHC
0
X
m
5
O
>
r
"D
3D
g BHC
C
q
en
BHC
1
BHC
BHC
BHC
Organism
Black fly
(larvae)
Rainbow
trout
Caddisfly
Blue crab
Marsh fiddler
crab
Red-jointed
fiddler crab
Cyprinodon
variegatus
Leiostomus
xanthurus
Mugil
curema
Fathead
minnow
Bluegill
Goldfish
Guppy
Fathead
minnow
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Pimephales
promelas
Lepomis
macrochirus
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study(1> Location(2) ppm(3)
F Alaskan 0.5 (O)
streams 5.0 (O)
0.5 (0)
FE Bombay (0)
Hook (0)
Island,
Del. (0)
(0)
(0)
(0)
BSA - 2.3 (T4A)
0.79 (T4A)
2.3 (T4A)
21.7 (T4A)
BSA - 2.0 (T4A)
BSA - 2.30 (T4A)
0.79 (T4A)
2.3 (T4A)
2.17 (T4A)
BSA - 2.3 (T4A)
0.79 (T4A)
Experimental
Variables
Controlled
or NotedW Comments
The chemical was applied for control of black flies, and
because the acetone solution was most effective, only that
data is reported here. The figures reported are for minimum
effective dosages, for black fly larvae and maximum non-
lethal dosages for rainbow trout and caddisfly larvae. The
value given for black flies was the highest dosage tested, and
was ineffective.
— The location under study was a salt marsh bounded by
Delaware Bay.
Organisms were confined in cages within the test area.
BHC was applied at 0.1 pound per acre. C. variegatus.
L. xanthurus, and M. curema showed 35 percent
mortality in 7 days.
Blue crabs showed 10 percent mortality when exposed for
7 days in streams and 10 percent mortality in ponds.
Marsh fiddler crabs and red-jointed fiddler crabs showed
mortalities of 80 and 35 percent, respectively, in 7 days.
jj It was the authors opinion that pH, alkalinity and hardness.
within the usual range in natural waters, had little effect on
the toxic effect of the compounds studied. The values given
are from Henderson, Pickering, and Tarzwell, "The Relative
Toxicity of Ten Chlorinated Hydrocarbon Insecticides to
Four Species of Fish" It is interesting that the different
tables from the above book (as reported in this paper)
report widely different values for the same compounds.
This experiment was performed in soft water.
a Comment same as above.
_a d e f Concentrations were based on percent active ingredient.
a Bioassay investigations of the new insecticides indicate that
in general the organic phosphorus compounds are not as
toxic to fish as are the chlorinated hydrocarbons. The
toxicity of most of these materials was not significantly
influenced by water quality. Therefore it is to be expected
that the toxicity of these materials will not differ significantly
in different streams.
Reference
(Year)
Gjulian, et al
(1949)
George, et al
(1957)
Tarzwell
(1959)
Tarzwell
(1959)
Henderson, et al
(1959)
Tarzwell
(1959)
£
3
m
Z
O
X
00
-------
BHC
BHC
BHC
BHC
BHC
U)
BHC
BHC
BHC
O BHC
2 (crude)
m
3)
O
O
I
m
2 BHC
O (emulsion)
-o
3)
O
O
C
O
Algae
Salmo
trutta
Invertebrates
FR
FR
Isle of
Man,
Eng.
Flint
Creek,
Ala.
Heteropneustes
fossilis
Bluegill
Golden shiner
Cyclops sp
BSA
BSA
BSA
Tubifex spp
Limnodrilus spp
Puntius
puckelli
Oncorhynchus
kisuKh
Sesarma
africanum
Micropterus
salmoides
(fry)
Ictalurus
punctatus
(fry)
Lepomis
macrochirus
(fry)
BSA
BSA
BSA
BSA
FR
BSA
Sierra
Leone
0.456 (K)
(O)
0.79 (T4A)
0.062-1.5 (O)
0.062-0.5 (O)
a c d e p
3.0-15 (L4A)
3.8 (T4A)
0.2 (T2A)
65(K<1)
6.5 (K1)
0.65 (SB)
0.065 (NTE)
325
0.05 (SB3)
0.2 (SB3)
0.1 (SB3)
ac d e I m
a c d e f p
Report notes that the fish were not killed, but may have
moved from polluted areas when their normal insect food
was no longer available. Tables give percentage composition
of fauna at 8 collecting stations, given in yards above and
below point of origin.
Conventional treatment in a water purification plant did not
reduce the amount of chemical found in the stream. Data
are given for 4 years 1959-1962, with a range of concentra-
tions. Only the highest value is reported here. Some fish
kill is reported, but species are not identified here. Data
for different seasons are reported. The one listed here is
for summer 1961.
Experiments were conducted in a small battery jar containing
5 liters of water sprayed with 25 cc of BHC (20%). The fish
died in 1 hour and 30 min.
Assays were conducted in soft water at 25 C. Decrease in
brain cholinesterase was measured in fish exposed to the
toxicant.
The 1 .5 ppm value cited is for a 2-day period with the active
ingredient added as a wettable powder to water. Threshold
values, (LD/O) for the BHC dissolved in a number of sol-
vents were somewhat lower. Some of the solvents caused
a 25-fold increase in toxicity of BHC to golden shiner. A
TLm 48 hr of 0.1 25-0.25 ppm BHC was obtained for
Cyclops. Formulations containing oil were more toxic
than dust formulations of BHC.
Toxicity is reported as the mean lethal dose
48, and 96 hours.
for 24,
Hynes
(1961)
Nicholson, et al
(1964)
Tap water was used as diluent. Toxicity data are given as
TLm's in ppm for 24, 48, 96 hr. The pH of the water
averaged 8.3. The study was conducted in India.
The rate of decay of the gamma isomer of BHC is suspected
to be appreciable. The half-life in fresh water would be
somewhere in the vicinity of 7-8 days.
BHC caused complete lack of coordination within 24 hours.
In rice fields, sprays with as low as 325 ppm BHC gave
adequate protection from crabs to young rice seedlings.
Initial results given were derived from contact with aqueous
suspensions of varying concentrations in bioassay evaluations.
At least 90 percent of the fry survived for a period of 72
hours at the concentration listed.
Mathur
(1964)
Weiss
(1964)
Meyer
(1965)
Whitten and
Goodnight
(1966)
Rao, et al
(1967)
Velsen and
Alderdice
(1967)
Jordan
(1955)
Jones
(1965)
m
O
X
00
-------
o
o
s
s
m
o Chemical
<~ BHC (45%
2 gamma isomer)
5 BHC (45%
Q gamma isomer)
r BHC
•o (tech,
0 15.5%)
0
C
en
BHC
(WP)
tjO Bidrin
U> (tech )
(0
Bidrin
Bomyl (EC4,
GC-3707)
Borate
BP 1 002
Buramine
Organism
Oyster
Oyster
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Micropterus
salmoides
(fry)
Ictalurus
punctatus
(fry)
Lepomis
macrochirus
(fry)
Procambarus
dark!
Pteronarcys
californica
(naiads)
Gambusia
affinis
Salmo
gairdnerii
Panda/us
montagui
Crangon
crangon
Carcinus
maenas
Cardium
edule
Semotilus
atromaculatus
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study (D Location<2) ppm<3) or Noted*4)
BCF - 1.0 (O) a
BCF - 0.36 (O) a
BSA - 15(T4A) ^becd_f_
5.I (T4A)
15 (T4A)
14 (T4A
BSA - 0.2 (SB3) acdef
0.4 (SB3)
0.5 (SB3)
BSA - 3.0 (T3A) a c d o
BSA — 0.43 (T4A) _§_£
•o
m
z
D
X
CO
"critical range" (CR), which was defined as that concentra-
tion in ppm below which the 4 test fish lived for 24 hr and
above which all test fish died. Additional data are presented.
-------
C-56
C-2059
C-2059
C-8514
Lepomis
macrochirus
Micropterus
salmoides
Lepomis
macrochirus
Lepomis
macrochirus
Oncorhynchus
kisutch
Camphene
(chlorinated)
Captan
(N-trichloro-
methylthio-4-
cyclohexene-1,2-
dicarboxyimide)
Carbaryl
Silverling
minnows
Spotfin
shiner
Creek
chub
Fall fish
Blacknosed
dace
Brachydanio
rerio
(larvae)
Procambarus
clarkii
BSA
BSA
BSA
BSA
BSA
30(T2A)
35 (T2A)
55 (T1A)
90(T1A)
21.5 (T2A)
0.04 (K)
a b e
a b e
BSA
FO
Crowley
La.
30(T1A)
1.0(0)
(T 70 min)
(O)
c d e p
8
m
3)
o
Carbaryl
O
X Carbaryl
Prosimulum spp
Cnephia spp
Simulium spp
(larvae)
Australorbis
glabratus
LCFA
0.4 (O)
BSA and
FL
Puerto Rico (O)
The response of bluegill and bass fingerlings to nine agricul-
tural chemicals as determined by bioassay using river water
is presented in this report. Bluegills were more tolerant of
the chemicals tested than bass.
This report is a simple and straightforward determination of
a median tolerance limit for a selected group of herbicides.
Comment same as above.
Physical instability of this formulation would suggest that
toxicity in the aquatic environment could be a problem
if the preparation is to be used in or near water courses
under field conditions.
The "Threshold" for bluegills was 0.01 ppm. A field study
in W. Va. is also described.
TLm was 70 min for larvae. Ninety-eight percent of the
larvae died in 90 min.
Experiment was conducted in a flooded rice field Area
was divided into 4 blocks with a fence restricting crawfish
to the desired area. The rearing of crawfish in rice fields
is of considerable commercial importance in Louisiana.
It is fortunate that the chemicals discussed in this report
had no untoward effect at the levels used. The chemical
was applied at the rate of 0.8 Ibs/acre.
Stones heavily populated with larvae were placed in troughs
of running water containing the toxicant. When the larvae
became detached from the rocks and floated away, they
were assumed to have undergone lethal intoxication. The
larvae were exposed to the toxicant for 5 minutes, then in
clean water for 24 hours. At that time the number
detached amounted to 47 percent.
Seven of the tested compounds failed to meet acceptability
criteria—that is, complete kill after 6-hr exposure to 10 ppm.
They were not used in field tests. Field tests showed WL
8008 to be highly effective. All others failed.
Davis and
Hardcastle
(1959)
Hughes and
Davis
(1967)
Hughes and
Davis
(1967)
Velsen and
Alderdice
(1967)
Linduska and
Surber
(1948)
Dawood and
Dazo
(1966)
Hendrick, et al
(1966)
m
O
X
03
Jamnback and
Frempong-
Boadu
(1966)
Seiffer and
Schoof
(1967)
3D
O
O
C
-------
o
o
s
£
m
o Chemical
r~ Carharyl
O
X
m
S
0
r~
TJ
3)
o
O
C
O Carbo-
v> phenothion
(Trithion)
Carbo-
phenothion
(EC4)
Carbo-
phenothion
(EC4)
Casoron
OJ
-**• Casoron
Casoron
Casoron
Casoron
(WP)
Catechol
Ceresan M
Bioassay
or Field
Organism Study^)
Pteronarcys BSA
ca/ifornica
(naiads)
Pteronarcella
badia
(naiads)
Claasenia
sabulosa
(naiads)
Culex pipiens BSA
quadrimacula tus
Gambusia F L
affin/s
Rana
catesbeiana
Micropterus BSA
sa/moides
Redear BSA
sunfish
Pteronarcys sp BSA
(nymphs)
Simocepha/us BSA
serrulatus
Daphnia
pu/ex
Rainbow BSA
trout
Bluegill
Rainbow BSA
trout
Bluegill
Microcystis L
aeruginosa
Channel BSA
catfish
(fingerlings)
Toxicity,
Active
Field Ingredient,
Location(2) ppm'3)
0.0048 (T4A)
0.0017 (T4A)
0.0056 (T4A)
(0)
Ponds in (O)
III.
1.0(0)
(0)
6.6 (T4A)
5.8 (SB)
3.7 (SB)
22 (T2A)
20 (T2A)
18 (T4A)
10 (T4A)
100 (K)
1.8 (K1A)
Experimental
Variables
Controlled
or Noted(4) Comments
a c d e f Data reported as LCso at 15.5 C in 4 days.
c Tests were conducted in tap water and artif ically polluted
tap water. The values reported are the concentration range
for an LCgQ, 0.085 to 0.280 ppm for polluted, and 0.01 7 to
0.034 ppm for tap water.
— When applied at 0.2 and 1 .6 pounds per acre active ingredient,
98 and 100 percent fish mortality occurred respectively in
1 day.
When applied at 0.4 pound per acre, 100 percent bullfrog
mortality occurred in 1 day.
a e At 1.0 ppm, 10 percent mortality occurred in 1 day. Experi-
ments were carried out in fiber glass tubs filled with well
water. Fish weights ranged from 2 to 6 pounds.
a No mortality was noted in fish weighing 3 g with concentra-
tions of 20,000 mg/1 at 48 hr.
^ Experiments were all conducted at 60 F in 1964. The
values were listed as \-C$Q.
— Concentration reported is for immobilization.
Time for immobilization was 64 hr.
Data cited are for 78 F, but assays were performed at
varied temperatures.
Water chemistry (unspecified) was "controlled" during the
assay period.
— Data are given as LC$Q,
a This is an estimated LCsg value at temperatures from 55 to
75 F.
a_, etc The chemical was tested on a 5-day algae culture, 1 x 10^ to
2 x 106 cells/ml, 75 ml total volume. Chu No. 10 medium
was used.
_a Tap water was used. Considerable additional data are
presented.
Reference
(Year)
Sanders and
Cope
(1968)
Lewallen and
Wilder
(1963)
Mulla, et al
(1963)
Mulla, et al
(1967)
Cope
(1963)
Cope
(1965)
Sanders and
Cope
(1966)
Bohmont
(1967)
Cope
(1965)
Fitzgerald, et al
(1952)
Clemens and
Sneed
(1959)
•o
-o
m
z
o
X
CD
-------
OJ
Chem Ban
Chem Fish
Special
Chem Mite
Chem Sen 56
Chemagro
Chemagro
4497
Chlorax
Chlordane
Chlordane
Chlordane
m
3
Q Chlordane
>
r
o
m
T3
•3)
O
O
Channel
catfish
(fingerlings)
Channel
catfish
(fingerlings)
Channel
catfish
(fingerlings)
Channel
catfish
(fingerlings)
Leiostomus
xanthurus
(juvenile)
Leiostomus
xanthurus
(juvenile)
Channel
catfish
(fingerlings)
Bluegill
Black fly
(larvae)
Rainbow
trout
Caddisfly
Lepomis
macrochirus
Carassius
auratus
Micropterus
salmoides
Fathead
minnow
Bluegill
Goldfish
Guppy
BSA
BSA
BSA
BSA
BSA
BSA
BSA
FR
BSA
Auburn,
Ala.
BSA
26 (K1A)
0.56 (K1A)
1.29 (K1A)
97.7 (K30hr A)
0.032 (O)
0.032 (O)
3157 (K1A)
(O)
Alaskan 0.5 (O)
streams 20 (0)
10(0)
0.1 (NTE)
0.2 (K)
0.052 (T4A)
0.022 (T4A)
0.082 (T4A)
0.19 (T4A)
Comment same as above.
Comment same as above.
Comment same as above.
Comment same as above.
Water temperature was 21 C. The figure reported is a
48-hr EC50.
Comment same as above.
Tap water was used. Considerable additional data are
presented.
At 1 Ib per acre, 87 percent of the bluegill sunfish were
killed. At 0.5 Ib per acre most of the bluegills as well as
other species survived.
The chemical was applied for control of black flies, and
because the acetone solution was most effective, only that
data is reported here. The figures reported are for mini-
mum effective dosages of black fly larvae and maximum
nonlethal dosages for rainbow trout and caddisfly larvae.
The value given for black flies was the highest dosage
tested. The value given for trout was also the highest
tested.
At this concentration, there was no apparent effect.
At this concentration, bluegill and bass were killed, but
goldfish survived.
It was the authors opinion that pH, alkalinity and hardness,
within the usual range in natural waters, had little effect on
the toxic effect of the compounds studied. The values given
are from Henderson, Pickering, and Tarzwell, "The Relative
Toxicity of Ten Chlorinated Hydrocarbon Insecticides to
Four Species of Fish". It is interesting that the different
tables from the above book (as reported in this paper)
report widely different values for the same compound.
This experiment was performed in soft water.
Clemens and
Sneed
(1959)
Clemens and
Sneed
(1959)
Clemens and
Sneed
(1959)
Clemens and
Sneed
(1959)
Butler
(1965)
Butler
(1965)
Clemens and
Sneed
(1959)
Linduska and
Surber
(1948)
Gjulian, et al
(1949)
Lawrence
(1950)
Tarzwell
(1959)
-------
o
o
s
s
m
o Chemical
r~ Chlordane
0
m
S
O
r~
-o
O
0
c
^ Chlordane
C/l
Chlordane
(100%)
Chlordane
OJ
Chlordane
(75%)
Chlordane
Chlordane
Organism
Fathead
minnow
Channel
catfish
(fingerlings)
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticu/atus
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticu/atus
Pimephales
promelas
Pimephales
promelas
Lepomis
macrochirus
Oncorhynchus
kisutch
Oncorhynchus
tshawytscha
Salmo
gairdnerii
Gasterosteus
aculeatus
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study ( 1 ) Location ( 2 ) ppm (3 )
BSA _ 0.069 (T4A)
BSA - 0.74 (K1A)
BSA - 0.069 (T4A)
0.022 (T4A)
0.082 (T4A)
0.19 (T4A)
BSA - 0.05 (T4A)
0.01 (T4A)
0.08 (T4A)
0.19 (T4A)
BSA - 0.18 (T4A)
BSA - 0.052 (T4A)
0.022 (T4A)
BSA - 56 (T4A)
57 (T4A)
44 (T4A)
90 (T4A)
Experimental
Variables
Controlled
or Noted'*) Comments
a It was the authors opinion that pH, alkalinity and hardness,
within the usual range in natural waters, had little effect on
the toxic effect of the compounds studied. The values
given are from Henderson, Pickering, and Tarzwell, "The
Relative Toxicity of Ten Chlorinated Hydrocarbon Insecti-
cides to Four Species of Fish" It is interesting that the
different tables from the above book (as reported in this
paper) report widely different values for the same compounds.
The experiment was performed in hard water.
a Tap water was used. Considerable additional data are
presented.
a b e c d f Dilution water was usually soft although some studies were
conducted with hard water.
a d e f Concentrations were based on percent active ingredient.
^ b e c d f Dilution water was usually soft although some studies were
conducted with hard water.
a Bioassay investigations of the new insecticides indicate that
in general the organic phosphorus compounds are not as
toxic to fish as are the chlorinated hydrocarbons. The
toxicity of most of these materials was not significantly
influenced by water quality. Therefore it is to be expected
that the toxicity of these materials will not differ signifi-
cantly in different streams.
a_c d^ Chemical dissolved in acetone. TLm expressed in ppb.
Reference
(Year)
Tarzwell
(1959)
Clemens and
Sneed
(1959)
Henderson, et al
(1959)
Henderson, et al
(1959)
Henderson, et al
(1959)
Tarzwell
(1959)
Katz
(1961)
=£
•o
m
z
o
X
DO
-------
Chlordane
OJ
-J
Chlordane
(EC 7.5)
Chlordane
Gammarus
lacustris
lacustris
Gambusia
affinis
Rana
catesbeiana
(tadpoles)
Bluegill
BSA
(O)
FU
Cal.
BSA
Chlordane
Chlordane
(tech)
Chlordane
Pteronarcys sp
(nymphs)
Rainbow
trout
Bluegill
Simocephalus
serrulatus
Daphnia
pulex
BSA
BSA
BSA
Chlordane
(75% emulsion)
Chlordane
8
m
30
o
Green
sunfish
Vascular
plants
Algae
Chubs
Largemouth
bass
Clams
BSA
FL
Tule
Lake,
Ore.
0.5 (O)
0.022 (T4A)
0.015 (T4A)
0.0078 (T4A)
0.040 (T4A)
0.020 (SB)
0.029 (SB)
1.0 (NTE)
(O)
a e p The mortality might have been partially due to the McDonald
susceptibility of the organism to higher temperatures, (1962)
toxicity from extended exposure to copper electrodes
(used to shock the organism to determine death), or the
increase of CO2- Results were expressed as LTsfj; for
example, at 0.5 ppm, 50 percent of the shrimp were
killed in 235 (±35) min.
a c Mixed populations of the indicated test species contained Mulla
in cages were exposed to various insecticidal chemicals (1963)
applied as dilute sprays to ponds 1/16 acre in size. The
indicated toxicant concentration is in Ib/acre, and
resulted in a 70 percent mortality for the fish, and a
0 percent mortality for the tadpoles in 24 hr.
a Assays were conducted in soft water at 25 C. Decrease Weiss
in brain cholinesterase was measured in fish exposed (1964)
to the toxicant.
ji Experiments were all conducted at 60 F in 1964. The Cope
values were listed as LC5Q. (1965)
— The values reported are given as LCgo- c°Pe
(1965)
— Concentration reported is for immobilization. Sanders and
Time for immobilization was 48 hr. Cope
Data cited are for 60 F, but assays were performed at (1966)
varied temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
— Fish were repelled by concentrations of 5, 10, and 20 ppm. Summerfelt
No lethal effects were noted at concentrations less than and Lewis
5 ppm. (1967)
— The amount of chemical applied as a spray was not specified. Godsil and
Plants contained 1.5 to 6.0 ppb. Algae contained 1.7 to Johnson
50.0 ppb. Chubs were analyzed to show a content of 8.0 to (1968)
24.0 ppb. Bass contained 7.5 to 43.0 ppb. Clams contained
2.0 to 25.0 ppb. The water contained 0.01 to 0.51 ppb.
m
z
O
X
o
in
2
£
30
O
O
c
-------
o
o
s
m
o Chemical
I— Chlordane
O
I
m
2
o
r~
33
o
o
C
3
Organism
Labeo
rohita
Chamna
punctatus
Mastocembelus
pancalus
Trichogaster
fascia tus
Mystus
vina tus
Nandus
nandus
Puntius
sophore
He terop neustes
fossilis
Amphipnous
cuchia
Phytoplankton:
Bioassay
or Field
Study d)
BSA
Toxicity, Experimental
Active Variables
Field Ingredient, Controlled
Location^) ppm(3) or Noted(4)
0.0000709 (T7A) a e
0.0001 (K40hr)
0.001 (K 115hr)
0.0001 (T7)
0.0008 (T7)
0.0016 (K51 hr)
0.002 (K 130 hr)
0.00032 (T7)
0.002 (K60hr)
0.001 (T7)
0.0025 (K 25 hr)
0.0008 (T7)
0.005 (K 18 hr)
0.0008 (T7)
0.005 (K 51 hr)
0.001 (T7)
0.08 (K45hr)
0.01 (T7)
0.001 to 0.50 (K7)
Comments
Chlordane was found to be highly toxic but not selective
to fish. Its prolonged toxicity makes it unsuitable for
fishery management and it is recommended that chlordane
not be used in fields adjacent to fishery reservoirs.
Reference
(Year)
Konar
(1968)
Volvox, Pandorina, Closterium
v
OJ
00 Chlordane
Chlorea
(granular)
Zooplankton:
Cyclops
Naupllus
Daphnia
Cypris
Pteronarcys
californica
(naiads)
Althernanthera
philoxeroides
A/a/as
quada/upensis
Spatterdock
Ceriodaphnia
Diaptomus
Gastrotrica
Brachionus
BSA
FL
0.10 to 0.50 (K7)
0.01 5 (T4A) !_cd^f_
Fla. (0)
Gastrotrica were not affected and Brachionus was not killed
at 0.10 ppm.
Data reported as LCgrj at 15.5 C in 4 days.
The degree of control was as follows:
A. philoxeroides (393 Ib/acre) - 30 percent
N. quadalupensis (393 Ib/acre) — none
spatterdock (454 Ib/acre) - 2 percent
>
•o
m
Z
^j
Sanders and —
Cope ^
(1968) CO
Copeland and
Woods
(1959)
-------
Chloretone
vo
Chlorophenyl
Chlorothion
Chlorothion
Chlorothion
8
m
3)
O
^ Chlorothion
O
m Chlorothion
2
O
•3)
O
O
c
Brachydanio
rerio
(fertilized
eggs, 2 hr)
(fertilized
eggs, 24 hr)
BSA
Salmo
gairdnerii
Pimephales
promelas
Fathead
minnow
Pimephales
promelas
Pimephales
promelas
Lepomis
macrochirus
Micropterus
salmoides
Notemigonus
crysoleucas
Carassius
auratus
BSA
BSA
BSA
BSA
BSA
BSA
1OO*
(K 37 mini
50*
(K 3-1/4 hr)
10* (K5hr)
5*
(SB 1-1/2 hr)
1MNTE)
100*
(K 37 min)
50*
(K 7-1/2 hr)
10*
(K119hr)
5*
(SB 1-1/2 hr)
1* (IMTE)
*% of saturated
solution
975 (T1A)
925 (T2A)
3.3 (T4A)
3.2 (T4A)
^ e
3.2 (T4A)
3.2 (T4A)
0.1 (O)
0.1 (0)
0.1 (0)
0.1 (O)
t±d e f
_a£d_f_
Saturated solutions and dilutions of saturated solutions were
used. 4.5 g of the chemical saturated 500 ml of water at
RT. Percent dilutions used were 100, 50, 10, 5.0, 4.0, 3.0,
2.0, and 1.0. Immobilization times are given. Histological
observations were also made.
Blumenkrantz
(1956)
Most of the weed-killer formulations in this study consisted of
more than one substance, i.e., oils, emulsifiers, stabilizers, and
other adjuvants.
Tests were performed in both hard and soft water. Additional
tolerance limit values are given.
It was the authors opinion that pH, alkalinity and hardness,
within the usual range in natural waters, had little effect on
the toxic effect of the compounds studied. The values
given are from Henderson, Pickering, and Tarzwell, "The
Relative Toxicity of Ten Chlorinated Hydrocarbon Insecti-
cides to Four Species of Fish". It is interesting that the
different tables from the above book (as reported in this paper)
report widely different values for the same compounds.
This experiment was performed in hard water.
Bioassay investigations of the new insecticides indicate that in
general the organic phosphorus compounds are not as toxic
to fish as are the chlorinated hydrocarbons. The toxicity of
most of these materials was not significantly influenced by
water quality. Therefore it is to be expected that the
toxicity of these materials will not differ significantly in
different streams.
Concentrations were based on percent active ingredient.
This paper reports the effect of insecticides in reducing the
anticholinesterase in a fish brain within 2-8 hours. The
inhibition of the enzyme was a function of the concentra-
tion of the insecticide, extent of exposure, and specific
chemical nature of the compound.
Alabaster
(1956)
Henderson and
Pickering
(1958)
Tarzwell
(1959)
m
O
X
oo
Tarzwell
(1959)
Henderson, et al
(1959)
Weiss
(1959)
-------
COMMERCIA
r-
0
i
m
2
2
r~
T>
O
O
;^
tn
s
O
Chemical
Chlorothion
Chlorothion
(tech,
98 percent)
Chlorothion
Chlorothion
Chloroxuron
(granular)
Chloroxuron
(WP)
CIPC
Cleanosol
Organism
Pimephales
promelas
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Carassius
auratus
Lepomis
macrochirus
Notemigonus
crysoleucus
Bluegill
Lepomis
macrochirus
Lepomis
macrochirus
Lepomis
macrochirus
Micropterus
salmoides
Pandalus
montagni
Crangon
crangon
Carcinus
maenas
Cardium
edule
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study'1' Location*2* ppm'3>
BSA - 0.5 (O)
BSA - 2.8 (T4A)
0.71 (T4A)
2.3 (T4A)
1.2 (T4A)
BSCH - 1.0(O)*
* no response.
15 days
BSA - 0.7 (T4A)
BSA - 60 (T1A)
BSA - 25 (T1A)
BSA - 12 (T2A)
10 (T2A)
BSA - 32 (T2A)
44 (T2A)
102 (T2A)
19.2 (T2A)
Experimental
Variables
Controlled
or Noted'4) Comments
— The degree of reaction to the cholinesterase-inhibiting
insecticides is not only a function of time and concentra-
tion, but also of chemical and biological species. This
paper reports many analyses of brain cholinesterase
activity which is expressed as percentage of normal.
The data are reported as LT^Q which was the time
required for 0.5 ppm of the chemical to kill 50 percent
of the fish. The \-T^Q for the fathead was 72 hr.
acde Soft water primarily was the test medium. TLm's reported
for 24, 48, and 96 hr. Acetone or alcohol used as solvent
or carrier in most cases.
acde Toxicity was determined by measuring acetylcholinesterase
activity in the brains of fish. Concentrations are given in
ppb as either response or not response in 15 or 30 days.
a Assays were conducted in soft water at 25 C. Decrease in
brain cholinesterase was measured in fish exposed to the
toxicant.
a b e This report is a simple and straightforward determination of
a median tolerance limit for a selected grou p of herbicides.
a b e Comment same as above.
a c o This response of bluegill and bass fingerlings to nine
agricultural chemicals as determined by bioassay using
river water is presented in this report. Bluegills were
more tolerant of the chemicals tested than bass.
a_e Experiments were conducted in tanks holding 10 liters of
of sea water at 25 C.
It was shown that the toxicity of this solvent emulsifier
decreased with time, due to evaporation of the solvent.
Cleansol at a concentration of 33.3 ppm killed 100% of
Crangon crangon larvae in 3 hr.
Reference
(Year)
Weiss
(1961)
Pickering, et al
(1962)
Weiss and
Gakstatter
(1964)
Weiss
(1964)
Hughes and
Davis
(1967)
Hughes and
Davis
(1967)
Davis and
Hardcastle
(1959)
Herbert, et al
(1965)
3^
-o
m
z
D
X
03
-------
Clostridium
botulinum
(Type A
toxin)
CMU
CMU
Conco
LCP-12
Coral
Co-ral
Co-Ral
m
o
m
-O
30
O
O
Co-Ral
Pimephales
promelas
Algae
(Mixed
culture)
Lepomis
macrochirus
Lepomis
cyanellus
Pomoxis
nigromaculatus
Hyborhyncus
notatus
Lebistes spp
Channel
catfish
(fingerlings)
Daphnia
magna
Pimephales
promelas
Lepomis
macrochirus
Pimephales
promelas
Lepomis
macrochirus
Oncorhynchus
kisutch
Salmo
gairdnerii
Gasterosteus
aculeatus
Micropterus
salmoides
Pimephales
promelas
BSA
LBSA
BSA
BSA
BSA
BSA
BSA
BSA
(O)
0.5-1.0 (K)
(O)
a c d e
75.9
(K25hrA)
694 (T1A)
290 (T2A)
204 (T3A)
>18 (T4A)
0.18 (T4A)
>18(T4A)
0.18 (T4A)
15,000 (T4A)
1,500 (T4A)
1,862 (T4A)
0.5 (0)
0.5 (O)
adef
a c d e
Fish survived high does rates of 102,000 mouse LDgo/ml
for 24 hr and 17,000 mouse LDso/ml for 96 hr. Fish
cannot be used to detect this chemical at levels critical
for man.
Tests with 22 species of algae indicated that 0.5 to 1.0
ppm CMU prevented growth. No adverse effects on the
fish were found in 23 days with concentrations of 10,
20, and 40 ppm.
Pickering and
Henderson
(1959)
Fitzgerald
(1958)
Tap water was used. Considerable additional data are
presented.
When emulsifier was mixed with crude oil, the TLm value
was one-half the values cited.
Concentrations were based on percent active ingredient.
Clemens and
Sneed
(1959)
Dowden
(1962)
Henderson, et al
(1959)
Bioassay investigations of the new insecticides indicate that
in general the organic phosphorus compounds are not as
toxic to fish as are the chlorinated hydrocarbons. The
toxicity of most of these materials was not significantly
influenced by water quality. Therefore it is to be expected
that the toxicity of these materials will not differ significantly
in different streams.
Chemical dissolved in acetone. TLm expressed in ppb.
The degree of reaction to the cholinesterase-inhibiting
insecticides is not only a function of time and concentra-
tion, but also of chemical and biological species. This
paper reports many analyses of brain cholinesterase
activity which is expressed as percentage of normal. The
data are reported as LTso which was the time required
for 0.5 ppm of the chemical to kill 50 percent of the fish.
For bass the LTsg was 36 hr and for the fathead 72 hr.
Tarzwell
(1959)
Katz
(1961)
Weiss
(1961)
-------
0
o
s
m
g Chemical
r- Co-Ral
<"> (tech
S 97.5
5 percent)
o
> Co-Ral
r~
T>
g Co-Ral
0
C
— 4
ff>
CO-RAL
Co Ral
s
to
Co-ral
(97.5% active
in acetone)
Organism
Carassius
auratus
Lebistes
reticulatus
Chaoborus
as tic top us
Carassius
auratus
Lepomis
macrochirus
Notemigonus
crysoleucus
Cyprinodon
variegatus
(juvenile)
Salmo
gairdenerii
Salmo
trutta
Salvelinus
fontinalis
Salvelinus
namaycush
Ictalurus
punctatus
Lepomis
macrochirus
Hexagenia sp
Hydropsyche sp
(larva)
Bluegill
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study '1) Location'2) ppm<3) or Noted'4)
BSA - 18 (T4A) acde
0.56 (T4A)
BSA - 0.39 (T1A) a_
BSCH - 1.0 (O)* ^cd^
1.0? (O)**
1.0 (O)*
* no response.
15 days
"response,
15 days
BSA - 0.28 (O) a
BSA - 0.55 (T2A) £f
0.73 (T2A)
0.8 (T2A)
4.0 (T2A)
6.8 (T1A)
8.0 (T2A)
BSA - 0.43 (T1 A) ae
0.005 (T1A)
1.4 (T1A)
Comments
Soft water primarily was the test medium. TLm's
reported for 24, 48, and 96 hr. Acetone or alcohol
used as solvent or carrier in most cases.
Toxicity value given is for the fourth instar larvae.
Toxicity was determined by measuring acetylcholinesterase
activity in the brains of fish. Concentrations are given in
ppb as either response or not response in 1 5 or 30 days.
Water temperature was 1 2 C. The figure reported is a
48-tir EC50.
Variance and the 95-percent confidence interval (C.I.)
were also determined.
Dissolved oxygen was measured before and after assay.
Assays were conducted in Mississippi River water.
Reference
(Year)
Pickering, et al
(1962)
Hazeltine
(1963)
Weiss and
Gakstatter
(1964)
Butler
(1965)
Willford
(1966)
Carlson
(1966)
•o
m
Z
O
00
-------
Cube
powder
(7.3%
rotenone)
Cube root
E
Cumate
Cuprose
2, 4-D
I
m
3)
O
>
O
m
2, 4-D
Cyprinus
carpio
Micropterus
satmoides
Pimephales
promelas
Carassius
auratus
Lepomis
macrochirus
L. cyanellus
Notemigonus
crysoleucas
Icta/urus
nebulosus
marmoratus
Pimephales
promelas
Pimephales
promelas
Lepomis
macrochirus
Chlorella
pyrenoidosa
Killifish
(minnow)
Eupomotis
gibbosus
Ameiurus
nebulosus
Eichornia
crassipes
BSA
BSA
BSA
BSA
FR
Fla.
0.115 (L3)
0.164 (L3)
0.200 (L3)
0.218 (L3)
0.268 (L3)
0.246 (L3)
0.620 (L3)
0.346 (L3)
0.066 (T4A)
a cd e i
0.071 (T4A)
0.32 (T4A)
20 (AS 1)
2000 (O)
1000(O)
2000 (O)
(O)
a c d f g
a c d e f
Such variables as temperature, species, and size of fish
were studied. Toxicity is expressed as LD5gfor 72 hr.
Smaller concentrations of rotenone were required when
used in conjunction with sulfoxide. The data shown are
for 70 F. The chemical was considerably more toxic at
this temperature.than at 40 F for all fish species.
Hester
(1959)
Test water was spring water diluted with distilled water.
Removal of toxic chemicals by carbon adsorption,
chlorine and chlorine dioxide treatment, and alum
coagulation was studied. The most effective method to
remove fish poisons was by use of activated charcoal
adsorption.
The toxicity of this substance was influenced by the
quality of the water (pH, hardness, alkalinity). The
chemical was more toxic in soft water.
Describes a bioassay method to differentiate between an
algicide (AC) and an algistat (AS). The treated culture
was subcultured as time progressed. Allen's medium was
used.
Temperature was held at 20-25 C, and the water was
aerated by circulating water pumps. Data reported as
deaths in 7 days. Upper safe limit concentrations were
established.
Control of water hyacinth was affected with 1:1140 dilution
applied to 100-150 sq ft plots. Author notes that no adverse
effects to the water fauna (fingerling fish, etc.) were observed
up to the time of disappearance of the water hyacinth. The
roots were not killed, but did not readily produce shoots.
Addition of carbowax as a wetting atent did not improve
herbicidal action.
Cohen, et al
(1961)
Pickering and
Henderson
(1966)
Fitzgerald and
Faust
(1963)
Harrison and
Rees
(1946)
Hildebrand
(1946)
m
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o
X
00
o
-o
3D
O
O
c
-------
o
o
2
m
o Chemical
>
r 2.4-D
m
o
>
r
TJ
3)
O
D
C
q
OT 2,4-D
tp 2,4-D
£
4*
2,4-D
2,4-D
2,4-D
2,4-D
(granular)
2,4-D/
2.4-5T
+ TCA
Bioassay
or Field
Organism StudyC"
Eichhornia FRLO
crassipes
Alternanthera
philoxero/des
Cy/indrospermum L
lichen/forme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Cp)
Nitzschia
palea (Np)
Salmo BSA
gairdnerii
Salmo BSA
gairdnerii
Salmo BSA
gairdnerii
Lepomis BSA
macrochirus
Micropterus
salmoides
Nympheae sp FL
Myriophyllum
brasiliense
Myriophyllum
heterphyllum
Brasen/a
schreberi
Utricularia sp
Althernanthera FL
philoxeroides
Toxicity,
Active
Field Ingredient,
Location(2) ppm(3)
Mississippi (O)
R., Delta,
La.
2.0 (O)
2300(71 A)
2050 (T2A)
4.4 (T1 A)
3.3 (T2A)
3.0 (T1 A)
2.2 (T2A)
375 (T2A)
350 (T2A)
Farm (0)
ponds
in Ga.
Fla. (O)
Experimental
Variables
Controlled
or Noted^4) Comments
— 2,4-D was applied over weed-infested areas of the following
types: borrow pits, drainage ditches, a shallow lake, a
small tributary of the Mississippi River, and land areas.
Water hyacinth was killed and sank under any condition
in which it grows in South Louisiana by application of
8 Ib/acre (free acid equivalent) of the amine salt of
2,4-D. A single application of 2,4-D at 8 Ib/acre did
not give complete elimination of alligator weed from
borrow pits and deep ditches but it did reduce the popula-
tion considerably.
a Observations were made on the 3rd, 7th, 14th, and 21st
~ days to give the following (T = toxic, NT = nontoxic,
PT = partially toxic with number of days in parentheses.
No number indicates observation is for entire test
period of 21 days):
Cl - PT (3)
Ma -NT
So -NT
Cv -NT
Gp- NT
Np-T (3)
a e Most of the weed-killer formulations in this study consisted
of more than one substance, i.e., oils, emulsifiers, stabilizers,
and other adjuvants.
a e Comment same as above.
a e Comment same as above.
a c o The response of bluegill and bass fingerlings to nine agri-
cultural chemicals as determined by bioassay using river
water is presented in this report. Bluegills were more
tolerant of the chemicals tested than bass.
— Granular 2,4-D controlled Nympheae sp., Myriophyllum
heterphyllum, Brasenia schreberi, and Utricularia sp. at
the rate of 100 Ib/acre (20 Ib acid).
— At 19.2 pounds per acre, only 1 -2 percent control of
alligator weed was obtained.
Reference
(Year)
Eggler
(1953)
Palmer and
Maloney
(1955)
Alabaster
(1956)
Alabaster
(1956)
Alabaster
(1956)
Davis and
Hardcastle
(1959)
Thomaston, et al
(1959)
Copeland and
Woods
(1969)
m
z
o
x
CO
-------
2,4-D/
2.4-5T
2,4-D
(pellets)
2,4-D
+ TCA
2,4-D
(ester)
2,4-D
(pellets)
2,4-D
Althernanthera FL
philoxeroides
Typha 1
la ti folia
Spatterdock
Najas FL
quadalupensis
Spatterdock
Panicum FL
hemitomum
Althernan thera F L
philoxeroides
Pontederia
cordata
Spatterdock
Bushy FL
pondweed
Lepomis BSA
Fla. (0)
Fla. (0)
Fla. (0)
Fla. (O)
Lakes in (O)
Fla.
2.1
(butoxyethanol macrochirus
ester)
2,4-D (acid,
with emulsifiers)
Lepomis
macrochirus
BSA
8.0 (T2A)
2,4-D
(isopropyl
ester)
2,4-D
(propylene
glycol
butylether
ester)
2,4-D
(ethylester)
8
2 2,4-D
jjj (di-n,n-dimethyl-
30 cocoamine
9 ester)
Lepomis
macrochirus
Lepomis
macrochirus
Lepomis
macrochirus
Lepomis
macrochirus
m
3D
O
O
2,4-D Lepomis
(isooctyl macrochirus
ester)
2,4-D Lepomis
(mixed butyl and macrochirus
isopropyl esters)
BSA
BSA
BSA
BSA
BSA
BSA
0.8 (T2A)
2.1 (T2A)
1.4CT2A)
1.5 (T2A)
36 (T2A)
1.5 (T2A)
The degree of control was as follows:
A. philoxeroides (5.0 Ib/acre) — 1-2 percent
T. latifolia (10.0 Ib/acre) — 80 percent
Spatterdock (5.0 Ib/acre) — 5 percent
Copeland and
Woods
(1959)
At 80.0 and 43.6 Ib/acre, only 2 percent control of both
species was obtained.
At 90.0 Ib/acre, 75 percent control of P. hemitomum
was obtained.
At 4.2 Ib/acre, the degree of control was as follows:
A. philoxeroides — 2 percent
P. cordata — 85 percent
Spatterdock — 3 percent
Copeland and
Woods
(1959)
Copeland and
Woods
(1959)
Copeland and
Woods
(1959)
Concentrations of 1.5 to 2.5 ppm controlled the bushy
pondweed.
The various salts of the chemicals showed wide variations
in toxicity.
Comment same as above.
Comment same as above.
Comment same as above.
Phillippy
(1961)
Hughes and
Davis
(1963)
Hughes and
Davis
(1963)
Hughes and
Davis
(1963)
Hughes and
Davis
(1963)
1
m
O
X
00
Comment same as above.
The various salts of the chemicals showed wide variations
in toxicity.
Hughes and
Davis
(1963)
Hughes and
Davis
(1963)
Comment same as above.
Comment same as above.
Hughes and
Davis
(1963)
Hughes and
Davis
(1963)
-------
COMMERCI
r-
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Chemical
2,4-D
(dimethylamine
ester)
2,4-D
(al kanolamine,
ethanol and
isopropanol
series)
2,4-D (oleic
-1,3-propylene
diarnine)
2,4-D (butyl
ester, oil
soluble)
2,4-D (butyl
ester)
2,4-D (butyl
ester)
2,4-D
(acid)
2,4-D
(propylene
glycol butyl
ether ester)
Organism
Lepomis
macrochirus
Lepomis
macrochirus
Lepomis
macrochirus
L epomis
macrochirus
Lepomis
macrochirus
Lepomis
macrochirus
Crassostrea
virginica
Penaeus
aztecus
Leiostomus
xanthurus
Phytoplankton
Crassostrea
virginica
Penaeus
duorarum
Leiostomus
xanthurus
Fundulus
si mil is
Mugil
cephalus
Cyprinodon
variegatus
Phytoplankton
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study*1 > Location*?) ppm*3)
BSA - 416IT2A)
BSA - 580 (T2A)
BSA - 4.0 (T1A)
BSA - 4.9 (T1 A)
BSA - 10IT1A)
BSA - 1.3IT2A)
BCFA& - 2.0 (NTE)
BSA
2.0 (K10%)
50 (NTE)
-
BCFA& - 1.0(0,39%)
BSA
1.0 (NTE)
4.5 (T4A)
44% (0)
Experimental
Variables
Controlled
or Noted*4' Comments
a e The various salts of the chemicals showed wide variations
in toxicity.
a e Comment same as above.
— The bioassay methods employed in this experiment were
not given in the paper but it was stated that the same
procedures were employed as in previous work.
— Comment same as above.
— Comment same as above.
a e The various salts of the chemicals showed wide variations
in toxicity.
— Sea water was pumped continuously into test aquaria.
Salinity, temperature, and plankton fluctuated with tide,
and ambient weather conditions. Some bioassays with
fish were static. Toxicity was reported for the following:
Oyster — 96-hr ECso — Cone, which decreased
shell growth.
Shrimp — 48-hr ECso — Cone, which killed or
paralyzed 50% of test animals.
Fish - 48-hr ECso - Cone, which killed 50%.
Phytoplankton — Percent decrease of CO2 fixation to a
4-hr exposure at 1 .0 ppm chemical
concentration.
— Comment same as above.
Reference
(Year)
Hughes and
Davis
(1963)
Hughes and
Davis
(1963)
Davis and
Hughes
(1963)
Davis and
Hughes
(1963)
Davis and
Hughes
(1963)
Davis and
Hughes
(1963)
Butler
(1965)
Butler
(1965)
^
•o
m
O
X
00
-------
2.4-D (2-ethyl
hexyl ester)
2,4-D
(iso-octyl
ester)
2,4-D (propy-
lene glycol
butyl ether
ester)
2,4-D (butoxy
ethanol
ester)
2,4-D (butoxy
ethanol
ester)
2,4-D
(dimethyl-
amino salt)
8
m
a
O
2,4-D (butoxy
ethanol ester)
O 2,4-D
m
£
O
Crassostrea
virginica
Penaeus
aztecus
Mugil cephalus
cephalus
Phytoplankton
Lepomis
macrochirus
Lepomis
macrochirus
Lepomis
macrochirus
Crassostrea
virgin/03
Penaeus
duorarum
Fundulus
similis
Phytoplankton
BCFA&
BSA
BSA
BSA
BSA
BCFA&
BSA
Crassostrea
virginica
Penaeus
aztecus
Fundulus
similis
Phytoplankton
Crassostrea
virginica
Pleurobena
cordatum
Daphnia
magna
BCFA&
BSA
BCFA &
BSA
BSA
5.0 (0,38%)
2.0 (0,10%)
10 (NTE)
49% (O)
(L) 8.8-59.7
(T2A)
(G) 116-1000
(T2A)
(L) 2.1 (T2A)
(G) 9.3 (T2A)
(L) 2.1 (T2A)
(G) 34.5 (T2A)
3.75 (O)
1.0 (NTE)
5.0 (T2A)
Comment same as above.
Butler
(1965)
a c d e g
a c d e g
a c d e g
2.0 (NTE)
2.0 (0,10%)
15IT2A)
2.0 (O)
5.0 (NTE)
>100 (O)
a c d i q
Toxicity data for 24 and 48 hours are presented for liquid (L)
and granular (G) formulations. Various commercial formula-
tions were tested. The liquid formulations were almost
invariably more toxic than the granular ones.
Comment same as above.
Comment same as above.
Sea water was pumped continuously into test aquaria.
Salinity, temperature, and plankton fluctuated with tide,
and ambient weather conditions. Some bioassays with
fish were static. Toxicity was reported for the following:
Oyster — 96-hr ECso — Cone, which decreased
shell growth.
Shrimp — 48-hr EC§o — Cone, which killed or
paralyzed 50% of test animals.
Fish - 48-hr ECso ~ Conc- which killed 50%.
Phytoplankton — Percent decrease of CO2 fixation to a
4-hr exposure at 1.0 ppm chemical
concentration.
Comment same as above.
Comment same as above.
Toxicity, in terms of median immobilization concentration
), is presented.
Hughes and
Davis
(1965)
Hughes and
Davis
(1965)
Hughes and
Davis
(1965)
Butler
(1965)
•o
m
O
Butler
(1965)
Butler
(1965)
Crosby and
Tucker
(1966)
•o
3)
O
O
c
-------
COMMERCt
r~
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m
2
O
r
TJ
0
O
1
w
I
do
Chemical
2,4-D
2,4-D
2,4-D
(dimethylamine)
2,4-D
(isooctylester)
2,4-D
(butoxy-
ethanol
ester)
2,4-D
(esters)
2,4-D
(dimethyl-
amine salt)
Bioassay
or Field
Organism Study C"
Salmo BSA
gairdneri
Lepomis
macrochirus
Pteronarcys
californica
Daphnia
pulex
Simocephalus
serrulatus
Lepomis FO
macrochirus
Elliptis
crassidens
Lepomis BSA
macrochirus
Lepomis BSA
macrochirus
Pimephales BCFCH
promelas
Lepomis L
macrochirus
(eggs)
L. cyanellus
(eggs)
Micropterus
dolomieui (eggs)
Erimyzon
sucetta
L. macrochirus
(fry)
Lepomis L
macrochirus
(eggs)
L. cyanellus
(eggs)
Micropterus
dolomieui (eggs)
Erimyzon
sucetta (eggs)
L. macrochirus
(fry)
Toxicity,
Active
Field Ingredient,
Location (2) ppm'3)
- 1.1 (T2A)
0.9 (T2A)
1.8 (T2A)
3.2 (T2A)
4.9 (T2A)
Tenn. (O)
and Ala.
188 (T1A)
453 (T1A)
0.2-1.5(0)
50 (S),
10 (NTE),
5.0 (NTE)
10/4 (O)
10/5(O)
5.0 (NTE)
50 (S)
25 (NTE)
25 (NTE)
25 (NTE)
25 (NTE)
40 (S)
Experimental
Variables
Controlled
or Noted^) Comments
a This paper reports acute toxicity of a number of compounds,
and discusses sub-acute mortality as well. Effects on repro-
duction and behavior are also discussed. Data presented
as EC5Q.
— There was little uptake of 2,4-D (treatment was with a 20%
granular material at the rate of 100 Ib. of 2,4-D acid
equivalent per acre) by fish but some by mussels.
a b e This report is a simple and straightforward determination of
~~ a median tolerable limit for a selected group of herbicides.
a b e Comment same as above.
a c d e q Carbon-filtered tap water was used as diluent. Growth and
reproduction were not affected by 2,4-D at range of
concentrations indicated. No mortalities occurred.
— Fertilized fish eggs of indicated species were placed in
1 liter of test solution and allowed to hatch. Toxicity
data are presented as concentration in ppm/number of
days survival. Maximum length of test was 8 days. No
food was added. Small bluegill were tested to find the
highest concentration of chemical which did not cause
death in 12 days (S).
— Comment same as above.
Reference
(Year)
Cope
(1966)
Smith and
Isom
(1967)
Hughes and
Davis
(1967)
Hughes and
Davis
(1967)
Mount and
Stephan
(1967)
Hiltibran
(1967)
Hiltibran
(1967)
>
TJ
m
Z
D
X
09
-------
2,4-D
(butoxy-
ethanol
ester)
2.4-D
(Na salt)
2,4-D
(esters)
W
2,4-D
2,4-D
2,4-D
(PGBE
ester)
O 2,4-D
O (butoxy-
5 ethanol
m ester)
3)
o
o
m
•o
oj
O
o
I
Pimephales
promelas
Lepomis
macrochirus
(fry)
Lepomis
macrochirus
(eggs)
L. cyanellus
BSA &
CH
Micropterus
dolomieui
(eggs)
L. macrochirus
(fry)
Lepomis
macrochirus
(eggs)
Rainbow
trout
Bluegill
Lepomis
macrochirus
(eggs)
L. cyanellus
(eggs)
Micropterus
dolomieui
(eggs)
Erimyzon
sucetta
(eggs)
L. macrochirus
(fry)
Anopheles
quadri-
maculatus
(4th instar)
Lepomis
macrochirus
Elliptis
crassidens
Hexagenia
Tendipedidae
Heleidae
Chaoborus
Oligochaeta
Corbicula
and others
BSA
BSA
FS
5.6 (T4A)
100(S)
4/2 (O)
4.0 (NTE)
4.0 (NTE)
3.0 (S)
5/1 (O)
1.1 (T2A)
3.7 (T2A)
1/2 (O)
1/5(0)
1/5(0)
1/5 (O)
2(S)
(O)
a c d e f The fish could tolerate 1/19 this amount of 2,4-D for a
ten-month test.
Fertilized fish eggs of indicated species were placed in
1 liter of test solution and allowed to hatch. Toxicity
data are presented as concentration in ppm/number of
days survival. Maximum length of test was 8 days. No
food was added. Small bluegill were tested to find the
highest concentration of chemical which did not cause
death in 12 days (S).
Comment same as above.
Watts Bar
Reservoir
T.V.A.
Gunters-
ville
Reservoir
T.V.A.
Comment same as above.
Data are given as 1X50-
Fertilized fish eggs of indicated species were placed in
1 liter of test solution and allowed to hatch. Toxicity
data are presented as concentration in ppm/number of
days survival. Maximum length of test was 8 days. No
food was added. Small bluegill were tested to find the
highest concentration of chemical which did not cause
death in 12 days (S).
The Watts Bar test site was treated with a 20% granular
material at the rate of 100 Ib of 2,4-D acid equivalent per
acre. The Guntersville area was treated at the rate of
40 Ib per acre. The applications were made for control of
Eurasian watermilfoil, Myriophyllum spicatum. The toxic
effect of 2,4-D was evaluated by sampling the benthic
invertebrate communities of both reservoirs before treatment
and at least twice after treatment. Residue analysis of water,
fish, plants, mussels, and sediment were used to study diffu-
sion, accumulation, translocation, and/or degradation of
2,4-D. In both areas at both concentrations, a monitoring
device showed some movement of lake fish out of the treated
area, but no mortality of fish occurred. A total of 50
assorted frozen samples of plants, animal tissue, and mud
were analyzed for 2,4-D. Application of 2,4-D at the given
concentrations caused no measurable toxic effect on benthic
fauna.
Mount and
Stephan
(1967)
Hiltibran
(1967)
Hiltibran
(1967)
Hiltibran
(1967)
Bohmont
(1967)
Hiltibran
(1967)
1
m
O
X
CD
Smith and
Isom
(1967)
-------
COMMERCI
r-
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TJ
21
O
D
C
O
c/)
{JO
<-f\
O
Chemical
2,4-D
2,4-D
(butoxy
ethanol ester)
2,4-DA
(pellets)
DAC,
dodecylacetamido
dimethyl benzyl
ammonium
chloride
Dacthal
Dacthal
Dalapon
(sodium salt)
Organism
Pteronarcys
californica
(naiads)
Pteronarcys
californica
(naiads)
Water
lettuce
Pimephales
promelas
Lepomis
macrochirus
Crassostrea
virginica
Penaeus
aztecus
Cyprinodon
varlegatus
Phytoplankton
Fundulus
similis
(juvenile)
Oyster
Penaeus
aztecus
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study<1) Location!2) ppm<3'
BSA - 0.01 5 (T4A)
BSA - 0.001 6 (T4A)
FL Lakes in (O)
Fla.
BSA - 0.65 (T4A)
BSA - 1000(T1A)
BCFA & - 0.25 (O)
BSA
1.0 (NTE)
1.0 (NTE)
37% (O)
BSA - (O)
BCF
L
Experimental
Variables
Controlled
or Noted!4) Comments
a c d e f Data reported as \-C$Q at 1 5.5 C in 4 days.
a c d e f Comment same as above.
— An application rate of 10 Ib/acre controlled water lettuce.
a c d e f Toxicity to 30 species of algae also presented. DAC was
algicidal in the range 0.25 to 2.0 ppm.
a b e This report is a simple and straightforward determination of
a median tolerance limit for a selected group of herbicides.
— Seawater was pumped continuously into test aquaria.
Salinity, temperature, and plankton fluctuated with tide.
and ambient weather conditions. Some bioassays with fish
were static. Toxicity was reported for the following:
Oyster — 96-hr ECso — Cone, which decreased
shell growth.
Shrimp — 48-hr ECso — Cone, which killed or
paralyzed 50% of test animals.
Fish - 48-hr EC5Q - Cone, which killed 50%.
Phytoplankton — Percent decrease of CO2 fixation to a
4-hr exposure at 1 .0 ppm chemical
concentration.
a Water temperature was 20 C. No effect was noticed on
exposure to 1.0 ppm.
No effect on exposure to the chemical at 1 .0 ppm.
Toxicant chemicals were evaluated in seawater at tempera-
tures averaging about 28 C. The values are for 24-hr
Reference
(Year)
Sanders and
Cope
(1968)
Sanders and
Cope
(1968)
Phillippy
(1961)
Maloney and
Palmer
(1956)
Hughes and
Davis
(1967)
Butler
(1965)
Butler
(1965)
3^
•o
m
X
03
ECcjo or enough to cause loss of equilibrium or mortality.
A concentration of 1.0 ppm caused 30 percent mortality.
-------
Dalapon
(sodium salt)
T3
Dalapon
(sodium salt)
Dalapon
(Na salt)
Dalapon
Dalapon
(Radapon)
Dalapon
(tech)
Dalapon
O Dalapon
2
m
o
TJ
3)
O
O Dalapon
§
v>
virginica
Penaeus
aztecus
Fundulus
similis
Phytoplankton
BCFA &
BSA
Pteronarcys sp
(nymphs)
Pteronarcys
californica
(naiads)
Cattails and
other aquatic
plants
Lepomis
macrochirus
Pimephales
promelas
Bluegill
Simocephalus
serrulatus
Daphnla
pulex
Lepomis
macrochirus
(eggs)
L. cyanellus
(eggs)
Micropterus
dolomieui
(eggs)
E rimyz on
sucetta
(eggs)
L. macrochirus
(fry)
Salmon
Bluegill
BSA
BSA
FL
Farm
ponds
in Ga.
BSA
BSA
BSA
BSA
1.O (NTE)
1.0 (0,40%)
1.0 (NTE)
(O)
>1000 (T4A)
100 (NTE)
(O)
(S) 440 (T4A)
(S) 390 (T4A)
(H) 290 (T4A)
105(T4A)
16 (SB)
11 (SB)
50 (S),
50 (NTE)
50 (NTE)
50 (NTE)
50 (NTE)
50 (S)
340 (T2A)
115 (T2A)
Seawater was pumped continuously into test aquaria.
Salinity, temperature, and plankton fluctuated with tide,
and ambient weather conditions. Some bioassays with
fish were static. Toxicity was reported for the following:
Oyster — 96-hr £650 — Cone, which decreased
shell growth.
Shrimp — 48-hr £€50 — Cone, which killed or
paralyzed 50% of test animals.
Fish - 48-hr EC^Q - Cone, which killed 50%.
Phytoplankton — Percent decrease of CC>2 fixation to a
4-hr exposure at 1 .0 ppm chemical
concentration.
Experiments were all conducted at 60 F in 1964. The values
were listed as
Butler
(1965)
a c d e f Data reported as \-C$Q at 1 5.5 C in 4 days.
Dalapon was used primarily to control marginal grasses
and cattails.
Cattails can be eradicated at the rate of 1 Ib to 5 gal of
water or 20 Ib/acre.
It was indicated that 1 Ib to 7.5 gal (15 Ib per acre) proved
satisfactory for control of cattails.
Bioassay method in Standard Methods for Examination of
Water was used. Both hard (H) and soft (S) water were
used. TLm values for 24 and 48 hr are also presented.
This is an estimated
to 75 F.
value at temperatures from 55
Concentration reported is for immobilization.
Time for immobilization was 64 hr.
Data cited are for 78 F, but assays were performed at
varied temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
Fertilized fish eggs of indicated species were placed in
1 liter of test solution and allowed to hatch. Toxicity
data are presented as concentration in ppm/number of
days survival. Maximum length of test was 8 days. No
food was added. Small bluegill were tested to find the
highest concentration of chemical which did not cause
death in 12 days.
Data are given as LC5Q.
Cope
(1965)
Sanders and
Cope
(1968)
Thomaston, et al
(1959)
Surber and
Pickering
(1962)
Cope
(1965)
Sanders and
Cope
(1966)
Hiltibran
(1967)
1
m
D
X
09
Bohmont
(1967)
-------
8
m
n Chemical
£ 4-12,4-DB)
I
m
5
o
£ 4 (2,4) DB,
-o (tech)
3)
g DBrDT
C (DDT
5 analogue)
en
DBS
ODD
3 ODD
i
J
ODD (TDE,
tech)
Organism
Lepomis
macrochirus
Micropterus
sa/moides
Rainbow
trout
Goldfish
Gambusia
af finis
Culex
apicalis
(larvae)
Trout
Channel
catfish
(fingerlings)
White
catfish
Largemouth
bass
Brown
bullhead
Black
crappie
Bluegill
Hitch
Sacramento
blackfish
Carp
Salmo
gairdneri
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study'1' Location!2) ppm'3)
BSA - 8.0 (T2A)
10 (T2A)
BSA - 5.4 (T4A)
BSA - 0.06 (K)
0.01 (K)
0.0015 (K)
BCHA - 5.0-20 (SB)
BSA - <2.6
(K25hr A)
FLCH Cal. 0.014 (SB,
application
rate for
1949, -51,
-57)
BSA - 30 (T1 A)
Experimental
Variables
Controlled
or Noted'4) Comments
a c o The response of bluegill and bass fingerlings to nine agri-
cultural chemicals as determined by bioassay using river
water is presented in this report. Bluegills were more
tolerant of the chemicals tested than bass.
a This is an estimated LCso vaiue at temperatures trom 55 to
75 F
— Experiments were run a maximum of 3 days. No other
time data were reported.
— Fish exposed to 5.0 ppm of the chemical suffered a reduc-
tion of the epithelium and a loss of mucous cells on top
of the gill laminae. Exposure to 20 ppm for one hour
caused great destruction of the epithelium — followed by
death from suffocation.
a Tap water was used. Conserable additional data are
presented.
a g Gnat control program with follow-up on accumulation in
various species of wildlife. Ppm of ODD in edible flesh
white catfish in 1958 was 304-129.0, Concentrations in
remaining fish were 5.4-115 ppm.
a The experiment was conducted at 55 F. Fish were 2-3 in.
long.
Reference
(Year)
Davis and
Hardcastle
(1959)
Cope
(1965)
Odum and
Sumerford
(1946)
Schmid and
Mann
(1961)
Clemens and
Sneed
(1959)
Hunt and
Bischoff
(1960)
Cope
(1963)
^
•o
TJ
m
Z
X
CD
-------
TOE
(DDD)
Chironomus
riparius
Asellus
aquaticus
Salmo
gairdnerii
FL
Essendon (O)
Hertfordshire
DDD
Gambusia
affinis
affinis
BSA
0.46 to
(L 1-1/2)
DDD
(tech)
DDD
Bluegill
Pygosciles
adeloriae
Lobodon
carcinophagus
BSA
FM
Ross
Island,
Antarctic
0.042 (T4A)
(O)
TDE
(DDD)
Simocephalus
serrulatus
Daphnia
pulex
BSA
0.0045 (SB)
0.0032 (SB)
8
m
3
o
o
m
pp'DDD
Buteo
buteo
Accipiter
gentilis
Accipiter
nisus
Falco
tinnunculus
Tyto
alba
Strix
aluco
FO
Netherlands (O)
3)
O
O
Initial laboratory tests suggested that settleable powder Edwards, et al
formulations of TDE and DDT at application rates (1964)
greater than 0.5 Ib/acre would be effective in controlling
Chironomus larvae, and that while trout would not be
killed either directly (0.5-1 Ib/acre) or by feeding on TDE-
treated larvae, other invertebrates, e.g. Asellus, would be
affected. Tubificids were not killed at application rates
up to 2 Ib/acre. TDE was considered a more useful insecticide
than DDT because of its lower toxicity to fish. Carp were
kept in cages for 11 months following the insecticide treat-
ment; 35% died but the survivors grew well. By November
1962, fish tissues contained about 15 ppm TDE. In lab
studies a 50 percent kill occurred in 7 days, at 0.1 Ib per
acre for chironimid larvae, at 0.5 Ib per acre for A.
aquaticus, and 2 Ib per acre killed 10% of the tubificid
worms. No deaths of rainbow trout occurred in 7 days
at 2 Ib per acre.
The lower value is for fish that had never been exposed to Boyd and
the toxicant, and the higher value was obtained with fish Ferguson
that had been exposed to a sublethal dose in the past. (1964)
Apparently such an exposure produces a resistance that
can be retained when they are exposed later.
The values reported are given as 1X50- Cope
(1965)
Adult penguins assayed showed no residue. The pre-molts George and
examined had residues ranging from 0 to 16 ppb in the Frear
liver and 0 to 2 ppb in the fat. The crabeater seal (1966)
examined showed residues of 2 ppb in the liver and
7 ppb in the fat.
Concentration reported is for immobilization. Sanders and
Time for immobilization was 48 hr. Cope
Data cited are for 60 F, but assays were performed at varied (1966)
temperatures.
Water chemistry (unspecified) was "controlled" during the
assay period.
The results of this study show that birds of prey and fish- Koeman and
eating birds found dead in the Netherlands accumulated van Genderen
large amounts of different chlorinated hydrocarbon (1966)
insecticides. In most cases the liver had the highest con-
centration of toxicant, ranging from 0.08 to 8.6 ppm. Most
chlorinated hydrocarbons tend to accumulate in the fat
depots of the body. In instances where mesenterial fat was
analyzed the concentration of toxicant was found to be as
high as 5.1 ppm.
m
O
X
00
-------
o
o
s
s
m
o Chemical
<~ TDE
g (ODD)
m
O
r-
-D
3 ODD
O
O
c
W ODD
TDE
(ODD)
DDE
DDE
CO
3, DDE
*>•
DDE
pp'DDE
Toxicity,
Bioassay Active
or Field Field Ingredient,
Organism Study'"" Location'2) ppm (3)
Daphnia BSA - 0.0046 (SB)
magna
Atlantic salmon FR New (O)
Brook trout Brunswick
Limnephilus — Knights (O)
rhombicus Creek, Wise.
Sialis sp
Gammarus sp
Pteronarcys BSA - 0.38 (T4A)
californica
(naiads)
Penaeus L — 0.0068 (O)
a 2 tec us
Oyster BCF - 0.014 (O)
Leptonychotes FM Antarctic (O)
weddelli
Pygosalis
adeloriae
Catharacta
skua
maccormicki
Pygosciles FM Ross Island, (0)
adeloriae Antarctic
Lobodon
carcinophagus
Platalea FO Netherlands (O)
leucorodia
Haematopus
ostralegus
Sterna
sandvicensis
Sterna
hirundo
Larus
ridibundus
Somateria
mollissima
Tadorna
tatjorna
Experimental
Variables
Controlled
or Noted'4) Comments
— Concentration reported is for immobilization.
Time for immobilization was 64 hr.
Data cited are for 78 F, but assays were performed at varied
temperatures.
Water chemistry (unspecified) was "controlled" during the
assay period.
— Spraying with this chemical at 0.25 to 0.5 Ib/acre was no more
harmful than with DDT at 0.25 Ib/acre.
— Pesticide usage in an orchard did not significantly contaminate
the aquatic environment of this creek adjacent to the treat-
ment as determined by residue analysis.
a c d e f Data reported at LCgfj at 1 5.5 C in 4 days.
a Toxicant chemicals were evaluated in sea water at tempera-
tures averaging about 28 C. The values are for 24-hr EC§o
or enough to cause loss of equilibrium or mortality.
a The value reported is a 96-hr ECso (decreased shell growth).
a All residues are expressed as ppm wet weight. It was
established that residues in the water were less than
0.0005 ppm. No detectible residues were found in
tissues of L. weddelli.
No detectable residues were found in tissues of P. adelias.
Residues ranging from 0.01 to 0.73 ppm were found in
tissues of C. skua maccormicki.
a Adult penguins assayed had residues ranging from 20 to
28 ppb in the liver. The fat residues in the pre-molts
penguins ranged from 19 to 45 ppb. Crabeater seal
examined showed residues of 7 ppb in the liver and 17 ppb
in the fat.
— The results of this study show that birds of prey and fish-
eating birds found dead in the Netherlands accumulated
large amounts of different chlorinated hydrocarbon
insecticides. In most cases the liver had the highest con-
centration of toxicant, ranging from 0.1 to 6.0 ppm.
Birds feeding predominantly on Crustacea, molluses, and
fish contained significant amounts.
Reference
(Year)
Sanders and
Cope
(1966)
Kerswill and
Edwards
(1967)
Moubry, et al
(1968)
Sanders and
Cope
(1968
Butler
(1965)
Butler
(1965)
George and
Frear
(1966)
George and
Frear
(1966)
Koeman and
van Genderen
(1966)
«O
-o
m
Z
g
x
00
-------
PP'DDE
pp'DDE
op'DDE
DDE
DDE
DDE
m
30
o
o
m
S
TJ
3D
O
O
c
DDE
Buteo
buteo
Accipiter
gentilis
Accipiter
nisus
Falco
tinnunculus
Tyto
alba
Strix
aluco
Oslo
otus
Falco
pereginus
Esox
lucius
FO
Netherlands
(O)
FR
Esox
lucius
Limnephilus
rhombicus
Sialis sp
Gammarus sp
Oyster
Vascular
plants
Algae
Chubs
Largemouth
bass
Clams
Alosa
pseudoharengus
Aplodinotus
grunniens
Coregonus
artedii
Lota
lota
FR
FE
FL
River
Nene,
Eng.
River
Nene,
Eng.
Knights
Creek,
Wise.
Galveston
Bay,
Texas
Tule Lake,
Ore.
(O)
(O)
(O)
(O)
BSA
(O)
The results of this study show that birds of prey and fish-
eating birds found dead in the Netherlands accumulated
large amounts of different chlorinated hydrocarbon
insecticides. In most cases the liver had the highest con-
centration of toxicant, ranging from 1.2 to 75.2 ppm.
Most chlorinated hydrocarbons tend to accumulate in
the fat depots of the body. In instances where mesenterial
fat was analyzed the concentration of toxicant was found
to be as high as 68.3 ppm.
Higher concentrations were found in larger fish, indicating
that they had been exposed to the pesticides for a longer
time. Tissue extracts from the pike were analyzed for
organochlorine pesticide residues by gas liquid chroma-
tography. The average of six determinations was:
0.72 ppm muscle
96.0 ppm fat
Comment same as above except that values for large fish
only were:
0.042 ppm muscle
6.6 ppm fat
Pesticide usage in an orchard did not significantly con-
taminate the aquatic environment of this creek adjacent
to the treatment as determined by residue analysis.
The chemical was found in the water at a concentration
of <0.001 ppm. Oysters from the area were found to
contain <0.01 to 0.05 ppm.
The amount of chemical sprayed in this area was not
specified. The residue found was in the range of 0.6 to
1.0 ppb. Residue in chubs was from 2.5 to 45.0 ppb.
The bass contained 11.0 to 38.0 ppb. Clams contained
0.75 to 6.3 ppb. The water contained 0.003 to 0.027 ppb.
The study showed that the levels of chlorinated hydrocarbon
pesticide residues in the fish meals and oils were, with the
exception of the oil sample taken from the Lake Michigan
alewife, below the regulatory tolerances established by
the Food and Drug Directorate of Canada (1965) for
certain foods intended for human consumption. Pesticide
levels were interpreted as being representative for each
species.
Koeman and
van Genderen
(1966)
Mawdesley-
Thomas and
Leahy
(1967)
Mawdesley-
Thomas and
Leahy
(1967)
Moubry, et al
(1968)
Casper
(1967)
Godsil and
Johnson
(1968)
Dugal
(1968)
-------
o
o
s
m
n Chemical
>
r DDE
O
I
m
(-j
>
r
-o
3)
0
D
o DDT
H
Cft
Organism
Potamogeton
pectinatus
Cladophora
Oscillator/a
Cynodon
dactyl on
Arundo
donax
Carassius
auratus
Bioassay
or Field
Study (D
FR
BSA
Toxicity,
Active
Field Ingredient,
Location(2) ppm(3)
Arizona (O)
(0)
Experimental
Variables
Controlled
or Noted<4)
_
_
Comments
Irrigation canals were examined for plants which might serve
as DDT collectors or indicators of DDT usage by con-
centrating this material and its metabolites. Highest
residues were found in Cladophora (19 ppm), followed by
Potamogeton (9 ppm), and finally Osci/latoria (5 ppm).
DDT was used in 2 forms, as a dust containing 5 percent of
DDT and in acetone solutions as a water suspension. The
Reference
(Year)
Ware, et al
(1968)
Eide, et al
(1945)
DDT
T3
Ol
Os
DDT
DDT
Huro
salmoides
Lepomis
macrochirus
Notemigonus
crysoleucas
Carassius
auratus
Invertebrates
Orders:
Annelida
Megaloptera
Ephemeroptera
Odonata
Plecoptera
Coleoptera
Trichoptera
Diptera
Mollusca
Daphnta
magna
Carassius
auratus
FR
Back Creek,
Glengary,
W. Va.
(O)
BSA
BSA
0.001 (SB1A)
2.0 (K1)
1.0 (O)
through a fine-mesh screen.
DDT produced characteristic symptoms in the goldfish in
24 hours when applied as either of the above formulations
at concentrations of 0.2-2.0 ppm, but not at lower con-
centrations. The nervous system was affected causing a
loss of equilibrium.
Whenp/7/sa sp were tested, only the DDT from acetone
solution was employed.
Aerial application of 1 pound per acre was made by plane. Hoffman and
Only 0.39 pounds of DDT per acre reached the stream Surber
surface. (1945)
Open live-boxes of fish were placed above, below, and within
the sprayed section at five points. Of the 452 fish in these
boxes, only 5 died from toxicity of the DDT. Predators
removed a considerable number of fish from one live-box,
and the handling of the fish was responsible for other losses.
However, the survival, even with these losses, amount to
89.8%.
Application of the chemical showed a rapid paralyzing effect
on invertebrates.
Application upon the bottom fauna revealed good survival
(67%) at the first station and poorer survival (26% and 33%)
at locations down stream.
Wettable DDT applied at 1 pound per acre is not so toxic
to fish and fish-food organisms as the same amount of
DDT applied in an oil spray.
Sublethal effect observed was immobilization of the Daphnia. Anderson
Lake Erie water was used. (1945)
Ethyl alcohol was used as a solvent for 2 percent DDT. At Ginsburg
1 ppm, 90 percent of the fish were killed in 1 day. (1945)
•o
m
Z
00
-------
DDT
(mosquito
larvicide
50-D)
Carassius
auratus
BSA
0.4 (O)
DDT
(Dust)
Carassius
auratus
BSA
0.1 (O)
DDT
Salmo
trutta
BSA
Ithaca, 0.25 (T1A)
N.Y.
DDT
DDT
Fall fish
Common
shiner
Bluegill
sunfish
Eastern
madtom
Silverling
minnow
FRK
Patuxent (O)
River,
Md.
FR
W. Va. (O)
•D
3D
O
O
c
Hyborhynchus
notatus
Micropterus
salmoides
1.0(0)
1.0(0)
8
m
3)
o
o
Lepomis
macrochirus
Pimephales
promelas
1.0(0)
Mosquito Larvacide 50-D is water-white kerosene con- Ginsbury
taining 3 percent DDT in solution and emulsified with (1945)
sodium lauryl sulfate. A concentration of 0.4 ppm caused
a mortality of 30 percent in 3 days at the spraying rate of
0.42 pounds per acre.
A concentration of 0.1 ppm killed 17 percent of the fish in Ginsburg
3 days at a spraying rate of 0.1 pounds per acre. 1.0 ppm (1945)
killed 17 percent of the fish in 3 days at a spraying rate
of 1.0 pounds per acre.
LDcjQ was determined in hours of survival time. The chemical Everhartand
was added as a wettable powder, as a solution in xylene Hassler
with an emulsifying agent, and as a kerosene solution. It (1945)
was most toxic as the emulsion.
Fish kill occurred after an area was sprayed with an oil solu- Cottam and
tion of DDT at the rate of 2.0 Ib/acre. Several other field Higgins
studies were discussed in this report, but without much (1946)
quantitative data. It is interesting that this paper presented
as the first recommendation "Don't use DDT unless you
must."
An oil preparation of DDT was applied from a plane. The
average deposit was 0.27 pounds per acre even though it
was applied at 1 pound per acre.
Thirteen stations were set up for sampling, Nrs. 1 and 2
were above point of application and the remainder were
at and below the application point up to 2.0 miles. In
general the closer the station to the point of application
the more toxic the chemical.
Bluntnose minnows were not affected by the spray.
Surber and
Friddle
(1946)
m
O
X
00
Greatest toxicity was noted at Station 10 (0.8 miles from
point of application) which showed 46% survival. 100%
survival occurred at Station 13 (2 miles from point of
application).
Greatest toxicity was noted at Station 10 (0.8 miles from
point of application) which showed 74% survival. All
other stations except 13, which had 100% survival, showed
92% survival of bluegill.
Blackhead minnows showed 68-74% survival at most stations;
100% at Station 13.
DDT proved to be more toxic when applied as an oil spray
rather than a suspension or a powder.
-------
o
o
s
s
m
o Chemical
"~ DDT
O
I
m
o
r~
-o
33
O
O
c
o
en
DDT
DDT
(Velsicol
NR-70)
DO
00 DDT
DDT-
copper
sulfate
Toxicity,
Bioassay Active
or Field Field Ingredient,
Organism Study ("" Location^) ppm<3)
Goldfish BSA - 0.07 (K)
Goldfish plus 0.1 6 (K)
Elodea spp and
Cabomba spp
Gambusia 0.1 (K<1)
af finis
Culex <0.0001 (K)
apical is
(larvae)
Culex 0.025 (K)
apicalis
(pupae)
Carassius BSA - 0.2 (K5)
auratus
Aedes 0.05 (K2)
aegypti
Numerous fish FL Tenn. (O)
species and other
aquatic
organisms
Mastigophora FL Savannah, (O)
Infusoria Ga.
Hydrocarina
Diatomaceae
Synura
Dinoflagellata
Phacus
Rototoria
Copepoda
Chroococcaceae
Scenedesmaceae
Chlamydomonas
Euglena
Trachelomonas
Sarcodina
Synedra spp FL Del. (O)
Daphnia spp
Cyclops spp
Experimental
Variables
Controlled
or Noted (^) Comments
— Data are also given for analogues of DDT. Experiments
were run a maximum of 3 days. No other time data
were reported.
— DDT fed to mosquito larvae at 1 part per 20 million killed
100 percent of the mosquitos in 2 days. DDT fed to gold-
fish at 1 part per 5 million killed 100 percent of the gold-
fish in 5 days. Mosquito larvae killed by DDT at the above
concentration when fed to goldfish did not have a toxic
effect.
— DDT was applied by thermal aerosol at the rate of 0.1 Ib/acre.
Rate at center of swath was 0.012 Ib/acre. Anopheline and
culicine mosquitoes were almost eliminated. After 16 appli-
cations, the conclusion was that fish populations were
unchanged when compared to controls.
— No drastic killing of any specific group of organisms occurred
from DDT treatment. At 0.5 Ib/acre DDT spray, the growth
of Mastigopnera, Synura, Dinoflagellata, and Copepoda was
inhibited; while Phacus, Rototaria, Chroococcaceae, and
Euglena, appeared to be stimulated. All others were
apparently unaffected. Similar results were obtained with
a 0.1-0.2 Ib/acre dust application of DDT. The author uses
line-graphs to indicate trends of populations before and
after treatment.
— Describes conditions, after DDT aerial spraying of a city
water reservoir. Zooplankton disappeared with an over
abundance of Synedra spp. Control of Synedra spp with
0.25 ppm CuSC>4 was not effective. A possible antagonism
of DDT to copper sulfate is noted.
Reference
(Year)
Odum and
Sumerford
(1946)
Ginsburg
(1947)
Hess and
Keener
(1947)
Bishop
(1947)
Shane
(1948)
•o
m
z
o
CD
-------
DDT
Bluegill
Largemouth
black bass
Small mouth
black bass
Golden-shiner
Black crappies
FL &
CF
Kearneysville,
W. Va.
(O)
DDT
CO DDT
Black fly
(larvae)
Rainbow
trout
Caddis
fly
Lebistes
reticulatus
FR
Alaskan
streams
0.3 (O)
BSA
0.025 (K1-
15%)
DDT
8
m
30
o
Lepomis
macrochirus
Micropterus
salmoides
Notemigonus
crysoleucas
auratus
Pomoxis
nigromaculatus
Megastoma tobus
cybrinella
Pimephalas
promelas
Carass/us
auratus
FL
Auburn,
Ala.
0.1 to 0.5
(K)
2 DDT
m
2
5
T3
•33
O
O
Bottom
organisms:
Ephemeroptera
Odonata
Plecoptera
Megaloptera
Coleoptera
Trichoptera
Diptera
FR
Wilkes Barre, (O)
Pa.
Small bluegills, largemouth black bass, and small mouth
black bass one inch in length were killed by DDT in oil
formulations in applications ranging from 0.25 to 1.0
pound per acre.
Golden shiner fry were killed by oil sprays in excess of
0.25 pound per acre in dirt-bottomed ponds.
Young black crappies 1.2 inches in length were killed by
0.5 pound per acre of DDT in both suspension and oil
formulations.
Fingerlings 2 inches or more in length were better able to
withstand the higher rates of application.
Fingerling bluegills, small mouth black bass, and black
crappies were found to be more sensitive to DDT than
largemouth black bass, golden shiners, and trout.
In continuous flow raceways, brook and rainbow trout,
smallmouth bass, and golden shiners were relatively
unaffected by a 1 pound per acre application of DDT.
The chemical was applied for control of black flies, and
because the acetone solution was most effective, only
that data is reported here. The figures reported are
for minimum effective dosages for black fly larvae and
maximum nonlethal dosages for rainbow trout and
caddis fly larvae.
This is a bioassay method for determining DDT residue
extracted from vegetables.
Adult fish were not killed at 0.2 ppm. All were killed at
0.5 ppm in earthen ponds, in concrete pools 0.04 ppm
was lethal.
Adult fish were killed at concentrations greater than
0.1 ppm.
This species withstood a concentration of 0.18 ppm.
Surber and
Hoffman
(1949)
Gjulian.et al
(1949)
Pagan and
Hageman
(1950)
Lawrence
(1950)
m
z
o
X
00
In concrete pools. 0.18 ppm was lethal to this species.
Withstood 1.0 ppm in earthen ponds.
The last two species withstood 0.4 ppm, but were killed
at 2.0 ppm.
The toxicity of DDT to all species seems to be partly
dependent on the form in which the chemical is added —
as wettable powder or emulsion.
The DDT application of 1 Ib/acre was made for control of
Porthetria dispar, gypsy moth. Aquatic insects of the
orders Megaloptera and Odonata appeared to be resistant
to DDT poisoning at the dosage applied. Trichoptera
were affected severely. Insect mortality increased as
DDT moved down stream.
Hoffman and
Drooz
(1953)
-------
o
o
m
n Chemical
r- DDT
O
I
m
5
o
r-
•o
0
O
O
tn
DDT
D
r\
3
Toxicity,
Bioassay Active
or Field Field Ingredient,
Organism StudyC" Location*2* ppm<3)
Cylindrospermum L — 2.0 (O)
lichen/forme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Labea sp FR Khartoum (O)
Synodontis
schall
Experimental
Variables
Controlled Reference
or Noted^4' Comments (Year)
a Observations were made on the 3rd, 7th, 14th, and 21st Palmer and
~ days to give the following (T = toxic, NT = nontoxic, Maloney
PT = partially toxic with number of days in parentheses. (1955)
No number indicates observation is for entire test period
of 21 days):
Cl -NT
Ma-T (7)
So -NT
Cv -NT
Gp - PT (7)
Np- NT
— A section of the Blue Nile was sprayed by air with an Burden
emulsified oil containing 30% DDT and 0.5% "Lissapol". (1956)
The material was applied about 10 miles above Khartoum.
It was hoped that by the time the treated water reached
Khartoum, the DDT concentration would have been diluted
4 times. The concentration at the time of arrival was 0.17
ppm, and was maintained at a level of 0.003 ppm for 6 hr.
It was reported that hundreds of fish were found dying
2 miles above Khartoum. Labea sp died in 8 hr and
Synodontis schall dted in 31 hr. The fish were analyzed
for DDT residue the next day. The results are given below:
Flesh
Fatty
Gills Viscera Deposit
Labea sp 0.9 ppm 2.5 ppm Nil
Synodontis 2.7 ppm 7.9 ppm 64 ppm
schall
•j>
•o
T)
m
z
D
X
09
DDT
DDT
DDT
DDT
Labea sp
Synodontis
schall
Young
salmon
Salmo
salar
Salvelinus
fon final is
Salmo
gairdnerii
Simulium sp
(larvae)
F
BSA
Khartoum
Canada
0.09 (K)
(O)
0.08 (L3)
FR
Streams,
S. C.and
Fla.
0.08 (L3)
0.16(L<2)
0.08 (L3)
0.16 (L<2)
0.1-3.4 (O)
Various levels of DDT were found in dead fish from 0.017 to Burdick, et al
0.003 ppm downstream from the application. Undeter- (1965)
mined degree of kill occurred.
No toxicity data on fish were reported. The report deals Ide
primarily with reduction of insects available as fish food. (1957)
100 percent mortality occurred at 0.16 ppm in 18 hours Hatch
for landlocked salmon, in 54 hours for rainbow trout, and (1957)
26 hours for brook trout.
In slow-moving streams in Florida and South Carolina, DDT at Davis, et al
the indicated concentrations controlled blackfly larvae for (1957)
up to 0.28 mile. Control lasted for approximately 2 weeks.
Data are presented as percent larval detachment in 1,2, and
3 days time. Emulsion (0.1 ppm), oil (O.I ppm), and granule
(O.5-1.0 Ib/acre) formulations had about the same degree of
effectiveness.
-------
DDT
DDT
DDT
DDT
DDT
DDT
S
DDT
O
o
m
2
33 DDT
O
O
§
Blue crab
Marsh fiddler
crab
Red-jointed
fiddler crab
Cyprinodon
variegatus
Leiostomus
xanthurus
Mugil
curema
Insectivorous
fish
Ephemeroptera
Trichoptera
Various aquatic
and terrestrial
organisms
FE
Bombay
Hook
Island,
Del.
(O)
FR
FL
Uganda
Salt Lake
Co., Utah
(O)
(O)
Atlantic
salmon
Brook, rainbow
and cutthroat
trout and
whitefish
Aquatic insects
Anemia
salina
Fathead
minnow
Bluegill
Goldfish
Guppy
Fathead
minnow
BSA
FR
0.049 (T1A)
0.047 (T2A)
Montana
a c d
BSA
BSA
BSA
0.142 (K<1)
0.032 (T4A)
0.016 (T4A)
0.027 (T4A)
0.043 (T4A)
0.034 (T4A)
The location under study was a salt marsh bounded by George, et al
Delaware Bay. (1957)
DDT was applied at 0.2 pound per acre.
Organisms were confined in cages within the test area.
C. variegatus, M. curema, and L. xanthurus showed no
mortality when exposed for 7 days.
Blue crabs showed 17 percent mortality when exposed for
7 days in streams and 10 percent mortality in ponds.
Marsh fiddler crabs and red-jointed fiddler crabs showed
75 and 36 percent mortality, respectively, in 7 days.
Rapid recolonization of aquatic insect populations decreased Corbet
the possibility of accumulation of DDT by fish. Applica- (1958)
tion rate was not given.
The chemical was applied at 0.3 Ib/acre. This concentration Graham and
was sufficient for mosquito larvae control. Anderson
At the above concentration no ill effects were observed in (1958)
mammals, birds, reptiles, and amphibians.
Invertebrates were not affected uniformly. Crustaceans were
not harmed, nor were larvae of the insect family Ephydridae.
Spiders and aquatic insects other than Ephydridae were
adversely affected in varying degrees. Aquatic beetles seemed
to be affected more seriously than other insects except
mosquito larvae.
Results are recorded in ppm of insecticide by weight in Keenleyside
water. (1958)
Changes in temperature had an effect on the toxicity of
the chemical.
This study involves 13 rivers and streams following aerial Graham and
spraying of DDT at rate of 1 Ib/acre for control of spruce Scott
bud worm. The DDT recovery rate varied from 0.19- (1958)
0.32 Ib/acre. Significant amounts of DDT in fish tissue
were found 16 months after spraying. The concentrations
varied from 0.01 JUg/mg to 4.0/Jg/mg. Aquatic bottom
invertebrates and adult insects were materially reduced in
number but recovered in 1 year.
Rock salt was used in rearing all cultures employed in bio- Tarpley
assay work. The optimum salt concentration was 3.5%. (1958)
It was the authors opinion that pH, alkalinity and hardness, Tarzwell
within the usual range in natural waters, had little effect (1959)
on the toxic effect of the compounds studied. The values
given are from Henderson, Pickering, and Tarzwell, "The
Relative Toxicity of Ten Chlorinated Hydrocarbon
Insecticides to Four Species of Fish" It is interesting that
the different tables from the above book (as reported in this
paper) report widely different values for the same compounds.
Comment same as above except that this experiment was per- Tarzwell
formed in hard water. (1959)
-------
o
o
s
m
o Chemical
r DDT
2 (50%
m dust)
£
0 DDT
>
-D
33
O
0
c
3
en
DDT
DDT
(screened)
Cp DDT
ON
NJ
DDT
(dust)
DDT
DDT
Organism
Channel
catfish
(fingerlings)
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Pimephales
promelas
Oncorhynchus
kisutch
Tilapia
melanopleura
Pimephales
promelas
Lepomis
macrochirus
Sucker
Trout
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study'1) Location'2) ppm'3)
BSA - >2.0
(K 25 hr A)
BSA - 0.03 (T4A)
0.02 (T4A)
0.03 (T4A)
0.04 (T4A)
BSA - 0.042 (T4A)
0.021 (T4A)
0.036 (T4A)
0.056 (T4A)
BSA - 0.026 (T4A)
BSA - (O)
FLCH Tanganyika 1 Ib (6.6% K)
BSA - 0.032 (T4A)
0.016 (T4A)
FR Mont. (0)
Experimental
Variables
Controlled
or Noted'4) Comments
a Tap water was used. Considerable additional data are
presented.
a d e f Concentrations were based on percent active ingredient.
a b e c d f Dilution water was usually soft although some studies were
~ conducted with hard water.
a b e c d f Comment same as above.
a This study provides information relating to an extensive
field survey conducted to assess the effect of DDT spray
deposition on aquatic fauna within the sprayed area.
Times to 50% mortality (ETsfj) were 850 minutes for
0.31 DDT, and 1 750 minutes for 0.08 ppm of DDT.
Levels of 0.05 ppm may be "safe" for coho salmon inas-
much as this level did not produce death in one week.
— Trial periods were for 20 weeks. Sublethal effects such as
impaired breeding, retarded growth, or altered taste were
not detected. Dosages are given as Ib/acre of surface water.
a Bioassay investigations of the new insecticides indicate that
in general the organic phosphorus compounds are not as
toxic to fish as are the chlorinated hydrocarbons. The
toxicity of most of these materials was not significantly
influenced by water quality. Therefore it is to be expected
that the toxicity of these materials will not differ significantly
in different streams.
— Aerial application rate was 1 Ib/acre. Recovery of DDT from
streams was 0.01 to 1.2 Ib/acre. Surface water 15 minutes
after spraying contained 1 .35 ppmg. Sub-surface 0.08 ppm.
and zero DDT before spraying. Initially, dead fish were
mostly suckers, but no trout. Dead trout began appearing
5-6 months after spraying. Trout body tissue contained
DDT. Considerable variation was found and no conclusions
could be made.
Reference
(Year)
Clemens and
Sneed
(1959)
Henderson, et al
(1959)
Henderson, et al
(1959)
Henderson, et al
(1959)
Alderdice and
Worthington
(1959)
Webbe and
Shute
(1959)
Tarzwell
(1959)
Graham and
Scott
(1959)
^
ip
•o
m
z
o
X
-------
DDT
DDT
T3
DDT
DDT
DDT
(technical,
25% active
in xylene)
O
o
S
m
30
O
Cambusia
affinis
Huro
salmoides
FL
Fla.
(O)
Salvelinus
fontinalis
Salmo
clarki
Prosopium
williamsoni
Salmo
gairdnerii
Salmo
trutta
Rhinichthys
cataractae
Daphnia
magna
Salmon
Acroneuria
pacifica
Pteronarcys
californica
Claassenia
sabulosa
Arctopsyche
grandis
FR
Mont. &
Wyo.
(O)
BSA
FR
BSA
Mitamichi
R., N.B.,
Can.
0.0014 (O)
(O)
0.18(T4A)
0.33 (T4A)
0.01 (T4A)
0.1 (T4A)
a c e f I n
Surface applications of DDT as a dust and in oils were not
harmful to fish in dosages used for mosquito control
(0.1 pound per acre) other cold-blooded aquatic life, such
as frogs, snakes, crayfish, spiders, and insects, were obviously
affected by suspensions of DDT.
No harmful effects on warm-blooded animals in the area were
noted. When a small pond was treated with 2.0 ppm of a
suspension containing 10 percent each of DDT and Nopco
1216 (sulfonated sperm oil) in cellosolve, at the end of
1 week all fish were killed. A third pond treated with the
same formulation at 0.2 ppm killed all the fish in 4 days.
This paper deals with the accumulation of DDT in trout and
whitefish after exposure to DDT sprayed over large areas
in Montana and Wyoming. The chemical was applied at
1 Ib/acre with an average of approximately one-quarter
pound per acre reaching the ground and the water. The
greatest concentration of DDT was found in fat, followed
by kidney, pyloric caecum and brain, in that order. At the
given rate of application, this chemical was toxic to all the
fish listed.
The indicated concentration immobilized Daphnia in
50 hours.
Spraying with DDT in unspecified amounts markedly re-
duced the salmon population in this river. In 1954, salmon
fry were virtually eliminated and most of the parr were
killed.
Assays were conducted in hard water.
Dupree
(1960)
Cope
(1961)
Anderson
(1960)
Kerswill.et al
(1960)
Gaufin
(1961)
O
I
m
S
O
33
O
O
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-------
o
0
5
S
m
o Chemical
o DDT
i
m
S
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r~
3)
O
D
C
q
V)
DDT
DDT
0
r\
^ DDT
DDT
(25 percent
EC)
DDT
(tech grade
emulsified
in xylene)
DDT
Organism
Brook
trout
White
suckers
Crayfish
Oncorhynchus
kisutch
Oncorhynchus
tshawytscha
Sal mo
gairdnerii
Gasterosteus
aculeatus
Salmo
gairdneri
Aedes
aegypti
(larvae)
Gambusia
affinis
Hydropsyche
californica
Arctopsyche
grandis
Acroneuria
pacifica
Pteronarcys
californica
Ephemeroptera
Trichoptera
Plecoptera
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study (D Location<2) ppm(3)
F Potter and (O)
Tioga
Counties,
Penn.
BSA - 44 (T4A)
11.5 (T4A)
42 (T4A)
18 (T4A)
BSA - 0.410 (T1A)
0.410 (T2A)
0.395 (T4A)
BSA
FL Ponds- (O)
Bakersfield,
Cal.
BSA - 0.048 (T4A)
0.175 (T4A)
0.41 (T4A)
0.56 (T4A)
FR Mont. -
Experimental
Variables
Controlled
or Noted (4) Comments
— DDT was applied as an aerial spray at 0.5 Ib/acre. Thirty-two
days after spraying, 10.6 ppm was found in brook trout,
but 122 days after treatment the amount was at pretreatment
level (0.7 ppm).
In white suckers, 32 days after treatment, 6.9 ppm was found;
and 122 days post-treatment, the concentration had dropped
to a pretreatment level (0.24 ppm).
Analyses of crayfish were anomalous — in some instances, the
pretreatment specimens contained 1 .9 ppm or more than
32 days later when the value was 1 .1 ppm.
This same paper gave some data on the DDE, TDE, and dieldrin
content of these same animals.
acde Chemical dissolved in acetone. TLm expressed in ppb.
a c d f g Hatchery artesian well water was employed for this
~ experiment.
a Increase in temperature during exposure to DDT (0.02
ppm — 1 hr) increased the toxic action. Additional data
are presented.
a c At 0.5 Ib/acre, 20 percent mortality occurred in 24 hours.
At 2.0 Ib/acre, 40 percent mortality occurred in 24 hours.
The experiments were conducted in cages placed in the
ponds.
a c d e I n Test water was obtained from a mountain stream.
— A large area in Montana was sprayed with 1 pound of techni-
cal DDT in 1 gallon of No. 2 diesel fuel per area. The streams
draining this area were assayed. It was found that a drastic
reduction in all biota took place in Hell roaring Creek and
Tower Creek. Pebble Creek, situated away from the test area.
served as a control and no reduction occurred. In both
Hellroaring and Tower Creeks, repopulation of plecopteran
populations occurred leveled by the following year while this
did not occur for the other organisms until 3 years had elapsed.
Reference
(Year)
Cohen, et al
(1961)
Katz
(1961)
Webb
(1961)
Das and
Needham
(1961)
Mulla and
Isaak
(1961)
Gaufin
(1961)
Hastings, et al
(1961)
TJ
•o
m
Z
g
x
DO
-------
DDT
DDT
DDT
DDT
DDT
m
3D
O
o
-a
3D
O
O
c
DDT
Lebistes
reticulatus
(Adult)
(Young)
Sa/mo
trutta
(2wk)
(10 wk)
(11 wk)
Salmo
trutta
Ephemeroptera
BSA
BSA
FR
Various insects
FS
Adirondack
Mountains
Africa
Protococcus sp
Chlorella sp
Dunaliella
euchlora
Phaedactylum
tricornutum
Monochrysis
lutheri
Cutthroat
trout
FL
Wyo.
0.018 (T14 A)
0.0024 (T14A)
<0.18 (T14A)
0.00056 (T14A)
0.014 (T14A)
fingerlings
0.5 and 0.1 (O)
(O)
(O)
0.6 (O)*
0.6 (O)*
0.6 (O)*
0.6 (O)*
0.6 (O)*
•obvious,
but inhibited
growth.
(O)
Deep well water was used as diluent. Histological observa-
tions were found to be similar for guppies and trout
despite age differences, DDT concentration, and exposure
periods.
Liver: degeneration
Kidney: no change in guppy — 1-2 days tubules occluded
in trout.
Other data and observations presented.
C14 labeled DDT was placed in the water at the concentra-
tions listed. Various organs and tissues of the trout were
analyzed for DDT. The analytical method is outlined. At
0.5 ppm, one fish died in 18 hours, and another at 160 hours.
At 0.1 ppm, one fish died in 30 hours and another at 230
hours. Only two fish were used at each concentration.
DDT was applied as low as 0.1 Ib/acre for effective control
of blackfly. There was a small number of Ephemeroptera
and Diptera in regularly treated streams, but the reduction
in overall numbers did not reach a significant level. The
treated and untreated streams were sampled in 1950-52
and in 1961.
This study showed that the effect of a single application
of DDT on an African stream eliminated the majority of
aquatic insect species for varying distances. It seems
fairly certain, however, that almost all the species survived
as eggs, from which the population was replenished.
The three major predators were, however, among the most
severely affected, and this led to an increase in the principal
prey organisms, Baetidae and Simulium. This was an
effect which has been observed in streams in Europe and
North America, and indicates that DDT treatments could
lead to severe outbreaks of Simulium species. The amount
of the DDT sprayed on an area was not specified.
This paper concerns the growth of pure cultures of marine
plankton in the presence of toxicants. Results were
expressed as the ratio of optical density of growth in
the presence of toxicants to optical density in the basal
medium with no added toxicants.
King
(1962)
Five lots of fish were given DDT once a week in their diets
at different rates for each lot.
Fish were fed in mg/kg of body weight. Analysis showed that
residues of DDT, DDE, and ODD were present in fish fed
3 and 1 mg/kg per body weight. Greatest number of deaths
occurred in fish lots fed 3 mg/kg of body weight.
Holden
(1962)
Jamnback and
Eabry
(1962)
Hynes and
Williams
(1962)
m
z
O
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09
Ukeles
(1962)
Cope
(1963)
-------
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DDT
T3
ON DDT
ON
DDT
DDT
EC 2
DDT
(tech)
DDT (anti-
resistant
50 percent WP)
Bioassay
or Field
Organism Study '^
Rainbow FL
trout
Bullhead
Crayfish
Acris Lab
crepitans
A. gryllus
Cladocerans FL
Copepods
Ostrocods
Rotifers
Volvox
Culex BSA
pipiens
quadrimaculatus
Rana FL
catesbeiana
(tadpoles)
Procambarus BSA
clarki
Salmo BSA
gairdneri
Toxicity,
Active
Field Ingredient,
Location»2) ppm(3)
Colo. 0.02 (O)
(0)
Minn. (O)
(0)
Cal. 1.0(0)
0.6 (T3A)
24(T1A)
21 (T2A)
16 (T4A)
Experimental
Variables
Controlled
or Noted W) Comments
- The pond was treated with DDT at a rate of 0.02 ppm.
The concentration of DDT in the pond was at its highest
point 30 min after treatment. None could be detected
after 21 days.
Bullheads and trout contained the greatest amounts of
chlorinated hydrocarbon 30-40 days after treatment,
with concentrations over 4 ppm. Levels slowly declined
after that, averaging 3.5 ppm in samples taken 9 and 10
months after treatment in both species, and 3 ppm in
rainbow trout taken 14 months after treatment.
Crayfish developed lower DDT residues than did trout.
and contained 0.33 ppm after 14 weeks.
a Possible resistance to DDT was demonstrated in natural
populations of frogs from several Mississippi localities
by exposure to different DDT concentrations for 36
hours. Frogs living near cottonfields heavily treated
with DDT for several years tended to be less susceptible
to the chemical than individuals having little or no prior
contact with DDT. The animals were placed on filter
paper impregnated with varying amounts of DDT. The data
are difficult to average because of the range. It would
appear that 30.0 g per liter was the TLm for 36 hours for
A. crepitans, and 9.0 g per liter for A. gryllus (sic).
— At an application rate of 1 Ib/acre, depression of micro-
crustacean populations occurred a few days after application.
but this was followed by an apparent rapid recovery.
c Tests were conducted in tap water and artificially polluted
tap water. The values reported are the concentration
range for an LCgo, 0.1 2 to 0.55 ppm for polluted and
0.33 to 128.0 ppm for tap water.
a c Mixed populations of the indicated test species contained
in cages were exposed to various insecticidal chemicals
applied as dilute sprays to ponds 1/16 acre in size. The
indicated toxicant concentration is in Ib/acre, and resulted
in a 30 percent mortality for the tadpoles in 24 hr.
a c d o There was no detectable difference in toxicity to male or
female crawfish.
a The experiments were conducted at 55 F. Fish were 2-3
in. long.
Reference
(Year)
Cope
(1963)
Boyd, et al
(1963)
Jones and
Moyle
(1963)
Le wall en and
Wilder
(1963)
Mulla
(1963)
Muncy and
Oliver
(1963)
Cope
(1963)
•n
\t
-o
m
2
o
03
-------
DDT (anti-
resistant
25 percent EC)
DDT, p-p'
DDT
DDT
8
DDVP
(tech)
Salmo
gairdneri
Salmo
gairdneri
BSA
BSA
Lepomis
macrochirus
Redear
Rainbow
trout
Long-nose
sucker
Cutthroat
trout
Brown
trout
Brook
trout
Mountain
whitefish
Gambusia
affinis
Salmo
gairdneri
BSA
BSA
10 (T1A)
18(T18hr)
11 (T32hr)
10 (T56hr)
10(T1A)
10(T1A)
6.0 (T1A)
5-6 (T1A)
6.0 (T1 A)
19 (T1A)
15(T1A)
(O)
0.05-0.10 (O)
BSA
500 (T1 A)
Comment same as above.
Comment same as above.
Cope
(1963)
Cope
(1963)
Comment same as above.
The experiment was conducted at 65 F. Fish weighed
0.6 g.
The experiment was conducted at 65 F. Fish weighed
0.4 g.
The experiment was conducted at 75 F. Fish weighed
1.5g.
The experiment was conducted at 75 F. Fish weighed
0.4 g.
The experiment was conducted at 75 F. Fish weighed
3g.
a d g Hatchery trout under 3.1 inches in length had a mortality Schoenthal
rate of 100% at all concentrations for 0.5 to 10.0 ppm. (1963)
The mortality rate decreased as size increased (66% for
those over 5 inches). Wild rainbow trout under three
inches had a mortality of 24%. Hatchery trout showed
a 50 to 75% higher mortality than the wild trout.
A comparison of six species of cold-water fish over four
inches in length tested in 1 ppm DDT showed that the
long-nosed sucker had a mortality rate of 94%, while
the rainbow trout, cutthroat trout, brown trout, brook
trout, and mountain whitefish had a mortality rate of
less than 10%.
— Mosquito fish from waters near cotton fields that have a Vinson, et al
long history of treatment with chlorinated hydrocarbon (1963)
pesticides exhibited a marked resistance to DDT compared
with fish from areas which had had no past exposure to
insecticides. As an example, for a DDT concentration
of 0.05 ppm:
72 hours 90% mortality occurred for fish from
untreated areas
72 hours 25-28% mortality occurred for fish from
DDT treated ponds.
a The experiment was conducted at 55 F. Fish were 2-3 in. Cope
long. (1963)
I
m
O
X
00
o
TJ
3J
O
O
§
-------
o
o
s
2
m
o Chemical
J>
"~ DDT
O
I
m
S
o
>
i-
-o
30
o
O
C
0
a
DDT
T3
ON
OO
DDT
DDT (tech,
98 percent
active in
acetone)
DDT
DDT
Organism
Sal mo
lewis i
clarki
Ophicephalus
punctatus
Barbus
stigma
Notemigonus
crysoleucas
Lepomis
macrochirus
L. cyanellus
Pteronarcys
californica
(naiad)
Acroneuria
pacifica
(naiad)
Gammanjs
lacustris
Bluegill
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study d) Location*2) ppm(3) or Noted <4>
BSA - (O) acef
BSA - 1.0 (K)
(0)
BSA - (B) 0.032 (T 1.5) act
(A) 0.028 (T 1.5)
(B) 0.028 (T 1.5)
(A) 0.033 (T 1.5)
(B) 25 (T 1.5)
(A) 22 (T 1.5)
BSA - 1.8IT4A) cdef
0.32 (T4A)
BSA - 0.009 (T4A) ae
BSA - 0.016 (T4A) a
Comments
This experiment concerns the periodic exposure of fish
to different levels of DDT in bath and in food over a
20-month period involving one spawning cycle. It was
decided that a threshold level exists around 0.1 ppm
monthly in contact form and around 0.3 mg DDT per
Kg of fish weekly in the diet for the toxic effects of DDT.
Fish lots given 0.1 ppm DDT monthly in bath form ex-
hibited significantly higher mortality, similar size, and
similar reproductive success when compared with the
control group.
Fish lots treated weekly with DDT in the diet at the rate of
0.3 milligrams per kilogram of body weight did not differ
from the control except, in a highly variable manner.
residue buildup, and a nonsignificant increase in mortality
during the last few months of the experiment.
Experiments were conducted in a trough containing 3500 cc
of water sprayed with 1 cc of a 25% DDT emulsion. Liver
and intestines were examined for residues and both were
found to contain 0.08083 g of DDT.
When 5 cc of a 25% DDT emulsion was sprayed, the fish died
in 2 hr. The fish were found to contain 0.1 344 g of DDT
residue in the intestine and 0.1292g in the liver.
When 5 cc of a 25% DDT emulsion was sprayed in a small
jar containing 2 liter of water, death occurred in 2 hr and
30 min. Residues found were 0.06523 g of DDT in liver and
0.07799 g in intestines.
Chemical was dissolved in acetone. Final concentration of
acetone was <2 ml/I. Data shows TLm ppb for insecticide-
resistant (A) and insecticide non-resistant (B) strains of
the test fish.
A. pacifica was much more sensitive to chlorinated hydro-
carbons and to organic phosphate insecticides than
P. californica.
Emulsible concentrates were prepared from technical
grade insecticides with acetone as the solvent.
Symptoms prior to death were observed and recorded
on graphs.
Assays were conducted in soft water at 25 C. Decrease
in brain cholinesterase was measured in fish exposed
to the toxicant.
Reference
(Year)
Allison, et al
(1964)
Mathur
(1964)
Ferguson, et al
(1964)
Jensen and
Gaufin
(1964)
Nebeker and
Gaufin
(1964)
Weiss
(1964)
>
•o
•o
m
O
X
-------
DDT
DDT
DDT + Toxa-
phene
DDT
DDT
DDT
DDT
8
m
3D
o
O DDT
m
2
O
TJ
35
O
o
Trout: brown
and rainbow
Cottus sp
Trichoptera
Plecoptera
Coleoptera
Diptera
Ephemeroptera
Salmo
gairdnerii
Ictalurus
punctatus
Lepomis
macrochirus
Pteronarcys
californica
Oyster
Oyster
FR
Mont.
0.02 mg/l
Cyprinodon
variegatus
(juvenile)
Fundulus
similis
(juvenile)
DDT + Strobane Oyster
Blue
crab
Rainbow
trout
BSA
Palaemonetes
kadiakensis
BCF
BCH
BSA
BCF
BCH
BSA
BSA
1.5 (T4A)
3.3 (T4A)
4.7 (T4A)
7.0 (T4A)
0.030 (O)
(O)
a c d
0.005 (O)
0.018 (O)
0.022 (O)
(O)
4.1 (T4A)
5.0 (T4A)
6.0 (T4A)
(N) 4.5 (T1-1/2A)
(TB)10(T1-1/2A)
acf
The application rate was 0.5 Ib/acre. Before and after
spraying, determination of DDT concentrations was made
on fish homogenates. Dead fish found after spraying were
found to contain up to 0.6 mg/kg DDT. However, live
fish caught were found to contain up to 3.4 mg/kg DDT.
Fish kills occurred up to 48 hours after spraying. Exten-
sive mortality of aquatic insects occurred, but not
consistently throughout sprayed area of river.
Toxicity values reported as median lethal cone.
for 24,48, 96 hr.
The value reported is a 96-hr ECgo (decreased shell growth).
Oysters exposed to DDT at a concentration of 0.0001 ppm
contained 70,000 times that concentration after 40 days.
Oysters exposed to the chemical at 0.001 ppm for 1 2 days
contained 12 to 20 ppm. Because the oyster can concen-
trate DDT so readily, it is an organism of choice to use in
monitoring for pesticide pollution.
Water temperature was 9 C. The figure reported is a 48-hr
Water temperature was 21 C.
The value reported is a 96-hr
(decreased shell growth).
DDT at a concentration of 0.001 ppm kills crabs in 8 days.
Crabs can live and grow in a concentration of 0.00025 ppm.
These experiments were performed to show the effect of
temperature on the toxicity.
For the toxicant concentrations listed, the temperatures
were respectively 45, 55, and 65 F. The fish all were
approximately one gram in weight.
Toxicant concentrations for one and 2-day times were also
listed.
Test organisms were collected from 2 locations. Twin Bayou
(TB), Sunflower Co., Miss, (agricultural area) and Noxubee
National Wildlife Refuge (N), Noxubee Co., Miss, (non-
agricultural area) and evaluated in laboratory bioassays .
The Twin Bayou shrimp were more resistant.
Welch and
Spindler
(1964)
Bridges and
Cope
(1965)
Butler
(1965)
Butler
(1965)
Butler
(1965)
Butler
(1965)
Butler
(1965)
Cope
(1965)
Ferguson, et al
(1965)
-------
0
o
s
s
m
o Chemical
j>
r DDT
O
I
m
^
O
£ DDT
-o
21
o
O
(-)
C/5
DDT
0
0
}
DDT
DDT
DDT
Organism
Gambusia
af finis
Ictalurus
me/as
Lepomis
cyane/lus
Gambusia
af finis
Ictalurus
me/as
Arctopsyche
grandis
Pteronarcys
californica
Acroneuria
pacifica
Ephemera/la
grandis
Hydropsyche
californica
Daphnia
magna
Gammarus
lacustris
Bluegill
Fathead
minnows
Acroneuria
pacifica
Ephemeral/a
grandis
Gammarus
lacustris
Pteronarcys
californica
Salmo
sa/ar
Fish
Shell fish
Birds
Mice
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Studyd) Location^2) ppm<3' or Noted'4)
BSA - 0.008-0.023 (T3A) £cde
0.009-0.275 (T3A)
F Miss. 0.52 (0)
BSA - 0.18IT4A) £
1.8(T4A)
0.3 (T4A)
0.03 (T4A)
0.05 (T4A)
0.001 (T50hr A)
0.009 (T4A)
0.03 (T4A)
0.03 (T4A)
BSA - 0.32 (T4A) £C
0.025 (T4A)
0.009 (T4A)
1.8IT4A)
BCFCH - 0.005-0.05(0) £6
FLR Conn. (O) —
Comments
Test fish were collected from 8 different locations of the
Mississippi River. The 3-day TLm values were made to
determine if a resistance gradient existed. The data
indicated that there was none.
Muds reduced the toxicity of chlorinated hydrocarbon
insecticides to fish. Lethal quantities of pesticides
enter national waters and muds may contain sorbed
pesticides in excess of lethal quantities. Although the
chemicals can be leached with organic solvents, they
were either not released in lethal amounts or slowly
released in standing water.
Unspecified chemical characteristics of assay water were
determined by standard methods. General comments
were made concerning "standardized" conditions, use
of "soft" water, and use of emulsifying agents. Addi-
tional data are presented.
Additional TLm data are given.
The fish were exposed to the reported sub-lethal doses
for 24 hours. Low dosages of DDT produced a downward
shift in the temperature response whereas higher doses
produced an upward shift.
The results showed that DDT was present in animals in areas
where no spraying had been conducted. Analyses showed
the following:
Whole fresh fish — 0.1 to 0.9 ppm DDT
Shell fish — 0.031 to 0.07 ppm
Birds — 0.1 to 0.8 ppm
Mouse kidney fat — 1.O1 to 8.19 ppm
Reference
(Year)
Ferguson, et al
(1965)
Ferguson, et al
(1965)
Gaufin, et al
(1965)
Gaufin, et al
(1965)
Ogilvie and
Anderson
(1965)
Turner
(1965)
>
*o
•o
m
z
o
X
CD
-------
DDT
DDT
DDT
DDT
T5
DDT
DDT
DDT
8
m
3)
o
m
Brown
trout
Oysters
Adult
Larvae
Crassostrea
virginica
Salmo
gairdnerii
Lepomis
macrochirus
Ictalurus
punctatus
Pteronarcys
californica
Baetus sp
Daphn/a
pulex
Simocephalus
serrulatus
Cyprinodon
variegatus
Gambusia
affinis
Pygosciles
adeloriae
Lobodon
carcinophagus
BSCH
BCF
BCF
BSA
0.10(0)
BSA
BSA
FM
(O)
1.0 (K6)
(O)
0.005 (T2A)
0.005 (T2A)
0.012 (T2A)
0.016 (T2A)
0.012 (T2A)
0.0004 (T2A)
0.002 (T2A)
0.020 (O)
0.030 (O)
0.040 (O)
(O)
Boss
Island,
Antarctic
(O)
Data given on DDT concentrations in various tissues on Weiss
weight basis are as follows: (1965)
Brain 0.6 ppm
Muscle 0.7 ppm
Sea water was employed in this experiment. As the Butler
concentration of DDT increased from levels of 1.0 ppb to (1966)
1.0 ppm, there was a logarithmic decrease in the rate of
oyster shell growth from about 20 to 90 percent.
Tests were conducted in flowing seawater. DDT in levels Butler
as low as 0.001 ppm caused marked reduction in oyster (1966)
growth.
This paper reports acute toxicity of a number of compounds. Cope
and discusses sub-acute mortality as well. Effects on repro- (1966)
duction and behavior are also discussed. Data presented as
EC50-
m
Holland, et al
(1966)
O
X
Ferguson and **•
Bingham
(1966)
A concentration of 0.020 ppm caused 80% mortality,
0.030 caused 87% mortality, and 0.040 caused 97%
mortality in 24 hr.
The effect of combinations of pesticides was studied. In
general, the results reflected the extreme levels of Endrin
and Toxaphene resistance in the resistant population. The
results failed to indicate additive effects wherein the com-
bination mortality exceeded the sum of the mortalities
produced by the individual insecticides.
Adult penguins assayed had residues ranging from 0 to 8 ppb. George and
The pre-molts examined had residues ranging from 1 to 16 Frear
ppb in the liver, and 0 to 69 ppb in the fat. The crab- (1966)
eater seal examined showed residues of 4 ppb in the liver
and 15 ppb in the fat.
TJ
3)
O
O
§
-------
o
o
S
2
m
n Chemical
J^ p,p' -DDT
I
m
S
O
r~
J)
0
c
q
en
3
j
J
DDT
DDT
DDT
Organism
Sal mo
gairdnerii
S. trutta
Salvelinus
Ion final is
S. namaycush
Esox
lucius
Carassius
auratus
Chrosomus
eos
Cyprinus
carpio
Pimephales
prome/as
Icta/urus
punctatus
Eucalia
inconstans
Lepomis
cyanellus
Lepomis
gibbosus
L. macrochirus
L. mega/otis
Micropterus
salmoides
Perca
flavescens
Aplodinotus
grunniens
1. me/as
Simocephalus
serrulatus
Daphnia
pulex
Daphnia
magna
Daphnia
carinata
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study'1' Location(2) ppm<3)
BSA - 0.0107IT4A)
0.0109 (T4A)
0.0115 (T4A)
0.093 (T4A)
0.0017 (T4A)
0.0587 (T4A)
0.0680 (T4A)
0.0082 (T4A)
(0)
0.0175 (T4A)
0.0670 (T4A)
0.0045 (T4A)
0.0045 (T4A)
0.0045 (T4A)
0.0087 (T4A)
0.0008 (T4A)
0.0009 (T4A)
0.0100 (T4A)
0.0258 (T4A)
BSA - 0.0025 (SB)
0.00036 (SB)
BSA - 0.0044 (SB)
BSA - 0.0022 (SB)
Experimental
Variables
Controlled Reference
or Noted'4) Comments (Year)
a Data are given for various lots within each species of fish Marking
obtained from different sources. However, a mean was (1966)
given which is reported here.
Data for fathead minnows were not consistent. The toxicity
did not increase uniformly with increased concentrations
up to 1.0 ppm.
— Concentration reported is for immobilization. Sanders and
Time for immobilization was 48 hr. Cope
Data cited are for 60 F, but assays were performed at (1966)
varied temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
— Comment same as above. Sanders and
Cope
(1966)
— Comment same as above. Sanders and
Cope
(1966)
^
^
•o
m
O
CO
-------
DDT
DDT
DDT
DDT
(mixed
isomers)
DDT
DDT
8
DDT
X
in
2
Oncorhynchus
kisutch
Tubifex spp
Limnodrilus spp
Salmo
gairdnerii
Rasbora
heteromorpha
Salmo
gairdnerii
Rasbora
heteromorpha
Mya
arenaria
Crassostrea
virginica
Mya
arenaria
Crassostrea
virginica
Corbicula
manillensis
Mercenaria
mercenaria
Rangia
cuneata
Aquatic insects:
Ephemeroptera
Diptera,
Simulidae
Plecoptera
Trichoptera
BSA
BSA
BSA
0.024 (T2A)
0.013 (T4A)
100 (L4A)
(O)
(O)
js c e j k
BCFA
0.0015
(threshold)
BSCH
BCFCH
(0)
(0)
FR
Ontario, (O)
Can.
DDT at the given concentrations seemed to cause a
coughing reaction in the fish. It was theorized that
this coughing reaction was a reversal of the water
flow over the gills as a gill cleansing reaction.
Toxicity is reported as the mean lethal dose (LD5g)
for 24, 48, and 96 hours.
This report derives as mathematical equation for deter-
mining a threshold concentration of a toxicant. For
many toxins, the rate of mortality is a linear function
of the concentration. The value of 0.02 ppm of DDT was
obtained by interpolation from three different curves for
the trout. The tests were conducted in hard water. A
value of 0.04 ppm for harlequin fish was also obtained
by interpolation from a graph.
Aerated hard water was used. Threshold concentrations
were examined by 4 methods.
1. Long term — survival related to concentration.
2. Short term — percentage kill in narrow range
of concentrations.
3. Comparison of survival times.
4. Extrapolation of short-term results by plotting
velocity of death against log of concentration.
Oysters were exposed to 2.0 to 4.0 ppm DDT and then fed to
shrimp and fish. At the end of 2 to 4 weeks, at least 50
percent of the experimental animals died. M. arenaria (soft
clam) proved to be the most sensitive or efficient in storing
organochloride residues.
Results are recorded as a range of uptake of the chemical by
5 species of aquatic mollusks. An uptake or concentration
of 1200-9000X resulted.
Schaumberg
(1967)
Whitten and
Goodnight
(1966)
Abram
(1967)
Abram
(1967)
Butler
(1967)
Butler
(1967)
m
z
O
X
00
This is a review paper on the effect of DDT in the reduction Ide
of insects, and the time it takes a population to reestablish (1967)
itself. The area was sprayed with DDT at a rate of 0.5 Ib/acre.
Most organisms recovered to normal populations within 2-3
years, but caddisflies required 4 or more years.
-u
30
O
o
c
-------
o
o
s
s
m
o Chemical
>
I" DDT
O
I
m
S
o
r-
-o
33
O
O
O
•H
DDT (prills)
p*
o
•3
±
Bioassay
or Field
Organism Study^""
Leptonychotes FM
weddelli
Pygoscelis
adeloriae
Catharacta
skua
maccormicki
Aptenodytes
forsteri
Rhigophila
dearborn!
Trematomus
bernacchii
T. hansoni
Invertebrate
samples
Arthropoda
Echinodermata
Nermertinea
Mollusca
Amphipoda FR
Elmidae
Grypopterygidae
Turbellaria
Oligochaeta
Gastropoda
Decapoda
Odonata
Plecoptera
Ephemeroptera
Hemiptera
Trichoptera
Megaloptera
Coleoptera
Diptera
Anguillidae
Galaxiidae
Eleotridae
Toxicity,
Active
Field Ingredient,
Location (2) ppm (3)
Antarctic (O)
(0)
(0)
(0)
(0)
(0)
(0)
(0)
New (O)
Zealand
(4
streams)
Experimental
Variables
Controlled
or Noted^) Comments
a All residues are expressed as ppm wet weight.
It was established that residues in the water were less than
0.0005 ppm. L. weddelli contained residues ranging
from 0.042 to 0.12 ppm in fat. No residues were found
in other tissues. Adult P. adeliae contained residues of
0.015 to 0.018 ppm of DDT in fat.
C. skua maccormicki contained residues ranging from 0.01
to 0.68 in 9 tissues examined. A. forsteri adults were
examined for residues and found to contain none.
Ten Ft. dearborn/' were examined and found to contain an
average of 0.44 ppm DDT residue. T. bernacchii and
T. hansoni were examined and contained no residues.
It was established that there were no residues at levels as
high as 0.005 ppm in invertebrates.
— DDT prills were applied from the air to 200 acres of sheep
pasture. The mean weight of active DDT reaching the
ground was 61.3 mg/square meter. Changes in the fauna
of streams draining the treated pasture were studied for
12 months after the application. A high mortality was
found in most of the aquatic insect fauna with the excep-
tion of Elmidae (Coleoptera) and Grypopterygidae
(Plecoptera). Amphipoda were virtually wiped out. At
the end of the investigation large number of insects were
again present but with a completely altered species com-
position. Mortality to freshwater crayfish was doubtful.
and unproven for fish. The levels of DDT found in whole
fish are discussed.
Reference
(Year)
George and
Frear
(1966)
Hopkins, et al ^
(1966) TJ
T)
m
z
g
00
-------
DDT and
"organo-
chlorine
residues"
Pontoporeia
affinis
A/osa
pseudoharengus
Coregonus
clupeafoimis
Leucichthys sp
FLCH
Wise.
DDT
Prosimulum spp
Cnephia spp
Simulium spp
(larvae)
LCFA
0.04 (O)
DDT
Fish
Cal.
(O)
pp DDT
8
m
3)
o
o
Buteo
buteo
Accipiter
gen til is
Accipiter
nisus
Falco
tinnunculus
Tyto
alba
Strix
aluco
Oslo
otus
Falco
pereginus
FO
Netherlands (O)
-o
3)
O
O
c
Pesticide residues were determined in mud sediments, Hickey, et al
insects, fish, and birds. (1966)
Conclusions were that the pesticides do not stay on land
but are accumulated and concentrated in moderately
large lakes.
Residues found in mud bottoms were:
DDT = 0.14ppm
DDE = 0.24 ppm
TDE = 0.03 ppm
Residues found in:
Gull food —
Insect — DDT = 0.12 ppm; DDE = 0.49;
TDE = 0.06
Alewives — DDT = 1.13 ppm; DDE = 1.77;
TDE = 0.43
Fish-
Chub - DDT = 1.6; DDE = 2.3; TDE = 0.29
Whitefisn - DDT = 1.7; DDE = 2.7;
(muscle) TDE = 0.75.
Additional residue data are presented.
Stones heavily populated with larvae were placed in troughs Jamnback and
of running water containing the toxicant. When the larvae Frempong-
became detached from the rocks and floated away, they Boadu
were assumed to have undergone lethal intoxication. The (1966)
larvae were exposed to the toxicant for 5 minutes, then in
clean water for 24 hours. At that time the number de-
tached amounted to 52 percent.
This study was primarily concerned with insecticides Keith
found in fish-eating birds. Limited fish studies were also (1966)
conducted. DDT was found in trace to 1.6 ppm concen-
trations in whole fish (wet weight).
The results of this study show that birds of prey and fish- Koeman and
eating birds found dead in the Netherlands accumulated van Genderen
large amounts of different chlorinated hydrocarbon (1966)
insecticides. In most cases the liver had the highest
concentration of toxicant, ranging from 1.6 ppm.
m
O
X
0)
-------
o
o
s
s
m
n Chemical
r DDT
O
m
2
o
^ DDT
3D
O
O
q DDT
H
p-p' DDT
DDT
03
-ij
o\
DDT-C14
DDT
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Organism Study'1) Location (2) ppm'3) or Noted'4)
Crassostrea BCFCH - (O) a
virginica
Pseudomonas 10 (SB)
piscicida
Oyster FE —
Stream insects: FR Maine (O) —
Ephemeroptera
Odonata
Plecoptera
Trichoptera
Neuroptera
Coleoptera
Diptera
Goldfish BSA & CH - 50m g/ml (K)
Atlantic F St. (O) -
salmon Andrews,
New
Brunswick
Lepomis BCFCH - (O) a
macrochirus
Carassius
auratus
Aquatic insects: FR Mitamichi — —
Diptera River,
Trichoptera New
Ephemeroptera Brunswick,
Chironomidae Canada
Comments
At 0.00001 ppm concentration, 0.1 1 ppm residue was found
in 20 days. At 0.000001 ppm concentration, 0.085 ppm
residue was found in 20 days. After extended periods of
time, small amounts of DDT actually stimulated growth
of P. piscicida.
The chemical was found in the water at a concentration
of <0.001 ppm. Oysters from the area were found to
contain <0.01 to 0.05 ppm.
At an application rate of 1/2 to 1 .0 pounds per acre, DDT
produced marked reductions in the quality and quantity
of the invertebrate fauna. Normally present fauna usually
repopulate in 2-4 years. Thirty-nine genera of aquatic
insects were studied.
Test fish were conditioned to alkyl benzene sulfonate
(4 JUg/ml) or sodium lauryl sulfate (4 )Hg/ml, for various
periods of time, then exposed to pesticides. Chronic exposure
to the detergent increased the toxicity of the pesticide.
After spraying DDT at the rate of 1/2 Ib/acre, all young
salmon were reduced in number. Underyearlings were only
2-10% as abundant, small parr 30% as abundant, and long
parr 50% as abundant.
Spraying at the rate of 1/4 Ib/acre reduced the numbers of
underyearlings by 50%, small parr by 20%, but hardly
affected large parr.
Spraying with DDT at 1/4 Ib per acre, applied twice, was
followed by low numbers of underyearlings, similar to the
effect of spraying at 1/2 Ib/acre. No equivalent data for parr
was available.
Fish were treated with carbon-labeled insecticides (0.03 ppm)
from 5 to 19 hr and uptake rates were determined. They
were placed in recovery tanks for up to 32 days. Whole
body samples were then made. It was found that in both
fish species >50 percent of the DDT absorbed was present
after 32 days.
Young salmon, both fry and parr, were seined and the stomachs
removed. Insects were removed from the stomachs, identi-
fied and counted. Forage ratios of the insects were deter-
mined and reported for 1953-1961. Reduction of all
insects by DDT was soon followed by resurgence of
Chironomidae and other Oiptera. Five years after the spray-
ing, the pre-spraying complexity of food for younger salmon
was approached. Trichoptera were the slowest to reappear.
Reference
(Year)
Butler and
Johnson
(1967)
Casper
(1967)
Dimond
(1967)
Dugan
(1967)
Elson
(1967)
Gakstatter and
Weiss
(1967)
Keenleyside
(1967)
^
TJ
T)
m
z
o
X
-------
DDT
DDT
pp'DDT
Salmo
salar
Atlantic
salmon
Brook
trout
Sucker
Cyprinids
Esox
lucius
FR
FR
FR
op'DDT
DDT
Esox
lucius
Puntius
puckelli
FR
BSA
St.
Andrews,
New
Brunswick
New
Bruns-
wick
(O)
(O)
River
Nene,
Eng.
River
Nene,
Eng.
(0)
(O)
0.048 (T4A)
a c d e I m
DDT at O.25 Ib/acre killed many insects and some fish, Elson and
but was only about half as damaging to aquatic fauna as Kerswill
a heavier dosage (0.5 Ib). After spraying at 0.5 Ib/acre, (1967)
young salmon of all size groups were found in reduced
numbers.
When DDT in an oil emulsion was sprayed at 0.5 Ib/acre, Kerswill and
heavy losses in underyearling salmon and parr were Edwards
observed. Wild young salmon were found in streams when (1967)
autumn water temperatures approached freezing after
June sprayings with DDT. Spraying with DDT at 0.25
Ib/acre had no effect on caged, or native fish during a
period of 2 or 3 weeks after spraying. In one area
suckers and cyprinids were extensively killed after 0.5
Ib/acre spraying of DDT.
Higher concentrations were found in larger fish, indicating Mawdesley-
that they had been exposed to the pesticides for a longer Thomas and
time. Tissue extracts from the pike were analyzed for Leahy
organochlorine pesticide residues by gas liquid chroma- (1967)
tography. The values for large pike were:
0.068 ppm muscle
6.7 ppm fat
Comment same as above except that: Mawdesley-
0.38 ppm muscle Thomas and
52.0 ppm fat Leahy
(1967)
Tap water was used as diluent. Toxicity data are given Rao, et al
as TLm's in ppm for 24, 48, 96 hr. The pH of the (1967)
water averaged at 8.3. The study was conducted in
India.
•O
m
o
X
a
S
m
r
o
m
•o
3)
O
O
-------
o
o
2
S
m
o Chemical
n DDT
O
I
m
p
>
r~
33
O
O
c
q
tn
0
J
Q
DDT
DDT
Bioassay
or Field
Organism Study 'T
Plankton FECH
Cladophora
gracilis
Shrimp
Opsanus
tau
(immature)
Menidia
menidia
Crickets
Nassarius
obsoletus
Gasterosteus
aculeatus
Anguilla
rostra ta
Flymg insects,
mostly Diptera
Spartina
patens
Mercenaria
mercenaria
Cyprinodon
variegatus
Fundulus
heteroclitus
Paralichthys
dentatus
Esox
niger
Strongylura
marina
Spartina
patens
Lamps! Us FR
siliquoidea
L. ventricosa
Anodonta
grandis
Vascular FL
plants
Algae
Chubs
Large mouth
bass
Clams
Toxicity,
Active
Field Ingredient,
Location(2) ppm(3)
Long 0.040 (O)
Island, 0.083 (O)
N'. Y.
0.16 (O)
0.17 (O)
0.23 (O)
0.23 (O)
0.23 (O)
0.26 (0)
0.28 (0)
0.30 (0)
0.33 (0)
0.42 (0)
0.94 (O)
1.24 (O)
1.28 (0)
1.33 (O)
2.07 (0)
2.80 (0)
Red Cedar (O)
River,
Mich.
Tule (O)
Lake,
Ore.
Experimental
Variables
Controlled Reference
or Noted<4> Comments (Year)
— DDT residues in soil of the defined estuary area averaged Woodwell, et al
more than 13 pounds per acre with a maximum of 32 (1967)
pounds per acre. These values are based on the wet weight
of the whole organism.
— The amount of the chemical sprayed in the area was not Godsil and
specified. Residue in plants ranged from 0.7 to 10.0 ppb. Johnson
Algae contained 0.4 to 3.0 ppb. Chubs contained 2.5 to (1968)
1 7 ppb. Bass - 6.0 to 50.0 ppb. Clams 1 .0 to 4.0 ppb.
The water contained 0.002 to 0.027 ppb.
— The mussels listed were analyzed for the toxicant and its Bedford, et al
metabolites. Mussels may be used as detectors for this (1968)'
toxicant, because they tend to concentrate the chemical
in much higher concentrations than it is ever found in the
water. The amount of chemical applied as a spray was not
specified.
-o
m
Z
O
00
-------
DDT
(and
analogues)
DDT
DDT
DDT
o.p-DDT
8
m
o
L imnephilus
rhombicus
Siat/s sp
Gammarus sp
Salvelinus
fontinalis
Semotilus
atromaculaWs
Cottus
bairdi
Rhinichthys
atratulus
Alosa
pseudoharengus
Aplodinotus
grunniens
Coregonus
artedii
Lota
lota
Salmo
salar L.
Knights
Creek,
Wise.
(O)
BSA
(O)
BCFA
(O)
Salvelinus
fontinalis
BSA
(SB)
ac d e p
Potamogeton
pectinatus
Cladophora
Oscillatoria
Cynodon
dactylon
Arundo
donax
FR
Ariz.
(O)
Pesticide usage in an orchard did not significantly
contaminate the aquatic environment of this creek
adjacent to the treatment as determined by residue
analysis.
The study showed that the levels of chlorinated
hydrocarbon pesticide residues in fish meals and oils
were, with the exception of the oil sample taken from
the Lake Michigan alewife, below the regulatory
tolerances established by the Food and Drug Director-
ate of Canada (1965) for certain foods intended for
human consumption. Pesticide levels were interpreted
as being representative for each species.
Fish were conditioned for at least 60 days at 12-16 C
in flowing water in the laboratory. The largest group,
20 parr with an average weight of 2.5 g, was killed in
9 hr by an aqueous suspension of 2.0 ppm p,p-DDT;
9 parr of the same size-group died in about 75 hr while
in a 0.1 ppm suspension; 7 smaller parr (1.4 g) kept
in a 0.01 ppm suspension, died in about 23 hours
When sexually maturing yearling brook trout were fed for
156 days with DDT at sublethal rates, fish fed at the lower
dosages produced more mature ova than untreated fish.
Those fed at highest dosages produced fewer mature ova
than untreated fish. The size of the male fish at the end
of the feeding period tended to increase according to the
dosage of DDT.
Irrigation canals were examined for plants which might
serve as DDT collectors or indicators of DDT usage by
concentrating this material and its metabolites. Highest
residues were found in Cladophora (19 ppm), followed
by Potamogeton (9 ppm), and finally Oscillatoria (5 ppm).
Moubry, et al
(1968)
Dugal
(1968)
Greer and
Paim
(1968)
Macek
(1968)
m
z
a
x
00
Ware, et al
(1968)
o
m
2
O
•o
3)
O
o
-------
o
o
2
m
o Chemical
r p,p'-DDT
O
I
m
S
o
r~
•o
3J
0
° p,p'-DDT
q
CO
DDT
i
§
DDT
DDT
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Organism Study'1) Location'2) ppm'3) or Noted'4)
Potamogeton FR Ariz. (O) —
pectinatus
Cladophora (
Oscillatoria
Cynodon
dactylon
Arundo
donax
Alosa BSA - (O)
pseudoharengus
Aplodinotus
grunniens
Coregonus
artedii
Lota
lota
Pteronarcys BSA - 0.0070 (T4A) a c d e f
californica
(naiads)
Pteronarcella 0.0019 (T4A)
bad/a
(naiads)
Claasenia 0.0035 (T4A)
sabulosa
(naiads)
Skeletonema L & CH - (O) a
costatum
Cocco/ithus
hyxleyi
Pyramimonas sp
Peridinium
trochoideum
Salvelinus BCH — 0 to 0.60 (SB) ae
fan Una/is
Comments
Irrigation canals were examined for plants which might serve
as DDT collectors or indicators of DDT usage by concen-
trating this material and its metabolites. Highest residues
were found in Cladophora (19 ppm), followed by
Potamogeton (9 ppm), and finally Oscillatoria (5 ppm).
The study showed that the levels of chlorinated hydrocarbon
pesticide residues in fish meals and oils were, with the excep-
tion of the oil sample taken from the Lake Michigan alewife,
below the regulatory tolerances established by the Food and
Drug Directorate of Canada (1965) for certain foods intended
for human consumption. Pesticide levels were interpreted as
being representative for each species.
Data reported as LCso at 15.5 C in 4 days.
Algal photosynthesis was reduced, as measured by
14CC>2 uPtake, It was decreased at concentrations of
a few ppb of DDT.
All experiments were conducted in 6 liters of water. When
brook trout are exposed for 24 hr to sublethal doses of
Reference
(Year)
Ware, et al
(1968)
Dugal
(1968)
Sanders and
Cope
(1968)
Wurster
(1968)
Anderson and
Peterson
DDT, the cold-blocking temperature for a simple reflex,
which shows lability related to thermal history, is altered
in a way suggesting that DDT is affecting the thermal
acclimation mechanism. Sublethal dosage of DDT also
prevents the establishment of a visual conditioned
avoidance response.
(1969)
-------
DDVP
Micropterus
sa/moides
Pimephales
promelas
BSA
0.5 (O)
0.5 (O)
DDVP
DDVP,
Tech.
DDVP
DDVP
T5
00
DDVP
8
m
3J
Q
i-
o
•o
3)
O
O
C/J
Salmo
gairdnerii
(one wk old
sac fry)
(one mo old
feeding fry)
Bluegill
Pteronarcys sp
(nymphs)
Simocephalus
serrulatus
Daphnia
pulex
Trichogaster
fasclatus
Chama
punctatus
Mastocembelus
pancalus
Macrognathus
aculeatum
Nandus
nandus
Rita rita
Amphipnous
cuchia
Mystus
vittaws
Puntius
sophore
Esomus
danrica
Labeo
rohita
Sphaerodema
annulatum
Nepa sp
Ranatra
filiformis
Dytiscus sp
Hydrophilus sp
Anisoptera
BSA
BSA
BSA
BSA
BSA
BSA
1.0 (K0%)
10 (K 100%)
1.0 (K0%)
10 (K 100%)
0.480 (T4A)
0.0001 (T4A)
0.00026 (SB)
0.000066 (SB)
3(K7)
3(K7)
5(K7)
5(K7)
5(K7)
5(K7)
5(K7)
10 (K7)
10 (K7)
30 (K7)
30 (K7)
0.1 (K7)
0.5 (K7)
0.2 (K7)
0.1 (K7)
0.5 (K7)
0.2 (K7)
The degree of reaction to the cholinesterase-inhibiting
insecticides is not only a function of time and concentra-
tion, but also of chemical and biological species. This
paper reports many analyses of brain cholinesterase
activity which is expressed as percentage of normal. The
data are reported as LT5g which was the time required
for 0.5 ppm of the chemical to kill 50 percent of the
fish. For bass the LTso was 48 hr and for the fathead
72 hr.
Results are averages of triplicate tests. Toxicity is reported
as percent mortality (K %).
The values reported are given as
Experiments were all conducted at 60 F in 1964. The
values were listed as LCgg.
Concentration reported is for immobilization.
Time for immobilization was 48 hr.
Data cited are for 60 F, but assays were performed at
varied temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
All the organisms listed are detrimental to culture of carp.
At the concentrations listed, there was 100 percent kill
of the organisms in 7 days.
Weiss
(1961)
Le wall en and
Wilder
(1962)
Cope
(1965)
Cope
(1965)
Sanders and
Cope
(1966)
Srivastava and
Konar
(1966)
m
Z
O
X
CO
-------
COMMERCIA
r-
o
I
m
2
O
r-
"D
3D
0
O
c
o
C/l
GO
V
oo
K)
Chemical
DDVP
Dead X
(95 percent
naphtha)
Dead-X
(EC)
Dead-X
Dead-X
(95 percent
naphtha)
Deet
DEF
DEF
Bioassay
or Field
Organism Study (1)
Cyprinus BSA
carpio
C.
carpio
Tilapia
mossambica
Cirrhina
mrigala
Labeo
fimbriatus
Frog tadpoles
Pteronarcys sp BSA
(nymphs)
Rainbow trout BSA
Bluegill
Simocephalus BSA
serrulatus
Daphnia
pulex
Pteronarcys BSA
californica
(naiads)
Prosimulum spp LCFA
Chephia spp
Simu/ium ispp
(larvae)
Leiostomus BSA
xanthurus
(juvenile)
Penaeus L
aztecus
Toxicity, Experimental
Active Variables
Field Ingredient, Controlled
Location(2) ppmJ3) or Noted(4)
15.0 (T2A) acdefp
5.5 (T2A)
3.0 (T2A)
25.0-30.0 (T2A)
18.0 (T2A)
10.0IT2A)
2.0 (T4A) £
8.8 (T4A) a
9.2 (T4A)
7.60 (SB) -
3.70 (SB)
0.0023 (T4A) Af-^l
4.0 (O) a
0.24 (0) a
0.028 (0) a
Comments
The test animals were conditioned for 48 hours prior
to use.
Experiments were all conducted at 60 F in 1964. The
values were listed as LC5Q.
This is an estimated LCsg value at temperatures from
55 to 75 F
Concentration reported is for immobilization.
Time for immobilization was 64 hr.
Data cited are for 78 F, but assays were performed at
varied temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
Data reported as LCso at 15.5 C in 4 days.
Stones heavily populated with wild larvae were placed in
troughs of running water containing the toxicant. When
the larvae became detached from the rocks and floated
away, they were assumed to have undergone lethal intoxi-
cation. The larvae were exposed to the toxicant for 5
minutes, then in clean water for 24 hours. At that time.
the number detached amounted to 0.0 percent.
Water temperature 27 C. The figure reported is a 48-hr
^SO-
Toxicant chemicals were evaluated in seawater at tempera-
tures averaging about 28 C. The values are for 24-hr ECsg
or enough to cause loss of equilibrium or mortality.
Reference
(Year)
Sreenivasan and
Swaminathan
(1967)
Cope
(1965)
Cope
(1965)
Sanders and
Cope
(1968)
Sanders and
Cope
(1968)
Jamnback and
Frempong-
Boadu
(1966)
Butler
(1965)
Butler
(1965)
f>
Tj
m
Z
X
CD
-------
DEF
DEF
DEF
(tech)
Delnav
Delnav
oo
OJ
Delnav
(emulsible
concentrate,
47 percent)
8
jf; Delnav
=0 (tech,
100 percent)
O
m
TJ
•3)
O
O
Delnav
Crassostrea
virginica
Penaeus
aztecus
Penaeus
duo/arum
Penaeus
setiferus
Leiostomus
xanthurus
Phytoplankton
Oyster
Pteronarcys
californica
Gambusia
affinis
Pimephales
promelas
BCFA & BSA -
Pimephales
promelas
Lepomis
macrochirus
Lebistes
reticulatus
Largemouth
bass
Green
sunfish
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Chaoborus
astictopus
BCF
BSA
BSA
BSA
BSA
BSA
BSA
0.1 (O)
0.03 (O)
0.24 (T2CFA)
75% (O)
0.1 (SB4)
0.0021 (T4A)
0.05 (K 3%)
0.5 (O)
12.0 (T4A)
0.063 (T4A)
0.57 (T4A)
0.076 (T4A)
0.13 (T4A)
10.0 (T4A)
0.034 (T4A)
32.0 (T4A)
0.21 (T4A)
0.052 (T1 A)
ac de f
a c d e
ac d e
Seawater was pumped continuously into test aquaria.
Salinity, temperature, and plankton fluctuated with tide,
and ambient weather conditions. Some bioassays with
fish were static. Toxicity was reported for the following:
Oyster — 96-hr ECgfj — Cone, which decreased
shell growth.
Shrimp — 48-hr EC5Q — Cone, which killed or
paralyzed 50% of test animals.
Fish - 48-hr EC5o - Cone, which killed 50%.
Phytoplankton — Percent decrease of CO2 fixation to a
4-hr exposure at 1.0 ppm chemical
concentration.
Seawater was employed in this experiment.
Data reported as
1 5.5 C in 4 days.
Chemicals were dissolved in acetone, and tests were run in
triplicate. Toxicity is given as average percent fish killed
in 24 hr.
The degree of reaction to the cholinesterase-inhibiting
insecticides is not only a function of time and concentra-
tion but also of chemical and biological species. This
paper reports many analyses of brain cholinesterase
activity which is expressed as percentage of normal.
The data are reported as LT^rj which was the time required
for 0.5 ppm of the chemical to kill 50 percent of the fish.
The LTso for the fathead was 72 hours.
Soft water primarily was the test medium. TLm's reported
for 24, 48, and 96 hr. Acetone or alcohol used as solvent
or carrier in most cases.
Comment same as above.
Toxicity value given is for the fourth instar larvae.
Butler
(1966)
Butler
(1965)
Sanders and
Cope
(1968)
Lewallen
(1959)
Weiss
(1961)
m
O
X
00
Pickering, et al
(1962)
Pickering, et al
(1962)
Hazeltine
(1963)
-------
o
o
2
S
m
o Chemical
j> ~ •
r Delnav
^
I
m
s
O Delnav
^
r~
TJ
3)
o
o
c
q
M
Delrad
Organism
Bluegill
Carassius
auratus
Lepomis
fwacrochirus
Pithophora spp
Lepomis
macrochirus
Micropterus
salmoides
Bioassay
or Field
Study 0)
BSA
BSCH
FL
Toxicity, Experimental
Active Variables
Field Ingredient, Controlled
Location^) ppm'3) Or Noted(^)
0.034 (T4A) a
1.0(O)* ^cde^
1.0 (O)**
* no response,
1 5 days
"response,
15 days
Ponds, (0) -
Ala.
Comments
Assays were conducted in soft water at 25 C. Decrease in
brain cholinesterase was measured in fish exposed to the
toxicant.
Toxicity was determined by measuring acetylcholinesterase
activity in the brains of fish. Concentrations are given in
ppb as either response or no response in 15 or 30 days.
0.25 to 0.3 ppm of the chemical killed large amounts of
Pithophora in ponds, but the effects were of short duration
(1 to 3 weeks). As many as 4 applications of Delrad at a
concentration of 0.3 ppm did not affect reproduction or
production of bluegill in experimental ponds. As many
Reference
(Year)
Weiss
(1964)
Weiss and
Gakstatter
(1964)
Lawrence
(1958)
00
Delrad 70
Delrad 70
Channel
catfish
(fingerlings)
Salvelinus
fontinalis
Salmo
trutta
Notemigonus
crysoleucas
BSA
FPCH
N.Y.
0.74
(K 25 hr A)
0.50 (S23)
a c d
as 3 applications of Delrad at the concentration of 0.3
ppm in bass brood ponds did not affect spawning of bass,
hatching of eggs, or survival of fry and small fingerlings.
The author states that "the minimal lethal dose" of this
chemical for bluegill and large-mouth bass fingerlings is
approximately 0.65 ppm. Microcrustaceans suffered
approximately a 50-percent mortality when the concentra-
tion of the chemical reached 0.5 ppm. The addition of
equal parts of Roccal (10%) to Delrad 50-S produced no better
kill of Pithophora in ponds, and the effects were usually of
longer duration (2 to 4 weeks).
Tap water was used. Considerable additional data are
presented.
Conventional farm ponds were used having an average sur-
face area of 0.3 acre and a maximum depth of 7-9 ft.
Toxicity (in ppm) to fish as maximum safe concentra-
tion (S) for 23 days was determined. Concentration of 0.5
ppm was required to control algae.
Clemens and
Sneed
(1959)
Eipper
(1959)
1
m
z
o
X
00
-------
Delrad
505
Demeton
Demeton
W
oo
Dermol
8
2 Derris
m
30
o
o
m
3J
O
O
Salvelinus FPCH
fontinalis
Salmo
gairdneri
Catostomus
commersoni
Notemigonus
crysoleucas
Ictalurus
punctatus
Micropterus
salmoides
Lepomis
macrochirus
Lepomis BSA
macrochirus
Micropterus
salmoides
Notemigonus
crysoleucas
Carassius
auratus
Carassius BSCH
auratus
Lepomis
macrochirus
Notemigonus
crysoleucas
Pandalus BSA
montagni
Crangon
crangon
Carcinus
maenas
Cardium edule
edule
Lepomis BSA
macrochirus
Lepomis
gibbosus
Catostomus
commersonii
Notemigonus
crysoleucas
Notropis cornutus
frontal is
Eucalia
inconstans
Umbra limi
Carassius
auratus
N.Y.
1.0 (S23)
1.0(323)
0.5 (S23)
0.25-1.0(523)
1.0 (S23)
1.0(323)
0.5 (S23)
0.1 (O)
0.1 (O)
0.1 (O)
0.1 (O)
1.0 (O)*
1.0(0)*
1.0(0)*
* no response,
15 days
148 (T2A)
156 (T2A)
435 (T2A)
148 (T2A)
1.0 (K)
0.5 (K)
1.0 (K)
0.5 (K)
0.5 (K)
0.5 (K)
0.5 (K)
0.5 (K)
0.5 (K)
0.5 (K)
ac d
Comment same as above.
Eipper
(1959)
acdf
a c d e
ad
This paper reports the effect of insecticides in reducing the
anticholinesterase in a fish brain within 2-8 hours. The
inhibition of the enzyme was a function of the concentra-
tion of the insecticide, extent of exposure, and specific
chemical nature of the compound.
Toxicity was determined by measuring acetycholinesterase
activity in the brains of fish. Concentrations are given in
ppbas either response or not response in 15 or 30 days.
Experiments were conducted in tanks holding 10 liters of
sea water at 15 C.
It was shown that the toxicity of this solvent emulsifier
decreased with time, due to evaporation of the solvent.
The action of Derris root appeared to be somewhat faster
in acid than alkaline waters. The derris employed in this
experiment contained 5 percent rotenone.
Weiss
(1959)
Weiss and
Gakstatter
(1964)
m
O
X
00
Portmann and
Connor
(1968)
Leonard
(1938)
-------
0
o
s
s
m
o Chemical
*" Dems root
2 (5% rotenone
m content)
S
r~
-D
O
D
C
O
en
D
0
r\
Derris
Detergents
Dexon
Dexon
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Organism Study'1) Location (2) ppm(3) or Noted'4)
Ambloplites FL Mich. 0.35-0.56(0) a
rupestris
Huro
sal m aides
Perca
flavescens
Sal mo
gairdneri
Salvelinus
f on final is
Sal mo
trutta
Catostomus c.
commersonii
Lepomis
gibbosus
Semotilus
astromaculatus
Cristivomer
namaycush
Umbra limi
Hyborhynchus
notatus
Eucalia
inconstans
Poecilichthys
exi/is
Fundulus
diaphanus
menona
Notemigonus
crysoleucas
auratus
Entosphenus
lamottenii
Tendipedidae FL Colo. 1.0(3) acde
Pimephales BSA - (5)61-63 acdf
promelas (T1-4A)
(juveniles) (H) 39-44
(T1-4A)
Oyster BCF - (O) a
Pteronarcys BSA — 0.024 (T4A) acdef
californica
(naiads)
Comments
The results of this experiment indicate that in certain trout
waters which are overrun with warm water fish, trout and
other cold water fish can withstand an application of derris
root at the concentration given, while other fish (warm
water fish) can be eliminated.
Derris is much less effective in colder water.
It is likely that a thermocline prevents the penetration of
the poison to deeper water.
No trout were killed in these experiments. All other fish
listed showed some mortality.
This is a study of lake bottom fauna. Oligochaeta were not
affected. Collection data of bottom fauna are given.
Syndets and soaps were of nearly equal toxicity in soft
water (S) but syndets were approximately 40X more toxic
than soap in hard water (H).
No effect on exposure to the chemical at 1.0 ppm.
Data reported as LC5Q at 15.5 C in 4 days.
Reference
(Year)
Greenbank
(1940)
Cushing and
Olive
(1957)
Henderson, et al
(1959)
Butler
(1965)
Sanders and
Cope
(1966)
TJ
•o
m
Z
D
X
00
-------
W
Dexon
Dexon
DFDT
(DDT
analogue)
Diazinon
Diazinon
Diazinon
Diazinon
(EC2)
Diazinon
8
m
3)
O
^ Diazinon
m
S
ft Diazinon,
Tech.
TJ
a
O
o
Penaeus
aztecus
Cyprinodon
variegatus
(juvenile)
Goldfish
Gambusia
affiriis
Culex
apicalis
(larvae)
Daphnia
magna
Lepomis
macrochirus
Micropterus
salmoides
Notemigonus
crysoleucas
Carrasius
auratus
Micropterus
salmoides
Pimephales
promelas
Gambusia
affinis
Carassius
auratus
Lepomis
macrochirus
Notemigonus
crysoleucus
Pteronarcys sp
(nymphs)
Rainbow
trout
Bluegill
BSA
BSA
BSA
BSA
BSA
FL
BSCH
Ponds in
BSA
BSA
(O)
(O)
0.9 (K)
0.175 (K)
0.0015 (K)
0.0043 (O)
0.1 (O)
0.1 (O)
0.1 (O)
0.1 (O)
0.5 (0)
0.5 (O)
(O)
1.0 (0)*
1.0(0)*
1.0(0)*
*no response,
15 days
0.025 (T4A)
0.090 (T4A)
0.022 (T4A)
Toxicant chemicals were evaluated in sea water at
temperatures averaging about 28 C. The values are for
24-hr ECso or enough to cause loss of equilibrium or
mortality. No effect occurred at 1.0 ppm.
Water temperature was 21 C. No effect was noticed
on exposure to 1.0 ppm.
Experiments were run a maximum of 3 days. No other
time data were reported.
£ The indicated concentration immobilized Daphnia in
50 hours.
.i£.?LL This paper reports the effects of insecticides in reducing
the anticholinesterase in a fish brain within 2-8 hours.
The inhibition of the enzyme was a function of the
concentration of the insecticide, extent of exposure,
and specific chemical nature of the compound.
— The degree of reaction to the cholinesterase-inhibiting
insecticides is not only a function of time and concentra-
tion, but also of chemical and biological species. This
paper reports many analyses of brain cholinesterase
activity which is expressed as percentage of normal. The
data are reported as LTsrj which was the time required
for 0.5 ppm of the chemical to kill 50 percent of the
fish. For bass the LT^rj was 1 hr and for the fathead
80 min.
— When applied at 0.3 pound per acre active ingredient,
100 percent mortality occurred in 1 day.
d e_ Toxicity was determined by measuring acetylcholinesterase
activity in the brains of fish. Concentrations are given in
ppb as either response or not response in 15 or 30 days.
Experiments were all conducted at 60 F in 1964. The
values were listed as
The values reported are given as
Butler
(1965)
Butler
(1965)
Odum and
Summerford
(1946)
Anderson
(1960)
Weiss
(1959)
Weiss
(1961)
m
Z
O
X
00
Mulla.et al
(1963)
Weiss
(1964)
Cope
(1965)
Cope
(1965)
-------
n
o
s
m
o Chemical
•"" Diazinon
n
m
S
O
r~
•n
0
O
f—
O
— 1
w Diazinon
Diazjnon
0
o
o
Diazjnon
Diazinon
Dibrom
Dibrom
Bioassay
or Field
Organism Study^'
Sal mo BSA
gairdnerii
Lepomis
macrochirus
Pteronarcys
californicus
Daphnia
pulex
Simocephalus
serrulatus
Prosimulum spp LCFA
Cnephia spp
Simulium spp
(larvae)
Simocephalus BSA
serrula tus
Daphnia
pulex
Daphnia
carinata
Leiostromus BCFH
xanthurus
Cyprinodon
variegatus
Pteronarcys BSA
ca/ifornica
(naiads)
Gambusia BSA
affinis
Salmo BSA
gairdnerii
(one wk. old
(one mo. old
feeding fry)
Toxicity, Experimental
Active Variables
Field Ingredient, Controlled
Location^) ppm'3' or Noted'4'
0.170IT2A) a
0.030 (T2A)
0.074 (T2A)
0.0009 (T2A)
0.002 (T2A)
0.4 (O) a
- 0.0018 (SB) -
0.00090 (SB)
0.0008 (SB)
- 0.001 (O) a
0.001 (0)
0.025 (T4A) l£d^_f_
0.03 (K 3%) a
- 1. OIK 23%) ae
10.0 (K 100%)
1.0 (K 0%)
10.0 (K 100%)
Comments
This paper reports acute toxicity of a number of
compounds, and discusses sub-acute mortality as well.
Effects on reproduction and behavior are also dis-
cussed. Data presented as ECsg-
Stones heavily populated with wild larvae were placed in
troughs of running water containing the toxicant. When
the larvae became detached from the rocks and floated
away, they were assumed to have undergone lethal
intoxication. The larvae were exposed to the toxicant
for 5 minutes, then in clean water for 24 hours. At that
time the number detached amounted to 13 percent.
Concentration reported is for immobilization.
Time for immobilization was 48 hr.
Data cited are for 60 F, but assays were performed at
varied temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
Concentration reported is for immobilization.
Time for immobilization was 64 hr.
Data cited are for 78 F, but assays were performed a
varied temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
At a concentration of .001 ppm, the following percent
acetylcholinesterase activity as compared to controls
was found:
L. xanthurus — 100
C. variegatus — 74
Data reported as LCgrj at 15.5 C in 4 days.
Chemicals were dissolved in acetone, and tests were run
in triplicate. Toxicity is given as average percent fish
killed in 24 hr.
Results are averages of triplicate tests. Toxicity is reported
as percent mortality (K %).
Reference
(Year)
Cope
(1966)
Jamnback and
Frempong-
Boadu
(1966)
Sanders and
Cope
(1966)
Butler and
Johnson
(1967)
Sanders and
Cope
(1968)
Lewallen
(1959)
Lewallen and
Wilder
(1962)
^
•o
m
z
D
X
CD
-------
oo
Dibrom
Dibrom
(tech)
Dibrom
(tech)
Dibrom
(tech)
Dibrom
Dibrom
Dibrom
Dicamba
(Banvel D)
Dicamba
(Banvel D)
Dicapthon
O Dichlobenil
in
3D
O
Sa/mo
gairdneri
Salmo
gairdneri
Procambarus
clarki
Bluegill
Oyster
Simocephalus
serrulatos
Daphnia
pulex
Leiostromus
xanthurus
Cyprinodon
variegatus
Mugil
cephalus
Oncorhynchus
kisutch
Salmo
gairdneri
Rainbow
trout
Bluegill
Chaoborus
astictopus
Lepomis
macrochirus
BSA
BSA
BSA
BSA
BCF
BSA
BCFCH
BSA
BSA
BSA
BSA
SO (T 18 hr)
70 (T1A)
4.0 (T3A)
0.180 (T4A)
0.1 (SB4)
1.0 (SB4)
0.0011 (SB)
0.00035 (SB)
0.05 (O)
0.05 (O)
0.001 (O)
151 (T1A)
120 (T2A)
320 (O)
35.0 (T2A)
130.0IT2A)
0.0057 (T1A)
17.0 (T2A) L
30.0 (T2A) G
The experiment was conducted at 55 F. Fish were
2-3 in. long.
Comment same as above.
a c d o There was no detectable difference in toxicity to male
or female crawfish.
The values reported are given as
a Sea water was employed in this experiment.
— Concentration reported is for immobilization.
Time for immobilization was 48 hr.
Data cited are for 60 F, but assays were performed
at varied temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
a At a concentration of 0.05 or 0.001 ppm, the following
percent acetylcholinesterase activity as compared to
controls was found:
L. xanthurus — 10
C. variegatus — 79
M. cephalus — 76
a c d The active ingredient of Dicamba is 2-methoxy-3, 6-
dichlorobenzoic acid (dimethylamine salt).
Tests were conducted in glass jars holding 15 liters of
water.
Concentrations of 320 ppm produced no mortalities
in rainbow trout.
— Data are given as LC5Q.
a Toxicity value given is for the first instar larvae.
£ c d e f Toxicitv data for 24 and 48 hours are presented for
liquid (L) and granular (G) formulations. Various
commercial formulations were tested. The liquid
formulations were almost invariably more toxic than
the granular ones.
Cope
(1963)
Cope
(1963)
Muncy and
Oliver
(1963)
Cope
(1965)
Butler
(1966)
Sanders and
Cope
(1966)
Butler and
Johnson
(1967)
Bond, et al
(1965)
Bohmont
(1967)
Hazeltine
(1963)
Hughes and
Davis
(1965)
m
O
X
09
O
m
2
O
-o
3D
O
o
c
CO
-------
o
o
S
S
m
o Chemical
n Dichlobenil
I
m
o
r~
-Q
33
O
C
o
Dichlobenil
(Casoran)
Dichlobenil
3
:>
3
Dichlobenil
Dichlone
(Phygon)
Dichlorvos
Dichlorvos
Organism
Sal mo
gairdnerii
Lepomis
macrochirus
Pteronarcys
californicus
Daphnia
pulex
Simocephalus
serrulatus
Daphnia
magna
Rainbow
trout
Bluegill
Lepomis
macrochirus
(eggs)
L. cyanellus
(eggs)
Microp terus
dolomieui
(eggs)
Erimyzon
sucetta
(eggs)
L. macrochirus
(fry)
Pteronarcys
californica
Daphnia
magna
Bluegill
Prosimulum spp
Cnephia spp
Simu/ium spp
(larvae)
Pteronarcys
californica
(naiads)
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
StudyCO Location^) ppm<3> or Noted<4>
BSA - 22.0 (T2A) a
20.0 (T2A)
8.4 (T2A)
3.7 (T2A)
5.8 (T2A)
BSA - 9.8 (8.8-10.7) (O) acdiq
22 (O)
20 (0)
L - 20 (S), 10 (NTE)
25 (NTE)
25 (NTE)
25 (NTE)
20 (S)
BSA - 0.007 (T4A) a c d e f_
BSA - 0.014(0) acdiq
0.04 (O)
LCFA - 0.4 (O) a
BSA - 0.001 (T4A) !£.!!_!
Comments
This paper reports acute toxicity of a number of com-
pounds, and discusses sub-acute mortality as well.
Effects on reproduction and behavior are also discussed.
Data presented as ECgrj'
Toxicity, in terms of median immobilization concentration
OCsfj), is presented for Daphnia; median lethal concentra-
tion (LCsfj) values for rainbow trout and bluegill are
reported.
Fertilized fish eggs of indicated species were placed in 1 liter
of test solution and allowed to hatch. Toxicity data are
presented as concentration in ppm/number of days sur-
vival. Maximum length of test was 8 days. No food was
was added. Small bluegill were tested to find the highest
concentration of chemical which did not cause death in
12 days (S).
Data reported as LC5Q at 15.5 C in 4 days.
Toxicity, in terms of median immobilization concentration
OC501), is presented for Daphnia; medium lethal concen-
tration (LC5Q) va'ues for bluegill are reported.
Stones heavily populated with wild larvae were placed in
troughs of running water containing the toxicant. When
the larvae became detached from the rocks and floated
away, they were assumed to have undergone lethal
intoxication. The larvae were exposed to the toxicant
for 5 minutes, then in clean water for 24 hours. At
that time the number detached amounted to 41 percent.
Data reported as LC$Q at 15.5 C in 4 days.
Reference
(Year)
Cope
(1966)
Crosby and
Tucker
(1966)
Hiltibran
(1967)
Sanders and
Cope
(1968)
Crosby and
Tucker
(1966)
Jamnback and
Frempong-
Boadu
(1966)
Sanders and
Cope
(1966)
^
•o
•o
m
O
X
00
-------
T3
VO
1— *
8
2
m
3)
o
r
o
m
£
9
•o
•3)
O
o
c
Diethanol
rosinamine
D acetate
DIDT
(DDT
analogue)
Dieldrin
Dieldrin (hexa-
chloroepoxy-
octahydrodi-
methanonaptha-
lene, 25 percent)
Dieldrin
(granules)
Dieldrin
Dieldrin
Dieldrin
Cylindrospermum
lichen/forme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Ch/orella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Npi
Goldfish
Gambusia
affinis
Culex
apical is
(larvae)
Carassius
auratus
Lepomis
macrochirus
Lymnaeid
snails
Simulium sp
(larvae)
Artemia
salina
Fish
Crustacea
fiddler crabs.
etc.
Mollusks
snails
oysters,
etc.
Fathead
minnow
Bluegill
Goldfish
Guppy
2.0 (O)
BSA
BSA
BSA
FR
BSA
FO (salt
marsh)
Streams,
S. C.
Fla.
0.175 (K)
0.025 (K)
0.003 (K)
4.0 (K) 2hr
(O)
0.04 (0)
1.172(1- 1)
(O)
BSA
0.016 (T4A)
0.0079 (T4A)
0.037 (T4A)
0.022 (T4A)
Observations were made on the 3rd, 7th, 14th, and Palmer and
21st days to give the following (T = toxic, NT = nontoxic, Maloney
PT = partially toxic with number of days in parentheses. (1955)
No number indicates observation is for entire test period
of 21 days):
Cl - T
Ma- T
So- T(3), PT(21)
Cv - T (7), PT
Gp- T
Np- T
Experiments were run a maximum of 3 days. No other Odum and
time data were reported. Sumerford
(1946)
The toxicity threshold for the 2 species was 0.031 ppm. Gray
Water taken from rice field that had been treated with (1950)
0.1 pound of Dieldrin per acre, 10 to 20 days previously,
killed fish unless diluted 1/2 with pond water.
Each test container, 500-ml beaker, was filled with ditch Batte, et al
water. 100% mortality occurred in concentrations of (1951)
1:400,000 and greater.
Dieldrin at a 0.04 Ib/acre rate of application controlled Davis, et al
blackfly larvae for up to 4 weeks. Data are presented as (1957)
percent larval detachment for this period of time.
Rock salt was used in rearing all cultures employed in Tarpley
bioassay work. The optimum salt concentration was 3.5%. (1958)
Two thousand acres of marsh were treated for sandfly Harrington and
control at rate of 1 Ib/acre. Fish reacted to the chemical Bidlingmayer
within a few minutes after treatment (list of fish names (1958)
given). An estimated 20-30 tons of fish of about 30
species died. Crustaceans, mollusks seemed to be un-
harmed. Fish repopulation began after the 4th week
and was climactic at the 10th week.
It was the authors opinion that pH, alkalinity and hardness, Tarzwell
within the usual range in natural waters, had little effect on (1959)
the toxic effect of the compounds studied. The values given
are from Henderson, Pickering, and Tarzwell, "The Relative
Toxicity of Ten Chlorinated Hydrocarbon Insecticides to Four
Species of Fish". It is interesting that the different tables
from the above book (as reported in this paper) report widely
different values for the same compounds.
This experiment was performed in soft water.
-------
to
o
o
2
o Chemical
"~ Dieldrin
O
I
m
2
o
r-
TJ
O
D
C
H Dieldrin
01 (dust)
Dieldrin
(granules)
Dieldrin 50
Dieldrin
3
>
>
Dieldrin
Dieldrin
Organism
Fathead
minnow
Tilapia
melanopleura
Tilapia
melanopleura
Channel
catfish
(fingerlings)
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Pimephales
promelas
Lepomis
macrochirus
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study' •' Location*?) ppm(3) or Noted^)
BSA - 0.01 6 (T4A) a
FLCH Tangan- 1 Ib (3.3% K)
yika 5lb(6.6%K-
3 wks)
10lb (66.6% K-
3 wks)
1 Ib (0% K)
BSA - 2.5 a
(K 25 hr A)
BSA - 0.01 (T4A) £def
0.01 (T4A)
0.04 (T4A)
0.02 (T4A)
BSA - 0.018 (T4A) ^becd_f
0.0088 (T4A)
0.041 (T4A)
0.025 (T4A)
BSA - 0.01 6 (T4A) a
0.0079 (T4A)
Comments
It was the authors opinion that pH, alkalinity and hardness,
within the usual range in natural waters, had little effect on
on the toxic effect of the compounds studied. The values
given are from Henderson, Pickering, and Tarzwell, "The
Relative Toxicity of Ten Chlorinated Hydrocarbon Insecti-
cides to Four Species of Fish" It is interesting that the dif-
ferent tables from the book (as reported in this paper)
report widely different values for the same compounds.
This experiment was performed in soft water.
Trial periods were for 20 weeks. Sublethal effects such as
impaired breeding, retarded growth, or altered taste were
not detected. Dosages are given as Ib/acre of surface water.
Comment same as above.
Tap water was used. Considerable additional data are
presented.
Concentrations were based on percent active ingredient.
Dilution water was usually soft although some studies were
conducted with hard water.
Bioassay investigations of the new insecticides indicate that
in general the organic phosphorus compounds are not as
toxic to fish as are the chlorinated hydrocarbons. The
toxicity of most of these materials was not significantly
influenced by water quality. Therefore it is to be expected
that the toxicity of these materials will not differ signifi-
cantly in different streams.
Reference
(Year)
Tarzwell
(1959)
Webb and
Shute
(1959)
Webb and
Shute
(1959)
Clemens and
Sneed
(1959)
Henderson, et al
(1959)
Henderson, et al
(1959)
Tarzwell
(1959)
>
•o
m
Z
O
X
DO
-------
Dieldrin
Dieldrin
Dieldrin
Dieldrin
Dieldrin
Dieldrin
Dieldrin
(EC 1.5)
Dieldrin
8
m
3D
O
Q Dieldrin
>
r
T)
30
O
O
I
Pimephales
promelas
Lepomis
macrochirus
Daphnia
magna
Oncorhynchus
kisutch
Oncorhynchus
tshawytscha
Salmo
gairdnerii
Gasterosteus
aculeatus
Salmo
gairdneri
Gammarus
lacustris
lacustris
Ophicephalus
punctatus
Heteropneustes
fossilis
Barbus
stigma
Trichogaster
fasciatus
Gambusia
affinis
Rana
catesbeiana
(tadpoles)
Gambusia
affinis
affinis
Lepomis
gibbosus
BSA
BSA
BSA
Cincin-
nati,
O.
BSA
BSA
BSA
FL
Cal.
BSA
BSA & CH
O.1 to 5.O (T4A)
0.0056-0.042
(T4A)
0.33 (O)
10.8 (T4A)
6.1 (T4A)
9.9 IT4A)
15.3IT4A)
0.0355 (T1A)
0.0233 (T2A)
0.0233 (T4A)
(O)
a c d e f p
4000-8000
(K<4hr)
2000-8000
(KOhr)
4000 (K<3hr)
2000-4000
(K<4hr)
0.5 (O)
0.016 to .50
0.0067 (T4A)
a c d e
^c df g
a e p
a c d e
Toxicity of run-off water from areas treated with Dieldrin
was evaluated.
Three different Dieldrin formulations were used: powder,
emulsion, and acetone solution. The acetone formulation
was generally the most toxic.
The indicated concentration immobilized Daphnia in 50
hours.
Chemical dissolved in acetone. TLm expressed in ppb.
Hatchery artesian well water was employed for this
experiment.
The mortality might have been partially due to the sus-
ceptibility of the organism to higher temperatures,
toxicity from extended exposure to copper electrodes
(used to shock the organism to determine death), or the
increase of CO2- Results were expressed as LT5Q; for
example, at 0.5 ppm, 50 percent of the shrimp were
killed in 74 (±7) min.
The dosage to produce toxic symptoms varied with each
species. At the very low dosage, these insecticides did not
produce observable changes, but at the higher dosage
changes were pronounced.
Mixed populations of the indicated test species contained
in cages were exposed to various insecticidal chemicals
applied as dilute sprays to ponds 1/16 acre in size. The
indicated toxicant concentration is in Ib/acre, and re-
sulted in a 100 percent mortality for the tadpoles in
24 hr.
The lower value is for fish that had never beep exposed to
the toxicant, and the higher value was obtained with fish
that had been exposed to a sublethal dose in the past.
Apparently such an exposure produces a resistance that
can be retained when they are later placed in clean water.
Other medium tolerance limits were:
0.0155 ppm — 24 hours
0.012 ppm — 48 hours
0.0075 ppm — 72 hours.
Chronic exposure to 0.00168 ppm for the period of 12
weeks affected the oxygen consumption and the cruising
speed ability.
Tarzwell and
Henderson
(1960)
Anderson
(1960)
Katz
(1961)
Webb
(1961)
McDonald
(1962)
Mathur
(1963)
Mulla
(1963)
Boyd and
Ferguson
(1964)
Cairns and
Scheier
(1964)
m
O
X
00
-------
COMMERCE
s>
r~
n
i
m
S
o
r-
33
O
c
o
en
co
^
Chemical
Dielclnn
Dieldnn
(tech,
100 percent
active in
acetone)
Dieldrin
Dieldrin
Dieldrin
(tech)
Dieldrin
Dieldrin
Dieldrin
Organism
Notemigonus
cryso/eucas
Lepomis
macrochirus
L. cyanellus
Pteronarcys
californica
(naiad)
Acroneuria
pacific a
Gammarus
lacustris
Bluegill
Rainbow
trout
Bluegill
Bluegill
Palaemonetas
kadiakensis
Gambusia
affinis
Ictalurus
melas
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient. Controlled
Study*"" Location(2) ppm(3> or Noted'4'
BSA - (B) 0.025 (T 1.5) acf
(A) 0.90 (T 1.5)
(B) 0.025 (T 1.5)
(A) 0.900 (T 1.5)
(B) 0.033 (T 1.5)
(A) 1.25 (T 1.5)
BSA - 0.03900 (T4A) c d e f
0.02400 (T4A)
BSA - 0.70 (T4A) ae
BSA - 0.0079 (T4A) a
BSA - 0.01 3 (T4A)
0.0028 (T4A)
BSA - 16(T4A) a
18 (T4A)
14.5 (T4A)
9.3 (T4A)
7.1 (T4A)
BSA - (N) 50.0 a c f
(T1-1/2A)
(TB) 135.0
(T1-1/2A)
BSA - 0.001-0.025 acde
(T3A)
0.003-0.028
(T3A)
Comments
Chemical was dissolved in acetone. Final concentration of
acetone was <2 ml/I. Data shows TLm in ppb for insecticide-
resistant and insecticide non-resistant strains of the test fish.
A. pacifica was much more sensitive to chlorinated hydro-
carbons and to organic phosphate insecticides that/3.
californica.
Emulsible concentrates were prepared from technical grade
insecticides with acetone as the solvent.
Symptoms prior to death were observed and recorded on
graphs.
Assays were conducted in soft water at 25 C. Decrease in
brain cholinesterase was measured in fish exposed to the
toxicant.
The values reported are given as \-Cc,Q.
These experiments were performed to demonstrate that at
increased temperatures the toxic effect of most chemicals
is increased.
For the toxicant concentrations listed, the temperatures
were respectively, 45, 55, 65, 75, and 85 F Data on the
effect of time as well as temperature was also reported.
The experimental animals all were approximately one
grain in weight.
Test organisms were collected from 2 locations. Twin Bayou
(TB), Sunflower Co., Miss, (agricultural area) and Noxubee
National Wildlife Refuge (N), Noxubee Co., Miss, (non-
agricultural area) and evaluated in laboratory bioassays.
The Twin Bayou shrimp were more resistant.
Test fish were collected from 8 different locations of the
Mississippi River. The 3-day TLm values were made to
determine if a resistance gradient existed. The data
indicated that there was none.
Reference
(Year)
Ferguson, et al
(1964)
Jensen and
Gaufin
(1964)
Nebeker and
Gaufin
(1964)
Weiss
(1964)
Cope
(1965)
Cope
(1965)
Ferguson, et al
(1965)
Ferguson, et al
(1965)
^
•o
m
X
00
-------
Dieldrin
Dieldrin
Dieldrin
Dieldrin
Dieldrin
2 Dieldrin
m
3)
O
Dieldrin
o
X
m
2
O
Pteronarcys
catifornica
Acroneur/a
pacifica
Ephemerella
grandis
Daphnia
magna
Gammarus
lacustris
Acroneuria
pacifica
Ephemerella
grandis
Gammarus
lacustris
Pteronarchys
californica
Carassius
carassius
Poecilia
reticulata
Salmo
galrdneri
Lepomis
macrochirus
Ictalurus
punctatus
Pteronarcys
californicus
Baetis sp
Daphnia
pulex
Simocephalus
serrulatus
Salmo
gairdnerii
Acroneuria
pacifica
Pteronarcys
californica
BSA
BSA
BSCH
BSA
BSA
BCFA
BSA&CFCH
0.04 (T4A)
0.02 (T4A)
0.008 (T4A)
0.3(T50hr A)
0.7 (T4A)
0.024 (T4A)
0.008 (T4A)
0.7 (T4A)
0.039 (T4A)
0.1 (SB-2 hrs)
0.075 (SB-4 hrs)
0.021 (T4A)
0.005 (T2A)
0.006 (T2A)
0.025 (T2A)
0.001 (T2A)
0.064 (T2A)
0.250 (T2A)
0.250 (T2A)
0.016 (K1)
0.024 (T4A)
0.0002 (T30A)
0.039 (T4A)
0.002 (T30CH)
ac de
Unspecified chemical characteristics of assay water were
determined by standard methods. General comments
were made concerning "standardized" conditions, use of
"soft" water, and use of emulsifying agents. Additional
data are presented.
Gaufin, et al
(1965)
Additional TLm data are given.
Gaufin, et al
(1965)
Data given on chemical residue found in tissue computed
from C^4 activity was:
37.2 mg/g in blood
10.5 mg/g in muscle.
Light was controlled in this experiment. All tests were
conducted in soft, synthetic dilution water.
This paper reports acute toxicity of a number of compounds,
and discusses sub-acute ntoxicity as well. Effects on repro-
duction and behavior are also discussed. Data presented as
Weiss
(1965)
Cairns and
Loos
(1966)
Cope
(1966)
m
z
Q
X
00
The gills, muscles, and livers of the fish were examined for
concentrations of the chemical. The trout tended to
accumulate this compound in all tissues studied.
Additional data are presented.
Holden
(1966)
Jensen and
Gaufin
(1966)
TJ
3D
O
O
-------
o
o
s
m
o Chemical
j>
^ Dieldrm
O
I
m
>
r~
T>
3)
O
O
c
q
w
Dieldrm
3
5
N
Dieldrin
Dieldrin
(20% active)
Toxicity,
Bioassay Active
or Field Field Ingredient,
Organism Study'^ Location'^) ppm(3)
Platalea FO Netherlands (O)
leucorodia
Haema topus
ostralegus
Sterna
sandvicensis
Sterna
Hirundo
Larus
ridibundus
Somateria
mol/issima
Tadorna
tadorna
Buteo FO Netherlands (O)
buteo
Accipiter
gen til is
Accipiter
nisus
Fa/co
tinnunculus
Tyto
alba
Strix
a/uco
Osio
otus
Fa/co
pereginus
Daphnia BSA - 0.740 (SB)
magna
Daphnia 0.250 (SB)
carinata
Simocephalus 0.240 (SB)
serru/atus
Daphnia 0.250 (SB)
pu/ex
Tubifex spp BSA - 6-71 (T4A)
Limnodrilus spp
Experimental
Variables
Controlled
or Noted (4) Comments
— The results of this study show that birds of prey and fish-
eating birds found dead in the Netherlands accumulated
large amounts of different chlorinated hydrocarbon
insecticides. In most cases the liver had the highest
concentration of toxicant, ranging from a trace to 9.5
ppm of endrin. Birds feeding on predominantly Crustacea,
molluscs, and fish contained significant amounts.
— The results of this study show that birds of prey and fish-
eating birds found dead in the Netherlands accumulated
large amounts of different chlorinated hydrocarbon
insecticides. In most cases the liver had the highest
concentration of toxicant, ranging from 0.4 to 44.0 ppm.
Most chlorinated hydrocarbons tended to accumulate
in the fat depots of the body. In instances where mesenterial
fat was analyzed the concentration of toxicant was found to
be as high as 17.0 ppm.
— Concentration reported is for immobilization.
Time for immobilization was 64 hr.
Data cited are for 78 F, but assays were performed at
varied temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
ace Toxicity is reported as the mean lethal dose (LDsg) for
24, 48, and 96 hours.
Reference
(Year)
Koeman and
van Genderen
(1966)
Koeman and
van Genderen
(1966)
Sanders and
Cope
(1966)
Whitten and
Goodnight
(1966)
>
•o
"O
m
Z
O
x
00
-------
Oieldrin
BCFCH
Dieldrin
Dieldrin
Dieldrin
Dieldrin-C14
Dieldrin
8
s
jj Dieldrin
O
O
5
TJ
33
O
O
arenaria
Crassostrea
virginica
Corbicula
manillensis
Mercenaria
mercenaria
Rang/a
cuneata
Poecilia
reticulata
(O)
BCH
0.0018 (O)
0.0056 (O)
0.01 (O)
Oyster
Goldfish
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
FE
BSA & CH
BCFCH
Galveston (O)
Bay,
Texas
50 mjllg/ml (K)
(O)
BSA
(O)
Sa/mo spp
Lebistes
reticulatus
Rasbora
heteromorpha
BSA & CH
(O)
a c d e f i
Results are recorded as a range of uptake of the chemical
by 5 species of aquatic mollusks. An uptake or concentra-
tion of 700-1800X resulted.
Butler
(1967)
The three levels of toxicant reported are near "the estimated
biologically safe concentration" for acute exposure of gup-
pies to dieldrin. The period of exposure was fourteen
months, during which time, conditions of "food, water,
temperature, and photo period" were controlled. At the
higher concentration, there was suggestive evidence that
long-term exposure to Dieldrin had a deleterious effect
on the reproductive process.
Oysters from the area were found to contain ^O.O'l to
0.01 ppm.
Test fish were conditioned to alkyl benzene sulfonate
(4 jUg/ml, or sodium lauryl sulfate (4jUg/ml), for various
periods of time, then exposed to pesticides. Chronic
exposure to the detergent increased the toxicity of the
pesticide.
Fish were treated with carbon-labeled insecticides (0.03 ppm)
from 5 to 19 hr and uptake rates were determined. They
were placed in recovery tanks for up to 32 days. Whole
body samples were then made. It was found that of the
dieldrin absorbed, ]>90% was eliminated from the fish
after 2 weeks.
The median lethal concentration for a 2 hour exposure
to Dieldrin for guppies was approximately 0.05 ppm. The
median concentration for Harlequin fish (Rasbora hetero-
morpha) and trout (Sa/mo sp) was approximately 0.01
ppm. This short exposure to dieldrin for guppies up to
the median lethal concentration had no harmful effects
on the reproduction of surviving guppies.
The median lethal concentration for a 2 hour exposure to
Dieldrin for trout was approximately 0.01 ppm. Reproduc-
tive capacity of surviving trout could not be determined.
The median lethal concentration for a 2 hour exposure to
Dieldrin for guppies was approximately 0.05 ppm. Reproduc-
tive capacity of surviving guppies was apparently unaffected.
The median lethal concentration for a 2 hour exposure to
Dieldrin for Harlequin fish was approximately 0.01 ppm.
Reproductive capacity of the surviving fish could not be
determined.
Cairns, et al
(1967)
Casper
(1967)
Dugan
(1967)
Gakstatter and
Weiss
(1967)
Hubble and
Reiff
(1967)
Hubble and
Reiff
(1967)
-------
o
o
2
m
o Chemical
"~ Dieldrin
O
I
m
O
1—
33
§ Dieldrin
C
H
CO
Dieldrin
m Dieldrin
i^
**O
OO
Dieldrin
Toxicity,
Bioassay Active
or Field Field Ingredient,
Organism Study'D Location(2) ppm (3)
Esox FR River (O)
lucius Nene,
Eng.
Navicula BSA - 12.8IT5A)
seminulum
var. Hustedtii
Limnephilus Knights (O)
rhombicus Creek,
Sialis sp Wise.
Gammarus sp
Salvelinus
fontina/is
Semoti/us
atromarulatus
Cottus
bairdi
Alosa BSA - (O)
pseudoharengus
Aplodinotus
grunniens
Coregonus
artedii
Lota
lota
Poecilia BSA - (O)
reticulata
Experimental
Variables
Controlled
or Noted'4) Comments
— Higher concentrations were found in larger fish, indicating
that they had been exposed to the pesticides for a longer
time. Tissue extracts from the pike were analyzed for
organochlorine pesticide residues by gas liquid chroma-
tography. The values for large pike were:
0.24 ppm muscle
28.0 ppm fat
a This diatom species survived concentrations of Dieldrin
considerably greater than those reported for fish and
aquatic invertebrates. Fish feeding on these algae could
receive lethal amounts of Dieldrin.
— Pesticide usage in an orchard did not significantly contami-
nate the aquatic environment of this creek adjacent to the
treatment as determined by residue analysis.
^
— The study showed that the levels of chlorinated hydrocarbon
pesticide residues in fish meals and oils were, with the
exception of the oil sample taken from the Lake Michigan
alewife, below the regulatory tolerances established by the
Food and Drug Directorate of Canada (1965) for certain
foods intended for human consumption. Pesticide levels
were interpreted as being representative for each species.
a The paper describes a method for continuously producing
a supply of an aqueous solution of Dieldrin by passing
water at a constant rate through a column of sand coated
Reference
(Year)
Mawdesley-
Thomas and
Leahy
(1967)
Cairns
(1968)
Moubry, et al
(1968)
Dugal
(1968)
Chadwick and
Kiigemagi
(1968)
^
•o
m
Z
g
00
Dieldrin
Pteronarcys
californica
(naiads)
Pteronarcella
bad/a
(naiads)
Claasenia
sabulosa
(naiads)
BSA
0.0005 (T4A)
0.0005 (T4A)
0.00058 (T4A)
Jl.£S[£.
with the insecticide. The concentration of HEOD, the
active ingredient of Dieldrin, was nearly constant over a
period of several months, but the toxicity of the water
declined steeply during the first few weeks until a
relatively stable level was attained.
Data reported as LCgrj at 15.5 C in 4 days.
Sanders and
Cope
(1968)
-------
Difolatan
Difolatan
[IM-(1, 1,2,2-
tetrachlorethyl-
thio)-4-cyclo-
hexane-1,2-di-
carboximide]
Difolatan
Dilan
Dilan
Dimecron
Dimethoate
Oyster
Fundulus
similus
(juvenile)
Brachydanio
rerio
Pteronarcys
ca/ifornica
(naiads)
Channel
catfish
(fingerlings)
Gambusia
affinis
Cyprinus
carpio
Anopheles
quadrimaculatus
Aedes aegypti
BCF
BSA
BSA
BSA
BSA
BSA
BSA
BSA
Dimethoate
Dimethoate
(tech)
Dimethoate
8
3
m
3)
O
(-
O
I
m
— Dimethoate
O
I-
-o
3)
O
O
C
O
Pteronarcys sp
(nymphs)
Bluegill
Prosimulum spp
Cnephia spp
Simulium spp
(larvae)
Pteronarcys
californica
(naiads)
BSA
BSA
LCFA
BSA
0.034 (O)
0.032 (O)
1 (O)
The value reported is a 96-hour £650 (decreased shell
growth).
Water temperature was 20 C. The figure reported is a 48-hr
0.0004 (T4A)
0.5
(K25hr A)
0.5 (LD*
0.4 (L1)**
* Resistant fish
**Nonresistant fish
51.5 (T2A)
3.5 (O)
4.0 (O)
0.043 (T4A)
6.0 (T4A)
4.0 (O)
ac d e f
a c d e f p
0.043 (T4A)
a c d e f
At 1 ppm all larvae were killed within 48 min. The
was 34 min. LC^Q was 0.21 ppm.
Data reported as
at 15.5 C in 4 days.
Tap water was used. Considerable additional data are
presented.
This paper deals with the resistance of mosquito fish to
chlorinated hydrocarbon compounds. Resistant fish
were not always less sensitive to these chemicals.
The test animals were conditioned for 48 hours prior to use.
4th instar larvae of mosquitos were used in this bioassay.
At the indicated concentrations, the following mortalities
occurred:
Anopheles quadrimaculatus 79%
Aedes aegypti 29%
Adsorption was determined by use of P^2 labeled dimethoate.
Experiments were all conducted at 60 F in 1964. The values
were listed as LC5Q.
The values reported are given as
Stones heavily populated with wild larvae were placed in
troughs of running water containing the toxicant. When
the larvae became detached from the rocks and floated
away, they were assumed to have undergone lethal intoxi-
cation. The larvae were exposed to the toxicant for 5
minutes, then in clean water for 24 hours. At that time
the number detached amounted to 4 percent.
Data reported as LC§o at 15.5 C in 4 days.
Butler
(1965)
Abedi and
Turton
(1968)
Sanders and
Cope
(1968)
Clemens and
Sneed
(1959)
Boyd and
Ferguson
(1964)
Sreenivasan and
Swaminathan
(1967)
Schmidt and 2
Weidhaas X
(1961) m
Cope
(1965)
Cope
(1965)
Jamnback and
Frempong-
Boadu
(1966)
m
Sanders and
Cope
(1968)
-------
o
0
s
s
m
n Chemical
j> -
*~ UimrMhrm
n
I
m
S
o
>
r~
-0
33
Q Dimethyl
C urea
O
tn
Dimetilan
Dimeton
3
2
2
Dipterex
Dipterex
Bioassay
or Field
Organism Study (1)
Prosimulum spp LCFA
Cnephia spp
Simulium spp
(larvae)
Sa/mo BSA
gairdnerii
Prosimulum spp LCFA
Cnephia spp
Simulium spp
(larvae)
Pimephales BSA
promelas
Rainbow BCFA
trout
Eastern brook
trout
Fathead BSA
minnow
Toxicity, Experimental
Active Variables
Field Ingredient, Controlled
Location(2) ppm(3) or Noted '4)
0.4 (0) a
975 (T1A) ae
925 (T2A)
180 (T1AC
100 (T2AI*
'with adjuvant
4.0 (O) a
0.5 (O) -
1-10(KO%) a
51 (T4A) £
Comments
Stones heavily populated with wild larvae were placed in
troughs of running water containing the toxicant. When
the larvae became detached from the rocks and floated
away, they were assumed to have undergone lethal intoxi-
cation. The larvae were exposed to the toxicant for 5
minutes, then in clean water for 24 hours. At that time
the number detached amounted to 89 percent.
Most of the weed-killer formulations in this study consisted
of more than one substance, i.e., oils, emulsifiers, stabilizers,
and other adjuvants.
Stones heavily populated with with wild larvae were placed
in troughs of running water containing the toxicant. When
the larvae became detached from the rocks and floated
away, they were assumed to have undergone lethal intoxi-
cation. The larvae were exposed to the toxicant for 5
minutes, then in clean water for 24 hours. At that time
the number detached amounted to 2 percent.
The degree of reaction to the cholinesterase-inhibiting insecti-
cides is not only a function of time and concentration, but
also of chemical and biological species. This paper reports
many analyses of brain cholinesterase activity which is
expressed as percentage of normal. The data are reported as
LT5Q which was the time required for 0.5 ppm of the
chemical to kill 50 percent of the fish. The LTgg for the
fathead was 72 hr.
Spring water (46 F) was used. The flow rate was 10 GPM.
The chemical was added by continuous drip dispenser.
0.02 ppm for 180 hr showed toxic effects, but no kill.
It was the authors opinion that pH, alkalinity and hardness,
within the usual range in natural waters, had little effect on
Reference
(Year)
Jamnback and
Frempong-
Boadu
(1966)
Alabaster
(1956)
Jamnback and
Frempong-
Boadu
(1966)
Weiss
(1961)
Hoffman
(1957)
Tarzwell
(1959)
>
•o
-o
m
z
o
00
Dipterex
Pimephales
promelas
BSA
180 (T4A)
a d e f
the toxic effect of the compounds studied. The values
given are from Henderson, Pickering, and Tarzwell, "The
Relative Toxicity of Ten Chlorinated Hydrocarbon Insecti-
cides to Four Species of Fish" It is interesting that the
different tables from the above book (as reported in this
paper) report widely different values for the same
compounds.
This experiment was performed in hard water.
Concentrations were based on percent active ingredient.
Henderson, et al
(1959)
-------
Dipterex
Dipterex
Dipterex
Dipterex
Dipterex
Dipterex
(99%)
Dipterex
g Diquat
5
jfj Diquat
33
O
Pimephales
promelas
Protococcus sp
Chlorella sp
Duna/iella
euchlora
Phaeodactylum
tricornutum
Monochrysis
lutheri
Chaoborus
astictopus
Bluegill
Daphnia
magna
Pimephales
promelas
Daphnia
carinata
Simocephalus
serrulatus
Daphnia
pulex
Onchorynchus
tshawytscha
Sa/mo
gairdneri
BSA
180 (T4A)
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
1000(K)
500 (K)
500 (K)
500 (K)
100 (K)
0.60 (T1A)
3.8 (T4A)
0.00012 (SB)
180(T4A)
0.00025 (SB)
0.00070 (SB)
0.00018 (SB)
29.5 (T1A)
28.5 (T2A)
(O)
a c d e f
a c d e
Bioassay investigations of the new insecticides indicate
that in general the organic phosphorus compounds are not
as toxic to fish as are the chlorinated hydrocarbons. The
toxicity of most of these materials was not significantly
influenced by water quality. Therefore it is to be expected
that the toxicity of these materials will not differ signifi-
cantly in different streams.
This paper concerns the growth of pure cultures of marine
plankton in the presence of toxicants. Results were ex-
pressed as the ratio of optical density of growth in the
presence of toxicants to optical density in the basal medium
with no added toxicants.
Toxicity value given is for the fourth instar larvae.
Assays were conducted in soft water at 25 C. Decrease in
brain cholinesterase was measured in fish exposed to the
toxicant.
Concentration reported is for immobilization.
Time for immobilization was 64 hr.
Data cited are for 78 F, but assays were performed at
varied temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
Tests were performed in both hard and soft water. Additional
tolerance limit values are given.
Concentration reported is for immobilization.
Time for immobilization was 64 hr.
Data cited are for 78 F, but assays were performed at
varied temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
Concentrations were based on percent active ingredient.
No mortality was noted with concentrations of 10,000
mg/1 at 55 F for 100 hr. Fish were 2-3 in. long.
Tarzwell
(1959)
Ukeles
(1962)
Hazel tine
(1963)
Weiss
(1964)
Sanders and
Cope
(1966)
Henderson and
Pickering
(1958)
Sanders and
Cope
(1966)
Bond, et al
(1960)
Cope
(1963)
TJ
m
Z
O
X
00
o
m
§
£
3)
O
O
1
-------
COMMERCI/
i>
r
o
I
m
§
O
r-
-o
33
0
O
c
o
CO
CO
to
Chemical Organism
Diquat
(1 1'-ethylene-
2: 2'-depyridyliurn
di bromide)
El odea
canadensis
Potamogeton
nodosus
Potamogeton
pectinatus
Diquat Lepomis
macrochirus
Pimephales
promelas
Micropterus
salmoides
Diquat Micropterus
salmoides
(fry)
Ictalurus
punctaius
(fry)
Lepomis
macrochirus
(fry)
Diquat Lemna
minor
Spirodela
polyrhyza
Wolffia
columbiana
Diquat Spirodela
polyrhyza
Lemna
minor
Wolffiella
flondana
Azolla
caroliniana
Wolffia
columbiana
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study (D Location'2) ppm'3)
BSA
5 (O)
100 (O)
5 (O)
100 (O)
5 (0)
100 (O)
BSA - 140 (T4A) H
72 (T4) S
130 (T4A) H
14 (T4) S
78 (T4A) S
BSA - 1.0 (SB3)
10.0 (SB3)
4.0 (SB3)
FL Fla. (0)
BSA - (O)
Experimental
Variables
Controlled
or Noted W) Comments
a Experiments were conducted in standing water. Results
were rated on a scale of 0 to 1 0, 0 standing for no toxic
effect and 10 signifying a complete kill. Evaluation was
based on visual observation of the plant response at weekly
intervals for 4 weeks.
Injury rating of 8.5.
Injury rating of 9.0.
Injury rating of 7.5.
Injury rating of 9.0.
Injury rating of 8.8.
Injury rating of 9.4.
ace Bioassay methods in Standard Methods for examination of
water was used. Both hard (H) and soft (S) water were
used. TLm values for 24 and 48 hr are also presented.
a c d e f p At least 90 percent of the fry survived for a period of 72
hours at the concentration listed.
— Common duckweed and watermeal in small ponds can be
controlled with diquat at rates as low as 0.25 ppmw, but
rates greater than 0.5 ppmw are required for control in
ponds infested with watermeal.
a_ 0.01 ppm caused 80% chlorosis in 7 days.
0.01 ppm caused 90% chlorosis in 7 days.
0.01 ppm caused 72% chlorosis in 7 days.
0.01 ppm caused 50% chlorosis in 7 days.
0.01 ppm caused 3% chlorosis in 7 days.
Reference
(Year)
Frank, et al
(1961)
Surber and
Pickering
(1962)
Jones
(1965)
Blackburn and
Weldon
(1965)
Blackburn and
Weldon
(1965)
^
2
m
z
o
X
00
Light intensity was kept at 500 foot-candles for 14 hours
per day. Light has been shown to Increase the rate of
kill with diquat.
Test containers were plastic petri dishes.
-------
Diquat Plankton
(1,1'-ethylene- Oligochaeta
2,2'-dipyridy- Chironomids
Mum dibromide)
FL
Fla.
0.5 (O)
Diquat
Diquat
Diquat
Diquat
m
3
O
Lepomis
macrochirus
Micropterus
salmoides
Pimephales
promelas
Ictalurus
punctatus
Sal mo
gairdneri
Oyster
Fundulus
si mil us
(juvenile)
Penaeus
setiferus
Crassostrea
virginica
Penaeus
setiferus
Fundulus
similis
Phytoplankton
BSA
BCF
BSA
BCFA & BSA
9-10 (L10)
10(L10)
10IL10)
10(L10)
5IL10)
(O)
(O)
(O)
1.0 (NTE)
1.0 (NTE)
1.0 (NTE)
45% (O)
Water samples from ponds taken at 3 and 11 days after
application showed concentrations of diquat at 0.25 ppm
and 0.001 ppm, respectively. No diquat was present
after 16 days.
Plankton appeared to be adversely affected by 0.5 ppm of
diquat, but recovered rapidly. Oligochaeta showed a
subtle chronic sensitivity to diquat.
Toxicity to fish was determined as the threshold concentra-
tion (LD10) in 96 hr at 75 F (65 F for trout). Herbicidal
evaluations are also presented.
No effect on exposure to the chemical at 1.0 ppm.
Water temperature was 19 C. No effect was noticed on
exposure to 1 .0 ppm.
Toxicant chemicals were evaluated in seawater at tempera
tures averaging about 28 C. The values are for 24-hr
or enough to cause loss of equilibrium or mortality. No
effect occurred at 1 .0 ppm.
Seawater was pumped continuously into test aquaria.
Salinity, temperature, and plankton fluctuated with tide,
and ambient weather conditions. Some bioassays with
fish were static. Toxicity was reported for the
following:
Oyster — 96-hr £659 — Cone, which decreased
shell growth.
Shrimp — 48-hr ECgrj — Concl which killed or
paralyzed 50% of test animals.
Fish - 48-hr EC50 - Cone, which killed 50%.
Phytoplankton — Percent decrease of CO2 fixation to a
4-hr exposure at 1 .0 ppm chemical
concentration.
Tatum and
Blackburn
(1965)
Lawrence, et al
(1965)
Butler
(1965)
Butler
(1965)
Butler
(1965)
m
O
X
CD
o
0)
O
O
-------
o
o
2
2
m
o Chemical
i~ Diquat
O
I
m
2
O
1-
T
0
o
Q
— 1
(ft
o
:>
^
Diquat
Diquat
Bioassay
or Field
Organism Study'1'
Ephemeroptera FL
Caenidae
Odonata
Coenagrionidae
Hemiptera
Hebridae
Mesoveliidae
Gerridae
Veliidae
Pleidae
Belostomaladae
Corixidae
Coleoptera
Halipidae
Dytiscidae
Diptera
Chironomidae
Amphipoda
Talitridae
Basommatophora
Planorbidae
Physidae
Copepoda
Ostracoda
Eucalia
inconstans
Salvelinus
fontinalis
Salmo BSA
gairdneri
Lepomis
macrochirus
Daphnia BSA
magna
Toxicity, Experimental
Active Variables
Field Ingredient, Controlled Reference
Location'2' ppm'3) or Noted'4' Comments (Year)
Price Co., (O) — An application of 1.0 ppm of Diquat was made to control Hilsenhoff
Wise. a nuisance weed, Elodea canadensis, in a pond. The effect (1966)
of this treatment on aquatic insects and related animals
was monitored. At 1 .0 ppm, Diquat appeared to be
harmless to the aquatic fauna, but caused sharp changes
in the numbers of most arthropods and mollusks by
destroying their habitats. Organisms affected to some
degree are recorded in the organisms column.
— 20.000 (T2A) a This paper reports acute toxicity of a number of compounds, Cope
and discusses sub-acute toxicity as well. Effects on repro- (1966)
19.000 (T2A) duction and behavior are also discussed. Data presented as
EC50-
— 7.1 (6.3-8.0) (O) a c d i q Toxicity, in terms of median immobilization concentration Crosby and
(ICsrj), is presented. Tucker
(1966)
^
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m
Z
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X
00
-------
Diquat
Diquat
Diquat
8
m
3)
r>
m
O
-o
jo
O
o
Diquat
Potamogeton
crispus
P. foliosus
P. pectinatus
P. pusillus
Myriophyllum
exalbescens
Ranunculus
trichophyllus
Elodea
canadensis
Cera toph y Ilium
demersum
A/a/as
flexilis
Cabomba
caroliniana
Typha
lati folia
T. angustifolia
Justicia
americana
J, repens var.
glabrescens
Sagittaria
lati folia
Scirpus
acutus
Salmon
Lepomis
macrochirus
Carassius
auratus
Esox
lucius
Salmo
gairdnerii
Stizostedion
vitreum vitreum
Daphnia
pulex
Cladocera
Lepomis
macrochirus
FL
Ponds,
Central
Illinois
BSA
BSA
BSCH
0.5 (K)
0.5 (K)
0.5 (K)
0.5 (K)
0.5 (K)
0.5 (K)
1.0 (K)
1.0 (K)
1.0 (K)
4.0 (NTE)
25.0 (O)
25.0 (O)
25.0(O)
25.0 (O)
25.0 (O)
(O)
28.5 (T2A)
35 (T4A)
35 (T4A)
16(T4A)
11.2 (T4A)
2.1 (T4A)
3(K8)
(O)
(O)
a c d f i I m n p
a c d f i m p
Liquid formulations containing two pounds of the
Diquat cation per gallon as the dibromide salt were
used in all experiments. Most applications were
based on the Diquat cation content in ppm, but some
rates were expressed as the volume of herbicide per
gallon of water, e.g., the 25.0 rate of application
resulted in a kill by a foliage application of 25 ml of
chemical diluted to 1 gallon with water. The paper states
that recently Scirpus acutus was killed by a foliage
application containing 10 ml of Diquat and 3 ml of
X-77, a non-ionic wetting agent, diluted to 1 gallon with
water.
Hiltibran
(1967)
Data are given as
The herbicide showed an acute toxicity to Cladocera. At
3 ppm the Cladocera population was reduced to a level
of 102 as opposed to a maximum in the control of 150.
Bohmont
(1967)
Glide rhus
(1967)
Elodea canadensis was used as an indicator of herbicidal
activity and to provide a nearly natural habitat in artificial
ponds. Fingerling and adult bluegills were used in this
experiment.
The pools were treated with 1 and 3 ppm of Diquat at various
frequencies. No fish kill occurred. After 24 weeks no residues
of the chemical were found in the bluegills at a treatment
rate of 3 ppm in one study. However, another experiment
indicated a residue of 1.1 ppm in bluegills.
Gilderhus
(1967)
-------
COMMERCI/
>»
r~
0
i
m
S
O
^>
r~
TJ
33
o
o
0
en
CO
1
O
Ox
Chemical
Diquat
Di-Syston
Di-Syston
Di-Syston
Di -system
(tech,
90 percent)
Di-syston,
(emulsible
concentrate,
20 percent)
Di-Syston
(tech, 89
percent
active in
acetone)
Organism
Lepomis
macmchirus
(eggs)
Microp terus
do/omieui
(eggs)
Erimyzon
sucetta
(eggs)
L. macrochirus
(fry)
Pimephales
prome/as
Lepomis
macrochirus
Pimephales
prome/as
Lepomis
macrochirus
Micropterus
sa/moides
Pimephales
prome/as
Carassius
auratus
Lebistes
reticulatus
Lepomis
macrochirus
Pteronarcys
californica
(naiad)
Acroneuria
pacifica
(naiad)
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study*1) Location!2* ppm(3) or Noted*4'
L - 2.5/3(0)
2.5/1 (0),
1.3/4 (O)
2.5/2 (O),
1.3/2 (O)
10 (S)
BSA - 3.7 (T4A) ^def
0.064 (T4A)
BSA - 3.7 (T4A) a
0.064 (T4A)
BSA - 0.5 (O)
0.5 (O)
BSA - 7.2 (T4A) a c d e
0.28 (T4A)
BSA - 0.082 (T4A) ^cde_
BSA - 0.0285 (T4A) c d e f
0.0082 (T4A)
Comments
Fertilized fish eggs of indicated species were placed in 1 liter
of test solution and allowed to hatch. Toxicity data are
presented as concentration in ppm/number of days survival.
Maximum length of test was 8 days. No food was added.
Small bluegill were tested to find the highest concentration
of chemical which did not cause death in 12 days (S).
Concentrations were based on percent active ingredient.
Bioassay investigations of the new insecticides indicate that
in general the organic phosphorus compounds are not as
toxic to fish as are the chlorinated hydrocarbons. The
toxicity of most of these materials was not significantly in-
fluenced by water quality. Therefore it is to be expected
that the toxicity of these materials will not differ significantly
in different streams.
The degree of reaction to the cholinesterase-inhibiting insecti-
cides is not only a function of time and concentration, but
also of chemical and biological species. This paper reports
many analyses of brain cholinesterase activity which is
expressed as percentage of normal. The data are reported
as LTso which was the time required for 0.5 ppm of the
chemical to kill 50 percent of the fish. For bass the LTsg
was 24 hr and for the fathead 72 hr.
Soft water primarily was the test medium. TLm's reported
for 24, 48, and 96 hr. Acetone or alcohol used as solvent
or carrier in most cases.
Soft water primarily was the test medium. TLm's reported
for 24, 48, and 96 hr. Acetone or alcohol used as solvent
or carrier in most cases.
A pacifica was much more sensitive to chlorinated hydro-
carbons and to organic phosphate insecticides than P.
californica.
Reference
(Year)
Hiltibran
(1967)
Henderson, et al
(1959)
Tarzwell
(1959)
Weiss
(1961)
Pickering, et al
(1962)
Pickering, et al
(1962)
Jensen and
Gaufin
(1964)
>
^
•o
m
X
00
-------
Di-Syston
Di-Syston
Di-Syston
Di-Syston
O
-J
Disulfoton
Dowacide A
Diuron
8
m Diuron
3)
O
O
O
T)
•3)
O
O
c
Diuron
Gammarus
lacustris
Bluegill
Bluegill
Pteronarcys
californica
Acroneuria
pacifica
Ephemeral/a
grandis
Gammarus
lacustris
Bluegill
sunfish
Fathead
minnow
Pteronarcys
californica
(naiads)
Protococcus sp
Chlorella sp
Dunaliella
euchlora
Phaeodactylum
tricornutum
Monochrysis
lutheri
Oncorhynchus
kisutch
Micropterus
salmoides
Protococcus sp
Chlorella sp
Dunaliella
euchlora
Phaeodactylum
tricoruntum
Monochrysis
lutheri
Penaeus
aztecus
BSA
BSA
BSCH
BSA
BSA
BSA
BSA
O.24 (T4A)
0.063 (T4A)
1.0(0)*
'response,
15 days
0.03 (T4A)
0.008 (T4A)
0.08 (T4A)
0.2 (T4A)
0.07 (T4A)
4.1 (T4A)
0.005 (T4A)
100(NG)
100 (NG)
100(NG)
100 (K)
50 (K)
33 (T1A)
16 (T2A)
(O)
0.004 (K)
0.04 (NG)
0.004 (NG)
0.004 (K)
0.00002 (K)
(O)
j c d e
acde
Emulsible concentrates were prepared from technical grade
insecticides with acetone as the solvent.
Symptoms prior to death were observed and recorded on
graphs.
Assays were conducted in soft water at 25 C. Decrease in
brain cholinesterase was measured in fish exposed to the
toxicant.
Toxicity was determined by measuring acetylcholinesterase
activity in the brains of fish. Concentrations are given in
ppbas either response or not response in 15 or 30 days.
Unspecified chemical characteristics of assay water were
determined by standard methods. General comments
were made concerning "standardized" conditions, use
of "soft" water, and use of emulsifying agents. Additional
data are presented.
'-)ata reported as
at 15.5 C in 4 days.
This paper concerns the growth of pure cultures on marine
plankton in the presence of toxicants. Results were ex-
pressed as the ratio of optical density of growth in the
presence of toxicants to optical density in the basal medium
with no added toxicants. NG = no growth, but the organisms
were viable.
Concentrations were based on percent active ingredient. Low
Low toxicity occurred with M. salmoides in the solubility
range of this compound.
This paper concerns the growth of pure cultures of marine
plankton in the presence of toxicants. Results were ex-
pressed as the ratio of optical density of growth in the
presence of toxicants to optical density in the basal medium
with no added toxicants. NG = no growth, but the
organisms were viable.
Toxicant chemicals were evaluated in sea water at tempera-
tures averaging about 28 C. The values are for 24-hr ECgg
or enough to cause loss of equilibrium or mortality. No
effect occurred at 1.0 ppm.
Nebeker and
Gaufin
(1964)
Weiss
(1964)
Weiss and
Gakstatter
(1964)
Gaufin, et al
(1965)
Sanders and
Cope
(1968)
Ukeles
(1962)
Bond, et al
(1960)
Ukeles
(1962)
Butler
(1965)
m
Z
o
X
00
-------
COMMERCIA
i-
o
I
m
Q
>
r~
•O
7
O
c
q
en
3
3
3
Chemical
Diuron
Diuron
(tech)
Diuron-TCA
(3lb/gal)
Diuron
(80 percent,
WP)
Diuron
Diuron
Diuron
Diuron
(Karmex)
Diuron
(tech)
Organism
Crassostrea
virginica
Penaeus
aztecus
Mugil
cephalus
Phytoplankton
Bluegill
Lepomis
macrochirus
Ictalums
nebulosis
Lepomis
macrochirus
Salmo
gairdneri
Lepomis
macrochirus
Daphnia
pulex
Simocephalus
serrulatus
Daphnia
magna
Bluegill
Simocephalus
serrulatus
Daphnia
pulex
Salmon
Bluegill
Pteronarcys
callforhica
(naiads)
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study'1) Location<2) ppm<3> or Noted <4'
BCFA & BSA - 1.8 (0)
1.0 (NTE)
6.3 (T2A)
87% (O)
BSA - 4.0 (T4A) a
BSA - 5.7 (T4A)
BSA - 11.0(T4A)
25.0 (T4A)
BSA - 4.300 (T2A) a
7.400 (T2A)
1 .400 (T2A)
2.000 (T2A)
BSA - 47 (41.6- ac di q
53.1) (0)
7.4 (0)
BSA - 2.00 (SB)
1.40 (SB)
BSA - 16.0IT2A) -
74.0 (T2A)
BSA - 0.0012 (T4A) _i£_d_e_f
Comments
Seawater was pumped continuously into test aquaria.
Salinity, temperature, and plankton fluctuated with tide.
and ambient weather conditions. Some bioassays with
fish were static. Toxicity was reported for the following:
Oyster — 96-hr EC5Q — Cone, which decreased
shell growth.
Shrimp — 48-hr ECsg — Cone, which killed or
paralyzed 50% of test animals.
Fish- 48-hr EC50 - Cone, which killed
50%.
Phytoplankton — Percent decrease of CO2 fixation to a
4-hr exposure at 1.0 ppm chemical
concentration.
This is an estimated LCsg value at temperatures from 55 to
75 F.
Laboratory bioassays indicated that toxicity of the different
formulations evaluated in this varied greatly with the fish
used. Mortality data are expressed as EC-|0. ECgrj. etc-
Comment same as above.
This paper reports acute toxicity of a number of compounds,
and discusses sub-acute mortality as well. Effects on repro-
duction and behavior are also discussed. Data presented as
EC5Q-
Toxicity, in terms of median immobilization concentration
(ICsg), is presented for Daphnia; median lethal concentra-
tion for (LCso) values for bluegill are reported.
Concentration reported is for immobilization.
Time for immobilization was 64 hr.
Data cited are for 78 F, but assays were performed at
varied temperatures.
Water chemistry (unspecified) was "controlled" during
during the assay period.
Data are given as LCgQ.
Data reported as LC$Q at 15.5 C in 4 days.
Reference
(Year)
Butler
(1965)
Cope
(1965)
Walker
(1965)
Walker
(1965)
Cope
(1966)
Crosby and
Tucker
(1966)
Sanders and
Cope
(1966)
Bohmont
(1967)
Sanders and
Cope
(1968)
m
z
D
X
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-------
T3
§
Oowco 139
(25 percent
EC)
Dowicide 31
(chloro-2-
phenyl phenol,
tech)
Dowicide F
(sodium 2,3,4,6-
tetrachlorophe-
nate, 80 percent)
Dowpon
(2,2-dichloro-
propionic acid)
Dowpon
Dowpon
2-(2,4DP)
(dimethylamine)
2-(2,4-DP)
(butoxyethanol
ester)
2-(2,4DP)
(isooctyl
ester)
2,4-DP
(ester)
o
O
m
3
o
n DPT
I (DDT
Sj analogue)
Drummer
(Pine)
Gambusia
affinis
Lymnaeid
snails
Lymnaeid
snails
Richardsonius
balteatus
hydroflox
Typha
latifolia
Panicum
hemitomum
Oncorhynchus
kisutch
Micropterus
salmoides
Lepomis
macrochirus
Lepomis
macrochirus
Lepomis
macrochirus
Lepomis
macrochirus
Erimyzon
sucetta
L. macrochirus
(fry)
Goldfish
Gambusia
affinis
Culex
apicalis
(larvae)
Guppy
FL
BSA
BSA
BSA
FL
BSA & CF
BSA
BSA
BSA
Ponds—
Bakers-
field,
Cal.
Fla.
BSA
BSA
(O)
(O)
(O)
444 (T1 A)
412IT2A)
395 (T4A)
(O)
340 (T1)
340 (T2)
165(T2A)
1.1 (T2A)
16(T2A)
10 (NTE)
1.5INTE)
20 (S)
10.0IK)
2.0 (K)
0.1 (K)
100 (K1)
a c d e f
ac de
a e
At 0.1 Ib/acre, 2 percent mortality occurred in 24 hours.
The experiments were conducted in cages placed in the
ponds.
Each test container (500-ml beaker) was filled with ditch
water. 100% mortality occurred at 1:200,000 and greater.
Each test container (500-ml beaker) was filled with ditch
water. 100% mortality occurred in concentrations of
1:600,000 and greater.
Results given were in soft water.
At 51.0 and 17.0 Ib/acre, 95 percent control of cattail
was obtained and 3-5 percent control of P. hemitomum.
Concentrations were based on percent active ingredient.
In constant flow experiments, no bass survived 48 hours'
exposure at 1000 ppm.
The various salts of the chemicals showed wide variations
in toxicity.
Comment same as above.
Comment same as above.
Fertilized fish eggs of indicated species were placed in
1 liter of test solution and allowed to hatch. Toxicity
data are presented as concentration in ppm/number of
days survival. Maximum length.of test was 8 days. No
food was added. Small bluegill were tested to find the
highest concentration of chemical which did not cause
death in 12 days (S).
Experiments were run a maximum of 3 days. No
other time data were reported.
Those fish that survived at lower concentrations were still
very active several days after they had been taken out and
in fresh water.
Mulla and
Isaak
(1961)
Batte, et al
(1951)
Batte, et al
(1951)
Webb
(1961)
Copeland and
Woods
(1959)
Bond, et al
(1960)
Hughes and
Davis
(1963)
Hughes and
Davis
(1963)
Hughes and
Davis
(1963)
Hiltibran
(1967)
I
m
O
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co
Odum and
Sumerford
(1946)
Anonymous
(1964)
-------
r>
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5
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n Chemical
> —
r~ Dursban
n
i.
m
S
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r-
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3)
O Dursban
W
c
q
en
Dursban
Dursban
hj Dursban
T^
O
Dursban
DVP-
iodine
Bioassay
or Field
Organism Study (D
Notemigonus BSA
crysoleucas
Gambusia
affinis
Lepomis
cyanellus
Prosimulum spp LCFA
Cnephia spp
Simulium spp
(larvae)
Leiostromus BCFCH
xanthurus
Callinectes
sapidus
Callinectes BCFCH
sapidus
Pteronarcys BSA
ca/ifornica
(naiads)
Pteronarcys BSA
ca/ifornica
(naiads)
Pteronarcel/a
bad/a
(naiads)
Claasenia
sabulosa
(naiads)
Photococcus sp BSA
Chlorella sp
Dunaliella
euchlora
Phaeodactylum
tricornutum
Monochrysis
lutheri
Toxicity, Experimental
Active Variables
Field Ingredient, Controlled
Location^) ppm(3) or Noted^4'
1.0(T<1A) ef
1.0 (T<1A)
1.0 (T<1A)
0.4 (0) a
0.001 (O) a
0.010 (K) a
0.01 (T4A) ac def
0.010(T4A) 1£^1
0.0038 (T4A)
0.0057 (T4A)
100(0)* a
100 (O)*
50 (NG)
50 (NG)
100 (K)
'obvious, but
inhibited
growth.
Comments
Fish used in the experiment were obtained from two sources,
Mississippi Delta and State College pond. The fish obtained
from the State College pond had not been exposed to insecti-
cides. The fish obtained from the Mississippi Delta were
known to be contaminated by cotton crop insecticides.
Higher tolerance of Delta populations was evident in longer
survival to 1.0 ppm Dursban.
Stones heavily populated with wild larvae were placed in
troughs of running water containing the toxicant. When
the larvae became detached from the rocks and floated
away, they were assumed to have undergone lethal intoxi-
cation. The larvae were exposed to the toxicant for 5
minutes, then in clean water for 24 hours. At that time the
number detached amounted to 32 percent.
At a concentration of .001 ppm, the following percent
acetylcholinesterase activity as compared to controls was
found:
L. xanthurus — 38
Little or no information was given about test procedures and
further tests.
Data reported as LCso at 15.5 C in 4 days.
Data reported as LC50, at 15.5 C in 4 days.
This paper concerns the growth of pure cultures of marine
plankton in the presence of toxicants. Results were ex-
pressed as the ratio of optical density of growth in the
presence of toxicants to optical density in the basal
medium with no added toxicants. NG = no growth, but
the organisms were viable.
Reference
(Year)
Ferguson, et al
(1966)
Jamnback and
Frempong-
Boadu
(1966)
Butler and
Johnson
(1967)
Butler and
Johnson
(1967)
Sanders and
Cope
(1968)
Sanders and
Cope
(1968)
Ukeles
(1962)
•o
•u
rn
Z
0
X
CD
-------
£
^
s
o
m
3D
o
>
r
o
3T
m
S
5
i-
T>
31
O
o
c
3
Dylox
Dylox
Dylox
(Dipterex),
(tech, 99
percent)
Dylox
(tech, 89
percent
active in
acetone)
Dylox
Dylox
Dylox,
(tech)
Dylox,
(tech)
Dylox
Dylox
Gambusia
affinis
Sal mo
gairdnerii
(one wk old
sac fry)
(one mo old
feeding fry)
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Pteronarcys
californica
(naiad)
Acroneuria
pacifica
(naiad)
Gammarus
lacustris
Cyprinodon
variegatus
(juvenile)
Bluegill
Rainbow
trout
Bluegill
Pteronarcys sp
(nymphs)
Pteronarcys
californica
Acroneuria
pacifica
Ephemerella
grandis
Gammarus
lacustris
Fathead
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
0.5
-------
COMMERCIA
r
I
m
O
r~
-o
3)
O
a
o
tp
>—
to
Chemical
Dylox
Dylox
(99% active
in water)
Dylox
Dymid
(WP)
EDB
EN 18133
(50 percent
EC)
Endosulfan
EC2
Endosulfan
EC2
Endosulfan
Organism
Acroneuria
pacifica
Ephemerella
grandis
Gammarus
lacustris
Pteronarcys
californica
Hexagenia
Hydropsyche
(larva)
Bluegill
Carassius
auratus
Lebistes
reticulatus
Bluegill
Rainbow
trout
Lepomis
macrochirus
Micropterus
salmoides
Gambusia
affinis
Micropterus
salmoides
Cyprinus
carpio
Micropterus
salmoides
Cyprinus
carpio
Pteronarcys
californica
(naiads)
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study<1> Location<2) ppm<3) or Noted <4>
BSA - 0.01 7 (T4A) ac
0.14 (T4A)
0.05 (T4A)
0.07 (T4A)
BSA - 0.91 (T1A) ae
0.017 (T1A)
12.0 (T1A)
BCFA - 0.4% (0) a
BSA? - 75.0 (T4A) a
97.0 (T4A)
BSA - 18(T2A) aco
15(T2A)
FL Ponds- 0.1 (K1) ac
Bakers- 0.4 (K1)
field, Cal.
BSA - 0.01 (O) a e
0.025 (K1)
0.005 (K5hr)
0.01
-------
Endothal
Endothal
Endothal
(pellets)
Semotilus
atromaculatus
Onchorynchus
tshawytscha
Micropterus
salmoides
Bushy
pondweed
Pondweed
Coontail
Endothal
and Silvex
Endothal
8
m
3)
o
m
2
9
Endothal
(liquid)
BSA
BSA, CF,
and FL
Endothal
[3,6-endoxohexa-
hydrophthalic
acid (endotha),
di-N,N-dimethyl-
cocoamine salt]
Elodea
canadensis
Potamogeton
nodosus
Potamogeton
pectinatus
Lepomis
macrochirus
Lepomis
macrochirus
Micropterus
salmoides
(fry)
Ictalurus
punctatus
(fry)
Lepomis
macrochirus
(fry)
FL
BSA
Lakes in
Fla.
BSA
BSA
BSA
1,6OO to
3,200 (CR)
155 (T1A)
136IT2A)
200 (T1A)
200 (T2A)
(O)
(O)
(O)
5(0)
100 (O)
5(0)
100 (K4wk)
5(0)
100 (K4wk)
400 (T2A) L
600 (T2A) G
280 (T2A) L
280 (T2A) G
10(SB3)
100 (SB3)
50 (SB3)
a e Test water used was freshly aerated Detroit River water.
~~ A typical water analysis is given. Toxicity is expressed as
the "critical range" (CR), which was defined as that con-
centration in ppm below which the 4 test fish lived for
24 hr and above which all test fish died. Additional data
are presented.
a c d e Concentrations were based on percent active ingredient.
In 96 hours of exposure in the constant-flow apparatus, no
largemouth bass mortalities were observed at 135 ppm,
which was the highest concentration tested.
In experimental field studies, Endothal controlled
Potamogeton pusillus at about 0.3 ppm with no loss of
largemouth bass or bluegills which were present in the pond.
— Concentrations of 0.5 to 2.0 ppm showed the best results in
a variety of lakes, and in one lake 16.0 ppm was required
to control bushy pondweed. 1.0 ppm controlled pondweed
and coontail.
a Experiments were conducted in standing water. Results
were rated on a scale of 0 to 10, 0 standing for no toxic
effect and 10 signifying a complete kill. Evaluation was
based on visual observation of the plant response at
weekly intervals for 4 weeks.
Injury rating of 8.5.
Injury rating of 9.0.
Injury rating of 9.1.
Injury rating of 9.8.
£c d e g Toxicity data for 24 and 48 hours are presented for liquid
~ (L) and granular (G) formulations. Various commercial
formulations were tested. The liquid formulations were
almost invariably more toxic than the granular ones.
a c d e g Comment same as above.
a c d e f p At least 90 percent of the fry survived for a period of
72 hours at the concentration listed.
Gillette, et al
(1952)
Bond, et al
(1960)
Phillippy
(1961)
Frank, et al
(1961)
I
m
D
X
09
Hughes and
Davis
(1965)
Hughes and
Davis
(1965)
Jones
(1966)
3D
O
rj
-------
o
0
5
S
m
o Chemical
>
n Endothal
2 (granular)
m
S
o
>
i—
TJ
3J
o
o
c
H Endothal
•o
T>
m
Z
o
00
-------
Endrin
Endrin
Endrin
Endrin
Endrin
Endrin
i
X
o
Endrin
(75%)
Carassius
auratus
Cyprinus
carpio
Carassius
auratus
Channa
argus
(eggs &
larvae)
Cyprinus
carpio
(adult)
(adult)
(eggs &
larvae)
Moina
macrocopa
Fathead
minnow
Bluegill
Goldfish
Guppy
Fathead
minnow
Daphnia
magna
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Pimephales
promelas
FL
BSCH
Japan (O)
BSA
BSA
BSA
BSA
BSA
0.003 (T1CH)
0.002 (T1CH)
0.0065-100
(T1CH)
0.003-0.42 (T1CH)
0.002-0.14 (T2CH)
0.046-19.9 (T1CH)
3.2(T1CH)
0.056 (T2CH)
0.001 (T4A)
0.00060 (T4A)
0.0019 (T4A)
0.0015 (T4A)
0.0013 (T4A)
0.352 (O)
0.001 (T4A)
0.0006 (T4A)
0.002 (T4A)
0.002 (T4A)
0.0032 (T4A)
adef
Four days after spraying at an application rate of 1 Ib/acre, Ivatomi, et al
all fish placed in pond were dead after 8 hours of exposure. (1958)
Endrin toxicity may persist in paddy fields as long as
1 month.
Endrin became less toxic as temperature was lowered. Eggs lyatomi, et al
and larvae of fishes were more resistant than adults, and (1958)
the granular form of Endrin persisted longer than dust form.
It was the authors opinion that pH, alkalinity and hardness,
within the usual range in natural waters, had little effect on
the toxic effect of the compounds studied. The values
given are from Henderson, Pickering, and Tarzwell, "The
Relative Toxicity of Ten Chlorinated Hydrocarbon Insecti-
cides to Four Species of Fish". It is interesting that the
different tables from the above book (as reported in this
paper) report widely different values for the same compounds.
This experiment was performed in soft water.
Comment same as above except that this experiment was
performed in hard water.
The indicated concentration immobilized Daphnia in
50 hours.
Concentrations were based on percent active ingredient.
Tarzwell
(1959)
Tarzwell
(1959)
Anderson
(1960)
Henderson, et al
(1959)
a b ecdf
Dilution water was usually soft although some studies were Henderson, et al
conducted with hard water. (1959)
o
m
2
o
TJ
3)
O
o
-------
o
o
5 Bioassay
m or Field
o Chemical Organism Study'D
r~ Endrin Pimephales BSA
2 (91 %) promelas
m Lepomis
5 macrochirus
jj Carassius
r~ auratus
r° Lebistes
O reticulatus
O
C Endrin Pimephales BSA
" (19.5%) promelas
OT Lepomis
macrochirus
Endrin Pimephales BSA
promelas
Endrin Live cars: FL
Pimephales
m promelas
Jl Ictalurus
•— ' me/as
Lepomis
cyanellus
Fish kill:
/'e/ca
flavescens
lepo/n/s
0//>/>OSUS
t. macrochirus
Pomixis
nigromaculatus
Cyprinus
carpio
Endrin Oncorhynchus BSA
Avsotc/j
Oncorh ynchus
tshawytscha
Salmo
gairdnerii
Gasterosteus
aculeatus
Toxicity, Experimental
Active Variables
Field Ingredient, Controlled
Location'2) ppm(3) or Noted (4)
0.0014 (T4A) abecdf
0.00066 (T4A)
0.0021 (T4A)
0.0016 (T4A)
0.0038 (T4A) abecdf
0.0037 (T4A)
0.0010 (T4A) a
Pond (O) a c d
0.51 (T4A) a c d e
1.2 (T4A)
0.58 (T4A)
0.44 (T4A)
Reference
Comments (Year)
Dilution water was usually soft although some studies were Henderson, et al
conducted with hard water. (1959)
Comment same as above. Henderson, et al
(1959)
Bioassay investigations of the new insecticides indicate that Tarzwell
in general the organic phosphorus compounds are not as (1959)
toxic to fish as are the chlorinated hydrocarbons. The
toxicity of most of these materials was not significantly
influenced by water quality. Therefore it is to be expected
that the toxicity of these materials will not differ signifi-
cantly in different streams.
A beet field located adjacent to the study pond was treated Bridges
with Endrin at the rate of 6 ounces of active ingredient per (1961 )
acre. Many fish were found dead after application. Live
cars of the fish listed were placed in the pond to assess the
residual toxic effects of Endrin. No mortality occurred in
the live cars for 4 days, but the fish did accumulate Endrin
in concentrations up to 1 .0 ppm. The acute toxicity of
Endrin appears to be less under these field conditions than
in the laboratory.
Chemical dissolved in acetone. TLm expressed in ppb. «atz
(1961)
TO
•o
m
Z
O
-------
Encfrin
Endrin
Satmo
gairdnerii
Oncorhynchus
tshawytscha
Oncorhynchus
kisutch
Lepomis
macrochirus
Gambusia
affinis
Lebistes
reticulatus
Gasterosteus
aculeatus
Gammarus
lacustris
lacustris
BSA
BSA
0.9O (T4A)
0.92 (T4A)
0.27 (T4A)
0.60 (T4A)
0.75 (T4A) 20 C
8.25 (T4A) 3 C
0.33(T4A)25C
0.90 (T4A)
1.65 (T4A) Salin-
ity 1.65 pp
thousand.
(O)
River water was diluent. TLm concentration is given in ppb.
a e p The mortality might have been partially due to the suscept-
ibility of the organism to higher temperatures, toxicity
from extended exposure to copper electrodes (used to
shock the organism to determine death), or the increase
of CO2- Results were expressed as LTso; for example, at
0.5 ppm, 50 percent of the shrimp were killed in 27 (±1)
Katz
(1961)
McDonald
(1962)
Cd Endrin
8
Endrin
(tech)
Endrin
EC 1.6
2
m
3D
o
> Endrin
£ (tech)
m
3 Endrin
TJ
•33
O
o
Pimephales
notatus
Lebistes
reticulatus
Adult 6
Adult 9
Adult 6
Adult 9
Lepomis
macrochirus
Gambusia
affinis
Rana
catesbeiana
(tadpoles)
Procambarus
clarki
Gambusia
affinis
affinis
BCFA
BSA
FL
Cal.
BSA
BSA
0.00047 (T4A)
0.0009 (T8A)
0.0009 (T10.6A)
0.00075 (T15A)
0.00075 (T15.5A)
0.4 (T1 A)
0.4 (T1A)
0.5 (O)
0.3 (T3A)
0.001 to 0.12
a c d f Chronic toxicity was also studied, as well as the effect of the Mount
toxicant on swimming and oxygen consumption. In the (1962)
chronic study, bluntnose minnows survived for extended
periods in 0.0001 ppm. Experiment on guppies was dis-
continued because they succumbed to a kidney disorder.
a The experiment was conducted at 75 F. Fish weight was Cope
0.4 g. (1963)
The experiment was conducted at 75 F. Fish weight was
0.6 g.
ac Mixed populations of the indicated test species contained in Mulla
cages were exposed to various insecticidal chemicals ap- (1963)
plied as dilute sprays to ponds 1/16 acre in size. The indi-
cated toxicant concentration is in Ib/acre, and resulted in
a 100 percent mortality for the fish, and a 100 percent
mortality for the tadpoles in 24 hr.
a c d o There was no detectable difference in toxicity to male or Muncy and
female crawfish. Oliver
(1963)
a The lower value is for fish that had never been exposed to the Boyd and
toxicant, and the higher value was obtained with fish that Ferguson
had been exposed to a sublethal dose in the past. Appar- (1964)
ently such an exposure produces a resistance that can be
retained when they are later placed in clean water.
m
O
X
(D
CO
-------
o
o
s
2
m
o Chemical
*" Endrin
O
x
m
O
r~
g Endrin
rj (technical,
C 100 percent
H active in
acetone)
Endrin
Endrin
Endrin
DO
!—
HI
00
Endrin
(tech)
Endrin
Endrin
Endrin
Organism
Notemigonus
crysoleucas
Lepomis
macrochirus
L. cyanellus
Pteronarcys
californica
(naiad)
Acroneuria
pacifica
(naiad)
Gammarus
lacustris
Bluegill
Bluegill
Rainbow
trout
Bluegill
Rainbow
trout
Leiostomus
xanthurus
(juvenile)
Fundulus
similis
(juvenile)
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study<1) Location!?) ppm(3) or Noted*4*
BSA - (B) 0.003 (T1 .5) a c f
(A) 0.310 (T1. 5)
(B) 0.0015 (T1.5)
(A) 0.300 (T1.5)
(B) 0.0034 (T1.5)
(A) 0.1 60 (T1. 5)
BSA - 0.00240 (T4A) c d e f
0.00039 (T4A)
BSA - 0.011 5 (T4A) ae
BSA - 0.0006 (T4A) a
BSA - 0.7 (T4A) a
0.7 (T4A)
0.4 (T4A)
0.4 (T4A)
0.7 (T4A)
BSA - 0.00086 (T4A)
0.00025 (T4A)
BSA - 2.4 (T4A) a
1.4(T4A) ~
1.1 (T4A)
0.75 (T4A)
BCH - (O)
BSA - 0.000079 (O) a
Comments
Chemical was dissolved in acetone. Final concentration of
acetone was <2 ml/l. Data shows TLm in ppb for
insecticide-resistant and insecticide non-resistant strains
of the test fish.
A. pacifica was much more sensitive to chlorinated hydro-
carbons and to organic phosphate insecticides than
P. californica.
Emulsible concentrates were prepared from technical grade
insecticides with acetone as the solvent.
Symptoms prior to death were observed and recorded on
graphs.
Assays were conducted in soft water at 25 C. Decrease in
brain cholinesterase was measured in fish exposed to the
toxicant.
These experiments were performed to demonstrate that at
increased temperatures the toxic effect of most chemicals
is increased.
For the toxicant concentrations listed, the temperatures
were respectively, 45, 55, 65, 75, and 85 F. Data on the
effect of time as well as temperature was also reported.
The experimental animals all were approximately one
grain in weight.
The values reported are given as LCsg.
These experiments were performed to show the effect of
temperature on the toxicity.
For the toxicant concentrations listed, the temperatures
were respectively, 45, 55, and 65 F. The fish all were
approximately one grain in weight.
Toxicant concentrations for one and 2-day times were
also listed.
Endrin at 0.0006 ppm killed half the shrimp exposed in
24 hours. The fish survived a concentration of
0.00005 ppm for 8 months, but a concentration of
0.0001 was usually lethal in 5 days.
Water temperature was 21 C. The figure reported is a 24-hr
ECgo-
Reference
(Year)
Ferguson, et al
(1964)
Jensen and
Gaufin
(1964)
Nebeker and
Gaufin
(1964)
Weiss
(1964)
Cope
(1965)
Cope
(1965)
Cope
(1965)
Butler
(1965)
Butler
(1965)
>
•o
m
z
o
X
00
-------
Endrin
Endrin
Endrin
Endrin
Endrin
Endrin
O Endrin
3,
m
3)
O
2 Endrin
o
TJ
3D
O
O
c
tn
Dorosoma
cepedianuen
Palaemonetes
kadiakensis
Gambusia
affinis
Ictalurus
me/as
Lepomis
cyanellus
Gambusia
affinis
Ictalurus
me/as
Acroneuria
pacifica
Ephemerella
grandis
Gammarus
lacustris
Pteronarcys
californica
Pteronarcys
californica
Acroneuria
pacifica
Ephemerella
grandis
Daphnia
magna
Gammarus
lacustris
Gambusia
affinis
Leiostomus
xanthurus
Mug/1
cephalus
Brevoortia
patronus
Fundulus
similis
Cyprlnodon
variegatus
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BCFA
(O)
(N) 6.5
(TV/4 A)
(TB) 9.5
(71 %A)
0.0005-
0.002 (T3A)
0.0004-
0.002 (T3A)
0.001-0.048(0)
0.0003 (T4A)
0.005 (T4A)
0.0115 (T4A)
0.0024 (T4A)
0.002 (T4A)
0.0004 (T4A)
0.005 (T4A)
0.4 (T 50 hr A)
0.01 (T4A)
(O)
0.00045(71 A)
0.0026(71 A)
0.00080 (71A)
0.00023 (71 A)
0.00032 (71A)
a d e 7he critical level of Endrin in the blood (O.10 JUg/g) of
~~ gizzard shad as a result of laboratory exposures was also
applicable for shad exposed to Endrin in a natural system.
a c f 7est organisms were collected from 2 locations, 7win Bayou
(7B), Sunflower Co., Miss, (agricultural area) and Noxubee
National Wildlife Refuge (N), Noxubee Co., Miss, (non-
agricultural area) and evaluated in laboratory bioassays.
7he 7win Bayou shrimp were more resistant.
£ c d e 7est fish were collected from 8 different locations of the
~~ Mississippi River. 7he 3-day 7Lrn values were made to
determine if a resistance gradient existed. 7he data indi-
cated that there was none.
— Muds reduced the toxicity of chlorinated hydrocarbon
insecticides to fish. Lethal quantities of pesticides enter
national waters and muds may contain sorbed pesticides in
excess of lethal quantities. Although the chemicals can be
leached with organic solvents, they were either not re-
leased in lethal amounts or slowly released in standing water.
a c Additional 7Lm data are given.
Unspecified chemical characteristics of assay water were de-
termined by standard methods. General comments were
made concerning "standardized" conditions, use of "soft"
water, and use of emulsifying agents. Additional data are
presented.
7he effect of combinations of pesticides was studied. In
general, the results reflected the extreme levels of Endrin
and 7oxaphene resistance in the resistant population.
7he results failed to indicate additive effects wherein the
combination mortality exceeded the sum of the mortalities
produced by the individual insecticides.
7he duration of exposure was important when determining
the sublethal concentrations of Endrin to fish. Data are
given as LC5Q.
Brungs and
Mount
(1967)
Ferguson, et al
(1965)
Ferguson, et al
(1966)
Ferguson, et al
(1965)
Gaufin, et al
(1965)
Gaufin, et al
(1965)
I
m
O
X
00
Ferguson and
Bingham
(1966)
Lowe
(1966)
-------
o
0
2
s
m
o Chemical
Endrin
O
I
m
o
r~
-D Endrin
D
O
2 Endrin
0
H
Endrin
CO
1
ro
Endrin
Endrin
Organism
Fathead
minnow
Oyster
Salmo
gairdneri
Lepomis
macrochirus
Ictalurus
punctatus
Pteronarcys
californicus
Baetis sp
Daphnia
pu/ex
Simocephalus
serrulatus
Ictalurus
natilis
1. me/as
Gambusia
affinis
Lepomis
cyanellus
Notemigonus
chrysoleneas
Acroneuria
pacifica
Pteronarcys
californica
Buteo
buteo
Accipiter
gen til is
Accipiter
nisus
Falco
tinnunculus
Tyto
alba
Strix
aluco
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
StudyCl) Location<2) ppm(3) or Noted <4>
BCFA - 0.47 ppb (T4A) acde
0.50 ppb (T4A)"
0.66 ppb (T4A)**
* clay
"charcoal
BCF - 0.01-1.0(364) a
BSA - 0.0005 (T2A) a
0.0003 (T2A)
0.001 (T2A)
0.001 (T2A)
0.005 (T2A)
0.020 (T2A)
0.026 (T2A)
FR Miss. (O) a
BSA & - 0.00032 (T4A) acde
CFCH 0.000035 (T30CH)
0.0024 (T4A)
0.0012 (T30CH)
FO Netherlands (O) -
Comments
The effect of suspended particles on Endrin toxicity was
studied. Presence of clay particles had no effect, while
activated charcoal reduced toxicity.
Seawater was employed in this experiment.
This paper reports acute toxicity of a number of compounds,
and discusses sub-acute mortality as well. Effects of repro-
duction and behavior are also discussed. Data presented as
EC-5Q.
This paper deals with Endrin resistance in fish. The TLm
36 hours values for yellow bullheads from a contaminated
area was 75 ppb, while the value for fish from an unsprayed
area was only 1 .25 ppb. Mosquito fish from a contaminated
area tolerated 1500 ppb of Endrin, while golden shiners
and green sunfish tolerated 1000 to 250 ppb, respectively.
Bullheads were apparently more susceptable to the poison,
but there seemed to be evidence that fish can develop a
tolerance to the toxicant.
Additional data are presented.
The results of this study show that birds of prey and fish-
eating birds found dead in the Netherlands accumulated
large amounts of different chlorinated hydrocarbon insecti-
cides. In most cases the liver had the highest concentration
of toxicant, ranging from 0.3 ppm. Most chlorinated hydro-
carbons tended to accumulate in the fat depots of the body.
In instances where mesenterial fat was analyzed the con-
centration of toxicant was found to be as high as 1 5.7 ppm.
Reference
(Year)
Brungs and
Bailey
(1966)
Butler
(1966)
Cope
(1966)
Ferguson and
Bingham
(1966)
Jensen and
Gaufin
(1966)
Koeman and
van Genderen
(1966)
^
•o
"O
m
Z
g
x
DO
-------
Endrin
Oslo
otus
Falco
pereginus
Platelea
leucorodia
Haematopus
ostralegus
Steran
sandvicensis
Sterna
hirundo
Larus
ridibundus
Somateria
mollissima
Tadorna
tadorna
Ictalurus
punctatus
Netherlands (O)
BCFCHA
(O)
to
J^ Endrin
Daphnia
carinata
BSA
0.050 (SB)
Simocephalus
serrulatus
Daphnia
pulex
BSA
0.026 (SB)
0.020 (SB)
8
m
3)
O
3
O
O
Endrin
Daphnia
magna
Simocephalus
serrulatus
Daphnia
pulex
Catfish
Buffalo fish
Perch
Bluegill
Carp
BSA
BSA
0.900 (SB)
4.90 (SB)
3.20 (SB)
(O)
The results of this study show that birds of prey and fish-
eating birds found dead in the Netherlands accumulated
large amounts of different chlorinated hydrocarbon insecti-
cides. In most cases the liver had the highest concentration
of toxicant, ranging from a trace to 3.0 ppm. Birds feeding
predominantly on Crustacea, molluses, and fish contained
significant amounts.
Koeman and
van Genderen
(1966)
Catfish blood content acutely toxic in 10 days or less—
0.25-0.3 ppb, nonlethal (exposure during 44 days)—
0.1-0.2 ppb. Endrin was not stored in blood and 0.3
ppb appeared to be the critical concentration level in
the blood.
Concentration reported is for immobilization.
Time for immobilization was 64 hr.
Data cited for 78 F, but assays were performed at varied
temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
Concentration reported is for immobilization.
Time for immobilization was 48 hr.
Data cited are for 60 F, but assays were performed at varied
temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
Concentration reported is for immobilization.
Time for immobilization was 64 hr.
Data cited are for 78 F, but assays were performed at varied
temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
Comment same as above.
Chemical analysis showed residues of <0.01 to 0.04 ppm
in catfish, <0.01 in buffalo fish, and 0.05 ppm in carp.
Perch were reported to contain 0.02 and bluegills 0.01
ppm, but this may be doubtful inasmuch as the method
of anaylsis uses was thought to have an interference from
toxaphene which had been used previously. The treated
area had been sprayed with Endrin at 0.3 Ib/acre.
Mount, et al
(1966)
Sanders and
Cope
(1966)
Sanders and
Cope
(1966)
m
O
X
CD
Sanders and
Cope
(1966)
Sanders and
Cope
(1966)
Sparr, et al
(1966)
-------
n
o
S
m
o Chemical
Endrin
o
I
m
S
o
r~
-D
3J
0
o
c
o
C/!
Endrin
Endrin
Endrin
Endrin
T5
(0
Endrin
Endrin
Organism
/Vfya
arenaria
Crassostrea
virginica
Corbicula
manillensis
Mercenaria
mercenaria
Rangia
cuneata
Fundulus
simi/is
Leiostomus
xanthurus
Oyster
Puntius
puckelli
Ictalurus
me/as
Vascular
plants
Algae
Chub
Largemouth
bass
Clam
Notemigonus
crysoleucas
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study'1 ) Location<2) ppm (3) or Noted<4)
BCFCH - (O)
BCFCH - 0.0001 (SB -
6 mo)
0.1 (SB
3 mo)
FE Galveston (O) -
Bay,
Texas
BSA - 0.001 25 (T4A) acdelm
BSA - 50ppb(T1/2A) a
FL Tule (O)
Lake,
Ore.
BSA - (0)
Comments
Results are recorded as a range of uptake of the chemical by
5 species of aquatic mollusks. An uptake or concentration
of 500-1 250X resulted.
When these fish were examined for residues at the end of
6 months, 92.0 ppb Endrin residue was found.
Oysters from the area were found to contain ^0.01 to
0.02 ppm.
Tap water was used as diluent. Toxicity data are given as
TLm's in ppm for 24, 48, 96 hr. The pH of the water
averaged 8.3. The study was conducted in India.
The principal mode of Endrin entry in the body of the fish
is by way of the gill surfaces.
The toxicity figure cited is for 10 hr.
Endrin was applied at the rate of 1 .6 Ib/acre/year. Plants
contained 1 .6 to 12. 5 ppb. Algae contained 2.0 to 22.3
ppb. Chubs contained 4.0 to 198.0 ppb. Bass contained
2.0 to 1 07.0 ppb. Clams contained 1 .7 to 90.0 ppb.
Concentrations of 0.007 to 0.01 ppb occurred in the water.
This paper deals with the resistance and susceptibility of
populations of golden shiners to Endrin. Two populations
Reference
(Year)
Butler
(1967)
Butler and
Johnson
(1967)
Casper
(1967)
Rao, et al
(1967)
Velsen and
Alderdice
(1967)
Godsil and
Johnson
(1968)
Ludke, et al
(1968)
>
TJ
m
2
D
00
Endrin
Limnephilus
rhombicus
Sialis sp
Gammarus sp
Knights
Creek,
Wise.
(O)
of golden shiners from agricultural areas possessed different
levels of resistance to Endrin. At 1.0 ppm, Endrin killed 50
susceptible golden shiners in 75 min, but only 40 of 50
resistant shiners in 40 hours. Endrin residues in whole bodies
of resistant shiners killed by Endrin were as much as 82 times
those of the susceptible shiners. It was concluded that the
use of a critical concentration in the blood for diagnosis of
Endrin-caused mortality must be based on the tolerance of
local populations.
Pesticide usage in an orchard did not significantly contaminate
the aquatic environment of this creek adjacent to the treat-
ment as determined by residue analysis.
Mowbry,et al
(1968)
-------
Endrin
Endrin
OJ
EPN miticide
(ethyl-p-nitro-
phenyl thio-
benzenephos-
phonate,
31.5 percent)
EPN-300
(25%)
EPN
m
y>
O
o
m EPN
5
O
O
§
EPN
Esox
americanus
Micropterus
salmoides
Lepomis
macrochirus
Rana
catesbeiana
Pseudemys
scripts elegans
Matrix
erythrogaster
flavigaster
Natrix
rhombifera
Ancistrodon
piscivorus
Pteronarcys
californica
(naiads)
Pteronarcella
badia
(naiads)
Claasenia
sabulosa
(naiads)
Lymnaeid
snails
Pimephales
promelas
Fathead
minnow
BSA
Daphnia
magna
Pimephales
promelas
BSA
BSA
BSA
BSA
BSA
BSA
(K) 7.1 hr (O)
(K) 12.6 hr
(K) 9.4 hr
(K) 15.6 hr
(K)65.4hr
(K) 54.0 hr
(O)
0.00025 (T4A)
0.00054 (T4A)
0.00076 (T4A)
(O)
Not given
a c d e f
0.80 (T4A)
0.25 (T4A)
acdef
0.0001 (O) a
0.2 (T4A) a d e f
Mosquitofish (Gambusia affinis) were exposed to 2 ppm
Endrin solutions for 7 days. The fish were somewhat
resistant to Endrin. These fish were then force-fed to
the 8 species of vertebrates listed. Survival time is
listed. Mortality was 100 percent in this time period
except for P. scripta elegans and A. piscivorus. For the
P. scripta elegans mortality was 72 percent in 112.8 hr
and for the A. piscivorus the mortality was 91 % in 27.1 hr.
Data reported as LC$Q at 15.5 C in 4 days.
Each test container (500-ml beaker) was filled with ditch
water. Less than 100% mortality occurred in concentra-
tions of 1:100,000.
Tests were performed in both hard and soft water. Addi-
tional tolerance limit values are given.
It was the authors opinion that pH, alkalinity and hardness,
within the usual range in natural waters, had little effect on
the toxic effect of the compounds studied. The values given
are from Henderson, Pickering, and Tarzwell, "The Relative
Toxicity of Ten Chlorinated Hydrocarbon Insecticides to
Four Species of Fish". It is interesting that the different
tables from the above book (as reported in this paper) report
widely different values for the same compounds.
This experiment was performed in hard water.
The indicated concentration immobilized Daphnia in 50
hours.
Concentrations were based on percent active ingredient.
Rosato and
Ferguson
(1968)
Sanders and
Cope
(1968)
Batte, et a I
(1951)
Henderson and
Pickering
(1958)
Tarzwell
(1959)
m
O
X
CD
Anderson
(1960)
Henderson, et al
(1959)
-------
8
s
m
o Chemical
r EPN
0
m
2
O
r~
•D
Q
Q t r 1\J
C
5
Cfl
EPN
0
£ EPN-300,
wettable
powder
(25 percent)
EPN
(tech,
100 percent)
EPN
EPN
Organism
Pimephales
promelas
Lepomis
macrochirus
Micropterus
salmoides
Notemigonus
cryso/eucas
Carassius
auratus
Micropterus
salmoides
Pimephales
promelas
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Chaoborus
astictopus
Bluegill
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study'1) Location'2) ppm'3)
BSA - 0.20 (T4A)
BSA - 0.1 (0)
0.1 (0)
0.1 (0)
0.1 (0)
BSA - 0.5 (O)
0.5 (O)
BSA - 1.1 (T4A)
0.44 (T4A)
2.3 (T4A)
BSA - 0.25 (T4A)
0.10(T4A)
0.45 (T4A)
0.032 (T4A)
BSA - 0.0036 (T1 A)
BSA - 0.1 (T4A)
Experimental
Variables
Controlled
or Noted'*) Comments
a Bioassay investigations of the new insecticides indicate that
in general the organic phosphorus compounds are not as
toxic to fish as are the chlorinated hydrocarbons. The
toxicity of most of these materials was not significantly
influenced by water quality. Therefore it is to be expected
that the toxicity of these materials will not differ signifi-
cantly in different streams.
a c d f This paper reports the effect of insecticides in reducing the
anticholinesterase in a fish brain within 2-8 hours. The
inhibition of the enzyme was a function of the concentra-
tion of the insecticide, extent of exposure, and specific
chemical nature of the compound.
— The degree of reaction to the cholinesterase-inhibiting
insecticides is not only a function of time and concentra-
tion, but also of chemical and biological species. This
paper reports many analyses of brain cholinesterase activity
which is expressed as percentage of normal. The data are
reported as UT§o which was the time required for 0.5 ppm
of the chemical to kill 50 percent of the fish. For bass the
LTso was 9 hr 30 min and for fatheads 72 hr.
a c d e Soft water primarily was the test medium. TLm's reported
for 24, 48, and 96 hr. Acetone or alcohol used as solvent
or carrier in most cases.
a c d e Comment same as above.
a Toxicity value given is for the fourth instar larvae.
a Assays were conducted in soft water at 25 C. Decrease
Reference
(Year)
Tarzwell
(1959)
Weiss
(1959)
Weiss
(1961)
Pickering, et al
(1962)
Pickering, et al
(1962)
Hazeltine
(1963)
Weiss
^
2
m
z
o
CO
in brain cholinesterase was measured in fish exposed
to the toxicant.
(1964)
-------
EPN
Eptam
N)
Erythromycin
thiocyanate
Carassius
auratus
Lepomis
macrochirus
Notemigonus
crysoleucas
BSCH
Crassostrea
virginica
Penaeus
setiferus
Mugil
cephalus
Phytoplankton
BCFA & BSA
Salmo
gairdnerii
Erythromycin
thiocyanate
8
g
m
3)
O
>
i-
o
X Essolvene
m
2
>
^
3
O
D
Sa/mo
gairdnerii
Salmo
trutta
Salvelinus
fontinalis
Salvelinus
namaycush
Ictalurus
punctatus
Lepomis
macrochirus
Pandalus
montagni
Crangon
crangon
Carcinus
maenas
Cardium
edule
BSA
BSA
BSA
10.0 (O)"
1.0 (O)**
0.05 (O)«**
1.0(0)'
0.05 (O)***
10.0(0)*
1.0(O)**
* response,
15 days
** no re-
sponse, 15
days
***no re-
sponse, 30
days
5.0 (0.43%)
0.63 (O)
20.0(10%T2A)
a c d e
(O)
100 (NTE)
a c e i p
af
8.6 (T2A)
9.6 (T2A)
17.5 (T2A)
63.0 (T2A)
Toxicity was determined by measuring acetylcholin-
esterase activity in the brains of fish. Concentrations
are given in ppb as either response or not response in
15 or 30 days.
Seawater was pumped continuously into test aquaria.
Salinity, temperature, and plankton fluctuated with tide,
and ambient weather conditions. Some bioassays with
fish were static. Toxicity was reported for the following:
Oyster — 96-hr ECgrj — Cone, which decreased
shell growth.
Shrimp — 48-hr ECgg — Cone, which killed or
paralyzed 50% of test animals.
Fish - 48-hr ECsg — Cone, which killed
50%.
Phytoplankton — Percent decrease of CO2 fixation to a
4-hr exposure at 1.0 ppm chemical
concentration.
A dosage of 500 milligrams of erythromycin thiocyanate
per kilogram per day (five times the usual therapeutic
level) was required to produce overt symptoms of toxicity
in rainbow trout.
Variance and the 95-percent confidence interval (C.I.) were
also determined.
Experiments were conducted in tanks holding 10 liters
of sea water at 15 C.
It was shown that the toxicity of this solvent emulsifier
decreased with time due to evaporation of the solvent.
Essolvene at a concentration of 10 ppm killed 100% of
Crangon crangon larvae in 3 hr; at 33.3 ppm it killed
100% of Carcinus maenas in 3 hr.
Weiss and
Gakstatter
(1964)
Butler
(1965)
Warren
(1963)
Willford
(1966)
m
O
X
a
Portmann and
Connor
(1968)
C/)
-------
o
o
2
S
m
o Chemical
*"" Eitron
I (2.4-5T)
m
O Esteron 99
r-
5 Esteron 99
O
O
C
H Esteron 99
M (EC)
Esteron 99
(2, 4-D)
4
;
)
Esteron 99
Ethion
Ethion
(tech)
Ethion
Ethyl
carbo-
phenothion
Ethyl
guthion
(EC2)
Organism
Pan tederia
cor data
Lepomis
macrochirus
Lepomis
sunf ish
Lepomis
macrochirus
Crassostrea
virgin ica
Penaeus
aztecus
Leiostomus
xanthurus
Phytoplankton
Pteronarcys sp
(nymphs)
Cyprinodon
variegatus
(juvenile)
Pimephales
promelas
Lepomis
macrochirus
Lebistes
reticulatus
Pteronarcys
californica
(naiads)
Chaoborus
astictopus
Gambusia
affinis
Rana
catesbeiana
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study C" Location (2) ppm(3)
FL Fla. (O)
BSA - 1,200(T18hr)
FL Okla. (O)
BSA - 700 (T1A)
BCFA & - 0.055 (O)
BSA
0.55 (0)
1.5 (T2SA)
BSA - 1 .6 (T4A)
BSA - 0.064 (0)
BSA - 2.4 (T4A)
0.13IT4A)
0.13IT4A)
BSA - 0.0028 (T4A)
BSA - 0.044 (T1 A)
FL Ponds in (O)
III.
Experimental
Variables
Controlled
or NotedW Comments
— At 6.4 Ib/acre, 80 percent control of pickerel weed was
obtained.
a The experiment was conducted at 65 F Fish were
2 in. long.
— Three ponds were partitioned with polyvinyl chloride
sheeting to provide 6 test spaces for fish. Mortality of
the fish was 19% in the 10-ppm pond in the first week.
a The experiment was conducted at 75 F. Fish weighed
0.6 g.
— Seawater was pumped continuously into test aquaria.
Salinity, temperature, and plankton fluctuated with tide.
and ambient weather conditions. Some bioassays with
fish were static. Toxicity was reported for the following:
Oyster — 96-hr ECgo ~ Cone, which decreased
shell growth.
Shrimp — 48-hr ECso — Cone, which killed or
paralyzed 50% of test animals.
Fish — 48-hr EC5Q — Cone, which killed
50%.
Phytoplankton — Percent decrease of CO2 fixation to a
4-hr exposure at 1.0 ppm chemical
concentration.
a Experiments were all conducted at 60 F in 1964. The
values were listed as LC5Q.
a Water temperature was 12 C. The figure reported is a
48-hr EC50.
a c d e f The toxicity of this substance was not influenced by the
quality of the water (pH, hardness, alkalinity).
a c d e f Data reported as LCsg at 1 5.5 C in 4 days.
a Toxicity value given is for the fourth instar larvae.
— When applied at 0.01 and 0.025 pound per acre active
ingredient, 88 and 100 percent fish mortality occurred
respectively in 1 day.
No bullfrog mortality occurred at 0.8 pound, per acre
Reference
(Year)
Copeland and
Woods
(1959)
Cope
(1963)
Cope
(1963)
Cope
(1963)
Butler
(1965)
Cope
(1965)
Butler
(1965)
Pickering and
Henderson
(1966)
Sanders and
Cope
(1968)
Hazel tine
(1963)
Mulla, et al
(1963)
1»
•o
m
Z
o
CD
in 1 day-
-------
Ethyl
parathion
Ethyl
parathion
Ethyl
parathion
Ethyl
guthion
Ethyl
guthion.
(tech)
Ethyl
guthion
Ethyl
guthion
Chaoborus
astictopus
Lepomis
macrochirus
Pteronarcys sp
(nymphs)
Simocephalus
serrulatus
Daphnia
pulex
Daphnia
carinata
Daphnia
magna
Pteronarcys sp
(nymphs)
Rainbow
trout
Sal mo
gairdneri
Lepomis
macrochirus
Pteronarcys
californica
Daphnia
pulex
Simocephalus
serrulatus
Simocephalus
serrulatus
Daphnia
pulex
BSA
BSA
BSA
BSA
BSA
BSA
BSA
8 Ethv'
2 guthion
5 EC4
m
o
>
r
o
m
S
Micropterus
sal mo ides
Cyprinus
carpio
BSA
(O)
0.021 (T9A)
0.0051 (T4A)
0.00037 (SB)
0.00060 (SB)
0.0005 (SB)
0.0008 (SB)
0.002 (T4A)
0.019 (T4A)
0.023 (T2A)
0.002 (T2A)
0.008 (T2A)
0.003 (T2A)
0.004 (T2A)
0.0042 (SB)
0.0032 (SB)
0.05 (O)
0.10 (O)
0.50 (K1)
0.01 (K1)
0.05 (K 5 hr)
0.10 (K 5 hr)
Tests were run on bluegill sunfish, C. astictopus first instar
larvae, and fourth instar larvae, results for larvae were as
follows:
Fourth instar 0.017 (T1A)
First instar 0.0018 (T1A)
Experiments were all conducted at 60 F in 1964. The
values were listed as LC5Q.
Concentration reported is for immobilization.
Time for immobilization was 64 hr.
Data cited are for 78 F, but assays were performed at
varied temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
Experiments were all conducted at 60 F in 1964. The
values were listed as LC5Q.
The values reported are given as
Hazeltine
(1963)
Cope
(1965)
Sanders and
Cope
(1966)
This paper reports acute toxicity of a number of compounds,
and discusses sub-acute mortality as well. Effects on repro-
duction and behavior are also discussed. Data presented as
Cope
(1965)
Cope
(1965)
Cope
(1966)
m
Z
D
X
00
Concentration reported is for immobilization.
Time for immobilization was 48 hr.
Data cited are for 60 F, but assays were performed at
varied temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
At 0.05 ppm, 25 percent mortality occurred in 1 day.
At 0.10 ppm, 90 percent mortality occurred in 1 day.
For bass:
Experiments were carried out in fiber glass tubs filled
with well water. Fish weights ranged from 2 to 6 pounds.
For carp:
Experiments were carried out in plastic tubs lined with
saran plastic. Fish weights averaged 217 grams.
Sanders and
Cope
(1966)
Mulla, et al
(1967)
-o
3)
O
o
c
-------
COMMERCE
>*
r-
I
m
s
0
r~
•o
3)
O
O
1
C/J
«P
K>
00
Chemical
Exalgae
F-98
Fairfield 279
Fairfield
OT60-6
Fenac
(sodium salt)
Fenac
Fenac
(sodium salt)
Fenac
acid
(tech)
Fenac
(sodium
salt, WP)
Fenac
(acid)
Fenac, Na
Fenac
(Na salt)
Organism
Chlorella
pyrenoidsa
Onchorynchus
tshawytscha
Sal mo
gairdneri
Salmo
gairdneri
Redear
sunfish
Salmo
gairdneri
Lepomis
macrochirus
Pteronarcys sp
(nymphs)
Bluegill
Bluegill
Pteronarcys sp
(nymphs)
Salmo
gairdneri
Lepomis
macrochirus
Pteronarcys
californica
Daphnia
pulex
Simocephalus
serrulatus
Daphnia
magna
Rainbow
trout
Bluegill
Toxicity,
Bioassay Active
or Field Field Ingredient,
StudyCl) Location<2) ppm(3)
L - 5 (AC 1/2 hr)
BSA - 0.08 (T1 A)
BSA - 360 (T1 A)
BSA - 100 (T1A)
BSA - (O)
10,000 (T1A)
7,500 (T2A)
BSA - 22.5 (T2A) L
15.0 (T2A) G
BSA - 47 (T4A)
BSA - 41 (T4A)
BSA - 14 (T4A)
BSA - 56 (T4A)
BSA - 7.500 (T2A)
19.000 (T2A)
80.000 (T2A)
4.500 (T2A)
6,600 (T2A)
BSA - 100(0)
7.5 (0)
19 (O)
Experimental
Variables
Controlled
or Noted'4) Comments
— Describes a bioassay method to differentiate between an
algicide (AC) and an algistat (AS). The treated culture
was subcultured as time progressed. Allen's medium was
used.
a c d e Concentrations were based on percent active ingredient.
a The experiment was conducted at 55 F Fish weighed
0.5 g.
a The experiments were conducted at 55 F. Fish weighed
0.8 g.
a The experiment was conducted at 75 F. Fish weighed
3g.
No mortality was noted with concentrations of 12,000
mg/1 at 48 hr.
The experiments were conducted at 65 F Fish weighed
0.6 g.
a c d e g Toxicity data for 24 and 48 hours are presented for liquid
(L) and granular (G) formulations. Various commercial
formulations were tested. The liquid formulations were
almost invariably more toxic than the granular ones.
£ Experiments were all conducted at 60 F in 1964. The
values were listed as LCsfj.
a This is an estimated LC§o value at temperatures from 55 to
75 F.
a Comment same as above.
£ Experiments were all conducted at 60 F in 1964. The
values were listed as UCsrj.
a This paper reports acute toxicity of a number of compounds.
and discusses subacute mortality as well. Effects on repro-
duction and behavior are also discussed. Data presented as
ECso-
a c d i q Toxicity, in terms of median immobilization concentration
(ICgg), is presented for Daphnia; median lethal concentra-
tion (LCsrj) for rainbow trout and bluegill are reported.
Reference
(Year)
Fitzgerald and
Faust
(1963)
Bond, et al
(1960)
Cope
(1963)
Cope
(1963)
Cope
(1963)
Hughes and
Davis
(1965)
Cope
(1965)
Cope
(1965)
Cope
(1965)
Cope
(1965)
Cope
(1966)
Crosby and
Tucker
(1966)
•p
*o
•o
m
z
g
DO
-------
Fenac
(sodium
salt)
Fenac (sodium
salt, WP)
Fenac
Fenac
Fenac
(Na salt)
"-* Fenthion
Fenthion
(Baytex)
S
m
3D
o
o
o
-o
3D
O
o
Fenthion
Simocephalus
serrulatus
Daphnia
pulex
Rainbow
trout
Bluegill
Lepomis
macmchirus
(eggs)
Erimyzon
sucetta
(eggs)
L. macmchirus
(fry)
Pteronarcys
californica
(naiads)
Pteronarcys
californica
(naiads)
Prosimulum spp
Cnephia spp
Simulium spp
(larvae)
Micropterus
salmoides
Lepomis
macrochirus
Gambusia
affinis
Lebistes
reticulatus
Palomonetes
patudosus
Hyalella
azteca
Plankton
(Euglena,
Coleops)
Rotifers
Micropterus
salmoides
BSA
BSA
BSA
BSA
UCFA
BSA
BSA
6.6 (SB)
4.5 (SB)
7.5 (T2A)
19.0 (T2A)
20/5(O)
20 (NTE)
50 (S)
0.06 (T4A)
0.055 (T4A)
0.4 (O)
1.75 (L1A)
1.75 (L1A)
2.0 (L1A)
1.75 (L1A)
0.011 (U1A)
0.016 (L1 A)
1.0(K2)
1.0 (K2)
5.0 (K 3 hr)
Concentration reported is for immobilization.
Time for immobilization was 64 hr.
Data cited are for 78 F, but assays were performed at
varied temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
Data are given as
— Fertilized fish eggs of indicated species were placed in
1 liter of test solution and allowed to hatch. Toxicity
data are presented as concentration in ppm/number of
days survival. Maximum length of test was 8 days. No
food was added. Small bluegill were tested to find the
highest concentration of chemical which did not cause
death in 12 days (S).
£_£.dj!_t Data reported as LC5Q at 15.5 C in 4 days.
a c d e f Comment same as above.
Stones heavily populated with wild larvae were placed in
troughs of running water containing the toxicant. When
the larvae became detached from the rocks and floated
away, they were assumed to have undergone lethal intoxi-
cation. The larvae were exposed to the toxicant for 5
minutes, then in clean water for 24 hours. At that time
the number detached amounted to 89 percent.
Abate was toxic to fish at a dosage rate necessary to con-
trol the larvae of the chironomid midge.
Experiments were carried out in plastic tubs lined with
saran plastic. Fish weights averaged 217 grams.
Sanders and
Cope
(1966)
Bohmont
(1967)
Hiltibran
(1967)
Sanders and
Cope
(1968)
Sanders and
Cope
(1968)
Jamnback and
Frempong-
Boadu
(1966)
Von Windeguth
and Patterson
(1966)
m
O
X
CD
Mulla, et al
(1967)
-------
COMMERCE
r
r~
o
I
m
5
O
f—
T3
33
Q
0
C
3
CD
i
U>
O
Chemical
Fenthjon
Fenuron
Fenuron
Fenuron
Fenuron
Fenuron
(25 percent
pellet)
Fenuron-TCA
(tech)
Fenuron-TCA
(3lb/gal)
Organism
Pteronarcys
californica
(naiads)
Protococcus sp
Chlorella sp
Dunaliella
euchlora
Phaeodactylum
tricornutum
Monochrysis
lutheri
Leiostomus
xanthurus
(juvenile)
Penaeus
aztecus
Crassostrea
virginica
Penaeus
aztecus
Leiostomus
xanthurus
Phytoplankton
Lepomis
macrochinis
Lepomis
macrochinis
Lepomis
macrochinis
Micropterus
salmoides
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study''' Location'2) ppm (3)
BSA - 0.0045 (T4A)
BSA - 29.0 (K)
2.9 (NG)
2.9 (NG)
2.9 (NG)
2.9 (K)
BSA - (O)
L - (0)
BCFA & - 2.0 (NTE)
BSA
2.0 (0, 10%)
1.0 (NTE)
41% (O)
BSA - 53.0 (T4A)
BSA - 5.3 (T4A)
BSA - 4.8-6.5 (T4A)
7.4 (T4A)
Experimental
Variables
Controlled
or NotedW Comments
a c d e f Data reported as LC^Q at 1 5.5 C in 4 days.
a This paper concerns the growth of pure cultures of marine
plankton in the presence of toxicants. Results were ex-
pressed as the ratio of optical density of growth in the
presence of toxicants to optical density in the basal medium
with no added toxicants. NG = no growth, but the organ-
isms were viable.
a Water temperature was 25 C. Fish showed irritation at
1.0 ppm.
a Toxicant chemicals were evaluated in sea water at tempera-
tures averaging about 28 C. The values are for 24-hr ECgo
or enough to cause loss of equilibrium or mortality. A
concentration of 1.0 ppm caused 10 percent mortality.
— Seawater was pumped continuously into test aquaria.
Salinity, temperature, and plankton fluctuated with tide,
and ambient weather conditions. Some bioassays with fish
were static. Toxicity was reported for the following:
Oyster — 96-hr ECso — Cone, which decreased
shell growth.
Shrimp — 48-hr ECgo — Cone, which killed or
paralyzed 50% of test animals.
Fish — 48-hr EC$Q — Cone, which killed
50%.
Phytoplankton — Percent decrease of CO2 fixation to a
4-hr exposure at 1.0 ppm chemical
concentration.
— Laboratory bioassays indicated that toxicity of the different
formulations evaluated in this varied greatly with the fish
used. Mortality data are expressed as BC-\rj, ECso, etc.
— Comment same as above,
— Comment same as above.
Reference
(Year)
Sanders and
Cope
(1968)
Ukeles
(1962)
Butler
(1967)
Butler
(1965)
Butler
(1965)
Walker
(1965)
Walker
(1965)
Walker
(1965)
m
g
X
00
-------
Fenuron
TCA
Fermate
Fermate
Fermate
,L Folidol
m
x
r>
o
m
2
5
T)
3)
o
o
I
Folpet
[N-(trichloro-
methylthio)-
phythalimide]
Folithion or
Sumithion
(=fenitrothion)
Furron
Furazolidone
Lepomis
macrochirus
L. cyanellus
Micropterus
dolomieui
Erimyzon
sucetta
L. macrochirus
(fry)
Channel
catfish
(fingerlings)
Sa/velinus
fontinalis x
Salmo
trutta
Catostomus
commersoni
Micropterus
salmoides
Pimephales
promelas
Lepomis
Tilapia
massambica
Gambusia
affinis
Brachydanio
Prosimulum spp
Cnephia spp
Simulium spp
(larvae)
Water lettuce
Salmo
trutta
Salmo
gairdnerii
Salvelinus
fontinalis
BSA
FPCH
N.Y.
BSA
BSA
BSA
LCFA
FL
BCH
10 (NTE)
10(NTE)
10(NTE)
10 (NTE)
20 (S)
12.6
(K 27 hr A)
0.5 (S23)
0.5 (S23)
0.5 (S23)
3.1 (T4A)
0.6 (T2A)
0.1 (T2A)
1(0)
0.4 (O)
Lakes in (O)
Fla.
(O)
Fertilized fish eggs of indicated species were placed in
1 liter of test solution and allowed to hatch. Toxicity
data are presented as concentration in ppm/number of
days survival. Maximum length of test was 8 days. No
food was added. Small bluegill were tested to find the
highest concentration of chemical which did not cause
death in 12 days (S).
a Tap water was used. Considerable additional data are
presented.
a c d Conventional farm ponds were used having an average
surface area of 0.3 acre and a maximum depth of
7-9 ft. Toxicity (in ppm) to fish as maximum safe
concentration (S) for 23 days was determined. Con-
centration of 0.5 ppm was required to control algae.
a c d e f The toxicity of this substance was influenced by the
quality of the water (pH, hardness, alkalinity). The
TLm was lower in hard water.
a c d e f p The test animals were conditioned for 48 hours prior to
use.
At 1 ppm all larvae were killed within 48 min. The TI-50
was 34 min and LD5Q was 0.71 ppm.
Stones heavily populated with wild larvae were placed in
troughs of running water containing the toxicant. When
the larvae became detached from the rocks and floated
away, they were assumed to have undergone lethal intoxi-
cation. The larvae were exposed to the toxicant for 5
minutes, then in clean water for 24 hours. At that time
the number detached amounted to 65 percent.
Application rates of 4 to 5 Ib/acre controlled water lettuce.
The chemical was nontoxic to brown, rainbow, and brook
trout at levels up to 500 mg per kg of body weight per day
when force-fed for 14 consecutive days. Therapeutic
levels for control of furnuculosis appear to be as low as
or lower than 10 milligrams of chemical per kilogram of
body weight per day for 14 days. To have complete con-
trol of the disease, a dosage of at least 75 milligrams of
furazolidone per kilogram of body weight was given.
Hiltibran
(1967)
Clemens and
Sneed
(1959)
Eipper
(1959)
Pickering and
Henderson
(1966)
Sreenivasan and
Swaminathan
(1967)
Abedi and
Turton
(1968)
Jamnback and
Frempong-
Boadu
(1966)
Phillippy
(1961)
Post and
Keiss
(1962)
O
X
09
-------
COMMERCE
s>
r
o
i
m
S
O
r-
-o
3)
O
O
C
3
C/5
CO
,L
OJ
K)
Chemical
Furoxone
G-27365
(EC2)
G-28029
(EC2)
G-30493
(EC2)
G- 30494
(EC2)
GCM05 (zinc
nicotinyl
fluosilicate)
GC-2131
(1-chloro-2,4-
phenylene-bis-
(0,0-diethyl phos-
phorothiolate]
GC-3582
(EC4)
Organism
Salvelinus
fontinalis
Gambusia
affinis
Rana
catesbeiana
Gambusia
affinis
Rana
castesbeiana
Gambusia
affinis
Bufo
boreas
Scophiopus
hammondi
Gambusia
affinis
Bufo
boreas
Scophiopus
hammondi
Australorbis
glabratus
Australorbis
glabratus
Gambusia
affinis
Rana
catesbeiana
Toxicity,
Bioassay Active
or Field Field Ingredient,
StudyCI) Location'2* ppm(3)
BSA - (O)
FL Ponds (O)
in III.
FL Ponds (O)
in III.
FL Ponds (O)
in III.
(0)
(0)
FL Ponds (O)
in III.
(0)
(0)
BSA and Puerto Rico Failed
FL
BSA and Puerto Rico Failed
FL
FL Ponds (O)
in III.
Experimental
Variables
Controlled
or Noted^' Comments
a e Aeromonas salmonicida is the bacterium causing furunculosis
in fish. The toxicity level of this chemical indicates that
this drug could be used as a therapeutic measure for
A. salmonicide. 500 milligrams per kilogram per day used
for 15 successive days showed no pathological effect on
brook trout.
— When applied at 0.2 and 0.4 pound per acre active ingredient,
8 and 100 percent fish mortality occurred respectively in
1 day.
No bullfrog mortality occurred at 0.8 pound per acre in
1 day.
— When applied at 1 .6 pounds per acre active ingredient, 6 per-
cent fish mortality occurred in 1 day.
No bullfrog mortality occurred at 1 .6 pounds per acre in
1 day.
— When applied at 0.8 pound per acre active ingredient, 2 per-
cent fish mortality occurred in 2 days.
No toad mortality occurred at 0.8 pound per acre in 1 day.
— When applied at 0.8 pound per acre active ingredient.
100 percent fish mortality occurred in 1 day.
When applied at 0.4 pound per acre, 5 percent toad mortal-
ity occurred in 1 day.
c Seven of the tested compounds failed to meet acceptability
criteria — that is, complete kill after 6-hr exposure to
10 ppm. They were not used in field tests. Field tests
showed WL 8008 to be highly effective.
c Comment same as above.
— When applied at 0.025 and 0.05 pound per acre active in-
gredient, 4 and 80 percent fish mortality occurred in 1 day.
When applied at 1.6 pounds per acre, 100 percent bullfrog
mortality occurred in 1 day.
Reference
(Year)
Post
(1959)
Mulla, et al
(1963)
Mulla, et al
(1963)
Mulla, et al
(1963)
Mulla, et al
(1963)
Mulla, et al
(1963)
Seiffer and
Schoof
(1968)
Seiffer and
Schoof
(1968)
Mulla, et al
(1963)
^
4g
•o
m
z
O
X
00
-------
GC-3582
(EC4)
GC-3583
(EC4)
GC-3707
(tech)
GC-3707
(EC)
GC-3707
(WP)
GC-4072
(50 percent
EC)
GC-4072
(tech)
GC-4072
(EC4)
GC-9160
(EC2)
GS-12968
(EC4)
GS-13005
g (EC4)
S
oo
OJ
m
3
o
m
•a
O
O
c
GS-13005
Gamlen CW
Microp terus
sal mo ides
Cyprinus
carpio
Micropterus
salmoides
Lepomis
macrochirus
Salmo
gairdneri
Salmo
gairdneri
Gambusia
affinis
Lepomis
macrochirus
Micropterus
salmoides
Gambusia
affinis
Tadpole
shrimp
Gambusia
affinis
Gambusia
affinis
ftana
catesbeiana
Prosimulum spp
Cnephia spp
Simulium spp
(larvae)
Panda/us
montagni
Cardium
edule
BSA
BSA
BSA
BSA
BSA
FL
BSA
BSA
FL
FL
FL
LCFA
Ponds
Bakers-
field,
Cal.
Cal.
Cal.
Cal.
BSA
0.05 (O)
0.10 (K1)
0.005 (K1)
0.01 (K5hr)
0.05 (K3hr)
0.10 (O)
0.50 (K1)
600 (T1A)
170 (T1A)
95 (T1A)
0.2 (K1)
0.8 (K1)
3IT1A)
0.50 (O)
1.00(0)
(O)
(O)
(O)
0.4 (K1)
(O)
0.4 (0)
14.6 (O)
69.5(0)
a c
a e
At 0.05 ppm, 60 percent mortality occurred in 1 day.
For bass:
Experiments were carried out in fiber glass tubs filled with
well water. Fish weights ranged from 2 to 6 pounds.
For carp:
Experiments were carried out in plastic tubs lined with
saran plastic. Fish weights averaged 217 grams.
No mortality occurred at 0.10 ppm in 4 days. Experiments
were carried out in fiber glass tubs filled with well water.
Fish weights ranged from 2 to 6 pounds.
The experiment was conducted at 75 F.
The experiment was conducted at 65 F.
The experiment was conducted at 65 F.
Toxicity values indicate application rates in Ib/acre. The ex-
periments were conducted in cages placed in the ponds.
The experiments were conducted at 75 F.
At 0.50 ppm, 6 percent mortality occurred in 1 day.
At 1.00 ppm, 66 percent mortality occurred in 1 day.
At 1.50 ppm, 100 percent mortality occurred in 2 days.
Experiments were carried out in fiber glass tubs filled with
well water. Fish weights ranged from 2 to 6 pounds.
At an application rate of 2.0 Ib/acre, 62% mortality of the
fish occurred in 24 hours. Tadpole shrimp survived this
treatment.
At a concentration of 0.4 Ib/acre, 72% mortality of the
fish occurred in 24 hours.
Toxicity value in Ib/acre. No mortality in tadpoles of
Ft. catesbeiana occurred during an exposure period of
one week.
Stones heavily populated with wild larvae were placed in
troughs of running water containing the toxicant. When
the larvae became detached from the rocks and floated
away, they were assumed to have undergone lethal intoxi-
cation. The larvae were exposed to the toxicant for
5 minutes, then in clean water for 24 hours.
Experiments were conducted in tanks holding 10 liters of
sea water at 15 C.
It was shown that the toxicity of this solvent emulsifier de-
creased with time due to evaporation of the solvent.
Gamlen CW at a concentration of 33.3 ppm killed 95% of
Crangon crangon larvae in 3 hr.
Mulla, et al
(1967)
Mulla, etal
(1967)
Cope
(1963)
Cope
(1963)
Cope
(1963)
Mulla and
Isaak
(1961)
Cope
(1963)
Mulla, etal
(1967)
Mulla
(1966)
Mulla
(1966)
Mulla
(1966)
Jamnback and
Frempong-
Boadu
(1966)
Portmann and
Connor
(1968)
m
O
X
0
-------
o
o
m
o Chemical
f~ Gamlen D
O
I
m
S
o
i-
3) Gamlen OSR
O
O
C
_l
en
Gammexane
powder
(larvicide)
Gamosol
solvent "D"
3 Garlon
j
k
Guthion
(25% WP)
Organism
Panda/us
montagni
Crangon
crangon
Card/um
edule
Pandalus
montagni
Crangon
crangon
Carcinus
maenas
Cardium
edule
Tilapia
melanopleura
Daphnia
magna
Myriophyllum
heterophyllum
Utricularia sp
Green
sunfish
Orange spotted
sunfish
White
crappie
Bluegill
Largemouth
bass
Gizzard
shad
Freshwater
drum
Gar
Carp
Longnose
gar
Golden
shiners
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study(1> Location(2) ppm(3)
BSA - 11.5IT2A)
9,6 (T2A)
38.8 (T2A)
BSA - 12.5(T2A)
8.8 (T2A)
20.4 (T2A)
15.8(T2A)
FLCH Tanganyika 1 Ib (0% K)
BSA - 13.7 (T1A)
2.9 (T2A)
1 .5 (T3A)
FL Farm (O)
ponds
in Ga.
FL Ponds 0.25-1.8(0)
in
Ark.
Experimental
Variables
Controlled
or NotedW Comments
a e Experiments were conducted in tanks holding 10 liters of sea
~ water at 15 C.
It was shown that the toxicity of this solvent emulsifier de-
creased with time due to evaporation of the solvent.
Gamlen D at a concentration of 33.3 ppm killed 100% of
Crangon crangon larvae in .1 hr.
a e Comments same as above except that Gamien OSR at a
concentration of 10 ppm killed 95% of Crangon crangon
larvae in 3 hr.
— Trial periods were for 20 weeks. Sublethal effects such as
impaired breeding, retarded growth, or altered taste were
not detected. Dosages are given as Ib/acre of surface water.
e Crude oil plus emulsifier had the following values.
24.4 (T1A)
10.7 (T2A)
9.1 (T3A)
— Garlon was developed as an overall herbicide containing
4 Ib/gal dalapon and 1/2 Ib/gal Silvex acid. It has given in-
dications of control of several species of weeds, such as
Myriophyllum heterophyllum and Utricularia sp.
However, present results are inconclusive and this herbicide
warrants further investigation and experimentation.
d g Catfish were more tolerant to Guthion than the other species
of fish tested. All other species of fish were quickly affected
by applications of 1 .0 ppm. Field studies were conducted in
ponds ranging from 0.25-1 .8 acre-feet in volume. Survival
values were determined by draining the ponds whenever pos-
sible. Residue studies indicated that the chemical disappeared
from the water in less than 2 weeks and that the chemical is
no longer detectable in catfish flesh after 6 weeks. Cladocera
and rotifers were not eliminated from the treated ponds and.
in many field collections, were more numerous than in un-
treated ponds.
Reference
(Year)
Portmann and
Connor
(1968)
Portmann and
Connor
(1968)
Webbe and
Shute
(1959)
Dowden
(1962)
Thomaston, et al
(1959)
Surber
(1943)
^
Eg
•o
m
•z.
o
X
-------
Guthion
Guthion
Guthion
Guthion
Guthion
8
m
O Guthion
O
m
2
5
Guthion
O
Fathead
minnows
Bigmouth
buffalo
Black
bullheads
Channel
catfish
Warmouth
Pimephales
promelas
Lepomis
macrochirus
Gambusia
affinis
Pimephales
promelas
Lepomis
macrochirus
Lepomis
macrochirus
Micropterus
salmoides
Notemigonus
crysoleucas
Carassius
auratus
Oncorhynchus
kisutch
Oncorhynchus
tshawytscha
Salmo
gairdnerii
Gasterosteus
aculeatus
Micropterus
salmoides
Pimephales
promelas
Cyprinodon
variegatus
BSA
BSA
BSA
BSA
BSA
BSA
BCFCH
0.09 (T4A)
0.005 (T4A)
0.05 (K 53%)
0.093 (T4A)
0.0052 (T4A)
0.1 (O)
0.1 (O)
0.1 (O)
0.1 (O)
4.2 (T4A)
4.3 (T4A)
3.2 (T4A)
12.1 (T4A)
0.5 (O)
0.5 (O)
a d e f Concentrations were based on percent active ingredient.
a Chemicals were dissolved in acetone, and tests were run in
triplicate. Toxicity is given as average percent fish killed
in 24 hr.
a Bioassay investigations of the new insecticides indicate that
in general the organic phosphorus compounds are not as
toxic to fish as are the chlorinated hydrocarbons. The
toxicity of most of these materials was not significantly
influenced by water quality. Therefore it is to be expected
that the toxicity of these materials will not differ signifi-
cantly in different streams.
a c d f This paper reports the effect of insecticides in reducing the
anticholinesterase in a fish brain within 2-8 hours. The
inhibition of the enzyme was a function of the concentra-
tion of the insecticide, extent of exposure, and specific
chemical nature of the compound.
a c d e Chemical dissolved in acetone. TLm expressed in ppb.
0.01 (SB1)
The degree of reaction to the cholinesterase-inhibiting insecti-
cides is not only a function of time and concentration, but
also of chemical and biological species. This paper reports
many analyses of brain cholinesterase activity which is ex-
pressed as percentage of normal. The data are reported as
LTso which was the time required for 0.5 ppm of the chem-
ical to kill 50 percent of the fish. For bass the LTso was
40 min and for the fathead 40 min.
Little or no information was given about test procedures and
further results.
Henderson, et al
(1959)
Le wall en
(1959)
Tarzwell
(1959)
Weiss
(1959)
I
m
Z
o
X
00
Katz
(1961)
Weiss
(1961)
Das and
Needham
(1961)
-------
COMMERCIAI
O
I
m
s
O
1-
-o
o
D
o
H
C/l
5!
w
c\
Chemical
Guthion
(tech,
90 percent)
Guthion
(EC1.5)
Guthion
Guthion
Guthion
Guthion
Guthion
Organism
Carassius
auratus
Lebistes
reticulatus
Gambusia
affinis
Bufo
boreas
Scophiopus
hammondi
Carassius
auratus
Lepomis
macrochirus
Notemigonus
crysoleucas
Gammarus
lacustris
Bluegill
Acroneuria
pacifica
Ephemeral/a
grandis
Gammarus
lacustris
Pteronarcys
californica
Pteronarcys
californica
Acroneuria
pacifica
Ephemerella
grandis
Gammarus
lacustris
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study'1) Location'2' ppm'3) or Noted'4)
BSA - 1 .4 (T4A) a c d e
0.12 (T4A)
FL Ponds (O)
in III.
(0)
(0)
BSCH - 1.0(0)* acde
0.1 (O)** ~ ~
10.0(0)*
1.0 (0)*
0.1 ?(0)«
"response,
15 days
**no response,
1 5 days
BSA - 0.0001 26 (T4A) a e
BSA - 0.0052 (T4A) a
BSA - 0.0085 (T4A) ac
0.014 (T4A)
0.0001 3 (T4A)
0.022 (T4A)
BSA - 0.02 (T4A) a
0.009 (T4A)
0.01 (T4A)
0.0001 (T4A)
Comments
Soft water primarily was the test medium. TLm's reported
for 24, 48, and 96 hr. Acetone or alcohol used as solvent
or carrier in most cases.
When applied at 0.1 pound per acre active ingredient,
100 percent fish mortality occurred in 1 day.
No toad mortality occurred at 0.4 pounds per acre in 1 day.
Toxicity was determined by measuring acetylcholinesterase
activity in the brains of fish. Concentrations are given in
ppb as either response or not response in 1 5 or 30 days.
Emulsible concentrates were prepared from technical grade
insecticides with acetone as the solvent.
Symptoms prior to death were observed and recorded on
graphs.
Assays were conducted in soft water at 25 C. Decrease in
brain cholinesterase was measured in fish exposed to the
toxicant.
Additional TLm data are given.
Unspecified chemical characteristics of assay water were de-
termined by standard methods. General comments were
made concerning "standardized" conditions, use of "soft"
water, and use of emulsifying agents. Additional data are
presented.
Reference
(Year)
Pickering, et al
(1962)
Mulla, et al
(1963)
Weiss and
Gakstatter
(1964)
Nebeker and
Gaufin
(1964)
Weiss
(1964)
Gaufin, et al
(1965)
Gaufin, et al
(1965)
^
•o
m
X
-------
Guthion
(25% WP)
Guthion
(tech,
95 percent
active in
acetone)
Guthion
Guthion
Guthion
8
Guthion
m
j!> Guthion
(EC2)
I Guthion
m
S
Ictiobus BSA
cyprinellus
Ictalurus
puntatus
Lepom/s
cyanellus
Rana
catesbeiana
Notemigonus
crysoleucas
Lepomis
macrochirus
Micropterus
salmoides
Pteronarcys BSA
californica
(naiad)
Acroneuria
pacifica
(naiad)
Acroneuria BSA &
pacifica CFCH
Pteronarcys
californica
Lepomis BSA
gibbosus
Lepomis
gibbosus
Ictalurus
melas
Pseudopleuronectes
americanus
Myoxocephalus
scorpius
Leiostromus BCFCH
xanthurus
Cyprinodon
variegatus
Micropterus BSA
salmoides
Pteronarcys BSA
californica
(naiads)
(O) a c d e
9.0 (T2A)
9.0 (T2A)
0.025 (T2A)
(O)
0.10(T2A)
0.025 (K2)
0.025 (T2A)
0.0220 (T4A) c d e f
0.0085 (T4A)
0.0085 (T4A) a c d e
0.00024 (T30CH)
0.022 (T4A)
0.0013 (T30CH)
1/4 (O)
8.74 ±1.72(0)
3.64 ±0.67 (O)
11.24 ± 1.60 (O)
0.03 ±0.01 (O)
0.01 (O) a
0.01 (O)
1.0(0) ae
1.50(K1)
0.0015 (T4A) acdef
At 1.0 ppm concentration, bullfrog tadpoles and bigmouth
buffalo were not affected. The compound performed
effectively under various water conditions which included
water from a bayou, lake, and in ponds filled with well
water. 1.0 ppm of Guthion effectively controlled green
sunfish without apparent effect on channel catfish.
Meyer
(1965)
A. pacifica was much more sensitive to chlorinated hydro-
carbons and to organic phosphate insecticides than
P. californica.
Additional data are presented.
The figures given are for mortality in 2 hours when the amount
of chemical was 16 mg/kg, given by injection.
This paper is a study of the amounts of organic thiophosphate
and their oxygen analogues which accumulate in liver slices
in an in vitro study of insecticides. The numbers given are
for m JUm of chemical (in the case of Parathion, Malathion,
and Guthion — the oxygen analogue) accumulated in 100 mg
(dry weight) of liver in 30 minutes.
At a concentration of 0.01 ppm, the following percent acetyl-
cholinesterase activity as compared to controls was found:
L. xanthurus — 79
C. variegatus — <10.
At 10 ppm no mortality occurred in 1 day. Experiments
were carried out in fiber glass tubs filled with well water.
Fish weights ranged from 2 to 6 pounds.
Data reported as LC^Q at 15.5 C in 4 days.
Jensen and
Gaufin
(1966)
Jensen and
Gaufin
(1966)
Murphy
(1966)
Murphy
(1966)
Butler and
Johnson
(1967)
Mulla, et al
(1967)
Sanders and
Cope
(1968)
m
z
O
X
CD
•D
•31
O
O
-------
o
o
2
2
m
o Chemical
r~ Guthion
0
I
m
2
0
r~
•D
3)
o
0
c
o
-t
05 Gutoxon
Gutoxon
HCA
CO
1
OJ
oo
Hept
Heptachlor
Bioassay
or Field
Organism Study'T
Lepomis BSA
gibbosus
Ictaluras
me/as
Micropterus
dolomieui
Myxocephalus
scorpius
Pseudopleuronectes
americanus
Lepomis
gibbosus
Ictalurus
me/as
Pseudopleuronectes
americanus
Myxocephalus
scorpius
Lepomis BSA
gibbosus
Panicum f L
hemitomum
Pontederia
cordata
Spatterdock
Channel BSA
catfish
(fingerlings)
Various FL
Toxicity, Experimental
Active Variables
Field Ingredient, Controlled
Location'2' ppm'3) or Noted'4'
- (0) ap
0.205 ± 0.01 0 (O)
0.101 ±0.044 (O)
0.039 ±0.030(0)
0.1 09 ± 0.020 (O)
4/4 (0)
Fla. (0)
12.4(K25hrA) a
Salt Lake (O) -
Co.,
Utah
Comments
The chemicals were poor inhibitors of brain cholinesterases
in vitro; their oxygen analogs were potent inhibitors.
This paper is a study of the amounts of organic thiophos-
phate and their oxygen analogues which accumulate in
liver slices in an in vitro study of the insecticides. The
numbers given are for mjUm of the chemical accumulated
in 50 mg of liver (wet weight) in 10 minutes.
The figures given are for mortality in 2 hours when the
amount of chemical was 1.0 mg/kg, given by injection.
The degree of control was as follows:
P. hemitomum (80 Ib/acre) — 85 percent
P. cordata (80 Ib/acre) — 85 percent
spatterdock (160 Ib/acre) — none.
Tap water was used. Considerable additional data are
presented.
The chemical was applied at 0.1 Ib/acre.
At the above concentration no ill effects were observed in
mammals, birds, reptiles, and amphibians.
Reference
(Year)
Murphy, et al
(1968)
Murphy
(1966)
Murphy
(1966)
Copeland and
Woods
(1959)
Clemens and
Sneed
(1959)
Graham and
Anderson
(1958)
Invertebrates were not affected uniformly. Crustaceans
were not harmed, nor were larvae of the insect family
Ephydridae.
Spiders and aquatic insects other than Ephydridae were
adversely affected in varying degrees. Aquatic beetles
seemed to be affected more seriously than other insects
excepting mosquito larvae.
m
z
g
x
00
-------
Heptachlor
vo
Heptachlor
I
m
3)
O
Heptachlor
Heptachlor
(25%)
O
m Heptachlor
5
O
D
Dorosoma
cepedianum
Esox
americanus
Erimyzon
bucetta
Notemigonus
crysoleucas
Opsopoeodus
emiliae
Ictalurus
melas
Fundulus
chrysotus
Gambusia
affinis
Aphredoderus
sayanus
Micropterus
salmoides
Chaenobryttus
coronarius
Lepomis
symmetricus
L. megalotis
L. macrochirus
Pomoxis
nigromaculatus
Etheostoma
gracile
Fathead
minnow
Bluegill
Goldfish
Guppy
Fathead
minnow
Channel
catfish
(fingerlings)
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
FR
Texas
(O)
BSA
BSA
BSA
BSA
0.094 (T4A)
0.019 (T4A)
0.230 (T4A)
0.170 (T4A)
0.056 (T4A)
1.8 (K24hr A)
0.09 (T4A)
0.02 (T4A)
0.23 (T4A)
0.11 (T4A)
adef
Experiments were conducted in fish streams and canals
which bisect a farm treated with 10% Heptachlor at the rate
of 20 pounds per acre to control fire ants.
Fish were showing symptoms of distress 3 days after applica-
tion of the Heptachlor. In a depression filled with water
in a rice field 100% kill was noted for Gambusia and bantam
sunfish (the most abundant species). There was no effect on
tadpoles.
Boudreaux, et al
(1959)
m
O
X
00
It was the authors opinion that pH, alkalinity and hardness,
within the usual range in natural waters, had little effect on
the toxic effect of the compounds studied. The values
given are from Henderson, Pickering, and Tarzwell, "The
Relative Toxicity of Ten Chlorinated Hydrocarbon Insecti-
cides to Four Species of Fish". It is interesting that the
different tables from the above book (as reported in this
paper) report widely different values for the same compounds.
This experiment was performed in soft water.
Comment same as above except that this experiment was
performed in hard water.
Tap water was used. Considerable additional data are
presented.
Concentrations were based on percent active ingredient.
Tarzwell
(1959)
Tarzwell
(1959)
Clemens and
Sneed
(1959)
Henderson, et al
(1959)
-------
COMMERCI
r
o
i
m
2
O
f-
TJ
3)
0
O
o
w
*p
^-
o
Chemical
Heptachlor
(72%)
Heptachlor
Heptachlor
Heptachlor
Heptachlor
(heptachloro-
4,7-methano-
tetrahydro-
indene)
Heptachlor
Heptachlor
Heptachlor
Organism
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Pimephales
promelas
Lepomis
macrochirus
Daphnia
magna
One orh ynchus
kisutch
Oncorhynchus
tshawytscha
Salmo
gardnerii
Gasterosteus
aculeatus
Richardsonius
balteatus
hydro flox
Lepomis
microlophus
Gammarus
lacustris
lacustris
Salmo
gairdneri
Redear
sunfish
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
StudyCU Location(2) ppm<3) or Noted W
BSA - 0.18IT4A) abecdf
0.026 (T4A)
0.320 (T4A)
0.148 (T4A)
BSA - 0.094 (T4A) a
0.019 (T4A)
BSA - 0.05777 (O) a
BSA - 59.0 (T4A) a c d e
17.3(T4A)
19.4 (T4A)
111.9 (T4A)
BSA - >0.13(T1A) acdef
0.11 (T2A)
0.096 (T4A)
BSA - 0.02-0.09 (T1 A) a
BSA - (O) aep
BSA - 150 (T1A) a
90 (T2A)
70 (T4A)
0.092 (T1 A)
0.064 (T1A)
O.O47 (T1 A)
0.034 (T1 A)
0.022 (T1 A)
Comments
Dilution water was usually soft although some studies were
conducted with hard water.
Bioassay investigations of the new insecticides indicate that
in general the organic phosphorus compounds are not as
toxic to fish as are the chlorinated hydrocarbons. The
toxicity of most of these materials was not significantly in-
fluenced by water quality. Therefore it is to be expected
that the toxicity of these materials will not differ signifi-
cantly in different streams.
The indicated concentration immobilized Daphnia in 50 hours.
Chemical dissolved in acetone. TLm expressed in PPB.
Results given were in soft water.
Results in hard water were as follows: 0.15 (T1 A),
0.12 (T2A), and 0.11 (T4A).
This is a time-temperature study with considerable additional
data presented.
The mortality might have been partially due to the suscept-
ibility of the organism to higher temperatures, toxicity from
extended exposure to copper electrodes (used to shock the
organism to determine death), or the increase of CO2- Re-
sults were expressed as LTsg; for example, at 0.5 ppm.
50 percent of the shrimp were killed in 240 (±30) min.
The experiments were conducted at 55 F. Fish were 2-3 in.
long.
The experiment was conducted at 45 F.
The experiment was conducted at 55 F.
The experiment was conducted at 65 F.
The experiment was conducted at 75 F.
The experiment was conducted at 86 F.
Higher temperatures caused a moderate increase in toxic effects.
Reference
(Year)
Henderson, et al
(1959)
Tarzwell
(1959)
Anderson
(1960)
Katz
(1961)
Webb
(1961)
Brown
(1961)
McDonald
(1962)
Cope
(1963)
^
TJ
m
Z
O
X
CD
-------
Heptachlor
Heptachlor
(EC2)
Heptachlor
Heptachlor
Lepomis
cyanellus
Lepomis
macrochirus
Rana
catesbeiana
Gambusia
affinis
Rana
catesbeiana
(tadpoles)
Gambusia
affinis
affinis
Bluegill
FL
FL
Miss.
Cal.
(O)
BSA
BSA
Heptachlor
(tech)
i Heptachlor
1— *
£
Heptachlor
8
m
Q Heptachlor
r
o
m
2
Rainbow
trout
Salmo
gairdneri
Lepomis
macrochirus
Pteronarcys
californica
Baetis sp
Daphnia
pulex
Simocephalus
serrulatus
Simocephalus
serrulatus
Daphnia
pulex
Daphnia
carinata
BSA
BSA
BSA
BSA
a c
0.07 to 1.3(O)
0.019 (T4A)
0.008 (T4A)
0.009 (T2A)
0.026 (T2A)
0.006 (T2A)
0.032 (T2A)
0.042 (T2A)
0.047 (T2A)
0.047 (SB)
0.042 (SB)
0.02 (SB)
Limited mortality of fish and amphibians occurred as a result
of Heptachlor applications used to control fire ants. At a
concentration of 2.0 (Ib/acre) only one bullfrog was killed
during the entire study. At a concentration of 0.25 plus
0.25 Ib/acre (2 applications approximately 4 months apart)
there were 8 dead green sunfish.
Mixed populations of the indicated test species contained in
cages were exposed to various insecticidal chemicals applied
as dilute sprays to ponds 1/16 acre in size. The indicated
toxicant concentration is in Ib/acre, and resulted in a 28 per-
cent mortality for the fish, and a 50 percent mortality for
the tadpoles in 24 hours.
The lower value is for fish that had never been exposed to the
toxicant, and the higher value was obtained with fish that
had been exposed to a sublethal dose in the past. Appar-
ently such an exposure produces a resistance that can be
retained when they are later placed in clean water.
Assays were conducted in soft water at 25 C. Decrease in
brain cholinesterase was measured in fish exposed to the
toxicant.
The values reported are given as
This paper reports acute toxicity of a number of compounds,
and discusses sub-acute mortality as well. Effects on re-
production and behavior are also discussed. Data pre-
sented as EC5Q.
Concentration repotted is for immobilization.
Time for immobilization was 48 hr.
Data cited are for 60 F, but assays were performed at varied
temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
Concentration reported is for immobilization.
Time for immobilization was 64 hr.
Data cited are for 78 F, but assays were performed at varied
temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
Ferguson
(1963)
Mulla
(1963)
Boyd and
Ferguson
(1964)
Weiss
(1964)
Cope
(1965)
Cope
(1966)
Sanders and
Cope
(1966)
Sanders and
Cope
(1966)
•o
3D
O
O
-------
o
o
2
2
m
g Chemical
J*
*~ Heptachlor
O
I
m
s
O
r~
-a
3)
O
rj
C
o
Heptachlor
Heptachlor
Heptachlor
*?
[•v
Heptachlor
Heptachlor
epoxide
Toxicity,
Bioassay Active
or Field Field Ingredient,
Organism Study^) Location^) ppm(3)
Mya BCFCH - (O)
arenaria
Crassostrea
virginica
Corbicula
manillensis
Mercenaria
mercenaria
Ftangia
cuneata
Oyster FE Galveston (O)
Bay, Texas
Micropterus FL Va. (O)
salmoides
salmoides
Lepomis
macrochirus
Chelydra
serpentine
Pteronarcys BSA - 0.0011 (T4A)
californica
(naiads)
Pteronarcella 0.0009 (T4A)
bad/a
(naiads)
Claasenia 0.0028 (T4A)
sabulosa
(naiads)
Alosa BSA - (O)
pseudoharengus
Aplodinotus
grunniens
Coregonus
artedii
Lota
lota
Buteo FO Netherlands (O)
buteo
Accipiter
gent His
Accipiter
nisus
Falco
tinnunculus
Tyto
Alba
Experimental
Variables
Controlled
or NotedW) Comments
— Results are recorded as a range of uptake of the chemical by
5 species of aquatic mollusks. An uptake or concentration
of 250-2500X resulted.
— The chemical was found in the water at a concentration of
<0.001 ppm. Oysters from the area were found to contain
<0.01 ppm.
— The amount of chemical applied was not specified in this
report.
None of the chemical was found in the tissues of either bass
or bluegill taken from polluted ponds. However, a snapping
turtle taken from a pond that had no residue of chemical in
the water or bottom mud was found to contain 5100 ppb
in the body fat, egg yolk, and liver tissues.
a c d e f Data reported as 1X50 at 1 5.5 C in 4 days.
— The study showed that the levels of chlorinated hydrocarbon
pesticide residues in fish meals and oils were, with the ex-
ception of the oil sample taken from the Lake Michigan
alewife, below the regulatory tolerances established by the
Food and Drug Directorate of Canada (1965) for certain
foods intended for human consumption. Pesticide levels
were interpreted as being representative for each species.
— The results of this study show that birds of prey and fish-
eating birds found dead in the Netherlands accumulated
large amounts of different chlorinated hydrocarbon insecti-
cides. In most cases the liver had the highest concentration
of toxicant, ranging from 0.07 to 4.7 ppm. Most chlorinated
hydrocarbons tend to accumulate in the fat depots of the
body. In instances where mesenterial fat was found the con-
centration of toxicant was found to be as high as 3.0 ppm.
Reference
(Year)
Butler
(1967)
Casper
(1967)
Weatherholtz,
et al
(1967)
Sanders and
Cope
(1968)
Dugal
(1968)
Koeman and
van Genderen
(1966)
^
•wt
U
m
z
g
03
-------
Heptachlor
epoxide
O
>
Hercules
528
Hercules
3895 G
Hercules
7175
(tech)
Hercules
7531
(tech)
HRS-1622
(octachloro-
propane)
Hyamine
8
S Hyamine
1622
O Hyamine
m 2389
' Hydram
"D
3)
O
O Hydram
I
Strix
aluco
Oslo
otus
Falco
pereginus
Alosa
pseudoharengus
Aplodinotus
grunniens
Coregonus
artedii
Lota
lota
Lepomis
macrochirus
Micropterus
salmoides
Notemigonus
crysoleucas
Carassius
auratus
Gambusia
affinis
Lepomis
macrochirus
Lepomis
macrochirus
Austral orbis
glabratus
Oncorhynchus
kisutch
Lepomis
macrochirus
Pimephales
promelas
Lepomis
macrochirus
Pimephales
promelas
Oyster
Penaeus
aztecus
BSA
BSA
BSA
BSA
BSA
BSA
and
FL
BSA
BSA
BSA
BCF
L
(O)
0.1 (O)
0.1 (O)
0.1 (O)
0.1 (O)
0.05 (K0%)
40,000(71 A)
25,000 (T1A)
Puerto Rico Failed
57(T1A)
53 (T2A)
(S) 1.6 (T4A)
(H) 3.8 (T4A)
(S) 1.6 (T4A)
(H) 3.8 (T4A)
(S) 1.2 (T4A)
(H) 4.8 (T4A)
(S) 2.4 (T4A)
(H) 4.2 (T4A)
(O)
(O)
— The study showed that the levels of chlorinated hydrocarbon
pesticide residues in fish meals and oils were, with the ex-
ception of the oil sample taken from the Lake Michigan
alewife, below the regulatory tolerances established by the
Food and Drug Directorate of Canada (1965) for certain
foods intended for human consumption. Pesticide levels
were interpreted as being representative for each species.
a c d f This paper reports the effect of insecticides in reducing the
anticholinesterase in a fish brain within 2-8 hours. The
inhibition of the enzyme was a function of the concentra-
tion of the insecticide, extent of exposure, and specific
chemical nature of the compound.
Chemicals were dissolved in acetone, and tests were run in
triplicate. Toxicity is given as average percent fish killed
in 24 hours.
The experiment was conducted at 75 F. Fish weighed 0.4 g.
Comment same as above.
c Seven of the tested compounds failed to meet acceptability
criteria — that is, complete kill after 6-hr exposure to
10ppm. They were not used in field tests. Field tests
showed WL 8008 to be highly effective.
a c d e Concentrations were based on percent active ingredient.
£ cj! Bioassay method in Standard Methods for examination of
~~ water was used. Both hard (H) and soft (S) water were
used. TLm values for 24 and 48 hr are also presented.
ace Comment same as above.
No effect on exposure to the chemical at 1.0 ppm.
Toxicant chemicals were evaluated in sea water at tempera-
tures averaging about 28 C. The values are for 24-hr ECso
or enough to cause loss of equilibrium or mortality. A con-
centration of 1.0 ppm caused 10 percent mortality.
Dugal
(1968)
Weiss
(1959)
Lewallen
(1959)
Cope
(1963)
Cope
(1963)
Seiffer and
Schoof
(1967)
Bond, et al
(1960)
Surber and
Pickering
(1962)
Surber and
Pickering
(1962)
Butler
(1965)
Butler
(1965)
I
m
o
X
09
-------
COMMERCI
r~
o
m
o
>
f~
OJ
O
o
c
o
(fl
s°
-P-
Chemical
Hydram
Hydram
Hydram
Hydram
(tech)
Hydram
Hydram
(tech)
Hydrothat
191
Hydrothal
plus
Ibcol
I mi dan
Organism
Leiostomus
xanthurus
(juvenile)
Crassostrea
virginica
Penaeus
aztecus
Leiostomus
xanthurus
Phytoplankton
Pteronarcys sp
(nymphs)
Rainbow
trout
Bluegill
Sal mo
gairdneri
Lepomis
macrochirus
Pteronarcys
californica
Rainbow
trout
Bluegill
Rainbow
trout
Lepomis
macrochirus
Guppy
Prosimulum spp
Cnephia spp
Simulium spp
(larvae)
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study'1 ) Location'2) ppm'3)
BSA - (O)
BCFA & - 1.0 (NTE)
BSA
1.0 (0,30%)
1.0 (20%
T2CFA)
9% (O)
BSA - 0.370 (T4A)
BSA - 0.200 (T4A)
0.355 (T4A)
BSA - 0.290 (T2A)
0.475 (T2A)
0.700 (T2A)
BSA - 0.29 (T2A)
0.475 (T2A)
BSA - 1.5(T2A)
BSA - 3.5 (T1 A)
BSA - 100 (K1)
LCFA - 4.0 (O)
Experimental
Variables
Controlled
or Noted '^) Comments
a Water temperature was 25 C. 20% mortality at 1.0 ppm.
— Sea water was pumped continuously into test aquaria.
Salinity, temperature, and plankton fluctuated with tide,
and ambient weather conditions. Some bioassays with
fish were static. Toxicity was reported for the following:
Oyster - 96-hr EC5Q - Cone, which decreased
shell growth.
Shrimp — 48-hr EC$Q — Cone, which killed or
paralyzed 50% of test animals.
Fish - 48-hr EC50 - Cone, which killed 50%.
Phytoplankton — Percent decrease of CO2 fixation to a
4-hr exposure at 1 .0 ppm chemical
concentration.
a Experiments were all conducted at 60 F in 1 964. The values
~ were listed as LCsfj.
a This is an estimated LC$Q value at temperatures from 55
to75F.
a This paper reports acute toxicity of a number of compounds,
and discusses sub-acute mortality as well. Effects on repro-
duction and behavior are also discussed. Data presented
as EC5Q.
— Data are given as LCsg.
— Comment same as above.
a b e This report is a simple and straightforward determination of
~ a median tolerable limit for a selected group of herbicides.
a Those fish that survived at lower concentrations were still
~~ very active several days after they had been taken out and
placed in fresh water.
a Stones heavily populated with wild larvae were placed in
troughs of running water containing the toxicant. When
the larvae became detached from the rocks and floated
away, they were assumed to have undergone lethal intoxica-
tion. The larvae were exposed to the toxicant for 5 minutes.
then in clean water for 24 hours. At that time the number
detached amounted to 85 percent.
Reference
(Year)
Butler
(1965)
Butler
(1965)
Cope
(1965)
Cope
(1965)
Cope
(1966)
Bohmont
(1967)
Bohmont
(1967)
Hughes and
Davis
(1967)
Anonymous
(1964)
Jamnback and
Frempong-
Boadu
(1966)
>
•o
m
X
CD
-------
Inverton
(2,4,5-T)
lodophor
I PC 50%
I PC
(tech)
I PC
8
m
o
>
o
•
O
I PC
(tech)
Isodrin
(EC 1.6)
Isolan
(EC2)
Isotex 25
K-6882
(25 percent
EC)
Karmex Wc
[3-(p-chloro-
phenyl)-1,1-
dimethylurea)
80% active
ingredient]
Kel thane
Kelthane
Kepone
Nympheae sp
Parrot feathers
Guppy
Channel
catfish
(fingerlings)
Bluegill
Simocephalus
serrulatus
Daphnia
pulex
Bluegill
Gambusia
affinis
Gambusia
affinis
Channel
catfish
(fingerlings)
Gambusia
affinis
Richardsonius
balteatus
hydroflox
Salmo
gairdneri
Gambusia
affinis
Lepomis
microlophus
FL
BSA
BSA
BSA?
BSA
Farm
ponds in
Georgia
BSA
FL
FL
BSA
FL
BSA
Cal.
Cal.
Ponds —
Bakersfield,
Cal.
BSA
BSA
BSA
(O)
6250 (K1)
>100(K1A>
29.0 (T4A)
10.0 (SB)
10.0 (SB)
32.0 (T2A)
0.5 (O)
2.0 (K1)
0.54 (K1A)
(0)
42.5 (T1A)
41.5IT2A)
41.5CT4A)
110 (T1A)
2.1 (LD*
1.9 (L1)*»
*Resistant fish
**Nonresistant fish
0.1-0.6 (T1A)
a c d e f
Nympheae sp and parrot feathers were killed at the recom-
mended application rate of one gallon Inverton mixed with
15 gallons of fuel, and 84 gallons of water per acre killed
completely in less than a week.
Those fish that survived at lower concentrations were still
very active several days after they had been taken out
and placed in fresh water.
Tap water was used. Considerable additional data are
presented.
value at temperatures from 55 to
This is an estimated
75 F.
Concentration reported is for immobilization.
Time for immobilization was 64 hr.
Data cited are for 78 F, but assays were performed at
varied temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
Data are given as LC$Q.
Mixed populations of the indicated test species contained
in cages were exposed to various insecticidal chemicals
applied as dilute sprays to ponds 1/16 acre in size. The
indicated toxicant concentration is in Ib/acre, and
resulted in a 100 percent mortality for these fish.
Toxicity value is in Ib/acre.
Tap water was used. Considerable additional data are
presented.
No fish mortality occurred at 0.2 to 0.8 Ib/acre rates of
application. The experiments were conducted in cages
placed in the ponds.
Results given were in soft water.
Results in hard water were as follows: 60.3+(T1 A),
41.2 (T2A), and 40.1 (T4A).
The experiment was conducted at 55 F. Fish weighed
0.7 g.
This paper deals with the resistance of mosquito fish to
chlorinated hydrocarbon compounds. Resistant fish
were not always less sensitive to these chemicals.
This is a time-temperature study with considerable addi-
tional data presented.
Thomaston, et al
(1959)
Anonymous
(1964)
Clemens and
Sneed
(1959)
Cope
(1965)
Sanders and
Cope
(1966)
Bohmont
(1967)
Mulla
(1963)
Mulla
(1966)
Clemens and
Sneed
(1959)
Mulla and
Isaak
(1961)
Webb
(1961)
Cope
(1963)
Boyd and
Ferguson
(1964)
Brown
(1961)
m
z
o
X
00
-------
o
o
2
S
m
o Chemical
*" Kepone
o
i
m
S
o
r
•o
O
O
q
1/1 Kepone
(EC 2)
Kepone
(tech)
Knoxweed 42
™ Knoxweed 42
£
Knoxweed 42
Knoxweed 42
Korlan
Organism
Lepomis
macrochims
Redear
sunfish
Gambusia
affinis
Rana
catesbeiana
(tadpoles)
Rainbow
trout
Leiostomus
xanthurus
(juvenile)
Oyster
Penaeus
aztecus
Crassostrea
virginica
Penaeus
aztecus
Leiostomus
xanthurus
Phytoplankton
Gambusia
affinis
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study'"" Location'2) ppm (3) or Noted'4)
BSA - 380(T18hr) a
240 (T 32 hr)
110 (T56hr)
0.62 (T1A)
0.54 (T1A)
0.34 (T1A)
0.24 (T1A)
0.12 (T1A)
FL Cal. 0.5(0) ac
BSA - 0.020 (T4A)
BSA - (O) a
BCF - (O) a
L - (0) a
BCFA&BSA - 1.0(0)
0.48 (0)
1.0 (NTE)
1.0 (NTE)
BSA - 0.1 (K 3%) a
Comments
The experiment was conducted at 65 F Fish were
2 in. long.
The experiment was conducted at 45 F.
The experiment was conducted at 55 F.
The experiment was conducted at 65 F.
The experiment was conducted at 75 F.
The experiment was conducted at 85 F.
Higher temperatures caused a moderate increase in toxic
effects.
Mixed populations of the indicated test species contained
in cages were exposed to various insecticidal chemicals
applied as dilute sprays to ponds 1/16 acre in size. The
indicated toxicant concentration is in Ib/acre, and re-
sulted in a 18 percent mortality for the fish, and a 0
percent mortality for the tadpole in 24 hr.
The values reported are given as \-C$Q.
Water temperature was 25 C. No effect was noticed on
exposure to 1 .0 ppm.
Exposure to a concentration of 1 ppm caused a 44.0%
decrease in shell growth.
Toxicant chemicals were evaluated in sea water at tempera-
tures averaging about 28 C. The values are for 24-hr EC$Q
or enough to cause loss of equilibrium or mortality. A
concentration of 1.0 ppm caused 40 percent mortality.
Seawater was pumped continuously into test aquaria.
Salinity, temperature, and plankton fluctuated with tide,
and ambient weather conditions. Some bioassays with
fish were static. Toxicity was reported for the following:
Oyster — 96-hr EC$Q — Cone, which decreased
shell growth.
Shrimp — 48-hr EC§Q — Cone, which killed or
paralyzed 50% of test animals.
Fish - 48-hr EC5Q - Cone, which killed
50%.
Phytoplankton — Percent decrease of CO2 fixation to
a 4-hr exposure at 1 .0 ppm chemical
Concentration.
Chemicals were dissolved in acetone, and tests were run in
triplicate. Toxicity is given average percent fish killed in
24 hr.
Reference
(Year)
Cope
(1963)
Mulla
(1963)
Cope
(1965)
Butler
(1965)
Butler
(1965)
Butler
(1965)
Butler
(1965)
Le wall en
(1959)
m
z
o
X
00
-------
Kuron
Kuron
Kuron
(silvex acid
equivalent)
Kuron
Kuron
CO Kuron
Kurosal
Kurosal G
Kurosal G
(silvex acid
equivalent)
O Kurosal SL
2
m
3D
O
j£ Kurosal SL
O (silvex acid
m equivalent)
2
O
Na/as
quadalupensis
Spatterdock
Onchorynchus
tshawytscha
Micropterus
salmoides
Micropterus
salmoides
(fry)
Ictalurus
punctatus
(fry)
Lepomis
macrochirus
(fry)
Pteronarcys sp
(nymphs)
Chinook
salmon
Bluegill
Simocephalus
serrulatus
Daphnia
pulex
Lepomis
macrochirus
Bluegill
Lepomis
macrochirus
(fry)
Oncorhynchus
kisutch
Lepomis
macrochirus
(fry)
FL
BSA
BSA
Fla.
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
(O)
1.35 (T1A)
1.23 (T2A)
3.5 (T1 A)
1.0 (SB3)
0.5 (SB3)
0.3 (SB3)
0.320 (T4A)
1.35 (T1A)
1.23 (T2A)
2.9 (T1A)
2.4 (T2A)
2.4 (SB)
2.00 (SB)
120,000 (T1A)
21 (T1A)
15(T2A)
150(SB3)
290 (T1A)
240 (T2A)
83(T1A)
83 (T2A)
100ISB3)
a c d e
a c d e f p
ac d
a
a c d
a c de f p
a c d
a c d e f p
At 2O Ib/acre, N. quadalupensis was not controlled while
5-10 percent control of spatterdock was obtained.
Concentrations were based on percent active ingredient.
At least 90 percent of the fry survived for a period of
72 hours at the concentration listed.
Experiments were all conducted at 60 F in 1964. The
values were listed as LC§Q.
Tests were conducted in glass jars holding 15 liters of
water.
Toxicity of Kuron varies with the supplier.
Concentration reported is for immobilization.
Time for immobilization was 64 hr.
Data cited are for 78 F, but assays were performed at
varied temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
The experiment was conducted at 75 F. Fish weighed
0.6 g.
Tests were conducted in glass jars holding 15 liters of water.
At least 90 percent of the fry survived for a period of
72 hours at the concentration listed.
Tests were conducted in glass jars holding 15 liters of water.
Active ingredient of Kurosal SL is silvex 2-(2,4,5-trichloro-
phenoxy) propionic acid, potassium salt.
At least 90 percent of the fry survived for a period of
72 hours at the concentration listed.
Copeland and
Woods
(1959)
Bond, et al
(1960)
Jones
(1965)
Cope
(1965)
Bond, et al
(1965)
Sanders and
Cope
(1966)
Cope
(1963)
Bond, et al
(1965)
Jones
(1965)
Bond, et al
(1965)
Jones
(1965)
m
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-o
3D
O
O
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-------
COMMERCI
r-
n
X
m
S
O
r~
TJ
3)
O
0
f*
H
C/)
S
[^
00
Chemical
Kurosal SL
(60% silvex)
Kyro-eo
(nonionic)
LAS
(degradation
product-
sulfophenyl-
undecanoic
acid, disodium
salt)
LAS C 1 2
(alkylbenzene
sodium
sulfonate)
LASC 14
(alkylbenzene
sodium
sulfonate)
Bioassay
or Field Field
Organism Study'^' Location'^)
Crassostrea BCFA & BSA -
virginica
Fundulus
similis
Phytoplankton
Brook BSA -
trout
Rainbow
trout
Mayflies
(Ephemeroptera
naiads)
Stoneflies
(Plecoptera
naiads)
Damsel flies
(Odonata naiads)
Diptera larva
(chiefly
Tendipedidae)
Bluegill BSA
(fingerlings)
Bluegill BSA -
(fingerlings)
Bluegill BSA -
(fingerlings)
Toxicity,
Active
Ingredient,
1.0 (NTE)
25.0 (NTE)
1.0 (NTE)
5.2 (L1)
4.8 (L2)
4.6 (L3)
5.5 (L1)
5.3 (L2)
5.1 (L3)
5.6 (L2)
5.4 (L3)
5.2 (L4)
5.1 (L2)
4.8 (L3)
4.7 (L4)
5.2 (L3)
4.9 (L4)
(0)
75.0 (T4A)
3.0 (T4A)
0.64 (T4A)
Experimental
Variables
Controlled
or NotedW Comments
— Seawater was pumped continuously into test aquaria.
Salinity, temperature, and plankton fluctuated with tide.
and ambient weather conditions. Some bioassays with
fish were static. Toxicity was reported for the following:
Oyster — 96-hr ECso — Cone, which decreased
shell growth.
Shrimp — 48-hr EC5Q — Cone, which killed or
paralyzed 50% of test animals.
Fish— 48-hr ECso — Cone, which killed
50%.
Phytoplankton — Percent decrease of CO2 fixation to
a 4-hr exposure at 1 .0 ppm chemical
concentration.
— Kyro-eo is a synthetic, non-sulfonated detergent. Experi-
mental water was not supplemented with oxygen because
bubbling caused suds. Control tanks were also static.
Control organisms apparently did not suffer from lack of
oxygen in the static aquarium for 120 hr. Dipteran larvae
withstood 10 ppm of Kyro-eo with no mortality.
c d£ f o The fish killed all showed severe hematomas of the
respiratory folds of the gills. This was followed by the
stripping of the mucous layers. Following this, soft
tissue beneath was completely destroyed in most cases.
c d e f o Comment same as above.
c d e f o Comment same as above.
Reference
(Year)
Butler
(1965)
Hepworth
(no date)
Swisher, et al
(1964)
Swisher, et al
(1964)
Swisher, et al
(1964)
•o
m
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D
CD
-------
LAS
Linear alkyl
sulfonate
Pimephales
promelas
Lethane 384
Lexone
^ Lignasan
Lignasan
Lindane
3)
O
o
m Lindane
£
Lepomis
macrochirus
Pimephales
promelas
Ictalurus
me/as
Notropis
atherinoides
Notropis
cornutus
Prosimulum spp
Cnephia spp
Simulium spp
(larvae)
Channel
catfish
(fingerlings)
Channel
catfish
(fingerlings)
Protococcus sp
Chlorella sp
Dunaliella
euchlora
Phaeodactylum
tricornutum
Monochrysis
lutheri
Fathead
minnow
Bluegill
Goldfish
Guppy
Fathead
minnow
BCF
BSA
LCFA
BSA
BSA
BSA
BSA
2.3 (T4A)
4.0 (T4A)
4.2 (T4A)
6.4 (T4A)
3.3 (T4A)
4.9 (T4A)
4.0 (O)
jJ c d e f Mortality range is given for exposure (days 1-9) with Pickering
various concentrations and controls. Additional data (1966)
are presented.
a c d e In all these tests the LAS stock powder contained 60.8% Thatcher and
LAS. The values reported were calculated on a basis of Santner
pure LAS. (1967)
BSA
5.2 (K 30 hr A)
2.0 (K 28 hr A)
0.006 (K)
0.006 (K)
0.06 (K)
0.06 (K)
0.006 (K)
0.062 (T4A)
0.077 (T4A)
0.152(T4A)
0.138(T4A)
0.056 (T4A)
Stones heavily populated with wild larvae were placed in Jamnback and
troughs of running water containing the toxicant. When Frempong-
the larvae became detached from the rocks and floated Boadu
away, they were assumed to have undergone lethal intoxi- (1966)
cation. The larvae were exposed to the toxicant for 5
minutes, then in clean water for 24 hours. At that time
the number detached amounted to 2 percent.
Tap water was used. Considerable additional data are
presented.
Comment same as above.
Clemens and
Sneed
(1959)
Clemens and
Sneed
(1959)
Ukeles
(1962)
This paper concerns the growth of pure cultures of marine
plankton in the presence of toxicants. Results were ex-
pressed as the ratio of optical density of growth in the
presence of toxicants to optical density in the basal
medium with no added toxicants.
It was the authors opinion that pH, alkalinity and hardness, Tarzwell
within the usual range in natural waters, had little effect on (1959)
the toxic effect of the compounds studied. The values
given are from Henderson, Pickering, and Tarzwell, "The
Relative Toxicity of Ten Chlorinated Hydrocarbon Insecti-
cides to Four Species of Fish". It is interesting that the
different tables from the above book (as reported in this
paper) report widely different values for the same compounds.
This experiment was performed in soft water.
Comment same as above, except experiment was conducted Tarzwell
in hard water. (1959)
m
Z
O
X
00
3)
O
O
§
-------
o
o
s
s
m
o Chemical
r Lindane 3%
2 (Methoxychlor
m 50%)
O Lindane
*•
•o
3)
O
0
C
O
C"
Lindane
(100%)
Lindane
V
O
Lindane
Lindane
Organism
Channel
catfish
(fingerlings)
Pimephales
prome/as
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Pimephales
prome/as
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Pimephales
promelas
Lepomis
macrochirus
Oncorhynchus
kisutch
Oncorhynchus
tshawytscha
Sal mo
gairdnerii
Gasterosteus
acu/eatus
Gammarus
lacustris
lacustris
Toxicity,
Bioassay Active
or Field Field Ingredient,
StudyCI) Location<2) ppm(3)
BSA - 2.0 (K1A)
BSA - 0.06 (T4A)
0.09 (T4A)
0.15 (T4A)
0.14 (T4A)
BSA - 0.062 (T4A)
0.077 (T4A)
0.152 (T4A)
0.138 (T4A)
BSA - 0.062 (T4A)
0.077 (T4A)
BSA - 50.0 (T4A)
40.0 (T4A)
38.0 (T4A)
44.0 (T4A)
BSA - (0)
Experimental
Variables
Controlled
or Noted!4) Comments
a Tap water was used. Considerable additional data are
presented.
£d e f Concentrations were based on percent active ingredient.
a_ b e c d_f_ Dilution water was usually soft although some studies
were conducted with hard water.
a Bioassay investigations of the new insecticides indicate
that in general the organic phosphorus compounds are
not as toxic to fish as are the chlorinated hydrocarbons.
The toxicity of most of these materials was not signifi-
cantly influenced by water quality. Therefore it is to
be expected that the toxicity of these materials will
not differ significantly in different streams.
_?_cdj: Chemical dissolved in acetone. TLm expressed in ppb.
a e P The mortality might have been partially due to the suscepti-
bility of the organism to higher temperatures, toxicity from
extended exposure to coooer electrodes (useri tn ehnrk tho
Reference
(Year)
Clemens and
Sneed
(1959)
Henderson, et al
(1959)
Henderson, et al
(1959)
Tarzwell
(1959)
Katz
(1961)
McDonald
(1962)
m
Z
O
X
CD
organism to determine death), or the increase of CO2- Re-
sults were expressed as LT^rj; for example, at 0.5 ppm, 50
percent of the shrimp were killed in 11 (±2) min.
-------
Lindane
Lindane
8
m
3)
o
O
m
2
3)
O
O
Lindane
Lindane
EC 1.65
Lindane
Lindane
(tech)
Lindane
Lindane
Lindane
Protacoccus sp
Chlorella sp
Dunaliella
euchlora
Phaeodac tylum
tricornutum
Monochrysis
lutheri
Ophicephalus
punctatus
Heteropneustes
fossilis
Barbus
stigma
Trichogaster
fasciatus
Golden
shiner
Rana
catesbeiana
(tadpoles)
Gambusia
affinis
affinis
Rainbow
trout
Pteronarcys sp
(nymphs)
Bluegill
BSA
Pteronarcys
(stone fly
nymphs)
BSA
BSA
FL
BSA
BSA
BSA
BSA
Cal.
BSA
9.O (O)*
9.0 (O)*
9.0 (O)
9.0 (NG)
7.5 (NG)
"obvious,
but inhib-
ited growth
4000-5000
(K<1 hr)
2000-5000
(K<7hr)
1000 (K<2hr)
2000-3000
(K<1 hr)
>0.062-
0.125(0)
0.5(0)
0.15 to 1.7 (O)
0.022 (T4A)
0.001 (T4A)
65 (T4A)
53 (T4A)
56 (T4A)
38 (T4A)
25 (T4A)
0.001 (T4)
acdep
ac
This paper concerns the growth of pure cultures of marine
plankton in the presence of toxicants. Results were ex-
pressed as the ratio of optical density of growth in the
presence of toxicants to optical density in the basal medi-
um with no added toxicants. NG = no growth, but the
organisms were viable.
The dosage to produce toxic symptoms varied with each
species. At the very low dosage, these insecticides did
not produce observable changes, but at the higher dosage
observable changes were pronounced. Lindane at low
concentrations had no noticeable effect but at higher
concentrations the rate or mortality was very high.
A number of values for a threshold limit (LD/O) of the
toxicant in various solvents are given. Values from
0.062 ppm to 0.125 ppm for Lindane solvents in
addition to water were obtained. Acetone and mixed
solvents caused the greatest Lindane lethality.
Mixed populations of the indicated test species contained
in cages were exposed to various insecticidal chemicals
applied as dilute sprays to ponds 1/16 acre in size. The
indicated toxicant concentration is in Ib/acre, and re-
sulted in a 10 percent mortality for the tadpoles in 24 hr.
The lower value is for fish that had never been exposed to
the toxicant, and the higher value was obtained with fish
that had been exposed to a sublethal dose in the past.
Apparently such an exposure produces a resistance that
can be retained when they are later placed in clean water.
The values reported are given as
Ukeles
(1962)
Experiments were all conducted at 60 F in 1964. The
values were listed as
These experiments were performed to demonstrate that
at increased temperatures the toxic effect of most chemi-
cals is increased.
For the toxicant concentrations listed, the temperatures
were respectively, 45, 55, 65, 75, and 85 F. Data on the
effect of time as well as temperature was also reported.
The experimental animals all were approximately one
gram in weight.
These experiments were all conducted at 60 F. The values
were listed as LC5Q.
Mathur
(1963)
Meyer
(1965)
Mulla
(1963)
Boyd and
Ferguson
(1964)
Cope
(1965)
Cope
(1965)
Cope
(1965)
Snow
(1958)
-------
o
o
s
s
m
o Chemical
r~ Lindane
O
m
S
O
r~
T)
ID
O
D
O
*> Lindane
03
,1.
to
Lindane
Lindane
Lindane
Organism
Salmo
gairdnerii
Lepomis
macrochirus
Pteronarcys
californica
Daphnia
pulex
Simocephalus
serrulatus
Buteo
buteo
Accipiter
gen til is
Accipiter
nisus
Falco
tinnunculus
Tyto
alba
Strix
aluco
Asio
otus
Falco
pereginus
Puntius
javanicus
Tilapia
mossambica
Cyprinus
carpio
Puntius
Javanicus
Tilapia
mossambica
Cyprinus
carpio
Simocephalus
serrulatus
Daphnia
pulex
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study*1 1 Location*2* ppm<3)
BSA - 0.022 (T2A)
0.053 (T2A)
0.002 (T2A)
0.460 (T2A)
0.520 (T2A)
FO Netherlands (O)
FL Japan 1.0% (O)
4.0% (O)
1.0% (0)
4.0% (O)
1.0% (O)
4.0 % (O)
BSA - 2.0 (K2)
2.0 (K2)
2.0 (0)
BSA - 0.520 (SB)
0.460 (SB)
Experimental
Variables
Controlled
or Noted*4) Comments
a This paper reports acute toxicity of a number of com-
pounds, and discusses subacute mortality as well.
Effects on reproduction and behavior are also dis-
cussed. Data presented as EC5Q.
- The results of this study show that birds of prey and fish-
eating birds found dead in the Netherlands accumulated
large amounts of different chlorinated hydrocarbon in-
secticides. Most chlorinated hydrocarbons tended to
accumulate in the fat depots of the body. In instances
where mesenterial fat was analyzed the concentration
of toxicant was found to be as high as 89 ppm.
- No fish deaths occurred at the 1 .0 percent concentration.
The following mortality occurred at the 4.0 percent
level:
P. javanicus - 56.5 percent (2 days)
T. mossambica — 86.0 percent (2 days)
C. carpio — 7.5 percent (2 days)
e The purpose of this experiment was to determine the
effect of Lindane on three species of fish. The Lindane
was Dol granule, a granular formulation containing 6
percent Lindane and 94 percent carrier. With C. carpio.
the 2.0 ppm killed 77.5 percent of the test fish in 2 days.
The data given are concerned with exposure in water
solutions. When soil was added to the water, the mortality
was reduced.
— Concentration reported is for immobilization.
Time for immobilization was 48 hr.
Data cited are for 60 F, but assays were performed at
varied temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
Reference
(Year)
Cope
(1966)
Koeman and van
Genderen
(1966)
Kok and
Pathak
(1966)
Kok and
Pathak
(1966)
Sanders and
Cooe
(1966)
m
z
o
x
00
-------
Lindane
Lindane
Lindane
Lindane-C14
Lindane
U)
IW-502
8M-1499
(granular
g Silvex)
m
3)
9 M-1500
M-1845
(liquid
Silvex)
Daphnia
magna
Mya
arenaria
Crassostrea
virginica
Corbicula
manillensis
Mercenaria
mercenaria
Rangia
cuneata
Oyster
Lepomis
macrochirus
Carassius
auratus
Esox
lucius
BSA
BCFCH
1.1 (SB)
(O)
FE
BCFCH
FR
Althernanthera
philoxeroides
Pestia
stratiotes
Spatterdock
Bushy pondweed
Water Hyssop
Parrot's Feather
Bladderwort
Bushy pondweed
Spatterdock
Bushy pondweed
FL
FL
FL
FL
Galveston
Bay,
Texas
River
Nene,
Eng.
Fla.
Lakes in
Fla.
Lakes in
Fla.
Lakes in
Fla.
(O)
(O)
(O)
(O)
(O)
(O)
Concentration reported is for immobilization.
Time for immobilization was 64 hr.
Data cited are for 78 F, but assays were performed at
varied temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
Results are recorded as a range of uptake of the chemical
by 5 species of aquatic mollusks. An uptake or concentra-
tion of 10-250X resulted.
The chemical was found in the water at a concentration of
<0.001 ppm. Oysters from the area were found to con-
tain <0.01 to 0.01 ppm.
Fish were treated with carbon-labeled insecticides (0.03 ppm)
from 5 to 19 hr and uptake rates were determined. They
were placed in recovery tanks for up to 32 days. Whole
body samples were then made. Almost all of Lindane
absorbed was eliminated in 1 days.
Higher concentrations were found in larger fish, indicating
that they had been exposed to the pesticides for a longer
time. Tissue extracts from the pike were analyzed for
organochlorine pesticide residues by gas liquid chroma-
tography. The values for large pike were:
0.042 ppm muscle
7.5 ppm fat
At 1.0 Ib/acre, the degree of control was:
A. philoxeroides — 85-90 percent
P. stratiotes — 80 percent
spatterdock — 3 percent
Concentrations of 2.3 to 2.5 ppm controlled bushy pond-
weed while 1.0 to 4.0 ppm controlled the other species
indicated.
A concentration of 1.5 ppm controlled bushy pondweed.
A concentration of 0.5 ppm controlled the spatterdock
while 1.0 ppm per acre controlled the bushy pondweed.
Sanders and
Cope
(1966)
Butler
(1967)
Casper
(1967)
Gakstatter and
Weiss
(1967)
Mawdesley-
Thomas and
Leahy
(1967)
Copeland and
Woods
(1959)
Phillippy
(1961)
Phillippy
(1961)
m
O
X
00
-o
33
O
o
-------
COMMERCIA
r~
O
m
S
O
r~-
~O
03
O
O
o
—1
t/1
03
i
Ul
Chemical
MCP
(Amine)
MCPA
(alkyl amine)
MCPA
MCPA
4-IMCPB)
Malamar-50
Malaoxon
Malaoxon
Malathion
(25 percent
wettable
powder)
Malathion
(emultifiable)
Bioassay
or Field
Organism Study 'D
Crassostrea BCFA &
virginica BSA
Penaeus
aztecus
Fundulus
similis
Phytoplankton
Lepomis BSA
macrochirus
Lepomis BSA
macrochirus
Daphnia BSA
magna
Lepomis BSA
macrochirus
Micropterus
salmoides
Cyprinus BSA
carpio
C. carpio
Tilapia
mossambica
Cirrhina
mrigala
Labeo
fimbriatus
Dan/'o sp
Labeo
rohita
Lepomis BSA
gibbosus
Lepomis L
gibbosus
Ictalurus
me/as
Pseudopleuronectes
americanus
Myxocephalus
scorpius
Cyprinus BSA
carpio
Cyprinus BSA
carpio
Toxicity, Experimental
Active Variables
Field Ingredient, Controlled
Location'2) ppm(3) or Noted'4'
1.0 (NTE)
163.5IT1A)
1.5(T1A) abe
100 (O) acdiq
15IT2A) a co
10 (T2A)
10.0 (T2A) acdefp
8.5 (T2A)
8.3 (T2A)
7.0 (T2A)
8.5 (T2A)
13.5 (T2A)
8.0 (T2A)
2/4 (0)
1. 59 ± 0.17(0)
0.97 ± 0.28 (O)
0.81 ± 0.09 (O)
1.27 ±0.14 (O)
(O) ace
(0) ace
Comments
Seawater was pumped continuously into test aquaria.
Salinity, temperature, and plankton fluctuated with tide,
and ambient weather conditions. Some bioassays with
fish were static. Toxicity was reported for the following:
Oyster — 96-hr ECsg — Cone, which decreased
shell growth.
Shrimp — 48-hr ECgg — Cone, which killed or
paralyzed50% of test animals.
Fish - 48-hr ECgfj - Cone, which killed 50%.
Phytoplankton — Percent decrease of CO2 fixation to a
4-hr exposure at 1 .0 ppm chemical
concentration.
The bioassay methods employed in this experiment were
not given in the paper but it was stated that the same
procedures were employed as in previous work.
This report is a simple and straightforward determination
of a median tolerance limit for a selected group of
herbicides.
Toxicity, in terms of median immobilization concentra-
tion (IC50), is presented.
The response of bluegill and bass fingerlings to nine
agricultural chemicals as determined by bioassay using
river water is presented in this report. Bluegills were
more tolerant of the chemicals tested than bass.
The test animals were conditioned for 48 hours prior
to use.
The figures given are for mortality in 2 hours when the
amount of chemical was 0.25 mg/kg, given by injection.
This paper is a study of the amounts of organic thiophos-
phate and their oxygen analogues which accumulate in
liver slices in an in vitro study of the insecticides. The
numbers given are for m;Um of the chemical accumulated
in 50 mg of liver (wet weight) in 10 minutes.
100 percent mortality occurred in 6 days at 5 ppm. 80
percent mortality occurred in 4 days at 7 ppm.
6O percent mortality occurred in 143 hr at 3 ppm. O per-
cent mortality occurred in 4 dayi at O.O1 ppm. O percent
mortality occurred In 14O hr at 1 OPm. 1OO oercent
Reference
(Year)
Butler
(1965)
Davis and
Hughes
(1963)
Hughes and
Davis
(1967)
Crosby and
Tucker
(1966)
Davis and
Hardcastle
(1959)
Sreenivasan and
Swaminathan
(1967)
Murphy
(1966)
Murphy
(1966)
Hayes
(1965)
Hayet
(1966)
^
^
T)
g
00
-------
Malathion
Malathion
Malathion
Malathion
Malathion
Malathion
Malathion 25%
Malathion
Fall Chinook
salmon
(finger-lings)
Various
BSA
FL
Salt
Lake
Co.,
Utah
O.17 (T1A)
0.15 (T2A)
0.12 (T4A)
(O)
Pimephales
promelas
Atlantic
salmon
Fathead
minnow
Daphnia
magna
Channel
catfish
(fingerlings)
Fundu/us
oceltaris
r-
2 Malathion
m
2
O
j£ Malathion
-3
3)
O
D
C
O
Pimephales
promelas
Gambusia
affinis
Pimephales
promelas
Lepomis
macrochirus
BSA
BSA
BSA
22.0 (T4A)
0.033 (T1A)
0.033 (T2A)
12.5(T4A)
BSA
BSA
FL(E)
Odessa,
Del.
0.0009 (O)
>100 (K1A)
(O)
BSA
BSA
BSA
12.5 (T4A)
0.05 (K 40%)
17 (T4A)
£ d e f
At O.32 ppm there were no survivals after 48 hours.
The chemical was applied at 0.5 Ib/acre.
At the above concentration no ill effects were observed
in mammals, birds, reptiles, and amphibians.
Invertebrates were not affected uniformly. Crustaceans
were not harmed, nor were larvae of the insect family
Ephydridae.
Spiders and aquatic insects other than Ephydridae were ad-
versely affected in varying degrees. Aquatic beetles seemed
to be affected more seriously than other insects excepting
mosquito larvae.
Tests were performed in both hard and soft water.
Additional tolerance limit values are given.
Results are recorded in ppm of insecticide by weight in
water.
Changes in temperature had an effect on the toxicity of
the chemical.
It was the authors opinion that pH, alkalinity and hardness,
within the usual range in natural waters, had little effect
on the toxic effect of the compounds studied. The values
given are from Henderson, Pickering, and Tarzwell, "The
Relative Toxicity of Ten Chlorinated Hydrocarbon Insecti-
cides to Four Species of Fish". It is interesting that the
different tables from the above book (as reported in this
paper) report widely different values for the same compounds.
The experiment was performed in hard water.
The indicated concentration immobilized Daphnia in 50
hours.
Tap water was used. Considerable additional data are
presented.
The extent of mortality at an application rate of 0.5
Ib/acre in tidal marshes while another 33% of the fish
were not affected at all. The fate of those individuals
that were poisoned, but remained alive, is in question.
The tests indicated that 56% would recover if transferred
to fresh water following the exposure period.
Concentrations were based on percent active ingredient.
Chemicals were dissolved in acetone, and tests were run in
triplicate. Toxicity is given as average percent fish killed
in 24 hr.
Bioassay investigations of the new insecticides indicate that
in general the organic phosphorus compounds are not as
toxic to fish as are the chlorinated hydrocarbons. The
toxicity of most of these materials was not significantly
influenced by water quality. Therefore it is to be ex-
pected that the toxicity of these materials will not differ
significantly in different streams.
Parkhurst and
Johnson
(1955)
Graham and
Anderson
(1958)
Henderson and
Pickering
(1958)
Keenleyside
(1958)
Tarzwell
(1959)
m
Z
o
X
CD
Anderson
(1960)
Clemens and
Sneed
(1959)
Darsie and
Corriden
(1959)
Henderson, et at
(1959)
Lewallen
(1959)
Tarzwell
(1959)
-------
COMMERCE
>*
o
I
m
2
O
f-
-o
O
O
C
q
en
3
1
N
Chemical
Malathion
Malathion
(tech.
57% active
in xylene)
Malathion
(57% concen-
trate emulsified
in xylene)
Malathion
Malathion
(81 percent
EC)
Malathion
(0,0-di methyl
dithiophosphate
of diethyl
mercapto-
succinate)
Organism
Lepomis
macrochirus
Micropterus
salmoides
Notemigonus
crysoleucas
Carassius
auratus
Acroneuria
pacifica
Pteronarcys
californica
Claassenia
sabulosa
Arctopsyche
grandis
Acroneuria
pacifica
Hydropsyche
californica
Arctopsyche
grandis
Claassenia
sabulosa
Pteronarcys
californica
Oncorhynchus
tshawytscha
Gasterosteus
aculeatus
Gambusia
affinis
Richardsonius
balteatus
hydroflox
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
StudyCO Location(Z) ppm(3) or Noted<4>
BSA - 0.1 (0) 1£^1
0.1 (O)
0.1 (0)
0.1 (O)
BSA - 0.0056 (T4A) a c e f I n
0.1 (T4A)
0.056 (T4A)
0.032 (T4A)
BSA - 0.0072 (T4A) ^c d e I m
0.0225 (T4A)
0.032 (T4A)
0.056 (T4A)
0.1 (T4A)
BSA - 23 (T4A) ^cde
94 (T4A)
FL Ponds- (0) ac
Bakers-
field,
Cal.
BSA - 13.6 (T1 A) acdef
1 1 .4 (T2A)
8.9 (T4A)
Comments
This paper reports the effect of insecticides in reducing the
anticholinesterase in a fish brain within 2-8 hours. The
inhibition of the enzyme was a function of the concentra-
tion of the insecticide, extent of exposure, and specific
chemical nature of the compound.
Assays were conducted in hard water.
Test water was obtained from a mountain stream.
Chemical dissolved in acetone. TLm expressed in ppb.
At 0.5 Ib/acre, 48 percent mortality occurred in 24 hours.
At 2.0 Ib/acre, 54 percent mortality occurred in 24
hours. The experiments were conducted in cages placed
in the ponds.
Results given were in soft water.
Results in nard water were as follows:
1 1.7 (T1A), 9.6 (T2A), and 9.6 (T4A).
Reference
(Year)
Weiss
(1959)
Gaufin
(1961)
Gaufin, et al
(1961)
Katz
(1961)
Mullaand
Isaak
(1961)
Webb
(1961 )
•o
m
Z
o
w
-------
Malathion
Malathion
Killifish
Cyprinodon
Fundulus
Gambus/a
Mollienesia
Salmon
(fingerlings)
Carp
Bluegill
(fingerlings)
Goldfish
Rainbow
trout
Sunfish
Yellow
perch
Fathead
minnow
Micropterus
sa/moides
Pimephales
promelas
BSA
BSA
COMME
3)
O
IAL CHEMICAl
. PRODUC
3
Malathion
(granular)
Malathion
Malathion,
emulsible
concentrate
(20 percent)
Malathion,
(tech,
1 00 percent)
Malathion,
emulsible
concentrate
(57 percent)
Stizostedion
vitreum
Salmo
gairdnerii
(one wk old
sac fry)
(one mo old
feeding fry)
Lepomis
macrochirus
Green
sunfish
Largemouth
bass
Pimephales
promelas
Lepomis
macrochirus
Lebistes
reticulatus
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
BSA
BSA
BSA
BSA
BSA
BSA
0.2-O.75
Ib/acre (O)
0.1 (K 100%)
3.0 (K 60%)
5.0 (K 100%)
25(0)
0.5 (O)
0.5 (O)
1.84(0)
1.0 (K26%)
10.0(K 100%)
1.0 (K 100%)
10.0 (K 100%)
Large 1.2 (T4A)
Small 0.55 (T4A)
0.60 (T4A)
0.25 (T4A)
23 (T4A)
0.090 (T4A)
0.84 (T4A)
25 (T4A)
0.088 (T4A)
0.79 (T4A)
a c d e
a c d e
a c de
Extensive mortality.
Decidedly toxic.
Killed 60% of test fish.
Lethal dose.
Spiller
(1961)
LD5Q in 24 hours.
The degree of reaction to the cholinesterase-inhibiting
insecticides is not only a function of time and concen-
tration, but also of chemical and biological species.
This paper reports many analyses of brain cholinesterase
activity which is expressed as percentage of normal. The
data are reported as LT§g which was the time required
for 0.5 ppm of the chemical to kill 50 percent of the
fish. For bass the LJ^Q was 2 hr and 40 min and for
fatheads 72 hr.
Five percent of the fish survived 24 hours at the indi-
cated concentration. Emulsions were more toxic than
granular formulations of the chemical.
Results are averages of triplicate tests. Toxicity is re-
ported as percent mortality (K %).
Soft water primarily was the test medium. TLpp's reported
for 24,48, and 96 hr. Acetone or alcohol used as solvent
or carrier in most cases.
Comment same as above.
Soft water primarily was the test medium. TLm's reported
for 24, 48, and 96 hr. Acetone or alcohol used as solvent
or carrier in most cases.
Weiss
(1961)
Hilsenhoff
(1962)
Lewallen and
Wilder
(1962)
Pickering, et al
(1962)
Pickering, et al
(1962)
Pickering, et al
(1962)
•o
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-------
COMMERCI
r~
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Chemical
Malathion
Malathion
Malathion
(tech)
Malathion
Malathion
Malathion
(tech.
95 percent
active In
acetone)
Malathion
Malathion
Malathion
Bioassay
or Field
Organism Study *D
Lepomis BSA
macrochirus
Cu/ex pipiens BSA
quadnmacula tus
Salmo BSA
gairdneri
Redear
Lepomis
macrochirus
Daphnia BSA
magna
Gammarus BSA
lacustris
Pteronarcys BSA
californica
(naiad)
Acroneuria
p'acifica
(naiad)
Bluegill BSA
Carassius BSCH
auratus
Lepomis
macrochirus
Notemigonus
crysoleucus
Rainbow BSA
trout
Toxicity, Experimental
Active Variables
Field Ingredient, Controlled
Location*2) ppm<3) or Noted*4*
0.28 (T1 A) a
0.22 (T1A)
0.135 (T1 A)
0.124 (T1A)
0.07 (T1A)
(0) c
100 (T1A) a
170(T1A)
100 (T2A)
60 (T4A)
45 (T1A)
35 (T2A)
120 (T1A)
0.002 (T2A) ace
0.010 (K)
- 0.00162 a e
(T4A)
0.0500 (T4A) c d e f
0.0070 (T4A)
0.090 (T4A) a
1.0 (O)* lcdl
1.0 (O)*
1.0(0)*
'response,
1 5 days
77 (T4A) a
68 (T4A)
110 (T4A)
Comments
The experiment was conducted at 45 F
The experiment was conducted at 55 F
The experiment was conducted at 65 F.
The experiment was conducted at 75 F.
The experiment was conducted at 85 F.
Tests were conducted in tap water and artificially polluted
tap water. The values reported are the concentration range
for an LCgrj, 0.045 to 0.120 ppm in polluted water and
0. 1 00 to 0.240 i n tap water.
The experiment was conducted at 55 F. Fish were 2-3 in.
long.
The experiment was conducted at 75 F Fish weighed
3g.
The experiment was conducted at 75 F. Fish weighed
0.4 g.
The experiment was conducted at 75 F Fish weighed
0.6 g.
Acetone was used as a solvent for the Malathion. Each
test solution contained 0.1% acetone.
Emulsible concentrates were prepared from technical
grade insecticides with acetone as the solvent.
Symptoms prior to death were observed and recorded
on graphs.
A. pacifica was much more sensitive to chlorinated hydro-
carbons and to organic phosphate insecticides than
P. californica.
Assays were conducted in soft water at 25 C. Decrease
in brain cholinesterase was measured in fish exposed
to the toxicant.
Toxicity was determined by measuring acetylcholinesterase
activity in the brains of fish. Concentrations are given in
ppb as either response or not response in 1 5 or 30 days.
These experiments were performed to show the effect of
temperature on the toxicity.
For the toxicant concentrations listed, the temperatures
were respectively 45, 55, and 65 F. The fish all were approxi-
mately one g in weight. Toxicant concentrations for one
and 2-day times were also listed.
Reference
(Year)
Cope
(1963)
Lewallen and
Wilder
(1963)
Cope
(1963)
Gillespie
(1964)
Nebeker and
Gaufin
(1964)
Jensen and
Gaufin
(1964)
Weiss
(1964)
Weiss and
Gaks tatter
(1964)
Cope
(1965)
^
•o
o
X
00
-------
Mai a th ion
Malathion
Malathion,
3,2,dibrom
2
m
o
o
>
a
O
o
Acroneuria
pacifica
Ephemere/la
grandis
Gammarus
lacustris
Pteronarcys
californica
Pteronarcys
californica
Acroneuria
pacifica
Ephemerella
grandis
Arctopsyche
grandis
Hydropsyche
californica
Daphnia
magna
Gammarus
lacustris
Fathead
minnow
Lepomis
gibbosus
Lepomis
macrochirus
Enneacanthus
gloriosus
Esox
niger
Enneacanthus
chaetodon
Lepomis
microlophus
Sal mo
trutta
Salmo
gairdnerii
Lepomis
auritus
Perca
flavescens
Microp terus
salmoides
Fundulus
diaphanus
Catostomus
commersoni
Notemigonus
crysoleucas
Erimyzon
oblongus
BSA,
BSA
BSA
0.007 (T4A)
0.10 (T4A)
0.0016 (T4A)
0.05 (T4A)
0.05 (T4A)
0.007 (T4A)
0.100 (T4A)
0.02 (T4A)
0.007 (T4A)
0.009 (T 50 hr A)
0.002 (T4A)
12.5(T4A)
0.075 (T2A)
0.075 (T2A)
0.075 (T2A)
0.075 (T2A)
0.075 (T2A)
0.08 (T2A)
0.08 (T2A)
0.08 (T2A)
0.085 (T2A)
0.09 (T2A)
0.10 (T2A)
0.10IT2A)
1.5(72 A)
3.2 (T2A)
4.2 (T2A)
Additional TLm data are given.
Gaufin, et al
(1965)
Unspecified chemical characteristics of assay water were
determined by standard methods. General comments
were made concerning "standardized" conditions, use
of "soft" water, and use of emulsifying agents. Addi-
tional data are presented.
Gaufin, et al
(1965)
This paper contained both bioassay and field studies. The
tests revealed that a mixture of 3 parts of actual Dibrom
and 2 parts of actual Malathion (by weight) applied at
0.10 ppm was more toxic to bluegills and pumpkinseeds
than to largemouth bass.
Hoff and
Westman
(1965)
m
z
o
X
09
-------
o
o
s
2
m
o Chemical
j» •
*" Malathion,
2 3,2,dibrom
m
S
O
>
1-
T)
JO
0
O
Q
CO
3
IN
-j
*>
Malathion,
(95% active
in acetone)
Malathion
Bioassay
or Field
Organism Study'1 )
Yellow perch FL
Pumpkinseed
Bluegill
Golden shiner
Brown bullhead
Chain pickerel
Largemouth bass
Black crappie
Pumpkinseed
Yellow perch
White perch
Largemouth bass
Brown bullhead
Rainbow trout
Pumpkinseed
Bluegill
Largemouth bass
White perch
Bluegill
Largemouth bass
Yellow perch
Black crappie
Channel catfish
Gizzard shad
Carp
Largemouth bass
Black crappie
Chain pickerel
Bluegill
Yellow perch
Golden shiner
Pumpkinseed
Banded sunfish
Brown bullhead
Hexagenia BSA
Hydropsyche
(larva)
Bluegill
Salmo BSA
gairdnerii
Lepomis
macrochirus
Ictalurus
punctatus
Pteronarcys
californica
Baetis sp
Field
Location^)
Silver Lake,
Conn.
Pooley
Lake,
Conn.
A lake in
N.J.
Green-
wich
Lake,
N.J.
2 lakes in
Mass.
-
-
Toxicity,
Active
Ingredient,
ppm (3)
(0)
(0)
(0)
(0)
(0)
0.63 (T1A)
0.102 (T1A)
0.14 (T1A)
0.079 (T2A)
0.086 (T2A)
8.900 (T2A)
0.020 (T2A)
O.OO6 (T2A)
Experimental
Variables
Controlled Reference
or Noted<4> Comments (Year)
ace At 0.10 ppm sunfish kill was extremely heavy, the fish Hoff and
were still dying after 7 days. Many young of the year Westman
fish of all species were killed. (1965)
Kill of pumpkinseeds was slight. A few young of the year
bass were killed at a concentration of 0.10 ppm.
At a concentration of 0.10 the kill of bluegills was very
heavy by the second day after treatment. Seining before
treatment indicated that about 70 percent of the bluegills
were killed, largemouth bass were still common.
The first application at 0.10 percent concentration appeared
to kill about 80 percent of the white perch population and
about 50 percent of bluegills.
The results were quite similar to those' noted above at a
concentration of 0.10. Largemouth bass were abundant
and apparently minimally affected. Bioassay results are
also presented.
a e Dissolved oxygen was measured before and after assay. Carlson
Assays were conducted in Mississippi River water. (1966)
a This paper reports acute toxicity of a number of compounds. Cope
and discusses subacute mortality as well. Effects on repro- (1966)
duction and behavior are also discussed. Data presented as
EC50-
>
%
•o
z
g
X
-------
Malathion
Malathion
Malathion
s
ON
Malathion
3)
o
o
m
S
•o
3)
O
O
Malathion
Malathion
Malathion
Malathion
Malathion
Daphnia
pulex
Simocephalus
serrulatus
Lepomis
gibbosus
Ictalurus
me/as
Pseudopleuronec tes
americanus
Myxocephalus
scorpius
Lepomis
gibbosus
Sewage
organisms
BSA
BOD
Daphnia
magna
Daphnia
carinata
Simocephalus
serrulatus
Daphnia
pulex
Tubifex spp
Limnodrilus spp
Leiostomus
xanthurus
Leiostomus
xanthurus
Cyprinodon
variegatus
BSA
BSA
BSA
BSA
BCFCH
BCFCH
0.002 (T2A)
0.003 (T2A)
161.0 ±19.5(0)
11.6 ±2.0 (O)
16.9 ±3.8 (O)
6.1 ±0.8(0)
2/4 (O)
(O)
0.0009 (SB)
0.0002 (SB)
0.0035 (SB)
16-7 (L4A)
0.01 (SB 182)
0.1 (O)
0.1 (O)
ace
This paper is a study of the amounts of organic thio-
phosphate and their oxygen analogues which accumulate
in liver slices in an in vitro study of insecticides. The
numbers given are for m^lm of chemical (in the case of
Parathion, Malathion, and Guthion — the oxygen analogue)
accumulated in 100 mg (dry weight) of liver in 30 minutes.
The figures given are for mortality in 2 hours when the
amount of chemical was 100.0 mg/kg, given by injection.
Shock loadings of the chemical as high as 100.0 mg/l
were assimilated by microbial systems of 2000.0 mg/l
with no observable toxic effect. Organophosphate insecti-
cides in low concentration stimulated microbial respira-
tion; however, greater concentrations inhibited the
system and eventually destroyed the organisms. The
amount of Organophosphate insecticide required to
inhibit the respiration of freshwater microorganisms was
shown to be function of the amount of organisms
present and not the volume of water in which the
organisms are dispersed.
Concentration reported is for immobilization.
Time for immobilization was 64 hr.
Data cited are for 78 F, but assays were performed at
varied temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
Comment same as above.
Comment same as above, except that time for immobili-
zation was 48 hr and data were cited for 60 F.
Toxicity is reported as the mean lethal dose (LDsg) for
24, 48, and 96 hours.
A concentration of 0.050 ppm killed juvenile spat in
14 days.
At a concentration of 0.1 ppm, the following percent
acety'cholinesterase activity as compared to controls
was found:
L. xanthurus —76
C. variegatus -39
Murphy
(1966)
Murphy
(1966)
Randall
(1966)
Sanders and
Cope
(1966)
Sanders and
Cope
(1966)
Sanders and
Cope
(1966)
Whitten and
Goodnight
(1966)
Butler and
Johnson
(1967)
Butler and
Johnson
(1967)
I
m
Z
O
X
oo
-------
o
o
s
s
rn
o Chemical
i- Malathion
O
I
m
S
O
r~
TJ
jj
O
^ Malathion
2
H
DO Malathion
i
ON
to
Malathion
Malathion
Malathion
Malathion
Malathion
Organism
Stream insects:
Ephemeroptera
Odonata
Plecoptera
Trichoptera
Diptera
Coleoptera
Neuroptera
Mercenaria
mercenaria
American
eel
Mummichog
Striped
mullet
Northern
puffer
Atlantic
silvers! de
Grass shrimp
Sand shrimp
Hermit crab
Atlantic
salmon
Brook
trout
Pimephales
prome/as
Pimephales
promelas
Puntius
puckelli
Pteronarcys
californica
(naiads)
Pteronarcys
californica
(naiads)
Pteronarcella
badia
(naiads)
Classen ia
sabulosa
(naiads)
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study'1) Location'2) ppm'3) or Noted'4'
FR Maine (O)
BSA - (O) ace
FR New (O)
Bruns-
wick
BSA&CH - 9.0 (T4A) acdef
BCFCH - 0.2-0.58(0) acdeq
BSA - 3.7 (T4A) ^cdelm
BSA - 0.01 (T4A) l£dj_f
BSA - 0.010 (T4A) acdef
0.0011 (T4A)
0.0028 (T4A)
Comments
At an application rate of 1 .2 pounds per acre, percent reduc-
tion of the number of major insects is given with 0 to 66%
reduction estimated. Population modifications were not
severe and were considered transitory. Malathion is a safer
chemical than DDT because it is not known to leave per-
sistent residues. Thirty genera of aquatic insects were
studied.
A 37,000 ppb exposure for 4 days caused no mortality of
quahog clams. The LC^Q values (96 hour) for this chemi-
cal extended from 8 to 3,250 ppb for fish, and from 33 to
83 ppb for crustaceans.
Spraying with this chemical at 1/8 Ib per acre was no more
harmful than the application of DDT at 1/4 Ib per acre.
The fish could tolerate 1/45 this amount of malathion for a
10-month test.
Carbon-filtered tap water was used as diluent. Malathion
at indicated range of concentrations did not affect growth
and reproduction, although 20% of fish died at the 0.58
ppm concentration during 7 weeks of exposure.
Tap water was used as diluent. Toxicity data are given as
TLm's in ppm for 24, 48, 96 hr. The pH of the water
averaged 8.3. The study was conducted in India.
Data reported as LCsg at 1 5.5 C in 4 days.
Comment same as above.
Reference
(Year)
Dimond
(1967)
Eisler and
Weinstein
(1967)
Kerswill and
Edwards
(1967)
Mount and
Stephan
(1967)
Mount and
Stephan
(1967)
Rao, et al
(1967)
Sanders and
Cope
(1968)
Sanders and
Cope
(1968)
^
£g
•o
m
z
o
X
00
-------
Malathion
Trout
Red
shiner
BSA
Malathion
Manzate
2-mercaptobenzo-
thiazole
Lepomis
gibbosus
Ictalurus
me/as
Micropterus
dolomieui
Myxocephalus
scorpius
Pseudopleuronectes
americanus
Channel
catfish
(fingerlings)
Daphnia
magna
BSA
OJ
COMMERCI
>
r~
o
Merthiolate
Metacide (dialkyl
nitroaryl thio-
phosphate.
33.4 percent)
Meta-Svstox R
Salmo
gairdnerii
Salmo
trutta
Salvelinus
fontinalis
Salvelinus
namaycush
Ictalurus
punctatus
Lepomis
macrochirus
Lymnaeid
snails
Ovster
Metasystox
•D
J3
O
O
Cyprinus
carpio
C. carpio
Tilapia
mossambica
Cirrhina
mriga/a
Labeo
fimbriatus
BSA
BSA
BSA
BSA
BCF
BSA
0.0050 (T1A)
0.0046 (T2A)
0.0028 (T4A)
0.0023 (T5A)
0.040 (T1 A)
0.036 (T2A)
0.025 (T4A)
0.023 (T5A)
(O)
a c d e f i
2.7 (K1A)
2(K2)
21.2IT2A)
54.0 (T2A)
74.5 (T2A)
2.13IT2A)
5.65 (T2A)
64.5 (T2A)
(O)
(O)
9.0 (T2A)
20.0-25.0 (T2A)
12.0-12.5 (T2A)
17.0 (T2A)
16.0(T2A)
a p
af
ac d e f p
The objects of this investigation were the recovery of
organic micropollutants from subsurface and surface
Missouri waters, characterization and identification of
these substances, and evaluation of their toxic effects,
both acute and long-term, in order to develop methods
for their destruction or removal.
The chemicals were poor inhibitors of brain cholinesterases
in vitro; their oxygen analogs were potent inhibitors.
Tap water was used. Considerable additional data are
presented.
An attempt was made to correlate the biological action
with the chemical reactivity of selected chemical
substances. Results indicated a considerable correla-
tion between the aquarium fish toxicity and anti-
autocatalytic potency of the chemicalsjn marked con-
trast to their toxicity on systemic administration.
Variance and the 95-percent confidence interval (C.I.)
were also determined.
Each test container, 500-ml beaker, was filled with ditch
water. 100% mortality occurred at 1:300,000 and greater.
No effect on exposure to the chemical at 1.0 ppm.
The test animals were conditioned for 48 hours prior to use.
Smith and
Grigoropoulos
(1968)
Murphy, et al
(1968)
Clemens and
Sneed
(1959)
Sollman
(1949)
Willford
(1966)
I
m
O
X
CO
Batte, et al
(1951)
Butler
(1965)
Sreenivasan and
Swaminathan
(1967)
-------
o
o
s
2
m
o Chemical
j> • -
"~ Methoxychlor
O
I
m
5
O
>
r~
•D
3)
o
o
c
H Methoxychlor
Methoxychlor
Methoxychlor
9°
O\
-P.-
Methoxychlor
(100%)
Methoxychlor
Methoxychlor
Organism
Fathead
minnow
Fathead
minnow
Bluegill
Goldfish
Guppy
Daphnia
magna
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Pimephales
promelas
Lepomis
macrochirus
Oncorhynchus
kisutch
Oncorhynchus
tshawytscha
Salmo
gairdnerii
Gasterosteus
aculoatus
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study (1) Location <2) ppm(3)
BSA - 0.035 (T4A)
BSA - 0.064 (T4A)
0.062 IT4A)
0.056 (T4A)
0.120 (T4A)
BSA - 0.0036 (O)
BSA - 0.06 (T4A)
0.06 (T4A)
0.06 (T4A)
0.12 (T4A)
BSA - 0.064 (T4A)
0.062 (T4A)
0.056 (T4A)
0.120 (T4A)
BSA - 0.064 (T4A)
0.062 (T4A)
BSA - 66.2 (T4A)
27.9 (T4A)
62.6 (T4A)
86.4 (T4A)
Experimental
Variables
Controlled
or IMotedW Comments
a_ It was the authors opinion that pH, alkalinity and hardness,
within the usual range in natural waters, had little effect
on the toxic effect of the compounds studied. The values
given are from Henderson, Pickering, and Tarzwell, "The
Relative Toxicity of Ten Chlorinated Hydrocarbon Insecti-
cides to Four Species of Fish" It is interesting that the
different tables from the above book (as reported in this
paper) report widely different values for the same compounds.
This experiment was performed in hard water.
a_ Comment same as above except that experiment was con-
ducted in soft water.
_a_ The indicated concentration immobilized Daphnia in 50
hours.
^ d e f Concentrations were based on percent active ingredient.
a^be c d_f_ Dilution water was usually soft although some studies were
conducted with hard water.
a Bioassay investigations of the new insecticides indicate that
in general the organic phosphorus compounds are not as
toxic to fish as are the chlorinated hydrocarbons. The
toxicity of most of these materials was not significantly
influenced by water quality. Therefore it is to be expected
that the toxicity of these materials will not differ signifi-
cantly in different streams.
.acdjj Chemical dissolved in acetone. TLm expressed in ppb.
Reference
(Year)
Tarzwell
11959)
Tarzwell
(1959)
Anderson
(1960)
Henderson, et al
(1959)
Henderson, et al
(1959)
Tarzwell
(1959)
Katz
(1961)
>
*0
TJ
m
Z
O
X
00
-------
Methoxychlor
(EC 2)
Gam bus/a
affinis
FL
Cal. 2.0 (O)
Methoxychlor
(tech)
Methoxychlor
Salmo
gairdnerii
Gambusia
affinis
BSA
BSA
Methoxychlor
Methoxychlor
Methoxychlor
T3
^ Methoxychlor
Methoxychlor
Methoxychlor
8
i
30
O
O
rn
S
5
Bluegill
Pteronarcys sp
(nymphs)
Prosimulum spp
Cnephia spp
Simulium spp
(larvae)
Daphnia
magna
Simocepha/us
serrulatus
Daphnia
pulex
Mya
arenaria
Crassostrea
virginica
Corbicula
manillensis
Mercenaria
mercenaria
Rang/a
cuneata
BSA
BSA
LCFA
BSA
BSA
BCFCH
20 (T1 A)
0.6 (L1)*
0.9 (L1)**
* Resistant fish
**Nonresistant fish
0.062 (T4A)
0.0014 (T4A)
0.04 (O)
0.0037 (SB)
0.005 (SB)
0.00078 (SB)
(O)
Mixed populations of the indicated test species contained Mulla
in cages were exposed to various insecticidal chemicals (1963)
applied as dilute sprays to ponds 1/16 acre in size. The
indicated toxicant concentration is in Ib/acre, and re-
sulted in a 6 percent mortality for these fish.
The experiment was conducted at 55 F. Fish weighed Cope
0.7 g. (1963)
This paper deals with the resistance of mosquito fish to Boyd and
chlorinated hydrocarbon compounds. Resistant fish Ferguson
were not always less sensitive to these chemicals. (1964)
Assays were conducted in soft water at 25 C. Decrease in Weiss
brain cholinesterase was measured in fish exposed to the (1964)
toxicant.
Experiments were all conducted at 60 F in 1964. The Cope
values were listed as LC^g. (1965)
Stones heavily populated with wild larvae were placed in Jamnback and
troughs of running water containing the toxicant. When Frempong-
the larvae became detached from the rocks and floated Boadu
away, they were assumed to have undergone lethal intoxi- (1966)
cation. The larvae were exposed to the toxicant for 5
minutes, then in clean water for 24 hours. At that time
the number detached amounted to 33 percent.
Concentration reported is for immobilization. Sanders and
Time for immobilization was 64 hr. Cope
Data cited are for 78 F, but assays were performed at (1966)
varied temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
Comment same as above except that time for immobiliza- Sanders and
tion was 48 hr and data were cited for 60 F. Cope
(1966)
Results are recorded as a range of uptake of the chemical Butler
by 5 species of aquatic mollusks. An uptake or concentra- (1967)
tion of 300-1500 ppb resulted.
m
z
O
X
09
O
0
-------
o
o
s
m
o Chemical
r~ Methoxychlor
O
m
S
O
r~
•o
O
0
C
o
Methoxychlor
Methoxychlor
T.
O^ Methylene
^ blue
Methylene
blue
Methylene
blue
Organism
Mercenaria
mercenaria
American
eel
Mummichog
Striped
mullet
Northern
puffer
Atlantic
silverside
Grass shrimp
Sand shrimp
Hermit crab
Lamps His
siliguoidea
L. vertricosa
Anodonta
grandis
Pteronarcys
californica
(naiads)
Microcystis
aeruginosa
Micropetrus
salmoides
(fry)
Ictaluws
punctatus
(fry)
Lepomis
macrochims
(fry)
Salmo
gairdneri
Salmo
trutta
Salvelinus
fonti nails
Salvelinus
namaycush
Ictalurus
punctatus
Lepomis
macrochirus
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study'1' Location(2) ppm(3> or Noted '4>
BSA - (O) ace
FR Red Cedar (O)
River,
Mich.
BSA - 0.0014 (T4A) I c^ej
L - 100 (K) a, etc
BSA - 5.0 (SB3) acdefp
5.0 (SB3)
5.0 (SB3)
BSA - 10.0IT2A) ^f
32.8 (T2A)
22.9 (T2A)
34.0 (T2A)
104 (T2A)
33.0 (T2A)
Comments
At 1,100 ppb exposure for 4 days caused no mortality of
the quahog clam. Although this organism was quite resis-
tant to this chemical, other organisms were susceptible.
A 4 day TLm of 12 to 150 ppb was found for such fish
as the American eel, mummichog, striped mullet, northern
puffer, Atlantic silverside; and between 4 and 12 ppb for
crustaceans (including grass shrimp, sand shrimp, and
hermit crab).
The mussels listed were analyzed for the toxicant and its
metabolites. Mussels may be used as detectors for this
toxicant because they tend to concentrate the chemical
in much higher concentrations than it is ever found in the
water. The amount of chemical applied as a spray was not
specified.
Data reported as LCcjQ at 1 5.5 C in 4 days.
The chemical was tested on a 5-day algae culture, 1x10^
to 2x 106 cells/ml, 75 ml total volume. Chu No. 10
medium was used.
At least 90 percent of the fry survived for a period of 72
hours at the concentration listed.
Variance and the 95-percent confidence interval (C.I.)
were also determined.
Reference
(Year)
Eisler and
Weinstein
(1967)
Bedford, et al
(1968)
Sanders and
Cope
(1968)
Fitzgerald, et al
(1952)
Jones
(1965)
Willford
(1966)
>
^
m
z
o
X
00
-------
Methyl
carbo-
phenothion
Methyl
green
Methyl
parathion
Methyl
parathion
Methyl
parathion
Methyl
parathion
Methyl
parathion
(tech,
80 percent)
o Methyl
O parathion
I (tech)
3 Methyl
O parathion
o
m
S Methyl
O parathion
r
•o
3>
O
O
Chaoborus
astictopus
Microcystis
aeruginosa
Pimephales
prome/as
Fathead
minnow
BSA
Pimephales
promelas
Pimephales
promelas
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Lepomis
macrochirus
Chaoborus
astictopus
Chaoborus
astictopus
Lepomis
macrochirus
BSA
BSA
BSA
BSA
BSA
BSA
FL
BSA
0.0064 (T1 A)
100(K)
10.4IT4A)
7.5 (T4A)
Toxicity value given is for the fourth instar.
8.3 (T4A)
8.3 (T4A)
9.5 (T4A)
2.4 (T4A)
12.0 (T4A)
9.8 (T4A)
8,500 (T1 A)
a, etc The chemical was tested on a 5-day algae culture, 1x10^
to 2 x 106 cells/ml, 75 ml total volume. Chu No. 10
medium was used.
£.£..d_e.i Tests were performed in both hard and soft water. Addi-
tional tolerance limit values are given.
a^ It was the authors opinion that pH, alkalinity and hardness,
within the usual range in natural waters, had little effect on
the toxic effect of the compounds studied. The values
given are from Henderson, Pickering, and Tarzwell, "The
Relative Toxicity of Ten Chlorinated Hydrocarbon Insecti-
cides to Four Species of Fish". It is interesting that the
different tables from the above book (as reported in this
paper) report widely different values for the same compounds.
This experiment was performed in hard water.
Concentrations were based on percent active ingredient.
a Bioassay investigations of the new insecticides indicate that
in general the organic phosphorus compounds are not as
toxic to fish as are the chlorinated hydrocarbons. The
toxicity of most of these materials was not significantly
influenced by water quality. Therefore it is to be expected
that the toxicity of these materials will not differ signifi-
cantly in different streams.
d e_ Soft water primarily was the test medium. TLm's reported
for 24, 48, and 96 hr. Acetone or alcohol used as solvent
or carrier in most cases.
Clear (O)
Lake, other
ponds &
lakes,
Cal.
(O)
0.115(T10A)
Hazel tine
(1963)
Fitzgerald, et al
(1952)
Henderson and
Pickering
(1958)
Tarzwell
(1959)
Henderson, et al
(1960)
Tarzwell
(1959)
Pickering, et al
(1962)
m
Z
O
X
00
The experiment was conducted at 75 F. Fish weighed Cope
0.6 g. (1963)
Methyl parathion applied to 2.3 ppb and 3.3 ppb at Hazeltine
intervals within 2 months was sufficient to control gnats (1963)
in clear lake.
Tests were conducted on bluegill, sunfish, C. astictopus Hazeltine
first instar larvae, and fourth instar larvae, results on (1963)
larvae were as follows:
Fourth instar 0.0058 (T1A)
First instar 0.0012 (T1 A)
(ft
-------
COMMERCI/
>>
r~
O
m
2
o
r~
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3)
O
c
q
CO
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z.
oo
Chemical
Methyl
parathion
(EC7.5)
Methyl
parathion
(tech grade)
Methyl
parathion
Methyl
parathion
Methyl
parathion
Methyl
parathion
Methyl
parathion
Methyl
parathion
Organism
Gambusia
af finis
Bufo
boreas
Scophiopus
hammondi
Procambarus
clarki
Bluegill
Carassius
auratus
Lepomis
macrochirus
Notemigonus
cryso/eucus
Phytoplankton
Zooplankton
Chironomids
Oligochaetes
Fish
Procambarus
clarkii
(juvenile)
Gambusia
affinis
Procambarus
clarkii
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study(l) Location'?) pprr>(3) or Noted'4)
FL Ponds in (O) -
III.
(0)
(0)
BSA - 0.04 (T3A) acdo
BSA - 1.9IT4A) a
BSCH - 10 (O)* acde
1.0(0)*
10.0 (0)**
1.0? (O)**
1.0 (R-30da)
1.0 (O)**
* no response,
1 5 days
•"response,
1 5 days
FL Clear - a
Lake,
Cal.
BSA - < 1 .0 (T5A) acdo
BSA - (O) a_
FO Crowley, (O) c d e p
La.
Comments
When applied at 0.8 pound per acre active ingredient,
10 percent fish mortality occurred in 1 day.
No toad mortality occurred at 0.4 pound per acre
in 1 day.
There was no detectable difference in toxicity to male
or female crawfish.
Assays were conducted in soft water at 25 C. Decrease in
brain cholinesterase was measured in fish exposed to the
toxicant.
Toxicity was determined by measuring acetylcholinesterase
activity in the brains of fish. Concentrations are given in
ppb as either response or not response in 1 5 or 30 days.
The purpose of this field study was to determine the effect
of methyl parathion at 3 ppb or .003 ppm (used to control
gnats Chaoborus astictopus) on other organisms in the
treated area. It appears that the treatments of Clear Lake
had minimal influence upon the biota of the lake with the
exception of the Clear Lake gnat larvae and to a lesser degree.
perhaps, species of the zooplankton. This is a very general
paper and there are no numerical data given.
The pesticides studied in this report are widely used in rice
culture in Louisiana and are toxic to crawfish.
The effect of combinations of pesticides was studied. In
general, the results reflected the extreme levels of Endrin
and Toxaphene resistance in the resistant population. The
results failed to indicate additive effects wherein the combi-
nation mortality exceeded the sum of the mortalities pro-
duced by the individual insecticides.
Experiments were conducted in a flooded rice field. Area
was divided into 4 blocks with a fence, restricting craw-
fish to desired areas. The rearing of crawfish in rice fields
is of considerable commercial importance in Louisiana. No
untoward effect on the crawfish occurred. The chemical
was applied at the rate of 25 Ib/acre.
Reference
(Year)
Mulla, et al
(1963)
Muncy and
Oliver
(1963)
Weiss
(1964)
Weiss and
Gakstatter
(1964)
Cook and
Conners
(1963)
Hendrick and
Everett
(1965)
Ferguson and
Bingham
(1966)
Hendrick, et al
(1966)
•o
m
z
o
00
-------
3
\
)
8
s
m
3)
0
j£
o
i
m
2
Methyl
parathion
Methyl
trithion
(50 percent
EC)
Methyl
zimate
MGK's Evergreen
MGK's 61 03
MGK's 6243
Ortho-MH 30
Mi rex
Mobam (r-benzo-
thienyl-N-methyl
carbamate)
Molinate
(Ordram)
Molinate
(tech)
Molucid
(isobutyl-
triphenyl-
methylamine
Punt/us
puckelli
Gam bus/a
a f finis
Pimephales
prome/as
Salmo
gairdneri
Salmo
gairdneri
Salmo
gairdneri
Channel
catfish
(fingerlings)
Lepomis
macrochirus
Carassius
auratus
Salmo
clarki
Austra/orbis
g/abratus
Daphnia
magna
Rainbow
trout
Bluegill
Pteronarcys
ca/ifornica
(naiads)
Bulinus
truncatus
Biomorph olaria
alexandrina
Lymnaea
caillaudi
BSA
FL
BSA
BSA
BSA
BSA
BSA
FLCH
BSA a
BSA
BSA
FO
O
-D
3)
O
o
c
Ponds-
Bake rs-
field,
Cal.
Rico
Arabia
2.1 (T4A)
(O)
0.25 (T4A)
800 (T1 A)
150 (T1A)
750 (T1 A)
>2.4 (K1A)
5.0 (SB)
0.1-1.0
(SB 224)
75.0 (SB 14)
(0)
0.70 (.46-
1.05(0)
0.29 (O)
0.48 (O)
.00034 (T4A)
1.6-2.0(0)
i c d e I m
ac d e f
a c d i q
ac d e f
a b g
Tap water was used as diluent. Toxicity data are given as
TLm's in ppm for 24, 48, 96 hr. The pH of the water
averaged 8.3. The study was conducted in India.
At 0.5 Ib/acre, 14 percent mortality occurred in 24 hours.
At 2.0 Ib/acre, 76 percent mortality occurred in 24 hours.
The experiments were conducted in cages placed in the
ponds.
The toxicity of this substance was influenced by the quality
of the water (pH, hardness, alkalinity). The chemical was
more toxic in soft water.
The experiment was conducted at 55 F. Fish weighed
0.4 g.
The experiment was conducted at 55 F. Fish weighed
0.5 g.
The experiment was conducted at 55 F. Fish weighed
0.8 g.
Tap water was used. Considerable additional data are
presented.
No histological lesions or effects on hematocrit or serum
protein were observed in the bluegill. Lesions on and
fusion of gills occurred with the trout at the indicated
concentration. Gill changes and accumulation in gold-
fish were found in concentrations of 2.0-1372 ppm in
skin, muscle, liver, and gut.
Seven of the tested compounds failed to meet accepta-
bility criteria — that is, complete kill after 6-hr exposure
to 10 ppm. They were not used in field tests. Field
tests showed WL 8008 to be highly effective.
Toxicity, in terms of median immobilization concentra-
tion (ICso), is presented f or Daphnia; median lethal
concentration (LCgg) values for rainbow trout and
bluegill are reported.
Data reported as LC5Q at 15.5 C in 4 days.
Tests were conducted in the Hod el Malaha canal which
has a maximum discharge of 11,250 m^/day. The mollus-
cicide was dispersed by the injection method, with flow
regulated by a tap, a concentration of 2 ppm being main-
tained during 6 hr of continuous application. The Meyling,
Schutte & Pitchford method was used for determining the
concentration of molluscicide in the canal. No live
organisms were observed for 2,3, and 4 months after
treatment. Egg masses were apparently unaffected.
Rao, et al
(1967)
Mulla and
Isaak
(1961)
Pickering and
Henderson
(1966)
Cope
(1963)
Cope
(1963)
Cope
(1963)
Clemens and
Sneed
(1959)
Van Valin, et al
(1968)
Seiffer and
Schoof
(1967)
Crosby and
Tucker
(1966)
Sanders and
Cope
(1968)
Dawood and
Dazo
(1966)
m
O
X
00
-------
COMMERCI/
&
o
i
m
S
0
r~
-D
3)
Q
O
C
_j
en
CO
V
^l
o
Chemical
Monuron
Monuron
Monuron
Monuron
(25 percent
pellet)
Monuron
(80 percent
WP)
Monuron
Monuron
(CMV)
Monuron-borate
(4-percent
granular)
Monuron-TCA
(3lb/gal)
Organism
Oncorhynchus
kisutch
Protococcus sp
Chlorella sp
Dunaliella
euchlora
Phaeodactylum
tricornutum
Monochrysis
lutheri
Crassostrea
virginica
Penaeus
setiferus
Mugil
cephalus
Phytoplankton
Lepomis
macrochirus
Lepomis
macrochirus
Ictalurus
nebulosis
Lepomis
macrochirus
Daphnia
magna
Salmon
Lepomis
macrochirus
Lepomis
macrochirus
Micropterus
salmoidos
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study*1' Location <2) ppmO) or Noted<4>
BSA and FL - 115(T1) acde
110 (T2)
L - 0.02 (NG) a
0.02 (NG)
0.02 (NG)
0.02 (NG)
0.02 (K)
BCFA&BSA - 2.0(0,12%)
0.55 (0)
16.3 (T2A)
94% (O)
BSA - 40.0 (T4A)
47.0 (T4A)
BSA - 57.0 (T4A)
33.0 (T4A)
BSA - 106 (O) acdiq
BSA - 110.3(T2A)
BSA - 26.0 (T4A)
BSA - 1.5-1. 8 (T4A) -
2.7 (T4A)
Comments
Concentrations were based on percent active ingredient.
Treatment of ponds with 5 and 10 ppm Monuron apparently
caused no mortality of frogs, tadpoles, or fishes.
This paper concerns the growth of pure cultures of marine
plankton in the presence of toxicants. Results were ex-
pressed as the ratio of optical density of growth in the
presence of toxicants to optical density in the basal medium
with no added toxicants. NG = no growth, but the organisms
were viable.
Seawater was pumped continuously into test aquaria.
Salinity, temperature, and plankton fluctuated with tide,
and ambient weather conditions. Some bioassays with
fish were static. Toxicity was reported for the following:
Oyster — 96-hr ECsg — Cone, which decreased
shell growth.
Shrimp — 48-hr ECso — Cone, which killed or
paralyzed 50% of test animals.
Fish- 48-hr EC5Q- Cone, which killed
50%.
Phytoplankton — Percent decrease of CO2 fixation to a
4-hr exposure at 1 .0 ppm chemical
concentration.
Laboratory bioassays indicated that toxicity of the different
formulations evaluated in this varied greatly with the fish
used. Mortality data are expressed as ECig. EC50- etc.
Comment same as above.
Toxicity, in terms of median immobilization concentra-
tion (ICso), is presented.
Data are given as LC5Q.
Laboratory bioassays indicated that toxicity of the different
formulations varied greatly with the fish used. Mortality
data are expressed as EC-jQ. ££50, etc-
Comment same as above.
Reference
(Year)
Bond, et al
(1960)
Ukeles
(1962)
Butler
(1965)
Walker
(1965)
Walker
(1965)
Crosby and
Tucker
(1966)
Bohmont
(1967)
Walker
(1965)
Walker
(1965)
^
T)
TJ
m
D
00
-------
Monuron-TCA
(22 percent
granular)
Monuron-TCA
(11 percent
granular)
Monuron-TCA
(tech)
Monuron
TCA
MS-222
8
m
3)
o
Lepomis
macrochirus
Lepomis
macrochirus
Lepomis
macrochirus
Lepomis
microlophus
Micropterus
salmoides
Pumpkinseed
Lepomis
macrochirus
(eggs)
L. cyanellus
(eggs)
Micropterus
dolomieui
Erimyzon
sucetta
(eggs)
L. macrochirus
(fry)
Salmo
gairdnerii
Salmo
trutta
Salvelinus
fontinalis
Salvelinus
namaycush
Esox
lucius
Lepomis
macrochirus
Micropterus
salmoides
Stizostedion
vitreum
BSA
BSA
BSA
BSA
4.8 (T4A)
3.8 (T4A)
4.5 to 5.0 (T4A)
5.4 (T4A)
4.8 (T4A)
3.3 (T4A)
10(NTE)
10/5(0)
10/4 (O)
10(NTE)
20 (S)
39.0 (T1 A)
39.0 (T2A)
38.5 (T1 A)
37.5 (T2A)
50.7 (T1 A)
50.0 (T2A)
33.8 (T1 A)
33.0 (T2A)
56.0 (T1A)
52.0 (T2A)
45.7 (T1 A)
45.7 (T2A)
42.0 (T1 A)
42.0 (T2A)
49.0 (T1 A)
48.5 (T2A)
Comment same as above.
Comment same as above.
Comment same as above.
Walker
(1965)
Walker
(1965)
Walker
(1965)
Fertilized fish eggs of indicated species were placed in
1 liter of test solution and allowed to hatch. Toxicity
data are presented as concentration in ppm/number
of days survival. Maximum length of test was 8 days.
No food was added. Small bluegill were tested to find
the highest concentration of chemical which did not
cause death in 12 days (S).
Hiltibran
(1967)
I
m
O
a e f Large specimens of given species were usually more resis-
tant to MS-222 than small ones. Trout were more tolerant
at lower temperatures. A safety index of concentration
is suggested.
Marking
(1967)
o
m
S
9
3)
O
O
-------
COMMERCI
r-
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m
S
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r-
TJ
J)
0
o
o
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sp
— J
K>
Chemical
MS-222
Tricaine
methane-
sulfonate
(MS-222)
MS-222
(tricaine
methane-
sulfonate)
MS-222
(tricaine
methane-
sulfonate)
M.S. 222
(tricaine
methane-
sulfonate)
Organism
Ictalurus
punctatus
Sal mo
gairdnerii
Salmo
trutta
Salvelinus
f on final is
Salvelinus
namaycush
Rainbow
trout
Rainbow
trout
Brown
trout
Brook
trout
Lake
trout
Salmo
gairdneri
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study'1 1 Location'2) ppm<3)
BSA - 1 2C
58.0 (T1A)
55.0 (T2A)
51.1 (T4A)
17C
60.5 (T1A)
60.0 (T2A)
60.0 (T4A)
22C
59.8 (T1A)
58.8 (T2A)
58.8 (T4A)
BSA - 100 (SB)
80 (SB)
120 (SB)
135 (SB)
BSA - (O)
BSA - (O)
BCFA - (O)
Experimental
Variables
Controlled
or Noted W Comments
a c d e f Anesthesia was induced within 2 minutes by concentra-
tions of this chemical of 20 to 40 ppm. Concentrations
of 20 to 40 ppm maintained sedation for 6 hours. Safety
indices were determined for the anesthesia of channel
catfish with MS-222.
The toxicity of the chemical is greatly influenced by the
size of the fish and also by temperature.
TLm's are recorded at 12, 17, and 22 degrees centigrade.
It was found that catfish are relatively more resistant when
the anesthetic is dissolved in soft water.
a c f In this assay the chemical was tested for its efficacy as an
anesthetic for the given fish at varied temperatures. Con-
centrations of 80-135 ppm of the chemical anesthetized
all of these fish within 3 min at 7 to 1 7 C. 50 to 60 ppm
induced a moderate rate of anesthesia which could be
maintained for approximately 30 minutes. At 1 5 to 30
ppm, sedation was produced within 15 minutes and
maintained for 5 to 6 hours. Lake trout required larger
doses than the other salmonids for complete anesthesia.
There was no relation between size of fish and efficacy of
MS-222.
— MS-222 can be detected in fish tissues by a modified
Bratton-Marshall method. Interfering substances were more
prevalent in liver and kidney than in .blood and muscle. The
recovery of spiked samples ranged from 89 to 1 1 2 percent.
The method was more accurate for measuring MS-222 in
blood and muscle than in kidney and liver.
a f The residues of MS-222 in selected tissues of fish at 7, 12,
and 17 C and in waters of various hardnesses were measured
by a modified Bratton-Marshall colorimetric method. The
concentrations of drug in the blood, muscle, liver, and
kidney of deeply anesthetized rainbow trout dissipated
rapidly within 1 to 6 hours. The mean concentrations were
18 to 42 ppm in rainbow trout, 1 3 to 44 ppm in brown
trout, 15 to 28 ppm in brook trout, and 15 to 32 ppm in
lake trout.
a Fish anesthetized in 100 mg/l of M.S. 222 at 1 2 C excreted
the drug in free and acetylated forms via the urine during
a 24-hr recovery period in fresh water. Of the M.S. 222 ex-
creted, 77-96% was acetylated. Blood and urine were
cleared of the two fractions of M.S. 222 in 8 and 24 hr.
respectively. Intraperitoneal injections of 10-100 mg/kg
of M.S. 222 did not induce anesthesia; however, the 24-hr
pattern of drug excretion was similar to that observed after
anesthesia by immersion.
Reference
(Year)
Schoettger, et al
(1967)
Schoettger and
Julin
(1967)
Walker and
Schoettger
(1967)
Walker and
Schoettger
(1967)
Hunn, et al
(1968)
^
•n
v
m
z
X
CO
-------
IM-24O4 EC4
N-2788 EC4
N-2790 EC4
N-2790 EC4
Nabam
Naled
(ECS)
Naled
Naled
3 Neburon
Neburon
Gambusia
affinis
Diving
beetle
(larvae)
Chironomid
(larvae)
Dragonfly
(naiads)
Gambusia
affinis
Gambusia
affinis
Gambusia
affinis
Rana
catesbeiana
Protococcus sp
Chlorella sp
Dunaliella
euchlora
Phaeodactylum
trocornutum
Monochrysis
lutheri
Gambusia
affinis
Rana
catesbeiana
Prosimulum spp
Cnephia spp
Simulium spp
(larvae)
Pteronarcys
californica
(naiads)
Protococcus sp
Chlorella sp
Duraliella
euchlora
Phaeodac tylum
tricornutum
Monochrysis
lutheri
Leiostomus
xanthurus
(juvenile)
FL
Cal.
FL
FL
FL
BSA
Cal.
Cal.
Cal.
FL
LCFA
BSA
BSA
BSA
0.1 (K1)
(O)
(O)
(O)
0.1 (K1)
0.2 (K1)
1.0 (K1)
(O)
10.CMK)
10.0 (K)
1.0 (K)
1.0 (NG)
10.0 (K)
1.0 (K)
Ponds in (O)
III.
0.4 (O)
0.008 (T4A)
0.20 (NG)
0.20 (K)
0.20 (NG)
0.20 (NG)
0.004 (K)
0.032 (O)
ac de f
Toxicity value is in Ib/acre. At the given rates, there was
appreciable kill of diving beetle larvae and adults, chirona-
mid larvae, and dragonfly naiads.
Mulla
(1966)
Toxicity value is in Ib/acre.
Comment same as above.
Toxicity value is in Ib/acre. No mortality in tadpoles of
H. catesbeiana occurred during an exposure period of
one week.
This paper concerns the growth of pure cultures of marine
plankton in the presence of toxicants. Results were ex-
pressed as the ratio of optical density of growth in the
presence of toxicants to optical density in the basal
medium with no added toxicants. NG = no growth, but
the organisms were viable.
When applied at 2.0 pounds per acre active ingredient, 20
percent fish mortality occurred in 1 day.
No bullfrog mortality occurred at 0.5 pound per
acre in 1 day.
Stones heavily populated with wild larvae were placed in
troughs of running water containing the toxicant. When
the larvae became detached from the rocks and floated
away, they were assumed to have undergone lethal intoxi-
cation. The larvae were exposed to the toxicant for 5
minutes, then in clean water for 24 hours. At that time
the number detached amounted to 22 percent.
Data reported as LCso at 15-5 C in 4 days.
This paper concerns the growth of pure cultures of marine
plankton in the presence of toxicants. Results were ex-
pressed as the ratio of optical density of growth in the
presence of toxicants to optical density in the basal
medium with no added toxicants. NG = no growth, but
the organisms were viable.
Water temperature was 21 C. The figure reported is a
48-hr EC50.
Mulla
(1966)
Mulla
(1966)
Mulla
(1966)
Ukeles
(1962)
Mulla
(1963)
Jamnback and
Frempong-
Boadu
(1966)
Sanders and
Cope
(1968)
Ukeles
(1962)
O
X
CO
Butler
(1965)
-------
n
o
2
2
m
o Chemical
r~ Neburon
O
m
2
n
r~
Tl
O
u
c
o
c/)
Neburon,
4 percent
granular
3 Nectran
j
i. Neguvon
Nemagon
Neotran
Nigrosine
Organism
Crassostrea
virginica
Penaeus
setiferus
Leiostomus
xanthurus
Phytoplankton
Pimephales
notatus
Notropis
umbratilis
Lepomis
macrochirus
Lepomis
microlophus
Sal mo
gairdneri
Sal mo
gairdnerii
Salmo
trutta
Salvelinus
ton final is
Salvelinus
namaycush
Ictalurus
punctatus
Lepomis
macrochirus
Lepomis
macrochirus
Micropterus
salmoides
Channel
catfish
(fingerlings)
Daphnia
magna
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study d) Location(2) ppm(3)
BCFA & BSA - 0.41 (O)
0.55 (O)
0.22 (T2CFA)
90% (O)
BSA - 0.6 (T4A)
0.9 (T4A)
0.7 (T4A)
0.8 (T4A)
BSA - 7,000 (T 1 8 hr)
BSA - 12.2(T2A)
16.5IT2A)
16.8(T2A)
9.0 (T2A)
32.0 (T2A)
71.0 (T2A)
BSA - 20 (T2A)
20 (T2A)
BSA - 146 (K1A)
L - (0)
Experimental
Variables
Controlled
or Noted*4' Comments
— Seawater was pumped continuously into test aquaria.
Salinity, temperature, and plankton fluctuated with tide,
and ambient weather conditions. Some bioassays with
fish were static. Toxicity was reported for the following:
Oyster — 96-hr EC^rj — Cone, which decreased
shell growth.
Shrimp — 48-hr ECsg — Cone, which killed or
paralyzed 50% of test animals.
Fish — 48-hr ECsg — Cone, which killed
50%.
Phytoplankton — Percent decrease of CO2 fixation to a
4-hr exposure at 1 .0 ppm chemical
concentration.
— Laboratory bioassays indicated that toxicity of the different
formulations evaluated in this varied greatly with the fish
used. Mortality data are expressed as ECig> ECgg, etc-
a -The experiment was conducted at 55 F. Fish were 2-3
in. long.
a f Variance and the 95-percent confidence interval (C.I.) were
also determined.
a c o The response of bluegill and bass fingerlings to nine agri-
cultural chemicals as determined by bioassay using
river water is presented in this report. Bluegills were
more tolerant of the chemicals tested than bass.
_a Tap water was used. Considerable addtional data are
presented.
a Aquaria were treated with 1 .2, 2.4, 3.6, and 7.2 ppm
nigrosine, corresponding to 10, 20, 30, and 60 pounds
Reference
(Year)
Butler
(1965)
Walker
(1965)
Cope
(1963)
Willford
(1966)
Davis and
Hardcastle
(1959)
Clemens and
Sneed
(1959)
Surber
(1943)
>
•o
m
Z
rj
DO
per acre. It was shown that Daphnia could survive the
7.2 ppm concentration for at least 5 days and probably
for much longer.
-------
N-Serve
Nonic218
Noxfish
(5.0% rote-
none, 10.0%
cube extracts
emulsifier)
8
m
3D
o
I Noxfish
2 (5% rotenone)
3J
O
O
c
Panaeus
aztecus
Leiostomus
xanthurus
(juvenile)
Crassostrea
virginica
Penaeus
aztecus
Leiostomus
xanthurus
Phytoplankton
Semotilus
atromaculatus
Cyprinus
carpio
Micropterus
salmoides
Pimephales
promelas
Carassius
auratus
Lepomis
macrochirus
L. cyanellus
Notemigonus
crysoleucas
Ictalurus
nebulosus
marmoratus
Cyprinus
carpio
(eggs)
(fry)
Pimephales
promelas
(eggs)
(fry)
BSA
BCFA & BSA
BSA
BSA
BSA
O.28 (O)
(O)
(O)
0.28 (O)
1.0 (NTE)
1.0 (NTE)
15% (O)
20 to 60 (CR)
0.081 (T3A)
0.147IT3A)
0.159 (T3A)
0.175(T3A)
0.179 (T3A)
0.165IT3A)
0.470 (T3A)
0.247 (T3A)
0.091 (O)
0.081 (O)
0.142 (L)
0.159 (L)
i c d e i
The value, reported Is a eG-tir EG§Q (decreased shell
0rowfh).
Toxicant chemicals were evaluated in seawaterat tempera-
tures averaging about 28 C. The values are for 24-hr EC5Q
or enough to cause loss of equilibrium or mortality. No
effect occurred at 1.0 pprn.
Water temperature was 16 C. No effect was noticed on
exposure to 1.0 ppm.
Seawater was pumped continuously into test aquaria.
Salinity, temperature, and plankton fluctuated with tide,
and ambient weather conditions. Some bioassays with
fish were static. Toxicity was reported for the following:
Oyster — 96-hr ECso — Cone, which decreased
shell growth.
Shrimp — 48-hr £650 — Cone, which killed or
paralyzed 50% of test animals.
Fish— 48-hr EC5Q - Cone, which killed
50%.
Phytoplankton — Percent decrease of CC<2 fixation to a
4-hr exposure at 1 .0 ppm chemical
concentration.
Test water used was freshly aerated Detroit River water. A
typical water analysis is given. Toxicity is expressed as
the "critical range" (CR), which was defined as that
concentration in ppm below which the 4 test fish lived for
24 hr and above which all test fish died. Additional data
are presented.
Such variables as temperature, species, and size of fish were
studied. Toxicity is expressed as LDsg for 72 hr. Smaller
concentrations of rotenone were required when used in
conjunction with sulfoxide. The data shown are for 70 F.
The chemical was considerably more toxic at this tempera-
ture than at 40 F for all fish species.
Butler
11965)
Toxicity is reported as
in ppm, at 75 F.
Butler
(1965)
Gillette, etal
(1952)
Hester
(1959)
I
m
O
X
CD
Hester
(1959)
-------
o
o
z
m
an
o
o
m
2
o
>
r-
T>
3)
o
o
I
m
Chemical
Oil.
crude
Omazene
OMPA
(70%)
OMPA
OMPA
OMPA
OMPA
(tech,
90 percent)
OMS-3
(EC2)
QMS 44
(Bayer
37343)
Organism
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study(1> Location<2) ppm(3) or NotedW)
Comments
Reference
(Year)
Nytron
Penaeus
aztecus
L
— 0.001 5 (O) a Toxicant chemicals were evaluated in sea water at tempera-
tures averaging about 28 C. The values are for 24-hr ECsg
or enough to cause loss of equilibrium or mortality.
Butler
(1965)
Daphnia
magna
Onchorynchus
tshawYtscha
Pimephales
promelas
Fathead
minnow
BSA
BSA
BSA
BSA
Pimephales
promelas
Pimephales
promelas
BSA
BSA
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Gambusia
affinis
Prosimulum spp
Cnephia spp
Simulium spp
(larvae)
FL
LCFA
Ponds in
10,000 (T1A)
4,613 (T2A)
752 (T3A)
0.83 (T1A)
0.83 (T2A)
135(T4A)
135 (T4A)
121 (T4A)
121 (T4A)
88 (T4A)
1 20 (T4A)
680 (T4A)
22 (T4A)
(O)
0.4 (O)
a c d e
This study is concerned with waste oil emulsifiers.
Concentrations were based on percent active ingredient.
Tests were performed in both hard and soft water. Addi-
tional tolerance limit values are given.
It was the authors opinion that pH, alkalinity and hardness,
within the usual range in natural waters, had little effect
on the toxic effect of the compounds studied. The values
given are from Henderson, Pickering, and Tarzwell, "The
Relative Toxicity of Ten Chlorinated Hydrocarbon Insecti-
cides to Four Species of Fish". It is interesting that the
different tables from the above book (as reported in this
paper) report widely different values for the same compounds.
This experiment was performed in hard water.
Concentrations were based on percent active ingredient.
Bioassay investigations of the new insecticides indicate that
in general the organic phosphorus compounds are not as
toxic to fish as are the chlorinated hydrocarbons. The
toxicity of most of these materials was not significantly
influenced by water quality. Therefore it is to be expected
that the toxicity of these materials will not differ signifi-
cantly in different streams.
Soft water primarily was the test medium. TLm's reported
for 24, 48, and 96 hr. Acetone or alcohol used as solvent
or carrier in most cases.
Dowden
(1962)
Bond, et al
(1960)
Henderson and
Pickering
(1958)
Tarzwell
(1959)
Henderson, et i
(1960)
Tarzwell
(1959)
When applied at 1.0 pound per acre active ingredient, 100
percent mortality occurred in 1 day.
Stones heavily populated with wild larvae were placed in
troughs of running water containing the toxicant. When
the larvae became detached from the rocks and floated
away, they were assumed to have undergone lethal intoxi-
cation. The larvae were exposed to the toxicant for 5
minutes, then in clean water for 24 hours. At that time the
number detached amounted to 89 percent.
m
z
o
X
00
Pickering, et al
(1962)
Mulla, et al
(1963)
Jamnback and
Frempong-
Boadu
(1966)
-------
OMS-116
(EC2)
QMS-144
Gambusia
affinis
Prosimulum spp
Cnephia spp
Simulium spp
(larvae)
FL
LCFA
Ponds in (O)
III.
0.4 (O)
OMS-315
OMS-437
OMS-595
(SD8447)
OMS-648
OIVIS-658
OMS-659
OMS-711
8
£ OMS-712
OMS-754
OMS-868
Prosimulum spp
Cnephia spp
Simulium spp
(larvae)
Prosimulum spp
Cnephia spp
Simulium spp
(larvae)
Prosimulum spp
Cnephia spp
Simulium spp
(larvae)
Prosimulum spp
Cnephia spp
Simulium spp
(larvae)
Prosimulum spp
Cnephia spp
Simulium spp
(larvae)
Prosimulum spp
Cnephia spp
Simulium spp
(larvae)
Prosimulum spp
Cnephia spp
Simulium spp
(larvae)
Prosimulum spp
Cnephia spp
Simulium spp
(larvae)
Prosimulum spp
Cnephia spp
Simulium spp
(larvae)
Prosimulum spp
Cnephia spp
Simulium spp
(larvae)
LCFA
LCFA
LCFA
LCFA
LCFA
LCFA
LCFA
LCFA
LCFA
LCFA
4.0(0)
0.4 (0)
0.4 (O)
0.4 (O)
4.0 (O)
0.4 (O)
0.4 (O)
0.4 (O)
4.0 (O)
0.04 (0)
When applied at 0.5 pound per acre active ingredient, 1OO
percent mortality occurred in 1 day.
Stones heavily populated with wild larvae were placed in
troughs of running water containing the toxicant. When
the larvae became detached from the rocks and floated
away, they were assumed to have undergone lethal intoxi-
cation. The larvae were exposed to the toxicant for 5
minutes, then in clean water for 24 hours. At that time the
number detached amounted to 8 percent.
Comment same as above except that at that time the
number detached amounted to 35 percent.
Comment same as above except that at that time the
number detached amounted to 61 percent.
Comment same as above except that at that time the
number detached amounted to 9 percent.
Comment same as above except that at that time the
number detached amounted to 38 percent.
Comment same as above except that at that time the
number detached amounted to 35 percent.
Comment same as above except that at that time the
number detached amounted to 44 percent.
Comment same as above except that at that time the
number detached amounted to 10 percent.
Comment same as above except that at that time the
number detached amounted to 9 percent.
Comment same as above except that at that time the
number detached amounted to 15 percent.
Comment same as above except that at that time the
number detached amounted to 11 percent.
Mulla, et al
(1963)
Jamnback and
Frempong-
Boadu
(1966)
Jamnback and
Frempong-
Boadu
(1966)
Jamnback and
Frempong-
Boadu
(1966)
Jamnback and
Frempong-
Boadu
(1966)
Jamnback and
Frempong-
Boadu
(1966)
Jamnback and
Frempong-
Boadu
(1966)
Jamnback and
Frempong-
Boadu
(1966)
Jamnback and
Frempong-
Boadu
(1966)
Jamnback and
Frempong-
Boadu
(1966)
Jamnback and
Frempong-
Boadu
(1966)
Jamnback and
Frempong-
Boadu
(1966)
m
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O
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GO
-------
o
0
s
2
m
o Chemical
i- OMS-869
0
m
S
O
r~
3)
O Organochlorines
C (pp'-DDT, pp'-
£j DDE. HEOD,
f Endrin)
3
J
o
Organo-
phosphorus
pesticides
Ortho 5305
EC2
Toxicity,
Bioassay Active
or Field Field Ingredient,
Organism Study''') Location'?) ppm'3)
Prosimulum spp LCFA - 4.0 (O)
Cnephia spp
Simulium spp
(larvae)
Ammodytes FO Britain (O)
lanceolatus
Phalacrocorax
aristotelis
Phalacrocorax
carbo
Gadus
morrhua
Mytilus
edulis
Somateria
mollissima
Cardium
edule
Paste/la
vulgata
Homarus
vulgaris
Calcinus
maenas
Cancer
poguras
Pleuronectes sp
Clupea
harengus
Gadus
merlangus
Sula
bassana
Halichoerus
grypus
Delphinus
del phis
Leiostomus FECH Atlantic (O)
xanthurus and
Cyprinodon Gulf
variegatus Coasts
Gambusia FL Cal. 0.8 (K1)
affinis
Experimental
Variables
Controlled Reference
or Noted'4) Comments (Year)
a Stones heavily populated with wild larvae were placed in Jamnback and
troughs of running water containing the toxicant. When Frempong-
the larvae became detached from the rocks and floated Boadu
away they were assumed to have undergone lethal intoxi- (1966)
cation. The larvae were exposed to the toxicant for 5
minutes, then in clean water for 24 hours. At that time the
number detached amounted to 13 percent.
— Residues of organochlorine insecticides tended to be greater Robinson, et al
in marine organisms of the higher trophic levels, but the (1967)
tendency was not found in all food chains.
— Describes method to detect low level concentration of pollu- Holland, et al
tion by measuring the degree of inhibition of acetyl cholin- (1967)
esterase (AChE). Of 93 samples from 43 stations, 1 7 showed
less than 90% of normal AChE activity.
— At a concentration of 0.2 Ib/acre, 88% mortality of the fish Mulla
occurred in 24 hours. At 0.8 Ib/acre, 100% mortality (1966)
occurred.
^
SQ
•o
m
2
g
X
00
-------
Ortho 5353
EC2
Ovex,
Tech.
Ovex
Oxydemeton-
methyl
Paramar-50
Para-oxon
Para-oxon
8
m
a
Q
Para-oxon
Para-oxon
Paraoxon
S
O Paraoxon
Gambusia
affinis
Rainbow
trout
Pimephales
promelas
Pteronarcys
californica
(naiads)
Cyprinus
carpio
Tilapia
massambica
Cirrhina
mrigala
Labeo
fimbriatus
Barbus
machecola
Pimephales
promelas
Fathead
minnow
Pimephales
promelas
Pimephales
promelas
FL
BSA
BSA
BSA
BSA
Col. 1.CHK1) —
0.620 (T4A)
2.5 (T4A) a c d e f
BSA
BSA
BSA
BSA
Lepomis
gibbosus
Lepomis
gibbosus
Ictalurus
melas
Pseudopleuronectes
americanus
Myxocephalus
scorpius
BSA
0.035 (T4A)
6.5 (T2A)
4.0-5.0 (T2A)
5.0 (T2A)
7.5 (T2A)
2.0 (T2A)
0.33 (T4A)
.25 (T4A)
a c d e f
a c d e f p
a c d e f
0.33 (T4A)
0.33 (T4A)
adef
2/4 (O)
0.120 ±0.022 (O)
0.122 ±0.005 (O)
0.041 ±0.006 (O)
0.076±0.010 (O)
Toxicity value is in Ib/acre.
The values reported are given as LCgrj-
The toxicity of this substance was not influenced by the
quality of the water (pH, hardness, alkalinity).
Data reported as (-650 at 15.5 C in 4 days.
The test animals were conditioned for 48 hours prior
to use.
Mulla
(1966)
Cope
(1965)
Pickering and
Henderson
(1966)
Sanders and
Cope
(1968)
Sreenivasan and
Swanithan
(1967)
Tests were performed in both hard and soft water. Addi-
tional tolerance limit values are given.
It was the authors opinion that pH, alkalinity and hardness,
within the usual range in natural waters, had little effect
on the toxic effect of the compounds studied. The values
given are from Henderson, Pickering, and Tarzwell, "The
Relative Toxicity of Ten Chlorinated Hydrocarbon Insecti-
cides to Four Species of Fish". It is interesting that the
different tables from the above book (as reported in this
paper) report widely different values for the same compounds.
This experiment was performed in hard water.
Concentrations were based on percent active ingredient.
Bioassay investigations of the new insecticides indicate
that in general the organic phosphorus compounds are
not as toxic to fish as are the chlorinated hydrocarbons.
The toxicity of most of these materials was not signifi-
cantly influenced by water quality. Therefore it is to be
expected that the toxicity of these materials will not
differ significantly in different streams.
The figures given are for mortality in 2 hours when the
amount of chemical was 16 mg/kg, given by injection.
This paper is a study of the amounts of organic thiophos-
phate and their oxygen analogues which accumulate in liver
slices in an in vitro study of insecticides. The numbers
given are for mflm of chemical (in the case of Parathion,
Malathion, and Guthion—the oxygen analogue) accumu-
lated in 50 mg of liver (wet weight) in 10 minutes.
Henderson and
Pickering
(1958)
Tarzwell
(1959)
O
X
CD
Henderson, et al
(1959)
Tarzwell
(1959)
Murphy
(1966)
Murphy
(1966)
-------
COMMERCIA
r~
o
m
S
O
•o
3)
O
0
C
£^
in
V
oo
0
Chemical
Paraquat
(cation)
Paraquat
Paraquat
Paraquat
Paraquat
Paraquat
-
Paraquat
Organism
Lepomis
macrochirus
Lepomis
macrochirus
Micropterus
salmoides
Pimephales
promelas
Ictalurus
punctatus
Salmo
gairdnerii
Spirode/a
polyrhyza
Lemna
minor
Wolffiella
floridana
Azolla
caroliniana
Wolffia
columbiana
Lemna
minor
Spirodela
polyrhyza
Wolffia
columbiana
Fundulus
similis
(juveniie)
Oyster
Penaeus
aztecus
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study!1' Location'2) ppm'3)
BSA - 400 (T1 A)
BSA - 5 (O)
5(0)
5 (O)
5(0)
5(0)
BSA - (O)
FL Fla. (O)
BSA - (O)
BCF - (0)
L - (0)
Experimental
Variables
Controlled
or Noted'4) Comments
— The bioassay methods employed in this experiment were
not given in the paper but it was stated that the same pro-
cedures were employed as in previous work.
— Toxicity to fish was determined as the threshold concen-
tration (LD-|o) in 96 hr at 75 F (65 F for trout). Herbi-
— cidal evaluations are also presented.
-
_
-
a 0.01 ppm caused 82% chlorosis in 7 days.
0.01 ppm caused 72% chlorosis in 7 days.
0.01 ppm caused 62% chlorosis in 7 days.
0.01 ppm caused 40% chlorosis in 7 days.
0.01 ppm caused 3% chlorosis in 7 days.
Light intensity was kept at 500 foot-candles for 14 hours
per day. Light has been shown to increase the rate of kill
with paraquat.
Test containers were plastic petri dishes.
— Common duckweed and watermeal in small ponds can be
controlled with paraquat at rates as low as 0.25 ppmw.
but rates greater than 0.5 ppmw are required for control
in ponds infested with watermeal.
a Water temperature was 19 C. No effect was noticed on
exposure to 1.0 ppm.
a No effect on exposure to the chemical at 1 .0 ppm.
a Toxicant chemicals were evaluated in sea water at tempera-
tures averaging about 28 C. The values for 24-hr EC$Q or
Reference
(Year)
Davis and
Hughes
(1963)
Lawrence, et al
(1965)
Blackburn and
Weldon
(1965)
Blackburn and
Weldon
(1965)
Butler
(1965)
Butler
(1965)
Butler
(1965)
•o
m
Z
O
00
enough to cause loss of equilibrium or mortality. No effect
occurred at 1.0 ppm.
-------
Paraquat
Paraquat
Paraquat
Paraquat
w
^ Paraquat
00
Parathion
8
m
3D
o
o
m
2
Crassostrea
virginlca
Penaeus
aztecus
Fundulus
similis
Phytoplankton
BCFA &
BSA
Parathion (15 per-
cent) 0,0-Diethyl-
o-p-nitrophenyl
thiophosphate)
Parathion
Parathion
(20% tech, para-
thion and 80%
triton X-100)
Pteronarcys sp
(nymphs)
Daphnia
magna
Simocephalus
serrulatos
Daphnia
pulex
Pteronarcys
ca/ifornica
(naiads)
Bluegill
Rainbow
trout
Brown
trout
Lymnaeid
snails
Simulium sp
(larvae)
Rainbow
trout
Eastern brook
trout
BSA
BSA
BSA
BSA
BSA
BSA
FR
Streams,
S. C.
and
Fla.
1.O (NTE)
1.0 (NTE)
1.0 (NTE)
53% (O)
>1000(T4A)
11.0 (9.1-12.2)
(O)
4.0 (SB)
3.7 (SB)
100 (NTE)
(O)
(O)
0.5-1.0 (O)
ac d i q
BCFA
0.05-1.0 (K0%)
Seawater was pumped continuously into test aquaria.
Salinity, temperature, and plankton fluctuated with tide,
and ambient weather conditions. Some bioassays with
fish were static. Toxicity was reported for the following:
Oyster- 96-hr £659 — Cone, which decreased
shell growth.
Shrimp - 48-hr £659 — Cone, which killed or
paralyzed 50% of test animals.
Fish - 48-hr EC50 - Cone, which killed 50%.
Phytoplankton — Percent decrease of CC>2 fixation to a
4-hr exposure at 1 .0 ppm chemical
concentration.
Experiments were all conducted at 60 F in 1964. The
values were listed as LC5Q.
Toxicity, in terms of median immobilization concentration
), is presented.
Butler
(1965)
Concentration reported is for immobilization.
Time for immobilization was 64 hr.
Data cited are for 78 F, but assays were performed at
varied temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
Data reported as LC5Q at 15.5 C in 4 days.
A concentration of 0.2 ppm was near the concentration
threshold for bluegills. Concentrations of 0.063, 0.189, and
0.378 ppm did not kill 1 -inch rainbow and brown trout.
Each test container, 500-ml beaker, was filled with ditch
water. 100% mortality occurred in concentrations of
1 :400,000 and greater.
In slow-moving streams in Florida, parathion at the indi-
cated concentrations eliminated blackfly larvae for dis-
tances up to 1.6 miles. In South Carolina, 100 percent
reductions for distances of up to 2.8 miles was obtained.
Data are presented as percent larval detachment in 1,2,
and 3-days time.
Spring water (46 F) was used. This flow rate was 10 GPM.
The chemical was added by continuous drip dispenser.
0.01 ppm kill mosquito larvae.
Cope
(1965)
Crosby and
Tucker
(1966)
Sanders and
Cope
(1966)
Sanders and
Cope
(1968)
Linduska and
Surber
(1948)
Batte, et al
(1951)
Davis, et al
(1957)
Hoffman
(1957)
O
X
09
-o
30
O
O
-------
o
o
s
5
m
o Chemical
r~ Parathion
O
m
S
r>
r~
J
o
o
c
o
— fl
C/)
Parathion
Parathion
Parathion
g
0
j
Parathion
Parathion
Parathion
Parathion
Parathion
Organism
Various
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study'1) Location'2) ppm'3)
FL Salt (O)
Lake
Co.,
Utah
Experimental
Variables
Controlled
or Noted'4' Comments
— The chemical was applied at 0.05 Ib/acre.
Careful application of the chemical at the above concentra-
tion controlled mosquito larvae without loss of fish. At the
above concentration no adverse effects were observed in
mammals, birds, reptiles, and amphibians although some
frogs were killed by the application of parathion at several
times the normal concentration.
Reference
(Year)
Graham and
Anderson
(1958)
Invertebrates were not affected uniformly. Crustaceans were not
harmed, nor were larvae of the insect family Ephydridae.
Spiders and aquatic insects other than Ephydridae were adversely
Pimephales
promelas
Lepomis
macrochirus
Artemia
salina
Fathead
minnow
Daphnia
magna
Pimephales
promelas
Gambusia
affinis
Pimephales
promelas
Lepomis
macrochirus
Micropterus
salmoides
Notemigonus
crysoieucas
BSA - 1.4(T4A)
0.71 (T4A)
BSA - 0.43 (L<1)
BSA - 1.6IT4A)
BSA - 0.0008 (O)
BSA - 1.4IT4A)
BSA - 0.004 (K 33%)
BSA - 1.4(T4A)
0.700 (T4A)
BSA - 0.1 (O)
0.1 (0)
0.1 (0)
affected in varying degrees. Aquatic beetles seemed to be af-
fected more seriously than other insects excepting mosquito
larvae.
a c d e f Tests were performed in both hard and soft water. Addi-
tional tolerance limit values are given.
a i Rock salt was used in rearing all cultures employed in bio-
assay work. The optimum salt concentration was 3.5%.
a It was the authors opinion that pH, alkalinity and hardness.
within the usual range in natural waters, had little effect on
the toxic effect of the compounds studied. The values given
are from Henderson, Pickering, and Tarzwell, "The Rela-
tive Toxicity of Ten Chlorinated Hydrocarbon Insecticides
to Four Species of Fish". It is interesting that the different
tables from the above book (as reported in this paper) re-
port widely different values for the same compounds.
a The indicated concentration immobilized Daphnia in 50
hours.
a d e f Concentrations were based on percent active ingredient.
a Chemicals were dissolved in acetone, and tests were run in
triplicate. Toxicity is given as avg. percent fish killed in
24 hr.
a Bioassay investigations of the new insecticides indicate that
in general the organic phosphorus compounds are not as
toxic to fish as are the chlorinated hydrocarbons. The
toxicity of most of these materials was not significantly
influenced by water quality. Therefore it is to be expected
that the toxicity of these materials will not differ signifi-
cantly in different streams.
^£^_[ Tnis Paper reports the effect of insecticides in reducing the
anticholinesterase in a fish brain within 2-8 hours. The in-
hibition of the enzyme was a function of the concentration
of the insecticide, extent of exposure, and specific chemical
nature of the compound.
Henderson and
Pickering
(1958)
Tarpley
(1958)
Tarzwell
(1959)
Anderson
(1960)
Henderson, et al
(1960)
Lewallen
(1959)
Tarzwell
(1959)
Weiss
(1959)
.
TJ
•o
m
Q
X
00
-------
Parathion,
(tech,
25% active
in xylene)
Parathion
(tech
grade emulsi-
fied in exlene)
Palathion
(50 percent
EC)
Parathion
s
oo
Parathion
Carassius
auratus
Acroneuria BSA
pacifica
Pteronarcys
californica
Arctopsyche
grandis
Hydropsyche BSA
californica
Acroneuria
pacifica
Arctopsyche
grandis
Pteronarcys
californica
Gambusia F L
affinis
Anopheles BSA
quadrimacula tus
Aedes
aegypti
A. taeniorhynchus
Micropterus BSA
salmoides
Pimephales
promelas
Ponds—
Bakers-
field,
Cal.
Parathion
8
m
3)
O
r~ Parathion,
g (tech.
m 99 percent)
2
5
r-
TJ
3)
O
0
C
0
Salmo
gairdnerii
(one wk. old
sac fry)
(one mo. old
feeding fry)
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
BSA
BSA
BSA
0.1 (O)
0.0001 (T4A)
0.0032 (T4A)
0.001 (T4A)
0.00043 (T4A)
0.001 (T4A)
0.007 (T4A)
0.0086 (T4A)
(O)
0.01 (K1)
0.005 (O)
0.005 (O)
0.5 (O)
0.5 (O)
a c e f I n
Assays were conducted in hard water.
a c d e I m
0.2 (K 0%)
2.0 (K 0%)
0.2 (K 0%)
2.0 (K 80%)
1.3 (T4A)
0.095 (T4A)
2.7 (T4A)
0.056 (T4A)
a c d e
Test water was obtained from a mountain stream.
At 0.1 Ib/acre, 22 percent mortality occurred in 24
hours. At 0.4 Ib/acre, 92 percent mortality occurred
in 24 hours. The experiments were conducted in cages
placed in the ponds.
4th instar larvae of mosquitos were used in this bioassay.
At the indicated concentrations, the following mortalities
occurred:
Anopheles quadrimaculatus 94%
A edes aegyp ti 52%
A. taeniorhynchus 78%
Adsorption was determined by use of P32 labeled parathion.
The degree of reaction to the cholinesterase-inhibiting in-
secticides is not only a function of time and concentration,
but also of chemical and biological species. This paper re-
ports many analyses of brain cholinesterase activity which
is expressed as percentage of normal. The data are reported
as LTso which was the time required for 0.5 ppm of the
chemical to kill 50 percent of the fish. For bass the LT^rj
was 24 hr and for the fathead 72 hr.
Results are averages of triplicate tests. Toxicity is reported
as percent mortality (K %).
Soft water primarily was the test medium. TLm's reported
for 24, 48, and 96 hr. Acetone or alcohol used as solvent
or carrier in most cases.
Gaufin
(1961)
Gaufin, et al
(1961)
Mulla and
Isaak
(1961)
Schmidt and
Weidhaas
(1961)
Weiss
(1961)
m
O
X
00
Le wall en and
Wilder
(1962)
Pickering, et al
(1962)
-------
COMMERCI
r-
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S
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TJ
3)
o
O
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q
in
W
T*
00
•^
Chemical
Parathion,
emulsible
concentrate
(25 percent)
Parathion
Parathion
(EC2)
"arathion
(tech.
95 percent
active in
acetone)
Parathion
Parathion
Parathion
Bioassay
or Field
Organism Study (""
Pimephales BSA
promelas
Lepomis
macrochirus
Carassius
auratus
Green
sunfish
Largemouth
bass
Culex pipiens BSA
quadrimaculatus
Gam bus/a FL
affinis
Bufo
boreas
Scaphiopus
hammondi
Pteronarcys BSA
californica
(naiad)
Acroneuria
pacifica
(naiad)
Gammarus BSA
lacustris
Bluegill BSA
Carassius BSCH
auratus
Lepomis
macrochirus
Notemigonus
crysoleucas
Toxicity, Experimental
Active Variables
Field Ingredient, Controlled
Location!2) ppm'3) or Noted!4'
3.0 (T4A) ^cde
Large 0.58 (T4A)
Small 0.26 (T4A)
2.6 (T4A)
1.7 (T4A)
,0.76 (T4A)
(0) c
Ponds in (O) -
III.
0.0320 (T4A) c d e f
0.0028 (T4A)
0.0128(T4A) £i
0.095 (T4A) a
10.0 (O)* acde
1.0(0)*
0.1 (0)**
0.1 (0)***
10.0 (O)*
1.0(0)*
0.1? (O)*
0.1 (0)***
'response.
1 5 days
**no response.
1 5 days
***no response.
30 days
Comments
Soft water primarily was the test medium. TLm's reported
for 24, 48, and 96 hr. Acetone or alcohol used as solvent
or carrier in most cases.
Tests were conducted in tap water and artificially polluted
tap water. The values reported are the concentration range
for an LCgo, 0.034 to 0.1100 ppm for polluted and 0.0072
to 0.0140 ppm for tap water.
When applied at 0.4 pounds per acre active ingredient, 96
percent fish mortality occurred in 1 day.
No toad mortality occurred at 0.4 pound per acre in 1 day.
A. pacifica was much more sensitive to chlorinated hydro-
carbons and to organic phosphate insecticides than P,
californica.
Emulsible concentrates were prepared from technical grade
insecticides with acetone as the solvent.
Symptoms prior to death were observed and recorded on
graphs.
Assays were conducted in soft water at 25 C. Decrease in
brain cholinesterase was measured in fish exposed to the
toxicant.
Toxicity was determined by measuring acetylcholinesterase
activity in the brains of fish. Concentrations are given in
ppb as either response or no response in 1 5 or 30 days.
Reference
(Year)
Pickering, et al
(1962)
Le wall en and
Wilder
(1963)
Mulla, et al
(1963)
Jensen and
Gaufin
(1964)
Nebeker and
Gaufin
(1964)
Weiss
(1964)
Weiss and
Gaks tatter
(1964)
*
-o
g
00
-------
Parathion
Parathion
00
Parathion
Parathion
8
I
3D
Q
>
O
rn
-o
8
O
Parathion
Parathion
Acroneurla
pacifica
Ephemerella
grandis
Gammarus
lacustris
Pteronarcys
californica
Arctopsyche
grandis
Pteronarcys
californica
Acroneuria
pacifica
Ephemerella
grandis
Hydropsyche
californica
Daphnia
magna
Gammarus
lacustris
Bluegill
sunfish
Fathead
minnow
Lepomis
gibbosus
Lepomis
gibbosus
Ictalurus
melas
Pseudopleuronec tes
americanus
Myxocephalus
scorpius
Sewage
organisms
BSA
BSA
BSA
BOD
Simocephalus
serrulatus
Daphnia
pulex
BSA
0.0028 (T4A)
0.003 (T4A)
0.0128 (T4A)
0.032 (T4A)
0.007 (T4A)
0.03 (T4A)
0.003 (T4A)
0.003 (T4A)
0.0004 (T4A)
0.0008 (T 50 hr A)
0.01 (T4A)
0.06 (T4A)
1.4IT4A)
0/4 (O)
19.97 ±7.09(0)
14.52 ± 1.56 (O)
5.20 ±0.81 (O)
0.4 ± 0.2 (O)
(O)
Additional TLm data are given.
Gaufin, et al
(1965)
0.00037 (SB)
Unspecified chemical characteristics of assay water were
determined by standard methods. General comments
were made concerning "standardized" conditions, use of
"soft" water, and use of emulsifying agents. Additional
data are presented.
The figures given are for mortality in 2 hours when the
amount of chemical was 40 mg/kg, given by injection:
number dead/number injected.
This paper is a study of the amounts of organic thiophos-
phate and their oxygen analogues which accumulate in
liver slices in an in vitro study of insecticides. The num-
bers given are for mjUm of chemical (in the case of Para-
thion, Malathion, and Guthion— the oxygen analogue)
accumulated in 100 mg (dry weight) of liver in 30
minutes.
Shock loadings of the chemical as high as 15.0 mg/l were
assimilated by microbial systems of 500.0 mg/l with no
observable toxic effect. Organophosphate insecticides
in low concentration stimulated microbial respiration;
however, greater concentrations inhibited th'e system and
eventually destroyed the organisms. The amount of
organophosphate insecticide required to inhibit the respira-
tion of freshwater microorganisms was shown to be func-
tion of the amount of organisms present and not the
volume of water in which the organisms are dispersed.
Concentration reported is for immobilization.
Time for immobilization was 48 hr.
Data cited are for 60 F, but assays were performed at
varied temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
Gaufin, et al
(1965)
Murphy
(1966)
Murphy
(1966)
I
m
O
X
a
Randall
(1966)
Sanders and
Cope
(1966)
-------
8
m
o Chemical
r~ Parathion
O
X
m
S
O Parathion
r~
3J
O
O
O Parathion
Parathion
Parathion
£
00
Os
Parathion
Bioassay
or Field
Organism Study''')
Tubifex spp BSA
Limnodrilus spp
Leiostromus BCFCH
xanthurus
Cyprlnodon
variegatus
Micropterus BSA
salmoides
Pteronarcys BSA
californica
(naiads)
Pteronarcys BSA
californica
(naiads)
Pteronarcella
bad/a
(naiads)
Claasenia
sabulosa
(naiads)
Lepomis BSSB
macrochirus
Toxicity,
Active
Field Ingredient,
Location'2^ ppm'3)
5-2 (L4A)
0.01 (0)
0.01 (0)
2.0 (O)
5.0 (K3hr)
0.0054 (T4A)
0.0054 (T4A)
0.0042 (T4A)
0.0015 (T4A)
0.0075, 0.032,
and 0.087 (O)
Experimental
Variables
Controlled
or Noted'*)
ace
a
a e
a cd e f
a cd e f
act
Comment!
Toxicity is reported as the mean lethal dose (LDgg) for 24,
48, and 96 hours.
At a concentration of .01 ppm, the following percent
acetylcholinesterase activity as compared to controls
was found:
L. xanthurus — 10
C. variegatus — 26
At 2.0 ppm, 40 percent mortality occurred in 1 day. Experi-
ments were carried out in plastic tubs lined with saran
plastic. Fish weights averaged 21 7 grams.
Data reported as LCgg at 15.5 C in 4 days.
Comment same as above.
Critical flicker frequency response in the bluegill was
measured by determining this species ability to maintain
position relative to continuously rotating stripes. Increas-
Reference
(Year)
Whitten and
Goodnight
(1966)
Butler and
Johnson
(1967)
Mulla, et al
(1967)
Sanders and
Cope
(1968)
Sanders and
Cope
(1968)
Scheier and
Cairns
(1968)
^
•o
m
O
03
Parathion
Parzate
Lepomis BSA
gibbosus
Ictaluras
me/as
Micropterus
dolomieui
Myxocephalus
scorpius
Pseudopleuronectes
americanus
Channel BSA
catfish
(fingerlings)
(0)
a p
ing or decreasing the rate of movement of the stripes
above or below a certain critical flicker threshold caused
the fish to return to random swimming. The effect of
different amounts of insecticide was measured. An
aberrant response was noted at all three sublethal con-
centrations noted.
The chemicals were poor inhibitors of brain cholinesterases
in vitro; their oxygen analogs were potent inhibitors.
Murphy, et al
(1968)
21.1 (K1A)
Tap water was used. Considerable additional data are
presented.
Clemens and
Sneed
(1968)
-------
Penicillin G,
potassium
(crystalline)
8
m
3D
o
o
m
•o
DO
O
O
I
Perthane
Phosdrin
Phosphamidon
(tech)
Phosphamidon
Phosphamidon
Cylindrospermum
lichenifoTne (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (Sot
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Gambusia
affinis
2.0 (O)
BSA
w
1
1— t
oo
Perthane
(tech)
Phorate
(Thimet)
Phosdrin
Phosdrin
(tech)
Phosdrin
Phosdrin
Rainbow
trout
- Oyster
Rainbow
trout
Eastern
brook
trout
Rainbow
trout
Bluegill
Pteronarcys sp
(nymphs)
Simocephalus
serrulatus
Daphnia
pulex
BSA
BCF
BCF,
BSA
BSA
BSA
Pteronarcys
californica
(naiads)
Procambarus
clarki
Salmo
gairdneri
Salmo
gairdneri
BSA
BSA
BSA
BSA
10.4 (LD*
10.0 (L1)**
•Resistant fish
**Nonresistant fish
0.005 (T4A)
0.64 (O)
0.05 (K 3 day)
0.1 (K 4 hr)
0.5 (K 80 min)
1.0(K 30 min)
10.0 (K 15 min)
0.012 (T4A)
0.023 (T4A)
0.0049 (T4A)
' 0.00043 (SB)
0.00016 (SB)
0.005 (T4A)
5.5 (T3A)
5,000 (T.1A)
5,000 (T 18hr)
Observations were made on the 3rd, 7th, 14th, and 21st
days to give the following (T = toxic, NT = nontoxic,
PT = partially toxic with number of days in parentheses.
No number indicates observation is for entire test period
of 21 days):
Cl -PT(7)
Ma-T
So - NT
Cv -NT
Gp-NT
Np - NT
This paper deals with the resistance of mosquito fish to
chlorinated hydrocarbon compounds; Resistant fish were
not always less sensitive to these chemicals.
Palmer and
Maloney
(1955)
The values reported are given as
The value reported is a 96-hr ECso (decreased shell growth).
Spring water (46 F) was used. The flow rate was 10 gpm.
The chemical was added by continuous drip dispenser.
0.01 ppm for 180 hr showed toxic effects, but no kill.
The values reported are given as LCsg.
Experiments were all conducted at 60 F in 1964. The
values were listed as
— Concentration reported is for immobilization.
Time for immobilization was 48 hr.
Data cited are for 60 F, but assays were performed at varied
temperatures.
Water chemistry (unspecified) was "controlled" during the
assay period.
a c d e f Data reported as LCsg at 15.5 C in 4 days.
a c d o There was no detectable difference in toxicity to male or
female crawfish.
The experiment was conducted'at 55 F. Fish were 2-3 in.
long.
Comment same as above.
Boyd and
Ferguson
(1964)
Cope
(1965)
Butler
(1965)
Hoffman
(1957)
Cope
(1965)
Cope
(1965)
Sanders and
Cope
(1966)
Sanders and
Cope
(1968)
Muncy and
Oliver
(1963)
Cope
(1963)
Cope
(1963)
I
m
Z
O
X
CD
-------
COMMERCI
r~
0
X
m
2
g
^
t~
-Q
30
O
5
w
M
i.
OO
Chemical
Phosphamidon
Phosphamidon
Phosphamidon
(in water)
Phosphamidon
Phygon XL
Phygon-XL
Phygon-XL
Phygon-XL
Phygon X-L
Organism
Simocephalus
serrulatus
Daphnia
pulex
Daphnia
magna
Co ho
salmon
(fry)
Atlantic
salmon
Brook
trout
Pteronarcys
californica
(naiads)
Oncorhynchus
kisutch
Micropterus
salmoides
Channel
catfish
(fingerlings)
Sa/velinus
f on final is x
Salmo
trutta
Notemigonus
crysoleucas
Ictalurus
punctatus
Micropterus
salmoides
Lepomis
macrochirus
Salmo
gairdneri
Richardfonius
batteatus
hydroflox
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study C" Location (2) ppm (3)
BSA - 0.01 2 (SB)
0.0088 (SB)
BSA - 0.01 25 (SB)
FR Moran 7.0 (T2A)
Creek,
B.C.
FR New (O)
Brunswick
BSA - 0.15IT4A)
BSA - 0.042 (NTE)
0.08 (T1A)
0.07 (T2A)
BSA - 0.14
(K29hr A)
FPA N.Y. 0.5 (S23)
0.5 (S23)
0.5 (S23)
0.5 (S23)
BSA - 0.075 (T1A)
0.075 (T2A)
BSA - 0.13 (T1A)
0.11 (T2A)
0.11 (T4A)
Experimental
Variables
Controlled
or NotedW
_
—
a
-
a cd e f
a cd e
a
a c d
a cd f g
a cd ef
Comments
Concentration reported is for immobilization.
Time for immobilization was 48 hr.
Data cited are for 60 F, but assays were performed at varied
temperatures.
Water chemistry (unspecified) was "controlled" during the
assay period.
Concentration reported is for immobilization.
Time for immobilization was 64 hr.
Data cited are for 78 F, but assays were performed at varied
temperatures.
Water chemistry (unspecified) was "controlled" during the
assay period.
The data indicated 1 .0 to 3.2 ppm would cause a slight
mortality of juvenile coho salmon. The value of 7.0 ppm
was taken from a preliminary bioassay.
Spraying with this chemical at 1.0 Ib per acre had no apparent
harmful effects on young salmon or trout.
Data reported as LC$Q at 15.5 C in 4 days.
Concentrations were based on percent active ingredient.
No toxicity to O. kisutch occurred at concentrations up
to 0.042 ppm.
Tap water was used. Considerable additional data are
presented.
Conventional farm ponds were used having an average
surface area of 0.3 acre and a maximum depth of 7-9 ft.
Toxicity (in ppm) to fish as maximum safe concentra-
tion (S) for 23 days was determined. Concentration of
0.5 ppm was required to control algae.
Hatchery artesian well water was employed for this
experiment.
Results given were in soft water.
Results in hard water were as follows: 0.15 (T1A), 0.16 (T2A),
and 0.14 (T4A).
Reference
(Year)
Sanders and
Cope
(1966)
Sanders and
Cope
(1966)
Schouwenberg
and Jackson
(1966)
Kerswlll and
Edwards
(1967)
Sanders and
Cope
(1968)
Bond.et al
(1960)
Clemens and
Sneed
(1959)
Eipper
(1959)
Webb
(1961)
Webb
(1001)
>
2
m
X
00
-------
£
oo
VD
o
3)
O
o
Phygon-XL
Phygon XL
(Dichlone)
Picloram
PM A
Polyclens
Polysan
Prometone
[2-methoxy-
4,6-bis(iso-
propylamino)-
s-triazine
(prometone)]
8
m
30
o
31 Prometone
m
Prometone
Prometone
Gammarus
lacustris
Salmon
Pteronarcys
californica
(naiads)
Salmo
gairdneri
Salmo
trutta
Salvelinus
fontinalis
Salvelinus
namaychush
Ictalurus
punctatus
t.epomis
macrochirus
Panda/us
montagni
Crangon
crangon
Carcinus
maenas
Cardium
edule
Guppy
Elodea
canadensis
Potamogeton
nodosus
Potamogeton
pectinatus
Leiostomus
xanthurus
(juvenile)
Penaeus
duorarum
Oyster
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
0.165(T4A)
0.043 (T2A)
0.048 (T4A)
3.75 (T2A)
6.22 (T2A)
10.7 (T2A)
7.60 (T2A)
2.89 (T2A)
16.0 (T2A)
8.5 (T2A)
15.7 (T2A)
23.2 (T2A)
70.0 (T2A)
100(K25min)
acdef
af
BCF
5(0)
100 (O)
5(0)
100 (O)
5(0)
100(0)
(O)
(O)
(O)
Emulsible concentrates were prepared from technical grade
insecticides with acetone as the solvent.
Symptoms prior to death were observed and recorded on
graphs.
Data are given as LC5Q.
Data reported as \-C$Q at 15.5 C in 4 days.
Variance and the 95-percent confidence interval (C.I.) were
also determined.
Experiments were conducted in tanks holding 10 liters of
seawater at 15 C.
It was shown that the toxicity of this solvent emulsif ier
decreased with time due to evaporation of the solvent.
Polyclens at a concentration of 3.3 ppm killed 100% of
Crangon crangon larvae in 3 hr.
Those fish that survived at lower concentrations were still
very active several days after they had been taken out and
placed in fresh water.
Experiments were conducted in standing water. Results
were rated on a scale of 0 to 10, 0 standing for no toxic
effect and 10 signifiying a complete kill. Evaluation was
based on visual observation of the plant response at weekly
intervals for 4 weeks.
Injury rating of 0.5.
Injury rating of 3.6.
Injury rating of 2.3.
Injury rating of 7.0.
Injury rating of 5.1.
Injury rating of 8.3.
Water temperature was 26 C. No effect was noticed on
exposure to 1.0 ppm.
Toxicant chemicals were evaluated in sea water at tempera-
tures averaging about 28 C. The values are for 24-hr ECso
or enough to cause loss of equilibrium or mortality. No
effect occurred at 1.0 ppm.
No effect on exposure to the chemical at 1.0 ppm.
Nebeker and
Gaufin
(1964)
Bohmont
(1967)
Sanders and
Cope
(1968)
Willford
(1966)
Portmann and
Connor
(1968)
Anonymous
(1964)
Frank, et al
(1961)
Butler
(1965)
Butler
(1965)
Butler
(1965)
-------
COMMERCI
>
O
I
rn
S
O
f—
3)
Q
D
cn
tjo
J.
VO
Chemical
Prometone
Prometryne
Prometryne
Prometryne
Pro-noxfish
(25% rotenone
+ 2.5%
sulfoxide)
Pro-noxfish
(2.5% rote-
none. 2.5%
sulfoxide.
5% cube
extracts
emulsifier)
Organism
Crassostrea
virginica
Penaeus
duorarum
Leiostomus
xanthurus
Phytoplankton
Oyster
Leiostomus
xanthurus
(juvenile)
Peneas
duorarum
Crassotrea
virginica
Penaeus
duorarum
Leiostomus
xanthurus
Phytoplankton
Cyprinus
carpio
(eggs)
(fry)
Pimephales
promelas
(eggs)
(fry)
Cyprinus
carpio
Micropterus
salmoides
Pimephales
promelas
Carassius
auratus
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study fl) Location!?) ppm'3)
BCFA& - 1.0 (NTE)
BSA
1.0 (NTE)
1.0 (NTE)
—
BCF - (O)
BSA
L - (0)
BCFA& - 1.0(0,19%)
BSA
1.0 (NTE)
1.0 (NTE)
—
BSA
0.178 (K)
0.1 63 (K)
0.233 (K)
0.191 (K)
BSA - 0.163(K3)
0.081 (K3)
0.191 (K3)
0.242 (K3)
Experimental
Variables
Controlled Reference
or Noted<4> Comments (Year)
— Seawater was pumped continuously into test aquaria. Butler
Salinity, temperature, and plankton fluctuated with tide, (1965)
and ambient weather conditions. Some bioassays with
fish were static. Toxicity was reported for the following:
Oyster — 96-hr £059 — Cone, which decreased
shell growth.
Shrimp — 48-hr ECgrj — Cone, which killed or
paralyzed 50% of test animals.
Fish — 48-hr ECso — Cone, which killed 50%.
Phytoplankton — Percent decrease of CO2 fixation to a
4-hr exposure at 1.0 ppm chemical
concentration.
s Exposure to a concentration of 1 ppm caused a 19.0% Butler
decrease in shell growth. (1965)
Water temperature was 28 C. No effect was noticed on
exposure to 1 .0 ppm.
a Toxicant chemicals were evaluated in sea water at tempera- Butler
tures averaging about 28 C. The values are for 24-hr EC^rj (1965)
or enough to cause loss of equilibrium or mortality. No
effect occurred at 1 .0 ppm.
— Seawater was pumped continuously into test aquaria. Butler
Salinity, temperature, and plankton fluctuated with tide, (1965)
and ambient weather conditions. Some bioassays with
fish were static. Toxicity was reported for the following:
Oyster — 96-hr EC§o — Cone, which decreased
shell growth.
Shrimp — 48-hr EC^Q — Cone, which killed or
paralyzed 50% of test animals.
Fish — 48-hr EC^Q — Cone, which killed 50%.
Phytoplankton — Percent decrease of CO2 fixation to a
4-hr exposure at 1 .0 ppm chemical
concentration.
a Toxicity is reported as LDgQ in ppm, at 75 F. Hester
(1959)
a c d e i Such variables as temperature, species, and size of fish were Hester
~~ studied. Toxicity is expressed as LD5Q for 72 hr. Smaller (1959)
concentrations of rotenone were required when used in
conjunction with sulfoxide. The data shown are for 70 F.
The chemical was considerably more toxic at this tempera-
ture than at 40 F for all fish species.
^
no
m
z
o
X
CD
-------
Lepomis
macrochirus
L. cyanellus
Notemigonus
crysoleucas
Ictalurus
nebulosus
marmoratus
0.255 (K3)
0.238 (K3)
0.555 (K3)
0.410 (K3)
Pro-noxfish
Pro-noxfish
W
Propanil
(Stam,
Rogue)
Pyrethrin
Pyrethrins
r>
o
S
m
o
>
r~
o
m
5
o
TJ
13
O
O
c
Pyrethrins
Oncorhynchus
kisutch
(eggs)
FR
Ore.
(O)
Oncorhynchus
tshawytscha
(fry, 100-day
old)
Oncorhynchus
kisutch
(eggs)
Daphnia
magna
Pteronarcys sp
(nymphs)
Simocephalus
serrulatus
Daphnia
pulex
Salmo
gairdneri
Lepomis
macrochirus
Ictalurus
punctatus
Pteronarcys
californicus
Daphnia
pulex
Simocephalus
serrulatus
BSA
Con/all is.
Ore.
BSA
BSA
BSA
BSA
0.15 to 5.0
(K1)
(O)
4.8 (3.8-
6.6) (O)
0.001 (T4A)
0.042 (SB)
a cd i q
0.054 (T2A)
0.070 (T2A)
0.082 (T2A)
0.006 (T2A)
0.025 (T2A)
0.042 (T2A)
Pro-noxfish is a formulation containing 2.5% rotenone. Garrison
5.0% related rotenoids and cube extractives, 2.5% sulfoxide (1968)
synergists, and 90% solvent emulsifier.
The goal of this experiment was to expose the eggs to the
chemical at a concentration of 2 ppm for 24 hr.
High survival occurred where the temperatures ranged from
46 to 56 F.
High temperatures of 60 and 65 F occurred in Middle Fork
and Quartzville Creek and contributed to the mortality
rate. No eggs survived.
Pro-noxfish is a formulation containing 2.5% rotenone. Garrison
5.0% related rotenoids and cube extractives, 2.5% sulfoxide (1968)
synergists, and 90% solvent emulsifier.
Experiments were conducted in aerated test jars.
Temperature was 53 F.
Temperature seems to have an influence upon toxicity.
Embryos exposed to the chemical for 24 hr showed the follow-
ing survival rates. All embryos survived in 1.0 ppm at 53 F,
all survived in 3 ppm at 46 F, and 90% survived in 4 ppm
at 39 F.
Toxicity, in terms of median immobilization concentration Crosby and
(I CSQ) , is presented. Tucker
(1966)
Experiments were all conducted at 60 F in 1964. The values Cope
were listed as LCgrj. (1965)
Concentration reported is for immobilization. Sanders and
Time for immobilization was 48 hr. Cope
Data cited are for 60 F, but assays were performed at varied (1966)
temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
This paper reports acute toxicity of a number of compounds. Cope
and discusses sub-acute mortality as well. Effects on repro- (1966)
duction and behavior are also discussed. Data presented as
m
O
X
00
-------
8
S
m
n Chemical
^
*~ Pyrethrum
o
I
m
O
>
w—
-u Pyrethrum
3>
o
O
c
-}
CO
Pyrethrum
Quaternary
ammonium
salt, commercial
Rivanol
£
*O Roccal
K \
I^J
Roccal
Roccal
Organism
Black fly
(larvae)
Rainbow
trout
Salmo
gairdneri!
Ictalurus
punctatus
Lepomis
macrochirus
Pteronarcys
californica
Pteronarcys
californica
(naiads)
Microcystis
aeruginosa
Channel
catfish
(fingerlings)
Micropterus
salmoides
(fry)
Ictalurus
punctatus
(fry)
Lepomis
macrochirus
(fry)
Guppy
Salmo
gairdneri
Salmo
trutta
Salvelinus
fontinalis
Salevelinus
namaycush
Ictalurus
punctatus
Lepomis
macrochirus
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study <1) Location<2) ppm(3)
FR Alaskan 0.1 (O)
streams
0.1 (0)
BSA - 54 (T4A)
80 (T4A)
74 (T4A)
1.0 (T4A)
BSA - 0.001 0(T4A)
L - 2.0 (K)
BSA - 2.8 (K1 A)
BSA - 1.0 (SB3)
1.0 (SB3)
0.25 (SB3)
BSA - 100 (K1)
BSA - 2.57 (T2A)
2.05 (T2A)
3.40 (T2A)
1.95 (T2A)
1.12IT2A)
1.68 (T2A)
Experimental
Variables
Controlled
or NotedW Comments
_ The chemical was applied to control black flies, and because
the acetone solution was most effective, only that data is
reported here. The figures reported are for minimum effec-
tive dosages for black fly larvae and maximum nonlethal
dosage for rainbow trout.
a c d Toxicity values reported as median lethan concentration
( LC5Q) for 24, 48, and 96 hr.
a c d e f Data reported as LCgrj at 1 5.5 C in 4 days.
a, etc The chemical was tested on a 5-day algae culture, 1 x 10^ to
~ 2 x 106 cells/ml, 75 ml total volume. Chu No. 10 medium
was used.
a Tap water was used. Considerable additional data are
~ presented.
a c d e f p At least 90 percent of the fry survived for a period of
72 hours.at the concentration listed.
a Those fish that survived at lower concentrations were still very
active several days after they had been taken out and placed
in fresh water.
a f Variance and the 95-percent confidence interval (C.I.) were
also determined.
Reference
(Year)
Gjulian, et al
(1949)
Bridges and
Cope
(1965)
Sanders and
Cope
(1968)
Fitzgerald, et al
(1952)
Clemens and
Sneed
(1959)
Jones
(1965)
Anonymous
(1964)
Willford
(1966)
>
^
m
O
00
-------
vo
Ronnel
Ronnel
(EC2)
Ronnel
Ronnel
Ronnel
Rosinamine
D acetate
Rosinamine
D acetate
Rosinamine
D sulphate
8
3D
O
O
Rosinamine
D sulphate
(RADS)
Chaoborus BSA
astictopus
Gambusia F L
affinis
Bufo
boreas
Penaeus L
aztecus
Leiostomus BSA
xanthurus
(juvenile)
Oyster BCF
Cylindrospermum L
lichen/forme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Pimephales BSA
promelas
Cylindrospermum L
licheniforme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Pimephales BSA
promelas
Ponds
in III.
0.046 (T1A)
(O)
0.015 (O)
0.32 (O)
0.17 (O)
2.0 (O)
0.23 (T4A)
2.0 (O)
a cd ef
0.16(T4A)
a c d e f
Toxicity value given is for the fourth instar larvae.
When applied at 0.8 pound per acre active ingredient, no
fish mortality occurred in 1 day.
At 0.2 pound per acre, 10 percent toad mortality occurred
in 1 day. In a duplicate test there was no mortality at
0.8 pound per acre.
Toxicant chemicals were evaluated in sea water at tempera-
tures averaging about 28 C. The values are for 24-hr £050
or enough to cause loss of equilibrium or mortality.
Water temperature was 13 C. The figure reported is a
48-hr EC50.
The value reported is a 96-hr EC5Q (decreased shell growth).
Observations were made on the 3rd, 7th, 14th, and 21st days
to give the following (T = toxic, NT = nontoxic, PT = par-
tially toxic with number of days in parentheses. No number
indicates observation is for entire test period of 21 days):
Cl -T
Ma-T
So - PT (7)
Cv -T
Gp-T
Np-T
Toxicity to 30 species of algae also presented. RADA was
algicidal in the range 0.25 to 2.0 ppm.
Observations were made on the 3rd, 7th, 14th, and 21st days
to give the following (T = toxic, NT = nontoxic, PT = par-
tially toxic with number of days in parentheses. No number
indicates observation is for entire test period of 21 days):
Cl -T
Ma-T
So -T(14),PT (21)
Cv -T
Gp-T
Np-T
Toxicity to 30 species of algae also presented. RADS was
algicidal in the range 0.25 to 2.0 ppm.
Hazeltine
(1963)
Mulla, et al
(1963)
Butler
(1965)
Butler
(1965)
Butler
(1965)
Palmer and
Maloney
(1955)
Maloney and
Palmer
(1956)
Palmer and
Maloney
(1955)
Maloney and
Palmer
(1956)
TJ
3D
O
O
-------
o
o
s
s
m
n Chemical
n Rosinamine D
O
I
m
5
r~
•o
X
O
o
c
to
Rosinamine D
pentachloro-
phenate
V
»—•
vo
Rosinamine
derivative
Rotenone
(derris or cube
with 5%
rotenone)
Bioassay
or Field
Organism Study (D
Cylindrospermum L
lichen/forme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Cylindrospermum L
lichen/forme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Cylindrospermum L
lichen/forme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Salvelinus F L
fontinal/s
(yearling)
Couesius
plumbeus
Catostomus
commersonnii
Eels
Pungitius
pungitius
Micropterus
dolomieu
Toxicity,
Active
Field Ingredient,
Location'2) ppm(3)
2.0 (0)
2.0 (O)
2.0 (0)
4 lakes, 0.20 (K)
Nova
Scotia
0.20 (K)
0.20 (K)
0.25 (K)
0.25 (K)
0.25 (K)
Experimental
Variables
Controlled
or Noted'4) Comments
a Observations were made on the 3rd, 7th, 24th, and 21st days
~ to give the following (T = toxic, NT = nontoxic, PT = par-
tially toxic with number of days in parentheses. No number
indicates observation is for entire test period of 21 days):
Cl -T
Ma-T
So -T (3),PT (14)
Cv -T
Gp-T
Np-T
a Comment same as above except that:
Cl -P (7),PT(14)
Ma-PT (14)
So -NT
Cv -T (7),PT (14)
Gp-NT
Np-T
a Comment same as above except that:
Cl -PT
Ma - PT (14)
So -PT
Cv - PT (3)
Gp-T
Np-T
a c d f The work was undertaken to test the feasibility of utilizing
poisons as a direct means of studying the production of
fish in streams and lakes. Caution must be used to prevent
irreparable damage by indiscriminate poisoning.
Reference
(Year)
Palmer and
Maloney
(1955)
Palmer and
Maloney
(1955)
Palmer and
Maloney
(1955)
Smith
(1939)
£
Tl
*o
m
Z
D
X
CO
-------
Rotenone
Rotenone
,_,•
i
Rotenone
(5% cube)
Rotenone
8
m
3
O
O
m
S
•o
30
O
o
i
Morone
americana
Carassius
auratus
Perca
flavescens
Brown
trout
Rock
bass
Creek
chub
Smallmouth
bass
Common
sucker
Brown
bullhead
Channel
catfish
(fingerlings)
Chironomus
plumosus
(larvae)
Rotenone
(2.5 percent,
5 percent cube
extractives, and
2.5 percent
sulfoxide)
Rotenone
(5 percent
and 15 percent
toxaphene)
Rotenone
(2.0 percent
and 7.0 percent
toxaphene)
Rotenone
(5 percent
and 10 percent
other extractives
BSA
BSA
Pimephales
promelas
Pimephales
promelas
Pimephales
promelas
Pimephales
promelas
BSA
BSA
FLA
Lake
Erken,
Sweden
BSA
BSA
BSA
BSA
0.25 (K)
0.100-2.00
(K 8 hr)
0.0600 (O)
0.0400 (T 8 hr)
0.0200 (O)
0.45 (K)
0.20 (K)
0.32 (K)
0.35 (K)
0.40 (K)
1.7 (K)
2.2 (K)
0.51 (K1A)
(O)
(O)
a cd e p
0.066 (T4A)
a cd f g
0.066 (T4A)
0.10 (T4A)
0.10(T4A)
a cd f g
a cd f g
a cd f g
Temperature in test containers was maintained at 27 ± 0.2 C.
Goldfish tested weighed between 2 and 4 g.
Rotenone, 0.0600 mg per liter, killed 86% of the fish in 8 hr;
0.0200 mg per liter killed 18% in 8 hr.
A range of concentrations between 0.05 and 0.8 ppm was
used in this study and kill occurred in 1 to 4 hr.
Tap water was used. Considerable additional data are
presented.
Laboratory studies were with and without silt. Without silt
100% kill occurred in 0.3 ppm rotenone, while 50% kill
occurred at 3.0 ppm with silt present. Further data were
obtained from field studies and from caged animal studies
at various depths and sections of the lake. Data on more
than 200 species are presented at 0.5 ppm rotenone lake-
bottom-dwelling organisms exhibit sensitivity. Use of
higher concentrations than this would mean partial or
complete disappearance of many species.
Test water was spring water diluted with distilled water.
Removal of toxic chemicals by carbon adsorption, chlorine
and chlorine dioxide treatment, and alum coagulation was
studied. The most effective method to remove fish poisons
was by use of activated charcoal adsorption.
Comment same as above.
Comment same as above.
Comment same as above.
Gersdorff and
Smith
(1940)
Burdick, et al
(1956)
Clemens and
Sneed
(1959)
Lindgren
(1960)
m
z
O
X
Cohen, et al
(1961)
Cohen, et al
(1961)
Cohen, et al
(1961)
Cohen, et al
(1961)
-------
o
o
2
2
m
o Chemical
n Rotenone
O
I
m
Q
r™
•o Rotenone
3)
o
O
C
H
Rotenone
fr-j (2.5 percent)
"r
i— »
CTs
Rotenone
(5.5 percent,
cube extract
11. 00 percent)
Rotenone
Toxicity,
Bioassay Active
or Field Field Ingredient,
Organism Study'1' Location'2* ppm'3)
Pimephales BSA - 0.006 (T4A)
promelas
Entomostraca FL Col. 1.0 (K)
Cyclops
Diaptomus
Ceriodaphnia
Bosmina
Leptodora
Rotaria
Filinia
Keratella
Po/yarthra
Asplanchna
Brachionus
Protozoa
Ceratium
Difflugia
Fish FL Mont. 0.95 (O)
Fish FL Mont. 0.7 (O)
Zooplankton FL Fern Lake 0.5 (O)
Experimental
Variables
Controlled
or Noted'4* Comments
a c d f g Test water was spring water diluted with distilled water.
Removal of toxic chemicals by carbon adsorption, chlorine
and chlorine dioxide treatment, and alum coagulation was
studied. The most effective method to remove fish poisons
was by use of activated charcoal adsorption.
a c d g p All chemical and physical data were collected and compiled
by standard limnological techniques. Chemical analyses were
conducted monthly. Biweekly plankton collection showed
"reduction to zero" of all organisms studied, but recovery of
populations to normal population numbers within several
months.
a c d e I Ponds were treated with the chemical to eradicate fish. The
fish population included largemouth bass, bluegills, black
crappie, yellow perch, carp, white sucker, and longnose
sucker. Counts were made of various fish at various later
times. The paper contains little quantitative data.
a c d e I Comment same as above.
a c d e f Rotenone (5%) was applied at the rate of 0.5 ppm.
Samples were taken biweekly. Open water species were
Reference
(Year)
Cohen, et al
(1961)
Hoffman and
Olive
(1961)
Wollitz
(1963)
Wollitz
(1963)
Kiser, et al
(1963)
^
TJ
m
X
00
Silver Lake 1.0 (O)
Rotenone
Gammarus
lacustris
BSA
3.52 (T4A)
completely removed, and remained absent for 3 mo.
Organisms along the shore edge resisted the effect of
rotenone, but eventually disappeared for several weeks.
Rotenone (5%) was applied at the rate of 1.0 ppm.
After application the greatest reduction, about 70%, occurred
within an hour. Two days after application, no zooplankton
were found alive in the open-water tows taken at all depths
in the lake.
The rotenone penetrated to the thermocline at the 30-ft
depth in the first 6 hr, killing Cladocera and Copepoda as
it sank.
Emulsible concentrates were prepared from technical grade
insecticides with acetone as the solvent.
Symptoms prior to death were observed and recorded on
graphs.
Nebeker and
Gaufin
(1964)
-------
Rotenone
Rotenone
Rotenone
Rotenone
Rotenone
Rotenone
Ruelene
s
31
O
>• Ryania
(Ryanicide
I 100)
m
Nereis
limnicola
Salmo
gairdnerii
Ictalurus
punctatus
Lepomis
macrochirus
Pteronarcys
californica
Pteronarcys sp
(nymphs)
Anax
Agrion
Siphlonurus
Phryganea
Simocephalus
serrulatus
Daphnia
pulex
Pteronarcys
californica
(naiads)
Salmo
gairdneri
Salmo
trutta
Salvelinus
fontinalis
Salvelinus
namaycush
Ictalurus
punctatus
Lepomis
macrochirus
Cyprinus
carpio
FL
BSA
Lake
Merced,
Cal.
BSA
BSA
BSA
BSA
BSA
BSA
0.025 (K)
27 (T4A)
28 (T4A)
23 (T4A)
250(T4A)
0.250 (T4A)
2.3 (T2A)
0.190 (SB)
0.100 (SB)
0.38 (T4A)
32.0 (T2A)
25.7 (T2A)
35.0 (T2A)
27.0 (T2A)
34.8 (T2A)
35.0 (T2A)
(O)
a c d
In a fish killing program, O.O25 ppm of rotenone was used
on October 26, 1963. By November 18 the population of
the nereid had been reduced from 500/m2 to no greater
than 10/m2. How important this organism is in the com-
plex food chain is unknown.
Toxicity values reported as median lethal concentration
for 24,48, and 96 hr.
£ Experiments were all conducted at 60 F in 1964. The values
~ were listed as LC5Q.
a c c g Death caused by rotenone is caused by the constriction of
the gill capillaries which prevent the passage of blood
through the gills.
— Concentration reported is for immobilization.
Time for immobilization was 48 hr.
Data cited are for 60 F, but assays were performed at varied
temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
££ cl_e_f Data reported as LC5Q at 15.5 C in 4 days.
Variance and the 95 percent confidence interval (C.I.) were
also determined.
0 percent mortality occurred in 4 days at 0.01 ppm. 0 per-
cent mortality occurred in 4 days at 3 ppm.
Oglesby
(1964)
Bridges and
Cope
(1965)
Cope
(1965)
Claffey and
Ruck
(1967)
Sanders and
Cope
(1966)
Sanders and
Cope
(1968)
Willford
(1966)
Hayes
(1955)
m
O
X
CD
3)
O
O
-------
COMMERCI/
.*»
i-
o
m
S
£
r-
•u
2Q
O
O
q
en
s
VO
oo
Chemical
Saponin
Sarin
Sarin
Sarin
Sarin
Schadran
SD-4294
(EC32)
SD-4402
(15 percent
EC)
Organism
Shrimp:
Caridina
denticulate
Penaeus
carinadus
Fish:
Elops
saurus
Tilapia
mossambica
Pimephales
promelas
Lepomis
cyanellus
Carassius
auratus
Pimephales
promelas
Lepomis
cyananellus
Carassius
auratus
Lepomis
macrochirus
Lepomis
cyanellus
Pimephales
promelas
Lebistes
re tic u /at us
Carassius
auratus
Pimephales
promelas
Channel
catfish
(finger! ings)
Gambusia
affinls
Gambusia
affinis
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
StudyCO Location*2) ppm'3) or Noted<4>
BSA & Taiwan a
FL 50.0 (K1)
70.0 (K1)
1.0 (K1)
1.5 (K)
BCFA - 10-40(0) acde
BSA - 0.1 to 50.0(0) acd
BSA + - (S) 3.2 (T4A) acde
BCFA (H) 23.5 (T4A)
(S) 4.2 (T4A)
(H) 15.2 (T4A)
(S) 4.4 (T4A)
(H) 31.9 (T4A)
(S) 1.4 (T4CF)
(H)4.2 (T4CF)
(S) 7.2 (T4A)
(H) 13.8 (T4A)
(S) 9.8 (T4A)
(S) 4.1 (T4CF)
BCFA - 18ppb acef
(T 2 hr A)
BSA - >8913(K1A) a
FL Ponds (O) -
in III.
FL Ponds- 0.1 (K1) ac
Bakers- 0.4 (K1>
field. Cat.
Comments
Saponin derived from Camellia spp selectively killed fish in
bioassays at the concentrations noted while 50-70X higher
concentrations were required to kill shrimp. Concentrations
of saponin ranging from 2.5-10.0 ppm were similarly effective
in pond studies in killing wild fish which prey on or compete
with shrimp. This appears to be a good treatment in shrimp
culture for shrimp predator control, but the authors caution
that further investigation is required.
The time for 50 percent (TSQ) of the fish to die was studied
when the toxic material was held constant while dissolved
oxygen, temperature and size of fish were varied. Toxic
concentrations of sarin were between 10 ppb and 40 ppb
oxygen consumption rates are also reported.
Data are presented as TLm/degree centigrade with some of the
results as follows: 50 ppm at 24 C was lethal in 0.8 minutes
and at 1.20 C in 1.3 minutes for fathead minnows. 50 ppm
at 24 C was lethal to sunfish in 0.95 minutes, and at 12 C in
1.55 minutes. 50 ppm at 24 was lethal to goldfish 1.5 min-
utes, and at 12 C, 2.3 minutes. The toxicity of Sarin was
shown to be very temperature dependent. Considerable
additional data are presented.
Both static and continuous flow bioassays were made in
hard (H) and soft (S) waters. 24, 48, and 96-hr TM|_ are
reported. Sarin was more toxic in hard water.
Describes a continuous flow method for bioassay of an organo-
phosphorus CW agent.
Tap water was used. Considerable additional data are
presented.
When applied at 0.2 pounds per acre active ingredient, 4 per-
cent mortality occurred in 1 day.
Toxicity values indicate application rates in Ib/acre. The
experiments were conducted in cages placed in the ponds.
Reference
(Year)
Tang
(1961)
Weiss and
Botts
(1957)
Weiss and
Botts
(1957)
Pickering and
Henderson
(1959)
Henderson and
Pickering
(1963)
Clemens and
Sneed
(1959)
Mulla, et a)
(1963)
Mulla and
Isaak
(1961)
^
^
m
Z
O
DO
-------
VQ
SD-7587
(EC2)
SD-8803
(EC2)
SD-9020
(EC2)
SD-9129
(ECS)
Separan
(poly-
acrylamide)
Sernyl
Sen/in
Sevin
(50%, and
Sevin-
tech)
Sevin
Sevin
8
S Sevin
m
•a
o
>
r
o
m
? Sevin
TJ
3)
O
O
c
Gambusia
affinis
Gambusia
affinis
Gambusia
affinis
Gambusia
affinis
Rainbow
trout
Carassius
auratus
Leiostomus
xanthurus
Carassius
auratus
Pimephales
promelas
Lepomis
macrochirus
Pimephales
promelas
Lepomis
macrochirus
Ephemeroptera
Plecoptera
Coleoptera
Trichoptera
Diptera
Annelida
Megaloptera
Oncorhynchus
kisutch
Salmo
gairdnerii
Gasterosteus
aculeatus
FL
FL
FU
FL
BSCH
Ponds
in III.
Cal.
Cal.
Cal.
(0)
0.4 (K1)
(0)
(0)
(0)
BSA
BCFCH
BSA
BSA
BSA
FR
Oneonta,
N. Y.
BSA
36 (T 1.5hr)
0.1 (SB 90)
25 (K2)
14 (L2)
35 (K2)
28 (L2)
12.0 (T4A)
5.3 (T4A)
12.0IT4A)
5.3 (T4A)
(O)
a b
a d e f
997 (T4A)
1,350(T4A)
3,990 (T4A)
When applied at O.40 pounds per acre active ingredient,
32 percent mortality occurred in 1 day.
Toxicity value is in Ib/acre.
At a concentration of 0.4 Ib/acre, 56% mortality of
Gambusia affinis occurred in 24 hours.
At a concentration of 0.8 Ib/acre, 16% mortality of the fish
occurred in 24 hours.
A concentration of 0.035 and 0.070 ppm of "Separan" for
4 months caused no rainbow trout mortality. No growth
retardation was evident in the lot exposed to 0.035 ppm,
and only slight retardation occurred at 0.070 ppm.
Fish reacted sluggishly and remained stationary at all con-
centrations evaluated. Median tolerance limits, median
lethal concentrations, and the relation of dosage to time
were calculated.
The toxicity of this chemical to fish was relatively low.
The wettable powder formulation (50% Sevin) was prepared
on the basis of active ingredient, and stirred directly into
water. As a comparison, results were given for Sevin (tech-
nical). The wettable powder appeared to be twice as toxic
as the Sevin alone under the conditions of this test.
Concentrations were based on percent active ingredient.
Bioassay investigations of the new insecticides indicate that
in general the organic phosphorus compounds are not as
toxic to fish as are the chlorinated hydrocarbons. The
toxicity of most of these materials was not significantly
influenced by water quality. Therefore it is to be expected
that the toxicity of these materials will not differ signifi-
cantly in different streams.
This chemical was highly toxic to mayflies, stoneflies, and
caddieflies at 1/4 Ib/acre. The fish food populations of
invertebrates in the sprayed sections of the streams were
reduced from 50.7 to 97.2 percent.
Chemical dissolved in acetone. TLm expressed in ppb.
Mulla, et al
(1963)
Mulla
(1966)
Mulla
(1966)
Mulla
(1966)
Olsen and
Foster
(1958)
Wilber
(1965)
Butler and
Johnson
(1967)
Haynes, et al
(1958)
m
O
Henderson, et al X
(1960) gg
Tarzwell
(1959)
Burdick, et al
(1960)
Katz
(1961)
-------
8
m
o Chemical
^
r Sevin
m
2
<-»
>
t~
TJ
3)
O
o
C Sevin
" (tech)
en
Sevin
(tech)
Sevin
?
8
0 Sevin
Sevin
(tech)
Sevin
(carbaryl)
Sevin
Sevin
(20% active)
Bioassay
or Field
Organism Study'1'
Protococcus sp BSA
Chlorella sp
Dunaliella
euchlora
Phaeodactylum
tricornutum
Monochrysis
lutheri
Procambarus BSA
clarki
Salmo BSA
gairdneri
Aquatic insects: FR
Ephemeroptera
Plecoptera
Ameletus
Iron
Heptagenia
Brachyptera
Alloperla
Ephemerella
Simulium
Pteronarcys sp BSA
(nymphs)
Bluegill BSA
Brown BSCFA
trout
(fingerlings)
Simocephalus BSA
serrulatus
Oaphnia
pulex
Tubifex spp BSA
Limnodrilus spp
Toxicity,
Active
Field Ingredient,
Location^) ppm<3)
10 (NG)
10 (K)
10 (NG)
0.1 (NG)
10 (K)
1.0 (NG)
2.0 (T3A)
3,500 (T1A)
2,000 (T2A)
Pa. (0)
0.0048 (T4A)
2.0 (T4A)
8.0 (K)
15 to 273
minutes
0.0076 (SB)
0.0064 (SB)
750 (L4A)
Experimental
Variables
Controlled
or NotedW Comments
a This paper concerns the growth of pure cultures of marine
plankton in the presence of toxicants. Results were ex-
pressed as the ratio of optical density of growth in the
presence of toxicants to optical density in the basal medium
with no added toxicants. NG = no growth, but the organ-
isms were viable.
a c d o There was no detectable difference in toxicity to male or
female crawfish.
a The experiment was conducted at 55 F. Fish were 2-3 in.
long.
— Insecticide spraying dosage was 1.1 kg/4.21 H20/hectare,
covering over 16,000 acres of woodland for control of
gypsy moth. It appeared that there was a drastic reduction
of the standing crop of aquatic insects as a result of spraying
despite precautions taken against direct spraying of open
water and washing spray equipment in the streams.
a Experiments were all conducted at 60 F in 1964. The values
were listed as \-C$Q.
— The values reported are given as LCsfj.
ace No significant different in toxicity was found between flow-
through and static evaluations. A wide range of concentra-
tions was studied in both hard and soft waters, and a range
of sizes of fish were used. The data is given considerable
mathematical treatment. The form in which the chemical
is used was shown to be important.
— Concentration reported is for immobilization.
Time for immobilization was 48 hr.
Data cited are for 60 F, but assays were performed at varied
temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
ace Toxicity is reported as the mean lethal dose (1.050) for 24,
48, and 96 hours.
Reference
(Year)
Ukeles
(1962)
Muncy and
Oliver
(1963)
Cope
(1963)
Coutant
(1964)
Cope
(1965)
Cope
(1965)
Burdick, et al
(1965)
Sanders and
Cope
(1966)
Whitten and
Goodnight
(1966)
^
^
m
Z
0
X
DO
-------
Sevin
(Carbaryl)
Shell 4072
Shell 4072
Shell
SD-7438
(tech)
Shell
SD-7438
to Shell
2 SD-7438
Shell
SD-7961
Salmo BSA
gairdneri
Lepomis
macrochirus
Ictalurus
punctatus
Pteronarcys
californicus
Daphnia
pulex
Simocephalus
serrulatus
Leiostomus BSA
xanthurus
(juvenile)
Oyster BCF
Rainbow BSA
trout
Bluegill
Penaeus L
aztecus
Oyster BCF
Crassostrea BCFA & BSA
virginica
Penaeus
setiferus
Leiostomus
xanthurus
Phytoplankton
8
2.000 (T2A)
2.500 (T2A)
19.000 (T2A)
0.015 (T2A)
0.006 (T2A)
0.008 (T2A)
(O)
0.60 (O)
0.030 (T4A)
0.250 (T4A)
0.028 (O)
0.10(0)
1.0 (NTE)
1.0 (NTE)
1.0 (NTE)
(O)
This paper reports acute toxicity of a number of com-
pounds, and discusses subacute mortality as well. Effects
on reproduction and behavior are also discussed. Data
presented
Cope
(1966)
2
2
m
30
0
>
o
I
m
2
o
1-
-D
3D
O
O
s
Shell
SD-7961
Shell
SD-7961
Shell
SD-S447
Oyster
Leiostomus
xanthurus
(juvenile)
Leiostomus
xanthurus
(juvenile)
Oyster
Penaeus
duorarum
BCF
BSA
BSA
BCF
L
(0)
(0)
(0)
(0)
0.42 (0)
a
a
a
a
a
Water temperature was 14 C. Fish lost equilibrium at
1.0 ppm.
The value reported is a 96-hr £650 (decreased shell growth).
The values reported are given as
Toxicant chemicals were evaluated in seawater at tempera-
tures averaging about 28 C. The values are for 24-hr EC5Q
or enough to cause loss of equilibrium or mortality.
The value reported is a 96-hr £€50 (decreased shell growth).
Seawater was pumped continuously into test aquaria.
Salinity, temperature, and plankton fluctuated with tide,
and ambient weather conditions. Some bioassays with
fish were static. Toxicity was reported for the following:
Oyster — 96-hr ECso — Cone, which decreased
shell growth.
Shrimp — 48-hr ECso — Cone, which killed or
paralyzed 50% of test animals.
Fish — 48-hr EC5Q — Cone, which killed
50%.
Phytoplankton — Percent decrease of CO2 fixation to a
4-hr exposure at 1.0 ppm chemical
concentration.
No effect on exposure to the chemical at 1.0 ppm.
Water temperature was 16 C. No effect was noticed on
exposure to 1.0 ppm.
Water temperature was 17 C. Fish showed irritation at
1.0 ppm.
No effect on exposure to the chemical at 1.0 ppm.
Toxicant chemicals were evaluated in sea water at tempera-
tures averaging about 28 C. The values are for 24-hr £650
or enough to cause loss of equilibrium or mortality.
Butler
(1965)
Butler
(1965)
Cope
(1965)
Butler
(1965)
Butler
(1965)
Butler
(1965)
Butler
(1965)
Butler
(1965)
Butler
(1965)
Butler
(1965)
Butler
(1965)
1
m
o
X
00
-------
COMMERCE
s*
r-
o
I
m
S
5
TJ
3J
O
O
o
(n
M
V
NJ
O
to
Chemical
Shell
SD-8448
Shell
SD-8448
Shell
SD-9129,
EC
Shell
SD-9129
Si 1 vex
Silvex
Organism
Penaeus
duorarum
Oyster
Leiostomus
xanthurus
(juvenile)
Rainbow
trout
Bluegill
Oyster
Fundulus
similis
(juvenile)
Penaeus
aztecus
Aquatic weeds
in Georgia
including
Najas sp
Potamogeton sp
Myriophyllum
heterophyllum
Utricularia sp
Myriophyllum
brasiliense
Eleocharis
acicularis
Bluegill
Bioassay
or Field
Study 0)
L
BCF
BSA
BSA
BCF
BSA
L
FL
FP
Toxicity,
Active
Field Ingredient,
Location (2) ppm(3)
0.28 (0)
0.40 (0)
(0)
4.90 (T4A)
4.0 (T4A)
(0)
(0)
0.32 (O)
Farm (O)
ponds
in Ga.
Okla. 1.5 to 3.0(O)
Experimental
Variables
Controlled
or Noted'4' Comments
a Toxicant chemicals were evaluated in seawater at tempera-
tures averaging about 28 C. The values are for 24-hr EC§g
or enough to cause loss of equilibrium or mortality.
a The value reported is a 96-hr £€50 (decreased shell growth).
Water temperature was 19 C. Lost equilibrium at 1 ppm.
— The values reported are given as LC5Q.
a No effect on exposure to the chemical at 1 .0 ppm.
a Water temperature was 20 C. No effect was noticed on
exposure to 1 .0 ppm.
a Toxicant chemicals were evaluated in seawater at tempera-
tures averaging about 28 C. The values are for 24-hr ECgn,
or enough to cause loss of equilibrium or mortality.
- Silvex in concentrations of 0.2 to 3.0 ppm killed 75 to 100
percent of the most prominent and damaging weeds.
A slow kill is desirable because there is less chance of a fish
kill due to an oxygen depletion resulting from weed decom-
position.
The results of 2 years' experimentation on control of aquatic
weeds in Georgia farm ponds using Silvex indicated that this
herbicide has a far wider range of satisfactory control than
any other herbicide used in Georgia.
- This paper concerns lack of growth in weight and length of
Reference
(Year)
Butler
(1965)
Butler
(1965)
Cope
(1965)
Butler
(1965)
Butler
(1965)
Thomaston, et al
(1959)
Houser
2
^
m
Z
_
X
00
Silvex
(Amchem)
Silvex
(K salt)
Lepomis
macrochirus
Lepomis
macrochirus
BSA
BSA
700(T18hr)
600 (T 32 hr)
83.0 (T2A) L
100.0IT2A) G
j cd e g
fish. A coefficient of condition C(TL) was derived from
fish lengths in inches and weights in grams, and is expressed
as a ratio of 100,000 x weight in pounds to the cube of the
length in inches. The C(TL) of the fish is reported to be a
result of the application of the herbicide over a 2-year
period.
The experiment was conducted at 65 F. Fish were 2 in. long.
Toxicity data for 24 and 48 hours are presented for liquid
(L) and granular (G) formulations. Various commercial
formulations were tested. The liquid formulations were
almost invariably more toxic than the granular ones.
(1962)
Cope
(1963)
Hughes and
Davis
(1965)
-------
Silvex
to
8
m
•3)
o
O
m
S
9
3D
O
O
Silvex
(Kuron)
Silvex
(pelletized)
Silvex
(butoxyethanol
ester)
Silvex
(isooctyl
ester)
Silvex
(potassium
salt)
Silvex
(propylene
glycol
butylether
ester)
Silvex
Filamentous algae FL
Cladophora
Spirogyra
Hydrodictyon
Submerged plants
Chara
Potamogeton
Emergent plants
Alisma
Sagittaria
Floating plants
Lemna
Zooplankton
Lepomis BSA
macrochirus
Pimephales
promelas
Lepomis BSA
macrochirus
Pimephales
promelas
Lepomis BSA
macrochirus
Lepomis BSA
macrochirus
Lepomis BSA
macrochirus
Lepomis BSA
macrochirus
Benthic FL
community of
a farm pond
N. Y.
Boone
County,
Mo.
(O)
(O)
2.0 (K)
(O)
2.0 (K)
(O)
(O)
2.0 (K)
(O)
2.4 (T4A)
7.2 (T4A)
(S) 14 (T4A)
(H) 86 (T4A)
(S) 13(T4A)
(H) 73 (T4A)
1.2 (T2A)
3.7 (T2A)
8.3 (T2A)
16.6 (T2A)
2.8 & 4.6 (O)
cd
2 ppm caused 20% kill.
2 ppm caused 35% kill.
2 ppm did not cause any kill.
Complete decomposition occurred in about 3 weeks.
2 ppm did not cause any kill.
2 ppm caused 20% kill.
Complete decomposition occurred in about 3 weeks.
Applications of 4 ppm produced significant reduction.
Bioassay method in Standard Methods for Examination of
Water was used. TLm values for 24 and 48 hr are also
presented.
Comment same as above.
The various salts of the chemicals showed wide variations
in toxicity.
Comment same as above.
Comment same as above.
Comment same as above.
Many different aquatic plants, insects, molluscs, and leeches
are listed, 79 organisms in all. Data list populations in
treated versus untreated pond areas as well as seasonal
variations in numbers. The tests were conducted in a series
of plastic enclosures 12x18 feet in area, and 4 feet deep.
The most conspicuous change in the pond benthos in the
enclosures treated with silvex was numerical increase at
both treatment concentrations. Tendipedids, oligochaetes,
Chaoborus, and libel I ud ids, increased markedly. The densi-
ties of damsel flies, leeches, and snails, were unaffected.
Chrysops alone decreased. Other groups of organisms were
not sufficiently numerous for analysis. The increases may
have been caused by the enriching influence of decaying
vegetation. The application rate of 2.8 ppm was within
the recommended range of concentrations while 4.6 ppm
was in excess of recommended rates.
Co well
(1965)
Surber and
Pickering
(1962)
Surber and
Pickering
(1962)
Hughes and
Davis
(1963)
Hughes and
Davis
(1963)
Hughes and
Davis
(1963)
Hughes and
Davis
(1963)
Harp and
Campbell
(1964)
o
X
oo
-------
o
o
2
m
o Chemical
r Silvex
2 (triethyl-
m amine)
2
O Silvex
> (triethyl-
.g amine)
O Silvex
O (polyglycol
3 butyl ether
ester)
Silvex
Silvex
(polyglycol
butyl
ether
ester)
BO
V
to
•£
Silvex
Silvex
(K salt)
Silvex
Organism
Lepomis
macrochirus
Lepomis
macrochirus
Penaeus
aztecus
Leiostomus
xanthurus
(juvenile)
Crassostrea
virginica
Penaeus
aztecus
Leiostomus
xanthurus
Phytoplankton
Salmo
gairdneri
Lepomis
macrochirus
Pteronarcys
californicus
Daphnia
pulex
Simocephalus
serrulatus
Daphnia
magna
Rainbow
trout
Bluegill
Salmon
Bluegill
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study<1) Location<2) ppm(3)
BSA - 20(T1A)
BSA - 16IT1A)
L - 0.28 (O)
BSA - 0.36 (O)
BCFA&BSA - 1.0(0,20%)
0.24 (O)
0.36 (T2CFA)
78% (O)
BSA - 1.4IT2A)
16.6(T2A)
0.76 (T2A)
2.40 (T2A)
2.0 (T2A)
BSA - 100(0)
21.9 (O)
14.5 (O)
BSA - 1.23(T2A)
0.60 (T2A)
Experimental
Variables
Controlled
or Noted(4) Comments
a b e This report is a simple and straightforward determination of
a median tolerance limit for a selected group of herbicides.
a b e Comment same as above.
a Toxicant chemicals were evaluated in seawater at tempera-
tures averaging about 28 C. The values are for 24-hr ECso
or enough to cause loss of equilibrium or mortality.
a Water temperature was 16 C. The figure reported is a 48-hr
ECso-
— Seawater was pumped continuously into test aquaria.
Salinity, temperature, and plankton fluctuated with tide.
and ambient weather conditions. Some bioassays with fish
were static. Toxicity was reported for the following:
Oyster — 96-hr ECso — Cone, which decreased
shell growth.
Shrimp — 48-hr EC5Q — Cone, which killed or
paralyzed 50% of test animals.
Fish — 48-hr ECso — Cone, which killed
50%.
Phytoplankton — Percent decrease of CO2 fixation to a
4-hr exposure at.1 .0 ppm chemical
concentration.
a This paper reports acute toxicity of a number of compounds.
and discusses subacute mortality as well. Effects on repro-
duction and behavior are also discussed. Data presented
as EC5Q.
a c d i q Toxicity, in terms of median immobilization concentration
((CSQ), is presented for Daphnia; median lethal concentra-
tion (LCsfj) for rainbow trout and bluegill are reported.
— Data are given as LC5Q.
Reference
(Year)
Hughes and
Davis
(1967)
Hughes and
Davis
(1967)
Butler
(1965)
Butler
(1965)
Butler
(1965)
Cope
(1966)
Crosby and
Tucker
(1966)
Bohmont
(1967)
^
•o
m
O
X
CD
-------
Silvex
(potassium
salt)
Lepomis
macrochirus
BSA
Silvex
(ester)
Silvex
(ester)
ts)
O
tfi
8
Silvex
(potassium
salt)
Silvex
(sodium
salt)
Silvex
m
3D
Q
Simazen
(granular)
O
Z Simazine
3D
O
O
L. cyanellus
(eggs)
Micmpterus
dolomieui
Erimyzon
sucetta
(eggs)
L. macrochirus
(fry)
Lepomis
macrochirus
L. cyanellus
(eggs)
L. macrochirus
(fry)
Lepomis
macrochirus
L. cyanellus
Micmpterus
dolomieui
Erimyzon
sucetta
L. macrochirus
(fry)
Lepomis
macrochirus
L. cyanellus
Lepomis
macrochirus
(fry)
Pteronarcys
californica
(naiads)
Althernanthera
philoxeroides
Nympheae sp
Leersia sp
Paspalum sp
Juncussp
BSA
BSA
BSA
BSA
FL
FL
Fla.
Farm
ponds in
Ga.
20 (NTE)
20 (NTE)
20 (NTE)
50 (S)
10 (NTE)
10 (NTE)
20 (S)
2.4/2 (O)
1.0 (NTE)
2.4/4 (O)
1.0/4(O)
2.4 (NTE)
1.0 (NTE)
2.0 (S)
30 (S)
10 (NTE)
50 (S)
0.00034 (T4A)
(O)
(O)
Fertilized fish eggs of indicated species were placed in 1
liter of test solution and allowed to hatch. Toxicity data
are presented as concentration in ppm/number of days
survival. Maximum length of test was 8 days. No food
was added. Small bluegill were tested to find the highest
concentration of chemical which did not cause death in
12days(S).
Hiltibran
(1967)
Comment same as above.
Comment same as above.
Comment same as above.
Comment same as above.
JLl Data reported as LCgg at 15.5 C in 4 days.
At 10.0 Ib/acre, alligator weed was not affected.
Although Nympheaesp was killed at a rate of 50 Ib/acre,
no epinastic effects were noted. The chemical did not
translocate and only killed the tops.
Treatments on Leersia sp.Paspalum sp, and Juncus sp were
unsuccessful and gave no encouraging results. Limited use
of simazine has not proven it to be a satisfactory aquatic
herbicide in Georgia.
Hiltibran
(1967)
Hiltibran
(1967)
m
z
O
X
09
Hiltibran
(1967)
Hiltibran
(1967)
Sanders and
Cope
(1968)
Copeland and
Woods
(1959)
Thomaston, et al
(1959)
-------
COMMERCI
i-
0
X
m
S
5
r
3)
O
0
c
en
(p
to
ON
Chemical
Simazine
Simazine
(herboxy-
1962)
Simazine
(herboxy-
1960)
Simazine
Simazine
Simazine
(WP)
Simazine
(WP)
Organism
Onchorynchus
tshawytscha
Phoxinus
phoxinus
Phoxinus
phoxinus
Micropterus
salmoides
(fry)
Ictalurus
punctatus
(fry)
Lepomis
macrochirus
(fry)
Phyto plankton
Hydrodictyon
reticulatum
Zygnema spp
etc.
Zooplankton
Fish
Micropterus
salmoides
Lepomis
cyanellus
Bluegill
Rainbow
trout
Lepomis
macrochirus
(eggs)
L. cyanellus
(eggs)
Micropterus
dolomieui
(eggs)
Erimyzon
sucetta
(eggs)
L. macrochirus
(fry)
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study!1) Location!2) ppm(3)
BSA&CF - 7.0 (T1A)
6.6 (T2A)
BSA - (O)
BSA - 1.25IK2A)
1.5 (T2A)
BSA - 25.0 (SB3)
10.0 (SB3)
10.0(SB3)
FL Ala. 2.0 (K1)
2.0 K1)
(0)
(0)
(0)
BSA - 118(T4A)
56 (T4A)
L - 10/4 (O)
10/5 (0)
10/3 (0)
10 (NTE)
0.3 (S)
Experimental
Variables
Controlled
or Noted!4' Comments
a c d e Concentrations were based on percent active ingredient.
Median tolerance limits for 72 and 96 hours estimated from
the constant flow experiment were 7.2 ppm and 6.5 ppm.
respectively, for this species.
a c d e Two series of aquarium aerated tests were performed, one
without plants (Callitriche, and Elodea). 20% kill occurred
in 3 days. The highest nonlethal concentration was 5 ppm.
a c d e Two series of aquarium tests were performed, with and
without plants, which lowered the toxicity. 90% kill
occurred at 5 ppm in 6 hr.
a c d e f p At least 90 percent of the fry survived for a period of 72
hours at the concentration listed.
a In a series of bass spawnings and rearing ponds, Simazine was
used at concentrations of 0.5, 1 .0, and 2.0 ppm to control
light to medium growths of phytoplankton which interfered
with bass production. Success was uniform with control last-
ing for as long as 85 days. No fish kills occurred and the
chemical was apparently not toxic to zooplankton.
a This is an estimated LCijQ value at temperatures from 55 to
75 F.
— Fertilized fish eggs of indicated species were placed in 1 liter
of test solution and allowed to hatch. Toxicity data are
presented as concentration in ppm/number of days survival.
Maximum length of test was 8 days. No food was added.
Small bluegill were tested to find the highest concentration
of chemical which did not cause death in 12 days (S).
Reference
(Year)
Bond, et al
(1960)
Vivier and
Nisbet
(1965)
Vivier and
Nisbet
(1965)
Jones
(1965)
Snow
(1963)
Cope
(1965)
Hiltibran
(1967)
m
Z
0
X
00
-------
Simazine
Simazine
Sinox
Slickgone 1
Slickgone 2
Slix
8
m
3)
o
Soaps
(household)
-o
3)
O
0
i
Sovicide
tetra
aminol
Stam F-34,
tech.
Rainbow
trout
Bluegill
Lepomis
macrochirus
BSA
L. cyanellus
(eggs)
Micropterus
dolomieui
(eggs)
Erimyzon
sucetta
Richardsonius
balteatus
hydroflox
Pandalus
montagni
Crangon
crangon
Cardium
edule
Carcinus
malmas
Pandalus
montagni
Crangon
crangon
Cardium
edule
Carcinus
maenas
Pandalus
montagni
Crangon
crangon
Carcinus
maenas
Cardium
edule
Pimephales
promelas
(juveniles)
Phoxinus
phoxinus
Salmo
gairdnerii
BSA
BSA
BSA
BSA
BSA
BSA
BSA
56.0 (T2A)
118.0(T2A)
10(NTE)
10/7 (O)
10(NTE)
10 (NTE)
10 (S)
0.16 (T1A)
0.14 (T2A)
0.13(T4A)
5.2 (T2A)
6.6 (T2A)
32.4 (T2A)
35.0 (T2A)
4.5 (T2A)
3.5 (T2A)
30.5 (T2A)
21.3 (T2A)
12.1 (T2A)
114.5(T2A)
150.0 (T2A)
12.7 (T2A)
(S) 34-39
(T1-4A)
(H) 1,470-1,530
(T1-4A)
8(100%K)
4,000 (T2A)
acdef
acdf
a cd e
Data are given as
Fertilized fish eggs of indicated species were placed in 1 liter
of test solution and allowed to hatch. Toxicity data are
presented as concentration in ppm/number of days survival.
Maximum length of test was 8 days. No food was added.
Small bluegill were tested to find the highest concentration
of chemical which did not cause death in 12 days (S):
Results given were in soft water.
Results in hard water were as follows:
0.24 (T1 A), 0.24 (T2A), and 0.24 (T4A).
Experiments were conducted in tanks holding 10 liters of
seawater at 15 C.
It was shown that the toxicity of this solvent emulsifier
decreased with time due to evaporation of the solvent.
Comment same as above.
Experiments were conducted in tanks holding 10 liters of
seawater at 15 C.
It was shown that the toxicity of this solvent emulsifier
decreased with time due to evaporation of the solvent.
Slix at a concentration of 10 ppm killed 100% of Crangon
crangon larvae in 3 hr; at 33.3 ppm it killed 70% of
Carcinus maenas larvae in 3 hr.
Syndets and soaps were of nearly equal toxicity in soft
water (S) but syndets were approximately 40X more toxic
than soap in hard water (H).
The highest concentration nonlethal in 6 hr was 4 ppm.
The experiment was conducted at 55 F. Fish were 2-3 in.
long.
Bohmont
(1967)
Hiltibran
(1967)
Webb
(1961)
Port man n and
Connor
(1968)
Portmann and
Connor
(1968)
m
O
X
oo
Portmann and
Connor
(1968)
Henderson, et al
(1960)
Vivier and
Nisbet
(1965)
Cope
(1963)
-------
COMMERCI
r~
s
m
_
o
r
T3
3)
O
O
tp
^^
00
Chemical
Stauffer
N2790
Stauffer
N-2790
(tech)
Stauffer
R-1910
Stauffer
(R-1910,
tech)
Stauffer
R-1910
Stauffer
R-4461
Stauffer
Organism
Leiostomus
xanthurus
(juvenile)
Oyster
Penaceus
aztecus
Rainbow
trout
Bluegill
Penaeus
aztecus
Leiostomus
xanthurus
(juvenile)
Oyster
Rainbow
trout
Bluegill
Crassostrea
virginica
Penaeus
setiferus
Leiostomus
xanthurus
Fundulus
similis
Mugil
cephalus
Cyprinodon
variegatus
Phytoplankton
Crassostrea
virginica
Penaeus
aztecus
Leiostomus
xanthurus
Phytoplankton
Oyster
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study C" Location*2' ppm (3)
BSA - 0.24 (O)
BCF 0.33 (O)
L 0.0024 (O)
BSA - 0.019 (T4A)
0.0062 (T4A)
L - (0)
BSA - (O)
BCF
BSA - 3.6 (T4A)
5.5 (T4A)
BCFA - 1.0 (NTE,
all species)
BCFA & - 0.45 (O)
BSA
1.0(0, 10%)
0.32 (T4CFA)
NTE
BCF - 0.45 (O)
Experimental
Variables
Controlled
or Noted'4' Comments
a Water temperature was 24 C. The figure reported is a
48-hr EC5Q.
The value reported is a 96-hr EC5Q (decreased shell growth).
Toxicant chemicals were evaluated in sea water at tempera-
tures averaging about 28 C. The values are for 24-hr EC§Q
or enough to cause loss of equilibrium or mortality.
— The values reported are given as LC5Q.
a Toxicant chemicals were evaluated in seawater at tempera-
tures averaging about 28 C. The values are for 24-hr ECso
or enough to cause loss of equilibrium or mortality. No
effect occurred at 1 .0 ppm.
a Water temperature was 25 C. No effect was noticed on
exposure to 1 .0 ppm.
No effect on exposure to the chemical at 1.0 ppm.
a This is an estimated LCtjQ value at temperatures from 55 to
75 F.
— Seawater was pumped continuously into test aquaria.
Salinity, temperature, and plankton fluctuated with tide.
and ambient weather conditions. Some bioassays with
fish were static. Toxicity was reported for the following:
Oyster - 96-hr EC$Q — Cone, which
decreased shell growth.
Shrimp — 48-hr EC$Q — Cone, which killed or
paralyzed 50% of test animals.
Fish - 48-hr EC50 - Cone, which killed 50%.
Phytoplankton — Percent decrease of CO2 fixation to
a 4-hr exposure at 1 .0 ppm chemical
concentration.
— Comment same as above.
a The value reported is a 96-hr ECgo (decreased shell growth).
Reference
(Year)
Butler
(1965)
Butler
(1965)
Butler
(1965)
Cope
(1965)
Butler
(1965)
Butler
(1965)
Butler
(1965)
Cope
(1965)
Butler
(1965)
Butler
(1965)
Butler
•o
m
z
o
09
R-4461
(1966)
-------
Stauffer
R-4461
Stauffer
R-4461
(tech)
Stauffer
R-4461
Stauffer
R-5092
Steramine
Streptomycin
i sulfate
N)
O
Strobane
8
m
a)
o
r
o
m
5 Strobane +
i~ methyl
2 parathion
§ Strobane
Penaeus
aztecus
Rainbow BSA
trout
Bluegill
Leiostomus BSA
xanthurus
(juvenile)
Leiostomus BSA
xanthurus
(juvenile)
Oyster BCF
Penaeus L
aztecus
Chlorella L
pyrenoidosa
Cylindrospermum L
licheniforme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (Sol
Chlorella
variegata (Cv)
Gomphonema
parvulum (Cp)
Nitzschia
palea (Npl
Blue FE
crab
Marsh fiddler
crab
Red-jointed
fiddler crab
Cyprinodon
variegatus
Mugil
curema
Leiostomus
xanthurus
Oyster BCF
Pteronarcys sp BSA
(nymphs)
Bombay
Hook
Island,
Del.
(O)
0.72 (T4A)
0.81 (T4A)
0.32 (O)
0.02 (O)
(O)
0.0032 (O)
20 (AC < 1/2
2.0 (O)
(O)
(O)
(O)
(O)
(O)
(O)
0.026 (O)
0.0005 (T4A)
Toxicant chemicals were evaluated in seawater at temper-
atures averaging about 28 C. The values are for 24-hr ECgrj
or enough to cause loss of equilibrium or mortality. No
effect occurred at 1.0 ppm.
This is an estimated UCso value at temperatures from 55
to 75 F.
Water temperature was 25 C. The figure reported is a
48-hr EC50.
Water temperature was 26 C. The figure reported is a
48-hr EC5Q.
No effect on exposure to the chemical at 1.0 ppm.
Toxicant chemicals were evaluated in seawater at temper-
atures averaging about 28 C. The values are for 24
or enough to cause loss of equilibrium or mortality.
Describes a bioassay method to differentiate between an
algicide (AC) and an algistat (AS). The treated culture was
subcultured as time progressed. Allen's medium was used.
Observations were made on the 3rd, 7th, 14th, and 21st days
to give the following (T = toxic, NT = nontoxic, PT = par-
tially toxic with number of days in parentheses. No number
indicates observation is for entire test period of 21 days):
Cl -T
Ma-T
So -T
Cv -NT
Gp-NT
Np-T(21)
Strobane was applied at the rate of 0.3 pound per acre.
The location under study was a salt marsh bounded by
Delaware Bay.
Organisms were confined in cages within the test area.
C. variegatus, M. curema, and L. xanthurus showed 16 per-
cent mortality in 7 days.
Blue crabs showed 27 percent mortality when exposed for
7 days in streams and 20 percent mortality in ponds.
Marsh fiddler crabs and red-jointed fiddler crabs showed
mortalities of 68 and 20 percent, respectively, when ex-
posed for 7 days.
The value reported is a 96-hr ECso (decreased shell growth).
Experiments were all conducted at 60 F in 1964. The values
were listed as
Butler
(1965)
Cope
(1965)
Butler
(1965)
Butler
(1965)
Butler
(1965)
Butler
(1965)
Fitzgerald and
Faust
(1963)
Palmer and
Maloney
(1955)
m
O
X
00
George, et al
(1957)
Butler
(1965)
Cope
(1965)
-------
8
m
o Chemical
*" Strobane
o
X
m
5 Strobane
p (tech)
•" Strobane
^0
30
O
o
C Sulfotepp
H
Cn
Swep
"Synthetic
detergent"
Systox
•F Systox
N>
O
Systox
Systox
Systox
(tech.
92 percent)
Organism
Oyster
Bluegill
Pteronarcys
californica
(naiads)
Channel
catfish
(fingerlings)
Lepomis
macrochirus
Sludge
worms
Pimephales
promelas
Fathead
minnow
Pimephales
promelas
Pimephales
promelas
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study (D Location<2) ppm<3) or Noted W
BCF - 0.02-0.059 (O) a
BSA - 0.0084 (T4A)
BSA - 0.0005 (T4A) a c d e f
BSA - <1.0(K1A) a
BSA - 6.0 (T1 A) abe
BSA - 23 (T4A) a c d i
BSA - 3.9 (T4A) a c d e f
BSA - 4.2 (T4A) a
BSA - 3.6 (T4A) adef
BSA - 3.6 (T4A) a
BSA - 2.9 (T4A) a c d e
0.11 (T4A)
12(T4A)
0.66 (T4A)
Comments
The value reported is a 96-hr ECgQ (decreased shell growth).
The values reported are given as LCgg.
Data reported as LC$Q at 15.5 C in 4 days.
Tap water was used. Considerable additional data are
presented.
This report is a simple and straightforward determination of
a median tolerance limit for a selected group of herbicides.
Data using hard and soft water are presented as well as
information on the effect of temperature. Additional
TLm data are presented.
Tests were performed in both hard and soft water. Additional
tolerance limit values are given.
It was the authors opinion that pH, alkalinity and hardness.
within the usual range in natural waters, had little effect on
the toxic effect of the compounds studied. The values
given are from Henderson, Pickering, and Tarzwell, "The
Relative Toxicity of Ten Chlorinated Hydrocarbon Insecti-
cides to Four Species of Fish" It is interesting that the
different tables from the above book (as reported in this
paper) report widely different values for the same compounds.
This experiment was performed in hard water.
Concentrations were based on percent active ingredient.
Bioassay investigations of the new insecticides indicate that
in general the organic phosphorus compounds are not as
toxic to fish as are the chlorinated hydrocarbons. The
toxicity of most of these materials was not significantly
influenced by water quality. Therefore it is to be expected
that the toxicity of these materials will not differ signifi-
cantly in different streams.
Soft water primarily was the test medium. TLm's reported
for 24, 48, and 96 hr. Acetone or alcohol used as solvent
or carrier in most cases.
Reference
(Year)
Butler
(1965)
Cope
(1965)
Sanders and
Cope
(1968)
Clemens and
Sneed
(1969)
Hughes and
Davis
(1967)
Wurtz and
Bridges
(1961)
Henderson and
Pickering
(1958)
Tarzwell
(1959)
Henderson, et al
(1959)
Tarzwell
(1959)
Pickering, et al
(1962)
^
m
Z
O
x
00
-------
2,4,5-T
w
to
8
m
3D
2,4,5-T
(pellets)
2,4,5-T
2,4,5-T
(dimethyl-
amine
ester)
2,4,5-T
(butoxy-
ethanol
ester)
2,4,5-T
(isooctyl
ester)
2,4,5-T
(propylene
glycol
butyl ether
ester)
2,4,5-T
(oleic-1.3-
propylene
diamine)
j£ 2,4,5-T
O (isopropyl
I ester)
1 2,4,5-T
5 (triethyl
i~ amine)
TJ
3)
O
O
2,4,5-T
Cylindrospermum L
lichen/forme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Althernan thera F L
philoxeroides
Naj'as
quadalupensis
Spatterdock
Althernan thera F L
philoxeroides
Lepomis BSA
macrochirus
Lepomis BSA
macrochirus
Lepomis BSA
macrochirus
Lepomis BSA
macrochirus
Lepomis BSA
macrochirus
Lepomis BSA
macrochirus
Lepomis BSA
macrochirus
Lepomis BSA
macrochirus
2.0 (O)
Fla.
Fla.
(O)
(0)
144(T2A)
1.4(T2A)
26 (T2A)
17 (T2A)
2.9 (T1A)
1.8 (T1A)
53.7 (T1A)
11.0IT1A)
a b e
Observations were made on the 3rd, 7th, 14th, and 21st days
to give the following (T = toxic, NT = nontoxic, PT = par-
tially toxic with number of days in parentheses. No number
indicates observation is for entire test period of 21 days):
Cl -NT
Ma - T (3)
So -NT
Cv -NT
Gp-NT
Np-NT
The degree of control was as follows:
A. philoxeroides (20 Ib/acre) — 95 percent
N. quadalupensis (24 Ib/acre) — none
Spatterdock (21.8 Ib/acre) — 3 percent.
At 0.5 Ib/acre, only 1-2 percent control of alligator weed
was obtained.
The various salts of the chemicals showed wide variations in
toxicity.
Comment same as above.
Comment same as above.
Comment same as above.
The bioassay methods employed in this experiment were not
given in the paper but it was stated that the same procedures
were employed as in previous work.
Comment same as above.
Comment same as above.
This report is a simple and straightforward determination of
a median tolerance limit for a selected group of herbicides.
Palmer and
Maloney
(1955)
Copeland and
Woods
(1959)
Copeland and
Woods
(1959)
Hughes and
Davis
(1963)
Hughes and
Davis
(1963)
Hughes and
Davis
(1963)
Hughes and
Davis
(1963)
Davis and
Hughes
(1963)
Davis and
Hughes
(1963)
Davis and
Hughes
(1963)
Hughes and
Davis
(1967)
m
O
X
00
-------
to
8
m
g Chemical
r 2,4,5-T
X (polyglycol
"J butyl ether
5 ester)
f. 2.4,5-T
TJ
X
O
° 2,4,5-T
O (polyglycol
W butyl ether
ester)
2,4,5-T
(acid)
2,4,5-T
(polyglycol
butyl ether
ester)
4
/
)
)
2,4,5-T
(acid)
2,4,5-T
(polyglycol
butyl ether
ester
2.4,5-T
(ester)
Organism
Oyster
Leiostomus
xanthurus
(juvenile)
Penaeus
aztecus
Penaeus
aztecus
Crassostrea
virginica
Penaeus
aztecus
Leiostomus
xanthurus
Phytoplankton
Crassotrea
virginica
Penaeus
aztecus
Mugil
caphalus
Phytoplankton
Crassostrea
virginica
Penaeus
aztecus
Leiostomus
xanthurus
Phytoplankton
Lepomis
macrochirus
(eggs)
L. cyanellus
L. macrochirus
(fry)
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study (1) Location<2> ppm(3)
BCF - 0.14(0)
BSA - 0.32 (O)
L - (0)
L - (0)
BCFA& - 0.14(0)
BSA
1.0 (O,20%)
0.32 (T2CFA)
89% (O)
BCFA & - 20 (NTE)
BSA
1.0 (NTE)
50.0 (NTE)
-
BCFA& - 0.14(0)
BSA
1.0(0,20%)
0.32 (T2CFA)
89% (O)
L - 10 (NTE)
10 (NTE)
10 (S)
Experimental
Variables
Controlled
or Noted'4' Comments
a The value reported is a 96-hr ECso (decreased shell growth).
a Water temperature was 16 C. The figure reported is a
48-hr EC50.
a Toxicant chemicals were evaluated in seawater at tempera-
tures averaging about 28 C. The values are for 24-hr EC5Q
or enough to cause loss of equilibrium or mortality.
a Toxicant chemicals were evaluated in seawater at tempera-
atures averaging about 28 C. The values are for 24-hr ECsg
or enough to cause loss of equilibrium or mortality. No
effect occurred at 1 .0 ppm.
- Seawater was pumped continuously into test aquaria.
Salinity, temperature, and plankton fluctuated with tide,
and ambient weather conditions. Some bioassays with
fish were static. Toxicity was reported for the following:
Oyster — 96-hr ECgQ — Cone, which
decreased shell growth.
Shrimp — 48-hr EC§Q — Cone, which killed or
paralyzed 50% of test animals.
Fish - 48-hr ECso - Cone, which killed 50%.
Phytoplankton — Percent decrease of CO2 fixation to a
4-hr exposure at 1.0 ppm chemical
concentration.
— Comment same as above.
— Comment same as above.
Fertilized fish eggs of indicated species were placed in 1 liter
of test solution and allowed to hatch. Toxicity data are
presented as concentration in ppm/number of days survival.
Maximum length of test was 8 days. No food was added.
Small bluegill were tested to find the highest concentration
of chemical which did not cause death in 12 days (S).
Reference
(Year)
Butler
(1965)
Butler
(1965)
Butler
(1965)
Butler
(1965)
Butler
(1965)
Butler
(1965)
Butler
(1965)
Hiltibran
(1967)
3^
•o
m
X
00
-------
to
1—*
OJ
8
o
2
m
3)
o
>
T~
O
m
S
8
•D
3J
O
o
c
S
2.4.5-T
(ester)
2,4,5-T
(sodium
salt)
TAG 10%
2,3,5-TBA
2,3,6-TBA
TCA 90%
Sodium
TCA
Sodium
TCA
Sodium
TCA
TD47
Lepomis
macrochirus
L. cyanellus
Micropterus
dolomieui
L. macrochirus
(fry)
Lepomis
macrochirus
(fry)
Channel
catfish
(fingerlings)
Lepomis
macrochirus
Micropterus
salmoides
Lepomis
macrochirus
Micropterus
salmoides
Channel
catfish
(fingerlings)
Onchorynchus
tshawytscha
Mugil
cephalus
(juvenile)
Penaeus
aztecus
Micropterus
salmoides
(fry)
Ictalurus
punctatus
(fry)
Lepomis
macrochirus
(fry)
L
L
BSA
BSA
BSA
BSA
BSA
BSA
L
BSA
1.0 (NTE)
4/1 (O),
1.0 (NTE)
4/0 (O),
1.0 (NTE)
1.0 (S)
50 (S)
1.5IK1A)
90 (T2A)
55 (T2A)
1750IT2A)
1250 (T2A)
>2000(K1A)
870 (NTE)
(O)
(O)
0.075 (SB3)
0.2 (SB3)
0.2 (SB3)
Comment same as above.
Hiltibran
(1967)
Comment same as above.
a Tap water was used. Considerable additional data are
~ presented.
a c o The response of bluegill and bass fingerlings to nine agricul-
~ tural chemicals as determined by bioassay using river water
is presented in this report. Bluegills were more tolerant of
the chemicals tested than bass.
a c o Comment same as above.
a Tap water was used. Considerable additional data are
~ presented.
a c d e Concentrations were based on percent active ingredient.
a Water temperature was 28 C. No effect was noticed on
exposure to 1.0 ppm.
a Toxicant chemicals were evaluated in seawater at tempera
tures averaging about 28 C. The values are for 24-hr
or enough to cause loss of equilibrium or mortality. No
effect occurred at 1.0 ppm.
a c d e f p At least 90 percent of the fry survived for a period of
72 hours at the concentration listed.
Hiltibran
(1967)
Clemens and
Sneed
(1959)
Davis and
Hardcastle
(1959)
Davis and
Hardcastle
(1959)
Clemens and
Sneed
(1959)
Bond, et al
(1960)
Butler
(1965)
Butler
(1965)
Jones
(1965)
O
X
DO
-------
COMMERCI/
*»
r-
m
5
r~
•o
30
O
O
§
en
(n
T5
to
"^
Chemical
TD-47
TD-72
(EC6)
TD-282
[di(N,N-
dimethyltri-
decylamine)
salt of
Endothalll
TD-283
(mono-N.N-
dimethyltri-
decylamine)
salt of
Endothall)
TD-440
TD-497
Talodrin
Telodrin
TEPP
Bioassay
or Field
Organ ism Study ( 1 )
Carp- BSA
goldfish
hybrid
Notropis
umbra tills
N. lutrensis
Pimephales
notatus
Ictaluris
natalis
1. me/as
Lepomis
macrochirus
L. microtophus
Micropteris
salmoides
Gambusia F L
affinis
Australorbis BSA &
glabratus F L
Australorbis BSA &
glabratus F L
Lepomis BSA
macrochirus
Lepomis BSA
macrochirus
Leiostomus BSA
xanthurus
(juvenile)
Leiostomus BCH
xanthurus
(juvenile)
Fish BSA
Toxicity, Experimental
Active Variables
Field Ingredient, Controlled
Location(2) ppm (3) or Noted'4'
175IT4A) a
95 (T4A)
105 (T4A)
120IT4A)
175IT4A)
180IT4A)
125IT4A)
125(T4A)
120IT4A)
Ponds (O)
in III.
Puerto Variable (O) c
Rico
Puerto 3.8-6.2 (0) c
Rico
3.0 (T1A) abe
4.0 (T1 A) abe
0.0003 (O) a
(0) a
0.25 (K)
Comments
In addition to the median tolerance limits, this report also
has data on the residue of the chemical in the fish, some of
the physiological effects, and degradation curves for the
chemical in water.
When applied at 0.5 pounds per acre active ingredient, 18 per-
cent mortality occurred in 1 day.
Seven of the tested compounds failed to meet acceptability
criteria — that is, complete kill after 6-hr exposure to
10 ppm. They were not used in field tests. Field tests
showed WL 8008 to be highly effective.
Comment same as above.
This report is a simple and straightforward determination of
a median tolerance limit for a selected group of herbicides.
Comment same as above.
Water temperature was 13 C. The figure reported is a
48-hr EC50.
A concentration of 0.000025 ppm will kill in 10 days. The
fish were able to survive for 5 months in a concentration
of 0.00001 ppm.
A concentration of 0.25 ppm was lethal in aquarium tests.
Reference
(Year)
Walker
(1963)
Mulla
(1963)
Seiffer and
Schoof
(1967)
Seiffer and
Schoof
(1967)
Hughes and
Davis
(1967)
Hughes and
Davis
(1967)
Butler
(1965)
Butler
(1965)
Linduska and
Surber
(1948)
•o
m
O
03
-------
TEPP
Fathead
minnow
BSA
1.O (T4A)
TEPP
TEPP
Pimephales
promelas
Lepomis
macrochirus
Pimephales
promelas
BSA
BSA
TEPP
CO
K> TEPP
»— »
TEPP
TEPP
(tech.
40 percent)
8
s
s
m
3D
o
> Terramycin
r
0
m
^
9
r
-o
3D
O
o
c
CO
Channel
catfish
(fingerlings)
Pimephales
promelas
Protococcus sp
Chlorella sp
Dunaliella sp
Phaeodactylum
tricornutum
Monochrysis
lutheri
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Cylin drospermum
lichen/forme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
BSA
BSA
L
BSA
L
1.7 (T4A)
0.84 (T4A)
1.7IT4A)
2.3 (K1A)
1.7 (T4A)
500 (NG)
500 (NG)
500 (K)
500 (K)
500 (K)
2.1 (T4A)
1.3(T4A)
21 (T4A)
1.8 (T4A)
2.0 (O)
It was the authors opinion that pH, alkalinity and hardness,
within the usual range in natural waters, had little effect on
the toxic effect of the compounds studied. The values
given are from Henderson, Pickering, and Tarzwell, "The
Relative Toxicity of Ten Chlorinated Hydrocarbon Insecti-
cides to Four Species of Fish". It is interesting that the
different tables from the above book (as reported in the
paper) report widely different values for the same compounds.
This experiment was performed in hard water.
Tests were performed in both hard and soft water. Additional
tolerance limit values are given.
Tarzwell
(1959)
a Bioassay investigations of the new insecticides indicate that
in general the organic phosphorus compounds are not as
toxic to fish as are the chlorinated hydrocarbons. The
toxicity of most of these materials was not significantly
influenced by water quality. Therefore it is to be expected
that the toxicity of these materials will not differ signifi-
cantly in different streams.
£ Tap water was used. Considerable additional data are
presented.
a_ d e f Concentrations were based on percent active ingredient.
a^ This paper concerns the growth of pure cultures of marine
plankton in the presence of toxicants. Results were
expressed as the ratio of optical density of growth in the
presence of toxicants to optical density in the basal medium
with no added toxicants. NG = no growth, but the
organisms were viable.
a c d e Soft water primarily was the test medium. TLm's reported
~ ~ for 24, 48, and 96 hr. Acetone or alcohol used as solvent
or carrier in most cases.
Observations were made on the 3rd, 7th, 14th, and 21st days
to give the following (T = toxic, NT = nontoxic, PT = par-
tially toxic with number of days in parentheses. No number
indicates observation is for entire test period of 21 days):
Cl - PT (7)
Ma-T
So -NT
Cv -NT
Gp-NT
Np-T(3) PT(7)
Henderson and
Pickering
(1958)
Tarzwell
(1959)
Clemens and
Sneed
(1959)
Henderson, et al
(1960)
Ukeles
(1962)
Pickering, et al
(1962)
Palmer and
Maloney
(1955)
-------
8
m
g Chemical
> -
*~ Thanite
X (isobornyl
JJ thiocyano-
- acetate)
P
£ Tetrachloro-
-o phene
30
D
C
-3
CO
TFM
trt
T3
to
ON
TFM
Bioassay
or Field
Organism Study'1)
Green BSA
sunfish
Cylindrospermum L
licheniforme (CD
Microcystis
aeruginosa (Ma)
Scenedesmus
obliquus (So)
Chlorella
variegata (Cv)
Gomphonema
parvulum (Gp)
Nitzschia
palea (Np)
Petromyzon BSA
mar in us
Micropterus
salmoides
Micropterus
dolomieui
Lepomis
macrochirus
Stizostedion v.
vitreum
Perca
flavescens
Ictalurus
natal is
Catostomus
commersoni
Notropis
heterolepis
Notemigonus
crysoleucas
Pimephales
promelas
Sal mo
gairdnerii
Lamprey BFR + L
(larvae)
Rainbow
trout
(fingerlings)
Toxicity, Experimental
Active Variables
Field Ingredient, Controlled
Location(2) ppm(3) or IMotedW
- 1.0(K6hr) aep
0.5 (K 6 hr)
2.0 (O) a
- 3-10(O) acde
22-42 (0)
34.5-42 (0)
21.5-44.0(0)
5.75-11.5 (O)
7.25-20.5 (0)
5.75-15.5 (O)
5.0-13.0(0)
13.25-28.0(0)
14.75-33.0 (0)
16.0-35.5 (O)
12.0-25.25 (O)
Great 1.5(K8hr) a
Lakes 2.0 (K 2 hr)
(Mich) 3.0(K19hr)
5.0 (K 3 hr)
Comments
The main purpose of this experiment was to determine the
repellent characteristics of certain chemicals. The experi-
ments were conducted in a wooden trough.
Observations were made on the 3rd, 7th, 14th, and 21st days
to give the following (T = toxic, NT = nontoxic, PT = par-
tially toxic with number of days in parentheses. No number
indicates observation is for entire test period of 21 days) :
Cl -T(3)PT(7)
Ma -NT
So - PT (7)
Cv - PT (3)
Gp-NT
Np-T(3)
Three types of dilution water used with hardness values of
95.4, 141.7, and 203.3 ppm. As a lamprey larvicide, 3-1 0
ppm required. Toxicity range (ppm) given as that which
kills 25 percent of the test fish.
Describes a portable field monitor, using water obtained at
the site.
Reference
(Year)
Summerfelt and
Lewis
(1967)
Palmer and
Maloney
(1955)
Applegate and
King
(1962)
Howell and
Marquette
(1963)
*^
5
•o
m
X
DO
-------
TFM
Thanite
to
~J
Thimet
Thimet
Thimet
Thiodan® I
EC2
8
| Thiodan® 1 1
m EC2
30
O
X Thiodan
"J (tech,
96.6 percent)
Hydra
Turbellarians
Eripidelidae
Burrowing
mayflies
Black
flies
Clams
Sea
lamprey
Rainbow
trout
Gambusia
affinis
Gambusia
affinis
Pimephales
promelas
Lepomis
macrochirus
Leiostomus
xanthurus
Cyprinodon
variegatus
Mugil
cephalus
Gambusia
affinis
Rana
catesbeiana
(tadpoles)
Gambusia
affinis
Rana
catesbeiana
(tadpoles)
Pimephales
promelas
Lebistes
reticulatus
Channel
catfish
(fingerlings)
BSA (L)
BSA
BSA
BSA
BCFCH
FL
Cal.
FL
BSA
BSA
Cal.
3.0 (K1A)
4.0-8.0 (K1A)
12.0 (K1A)
12.0 (K1A)
8.0 (K1A)
16.0 (K1A)
4.0 (K1A)
13.0(O)
0.8 (LD*
0.9 (L1)**
•Resistant
fish
**Nonresistant
fish
0.05 (K 83%)
0.25 (T4A)
0.0047 (T4A)
0.0005 (O)
0.0005 (O)
0.0005 (O)
0.5 (O)
0.5 (O)
0.0033 (T4A)
0.0037 (T4A)
>1.0 (K1A)
All numbers cited are for 1OO% kill in 22-24 hours.
The number given for rainbow trout was for a 60% kill in
22-24 hours.
Data were given for fourteen other aquatic species, but they
are not included here because of very low toxicity or doubtful
data. These included leeches, isopods, scuds, crayfish, stone-
flies, dragonflies, waterbugs, water boatmen, mayflies, caddis-
flies, bloodworms, snipe flies, and snails.
Smith
(1967)
This paper deals with the resistance of mosquito fish to
chlorinated hydrocarbon compounds. Resistant fish were
not always less sensitive to these chemicals.
a Chemicals were dissolved in acetone, and tests were run in
triplicate. Toxicity is given as average percent fish killed
in 24 hr.
a c d e f The toxicity of this substance was not influenced by the
quality of the water (pH, hardness, alkalinity).
At a concentration of 0.0005 ppm, the following percent
acetylcholinesterase activity as compared to controls was
found:
L. xanthurus— 84
C. variegatus— 68
M. cephalus - 69.
Mixed populations of the indicated test species contained in
cages were exposed to various insecticidal chemicals applied
as dilute sprays to ponds 1/16 acre in size. The indicated
toxicant concentration is in Ib/acre, and resulted in a 100
percent mortality for the fish, and a 100 percent mortality
for the tadpoles in 24 hr.
Comment same as above.
a c d e f The toxicity of this substance was not influenced by the
quality of the water (pH, hardness, alkalinity).
Tap water was used. Considerable additional data are
presented.
Boyd and
Ferguson
(1964)
Lewallen
(1959)
Pickering and
Henderson
(1966)
Butler and
Johnson
(1967)
Mulla
(1963)
Mulla
(1963)
Pickering and
Henderson
(1966)
Clemens and
Sneed
(1959)
m
o
X
00
-------
8
m
o Chemical
r Tiguron
X
m
S
2
r~
3
O
C
q
C/)
Tillam
*P
K)
00
TNT
Organism
Salmo
gairdneri
Salmo
trutta
Salvelinus
fontinalis
Salvelinus
namaycush
Ictalurus
punctatus
Lepomis
macrochirus
Crassostrea
virginice
Penaeus
duorarum
Penaeus
setiferus
Leiostomus
xanthurus
Fundulus
similis
Mugil
cephalus
Cyprinodon
variegatus
Phytoplankton
Lythrurus
umbratilis
Hyborhynchus
notatus
Cyprinella
whippli
Helioperca
incisor
Gambusia
affinis
Cristivomer n.
namaycush
Ericymba
buccata
Cyprinus
carpio
Ameiurus
melas
Moxostoma
aureolum
Toxicity,
Bioassay Active
or Field Field Ingredient,
StudyCl) Location<2) ppm<3)
BSA - 4.35 (T2A)
3.62 (T2A)
5.50 (T2A)
5.30 (T2A)
5.90 (T2A)
8.90 (T2A)
BCFA& - 1.0(0,20%)
BSA
1.0 (NTE)
6.3 (T2A)
24% (O)
BSA - (0)
Experimental
Variables
Controlled
or Noted(4) Comments
a f Variance and the 95 percent confidence interval (C.I.) were
~ also determined.
— Seawater was pumped continuously into test aquaria.
Salinity, temperature, and plankton fluctuated with tide.
and ambient weather conditions. Some bioassays with
fish were static. Toxicity was reported for the following:
Oyster — 96-hr ECgg — Cone, which decreased
shell growth.
Shrimp - 48-hr ECgrj — Cone, which killed or
paralyzed 50% of test animals.
Fish — 48-hr ECgrj - Cone, which killed 50%.
Phytoplankton — Percent decrease of CO2 fixation to a
4-hr exposure at 1.0 ppm chemical
concentration.
a c f I o All sensitive and young stages of fish died in concentrations
of TNT red liquor waste greater than approximately 1 to
600 dilution of average samples as described by Mohlman
(17 to 18 C). Increase in water temperature decreased
survival time of the fish in TNT waste and smaller speci-
mens died sooner than larger.
Reference
(Year)
Willford
(1966)
Butler
(1965)
Oegani
(1943)
I
m
O
X
00
-------
Tordon
Torden
Tordon
101
to Tordon
£ 1°1
Tordon
Tordon
Toxaphene
8
3)
O
O
rn
O
3)
O
O
Toxaphene
Toxaphene
Chaenobryttus
gulosus
Lepomis
cyanellus
Lepomis
macrochirus
Crassostrea
virginica
Penaeus
aztecus
Mugil
cephalus
Phyto plankton
BSA
BCFA&
BSA
43 (T1A)
1.0 (NTE)
1.0 (NTE)
1.0 (NTE)
(O)
a b e
Penaeus
aztecus
Oyster
Mugil
cephalus
(juvenile)
Rainbow
trout
Bluegill
Lepomis
macrochirus
Notemigonus
crysoleucas
Micropterus
salmoides
Carp
Perca
flavescens
Golden
shiners
Carp
G/'/a robusta
elegans
Large mouth
bass
Bluegill
Brown
trout
Bullhead
catfish
BCF
BSA
BSA
FL
FL
FL
Auburn,
Ala.
Beckers
Lake,
Ariz.
Lyman
Reser-
voir,
Ariz.
(O)
(O)
(O)
2.4 (T2A)
13.1 (T2A)
(O)
0.1 (K)
0.1 (K)
a b c g
a beg
This report is a simple and straightforward determination of
a median tolerance limit for a selected group of herbicides.
Seawater was pumped continuously into test aquaria.
Salinity, temperature, and plankton fluctuated with tide,
and ambient weather conditions. Some bioassays with fish
were static. Toxicity was reported for the following:
Oyster — 96-hr €C^Q — Cone, which decreased
shell growth.
Shrimp — 48-hr ECgg — Cone, which killed or
paralyzed 50% of test animals.
Fish - 48-hr EC50 - Cone, which killed 50%.
Phytoplankton — Percent decrease of CO2 fixation to a
4-hr exposure at 1 .0 ppm chemical
concentration.
Toxicant chemicals were evaluated in seawater at tempera-
tures averaging about 28 C. The values are for 24-hr
or enough to cause loss of equilibrium or mortality. No
effect occurred at 1 .0 ppm.
No effect on exposure to the chemical at 1 .0 ppm.
Water temperature was 28 C. No effect was noticed on
exposure to 1 .0 ppm.
Data are given as
0.02 ppm killed bluegills and golden shiners. The bass were
killed at 0.04 ppm. 0.2 ppm in an earthen pond killed
bluegill and bass fingerlings and bait-sized goldfish in
45 hours.
All fish died during an eleven-day period. The lake was
successfully stocked about 8 months later with
rainbow trout.
All fish died during a two-day period. The reservoir was
successfully stocked 10 months later with rainbow trout.
Hughes and
Davis
(1967)
Butler
(1965)
Butler
(1965)
Butler
(1965)
Butler
(1965)
Bohmont
(1967)
Lawrence
(1950)
Hemphill
(1954)
Hemphill
(1954)
I
m
0
X
00
-------
8
m
o Chemical
^ —
*" Toxaphene
O
m
/~i
£
f~
T3
3)
O
§
erf
Toxaphene
Toxaphene
tjC
N»
N>
O
Toxaphene
Toxaphene
Organism
Pimephales
promelas
Tandipedae
Chaoborus spp
Bluegill
Pumpkinseed
Large mouth
bass
Yellow
perch
Rock
bass
Bullhead
Bullhead
Carp
Bottom
fauna
Catostomus
macrochei/us
Ptychocheilus
oregonense
Cyprinus
carpio
Richardsonius
balteatus
Mylochoilm
caurinum
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study d) Location <2) ppm(3) or Noted(4)
BSA - 0.036 (T1 A) acdf
0.020 (T1 A)
0.0057 (T1A)
0.1 (0)
0.060 (T1 A)
0.10 (T1 A)
1.5 (T1A)
9.5 (T1A)
FL Colo. 0.1 (K3) acde
(0)
FL Lakes 0.005 (K) d
(Mich.)
BSA - <0.001 (T1A) a
F Iowa 0.005 (O)
0.005 (O)
-
FL Spectacle 0.07 (O) acd
Lake,
British 0.07 (O)
Columbia
0.07 (0)
0.07 (0)
0.07 (O)
Comments
At 50 F and 6 ppm methyl orange alkalinity.
At 50 F and 212 ppm methyl orange alkalinity.
At 75 F and 212 ppm methyl orange alkalinity.
At 212 ppm methyl orange alkalinity, 75 F, no aeration.
6.4-7.0 ppm dissolved C>2 and with light, 100% mortality
occurred in 2 days. Toxicant was added immediately
before fish.
At 55 F and 212 ppm methyl orange alkalinity.
At 55 F and 212 ppm methyl orange alkalinity.
At 55 F and 212 ppm methyl orange alkalinity.
At 55 F and 212 ppm methyl orange alkalinity.
The chemical becomes detoxified when left standing in water
by removal by microorganisms. The chemical is more toxic
to fish in hard water than in soft water.
0.05 ppm emulsified toxaphene is sufficient for fish eradica-
tion. Somewhat lower concentrations can be used in
shallow hard water lakes with a higher temperature.
This is a study of lake bottom fauna. Repopulation of lake
was not complete until nine months later.
Toxaphene at the indicated concentration killed the majority
of small fish while larger fish were not killed. According to
the authors, toxaphene at a 5 ppb concentration can be used
to reduce the population of small fish without greatly
affecting the population of large fish.
It was estimated that 25.0 ppb will eradicate an entire fish
population in a lake. A concentration of 20.0 ppb seemed
sufficient to kill all fish in aquarium tests. In highly turbid
water, 200 ppb were required. This suggests that the silt
in suspension has a detoxifying effect.
The field study reports what is believed to be the first in-
stance in which a lake is rid of all fish by chemical means.
Bottom fauna declined in volume due to the treatment
but recovered rapidly (1 mo).
Experiments were conducted in 8 lakes in British Columbia,
all of which were alkaline. These lakes had no permanent
inlet or outlet streams.
Initial results or symptoms were observed in 120 hr. All
caged fish were dead except 2 carp which managed to
survive for 1 to 2 months.
Reference
(Year)
Hooper and
Grzenda
(1955)
Cushing and
Olive
(1957)
Fukano and
Hooper
(1958)
Rose
(1958)
Stringer and
McMynn
(1958)
-------
Toxaphene
Toxaphene
to
Is)
3,
!JJ Toxaphene
O
O
O
Catostomus
macrocheilus
Ptychocheilus
oregonense
Cyprinus
carp/o
Richardson/us
balteatus
Perca
flavescens
Mylocheilus
caurinum
Couesius
plumbeus
Coregonus
williamsoni
Oncorhynhus
nerka
Sal mo
gairdneri
Lottus
asper
Catostomus
macrocheilus
Ptychocheilus
oregonense
Ftichardsonius
balteatus
Perca
flavescens
Mylocheilus
caurinum
Couesius
plumbeus
Coregonus
williamsoni
Oncorhynhus
nerka
Salmo
gairdneri
Catostomus
macrocheilus
Cyprinus
carpio
Ftichardsonius
balteatus
Mylocheilus
caurinum
Salmo
gairdneri
FL
Lady King
Lake,
British
Columbia
a c d
FL
FL
0.10 (K2)
0.10 (K2)
0.10 (K2)
Gallagher
Lake,
British
Columbia
Gladstone
Lake,
British
Columbia
0.10 (K2)
0.10(K2)
0.07 (K2)
0.07 (K2)
0.07 (K2)
0.07 (K2)
0.07 (K2)
0.07 (K2)
0.07 (K2)
0.07 (K2)
0.07 (K2)
0.03 (O)
0.03 (0)
0.03 (0)
0.03 (0)
0.03 (O)
Experiments were conducted in 8 lakes in British Columbia,
all of which were alkaline. These lakes had no permanent
inlet or outlet streams.
There was no sign of fish life after 24 hr.
Stringer and
McMynn
(1958)
a c d
Experiments were conducted in 8 lakes in British Columbia,
all of which were alkaline. These lakes had no permanent
inlet or outlet streams.
Stringer and
McMynn
(1958)
T)
m
O
X
03
a cd
Experiments were conducted in 8 lakes in British Columbia,
all of which were alkaline. These lakes had po permanent
inlet or outlet streams.
In 12 hours many trout and shiners were dead; all other
fish showed signs of distress.
Stringer and
McMynn
(1958)
-------
8
m
o Chemical
r~ Toxaphene
O
X
m
S
g
r
TJ
O
O
C
Toxaphene
Toxaphene
M Toxaphene
T
N)
N>
(O
Toxaphene
Organism
Catostomus
macrocheilus
Ptychocheilus
oregonense
Cyprinus
carpio
Richardsonius
balteatus
Mylocheilus
caurinum
Salmo
gairdneri
Catostomus
macrocheilus
Salmo
gairdneri
Cyprinus
carpio
Catostomus
macrocheilus
Ptychocheilus
oregonense
Cyprinus
carpio
Richardsonius
balteatus
Mylocheilus
caurinum
Salmo
gairdneri
Fathead
minnow
Bioassay
or Field Field
Study (1) Location<2)
FL Taylor
Lake,
British
Columbia
FL Alleyne
Lake,
British
Columbia
FL Round
Lake,
British
Columbia
FL Summit
Lake,
British
Columbia
BSA
Toxicity, Experimental
Active Variables
Ingredient, Controlled
ppm<3) or Noted W
0.01 (K.4) acd
0.01 (K.4)
0.01 (K4)
0.01 (O)
0.01 (K.4)
0.01 (0)
0.01 (O) acd
0.01 (O)
0.03 (K3) acd
0.10(0) acd
0.10 (0)
0.10 (O)
0.10(0)
0.10 (O)
0.10 (O)
0.0051 (T4A) a
Comments
Experiments were conducted in 8 lakes in British Columbia,
all of which were alkaline. These lakes had no permanent
inlet or outlet streams.
Rainbow trout and shiners showed definite signs of distress
in 4 days.
Experiments were conducted in 8 lakes in British Columbia,
all of which were alkaline. These lakes had no permanent
inlet or outlet streams.
In 24-48 hours many fish were dead while others were still
in distress.
Experiments were conducted in 8 lakes in British Columbia,
all of which were alkaline. These lakes had no permanent
inlet or outlet streams.
Experiments were conducted in 8 lakes in British Columbia,
all of which were alkaline. These lakes had no permanent
inlet or outlet streams. Initial results were recorded in
4 hours. Many dead trout and shiners were observed. All
caged fish were dead in 2 days.
It was the authors opinion that pH, alkalinity and hardness.
within the usual range in natural waters, had little effect on
Reference
(Year)
Stringer and
McMynn
(1958)
Stringer and
McMynn
(1958)
Stringer and
McMynn
(1958)
Stringer and
McMynn
(1958)
Tarzwell
(1959)
^
^
•V
rn
Z
O
x
00
Toxaphene
Fathead
minnow
Bluegill
Goldfish
Guppy
BSA
0.0075 (T4A)
0.0035 (T4A)
0.0056 (T4A)
0.020 (T4A)
the toxic effect of the compounds studied. The values
given are from Henderson, Pickering, and Tarzwell, "The
Relative Toxicity of Ten Chlorinated Hydrocarbon Insecti-
cides to Four Species of Fish". It is interesting that the
different tables from the above book (as reported in this
paper) report widely different values for the same compounds.
This experiment was performed in hard water.
Comment same as above except that this experiment was Tarzwell
performed in soft water. (1959)
-------
Toxaphene
Toxaphene
Toxaphene
Toxaphene
(100%)
to
Toxaphene
(tech)
8
2 Toxaphene
3)
O
O
m
2
5
Pimephales
promelas
Lepomis
macrochirus
Channel
catfish
(fingerlings)
Pimephales
promelas
Lepomis
macrochirus
Car ass! us
auratus
Lebistes
reticulatus
Pimephales
promelas
Lepomis
macrochirus
Carassius
auratus
Lebistes
reticulatus
Lepomis
cyanellus
Onchorhynchus
nerka
Notropis sp
Daphnia
pulex
D. magna
Ischnura sp
Enallagma sp
Scenedesmus
incrassatulus
Pimephales
promelas
BSA
BSA
BSA
BSA
BSCH
BSA
0.0075 (T4A)
0.0035 (T4A)
2.5 (K1 A)
0.008 (T4A)
0.004 (T4A)
0.006 (T4A)
0.02 (T4A)
0.0075 (T4A)
0.0035 (T4A)
0.0056 (T4A)
0.020 (T4A)
0.0036 (SC4)
0.0036 (SC4)
0.01 (SC4)
0.03 (SC7)
0.03 (SC5)
0.004 (SC4)
0.004 (SC4)
0.01 (SC384)
0.013 (T4A)
a d e f
abecdf
a e p
a cd f g
Bioassay investigations of the new insecticides indicate that
in general the organic phosphorus compounds are not as
toxic to fish as are the chlorinated hydrocarbons. The
toxicity of most of these materials was not significantly
influenced by water quality. Therefore it is to be expected
that the toxicity of these materials will not differ signifi-
cantly in different streams.
Tap water was used. Considerable additional data are
presented.
Concentrations were based on percent active ingredient.
Dilution water was usually soft although some studies were
conducted with hard water.
Toxicity is reported as the sublethal concentration (SC),
which is defined as that concentration which produced no
greater mortality among test animals than was sustained by
the controls. In fish study, test fish were challenged with
solvent extracts of toxaphene-exposed algae and periphyton.
Fish tested against the algae extract survived, but fish tested
against periphyton extracts died. Various technical grades
of toxaphene were evaluated.
Test water was spring water diluted with distilled water.
Removal of toxic chemicals by carbon adsorption, chlorine
and chlorine dioxide treatment, and alum coagulation was
studied. The most effective method to remove fish poisons
was by use of activated charcoal adsorption.
Tarzwell
(1959)
Clemens and
Sneed
(1959)
Henderson, et al
(1960)
Henderson, et al
(1959)
Cohen, et al
(1961)
3)
O
O
O
-------
8
m
o Chemical
> -
•" Toxaphene
O
m
o
>
r~
"O
3
O
O
Toxaphene
7*
N>
K)
A
Toxaphene
Toxaphene
Toxicity,
Bioassay Active
or Field Field Ingredient,
Organism Study <1> Location'2) ppm'3)
Gizzard FL Fla. (0)
shad
Bluegill
Black
crappie
Large mouth
bass
Brown
bullhead
Shortness
gar
Golden
shiner
Bowfin
Gambusia
affinis
Notropis
maculatus
Fundulus
semin olis
Oncorhynchus BSA — 9.4 (T4A)
kisutch
Oncorhynchus 2.5 (T4A)
tshawytscha
Salmo 8.4 (T4A)
gairdnerii
Gasterosteus 7.8 (T4A)
aculeatus
Entomostraca FL Col. 0.1% (K.)
Cyclops
Diaptomus
Ceriodaphnia
Bosmina
Leptodora
Rotaria
Filinia
Keratella
Polyarthia
Asp/anchna
Brachionus
Protozoa
Ceratium
Difflugia
Salmo BSA - (O)
gairdneri
Experimental
Variables
Controlled
or Noted M Comments
c d A variety of lake types was employed to discern selective
fish-killing properties of Toxaphene. Concentrations
ranging from 1 to 85 ppb were placed in fourteen bodies
of water varying in size from 0.5 to 2100 acres. Differences
in concentrations required to cause total kills of fish popula-
tions in treated lakes appeared to be related to bicarbonate
alkalinities, bottom types, amounts of plankton, vegetation,
and the sizes of fish present.
In 4 of the lakes, a total fish kill occurred at 1 5-36 ppb
Toxaphene.
a c d e Chemical dissolved in acetone. TLm expressed in ppb.
a c d g p All chemical and physical data were collected and compiled
by standard limnologipal techniques. Chemical analyses
were conducted monthly. Biweekly plankton collection
showed "reduction to zero" of all organisms studied, but
recovery of populations to normal population numbers
within several months.
£ c d f g Water employed for this experiment was a relatively hard.
alkaline-type taken from 3 sources: Mormon Reservoir,
Reference
(Year)
Huish
(1961)
Katz
(1961)
/
Hoffman and
Olive
(1961)
Webb
(1961)
Magic Reservoir, and Redfish Lake. The TLm given are
recorded respectively for each reservoir: 0.0136 (T4),
0.0165 (T4), and 0.0145 (T4).
-------
Toxaphene
Toxaphene
Toxaphene
to
K)
8
Toxaphene
(ECS)
Toxaphene
2
m
3
o
> Toxaphene
O
m
5
9
-o
3)
O
O
c
Gammarus
lacustris
lacustris
Protococcus sp
Chlorella sp
Dunaliella
euchlora
Phaeodactylum
tricornutum
Monochrysis
lutheri
Salmo
gairdneri
Ictalurus
me/as
Lepomis
cyanellus
Pimephales
promelas
I. natalis
Micropterus
dolomieui
Catastomus
commersoni
Potamageton spp
Semotilus
a tro macula tus
Gambusia
affinis
Rana
catesbeiana
(tadpoles)
Fish
Carassius
aura tus
Gambusia
affinis
Salmo
gairdnerii
BSA
BSA
FL
Clayton
Lake,
N. M.
FL
Cal.
FL
BSA
Mont.
(O)
0.15 (K)
0.15 (K) 0.07 (NG)
0.15 (K)
0.04 (NG)
0.04 (K)
0.01,0.02,
and 0.02 (O)*
'treatments on
3 alternate
days during
a 6-day period
0.5 (O)
0.13 (O)
0.005-0.066 (O)
0.005-0.059 (O)
0.013-0.054 (O)
a e p The mortality might have been partially due to the suscept- McDonald
ibility of the organism to higher temperatures, toxicity from (1962)
extended exposure to copper electrodes (used to shock the
organism to determine death), or the increase of CO2-
Results were expressed as LTgrj; for example, at 0.5 ppm,
50 percent of the shrimp were killed in 96 (± 11) min.
£ This paper concerns the growth of pure cultures of marine Ukeles
~ plankton in the presence of toxicants. Results were ex- (1962)
pressed as the ratio of optical density of growth in the
presence of toxicants to optical density in the basal
medium with no added toxicants. NG = no growth, but
the organisms were viable.
a c d e f g i o Paper chromatography was the method used to determine Kallman, et i
toxaphene residues in some of the species listed. Mortality (1962)
of native fish and others in live cars was 100%. Residues
in water and sediments were also determined. Residues
were as much as 4.2 ppm in dead trout following first
treatment, and as much as 15.2 ppm in dead or dying bull-
heads several days after the second treatment. Dead trout in
live cars contained up to 3.5 ppm toxaphene up to 8 mos
following initial treatment. Potomogeton spp contained up
to 18.3 ppm, 9 days after the final treatment. Although the
lake was still toxic 9 months after treatment, planting of rain-
bow trout was successful 12 months after treatment.
ac Mixed populations of the indicated test species contained in Mulla
cages were exposed to various insecticidal chemicals applied (1963)
as dilute sprays to ponds 1/16 acre in size. The indicated
toxicant concentration is in Ib/acre, and resulted in a
100 percent mortality for the fish, and a 100 percent mor-
tality for the tadpoles in 24 hr.
a c d e I Ponds were treated with the chemical to eradicate fish. The Wollitz
fish population included largemouth bass, bluegills, black (1963)
crappie, yellow perch, carp, white sucker, and longnose
sucker. Counts were made of various fish at various later
times. The paper contains little quantitative data.
acde Natural water from various sources were used. Chemical Workman and
added as either floating or sinking type formulations. Newhold
Toxicity given as LC$Q in ppm. (1963)
TJ
m
O
X
CD
-------
8
2
2
m
o Chemical
*~ Toxaphene
O
m
5
O
>
1-
T)
^j Toxaphene
O
Toxaphene
Organism
Notemigonus
crysolaucas
Lepomis
macrochirus
L. cyanellus
Gambusia
aff/nis
affinis
-
Bioassay
or Field
Study (1)
BSA
BSA
FR
Toxicity,
Active
Field Ingredient,
Location '2) ppm(3)
(B)30(T1.5)
(A) 1200(T 1.5)
(B) 23 (T 1.5)
(A) 1600(T 1.5)
(B)38(T 1.5)
(A) 1500 (T 1.5)
0.01 to 0.48 (O)
Flint 0.210 (K)
Creek,
Experimental
Variables
Controlled
or Noted<4>
acf
a
—
Comments
Chemical was dissolved in acetone. Final concentration of
acetone was <2 ml/I. Data shows TLm ppb for insecticide-
resistant (A) and insecticide nonresistant (B) strains of the
test fish.
The lower value is for fish that had never been exposed to
the toxicant, and the higher value was obtained with fish
that had been exposed to a sublethal dose in the past.
Apparently such an exposure produces a resistance that
can be retained when they are later placed in clean water.
Conventional treatment in a water purification plant did not
reduce the amount of chemical found In the stream. Data
Reference
(Year)
Ferguson, et al
(1964)
Boyd and
Ferguson
(1964)
Nicholson, et al
(1964)
S)
to
o\
Ala. are given for 4 years 1959-62, with a range of concentrations.
Only the highest value is reported here. Some fish kill is
reported, but species are not identified here. Data are also
reported for all seasons to show variation; the one listed
here is for summer 1960.
Toxaphene Bluegill BSA - 0.0035 (T4A) a Assays were conducted in soft water at 25 C. Decrease in Weiss
brain cholinesterase was measured in fish exposed to the (1964)
toxicant.
Toxaphene Leiostomvs BSFCHA — 0.003 (K) ao Assays were performed in seawater and results are reported Lowe
xanthurus simply as number dead. Concentrations above 0.0032 ppm (1964)
killed all test animals in 24 hr. Fish were also exposed to
0.01 ppb and 0.1 ppb for 5 months, and growth was not
different from those in the wild populations.
Toxaphene Pa/aemonetes BSA — (N) 57.5 acf Test organisms were collected from 2 locations. Twin Bayou Ferguson, et al
kadiakensis (TT/iA) (TB), Sunflower Co., Miss. (Agricultural area) and Noxubee (1965)
(TB) 170.0 National Wildlife Refuge (N), Noxubee Co., Miss, (non-
(TT/aA) agricultural area) and evaluated in laboratory bioassays.
Toxaphene Gambusia BSA - 0.01-0.04 (T3A) £cde Test fish were collected from 8 different locations of the Ferguson
affinis Mississippi River. The 3-day TLm values were made to (1966)
Ictalurus 0.004-0.050 determine if a resistance gradient existed. The data indi-
melas (T3A) cated that there was none.
Toxaphene Rainbow BSA - 5.4 (T4A) a_ These experiments were performed to show the effect of Cope
trout 2.7 (T4A) temperature on the toxicity. (1965)
1.8 (T4A) For the toxicant concentrations listed, the temperatures
were respectively 45, 55, and 65 F. The fish all were
approximately one grain in weight.
Toxicant concentrations for one and 2-day times were
also listed.
-------
Toxaphene
Toxaphene
Toxaphene
CO
K)
8
S
m
O
o
I
m
Toxaphene
Fish
Chironomus
(larvae and
pupae)
Chaoborus
(larvae and
pupae)
Physidae
Crustaceans
Salmo
gairdneri
Campostoma
anomalum
Carassius
auratus
Notemigonus
crysoleucas
Pimephales
notatus
Ictalurus
me/as
Oncorhynchus
garbuscha
O. keta
O. kisutch
Cattus
aleuticus
Salvelinus
ma/mo
Gasterasteus
aculeatus
Salmo
gairdnerii
Oncorhynchus
nerka
Pholis
laeta
Osmeridae
Fish
FL.
Wis.
BSA
FR
Big Kitoi
Creek,
Alaska
0.1 (K)
(O)
(O)
(O)
(0)
0.0084 (T4A)
0.014 (T4A)
0.094 (T4A)
0.0125(T4A)
0.03 (T4A)
0.025 (T4A)
(O)
a cd e f i m p
FL
Brush and
Long
Lakes,
N. D.
(O)
Elimination of fish population was accomplished with
toxaphene at the indicated concentration. This is a popu-
lation succession study over a 3-year period with observa-
tions on change in populations due to various ecological
factors.
Adult fish were employed in this bioassay. In most cases,
concentrations of toxaphene needed to cause 50 percent
mortality decreased as the temperature increased from
53 F to 63 F and to 73 F. Data cited are for 53 F.
The purpose of this experiment was to determine the extent
of predation by sculpins on pink salmon fry, and the effects
of toxaphene on the sculpins and bottom fauna.
Toxaphene applied to the experimental area was estimated
to be an average concentration of 1.5 ppm.
At the above concentration insects were completely eradi-
cated, bottom fauna decreased in numbers and weight,
but some other invertebrate groups were not completely
eliminated.
The organisms listed were organisms mentioned as fauna in
the experimental area.
Growth rates for yellow perch that survived a toxaphene
treatment in Brush and Long Lakes in North Dakota were
calculated. Brush Lake fish exhibited greatly increased
growth rates for two growing seasons following the treat-
ment. Increased growth rates were not evident for Long
Lake fish until the next growing season. The approximate
concentration of toxaphene for reducing the density of
fish populations is believed to be 25 percent of the rate
determined for fish eradication in most N. Dakota waters.
Hilsenhoff
(1965)
Mahdi
(1966)
Meehan and
Sheridan
(1966)
m
z
o
X
CO
Warnick
(1966)
T)
•33
O
o
I
-------
8
m
o Chemical
Toxaphene
I
m
o
r~
3D
O
o
§
en
Toxaphene
Toxaphene
Toxaphene
f
Is}
oo
Toxaphene
Toxaphene
Toxaphene
Organism
Polyanhra
Keratella
Asplanchna
Conochiloides
Brachionus
Trichocera
Daphnia
Bosmina
Ceriodaphnia
Cyclops
Cyanophyta
Lebistes
reticulatus
Carassius
auratus
Simocephalus
serrulatus
Daphnia
pulex
Fish
Salmo
gairdneri
Lepomis
macrochirus
Pteronarcys
californicus
Baetis sp
Daphnia
pulex
Simocephalus
serrulatus
Petromyzon
marinus
(larvae)
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
Study*1) Location<2) ppm(3) or Noted*4)
FL Various — a
lakes or
reservoirs.
N. D.
BSA & Canada 0.001 (T2A) ace
FL ~
BCF - 11.0mg/l -
(T4CF)
0.44-1.8
mg/l (S4)
BSA - 0.019 (SB)
0.01 5 (SB)
F Cal. (0)
BSA - 0.004 (T2A) a
0.004 (T2A)
0.007 (T2A)
0.047 (T2A)
0.01 5 (T2A)
0.019 (T2A)
FL East Bay, (O) ace
Alger
County,
Mich.
BSA - 0.080 (K1 5-20)
Comments
Marked reduction of many plankters followed a treatment
of 90 ppb toxaphene. The most abundant plant-inhabiting
organism and bottom fauna exhibited no marked changes
after this treatment. Populations of Gammarus, Physa, and
Gyraulus remained constant, while Callibaetis, Caenis,
Ischnura, and Tendipes decreased slightly but were again
numerous 1 year after treatment.
A bioassay method is described for determining the rate of
detoxification of lake water after toxaphene treatment
during a 1-year period.
This method was developed to detect sublethal effects by
observing behavioral aberrations. Detailed description of
conditioned avoidance response apparatus is presented.
Concentration reported is for immobilization.
Time for immobilization was 48 hr.
Data cited are for 60 F, but assays were performed at varied
temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
This study was primarily concerned with insecticides found
in fish-eating birds. Limited fish studies were also con-
ducted. Toxaphene was found in trace to 8.0 ppm concen-
trations in whole fish (wet weight).
This paper reports acute toxicity of a number of compounds,
and discusses sub-acute mortality as well. Effects on repro-
duction and behavior are also discussed. Data presented
as ECgo-
The amount of toxicant needed to give a concentration of
100 ppb (0.100 ppm) was applied over the surface of the
lake. Small fish were observed surfacing and dying the day
after treatment was made. Mortality increased daily and
reached a peak on the 3rd and 4th days. The first dead
larval lampreys were seen on the 4th day after treatment.
At the end of 36 days exposure in cages, only 2 of 90
ammocetes were alive.
Reference
(Year)
Needham
(1966)
Royer
(1966)
Warner, et al
(1966)
Sanders and
Cope
(1966)
Keith
(1966)
Cope
(1966)
Gaylord and
Smith
(1966)
•o
m
z
o
03
-------
Toxaphene
Toxaphene
8
o
>
r
o
m
2
Toxaphene
Carassius
auratus
Salmo
gairdnerii
FL
Big Bear
Lake,
Cal.
O.3-0.10 (O)
Salmo
gairdneri
Esox
lucius
Cyprinus
carpio
Notemigonus
crysoleucas
Pimephales
notatus
Catastomus
commersoni
Ictalurus
me/as
Ictalurus
nebulosus
Lepomis
humilis
Lepomis
macrochirus
Pomoxis
annularis
Pomoxis
nigromaculatus
Perca
flavescens
Stizostedion
vitreum
Gambusia
affinis
FL
Various
lakes,
N. D.
0.035 (O)
BSA
(O)
The chemical was sprayed from a plane into the lake to rid
it of goldfish. Small fish began dying in 2 hours, and brown
bullheads were seen to be in distress. At 0.10 ppm, large
goldfish appeared to be in distress. An estimated 95% of
the goldfish, and all the other fish were eliminated. The fat
and flesh of goldfish, brown bullheads, and some trout were
analyzed for the toxicant. In all instances the fat contained
the greatest amount. The paper recommends that toxaphene
not be used as a fish toxicant, because it detoxifies slowly
and is a contaminant for an unknown period of time. Some
trout were killed when stocked but no quantitative data
are given.
Minimum levels of toxaphene lethal to fish in prairie lakes
and reservoirs were determined.
Considering all lakes in general, 0.005 to 0.020 ppm resulted
in incomplete mortality, while 0.025 to 0.035 ppm resulted
in complete mortality. The minimum lethal concentration
for treatment of most North Dakota lakes was 0.025 ppm
of toxaphene.
Johnson
(1966)
Henegar
(1966)
m
z
o
X
00
The effect of combinations of pesticides was studied. In
general, the results reflected the extreme levels of Endrin
and Toxaphene resistance in the resistant population. The
results failed to indicate additive effects wherein the combi-
nation mortality exceeded the sum of the mortalities pro-
duced by the individual insecticides.
Ferguson and
Bingham
(1966)
3D
O
0
-------
COMMERCI/
>*
r
o
i
rn
s
o
>
f
T>
3)
O
O
C
OT
T5
to
w
Chemical
Toxaphene
Toxaphene
Toxaphene
2(2,4,5) TP
(tech)
2,4,5-TP
4(2,4)TP
(tech)
Treflan
Treflan
(EC)
Treflan
Organism
Pimephales
promelas
Leiostomus
xanthurus
Pteronarcys
californica
(naiads)
Pteronarcella
badia
(naiads)
Claasenia
sabu/osa
(naiads)
Rainbow
trout
Bluegill
Rainbow
trout
Bluegill
Bluegill
Pteronarcys sp
(nymphs)
Rainbow
trout
Bluegill
Rainbow
trout
Bluegill
Toxicity, Experimental
Bioassay Active Variables
or Field Field Ingredient, Controlled
StudyCl) Location^) ppm(3) or NotedW)
BSA - 0.05 (K9) ab
0.02 (K21)
0.05 (K6)
0.02 (K11)
BCF - 0.0075 (K1A) a
0.0056 (K1A)
0.0032 (K1 A)
0.001 8 (K2A)
0.0001 (SB 5 mo)
0.00001 (SB 5 mo)
BSA - 0.0023 (T4A) a c d e f
0.003 (T4A)
0.001 3 (T4A)
BSA - 14.8 (T4A) a
9.6 (T4A)
BSA - 1.3IT2A)
0.50 (T2A)
BSA - 8.6 (T4A) a
BSA - 3.0 (T4A) a
BSA - 0.010(T4A) a
0.018 (T4A)
BSA - 0.011 (T2A)
0.020 (T2A)
Comments
At 33 to 39 F a complete kill occurred at concentrations of
0.05 and 0.02 in 9 and 21 days, respectively.
At 56 F a complete kill occurred at concentrations of 0.05
and 0.02 ppm in 6 and 1 1 days, respectively.
Toxaphene will kill fish at near-freezing temperatures at con-
centration as low as 0.02 ppm but the length of time re-
quired for a complete kill is longer than at higher
temperatures.
Experiments were conducted in salt water.
Fish were held in plastic aquaria with a capacity of 25 liters.
During the 5-month exposure period there was no significant
difference in mortality among control and experimental
fish. No symptoms of distress were noted.
The total lengths of the fish at the end of 5 months were
approximately the same for all groups.
After the 5-month test the fish from the experimental and
the control groups were exposed 48 hours to concentra-
tions of 0.0005 to 0.0030 ppm. The fish from the experi-
mental group seemed to be more sensitive. Concentrations
of 0.0020 ppm caused complete kill whereas 0.0005 ppm
did not kill any fish.
• Data reported as (-€50 at 1 5.5 C in 4 days.
This is an estimated LCso value at temperatures from 55
to 75 F.
Data are given as LC5Q.
This is an estimated l-Cso value at temperatures from 55
to 75 F.
Experiments were all conducted at 60 F in 1964. The
values were listed as LCsQ.
This is an estimated LCijo value at temperatures from 55
to 75 F.
Data are given as LCtjg.
Reference
(Year)
Schaumberg,
et al
(1967)
Kaplan and
Overpeck
(1967)
Sanders and
Cope
(1968)
Cope
(1965)
Bohmont
(1967)
Cope
(1965)
Cope
(1965)
Cope
(1965)
Bohmont
(1967)
m
O
X
09
-------
K)
OJ
Trefmid
(WP)
Tri-6
(dust No. 30,
3 percent
BHC)
Trichlorofon
Tricon
(oil spill
eradicator)
Tricon
oil-spill
eradicator
Trifluralin
8
o
m
2
30
O
O
O
Trifluralin
Trifluralin
(tech)
Trifluralin
Rainbow
trout
Bluegill
Penaeus
aztecus
P. setiferus
Pteronarcys
californica
(naiads)
Pteronarcella
bad/a
(naiads)
Claasenia
sabulosa
(naiads)
Roccus
saxatilis
Roccus
saxatilis
Bluegill
Fathead
minnow
Goldfish
Bluegill
Bluegill
Rainbow
trout
Salmo
gairdneri
Lepomis
macrochirus
Pteronarcys
californicus
Daphnia
pulex
Simocephalus
serrulatus
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
0.110 (T4A)
0.345 (T4A)
0.035 (T1 A)
0.40CT1A)
0.035 (T4A)
0.011 (T4A)
0.022 (T4A)
0.001 (O)
0.005 (K 1 hr)
2.0 (K 7min)
(O)
0.0582 (O)
0.0934 (O)
0.585 (O)
8.4 (T4A)*
*ppb
0.068 (T4A)
0.086 (T4A)
0.011 (T2A)
0.019 (T2A)
4.200 (T2A)
0.240 (T2A)
0.450 (T2A)
ab
This is an estimated LC5O value at temperatures from 55
to 75 F.
P. aztecus and P. setiferus ranged in size from 29 to 50 mm
and 11 to 13 mm, respectively. The water was aerated until
the end of the assay.
————— Data reported as LC$Q at 15.5 C in 4 days.
At 0.001 percent, the fish showed signs of distress in
1-1/2 hours. This compound was toxic at low concen-
trations and should not be used to treat oil spills.
This chemical is a commercial product designed to emulsify
oil spilled on water. At 0.0005% concentration all test
fish survived. At 0.001% concentration all fish died within
10 hours. Additional data are presented.
In static soil-water tests, 48 and 227 times more Trifluralin
was required to produce an i-C^Q to bluegills for two
types of soil than was necessary in the static water tests.
In a simulated field test using swimming pools, Trifluralin,
applied at 1 Ib/acre to Brookston soil and then irrigated
with 10 inches of water, was not toxic to bluegills.
On the basis of these studies, it was concluded that LCgg
values derived from static water fish tests are unrealistic
in predicting the toxicity of Trifluralin to fish under
field conditions.
The temperature effect is extreme in the case of this com-
pound. The T4 listed is for a temperature of 85 F. At
45 F the T4 was 280 ppb. The T1 is even more striking.
At 85 F, the value was 10.0 ppb, and at 45 F, 1300 ppb.
This is an estimated LCso value at temperatures from 55
to 75 F.
This paper reports acute toxicity of a number of compounds,
and discusses subacute mortality as well. Effects on re-
production and behavior are also discussed. Data presented
as EC50.
Cope
(1965)
Chin and
Allen
(1957)
Sanders and
Cope
(1968)
Chadwick
(1960)
Chadwick
(1960)
Parka and
Worth
(1965)
I
m
Z
D
X
09
Cope
(1965)
Cope
(1965)
Cope
(1966)
-------
COMMERCI
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to
Chemical
Trifluralin
Trifluralin
Tris-
buffer
Trithion
Trithion
Trolene
Trypaflavine
(acriflavine
neutral)
Trypaflavine
(acriflavine
hydro-
chloride)
TV-1096
Organism
Simocephalus
serrulatus
Daphnia
pulex
Pteronarcys
californica
(naiads)
Homarus
americanus
Gambusia
affinis
Salmo
gairdnerii
(one wk old
sac fry)
(one mo old
feeding fry)
Salmo
gairdneri
Salmo
trutta
Salvelinus
f on final is
Salvelinus
namaycush
Ictalurus
punctatus
Lepomis
macrochirus
Ictalurus
punctatus
Channel
catfish
(fingerlings)
Salmo
gairdnerii
Salvelinus
fontinalis
Salvelinus
namaycush
Bioassay
or Field
Study (1)
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
BSA
Toxicity,
Active
Field Ingredient,
Location (2) ppmJ3)
0.450 (SB)
0.240 (SB)
0.003 (T4A)
2200-4400
(SB10)
0.2 (K 7%)
0.5 (K 0%)
5.0 (K 0%)
0.5 (K 7%)
5.0 (K 93%)
0.74 (T2A)
0.39 (T2A)
0.39 (T2A)
0.62 (T2A)
1.26(T2A)
1.00(T2A)
17.9 (K2)
11.5 (T2A)
11.5 (K1A)
16.1 (T2A)
19.0 (T2A)
16.5 (T2A)
Experimental
Variables
Controlled
or Noted'4) Comments
— Concentration reported is for immobilization.
Time for immobilization was 64 hr.
Data cited are for 78 F, but assays were performed at varied
temperatures.
"Water Chemistry" (unspecified) was "controlled" during
the assay period.
a c d e f Data reported as LCso at 1 5.5 C in 4 days.
ace Tris-buffer concentrations in the range tested were safe for
regulating activity. The lobsters employed weighed
500 grams.
a Chemicals were dissolved in acetone, and tests were run in
triplicate. Toxicity is given as average percent fish killed
in 24 hr.
a c Results are averages of triplicate tests. Toxicity is reported
as percent mortality (K %).
a f Variance and the 95-percent confidence interval (C.I.) were
also determined.
a c f i The experiment was conducted at 66 C.
a Tap water was used. Considerable additional data are
presented.
£f Variance and the 95-percent confidence interval (C.I.) were
also determined.
Reference
(Year)
Sanders and
Cope
(1966)
Sanders and
Cope
(1968)
Stewart and
Cornick
(1964)
Lewallen
(1959)
Lewallen and
Wilder
(1962)
Willford
(1966)
Clemens and
Sneed
(1958)
Clemens and
Sneed
(1959)
Willford
(1966)
^
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-------
to
UC-8305
(EC4)
Union Carbide,
UC 10854
Union Carbide,
UC21149
UC-21427
(EC2)
Urox
Vancide 51
salt
Vancide 512
Vapona
(DDVP)
Ictalurus
punctatus
Lepomis
macrochirus
Gambusia
affinis
Rainbow
trout
Bluegill
Rainbow
trout
Bluegill
Gambusia
affinis
Rana
catesbeiana
Water
lettuce
Pimephales
promelas
Pimephales
promelas
Lepomis
macrochirus
Lebistes
reticulatus
Pimephales
promelas
Lepomis
macrochirus
20.3 (T2A)
28.2 (T2A)
FL Cal. 0.5 (K1)
BSA - 0.180(T4A)
0.110(T4A)
BSA - 0.560 (T4A)
0.050 (T4A)
FL Cal. 0.5 (K1)
(0)
FL Lakes in (O)
Fla.
BSA - 0.83 (T4A)
BSA - 0.35 (T4A)
0.85 (T4A)
0.59 (T4A)
BSA - 4.0 (T4A)
0.27 (T4A)
Veon 100
8 Veon 245
S (2,4,5-T)
m
o
-o
3D
O
o
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Spatterdock
Crassostrea
virginica
Penaeus
aztecus
Leiostomus
xanthurus
Phytoplankton
FL
BCFA&
BSA
Fla.
(O)
1.0 (NTE)
1.0 (NTE)
1.0 (NTE)
1.0 (NTE)
a cd ef
a cd ef
a cd ef
Toxicity value is in Ib/acre.
The values reported are given as
The values reported are given as
Toxicity value is in Ib/acre. No mortality in tadpoles of
Rana catesbeiana occurred during an exposure period
of 1 week.
11.2 to 22.5 Ib/acre controlled water lettuce.
The toxicity of this substance was not influenced by the
quality of the water (pH, hardness, alkalinity).
Comment same as above.
Comment same as above.
At 10.0 Ib/acre, 5 percent control of spatterdock was
obtained.
Seawater was pumped continuously into test aquaria.
Salinity, temperature, and plankton fluctuated with tide,
and ambient weather conditions. Some bioassays with
fish were static. Toxicity was reported for the following:
Oyster - 96-hr EC5Q — Cone, which
decreased with shell growth.
Shrimp — 48-hr ECso — Cone, which killed
or paralyzed 50% of test animals.
Fish - 48-hr ECgrj - Cone, which killed 50%.
Phytoplankton — Percent decrease of CC>2 fixation to a
4-hr exposure at 1.0 ppm chemical
concentration.
Mulla
(1966)
Cope
(1965)
Cope
(1965)
Mulla
(1966)
Phillippy
(1961)
Pickering and
Henderson
(1966)
Pickering and
Henderson
(1966)
Pickering and
Henderson
(1966)
Copeland and
Woods
(1959)
Butler
(1965)
m
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COMMERCE
j>
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£
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Chemical
Veon 245
Vernam
Vernam
Vernam
(tech)
Vernam
Vernam
Versenol
(iron
chelate)
Versene
(acid)
Weedar,
MCP
Weedex
Organism
Leiostomus
xanthurus
(juvenile)
Oyster
Penaeus
aztecus
Crassostrea
virginica
Penaeus
aztecus
Leiostomus
xanthurus
Phytoplankton
Penaeus
aztecus
Bluegill
Leiostomus
xanthurus
(juvenile)
Oyster
Channel
catfish
(fingerlings)
Channel
catfish
(fingerlings)
Lepomis
macrochirus
Gardonus
rutilus
Tinea
tinea
(fry)
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study
-------
Weedex
(Weedazol,
Weedazol
T. L.)
Weptachlor
WL 8008
(isobutyl-
triphenyl-
methylamine)
Zinc
Q dimethyl
2 dithio-
S carbamate
3 (ZDD)
^ Zectran
r
o
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m Zectran
Zectran
Phoxinus
phoxinus
Daphnia
magna
Bui in us
truncatus
Biomorpholaria
alexandrina
Lymnaea
caillaudi
BSA
BSA
(O)
0.052 (SB)
FO
Arabia 0.24-0.25 (O)
w
to
OJ
WL 8008
(n-trityl-
morpholine)
Xylene + 2%
nonionic
emulsifier
Australorbis
glabratus
BSA&
FL
BSA
Puerto
Rico
1)
O
O
Elodea
canadensis
Potamogeton
nodosus
Potamogeton
pectinatus
Pimephales
promelas
Penaeus
aztecus
Cyprinodon
variegatus
(juvenile)
Oyster
Variable
BSA
BSA
BCF
5(0)
100 (O)
5(0)
100(0)
5(0)
100(O)
(0)
0.0068 (O)
(O)
(O)
a c d e The assays were conducted in dual aquaria with aeration.
Toxicity was low after 1 month at normally used concen-
trations, as follows: weedex — 40-80 ppm; weedazol —
15-30 ppm; weedazol — 20-40 ppm.
— Concentration reported is for immobilization.
Time for immobilization was 64 hr.
Data cited are for 78 F, but assays were performed at varied
temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
abg Tests were conducted in the Khurshid canal. Flow of
molluscicide was discharged directly into the canal and
was maintained at a concentration of 0.24 ppm during
the 6 hr of treatment. Formulation 1 killed all adult
organisms but did not affect eggs. Snail density reached
its pretreatment level after 4 months. Formulation 2 was
tested in Ganabiet el Sarania canal. Molluscicide was
applied for 6 hr by motor-operated dispenser to give a con-
centration of 0.25 ppm. Adult organisms were killed
while eggs were unaffected.
c Seven of the tested compounds failed to meet acceptability
criteria — that is, complete kill after 6-hr exposure to
10 ppm. They were not used in field tests. Field tests
showed WL 8008 to be highly effective.
a Experiments were conducted in standing water. Results were
rated on a scale of 0 to 10, 0 standing for no toxic effect
and 10 signifying a complete kill. Evaluation was based on
visual observation of the plant response at weekly intervals
for 4 weeks.
No toxic effect.
Injury rating of 9.3.
No toxic effect.
Injury rating of 7.9.
No toxic effect.
Injury rating of 8.6.
a c d e f Toxicity to 30 species of algae are also presented. ZDD was
algicidal in the range 0.25 to 2.0 ppm.
Toxicant chemicals were evaluated in sea water at tempera-
tures averaging about 28 C. The values are for 24-hr I
or enough to cause loss of equilibrium or mortality.
Water temperature was 12 C. No effect was noticed on
exposure to 1.0 ppm.
No effect on exposure to the chemical at 1.0 ppm.
Vivier and
Nisbet
(1965)
Sanders and
Cope
(1966),
Dawood and
Dazo
(1966)
Seiffer and
Schoof
(1967)
Frank, et al
(1961)
m
Z
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X
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Maloney and
Palmer
(1956)
Butler
(1965)
Butler
(1965)
Butler
(1965)
-------
8
m
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*" Zectran
O
m
S
O Zectran
>
p-
TJ
3)
o
a
§
co Zerlate
Zinc
disodium
verse nate
Zinophos
(EC4)
Zytron
™ Zytron
W
ON
Zytron
Organism
Pteronarcys
californica
(naiads)
Simocephalus
serrulatus
Daphnia
pulex
Channel
catfish
(fingerlings)
Channel
catfish
(fingerlings)
Micropterus
salmoides
Oyster
Leiostomus
xanthurus
(juvenile)
Crassostrea
virginica
Penaeus
aztecus
Leiostomus
xanthurus
Phytoplankton
Toxicity,
Bioassay Active
or Field Field Ingredient,
Study '1' Location'^) ppm(3)
BSA - 0.010 (T4A)
BSA - 0.013 (SB)
0.010 (SB)
BSA - 1.0 (K1A)
BSA - >500(K1A)
BSA - 0.25 (T2A)
0.5 (K2)
1.0 (K1)
BCF - 0.33 (O)
BSA - 0.32 (O)
BCFA & - 0.33 (O)
BSA
0.0003 (O)
0.32 (T2CFA)
59% (O)
Experimental
Variables
Controlled
or Noted (4) Comments
a c d e f Data reported as LC$Q at 15.5 C in 4 days.
— Concentration reported is for immobilization.
Time for immobilization was 48 hr.
Data cited are for 60 F, but assays were performed at varied
temperatures.
Water chemistry (unspecified) was "controlled" during
the assay period.
a Tap water was used. Considerable additional data are
~ presented.
a Comment same as above.
~
a e Experiments were carried out in fiber glass tubs filled with
well water. Fish weights ranged from 2 to 6 pounds.
a The value reported in a 96-hr EC5Q (decreased shell growth).
a Water temperature was 27 C. The figure reported is a
48-hr EC50.
— Seawater was pumped continuously into test aquaria.
Salinity, temperature, and plankton fluctuated with tide.
and ambient weather conditions. Some bioassays with fish
were static. Toxicity was reported for the following:
Oyster — 96-hr EC$Q — Cone, which
decreased shell growth.
Shrimp - 48-hr EC$Q - Cone, which killed
or paralyzed 50% of test animals.
Fish - 48-hr EC^Q - Cone, which killed 50%.
Phytoplankton — Percent decrease of CO2 fixation to a
4-hr exposure at 1 .0 ppm chemical
concentration.
Reference
(Year)
Sanders and
Cope
(1968)
Sanders and
Cope
(1966)
Clemens and
Sneed
(1959)
Clemens and
Sneed
(1959)
Mulla, et al
(1967)
Butler
(1965)
Butler
(1965)
Butler
(1965)
£
^
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X
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-------
APPENDIX C
SPECIES INDEX
FOR
APPENDICES A AND B
-------
APPENDIX C
SPECIES INDEX
FOR
APPENDICES A AND B
Abramis brama - A-9, A-166
Acartia clausi - A-42, A-64, A-84
Accipiter gentilis - B-53, B-55, B-75, B-96, B-142,
B-152
A. nisus - B-55, B-75, B-120, B-142, B-152
Acheilognathous limbata - A-72
Acris crepitans — B-66
A. gryllus B-66
Acroneuria paciflca - B-10, B-l 1, B-23, B-24, B-63,
B-64, B-68, B-70, B-95, B-106, B-107, B-l 10, B-l 11,
B-l 12, B-l 18, B-l 19, B-120, B-136, B-156, B-158,
B-159,B-183,B-184,B-185
Aedes aegypti - B-58, B-64, B-99, B-l83
A. tseniorhynchus — B-l83
Aeroneuria paciflca — B-94
Agrion spp — B-l 97
Algae - A-24, A-43, A-44, B-31, B-37, B-41, B-55, B-122
Alisma spp - A-l 18, B-203
Alloperla spp - B-200
A. pseudoharengus - B-75, B-142, B-l43
Althemanthera philoxeroides - B-16, B-17, B-38, B-44,
B45,B-153,B-205,B-211
Alosa chrysochloris — A-l 58
A. pseudoharengus - B-55, B-79, B-80, B-98
Ambloplites rupestris - A-54, A-87, A-90, A-96, A-l 54,
B-86
Ameiurus spp — B-218
A. nebulosus - A-80, B-43
Ameletus spp - B-200
Ammodytes lanceolatus — B-l 78
Amphipnous cuchia — B-38, B-81
Amphipoda - A-l 26, A-l 44, A-l46, B-74
Anabena spp - A-24, A-48, A-109, A-l 19
A. circinalis — A-47
A. flos-aquae A-73, A-96
Anacystis spp - A-24, A-48, A-109, A-l 19
Anarchis canadensis — A-l 15
Anax spp - B-197
Ancistrodon piscivorus — B-l 23
Anguilla anguilla — A-134
A. rostrata - B-78
Anguillidae - B-74
Anisoptera spp — B-81
Ankistrodesmus spp - A-24, A-48, A-109, A-l 19
Annelida-B-56,B-199
Anodonta grandis - B-l 3, B-78, B-166
Anopheles quadrimaculatus — A-97, B-23, B-49,
B-99, B-l 83
Aphredoderus say anus - B-l 39
Aplodinatusgrunniens - B-55, B-72, B-79, B-80,
B-98, B-142, B-143
Aptenodytes fasten — B-74
Aquatic insects — B-61
Arctopsychegrandis - B-63, B-64, B-70, B-156,
B-159,B-183,B-185
Argia spp — A-l 30, A-l 64
Artemia salina - A-42, A-64, A-84, B-61, B-91,
B-182
Arthropoda - B-74
Arundo donax - B-56, B-79, B-80
Asellus spp — A-l 30
A. aquaticus — B-53
A. communis- A-l 16, A-l30, A-l 64
Asiootus-B-152
Asplanchna spp - B-196, B-224, B-228
Australorbis glabratus - A-l 51, A-l 52, A-l 56, B-6,
B-33, B-132, B-143, B-169, B-216, B-235
Azolla caroliniana - B-102, B-180
Bacteria (see sewage organisms)
Baetis spp - B-71, B-95, B-120, B-141, B-160, B-228
Balanus balanoides - A-41, A-43, A-83, A-l 14, A-163
B. ebemeus — A-41, A-42
Barbus stigma - B-68, B-93, B-l51
B. machecola - B-l 79
Bass - A-44, A-51, A-69, A-76, A-l 13, A-l 15, B-37,
B-52, B-55, B-59, B-122, B-134, B-151, B-160,
B-184,B-195,B-219,B-220
Belostomidae-B-104
Biomorpholaria alexandrina — A-l 4, A-24, A-25,
A-38, A-65, A-66, A-81, A-103, A-108, A-129,
A-137, A-139, A-145, B-169, B-235
Black fish - B-52
Blackfly - B-29, B-30, B-35, B-59, B-192, B-217
Bladderwort-A-117,B-153
Blue crab - B-30, B-61, B-69, B-209
Bluegill - A-35, A-36, A-43, A-48, A-53, A-76, A-113,
A-l 15, A-l 17, A-l 18, B-7, B-9-12, B-27, B-30,
B-31, B-34, B-35, B-37, B-40, B-42, B-49, B-51,
B-52, B-53, B-57, B-59, B-61, B-68, B-70, B-81,
B-84, B-87, B-89, B-90, B-91, B-94, B-99, B-101,
B-107,B-108,B-111,B-112,B-115,B-118,B-121,
B-124, B-128, B-129, B-134, B-136, B-139, B-141,
B-144, B-145, B-147-149, B-151, B-157, B-158,
B-160, B-164, B-165, B-168, B-169, B-181, B-184,
B-185, B-187, B-200-202, B-204, B-206, B-207-210,
B-219, B-220, B-222, B-224, B-226, B-230, B-231,
B-234
C-l
-------
Boleosoma nigrum — A-81
Bosmina - B-196, B-224, B-228
Brachionus spp - B-38, B-196, B-224, B-228
Brachydanio rerio - A-58, A-89, A-105, A-107, A-161,
A-165, B-4, B-33, B-39, B-99, B-131
Brasenia schreberi - B-44
Brevoortia patronus - B-l 19
Buffalo fish - B-l 2, B-l 21, B-l 35
Bufo spp - A-69
B. boreas - B-25, B-l32, B-l 36, B-l68, B-l 84, B-l93
B. valliceps - A-20, A-38, A-40, A-79, A-83, A-84,
A-90,A-114,A-159
Bulinus truncatus - A-14, A-24, A-25, A-38, A-65, A-66,
A-81, A-103, A-108, A-129, A-137, A-139, A-145,
B-169,B-235
Bullaspp- A-71
Bullhead (see catfish)
Buteo buteo - B-53, B-55, B-75, B-96, B-120, B-142,
B-152
Cabomba spp - B-58, B-105
Caddisfly - B-29, B-30, B-35, B-59
Caenidae-B-104
Caenis spp — A-l 16
Calcinus maenas — B-l 78
Callibaetis spp - A-l 16
Callinectes sapidus - B-2, B-l 10
Calliriche spp - A-130
Calothrix spp - A-24, A-48, A-l09, A-l 19
CaUcofish-A-117
Cambarus spp — A-l 54
Campostoma anomalum - A-141, B-4, B-9, B-12, B-16,
B-227
Cancer poguras - B-l78
Carassius auratus - A-l 1, A-l6, A-18, A-20, A-29-32,
A-34, A-38, A-39, A-47, A-49, A-52, A-53, A-55,
A-56, A-58-60, A-62-65, A-67, A-69, A-72-75,
A-77, A-79, A-80, A-87, A-88, A-91, A-93, A-94,
A-96, A-99, A-100, A-107, A-l 10, A-l 18, A-l 34,
A-149, A-151, A-152, A-154, A-155, A-157, A-158,
A-165, B-8, B-13, B-15, B-16, B-18, B-23, B-30,
B-32, B-35, B-36, B-39, B-46, B-42, B-43, B-56-58,
B-59, B-62, B-72, B-76, B-83-85, B-87, B-91, B-92,
B-97, B-105, B-106, B-l 10, B-l 12, B-l 15, B-l 16,
B-124, B-125, B-135, B-136, B-139, B-140, B-143,
B-150,B-153,B-156-158,B-164,B-167-169,
B-175, B-176, B-183, B-184, B-190, B-195, B-198,
B-199, B-210, B-215, B-223, B-225, B-227-229
C. carassius - A-l 2, A-l 3, A-l 5, A-21, A-22, A-25,
A-39, A-43, A-63, A-65, A-80, A-81, A-85, A-96,
A-102, A-107, A-108, A-l 11, A-l 28, A-131, A-138,
A-139, A-148, A-149, B-95
Carp - A-47, B-52. B-121, B-134, B-157, B-160,
B-214,B-219,B-220
Carcinus maenas - A-40, A-l 32, B-19, B-32, B-40,
B-85, B-125, B-134, B-189, B-207
Cardium edule - B-19, B-32, B-40, B-85, B-125,
B-133, B-134, B-178, B-189, B-207
Catfish - A-3, A-41, A-49, A-64, A-66, A-68, A-76,
A-82, A-83, A-98, A-100, A-109, A-l 11-113,
A-l 17, A-142, B-12, B-16, B-18, B-19, B-21,
B-34-36, B-41, B-52, B-62, B-66, B-84, B-92,
B-99, B-121, B-131, B-135, B-138, B-139, B-145,
B-149, B-150, B-155, B-160, B-163, B-169, B-174,
B-186, B-188, B-192, B-195, B-198, B-210, B-213,
B-215, B-217, B-219, B-220, B-223, B-225, B-234,
B-236
Catharcta skua - B-54, B-74
Catostomus commersoni - A-80, A-154, B-9, B-l 7,
B-22, B-85, B-86, B-131, B-159, B-194, B-210,
B-225, B-229
C. macrocheilus - B-220-222
Cattails-B-51
Cattus aleuticus - B-227
Ceratium spp - B-196, B-224
Ceratophyllum spp — A-54
C. demersum — B-l04
Ceriodaphnia spp - B-38, B-196, B-224, B-228
Chaenobryttus coronarius — B-139
C. gulosus-B-21, B-219
Chalmydomonas spp A-l 19
Chama punctatus - B-38, B-81
Channel catfish (see catfish)
Chaoborus spp - A-47, B-49, B-101, B-220, B-227
C. astictopus - B-24, B42, B-83, B-89, B-124,
B-126,B-167,B-193
Chara spp - A-44, A-l 15, A-l 18, B-203
Chelydra serpenti - B-142
Chephia spp - B-8 2
Chironomidae - A-l 16, B-9, B-103, B-104, B-168,
B-173
Chironomus spp — B-227
C. plumosus - B-195
C. riparius - B-53
Chlamydomonas spp - A-25, A-48, A-109, B-58
Chlorella spp - A-24, A-33, A-48, A-53, A-98,
A-109, A-l 19, B-65, B-101, B-107, B-l 10, B-130,
B-149, B-151, B-170, B-173, B-200, B-215, B-225
C. pyrenoidosa - A-18, A-28, A47, A-67, B-2,
B-4, B-13, B-19, B-43, B-128, B-209
C. variegata - A-3, A-6, A-8, A-l7, A-24, A-28,
A-35-37, A-42, A45, A-50, A-54-57, A-60-63,
A-73, A-78, A-83, A-86, A-90, A-92, A-93, A-101,
A-102, A-l 12, A-l 13, A-128, A-129, A-142,
A-143, A-151, A-152, A-l 55, A-l 57, A-162,
A-163, B-7, B-28, B-29, B44, B-60, B-91, B-187,
B-193, B-194, B-209, B-211, B-215, B-216
C. vulgaris - A40
Chlorococcum humicola — A-3 7
Chroococcaceae — B-58
Chrosomus eos — B-12
C-2
-------
Chubs - B-33, B-37, B-55, B-122, 8-195
Cirrhina mrigala - B-82, B-154, B-163, B-179
Claassenia sabulosa - B-34, B-63, B-80, B-98, B-l 10,
B-123, B-142, B-156, B-162, B-186, B-231
Cladocera spp - A-47, B-66, B-105
Cladophora spp - A-l 15, A-l 18, B-56, B-79, B-80,
B-203
C. glomerata - B-13, B-14
C. gracilis - B-78
Clams - B-ll, B-37, B-55, B-122, B-l27
Closterium spp - A-24, A-48, A-109, A-l 19
Clupea harengus — B-l 78
Cnephia spp - B-2, B-14, B-26, B-33, B-75, B-88, B-90,
B-99, B-100, B-110, B-129, B-131, B-133, B-144,
B-149, B-165, B-173, B-176-178
Coccolithus huxleyi — B-80
Coleoptera - B-56, B-59, B-69, B-74, B-76, B-162,
B-l 99
Coenagrionidae — B-l 04
Coesius piumbeus — A-154
Colpidium spp — A-l 16
Coontail-B-113
Copepoda - A-47, B-58, B-66, B-l04
Conochiloides spp — B-228
Corbicula spp — B-49
C. manillemis - B-13, B-73, B-97, B-122, B-142, B-153,
B-165
Coregonusartedii - B-55, B-79, B-80, B-98, B-142, B-143
C. clupeiformis — B-75
C. williamsoni - B-221
Corixidae - B-l04
Corydoras paleatus — A-58
Cottus spp - B-69
Cottus bairdi - B-79, B-98
C. cognatus — A-81
Couesius piumbeus - B-194, B-221
Crabs - B-30, B-61, B-91, B-162, B-166, B-209
Crangon crangon - B-19, B-32, B-40, B-85, B-125, B-134,
B-l 89,8-207
Crappies - A-76, A-l 13, A-l 15, B-52, B-59, B-160
Crassostrea virginica - A-5, B-13, B-15, B-20, B-46, B-47,
B-50, B-51, B-71, B-73, B-76, B-83, B-97, B-103, B-108,
B-122, B-125, B-126, B-130, B-142, B-144, B-146, B-148,
B-153, B-154, B-165, B-170, B-174, B-175, B-181, B-190,
B-201, B-204, B-208, B-212, B-218, B-219, B-233,
B-234, B-236
Crayfish - A-76, B-64, B-66
Cristivomer namaycush — B-86, B-218
Culex spp - A-3, A-l 10, A-l 14, A-120, A-121, A-126,
A-131.A-146
C. apicalis - B-52, B-58, B-87, B-91, B-109
C. pipiens quadrimaculatus — B-27, B-34, B-66, B-158,
B-184
Cyclops spp - B-31, B-38, B-58, B-196, B-224, B-228
Cylindrospermum spp - A-24, A-48, A-109, A-l 19
C. licheniforme - A-3, A-6, A-8, A-17, A-24, A-27,
A-28, A-35, A-36, A-42, A-45, A-50, A-54-57,
A-60-63, A-72, A-73, A-78, A-83, A-86, A-90, A-92,
A-93, A-101, A-102, A-l 12, A-l 13, A-128, A-129,
A-142, A-143, A-151, A-152, A-155, A-157, A-162,
A-163, B-7, B-28, B-29, B-44, B-60, B-91, B-187,
B-193, B-194, B-209, B-211, B-215, B-216
Cynodon dactylon - B-56, B-79, B-80
Cyprinella whippli - B-218
Cyprinids-A-l30,8-77
Cyprinodon spp - B-l57, B-235
C. variegatus - B-25, B-26, B-30, B-42, B46, B-50, B-61,
B-69,8-71, B-78, B-87-89, B-l 11, B-l 19, 8-126,
8-135,8-137, 8-161, B-178,8-186, B-208, B-209,
8-217,6-218
Cyprinus carpio - A-59, A-69, A-72, A-80, A-134, A-158,
B-5, B-l 7, B-21,8-22, B43,8-72,8-82, B-99,8-112,
B-115, B-116, B-127,8-133,8-152, B-154, B-163,8-175,
B-179, B-190, B-197, B-218, B-220-222, B-229
Cypris spp — 8-38
Danio spp — B-154
Daphnia spp - A-54, A-57, B-38, B-58, B-228
D. carinata - 8-12,8-72, B-88, B-96, 8-101,8-121,8-127,
8-141,8-161
D. magna - A-2-4, A-7, A-8, A-l 1-16, A-20, A-22, A-23,
A-29, A-36, A-38-40, A-50, A-52, A-53, A-63, A-65,
A-66, A-68, A-70-73, A-75-81, A-83-85, A-90-92,
A-95, A-97, A-99, A-100, A-103, A-106-111, A-l 12,
A-l 14-116, A-l 18-129, A-131-141, A-143-150,
A-155-157,A-161,A-164,B-8,B-11,B-14-16,B-41,
B-47, B-54, B-56, B-63, B-70, B-72, B-87, B-90, B-93,
B-95, B-96,8-101, B-104, B-108,8-114,8-115,8-119,
B-121, B-123, B-127,8-128, 8-134, B-140, B-153-155,
8-158,8-159, 8-161, B-164, B-165, B-169, 8-170, B-173,
8-176, B-181, B-182,8-185, 8-188, B-191, B-204, B-223,
B-235, B-236
D. pulex - A-29, A-50, A-l 18, A-149, B-12, B-14, B-19,
8-27,8-34, B-37, B-48, B-51, B-5 3,6-71, B-72,8-81,
B-82, B-88, B-90, B-96, B-105, B-108,8-120, B-121,
B-127-129,6-141, B-145,8-147, B-152, B-161, B-165,
B-181, B-185, 8-187, B-188, B-191, B-197, B-200,8-201,
B-204, B-223, B-228, B-231, B-232
Decapoda — B-74
Delphinus delphis - B-178
Diatoms-A-163,B-58
Diaptomus spp - B-38,8-196, B-224
Difflugia spp - B-196, B-224
Dinoflagellata - B-58
Diptera - B-56, B-59, B-69, B-73, B-74, B-76,8-148,
B-162,8-199
Dorosoma cepedianum - A-158,8-16,8-119,6-139
D. peteneme - A-158
Dressenia spp — A-l 30
Drum-6-134
C-3
-------
Dugesia spp - A-l 12, A-l 26
DunalielJaspp-E-215
D. euchlora - A-33, A-53, A-98, B-65, B-101,
B-107, B-l 10, B-130, B-149, B-151, B-170, B-173,
B-200, B-225
Dytiscidae-B-104
Dytiscus spp- B-81
Echinodermata — B-74
Eel-B-162, B-166,B-194
Eichomia crassipes — B-43, B-44
Eleocharis achcularis - B-202
Eleotridae - B-74
Elliptis crassidens - B-48, B-49
Elmidae - B-74
Elminus modestus — A-42, A-64, A-84
Elodea spp - A-54, B-58
E. canadensis - A-5, A-110, A-153, B-102, B-104,B-113
E. canadensis - B-l89
Flops saurus - B-l98
Enallagma spp - B-223
Enneacanthus gloriosus — B-l 59
E. chaetodon - B-l 59
Entosphenus lamottenii — B-86
Ephemerella spp — B-200
E. grandis - B-10, 8-24, B-70, B-95, B-107, B-l 12, B-l 19,
B-136,B-159,B-185
Ephemeroptera - A-47, B-9, B-56, B-59, B-61, B-64,
B-65, B-69, B-73, B-74, B-76, B-162, B-199, B-200
Ericymba buccata - A-141, B-4, B-9, B-12, B-218
Erimyzon sucetta - B-16, B-20, B-48, B-49, B-51, B-90,
B-106, B-109, B-l 14, B-l 29, B-131, B-171,
B-205-207
E. oblongus- B-l59
Eriocaulon spp — A-44
Erisymba buccata - B-l39
Erpobdella punctata - A-130
Eucalia inconstans - B-86
Escherichia coli - A-l 32
Esomus danrica - B-81
Esox americanus — B-l 23, B-l 39
E. lucius - A-84, B-16, B-55, B-72, B-77, B-98, B-105,
B-153, B-171, B-229
E. niger- 8-78,8-159
Etheostoma blennoides - B-12
E. caeruleum - B-9, B-l 2
E. exile- B-l7
E. flabellare - B-12
E.gracile- B-l39
E. nigrum — B-12
E. zonale - B-9
Eucalia inconstans - B-l7, B-72, B-85
Euglena spp — B-58
Eupomotis gibbosus - B-43
Eurhynchium ruscifonne - B-l3
Falco tinnunculus - B-53, B-55, B-75, B-96, B-120,
B-142,6-152
F. peregrinus - B-55, B-75, B-96, B-121, B-143, B-152
FaU fish - B-33, B-57
Filinia spp - B-196, B-224
Fish - A-12, A-27, A49, A-52, A-70-72, A-101,
A-163, B-70, B-75, B-91, B-168, B-196, B-206, B-214
Fundulus spp — B-l 57
F. chrysotus - B-27, B-l39
F. diaphanus- B-l 59
F. heteroclitus - A-l59, B-78
F. notatus- A-l41, B-l 2
F. ocellaris - B-l 55
F. seminalis - 8-46, B-47, B-l 18, B-224
F. similis - A-5, A-103, B-50, B-51, B-69, B-86, B-99,
B-l 19, B-122, B-148, B-154, B-180, B-181, B-202,
B-208, B-218
Gadus merlangus — B-l 78
G. morrhua- B-l 78
Galaxiidae — B-74
Gambusia spp — B-l 57
G. affinis - A-2-4, A-7-12, A-14-18, A-20, A-22-25,
A-27, A-46, A-49, A-50, A-52, A-56, A-65-67, A-69,
A-70, A-79-82, A-89, A-92, A-97, A-102, A-103, A-105,
A-106, A-108, A-109, A-l 11, A-l 14, A-120, A-122,
A-124,A-126,A-130,A-132,A-135-138,A-140, A-141,
A-143-150, A-152, B-2, B-5, B-6, B-9, B-10, B-22-27,
B-32, B-34, B-37, B-52, B-53, B-58, B-62, B-64, B-67,
B-70, B-71, B-83, B-87, B-88, B-91, B-99, B-109, B-l 10,
8-112,6-117,8-119,6-120,6-129,6-131-133,6-135,
8-136, 8-139, 6-140, 8-143,6-145, 8-146,6-151,8-155,
8-156, B-165,8-168, 8-169, 8-173, 6-176-179,
B-182-184, 6-187, 8-193, 6-198,6-199, 8-214,8-217,
B-218, B-224-226, 6-229,6-232, B-233
Gammarus spp - B-54, B-55, B-79, 8-98, B-122
G. lacustris - A-47, 6-8, B-10, B-l 1, B-18, 8-23, 8-24,
8-37, 8-68, B-70, B-93, 8-94, B-107,8-111, 8-112,
8-117-119, B-136, B-140, 8-150, B-158, B-159, B-184,
6-185,6-189,8-196,6-224
G. pulex- A-134
Gar-8-134, B-224
Gardonus rutilus - B-234
Gasterosteus aculeatus - A-l, A-12, A-16, A-22, A-25,
A-27, A-37-39, A-40, A-42, A-79, A-81, A-83, A-92,
A-95, A-108, A-l 14, A-134, A-138, A-146, A-149,
A-159, A-164, 8-8, 8-36, 6-41, 6-64, 8-78, 8-93,6-116,
B-l 17, B-135, 6-140, 6-150, 6-156, 8-164, 8-199, B-224
Gastropoda — 8-74
Gastrotrica spp — 8-38
Gerridae - 8-104
Gilarobusta - 8-219
Gleocapsa spp - A-6, A-27, A-63, A-86, A-l 55
Gleotrichia echinulata - A-47
Gnathepogon gracilis - A-12
Gobiogobio - A-10, A-166, A-167
C-4
-------
Goldfish - A-7, A-17, A-24, A-66, A-97, A-125, A-136,
A-138, B-7, B-30, B-35, B-52, B-58, B-61, B-76, B-87,
3-91,8-109,6-115,6-139,6-149,8-157,6-164,
B-222,8-231
Gomphonema spp - A-25, A-48, A-54, A-109, A-l 19
G. parvulum - A-3, A-6, A-8, A-17, A-24, A-27, A-28,
A-35, A^36, A42, A-45, A-50, A-55-57, A-60-63,
A-73, A-78, A-83, A-86, A-90, A-92, A-93, A-101,
A-102, A-l 12, A-l 13, A-128, A-129, A-142, A-143,
A-151, A-152, A-155, A-157, A-162, A-163, 6-7,
B-28,6-29,6-44,6-60,8-91,6-187,8-193, 6-194,
6-209,8-211,8-215,6-216
Guppies - 6-7,6-30, B-35, B-61, B-91, 6-109, 6-115,
B-139,8-144,6-145, 8-149,6-164, 6-189, 6-192,
B-222
Gyraulus circumstriatus - A-46, A-l 30
Haematopus ostralegus - 8-54,8-96,8-121
Haliphidae - 8-104
Halichoerus grypus - B-178
Hebridae - 8-104
Heleidae spp - 6-49
Helioperca incisor - 6-218
Helisoma campanulata - A-130, A-165
Helix pomatia - A-48
Heloscidium spp — A-130
Hemigrammus crythrozonus - A-58
Heptagenia spp - 8-200
Heteropneustes fossilis - 8-31,6-38,6-93,6-151
Hexagenia spp - B-42, B-49, 8-112, 8-160
Hitch - B-52
Homarus americanus - A-l35, B-232
H. vulgaria- B-178
Hurmomya mutabilis - A-87
Huro salmoides - A-54, A-87, A-90, A-96, 6-56,6-63,
B-86
Hyalella azteca - 8-129
H. knickerbockeri - A-l 16
Hybopsis bigutta - 8-9
Hyborhynchus notatus - A-35, A-53, A-87, A-90, A-96,
A-97,6-41, 6-57,6-86, 8-218
Hydra spp - B-217
Hydracarina spp - A-l 16, B-58
Hydrodictyon spp - A-l 15, A-l 17,6-203, 8-206
Hydrophilus spp - 8-81
Hydropsyche spp - A-98, A-106, A-107, A-130,8-42,
6-112,6-160
H. californica - 6-64,8-70,8-159, 8-183, 6-185
H. stenonema - A-100
Hydropsychidae - A-145
Hypentelium nigricans - 6-9. N-12
Hypognathus nuchalis - 6-12
Ictalurus melas - A-59, A-69, A-154, 8-5,8-10, B-17,
B-19, B-22,6-70, 8-72, 6-94, 8-116, 6-119, 8-120,
6-122, B-137, 8-138, 6-154, 8-161, 8-163, 8-179,
8-185,8-186, 6-214, 6-225-227,8-229
C-5
/. natalis - A-134,6-3,6-17,8-120, 6-214, 6-216,
6-225
/. nebulosus - A-21, A-74, A-154, A-161,8-18,6-22,
8-43, 8-108,8-175, B-191, B-229
/. punctatus - A-3, A-68, A-71, A-82, A-92, A-101, A-l 11,
A-l 12, A-156,8-6,8-7, B-16, B-17,6-19,6-22,8-32,
8-42,6-69,8-71,6-72,8-85,8-95,8-102, B-103, B-l 14,
B-120,8-121, B-125,8-137, B-160, 8-163,8-166,
8-172,8-180,8-188,8-189,6-191,6-192,6-197,
8-201,6-206,6-213, B-218, B-232,6-233
Ictiobus cyprinellus - B-17, B-22,8-137
Infusoria spp — B-58
Ischnura spp - B-223
/. verticalis — A-l 16
Isonychia bicolor - 8-3
Jordanella florida — 8-4
Juncus spp - A-44,8-205
Justica americana — 8-105
/. repens - 8-105
Keratella spp - 8-196, B-224,6-228
Labea synodontis - 8-60
Labeo flmbriatus - 8-81, B-154,6-163,6-179
I. roMto-8-38,8-81
Lagodon rhomboides - A-2, A-5, A-6, A-52-54, A-70,
A-78, A-l 53
Lamprey - B-216,6-217
Lampsilis siliquoidae -8-13, 8-78,8-166
L. ventricosa - B-l 3, B-78,8-166
Larus ridibundus - B-54, 6-95, 8-121
Leander squilla - A-40, A-l32
Lebistes spp — 8-41
L. reticulatus - A-4, A-6, A-16, A-17, A-20, A-21, A-29,
A-34, A-38, A-40, A-47, A-49, A-51, A-52, A-63, A-64,
A-72, A-77-80, A-82, A-84, A-87, A-90, A-91, A-95,
A-99, A-107, A-l 14, A-142, A-149, A-152, A-157,
A-159, A-164, A-165,8-2,6-5,6-8,8-24,8-30, B-32,
B-36, 8-40,842,6-59, B-62, B-65, 6-83, 6-92,6-97,
6-106, B-l 11, B-l 12, B-l 15-117,8-124, 8-126, B-129,
B-136, B-139,6-140,8-150,6-157,6-164,6-167,
8-176, 8-183, B-198,8-210, B-215,8-217, B-223,
B-228,8-233
Leersia spp — 8-205
Leiostomasxanthurus - 6-5,8-6,8-15, 6-20,8-25, 8-30,
6-35,8-46, B-61, B-83, B-89, B-l 10,8-118, B-l 19,
6-122,6-126, 8-130, B-137, B-144,8-146,8-161,
8-173-175, B-178, 6-186,8-189, 8-190, B-193, B-199,
6-201,8-202,8-204,8-208,8-209,8-212,8-214,8-218,
B-226,8-230,8-233,6-234,8-236
Lemna spp — 8-203
Lemna minor - 6-102, B-180
L. trisulca - A-130
Lepisosteus osseus - A-134, A-l 58
L. steinii - A-37
Lepomis spp - A-l 17, 6-126
L. auritus - A-51, A-78,8-159
-------
L. cyanellus - A-15, A-59, A-69, A-133, A-134, B-10,
B-12, B-15, B-17, B-20, B-22, B-41, B-48, B-49, B-68,
B-70, B-72, B-91, B-94, B-l 10, B-l 14, B-l 18-120,
B-131, B-137, B-141, B-171, B-191, B-198,
B-205-207, B-212, B-213, B-219, B-223, B-225,
B-226
L. gibbosus - A-80, A-154, B-3, B-4, B-17, B-72, B-85,
B-86, B-93, B-l 16, B-137, B-138, B-l 54, B-161,
B-163,B-179,B-185,B-186
L. humilis- A-l41,8-229
L. macrochirus - A-2-9, A-l 1-13, A-15-17, A-19-21,
A-23-26, A-29, A-34, A-37-39, A-41, A-43, A-46-49,
A-52, A-57, A-59, A-64, A-69, A-70-72, A-78, A-79,
A-82, A-83, A-88, A-89, A-91, A-92, A-95, A-98-100,
A-102-106,A-108-110,A-112,A-114,A-117-121,
A-125, A-126, A-129, A-131, A-134,A-136-141,
A-143, A-146, A-148, A-149, A-152, A-156, A-158,
A-160-162,A-165,A-166, B-2-6, B-8-11, B-15-17,
B-20-24, B-27, B-30-33, B-35, B-36, B-39, B-40,
B-42, B-44-52, B-56, B-59, B-62, B-67-69, B-71,
B-72, B-76, B-83-85, B-88-95, B-97, B-102-106,
B-108,B-109,B-111-118,B-120, B-123-126,
B-128-131, B-135, B-136, B-139-144, B-146, B-149,
B-150, B-152, B-154-156, B-158, B-160, B-163,
B-164, B-166, B-168-171, B-l 74-176, B-180,
B-182-184, B-186, B-188, B-189, B-191, B-192,
B-197-199, B-201-207, B-210-219, B-223, B-226,
B-228.B-231-234
L. megalotis - B-17, B-72, B-l 39
L. microlophus - B-27, B-145, B-l 59, B-174, B-214
L. symmetricus — B-l 39
Leptodora spp - B-l96, B-224
Leptonychotes weddelli - B-54, B-74
Leucichthys spp — B-75
Libellula spp - A-l 16
Limnaea palustris - A-21, A-39, A-83, A-91, A-106,
A-109
Limnephilus rhombicus - B-54, B-79, B-98, B-l 22
Limnodrilus spp - B-31, B-73, B-96, B-161, B-186,
B-200
L. hoffmeisteri - A-46, A-l 30, A-l 64
Lobodon carcinophagus - B-54, B-71
Lota lota - B-55, B-79, B-80, B-98, B-142
Lottusasper - B-221
Lymnaea spp - A-l 2, A-23, A-29, A-36, A-44, A-57,
A-59-62, A-81, A-103, A-l 15, A-123, A-125, A-126,
A-131, A-135, A-138-141, A-143, A-146, B-7, B-18,
B-27, B-28, B-91, B-109, B-123, B-163, B-181
L. carillandi - A-24, A-25, A-38, A-108, A-l29, A-137,
A-145,B-169,B-235
Ly thrums umbratilis - B-218
Macrobdella decora - A-44
Macrogiwthus aculeatum - B-81
Maia squinado - A-84
Mayn.v - B-217
Mastigophora spp — B-58
Mastocembelus pancalus — B-81
Mayorella palestinensis — A-51, B-21, B-38
Megaloptera - B-56, B-59, B-74, B-l99
Megastomatobus cybrinella — B-59
Menidia menidia — B-78
Mercenaria mercenaria - B-13, B-73, B-78, B-97, B-122,
B-142, B-153, B-162, B-165, B-166
Mesocyclops obsoletus - A-44
Mesoueliidae — B-l 04
Microcystis spp — A-47
M. aeruginosa - A-3, A-5, A-6, A-8, A-15, A-16, A-24,
A-27, A-28, A-35, A-36, A-42, A45, A47, A-50,
A-52, A-54-57, A-59, A-62-64, A-71-73, A-77,
A-78, A-82, A-83, A-85, A-86, A-89, A-90, A-92, A-93,
A-96, A-100-102, A-104, A-l 10, A-l 12, A-l 13,
A-128, A-129, A-142, A-143, A-151, A-152, A-l55,
A-157, A-162, B-6, B-18, B-19, B-27-29, B-34, B44,
B-60, B-91, B-166, B-167, B-l 87, B-192-194, B-209,
B-211,B-215,B-216
Micropterus dolomieu(i) - A-15, B-20, B-22, B48, B49,
B-51, B-91, B-106, B-l 14, B-138, B-147, B-163, B-186,
B-194, B-205, B-213, B-216, B-225
M. salmoides - A-7, A-24, A-46, A-51, A-66, A-82, A-104,
A-125, A-134, A-136, A-138, B-2, B-12, B-15, B-17,
B-21, B-22, B-31, B-32, B-34, B-35, B-39, B40, B44,
B-52, B-57, B-59, B-72, B-81, B-84, B-85, B-102, B-103,
B-107, B-109, B-l 12-114, B-123, B-124, B-l 27, B-129,
B-130, B-133, B-135, B-137, B-139, B-142, B-143, B-147,
B-154, B-156, B-166, B-170, B-171, B-175, B-180, B-182,
B-183, B-186, B-188, B-190, B-192, B-206, B-214, B-216,
B-219, B-236
Minnows - A-17, A-34, A-35, A-159, B-30, B-33, B-57,
B-61, B-70, B-107, B-l 11,8-115, B-120, B-123, B-139,
B-149, B-155, 8-157, B-159, B-164, B-176,8-179, B-182
Moina macrocopa — 8-115
Mollienesia spp — B-l 57
M. latopinna - A-99, A-123, A-126, A-131, A-146
Mollusca - B-56, B-74
Monochrysis lutherii - A-33, A-53, A-98, B-65, B-l01,
B-107, B-l 10, B-130, B-149, B-l 51, B-170, B-l73,
B-200, B-215, B-225
Moroco steindachnerii — A-7 2
Morone americana - A44, B-195
Moxostoma aureolum - B-218
M. erythrurum - B-9
Mullet -B-162, B-166
Mummichog - B-162, B-166
Mugil cephalus - B-25, B-46, B47, B-89, B-108, B-l 19,
B-125, B-170, B-208, B-209, B-213, B-217-219, B-222
M. curema - B-30, B-61, B-73
Myaarenaria - B-13, B-97, B-122, B-142, B-165
Mylocheilus caurinum - B-220, B-221
Myriophyllum spp - A-54
M. brasilliensen - B44, B-202
C-6
-------
M. exalbescens — B-105
M. heterphyllum - B-44, B-134, B-202
Mystus vittatus - B-38, B-81
Mytilus edulis - A-50, B-178
Myxocephalus scorpius - B-137, B-138, B-154, B-161,
B-163,B-179,B-185,B-186
Ms spp - A-28, A-47, A-130, B-202
Najas flexilis - A-l 15, B-105, B-147 .
N. quadalupensis - B-19, B-38, B-45, B-211
Nandus nandus - B-38, B-81
Nassarius obsoletus — B-78
Matrix erythrogaster — B-123
N. rhombifera - ft-123
Naupluis - ft-12, B-38
Navicula spp - A-25, A-48, A-109, A-l 19
N. seminulum - B-3, B-98
Nemocheilus barbatulus — A-39
Nemertinea — B-74
Nepa spp- B-81
Nereis spp - A-40, A-l 32
N. limnicola - B-197
Neuroptera - B-76, B-162
Nitzchia spp - A-25, A-48, A-109, A-l 19, B-209
N. linearis - A-4, A-13, A-23, A-26, A-43, A-89, A-100,
A-103,A-104,A-108,A-121,A-126,A-131,A-146,
A-161,B-3,B-5
N. palea - A-3, A-6, A-8, A-17, A-24, A-27, A-28, A-35,
A-36, A-42, A-45, A-50, A-54, A-56, A-57, A-62,
A-63, A-73, A-78, A-83, A-86, A-90, A-92, A-93,
A-101, A-102, A-l 12, A-l 13, A-128, A-129, A-142,
A-143, A-151, A-152, A-155, A-157, A-162, B-7,
B-28, B-44, B-60, B-91, B-187, B-193, B-194,
B-211,B-215,B-216
Nodiflorum spp — A-130
Nostoc spp - A-24, A-48, A-109, A-l 19
Notemigonus crysoleucas — A-46, A-69, A-73, A-80,
A-96, A-l 17, B-10, B-16, B-23, B-39, B-40, B-42,
B-43, B-56, B-59, B-68, B-84-87, B-l 10, B-l 18,
B-120, B-122, B-124, B-125, B-135-137, B-139,
B-143, B-156, B-158, B-168, B-175, B-182, B-184,
B-188, B-191, B-216, B-219, B-226, B-227, B-229
Notropis spp - B-223
N. ardens-B-4, B-l 8
N. atherinoides - A-54, A-87, A-90, A-96, B-4, B-5,
B-l 49
N. blennius - B-l 1
N. chrysocephalus - B-9, B-94
N. comutus - A-80, B-5, B-l 1, B-85, B-149
N. heterolepis - B-216
N. hudsonius — A-l 16
A'; lutrensis- B-214
N. maculatus - B-224
N, spilopterus - B-9
N. stramineus ~ B-4, B-9, B-l 8
N. umbratilis - A-141, B-9, B-ll, B-174, B-214
C-7
N. volucellus - B-9
N. whipplii - A-141
Noturus miurus - B-l2
Nymphea spp - A-44, A-l 15, B-44, B-145, B-205
Odonata - B-56, B-59, B-74, B-76, B-104, B-148
Oedogonium spp — A-l 15
Oenanthe fluviatilis - A-130
Oligochaeta - B-49, B-74, B-103, B-168
Onchorhynchus garbuscha - B-227
O. keta - B-227
O. kisutch - A-59, A-71, A-87, A-125, A-136. A-142,
A-146, A-160, B-8, B-19, B-28, B-31, B-33, B-36, B-41,
B-62, B-64, B-73, B-89, B-93, B-107, B-109, B-l 16,
B-l 17, B-135, B-140, B-143, B-147, B-150, B-164,
B-170, B-188, B-191, B-199, B-224, B-227
O. nerka - B-221, B-223, B-227
O. tshawytscha - A-59, A-71, A-87, A-125, A-136, A-146,
B-6, B-8, B-21, B-36, B-64, B-93, B-101, B-l 13, B-l 16,
B-l 17, B-128, B-135, B-140, B-147, B-150, B-156, B-164,
B-176, B-191, B-206, B-213, B-224
Oocystis spp - A-24, A-48, A-109, A-l 19
Ophicephalus punctatus - B-68, B-93, B-151
Opsopoeodus emibiae - B-139
Orconectes rusticus — A-40, B-3
Osio otus - B-55, B-75, B-96, B-121, B-143
Oscillatoria spp - A-24, A-48, A-109, A-l 19, B-56, B-79
Osmeridae - B-227
Ostracoda - A-47, B-66, B-104
Oyster - A-5, B-5, B-6, B-12, B-13, B-15, B-20, B-27,
B-32, B-50, B-55, B-69, B-71, B-76, B-86, B-89, B-91,
B-97, B-98, B-103, B-120, B-122, B-142, B-143, B-146,
B-147, B-153, B-163, B-175, B-187, B-193, B-201,
B-202, B-208-210, B-212, B-234-236
Paleomonetes kadiakensis - B-10, B-94, B-l 19, B-226
P. paludosus - V-2,V-\29
Pandalus montagni - B-32, B40, B-85, B-125, B-133,
B-134, B-189,B-207
Panicum hemitomum — B-15, B-138
Pandorina spp - A-25, A-48, A-109, A-l 19
Paracheinodon innesi - A-5 8
Paralichthys dentatus - B-78
Paramecium spp - A-l 16
Parrot's feather - A-l 17, B-145, B-153
Paspalum spp - B-205
Pastella vulgata - B-178
Peneasaztecus - A-5, B-15, B-20, B-46, B-50, B-54, B-82,
B-83, B-87, B-107, B-126, B-130, B-143, B-144, B-146,
B-154, B-175, B-176, B-180, B-181, B-193, B-201, B-202,
B-204, B-208, B-209, B-212, B-213, B-219, B-231,
B-233-236
P. cardinadus - B-l98
P. duorarum - B-46, B-83, B-189, B-190, B-201, B-202, B-218
P. setiferus- B-83, B-103, B-125, B-170, B-174, B-201,
B-218, B-231
Perca flavescens - A-44, A-59, A-80, A-154, B-17, B-22,
B-72, B-86, B-159, B-195, B-216, B-221, B-229
-------
P. fluviatilis - A-9, A-10, A-166
Perch-B-157,B-160
Percina caprodes - A-154
P. maculata - B-9
Peridinium trochoideum — B-80
Periphyton - A-165
Pescilia latipinna — A-58
Pestia stradiotes - B-18, B-153
Petromyzon marinus - A-19, A-33, A-55, A-65, A-149,
A-153-155, B-101, B-216, B-228
Phaeodactylum tricomutum - A-33, A-53, A-98, B-65,
B-107, B-110, B-130, B-149, B-151, B-170, B-173,
B-200,B-215,8-225
Phalacrococax spp — B-178
Pholis leata - B-227
Phormodinium inundatum — A-47
Phoxinus phoxinus - A-25, A-49, A-79, A-97, A-l 15,
A-134, A-135, A-143, B-13, B-20, B-206, B-235
Phryganea spp - B-197
Physa heterostropha - A-13, A-46, A-51, A-89, A-100,
A-103-105, A-108, A-l30, A-161, A-163, A-l64,
B-3,B-5
Physidae-B-104, B-227
Phytoplankton - see plankton
Pimephales notatus - A-141, B-l 17, B-214, B-227,
B-229
P. promelas - A-4, A-6, A-9, A-l 5-17, A-21, A-22,
A-29, A-34, A-35, A-38, A-41, A-45-47, A-49,
A-52, A-55, A-64, A-66, A-72, A-77-79, A-87,
A-88, A-91, A-95, A-99, A-102, A-l04, A-l 17,
A-134, A-142, A-148, A-149, A-152, A-156,
A-l59, A-l60, A-165, A-166, B-4, B-5, B-8, B-9,
B-17, B-22, B-24, B-30, B-32, B-36,B-39-41, B-43,
B-48-50, B-57, B-59, B-62, B-72, B-81, B-83,
B-86, B-87, B-92, B-95, B-100-103, B-106, B-l 11,
B-l 14-116, B-123, B-124, B-126, B-131, B-l 35,
B-139, B-140, B-143, B-149, B-150, B-155, B-157,
B-162, B-164, B-167, B-169, B-174-176, B-179,
B-180, B-182-184, B-190, B-193, B-195, B-196,
B-198, B-203, B-210, B-215 -217, B-220, B-223,
B-225,B-230,B-233, B-235
Pithophora spp - A-l 17, B-84
Planorbidae-B-104
Plankton - A-5, A-43, A-l 18, B-15, B-20, B-38, B-46,
B-50, B-103, B-108, B-125, B-126, B-129, B-130,
B-144, B-146, B-148, B-154, B-168, B-174, B-175,
B-180, B-196, B-203, B-206, B-212, B-218, B-219,
B-233,B-236
Platalea leucorodia - B-54, B-96
Platyhelminths - A-163
Plecoptera - B-73, B-74, B-76, B-148, B-162, B-199,
B-200
Plectonema spp - A-24, A-48, A-109, A-l 19
Pleurobena cordatum — B-47
Pleuronectes spp — B-178
Pleuronectesplatessa - A-l 10
Poecilia reticulata - A-58, B-95, B-97
Poecilichthys exilis - B-86
Polyarthra spp - B-196, B-222, B-228
Polycelis nigra - A-114, A-120, A-124, A-128, A-131,
A-135-140, A-143, A-147-149
Pomoxis annularis - A-5, A-51, A-78, B-229
P. nigromaculatus - A-54, A-87, A-90, A-96, B-41,
B-59, B-l 16, B-139
Pondweed-B-l 13, B-153
Pontederia spp - A-44, B-126
P. cordata - B-45
Pontoporeria affinis — B-75
Potomogeton spp - A-44, A-l 18, B-202, B-203, B-225
P. crispus- A-l 15, B-l05
P. densus- B-l4
P.foliosus- A-115, B-l05
P. nodosus - A-5, A-110, A-153, B-102, B-189, B-235
P. pectinatus - A-5, A-l 10, A-130, A-153, B-14, B-56,
B-80, B-102, B-105, B-189, B-235
P. pusillus - B-105
P. annularis — B-17
Procambarus clarki - A-87, A-102, A-l 19, B-10, B-21, B-32,
B-66, B-89, B-l 17, B-168, B-187, B-200
P. simulons — B-24
Prosimulum spp - B-2, B-14, B-26, B-75, B-82, B-88, B-90,
B-99, B-100, B-110, B-129, B-131, B-133, B-144, B-149,
B-165, B-175, B-176, B-178
Protococcus spp - A-33, A-53, A-98, B-101, B-107, B-l 10,
B-130, B-149, B-151, B-170, B-173, B-200, B-215, B-225
Pseudemys scripta elegans — B-123
Pseudomones pisicida — B-76
Pseudopleuronectes americanus - B-l 37, B-l38, B-154,
B-161,B-163,B-186
Psidium idahoense — A-45
Pteronarcella badia - B-34, B-80, B-98, B-l 10, B-142,
B-162, B-186,B-230,B-231
Pteronarcys spp - A-55, A-60, A-l 18, B-14, B-25, B-26,
B-51,6-81, B-82, B-87, B-99, B-l 11, B-l26-128, B-144,
B-147, B-151, B-165, B-166, B-181, B-184, B-185, B-187,
B-191, B-197, B-200, B-209
P. californica - A-102, A-l 18, A-l 19, B-2, B-10, B-l 1, B-13,
B-14, B-22-25, B-32, B-34, B-38, B-48, B-50, B-51, B-54,
B-63, B-64, B-68-70, B-80, B-82, B-83, B-86, B-88, B-91,
B-94, B-95, B-98, B-99, B-106-108, B-l 10-112,
B-l 18-120, B-123, B-126, B-128-130, B-136, B-137,
B-141, B-142, B-144, B-152, B-l 56, B-158-160, B-162,
B-169, B-173, B-179, B-181, B-183, B-186-189, B-192,
B-197, B-201, B-204, B-205, B-210, B-228, B-230-232,
B-236
Ptychocheilus oregonensis - A-86, A-87, B-220-222
Pungitius pungitius - B-l94
Puntius javanicus - B-152
P. puckelli - B-5, B-31, B-77, B-122
Pungtungia herzi - A-72
Puntius sophore - B-38, B-81
Pygosciles adeloriae - B-54, B-71
C-8
-------
Pygosteus pungitius - A-31 , A-44, A-63, A-68, A-83,
A-164
Pylodictis olivaris — B-22
Pyramimonas spp — B-80
Rainbow trout - A-10, A-12, A-25, A-27, A-37, A-40,
A-99, B-2, B-10, B-14, B-18, B-22, B-24-26, B-28,
B-30, B-34, B-37, B-49, B-52, B-59, B-66, B-69, B-82,
B-87, B-89, B-90, B-94, B-100, B-l 1 1, B-l 12, B-l 18,
B-127-129, B-141, B-144, B-146, B-151, B-157,
B-169, B-172, B-179, B-181, B-216, B-217, B-219,
B-226, B-230, B-233
Rana spp — A- 16
R. catesbeiana - A-69, B-6, B-9, B-24-26, B-34,
B-37, B-66, B-l 17, B-123, B-127, B-132, B-133,
B-137, B-141, B-146, B-151, B-158, B-173, B-217,
B-225, B-233
R. pipens - A-46, A-69, A-81 , B-23
R. temporaria - A-134, B-93
Ranatia filiformis — B-8 1
Rangia cuneata - B-97, B-122, B-142, B-153, B-165
Ranunculus spp — B-l 05
R. pseudofluitans — B-l 3
Rasbora heteromorpha - A-82, A-99, A-106, A-147,
Rhigophila dearbomi — B-74
Rhinichthys atratulus - A-80, A-104, A-105, B-79
Richardsonius balteatus - B-18, B-l 09, B-l 40, B-l 45,
B-l 56, B-l 88, B-207, B-220-222
Ritarita- B-81
Roccus saxatilis - B-231
Rotifers - A-47, A-54, A-l 17, B-2, B-66, B-129
Rutilus rutilus - A-9, A-10, A-166
Saccharomyces ellipsoides - A- 132
Sagittaria spp - A-l 18
Sagittaria latifolia - B-l 05, B-203
Salmo spp - B-97
S. clarkii - A-71, A-87, A-125, A-136, A-146, B-63,
B-68,B-169
S. gairdneri(i) - A-9-13, A-16, A-18-21, A-28-34,
A-37, A-41, A-42, A-46, A-48, A-49, A-53, A-55,
A-56, A-58-60, A-62, A-63, A-67, A-68, A-74, A-75,
A-80, A-82, A-85, A-86, A-88, A-92-96, A-98,
A-100, A-101, A-104-106, A-l 1 1, A-l 12, A-l 18,
A-128, A-151, A-153-155, A-160, A-163-166, B-5,
B-6, B-8, B-9, B-16, B-17, B-22, B-26, B-32, B-36,
B-39, B-41 , B-42, B-44, B-48, B-52, B-53, B-60,
B-63, B-64, B-66, B-67, B-69, B-71, B-72, B-81,
B-86, B-88-90, B-92, B-95, B-100, B-101, B-103,
B-104, B-108, B-l 11,8-116, B-l 17, B-120, B-125,
B-127, B-128, B-131, B-133, B-135, B-140, B-141,
B-144, B-145, B-150, B-152, B-157-160,
B-163-166, B-169, B-171, B-172, B-174, B-180,
B-187-189, B-191, B-192, B-197, B-199-201,
B-204, B-216, B-218, B-221, B-222, B-224, B-225,
B-227-229,B-231,B-232
S. salar - A-40, A-43, A-47, A-49, A-100, A-158, A-160,
A-165,B-70,B-76,B-79
C-9
S. trutta - A-19, A-33, A-46, A-49, A-68, A-81, A-82,
A-92, A-l 12, A-134, A-153-155, A-165, B-6, B-16,
B-17, B-31, B42, B-57, B-60, B-63, B-65, B-72,
B-84-86, B-125, B-131, B-139, B-163, B-166, B-171,
B-172, B-174, B-188, B-189, B-192, B-197, B-218,
B-232
Salmon - A-5, A43, A-160, B-l5, B-51, B-54, B-60,
B-61, B-63, B-77, B-105, B-108, B-147, B-155, B-157,
B-l 62, B-204
Salvelinus fontinalis - A-46, A-59, A-68, A-82, A-92,
A-l 12, A-154, B-6, B-16, B-22, B-60, B-63, B-79,
B-80, B-84-86, B-98, B-104, B-125, B-131, B-132,
B-163, B-166, B-171, B-172, B-174, B-188, B-189,
B-192, B-194, B-197, B-218, B-227, B-232
S. namaycush - A-59, A-68, A-82, A-92, A-l 12, B-6,
B-16, B-42, B-72, B-125, B-166, B-171, B-172, B-174,
B-189, B-192, B-197, B-232
Sarcocheilichthys variegratus - A-72
Sarcodina — B-5 8
Scardinius erythrophthalmus - A-9
Scenedesmus spp - A-24, A-48, A-109, A-l 19, B-58
S. incrassulatus - B-223
S. obliquus - A-3, A-6, A-8, A-17, A-24, A-27, A-28,
A-35-37, A-42, A-45, A-50, A-54, A-56, A-57, A-62,
A-63, A-73, A-78, A-83, A-86, A-90, A-92, A-93, A-101,
A-102, A-l 12, A-l 13, A-128, A-129, A-142, A-143,
A-151, A-152, A-155, A-157, A-162, B-7, B-28, B-29,
B-44, B-60, B-91, B-187, B-193, B-194, B-211, B-215,
B-216
Scirpus spp — A-44
S. acutus - B-105
S. validus- A-l 15
Scophiopus hammondi - B-132, B-l68
Sea lamprey - A-19, A-30, A-58, A-67, A-68, A-74,
A-75, A-85, A-86
Semotilus atromaculatus - A-3, A-12, A-14, A-17, A-20,
A-52, A-53, A-56, A-57, A-62, A-64, A-70, A-76, A-77,
A-80, A-85, A-88, A-97, A-109, A-l 10, A-136, A-139-141,
A-152, A-154, A-156, B-9, B-32, B-79, B-85, B-98,
B-l 13,6-175, B-225
Sesarma africanum — B-31
Sewage organisms - A-2, A4, A-5, A-8, A-10, A-l8, A-22,
A-32, A-36-39, A45, A46, A49, A-56, A-57, A-61,
A-66, A-68, A-69, A-84, A-85, A-88, A-90, A-92, A-93,
A-95, A-98, A-102, A-104, A-105, A-107, A-l 13,
A-l 14, A-l 16, A-120, A-131-133, A-137, A-139, A-141,
A-150, A-152, A-155, A-157, A-160-162, A-164,
B-185,B-210
Shiners - A-26, A-76, A-97, B-33, B-57, B-l34, B-151,
B-160, B-163
Shrimp - B-78, B-133
Sialis spp - B-55, B-79, B-98, B-122
Simocephalus serrulatus - A-29, A-50, A-l 18, A-149,
B-12, B-14, B-19, B-34, B-37, B48, B-51, B-53, B-71,
B-72, B-81, B-82, B-88-90, B-95, B-96, B-101, B-108,
B-120, B-121, B-127-129, B-141, B-145, B-147, B-152,
B-161, B-165, B-181, B-185, B-187, B-188, B-191, B-197,
B-200, B-201, B-204, B-228, B-231, B-232, B-236
-------
Simulium spp - B-3, B-14, B-27, B-33, B-60, B-75, B-82,
B-88, B-90, B-91, B-99, B-100, B-l 10, B-129, B-131,
B-133, B-149, B-161, B-165, B-173, B-177, B-178,
B-181
Siphlonurus spp — B-l97
Skeletonema costatum - B-80
Snails-A-17, B-91, B-181
Somateria mollissima ~ B-54, B-96, B-l 21
Spartina patens — B-78
Spatterdock - B-14, B-38, B-45, B-l"!8, B-147, B-153,
B-211,B-237
Sphaerium c.f. tenue — A-130
Sphaerodema annulatum — B-81
Spirodela polyrhyza - B-102, B-180
Spirogyra spp — A-116, A-118
Sterna hirundo — B-l 21
S. sandvicensis - B-54, B-96, B-l21
Stenonema spp - A-98, A-106, A-107, A-130, B-3
S. ares - A-145, B-3
S. heterotarsale - A-145, B-3
S. hirundo - B-54
Stigeoclonium spp - A-24, A-48, A-109, A-l 19
Stizostedion vitreum - B-105, B-157, B-171, B-216,
B-229
Strix aluco - B-53, B-54, B-75, B-96, B-120, B-143,
B-152
Stylonichia spp - A-l 16
Suckers - B-62, B-64, B-67, B-77, B-l95
Sula bassana - B-178
Sunfish - A-9, A-21, A-26, A-36, A-52, A-76, A-95,
A-134, B-34, B-37, B-57, B-83, B-128, B-140, B-146,
B-157, B-160, B-216, B-220
Synedra spp — B-58
Synodontis schall — B-60
Tadorna tadorna - B-54, B-96, B-l 21
Tadpoles - A-68, A-76, A-141, B-81
Talifridae- B-l04
Tench — A-47
Tendipes decorus — A-46, A-l 64
T. plumosus - A-45
Tendipidae - B-49, B-149, B-220
Tilapia spp — A-69
T. massambica - B-22, B-82, B-131, B-152, B-l 54,
6-163,6-179,6-198
T. melanopleura - 6-8, B-92, 6-134
Tinea tinea — 6-234
Trachelomonas spp — 6-58
Trematomus bernacchii — 6-74
T. hansoni - B-74
Tribonema spp - A-25, A-48, A-109, A-l 19
Trichogaster fasciatus - B-81, B-93, 6-151
Trichoptera - A-47, B-59, 6-61, 6-64. 6-73, 6-74, 6-76,
6-162,6-199
Trout - A-9, A-26, A-27, A-51, A-53, A-99, A-l04,
A-l 11, A-l 13, A-l 17^-118^-135^-158^-164,
6-52,6-54,6-61, 6-62, B-64, B-65, B-67, B-71, B-77,
6-148,6-163,6-172, 6-181, B-187, B-192, B-195,
8-199-201,6-204, B-206, B-207
Tubifex spp - B-31, B-73, 6-96, 8-161, B-186, B-200
Tubificids - A-80, A-142, A-166
Turbellaria spp - B-74, B-217
Typha angustifolia - 8-105
T. latifolia - 8-16,8-45,8-105
Tyto alba - 8-53, B-54, B-75, B-96, B-120, 8-142,
B-152
Umbra limi-E-85,E-86
Utricularia spp - B-44,8-134, B-202
Vascular plants - B-37, B-54
Vaucheria spp — B-14
Vellidae - 8-104
Venus japonica — A-87
Volvox spp — B-66
Walleye-A-l 13
Warmouth-B-135
Water hyssop-A-l 17
Water lettuce -8-131, 6-233
Water plants- A-17
Whitefish-B-61,B-67
Wolffia columbiana - 8-102, B-180
Wolffiella floridana - B-180
Xiphophorus maculatus — A-58
Yellow perch - B-220
Zaccho platypus - A-72
Zebrafish - A-4
Zooplankton — see plankton
Zygnema spp - A-24, A-48, A-109, A-l 18, A-l 19, B-206
C-10
-------
APPENDIX D
IDENTIFICATION OF COMMERCIAL CHEMICALS
-------
APPENDIX D
Trade Name
2,4D
2,4,5-T
Abate®
ABS
AC 5727
AC 12009
AC 38023
AC 43064
AC 43913
AC 47031
AC 47921 EC4
AC 52160
ACP-M-569
Acriflavine
Acrolein
Acti-dione®
Aerosporin
Aldrin (Octalene®)
Algeeclear
Algibiol
Algimaster
Algimycin
Alticide
Ametryne (Ametryn®)
Aminotriazole
Amitrole (Aminotriazole, Amitrol)
Amitrol T
Amiton
Ammate
Amopyroquin
Antimycin A
Chemical Name or Active Ingredient
2,4-dichlorophenoxyacetic acid
2,4,5-trichlorophenoxyacetic acid
o,o,o',o'-tetramethyl o,o'-thiodi-p-phenylene
phosphorothioate
Alkyl benzene sulfonate
m-isopropylphenyl-N-methylcarbamate
No information available
o,o-dimethyl o,p-(dimethylsulfamoyl) phenyl
phosphorothioate
Cyclic ethylene (diethoxyphosphinothioyl)
dithiomidocarbonate
See Abate
Cyclic ethylene (diethoxyphosphinyl)
dithioimidocarbonate
No information available
No information available
Contains 3-amino-l,2,4-triazole
A mixture of 2,8-diamino-lO-methylacridinium
chloride and 2,8-diaminoacridine
Acrylic aldehyde
See cycloheximide
Polymyxin B
1,2,3,4,10,10-hexachloro-l ,4,4a,5,8,8a-hexahydro-
1,4-endo-exo-5,8-dimethanonaphthalene
No information available
No information available
Alkyl quaternary ammonium bromides, organic
polyamine, amine hydrobromides
No information available
Sodium chlorate
2-ethylamino-4-isopropylamino-6-merthyl-
mercapto-s-triazine
See Amitrole
3-amino-l ,2,4-triazole
3-amino-l ,2,4-triazole-ammonium thiocyanate
mixture
o,o-diethyl 5,2-diethylaminoethyl phosphorothioate
Ammonium sulfamate
No information available
No information available
D-l
-------
Trade Name
Chemical Name or Active Ingredient
Aquaherb
Aqualin
Aquathol®
Aramite®
Atabrine
Atlacide-2,4-D
Atlas 1901
Atlas A
Atlox
Atrazine (Gesaprim®)
Banvel-D®
Baron®
Barthrin
Bayer 73
Bayer 4731
Bayer 9018
Bayer 22408
Bayer 25141
Bayer 25198
Bayer 29492
Bayer 29493 (Baytex® & Fenthion)
Bayer 29952
Bayer 30749
Bayer 34042
Bayer 37289
Bayer 37342
Bayer 37343
Bayer 37344
Bayer 38156
Bayer 38819
Bayer 38920
Bayer 41831
o-dichlorobenzene and aromatic salt
85% acrolein
Disodium salt of endothal (19.2%-H-Pennsalt)
2-(p-tert-butylphenoxy) isopropyl-2'-chloroethyl
sulfite
6-chloro-9{[4-(diethylamino)-l-methylbutyl] amino}
2-methoxyacridine dihydrochloride
Sodium chlorate-2,3-dichloroxyacetic acid
No information available
Sodium arsenate
A series of pesticide emulsifiers
2-chloro-4-ethylamino-6-isopropylamino-s-triazine
See Dicamba
See Erbon
6-chloropiperonyl chrysanthemumate
5,2'-dichloro4'-nitrosalicylanilide
No information available
No information available
o,o-diethyl-o-naphthylamido phosphorothioate
o,o-diethyl-o,p-(methylsulfinyl)phenyl
phosphorothioate
o,o-dimethyl-o-(p-methylsulfinylphenyl)
phosphorothioate
o.o-diethyl o-(4-methylthio-m-tolyl)
phosphorothioate
o,o-dimethyl-o-[4-(methylthio)-m-tolyl]
phosphorothioate
o-ethyl-o-(p-methylthio) phenyl methyl-
phosphonothioate
No information available
o-ethyl o-(4-methylthio-m-tolyl) methyl
phosphoramidothioate
No information available
o,o-dimethyl o-(3,5-dimethyl-4-methyl-thiophenyl)
phosphorothioate
No information available
4-(methylthio)-3,5-xylyl methylcarbamate
o-ethyl-S-p-methylphenyl ethylphosphonodithioate
No information available
6,7,8,9,10,10-hexachloro-l ,5,53,6,9,9a-hexahydro-
3-methyl-6,8-methano-2,4-benzodioxathiepin
o,o-dimethyl-o-4-nitro-m-tolyl) phosphorothioate
D-2
-------
Trade Name
Chemical Name or Active Ingredient
Bayer 44646
Bayer 46676
Bayer 47940
Bayer 52957
Baygon®
Baytex®
Ben Venue #35
Ben Venue #3835
Ben Venue #52
Ben Venue #54
BHC (HCK, Hexyclan)
Bidrin®
Bomyl®
Borate
BP 1002
Buramine
C56
C2059
C8514
Camphene
Captan (Orthocide®)
Carbaryl (Sevin®)
Carbophenothion (Trithion®)
Casoron®
Catechol
Cela S-1942
Cela S-2225
Ceresan
Chemagro 4497
Chem Ban
Chem-Fish Special
Chem Mite
4-dimethylamino-3-tolyl N-methyl-carbamate
o-ethyl-o-2-ethylthio-4-methyl-6-pyrimidyl ethyl-
phosphonothioate
o,o-dimethyl o-(3-chloro-4-cyanophenyl)-
thionophosphate
o,o-diethyl o-5-chlorobenzisoxazolyl-3-phos-
phorothioate
o-isopropoxyphenyl methyl carbamate
See Bayer 29493
No information available
No information available
No information available
No information available
1,2,3,4,5,6-hexachloro-cyclohexane (benzene hexachloride)
3-(dimethoxyphosphinyloxy)-N ,N ,dimethyl-cis-
crotonamide
Dimethyl-l,3-di(carbomethoxy)-l-propen-2yl
phosphate
Boron trioxide
No information available
Crude N-mono-n-butyl urea
Hexachlorocyclopentadiene
n-(3-trifluoro-methylphenyi) n' ^i'-dimethylurea
No information available
2,2-dimethyl-3-methylenenorbornane
n-trichloromethylthio4-cyclohexene-1,2-
dicarboximide
1 -naphthyl-N-methyl-carbamate
S- {[(p-chlorophenyl)thio] methyl}o,o-diethyl
phosphoroditnioate
See Dichlobenil
o-dihydroxybenzene
o,o-dimethyl o-(2,5-dichloro-4-bromophenyl)
thionophosphate
o,o-diethyl o-(2,5-dichloro-4-bromophenyl)
thionophosphate
Ethylmercuric chloride
No information available
See Nabam
Rotenone
Xylene, p-chlorophenol, p-chlorobenzene sulphonate,
and rotenone
D-3
-------
Trade Name
Chemical Name or Active Ingredient
Chem Sen
Chlordane (Octachlor®, Octa-Klor®, Chlordan,
Velsicol 1068®)
Chlorea
Chloretone
ChJorobenzilate
Chlorothion
Chloroxuron (Tenoran®)
Chlorox
CIPC
Cleanosol
CMU
Conco LCP-12
Co-Ral®
Crop Rider
Cryolite
Cube root
Cumate
Cyanamid 12009
Cycloheximide (Actidione®)
Cygon
Dacthal®
Dalapon
DBrDT
ODD
DDE
DDT (Anofex®, Dinocide®, Gesapon®,
Cesarex®, Gesarol®, Guesapon®, Guesarol®,
Gyron®, Ixodex®, Neocid®, Zerdane, DND,
GNB, GNB-A
DDVP (Dichlorvos, Vapona®)
Dead X
Deet (Delphene®, Meta-delphene®)
DEF®
Dekafos®
Delnav®
Delrad
Sodium arsenite
l,23>5,6,7,8,8-octachloro-2,33a,4,7,7a-hexahydro-
4,7 methanoindene
Sodium chlorate, sodium metholate, and
3-(p-chlorophenyl)-l ,1 -dimethylurea)
Trichloro-tert-butyl alcohol
Ethyl 4,4'-dichlorobenzilate
o,o-dimethyl o-(3-chloro4-nitrophenyl)
phosphorothioate
N'-(4-chlorophenoxy) phenyl N,N-dimethylurea
Sodium hypochlorite
Isopropyl N-(3 -chlorophenyl)-carbamate
No information available
See Monuron
No information available
o,o-diethyl o-3-chloro^-methyl-l-oxo-2H-
1-benzopyran-7-yl phosphorothioate
No information available
Sodium aluminofluoride
See Rotenone
50% active copper salt of zimate
No information available
3-[2-(3,5-dimethyl-2-oxycyclohexyl)-2-hydroxyethyl]
glutarimide
See Dimethoate
Dimethyl ester of tetrachloroterephthalic acid
2,2-dichloropropionic acid
1,1 ,l-trichloro-2,2-bis(p-bromophenyl) ethane
See TDE
Dichlorodiphenyl dichloroethylene
a-bis (p-chlorophenyl) B33-tnchloroethane
o,o-dimethyl-o-2,2-dichlorovinyl phosphate
No information available
N^N-diethyl-m-toluamide
S 3 jS-Tributylphosphorotrithioate
3-pentadecylphenol o,o-diethylthionophosphate
See Dioxathion
Dehydroabiethylamine acetate
-------
Trade Name
Demeton (Systox®, Bayer 8173, Isosystov®)
Dermol
Derris
Dexon®
Diazinon (Basudin®)
Dibrom®
Dicamba (Banvel D®, Velsicol)
Dicapthon
Dichlobenil (Casoron®)
Dichlone (Phygon®)
Dichlorvos
Dicofol (Kelthane®)
DIDT
Dieldrin
Difolatan
Dilan
Dimecron
Dimethoate (Fostion MM®, Cygon®, Rogar®)
Dimethrin
Dimetilan®
Dinitrocresol (Sinox®, Elgetal®)
Dioxathion (Delnav®, Navadel®, Hercules 528)
Diphenamid (Dymid®)
Dipterex®
Diquat (Reglone®, FB/2®)
Disulfoton (Di-Systom®, Dithiosystox®,
Frumin Al®, Solvirex®, Frumin G®)
Di-Syston
Dithane D-14®
Diuron (Karmex®, Marmer®)
Chemical Name or Active Ingredient
Mixture of o,o-diethyl o-2-(ethylthio) ethyl phos-
phorothioate and o,o-diethyl S-2 (ethylthio) ethyl
phosphorothioate
No information available
See Rotenone
p-dimethylaminobenzenediazo sodium sulfonate
o,o-diethyl o-(2-isopropyl 4-methyl-6-pyrimidyl)
phosphorothioate
See Naled
3,6-dichloro-o-anisic acid 1
0-(2-chloro-4-nitrophenyl) o,o-dimethyl
phosphorothioate
2,6-dichlorobenzonitrile
2,3-dichloro-l ,4-naphthoquinone
See DDW
4,4'-dichloro-o:-trichloromethylbenzydrol
DDT analogue
l,2,3,4,10,10-hexachloro-6,7-epoxy-l,4,4a,5,6,7,8,
8a-octahydro-l ,4-endo-exo-5,8-dimethanonaphthalene
n-(l ,1,2,2-tetrachloroethylthio)-4-cyclohexene
1,2-dicarboximide
(A mixture of Bulan® [2-nitro-l,l-bis(p-chlorophenyl)
butane] and Prolan® [2-nitro-l,l-bis-
(p-chlorophenyl) propane]
See Phosphamidon
o,o-dimethyl S-(N-methylcarbamoyl-methyl)
phosphorodithioate
2,4-dimethylbenzyl 2,2-dimethyl-3-(2-methyl-
propenyl) cyclopropane carboxylate
2-dimethylcarbamyl-3-methylpyrazolyl-(5)-
dimethylcarb amate
4,6-dinitro-o-cresol
2,3-p-dioxane 5, S-bis-(o,o-diethyl-
phosphorodithioate)
n,n-dimethyl 2,2-diphenylacetamide
See Trichlorofon
1,1 '-ethylene-2,2'-dipyridinium dibromide
o,o-diethyl S-2-(ethylthio) ethyl phosphorodithioate
See Disulfoton
See Nabam
3-(3,4-dichlorophenyl)-l,l-dimethylurea
D-5
-------
Trade Name
Chemical Name or Active Ingredient
Dow K-6882
Dowacide
DPT
Drummer
Dursban®
DVP-iodine
Dylox®
Dymid
EDB
Endosulfan (Thiodan®, Malix®)
Endothall (Endothal®)
Endrin
EPN
Eptam®
Erbon (Baron®)
Essolvene
Esteron 99®
Ethion (Nialate®, Niagaia®)
Exalgae
Fairfield 279
Fairfield OT 60-6
F-98
Fenac
Fenthion
Fenuron TCA (Urab®)
Ferbam (Fermate®)
Flagyl
Folidol®
Folithion®
Forron
Fostion
Furazolidone
Furoxone
o-ethyl o-^AS-trichlorophenyl) methyl
phosphoramidothioate
Sodium 2,2-dichloropropionate
DDT analogue
No information available
o,o-diethyl o-3,5,6-trichloro-2-pyridyl
phosphorothioate
No information available
See Trichlorofon
See diphenamid
1,2-Dibromoethane
6,7,8,9,10)10-hexachloro-l(5,5a)6,9,9a-hexahydro-
6,9-methano-2,3,4-benzodioxathiepin 3-oxide
7oxabicyclo-[2.2.1] -heptane-2,3-dicarboxylic acid
l,2,3,4,10,10-hexachloro-6,7-epoxy-l(4,4a,5,6,7,8>
8a-octahydro-l,4-endo-endo-5,8-dimethano-
naphthalene
o-ethyl o,p-nitrophenyl phenylphosphonothioate
S-ethyl di-N,N-propylthiocarbamate
2-(2,4,5-trichlorophenoxy) ethyl-2,2-dichloro-
propionate
No information available
Propylene glycol butyl ether esters of 2,4-D
o,o,o',o'-tetraethyl-S,S'-methylene bis-
phosphorodithioate
Quaternary ammonium compounds
No information available
No information available
See Acrolein
2,3,6-trichlorophenyl-acetic acid
See Bayer 29493
3-phenyl-l,l-dimethylurea trichloroacetate
See Ferbam
l-(2-hydroxyethyl)-2-methyl-5-nitroimidazole
See Parathion
o,o-dimethyl o-(4-aitro-m-tolyl) phosphorothioate
2,3,5-trichlorophenoxyacetic acid propylene glycol
butyl ether esters
See Dimethoate
3-(5-nitrofurfurylideneamino)-2-oxazolidinone
N-5-nitro-2-furfurylidene-3-amino-2-oxazolidone
D-6
-------
Trade Name
G 27365
G 28029
G 30493
G 30494
Gamlen CW
Gamlen D
Gamlen OSR
Gammexane®
Gamosol Solvent D
Garlon®
GC-3582
GC-3583
GC-3707
GC-4072
GC-9160
GC-9879
GS-12968
GS-13005
Guthion®
Gutoxon
HCK
Kept
Heptachlor (Velsicol® 104)
Hercules 528
Hercules 3895 G
Hercules 7175
Hercules 7531
Hexyclan
Hyamine 1622
Chemical Name or Active Ingredient _
No information available
See Phencapton
o,o-dimethyl S-(3 ,4-dichlorophenylthio) methyl
phosphorodithioate
See Methyl phencapton
No information available
No information available
No information available
See Lindane
No information available
50.8% Dalapon and 7.7% 2{2,4,5-trichlorophenoxy)
propionic acid, propylene glycol butyl esters
1 -(2,5-dichlorophenyl)-2,2-dichlorovinyl diethyl
phosphate
2-chloro-l-(2,5-dichlorophenyl)-vinyl diethyl
phosphate
dimethyl- 1 ,3-di(carbomethoxy)-l -propen-2yl
phosphate
Diethyl- 1 -(2 ,4-dichlorophenyl)-2-chlorovinyl
phosphate
pentacyclo decyl) ethyl levulinate
onyl-(4)-methyl] -dithiophosphate
o,o-dimethyl S [4-oxo-l ,2,3-benzotriazin-3(4H)-
ylmethyl] phosphorodithioate
See Guthion
See BHC
Hexaethyl tetraphosphate
1 ,4,5 ,6 ,7 ,8 ,8-heptachloro-3a,4,7 ,7a-tetrahydro-
4 ,7-endo-methanoindene
See Dioxathion
2,2-bis(ethylthio)-vinyl diethylphosphate
1 -(chloro-2-norbornyl)-3 ,3-dimethylurea
No information available
See BHC
p-diisobutyl phenoxy ethoxy dimethyl benzyl
ammonium chloride
D-7
-------
Trade Name
Chemical Name or Active Ingredient
Hyamine 2389
Hydram®
Hydrothal
Ibcol
Imidan®
Inverton®
lodophor
IPC
Isobenzan (SD4402)
Isodrin
Isolan
Isotex
K6882
Karmex®
Kelthane®
Kepone®
Korlan®
Kuramine
Kurosal
Kurosal G
Kurosal SL
Kuron®
Kyro-Eo
Lethane 384
Lexeme
Lignasan
Lindane (Gammexane®]
M-502
M-1499
M-1500
M-1845
Malaoxon
40% Methyl dodecyl benzyl trimethyl ammonium
chloride and 10% methyl xylene bis-trimethyl
ammonium chloride
See Molinate
Potassium salt of 2,2,4,5 trichlorophenoxy)
propionic acid and di-(NJM dimethylalkylamine)
salt of 3,6 endoxo-hexahydrophthalic acid
No information available
o ,o -dimethy 1-S -phthalimidome thyl
phosphorodithioate
No information available
Iodine formulated with solubilizing agents
Isopropyl-N-phenylcarbamate
l,3,4,5,6,7,8,8-octachloro-3a,4,7,7a-tetrahydro-
4,7-methanophthalon
l,2,3,4,10,10-hexachloro-l,4,4a,5,8,8a-hexahydro-
1,4-endo,endo-5,8-dimethanonaphthalene
Dimethyl 5-{l-isopropyl-3-methyl-pyrazolyl)
carbamate
No information available
No information available
See Diuron
See Dicofol
Decachlorooctahydro-l,3,4-methano-2H-
cyclobuta-[cd] -pentalen-2-one
See Ronnel
Amine formulation of 2-(2,4,5-trichlorophenoxy)
propionic acid
No information available
No information available
No information available
Propylene glycol butyl ether esters of Silvex
No information available
2-(2-butoxyethoxy) ethyl thiocyanate
7-isomer of benzene hexachloride
Ethylmercury phosphate
7-isomer of 1,2,3,4,5,6-hexachlorocyclohexane
No information available
No information available
2,2,4,5-trichlorophenoxy propionic acid
No information available
62 analogue of Malathion
D-8
-------
Trade Name
Chemical Name or Active Ingredient
Malamar-50
Malathion
Manzate®
Maneb (Manzate®, Dithane®)
MCP
MCPA (Agroxone®, Methoxone®)
MCPB
Metasystox®
Methoxychlor
Methyl Demeton (Metasystox®)
Methyl parathion (DAEF®, Nitrox®,
Nitrox 80®)
Methyl phencapton
Methyl trithion®
MGA Evergreen
MGA 6103
MGA 6243
Mirex
Molinate (Hydram®, Ordram®)
Monuron (Telvar®, CMU)
Monuron-TCA (Urox®)
MS 222
N2404
N2788
N2790
Nabam (Chem Ban, Dithane D-
Naled (Dibrom®)
Neburon
Neguvon®
Nemagon®
Neotran®
Nigrosine
Noxfish®
N-serve
3>, Parzate®)
50% Malathion
S-[l,2-bis-(ethoxycarbonyl)ethyl] o,o-dimethyl
phosphorodithioate
See Maneb
Ethylene-bis-dithiocarbamate manganese
See MCPA
4-chloro-2-methyl phenoxy acetic acid
4-chloro-2-methyl phenoxy butyric acid
See Methyl Demeton
1,1 ,l-trichloro-2,2-bis-(p-methoxy-phenyl) ethane
Mixture of o,o-dimethyl-o-2-(ethylthio) ethyl phos-
phorothioate (A) and o,o-dimethyl S-2(ethylthio)
ethyl phosphorothioate (B)
o,o-dimethyl o,p-nitrophenyl phosphorothioate
o,o-dimethyl S-(2,5-dichlorophenylthio) methyl
phosphorodithioate
o,o-dimethyl s-(p-chlorophenylthio) methyl
phosphorodithioate
No information available
No information available
No information available
Dodecachlorooctahydro-l,3,4-methano-2H-
cyclobuta-[dc] -pentalene
S-ethyl hexahydro-lH-azepine-1-carbothioate
3-(p-chlorophenyl)-l,l-dimethylurea
[3(p-chlorophenyl)-l ,1-dimethylurea trichlor-
acetate]
No information available
o-isopropyl-o-(2-chloro-4-nitrophenyi)-ethyl-
phosphonothioate
o-ethyl-S-p-tolyl-ethylphosphonodithioate
o-ethyl-S-phenyl-ethylphosphonodithioate
Disodium ethylene bis-dithiocarbamate
l,2-dibromo-2,2-dichloroethyl dimethyl phosphate
3-(3,4-dichlorophenyl)-l -methyl-1 -n-butylurea
See Trichlorofon
1,2-dibromo-3-chloropropane
bis(p-chlorophenoxy) methane
Aniline black
Rotenone
2-chloro-6-(trichloromethyl) pyridine
D-9
-------
Trade Name
Nytron®
Omazine®
Octachlor
Octalene
OMPA
OMS-3
OMS-44
OMS-115
OMS-144
OMS-315
OMS-437
OMS-595
OMS-648
OMS-658
OMS-659
OMS-711
OMS-712
OMS-754
OMS-868
Ordram®
Ortho 5305
Ortho 5353
Ortho 5655
Ortho MH30
Orthocide
Ovex (Ovochlor, Ovotran®, Estonmite®,
DOW K-6451®)
Oxydemetonmethyl (Meta-Systox®)
Paramar-50
Para-Oxon (Mintacol®)
Paraquat
Parathion (Folidol®, Thiophos®, Niran®,
Alkron®, Phodiatox®)
Chemical Name or Active Ingredient
25% or more ammonium content
Cupric dihydrozinium sulfate
See Chlordane
See Aldrin
See Schiadan
No information available
o-3,5-dichloro-4-methylthiophenyl) o,o-dimethyl
phosphorothioate
No information available
No information available
S-p-chlorophenyl o,o-dimethyl phosphorodithioate
Toluene-o,a-dithiol bis-(o,o-dimethyl phos-
phorodithioate)
2-chloro-l-(2,4,5-trichlorophenyl) vinyl dimethyl
phosphate
o,o-diethyl-(5-chlorobenzisoxazolyl-3) phos-
phorothioate
o-(4-bromo-2,5-dichlorophenyl) o,o-dimethyl
phosphorothioate
o-(4-bromo-2,5-dichlorophenyl) o,o-diethyl
phosphorothioate
2-chloro-l-(2,5-dichlorophenyl) vinyl dimethyl
phosphate
2-chloro-l-(2,4-dichlorophenyl) vinyl dimethyl
phosphate
S-(o-chlorophenyl) o,o-dimethyl phosphorodithioate
No information available
See Molinate
3-sec-butylphenyl-N-methyl carbamate
3-sec-amylphenyl-N-methyl carbama
3-sec-butyl 6-chlorophenyl N-methyl carbamate
58% diethanolamine salt of 1,2-dihydro-pyridazine-
3,6-dione and 30% maleic hydroxide
See Captan
p-chlorophenyl, p-chlorobenzene sulfonate
No information available
50% Parathion
o,o-diethyl-o,p-nitrophenyl phosphate
l,r-dimethyl-4,4'-dipyridylium cation
o,o-diethyl-o,p-nitrophenyl phosphorothioate
D-10
-------
Trade Name
Parzate®
Pebulate (Tillam®)
Perthane®
Phencapton (Phenkaptone®)
Phorate (Thimet®)
Phosdrin®
Phosphamidon (Dimecron®)
Phygon®
Picloram (Tordon®)
PJV1A. (PMAC,PMAS)
Polyclens
Polysan
Prometone
Prometryne
Pro-noxfish
Propanil (Rogue®, Stam F-34®)
Pyramat
Pyrethiin
Rivanol
Roccal®
Rogue®
Ronnel (Korlan®, Trolene®, Viozene®,
Dow ET-5
Rotenone
Ruelene®
'®, Dow ET-14®)
Ryania (Ryanodine)
Sarin
Schradan (OMPA, Pestox
SD 44.02
SD 7727
SD 7772
SD8211
SD 8447 (OMS-595)
SD 8530
H Pestox
Chemical Name or Active Ingredient
See Nabam
S-propylbutylethylthiocarbamate
1,1 -dichloro-2,2-bis-(p-ethylphenyl) ethane
o,o-diethyl-S-(2,5-dichlorophenylthioiTiethyl)
phosphorodithioate
o,o-diethyl-S-(ethylthio) methyl phosphorodithioate
2-carbomethoxy-l-propen-2yl dimethyl phosphate
1 -chloro-diethyl-carbamoyl-1 -1 -propen-2yl dimethyl
phosphate
See Dichlone
4-amino-3,5,6-trichloro-picolinic acid
Phenylmercuric acetate
No information available
No information available
2-methoxy-4,6-bis(isopropylamino)-2-triazine
2-methylmercapto -4,6-bis(isopropylamino)-3 -triazine
Rotenone
3' ,4'-dichloropropion-anilide
2-n-propyl-4-pyridinyl-(6)-dimethyl-carbamate
See Barthrin
6,9 -diamino-2-ethoxy acridine
Alkyl dimethyl benzyl ammonium chloride
See Propanil
Dimethyl 2,4,5-trichlorophenyl phosphorothioate
Decrin
4-tert-butyl-2-chlorophenyl methyl methylphos-
phoromidite
Ground stemwood of Ryania speciosa
Isoproporymethyl phosphoryl fluoride
Octamethylpyrophosphoramide
See Isobenzan
2,4-dichlorophenyl methanesulfonate
Phosphoric acid, 2-chloro-l-(2,5-dichlorophenyl)
vinyl dimethyl ester
Phosphoric acid, 2-chloro-l-(2,5-dichlorophenyl)
vinyl dimethyl ester
2-chloro-l-(2,4,5-trichlorophenyl) vinyl dimethyl
phosphate
Carbamic acid, methyl-3,4,5-trimethyl phenyl ester
D-ll
-------
Trade Name
Chemical Name or Active Ingredient
SD 8803
SD 9129
Separan
Sernyl
Servin
Sevin®
Shadran
Shell 4072
Shell SD-7438
Shell SD-7961
Shell SD-8447
Shell SD-8448
Shell SD-9129
Silvex
Simazine (Gesatop®)
Sinox General
Slickgone 1
Slickgone 2
Slix
Sovicide
Stam F-34®
Stauffer N-2790
Stauffer R-1910
Stauffer R-4461
Stauffer R-5092
Steramine
Strobane®(Strobane AC-14®)
Styrene
Sulfotepp (Dithione®, Bladafume®)
Swep
Systox®
TEA
TCA
TD 47
Phosphorothioic acid, o-[2-chloro-l{2,4-dichloro-
phenyl) vinyl]-o,o-diethyl ester
Dimethyl phosphate of 3-hydroxy-N-methyl-cis-
crotonimide
No information available
l-(l-phenylcyclohexyl) piperidine hydrochloride
No information available
See Carbaryl
Octamethylpyrophosphoramide
No information available
Toluene-o, a-dithiol bis-(o,o-dimethyl phos-
phorodithioate)
No information available
2-chloro-l-{2,4,5-trichlorophenyl) vinyl dimethyl
phosphate
No information available
Dimethyl phosphate of 3-hydroxy-N-methyl-cis-
crotonimide
2-(2,4,5-trichlorophenoxy) propionic acid
2-chloro-4,6-bis-(ethylamino)-s-triazine
50% dinitro-o-secondary butyl and 10% dinitro-o-
secondary amyl butyl phenol
No information available
No information available
No information available
No information available
See Propanil
No information available
Ethyl-N,N-diisobutyl thiocarbamate
No information available
No information available
p-diisobutyl phenoxy ethoxy ethyl dimethyl benzyl
ammonium chloride monohydrate
Terpene polychlorinates
Phenyl ethylene
0,0,o,o-tetraethyl dithipyrophosphate
Methyl 3,4-dichlorocarbanilate
See Demeton
2,3,6-trichlorobenzoic acid
Trichloroacetic acid
Di-n,n-dimethylcocoamine salt of 3,6 endoxohexa-
hydrophthalic acid
D-12
-------
Trade Name
TD 72
TD440
TD497
IDE (ODD, Rhothane®)
Telvar®
Tenoran
Trithion
Telodrin
TEPP (Bladan®, Tetron®, HETP, TEP)
TFM
Thanite®
Tillam®
Thimet®
Thiodan®
Thionazin (Zinophos)
Thiram (Nomersan®, Pomasol®)
Tiguvon
Tordon®
Tordon 101®
Toxaphene (Phenocide®, Phenatox®)
2,4,5TP
Treflan®
Trefmid
Trichlorofon (Dipterex®, Dylox®, Neguvon®,
Tugon®)
Tricon
Trifluralin (Treflan®)
Trithion®
Trolene®
TV-1096
UC 8305
UC 10854
UC 19786
UC 20047
UC 21149
Chemical Name or Active Ingredient
No information available
No information available
Amine salt of 3,6-endoxohexahydrophthalic acid
2,2-bis-(p-chlorophenyl)-l,l-dichloroethane
See Monuron
See Chloroxuron
See Carbophenothion
82% isobornyl thiocyanoacetate
Tetraethyl pyrophosphate
3-trifluoromethyl-4-nitrophenol
Isobornyl thiocyanoacetate
See Pebulate
See Phorate
See Endosulfan
o,o-diethyl-o-2-pyrazinyl phosphorothioate
Tetramethylthiuram disulfide
o,o-dimethyl-o- [4-(methylthio)-m-tolyl] phos-
phorothioate
See Picloram
39.6% triisopropanol-amine salt of 2,4-D, and
10.2% picloram triisopropylamine salt
Chlorinated camphene
No information available
See Trifluralin
No information available
o,o-dimethyl-(l-hydroxy-2,2,2-trichloroethyl)
phosphate
No information available
a,Oi,a-trifluoro-2,6-dinitro-N^-dipropyl-p-toluidine
See Carbophenothion
See Ronnel
Lg-threo-2-(5-nitro-2-furyl)-5-(p-nitrophenyl)-
2-oxazoline-4-methanol
p-chloro-2,4-dioxa-5-methyl-p-thiono-3-phosphabi-
cyclo-(4.4.0)-decane
m-isopropylphenyl N-methycarbamate
2-sec butyl-4,6-dinitrophenyl isopropyl-carbonate
3-chloro-6-cyano-2-norbornanone o(methyl-
carbamoyl) oxime
2-methyl-2-(methylthio) propionaldehyde
o-methyl-carbamoyl) oxime
D-13
-------
Trade Name
Chemical Name or Active Ingredient
UC 21427
Urox®
Vancide 51Z
Vapona®
Velsicol
Velsicol 1068
Veon-100
Vernolate (Vernam®)
Vernam®
Versene
Versenol
Vis-ko Stop-Mold "B"
Weedar MCP
Weedex
Weed Rap
Zectran®
Zerlate®
Zinophos
Ziram (Zerlate®, Milbam®, Fuklasin®)
Zytron®
No information available
See Monuron-TCA
Mixture of zinc dimethyldithiocarbamate and
zinc 2-mercaptobenzothiazole
See DDVP
See Dicamba
See Chlordane
Dimethylamine salt of 2-4 dichlorophenoxyacetic
acid-dimethylamine salt-2,4,5-trichlorophenoxy-
acetic acid
S-propyl dipropylthiocarbamate
See Vernolate
Sodium acetate
A series of chelating agents
54% sodium-o-phenylphenate
No information available
41% sodium metarsenite
20(2-ethyl hexyl ester of 2,4-dichlorophenoxy-
acetic acid)
4-dimethylamino-3,5-xylyl n-methyl-carbamate
See Ziram
See Thionazin
Zinc dimethyldithiocarbamate
o-(2,4-dichlorophenyl)o-methyl isopropylphos-
phoramidothioate
D-14
-------
ACKNOWLEDGMENTS
Manufacturing Chemists Association (MCA) recognized for some years the urgent need to
summarize information regarding the effect of chemicals on aquatic life as a step toward
improved water usage. To this end MCA engaged Battelle to examine the scientific literature and
compile pertinent data. Guidance in this program was provided by chemical industry specialists
of the MCA Water Resources Committee. Financed by MCA, the planning and execution of the
compilation effort and preparation of this report were accomplished by staff members of
Battelle's Columbus Laboratories. The authors of this report are H. T. Kemp, J. P. Abrams, and
R. C. Overbeck. The Environmental Protection Agency, in supporting publication of this
document, is fulfilling its role of making information on water use problems generally available
to the scientific community.
-------
1
Accession Number
w
5
2
Subject Field & Group
05 A and 05C
SELECTED WATER RESOURCES ABSTRACTS
INPUT TRANSACTION FORM
Organization
Battelle's Columbus Laboratories, Columbus, Ohio
Title
Water Quality Criteria Data Book - Volo 3
Effects of Chemicals on Aquatic Life
IQ Authors)
H. T. Kemp,
J. P. Abrams, and
R. C. Overbeck
•tji Project Designation
18050GWV5/71
21 Note
Copies available
Laboratories for
22 Citation
only from GPO. By Battelle's Columbus
Manufacturing Chemist Association.
Data Book, Vol. 3, 528 pp., May, 1971.
23
Descriptors (Starred First)
* Toxicity
* Bioassay
* Industrial wastes
* Pesticides
* Aquatic organisms
* Aquatic animals
* Pest control
Pesticide toxicity
Bioindicators
Agricultural chemicals
Fish
Chemicals
Chemical wastes
Biochemical oxygen demand
Fresh water
Sea water
Bacteria
Algae
Aquatic fungi
Invertebrates
Aquatic insects
Oysters
Shrimp
Identifiers (Starred First)
27
Abstract
Original data from more than 500 technical publications concerning the specific effects of chemicals on individual
species of aquatic biota were collected and summarized in uniform format. Alphabetical assembly of the data by chemi-
cal allows rapid access to considerable detailed information. A Species Index facilitates search for information on the
toxicity of chemicals to individual aquatic species.
The details of major procedures in laboratory bioassay and field assessment of chemical toxicity in water are
discussed. Freshwater and marine procedures are included. A total of approximately 1000 references were utilized
in preparing this report.
Recommendations include:
(1) Establishment of an information-analysis center on chemical water pollution based to some
extent on the report prepared.
(2) Preparation of a listing of chemical constituents of effluents and continued up-dating of
this list.
(Kemp - Battelle)
Abstractor
H. T. Kemp
Institution
Battelle's Columbus Laboratories
WR:102 (REV. JULY 1969)
WRSIC
SEND, WITH COPY OF DOCUMENT. TO: WATER RESOURCES SCIENTIFIC INFORMATION CENTER
U.S. DEPARTMENT OF THE INTERIOR
WASHINGTON. D. C. 20240
* GPO: 1 970-389-930
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