Fenvalerate (EHC 95, 1990)

INTERNATIONAL PROGRAMME ON CHEMICAL SAFETY

ENVIRONMENTAL HEALTH CRITERIA 95

FENVALERATE

This report contains the collective views of an international group of
experts and does not necessarily represent the decisions or the stated
policy of the United Nations Environment Programme, the International
Labour Organisation, or the World Health Organization.

Published under the joint sponsorship of
the United Nations Environment Programme,
the International Labour Organisation,
and the World Health Organization

World Health Orgnization
Geneva, 1990

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WHO Library Cataloguing in Publication Data

Fenvalerate.

(Environmental health criteria ; 95)

1.Pyrethrins I.Series

ISBN 92 4 154295 0 (NLM Classification: WA 240)
ISSN 0250-863X

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CONTENTS

ENVIRONMENTAL HEALTH CRITERIA FOR FENVALERATE

INTRODUCTION

1. SUMMARY, EVALUATIONS, CONCLUSIONS, AND RECOMMENDATIONS

1.1. Summary and evaluation
1.1.1. Identity, physical and chemical properties,
analytical methods
1.1.2. Production and use
1.1.3. Human exposure
1.1.4. Environmental fate
1.1.5. Kinetics and metabolism
1.1.6. Effects on organisms in the environment
1.1.7. Effects on experimental animals and in vitro test systems
1.1.8. Effects on human beings
1.2. Conclusions
1.2.1. General population
1.2.2. Occupational exposure
1.2.3. Environment
1.3. Recommendations

2. IDENTITY, PHYSICAL AND CHEMICAL PROPERTIES, ANALYTICAL METHODS

2.1. Identity
2.2. Physical and chemical properties
2.3. Analytical methods

3. SOURCES OF ENVIRONMENTAL POLLUTION AND ENVIRONMENTAL LEVELS

3.1. Industrial production
3.2. Use patterns
3.3. Residues in food
3.4. Residues in the environment

4. ENVIRONMENTAL TRANSPORT, DISTRIBUTION, AND TRANSFORMATION

4.1. Transport and distribution between media
4.2. Photodecomposition
4.3. Decomposition in plants
4.4. Decomposition in soils
4.5. Decomposition in water

5. KINETICS AND METABOLISM

5.1. Metabolism in mammals
5.1.1. Rat
5.1.2. Mouse
5.1.3. Domestic animals
5.2. Enzymatic systems for biotransformation

6. EFFECTS ON ORGANISMS IN THE ENVIRONMENT

6.1. Aquatic organisms
6.1.1. Toxicity to aquatic invertebrates
6.1.2. Toxicity to fish
6.1.3. Field studies and community effects
6.2. Terrestrial organisms
6.2.1. Toxicity to soil microorganisms
6.2.2. Toxicity to beneficial insects
6.2.3. Toxicity to birds
6.3. Uptake, loss, and bioaccumulation

7. EFFECTS ON EXPERIMENTAL ANIMALS AND IN VITRO TEST SYSTEMS

7.1. Single exposures
7.2. Short-term exposures
7.2.1. Oral administration
7.2.2. Inhalation
7.2.3. Dermal application
7.3. Skin and eye irritation; sensitization
7.3.1. Skin and eye irritation
7.3.2. Skin sensitization
7.4. Long-term exposures and carcinogenicity
7.4.1. Mouse
7.4.2. Rat

7.5. Mutagenicity
7.5.1. Microorganisms and insects
7.5.2. Rat
7.5.3. Mouse
7.5.4. Hamster
7.6. Teratogenicity and reproduction studies
7.6.1. Teratogenicity
7.6.2. Reproduction studies
7.7. Neurotoxicity
7.8. Behavioural studies
7.9. Miscellaneous studies
7.10. Mechanism of toxicity - mode of action

8. EFFECTS ON HUMANS

8.1. Occupational exposure
8.2. Clinical studies

9. PREVIOUS EVALUATIONS BY INTERNATIONAL BODIES

REFERENCES

APPENDIX I

FRENCH TRANSLATION OF SUMMARY, EVALUATION, CONCLUSIONS, AND RECOMMENDATIONS

WHO TASK GROUP ON ENVIRONMENTAL HEALTH CRITERIA FOR FENVALERATE

Members

Dr V. Benes, Toxicology and Reference Laboratory,
Institute of Hygiene and Epidemiology, Prague,
Czechoslovakia

Dr S. Dobson, Institute of Terrestrial Ecology, Monks Wood
Experimental Station, Huntingdon, United Kingdom

Dr Y. Hayashi, Division of Pathology, National Institute
of Hygienic Sciences, Tokyo, Japan

Dr S. Johnson, Hazard Evaluation Division, Office of
Pesticide Programme, US Environmental Protection
Agency, Washington DC, USA (Chairman)

Dr S.K. Kashyap, National Institute of Occupational Health
(I.C.M.R.) Ahmedabad, India (Vice Chairman)

Dr Yu. I. Kundiev, Research Institute of Labour, Hygiene,
and Occupational Diseases, Kiev, USSR

Dr J.P. Leahey, ICI Agrochemicals, Jealotts Hill Research
Station, Bracknell, United Kingdom (Rapporteur)

Dr J. Miyamoto, Takarazuka Research Centre, Sumitomo
Chemical Company, Takarazuka, Hyogo, Japan

Dr J. Sekizawa, Section of Information and Investigation,
Division of Information on Chemical Safety, National
Institute of Hygienic Sciences, Tokyo, Japan
(Rapporteur)

Dr Y. Takenaka, Division of Information on Chemical
Safety, Tokyo, Japan

Representatives

Dr M. Ikeda, International Commission on Occupational
Health, Department of Environmental Health, Tohoku
University School of Medicine, Sendai, Japan

Dr H. Naito, World Federation of Poison Control Centres
and Clinical Toxicology, Institute of Clinical Medi-
cine, University of Tsukuba, Tsukuba-Shi, Ibaraki,
Japan

Dr N. Punja, Groupement International des Associations
Nationales de Fabricants de Produits Agrochimiques
(GIFAP), ICI Plant Protection Division, Fenhurst,
Haslemere, United Kingdom

Observers

Dr M. Matsuo, Sumitomo Chemical Company, Biochemistry &
Toxicology Laboratory, Osaka, Japan

Dr Y. Okuno, Sumitomo Chemical Company, Biochemistry &
Toxicology Laboratory, Osaka, Japan

Secretariat

Dr K.W. Jager, International Programme on Chemical Safety,
World Health Organization, Geneva, Switzerland
(Secretary)

Dr R. Plestina, Division of Vector Control, Delivery and
Management of Vector Control, World Health Organiz-
ation Geneva, Switzerland

NOTE TO READERS OF THE CRITERIA DOCUMENTS

Every effort has been made to present information in
the criteria documents as accurately as possible without
unduly delaying their publication. In the interest of all
users of the environmental health criteria documents,
readers are kindly requested to communicate any errors
that may have occurred to the Manager of the International
Programme on Chemical Safety, World Health Organization,
Geneva, Switzerland, in order that they may be included in
corrigenda, which will appear in subsequent volumes.

* * *

A detailed data profile and a legal file can be
obtained from the International Register of Potentially
Toxic Chemicals, Palais des Nations, 1211 Geneva 10,
Switzerland (Telephone No. 7988400 - 7985850).

* * *

The proprietary information contained in this document
cannot replace documentation for registration purposes,
because the latter has to be closely linked to the source,
the manufacturing route, and the purity/impurities of the
substance to be registered. The data should be used in
accordance with paragraph 82-84 and recommendations
paragraph 90 of the Second FAO Government Consultation
[39].

ENVIRONMENTAL HEALTH CRITERIA FOR FENVALERATE

A WHO Task Group on Environmental Health Criteria for
Fenvalerate, Permethrin, and d-Phenothrin met in Tokyo
from 4 to 8 July 1988. This meeting was convened with the
financial assistance of the Ministry of Health and
Welfare, Tokyo, Japan, and was hosted by the National
Institute of Hygienic Sciences (NIHS) in Tokyo.

Dr T. Furukawa and Dr K. Shirota opened the meeting on
behalf of the Ministry of Health and Welfare, and Dr A.
Tanimura, Director-General of the NIHS welcomed the par-
ticipants to the institute. Dr M. Mercier, Manager of the
IPCS, welcomed the participants on behalf of the three
IPCS cooperating organizations (UNEP/ILO/WHO). The group
reviewed and revised the draft monograph and made an
evaluation of the risks for human health and the environ-
ment from exposure to fenvalerate.

The first draft of this document was prepared by
Dr J. MIYAMOTO and Dr M. MATSUO of the Sumitomo
Chemical Company, Japan, with the assistance of the staff
of the National Institute of Hygienic Sciences, Tokyo,
Japan. Dr I. Yamamoto of the Tokyo University of Agricul-
ture and Dr M. Eto of Kyushu University, Japan, assisted
with the finalization of the draft.

The second draft was prepared by Dr J. SEKIZAWA, NIHS,
Tokyo, incorporating comments received following circu-
lation of the first draft to the IPCS contact points for
Environmental Health Criteria documents. Dr K.W. Jager and
Dr P.G. Jenkins, both members of the IPCS Central Unit,
were responsible for the technical development and
editing, respectively, of this monograph.

The assistance of the Sumitomo Chemical Company in
making available to the IPCS and the Task Group its toxi-
cological proprietary information on fenvalerate is grate-
fully acknowledged. This allowed the Task Group to make
its evaluation on the basis of more complete data.

The efforts of all who helped in the preparation and
finalization of the document are gratefully acknowledged.

ABBREVIATIONS

ai active ingredient

Cl-Vacid (= CPIA) 2-(4-chlorophenyl)isovaleric acid

ECD-GC gas chromatography with electron capture detector

FID-GC gas chromatography with flame ionization detector

GLC gas-liquid chromatography

HPLC high-performance liquid chromatography

NOEL no-observed-effect level

PBacid 3-phenoxybenzoic acid

PBalc 3-phenoxybenzyl alcohol

PBald 3-phenoxybenzaldehyde

PCB polychlorinated biphenyl

TOCP tri- ortho- cresyl phosphate

INTRODUCTION

SYNTHETIC PYRETHROIDS - A PROFILE

1. During investigations to modify the chemical struc-
tures of natural pyrethrins, a certain number of syn-
thetic pyrethroids were produced with improved physi-
cal and chemical properties and greater biological
activity. Several of the earlier synthetic pyrethroids
were successfully commercialized, mainly for the con-
trol of household insects. Other more recent
pyrethroids have been introduced as agricultural in-
secticides because of their excellent activity against
a wide range of insect pests and their non-persistence
in the environment.

2. The pyrethroids constitute another group of insecti-
cides in addition to organochlorine, organophosphorus,
carbamate, and other compounds. Pyrethroids commer-
cially available, to date include allethrin, res-
methrin, d-phenothrin, and tetramethrin (for insects
of public health importance), and cypermethrin, delta-
methrin, fenvalerate, and permethrin (mainly for agri-
cultural insects). Other pyrethroids are also avail-
able, including furamethrin, kadethrin, and tellalle-
thrin (usually for household insects), fenpropathrin,
tralomethrin, cyhalothrin, lambda-cyhalothrin, teflu-
thrin, cufluthrin, flucythrinate, fluvalinate, and
biphenate (for agricultural insects).

3. Toxicological evaluations of several synthetic
pyrethroids have been performed by the FAO/WHO Joint
Meeting on Pesticide Residues (JMPR). The acceptable
daily intake (ADI) has been estimated by the JMPR for
cypermethrin, deltamethrin, fenvalerate, permethrin,
d-phenothrin, cyfluthrin, cyhalothrin, and flucythri-
nate.

4. Chemically, synthetic pyrethroids are esters of spe-
cific acids (e.g., chrysanthemic acid, halo-substi-
tuted chrysanthemic acid, 2-(4-chlorophenyl)-3-methyl-
butyric acid) and alcohols (e.g., allethrolone, 3-
phenoxybenzyl alcohol). For certain pyrethroids, the
asymmetric centre(s) exist in the acid and/or alcohol
moiety, and the commercial products sometimes consist
of a mixture of both optical (IR/1S or d/1) and geo-
metric ( cis/trans ) isomers. However, most of the
insecticidal activity of such products may reside in
only one or two isomers. Some of the products (e.g.,
d-phenothrin, deltamethrin) consist only of such
active isomer(s).

5. Synthetic pyrethroids are neuropoisons acting on the
axons in the peripheral and central nervous systems by
interacting with sodium channels in mammals and/or
insects. A single dose produces toxic signs in mam-
mals, such as tremors, hyperexcitability, salivation,
choreoathetosis, and paralysis. The signs disappear
fairly rapidly, and the animals recover, generally
within a week. At near-lethal dose levels, synthetic
pyrethroids cause transient changes in the nervous
system, such as axonal swelling and/or breaks and
myelin degeneration in sciatic nerves. They are not
considered to cause delayed neurotoxicity of the kind
induced by some organophosphorus compounds. The mech-
anism of toxicity of synthetic pyrethroids and their
classification into two types are discussed in the
Appendix.

6. Some pyrethroids (e.g., deltamethrin, fenvalerate,
flucythrinate, and cypermethrin) may cause a transient
itching and/or burning sensation in exposed human
skin.

7. Synthetic pyrethroids are generally metabolized in
mammals through ester hydrolysis, oxidation, and con-
jugation, and there is no tendency to accumulate in
tissues. In the environment, synthetic pyrethroids are
fairly rapidly degraded in soil and in plants. Ester
hydrolysis and oxidation at various sites on the mol-
ecule are the major degradation processes. The
pyrethroids are strongly adsorbed on soil and sedi-
ments, and hardly eluted with water. There is little
tendency for bioaccumulation in organisms.

8. Because of low application rates and rapid degradation
in the environment, residues in food are generally
low.

9. Synthetic pyrethroids have been shown to be toxic for
fish, aquatic arthropods, and honey bees in laboratory
tests. But, in practical usage, no serious adverse
effects have been noticed because of the low rates of
application and lack of persistence in the environ-
ment. The toxicity of synthetic pyrethroids in birds
and domestic animals is low.

10. In addition to the evaluation documents of FAO/WHO,
there are several good reviews and books on the chem-
istry, metabolism, mammalian toxicity, environmental
effects, etc., of synthetic pyrethroids, including
those by Elliott [36], Miyamoto [126], Miyamoto &
Kearney [127], and Leahey [101].

1. SUMMARY, EVALUATION, CONCLUSIONS, AND RECOMMENDATIONS

1.1 Summary and Evaluation

1.1.1 Identity, physical and chemical properties,
analytical methods

Fenvalerate is a potent insecticide that has been in
use since 1976. It is an ester of 2-(4-chlorophenyl)-3-
methylbutyric acid and alpha-cyano-3-phenoxybenzyl alcohol,
but lacks a cyclopropane ring. However, in terms of its
insecticidal behaviour, it belongs to the pyrethroid
insecticides. It is a racemic mixture of four optical
isomers with the configurations [2S, alphaS], [2S, alphaR],
[2R, alphaS], and [2R, alphaR]. The [2S, alphaS] isomer is
the most biologically active, followed by the [2S, alphaR]
isomer.

Technical grade fenvalerate is a yellow or brown vis-
cous liquid having a specific gravity of 1.175 at 25 °C.
The vapour pressure is 0.037 mPa at 25 °C and it is rela-
tively non-volatile. It is practically insoluble in water
(approximately 2 µg/litre), but soluble in organic sol-
vents such as acetone, xylene, and kerosene. It is stable
to light, heat, and moisture, but unstable in alkaline
media due to hydrolysis of the ester linkage.

Residue and environmental analysis can be carried out
using a gas chromatograph equipped with an electron cap-
ture detector, the minimum detectable concentration being
0.005 mg/kg. A gas chromatograph with a flame ionization
detector is used for product analysis.

1.1.2 Production and use

Approximately 1000 tonnes per year of fenvalerate are
used worldwide (1979-1983 figures). It is mostly employed
in agriculture but also for insect control in homes and
gardens and on cattle, alone or in combination with other
insecticides. It is formulated as emulsifiable concen-
trate, ultra-low-volume concentrate, dust, and wettable
powder.

1.1.3 Human exposure

Exposure of the general population to fenvalerate is
mainly via dietary residues. Residue levels in crops grown
by good agricultural practice are generally low. The
resulting exposure of the general population is expected
to be very low, but data from total-diet studies are
lacking.

Analysis of residues in stored grain showed that over
70% of the applied dose remained on wheat after 10 months
at 25 °C. Following milling and baking, white bread has
about the same residue level as white flour (approximately
0.06-0.1 mg/kg).

Information on occupational exposure to fenvalerate is
very limited.

1.1.4 Environmental fate

In soil, degradation occurs via ester cleavage,
diphenyl ether cleavage, ring hydroxylation, hydration of
the cyano group to amide, and further oxidation of the
fragments formed to yield carbon dioxide as a major final
product. Studies to investigate the leaching potential of
fenvalerate and its degradation products showed that very
little downward movement will occur in soils.

In water and on soil surfaces, fenvalerate is photo-
degraded by sunlight. Ester cleavage, hydrolysis of the
cyano group, decarboxylation to yield 2-(3-phenoxyphenyl)-
3-(4-chlorophenyl)-4-methylpentane-nitrile (decarboxy-
fenvalerate), and other radical-initiated reactions have
been shown to occur.

On plants, fenvalerate has a half-life of approximate-
ly 14 days. Ester cleavage is a major reaction, followed
by oxidation and/or conjugation of the fragments formed.
Decarboxylation to yield decarboxy-fenvalerate also oc-
curs.

In general, the degradative processes which occur in
the environment lead to less toxic products.

The degradation of fenvalerate in the environment is
rather rapid. Half-lives are 4-15 days in river water,
8-14 days on plants, 1-18 days by photodegradation on soil
and 15 days-3 months in soil.

There is virtually no leaching of fenvalerate in soil.
Thus, it is unlikely that the compound will attain signif-
icant levels in the aquatic environment.

1.1.5 Kinetics and metabolism

The fate of fenvalerate in rats and mice has been
studied using fenvalerate radiolabelled in the acid moiety
or benzyl or cyano groups. The administered radioac-
tivity, except that of the cyano-labelled compounds, is
readily excreted (up to 99% in 6 days). The major meta-
bolic reactions are ester cleavage and hydroxylation at
the 4'position. Various oxidative and conjugation
reactions that lead to a complex mixture of products have
been shown to occur. When studies were carried out with
fenvalerate radiolabelled in the cyano group, elimination

of the radioactive dose was less rapid (up to 81% in 6
days). The remaining radioactivity was retained mainly in
the skin, hair, and stomach as thiocyanate. A minor, but
very important, metabolic pathway is the formation of a
lipophilic conjugate of [2R]-2-(4-chlorophenyl)isovalerate.
This conjugate, which is implicated in the formation of
granuloma, has been detected in the adrenals, liver and
mesenteric lymph nodes of rats, mice, and some other
species.

1.1.6 Effects on organisms in the environment

In laboratory tests, fenvalerate is highly toxic
for aquatic organisms. The LC₅₀ values range from
0.008 µg/litre for newly hatched mysid shrimps to
2 µg/litre for a stonefly. The no-observed-effect level
in life-cycle tests using Daphnia galeata mendotae is less
than 0.005 µg/litre. Fenvalerate is also highly toxic
for fish. The 96-h LC₅₀ values range from 0.3 µg/litre
for larval grunion to 200 µg/litre for adult Tilapia. The
no-observed-effect level, over 28 days, for early-life
stages of the sheepshead minnow is 0.56 µg/litre. Fenval-
erate is less toxic for aquatic algae and molluscs, with
96-h LC₅₀ values > 1000 µg/litre.

In field tests and in the use of the compound under
practical conditions, the potentially high toxicity to
aquatic organisms is not manifested. Some aquatic
invertebrates are killed when water is oversprayed, but
the effect on populations is temporary. There have been
no reports of fish kills. This reduced toxicity in field
use is related to the strong adsorption of the compound to
sediments.

Fenvalerate is highly toxic to honey bees. The topical
LD₅₀ is 0.41 µg/bee, but there is a strong repellent
effect of fenvalerate to bees, which reduces the effect in
practice. There is no evidence of significant kills of
honey bees under normal use. Fenvalerate is more toxic to
predator mites than to the target pest species.

Fenvalerate has very low toxicity to birds when given
orally or applied to the diet. LD₅₀ values are > 1500
mg/kg body weight for acute oral dosage and an LD₅₀ value
for dietary exposure of Bobwhite quail has been reported
at > 15 000 mg/kg diet.

Fenvalerate is readily taken up by aquatic organisms.
Bioconcentration factors ranged from 120 to 4700 for vari-
ous organisms (algae, snail, Daphnia and fish) in model
ecosystem studies. The fenvalerate taken up by aquatic
organisms is rapidly lost on transfer to clean water. The
compound can, therefore, be regarded as having no tendency
to bioaccumulate in practice.

1.1.7 Effects on experimental animals and in vitro test systems

Fenvalerate has moderate to low acute oral toxicity.
However, LD₅₀ values differ considerably (82 to > 3200
mg/kg) according to animal species and vehicle of adminis-
tration. The acute clinical signs of poisoning appear
rapidly but survivors become asymptomatic within 3-4 days.
The toxic signs of the racemic mixture, as well as of its
[2S, alphaS] isomer, include restlessness, tremors, pilo-
erection, diarrhoea, abnormal gait, choreo-athetosis, and
salivation (CS-syndrome); it is classified as a Type II
pyrethroid. Electrophysiologically it produces bursts of
spikes in the cercal motor nerve of the cockroach. There
is, however, no clear-cut link between electro-physiologi-
cal findings in insects and toxicity to mammals.

Rats fed fenvalerate at 2000 mg/kg diet for 8-10 days
showed typical signs of acute intoxication. Reversible
morphological changes in the sciatic nerve were observed
in rats administered fenvalerate at 3000 mg/kg diet.
Histopathological changes in sciatic nerves were also
observed in rats and mice treated with a single oral does
of fenvalerate at lethal or sublethal levels.

Hens administered fenvalerate orally at 1000 mg/kg per
day for 5 days did not show any clinical or morphological
signs of delayed neurotoxicity.

The acute intraperitoneal toxicity of fenvalerate
metabolites in mice was no greater than that of
fenvalerate itself.

In subacute and subchronic toxicity studies, mice,
rats, dogs, and rabbits were treated with fenvalerate by
oral, dermal, and inhalational routes for 3 weeks to 6
months. In 4-week mouse and rat inhalation studies, a no-
observed-effect level (NOEL) of 7 mg/m³ was established
in both species. The NOEL in a 90-day rat study was
125 mg/kg diet, in a 2-year feeding study it was 250 mg/kg
diet (12.5 mg/kg body weight), and in a 24-28 month study
it was 150 mg/kg diet, (7.5 mg/kg body weight). The NOEL
in a 2-year mouse study was 50 mg/kg diet, corresponding
to 6.0 mg/kg body weight, and 30 mg/kg diet, corresponding
to 3.5 mg/kg body weight, in a 20-month feeding study.
For dogs the NOEL was 12.5 mg/kg body weight in a 90-day
feeding study. Some fenvalerate formulations have caused
skin and eye irritation. However, technical fenvalerate
is non-irritant and has no sensitizing effects.

In long-term toxicity studies, microgranulomatous
changes were observed in mice, specifically when treated
with the [2R, alphaS] isomer of fenvalerate (125 mg/kg
diet) for 1 to 3 months. These changes were reversed when
fenvalerate was eliminated from the diet. The causative
agent for this change was the cholesterol ester of 2-(4-
chlorophenyl)isovaleric acid, a lipophilic metabolite of

fenvalerate from the [2R, alphaS] isomer. The NOEL for
these microgranulomatous changes in mice was 30 mg fenval-
erate per kg diet.

In a long-term toxicity study, microgranulomatous
changes were also observed in rats at a dose level of
500 mg/kg diet, the NOEL for these changes being 150 mg/kg
diet.

Fenvalerate was not carcinogenic to mice, when fed at
dietary levels up to 3000 mg/kg for 78 weeks or 1250 mg/kg
for 2 years. It was also not carcinogenic to rats when
fed at dietary levels up to 1000 mg/kg for 2 years.

Fenvalerate did not show any mutagenic or chromosome-
damaging activity in several in vitro and in vivo assays.

Fenvalerate is not teratogenic to mice or rabbits at
dose levels of up to 50 mg/kg body weight per day, nor did
it show any toxic effects (at up to 250 mg/kg diet) on
reproductive parameters in a 3-generation rat reproduction
study.

1.1.8 Effects on human beings

Fenvalerate can induce numbness, itching, tingling,
and burning sensations in exposed workers, which develop
after a latent period of approximately 30 min, peak by
8 h, and disappear within 24 hours. Some poisoning cases
have resulted from occupational exposure, owing to over-
exposure due to neglect of safety precautions.

There are no indications that fenvalerate will have an
adverse effect on human beings, provided it is used as
recommended.

1.2 Conclusions

1.2.1 General population

The exposure of the general population to fenvalerate
is expected to be very low. It is not likely to present a
hazard provided it is used as recommended.

1.2.2 Occupational exposure

With reasonable work practices, hygiene measures, and
safety precautions, fenvalerate is unlikely to present a
hazard to those occupationally exposed to it.

1.2.3 Environment

It is unlikely that fenvalerate or its degradation
products will attain levels of environmental significance
provided that recommended application rates are used.
Under laboratory conditions fenvalerate is highly toxic to

fish, aquatic arthropods, and honey bees. However, lasting
adverse effects are not likely to occur under field con-
ditions provided it is used as recommended.

1.3 Recommendations

Although dietary levels arising from recommended usage
are considered to be very low, confirmation of this
through inclusion of fenvalerate in monitoring studies
should be considered.

Fenvalerate has been used for many years and only a
few cases of temporary effects from occupational exposure
have been reported. Nevertheless, it would be wise to
maintain observations of human exposure.

2. IDENTITY, PHYSICAL AND CHEMICAL PROPERTIES, ANALYTICAL METHODS

2.1 Identity

Fenvalerate is a synthetic pyrethroid having no cyclo-
propane ring in the molecule. It is prepared by the es-
terification of (2RS)-2-(4-chlorophenyl)-3-methylbutyric
acid (also known as (2RS)-2-(4-chlorophenyl)isovaleric
acid, CPIA, or Cl-Vacid) with (alphaRS)-alpha-cyano-3-
phenoxybenzyl alcohol [137]. It has four stereoisomers as
a result of the two chiral centres in the acid and alcohol
moieties (Fig. 1).

The composition of the product is a racemic mixture of
the four isomers in equal proportions (Table 1). Technical
grade fenvalerate contains 90-94% of fenvalerate [41]. The
molecular formula is C₂₅H₂₂ClNO₃.

Table 1. Chemical identity of fenvalerate and its various stereoisomers
-----------------------------------------------------------------------------------------------------
Common name/ CAS Index name (9Cl) Stereoisomeric Synonyms and
CAS Registry no./ composition^c trade names
NIOSH Accession no.^a Stereospecific name^b
-----------------------------------------------------------------------------------------------------
Fenvalerate Benzeneacetic acid, (1):(2):(3):(4) Sumicidin, Belmark,
51630-58-1 4-chloro- alpha-(1-methylethyl)-, = 1:1:1:1
CY1576350 cyano(3-phenoxyphenyl)methyl ester Pydrin, S-5602
SD43775, WL43775
(RS)- alpha-cyano-3-phenoxybenzyl
(RS)-2-(4-chlorophenyl)-3-
methylbutyrate

alpha-Fenvalerate Same as fenvalerate
66230-04-4
Benzeneacetic acid, 4-chloro- alpha-
(1-methylethyl)-, cyano-3-phenylbenzyl
ester, [S-(R^*,R^*)]-

beta-Fenvalerate Same as fenvalerate
66267-77-4
Benzeneacetic acid, 4-chloro- alpha-
(1-methylethyl)-, cyano-3-phenoxybenzyl
ester, [R-R^*, S^*)]-

(S,S)-Fenvalerate
CY1576350
-----------------------------------------------------------------------------------------------------
^a Registry of Toxic Effects of Chemical Substances (1981-1982 edition).
^b (2S), d, (+) or (2R), 1, (-) in the acid part of fenvalerate signify the same stereospecific
conformation, respectively.
^c Numbers in parantheses identify the structures shown in Fig. 1.

2.2 Physical and Chemical Properties

Some physical and chemical properties of fenvalerate
are given in Table 2. It is stable to heat and moisture
and is relatively stable (compared with natural py-
rethrins) when exposed to light. It is more stable in
acidic than in alkaline media, optimum stability being at
pH 4 [41, 117, 207].

Table 2. Some physical and chemical properties of fenvalerate
--------------------------------------------------------------
Physical state viscous liquid

Colour yellow or brown

Odour mild "chemical" odour

Relative molecular mass 419.9

Boiling point 300 °C at 4.93 kPa (37 mmHg)

Water solubility 2 µg/Litre

Solubility in organic solvents soluble^a

Relative density (25 °C) 1.175

Vapour pressure (25 °C) 0.037 mPa

Log octanol-water partition
coefficient (log P_ow) 6.2
--------------------------------------------------------------
^a Acetone (>1 kg/kg), hexane (155 g/kg), xylene (>1 kg/kg),
ethanol, cyclohexanone, ether, kerosene, chloroform.

2.3 Analytical Methods

Methods for the analysis of fenvalerate are summarized
in Table 3. This table includes the procedures for (a) ex-
traction with solvent, (b) liquid-liquid partition, (c)
chromatographic separation (clean up), and (d) quantitat-
ive and qualitative determination by suitable analytical
instruments, and also includes minimum detectable concen-
tration (MDC) and percentage recovery data.

The separation of the cis and trans isomers of
fenvalerate has been carried out using a commercially
available Pirkle type 1-A chiralphase HPLC with, as sol-
vent system, 0.025% propen-2-ol in hexane (1 ml/min)
[24].

Fenvalerate can be determined by gas-liquid chromato-
graphy with a flame ionization detector (FID-GC) (3% OV-17
glass column with temperature programming) [11].

A laminar flow, microwave-induced plasma torch has
been evaluated for its use in gas chromatography [19]. The
detection limit of fenvalerate on the carbon channel was
0.054 µg/ml.

To analyse technical grade fenvalerate, the product is
dissolved in chloroform together with 2-(4-biphenyl)-5-
phenyl-1,3,4-oxadiazole (an internal standard), and the
solution is injected into an FID-GC system [79].

The Joint FAO/WHO Codex Alimentarius Commission has
published recommendations for methods for the analysis of
fenvalerate residues [48].

Table 3. Analytical methods for fenvalerate
--------------------------------------------------------------------------------------------------------------------------------------
Sample Sample preparation Determination MDC^b % Recovery Reference
GLC or HPLC; detector, (fortification
Extraction Partition Clean-up carrier flow, column, level)
solvent temperature, retention (mg/kg)^c
Column Elution time
--------------------------------------------------------------------------------------------------------------------------------------
Residue analysis

apple n-hexane ext.sol.^a silica gel CH₂Cl₂ ECD-GC, N₂, 50 ml/min, 0.01 89-108 6
pear acetone /H₂O 1 m, 3% OV-7, 235 °C (0.1-1.0)
cabbage (1/1)
potato

grape acetone saturated Florisil acetone/ ECD-GC, N₂, 30 ml/min, 0.005 94-99 67
pepper NaCl/ petroleum 1.1 m, 2% XE-60, (0.005-1.0)
petroleum ether (1/99) 215 °C, 7 min
ether

cabbage CH₃CN 1% NaCl/ Florisil benzene/ n- ECD-GC, argon/methane 0.005 88-104 103
lettuce petroleum hexane (1/1) (95/5), 45 ml/min, 1.8 m, (0.012-1.2)
ether silica gel benzene/ 4% SE-30/6% QF-1 or 15%
acetone (3/1) OV-101, 225 °C, 25-30 min

beef CH₃CN/ n-hexane/ Florisil CH₃CN/ ECD-GC, N₂, 100 ml/min, 0.005 82-94 16
muscle H₂0 2% NaCl CH₂Cl₂/ 1.8 m, Ultra-Bond 20M, (0.01-1.0)
egg yolk (85/15) solution n-hexane 220 °C, 11.5, 14.2 min
milk or CH₃CN (0.35/50/50)

Environmental analysis

soil acetone, 2% NaCl/ alumina ether/ ECD-GC, argon/methane 78-105 74
n-hexane/ ext.sol.^a n-hexane (95/5), 60 ml/min, (0.005-1.0)
acetone (1/9) 0.97 m, 6% OV-210,
(1/1), 230 °C, 10.6, 11.8 min
hexane

Product analysis

Technical CHCl₃ FID-GC, He, 60 ml/min, 79
grade 1.0 m, 2% Apiezon L,
245 °C
--------------------------------------------------------------------------------------------------------------------------------------
^a extraction solvent.
^b minimum detectable concentration (mg/kg).
^c fortification level indicates the concentration of fenvalerate added to control samples for the measurement of recovery.

3. SOURCES OF HUMAN AND ENVIRONMENTAL EXPOSURE:
ENVIRONMENTAL LEVELS

3.1 Industrial Production

Fenvalerate was first marketed in 1976 and the esti-
mated production was 1000 tonnes in 1979 and 889 tonnes in
1982 [203]. Recent world-wide production figures are
listed in Table 4.

Table 4. World-wide production of
fenvalerate
-------------------------------------
Year Production Reference
(tonnes)
-------------------------------------
1979 1016 200

1980 1067 201

1981 914 202, 203

1982 903 203

1983 1280 204

1984 919 9
-------------------------------------

3.2 Use Patterns

Of the total world-wide consumption of 473 tonnes of
fenvalerate in 1980 [8], 271 tonnes were used in the USA,
103 tonnes in Latin America, 43 tonnes in Africa, 28
tonnes in Western Europe, and 26 tonnes each in Australia
and Turkey. It was mostly used on cotton (90.3% of the
consumption) but some was used on other crops such as
vines, tomatoes, potatoes, pomes, and other fruit.

Fenvalerate has also been used for homes and gardens
and for the control of cattle insect infestation [8]. It
is formulated in emulsifiable concentrates (25-300
g/litre), ultra-low volume concentrates (25-75 g/litre),
dusts, and wettable powder, and is also used in combi-
nation with other pesticides (e.g., fenitrothion).

3.3 Residues in Food

Supervised trials have been carried out on a wide
variety of crops and comprehensive summaries of the re-
sults of residue analysis in these trials are contained in
the evaluation reports of the Joint FAO/WHO Meeting on
Pesticide Residues (JMPR) [41, 43, 45, 47, 50]. A compre-
hensive list of Maximum Residue Limits (MRLs) for a large
number of commodities resulted from these evaluations
[51].

In one study, apples in the USA were treated four
times with 30% emulsifiable concentrate at a rate of 0.67
kg active ingredient/ha. The residue levels were 2.2 mg/kg
in whole apples, 7.3 mg/kg in peel, and 0.03 mg/kg in
peeled fruits 6 weeks after the last application [41].

When wheat grain treated with fenvalerate at a rate of
1.01 mg/kg was stored at 25 °C, the residue levels were
0.86 mg/kg after 6.5 months of storage and 0.74 mg/kg
after 10 months^a.

Three lactating cows were fed ¹⁴C-(acid-labelled)-
fenvalerate at a dose level of 0.11 mg/kg diet daily for
21 days and sacrificed 12 h after receiving the last dose.
The recovery of ¹⁴C in the milk was less than 1% and the
levels ranged from < 0.0006 to 0.0019 µg/litre, with a
plateau occurring after 1 week of feeding. No ¹⁴C was
detectable in fat (< 0.02 mg/kg) or muscle (< 0.01 mg/kg).
In another study, fenvalerate was sprayed on cows at a
rate of 0.2, 0.4, or 2 g/animal. The residue level did not
exceed 0.01 mg/kg muscle. Maximum residues were 0.22 mg/kg
in fat and 0.02 mg/kg in milk at the dose rate of 2 g/cow
[132, 154].

When wheat containing 0.6 mg fenvalerate/kg was sub-
jected to milling and baking, white bread was found to
have about the same residue level as white flour, i.e.,
about 0.06-0.1 and 0.08-0.09 mg/kg, respectively^b.

3.4 Residues in the Environment

Data on actual levels of fenvalerate residues in air,
water, or soil are not available. Residues in air would
not be expected for a compound with a vapour pressure of
0.037 mPa at 25 °C.

----------------------------------------------------------
^a M. Bengston (1979), personal communication from final
report on silo-scale experiments 1977-1978 to the
Australian Wheat Board Working Party on grain protect-
ants. Queensland Department of Primary Industries
(unpublished report cited from FAO/WHO [41].

^b B.W. Simpson (1979), draft report to be published by
Queensland Department of Primary Industries Analyti-
cal Chemical Branch, Brisbane, Australia (unpublished
report cited in FAO/WHO [41].

4. ENVIRONMENTAL TRANSPORT, DISTRIBUTION, AND TRANSFORMATION

Appraisal

The major photodegradation routes for fenvalerate are de-
carboxylation to yield 3-(4-chlorophenyl)-4-methyl-2-(3-phenoxy-
phenyl)-valeronitrile, ester and ether cleavage, hydrolysis of
the cyanide group, and other radical-initiated reactions. Ester
cleavage and some photo-initiated reactions are the major
routes of decomposition on plants. In soils, the formation of
bound material and the evolution of carbon dioxide are the
major processes observed under both aerobic and anaerobic con-
ditions.

The degradation pathways of fenvalerate are summarized
in Fig. 2.

4.1 Transportation and Distribution Between Media

Hill [74] investigated the distribution of fenvalerate
residues in soil under field conditions using a microplot

technique. The microplots (20 x 20 cm) were treated with
fenvalerate at a rate of 150 g/ha. After 45 weeks, 11% of
the applied fenvalerate was located in the 0-2.5 cm soil
layer and less than 0.5% in the 2.5-5 cm soil samples.
Less than 0.1% of the applied fenvalerate was detected in
any of the soil samples taken after 3 or 4 weeks, despite
a rainfall of 95.4 mm during the first 4 weeks (including
a 25.9 mm downpour 15 days after application). These
results indicate that fenvalerate does not readily leach
downward and that lateral surface movement is very
limited.

A similar conclusion was obtained from laboratory
soil-leaching studies. More than 95% of the applied
fenvalerate remained in the treated portion of soil
columns when leaching was started immediately or 30 days
after treatment of the soil [133]. The possibility of
fenvalerate accumulating in orchard soils was assessed by
monitoring soil and leaf litter in an orchard in the
Okanagan valley, British Columbia, Canada, following
multiple annual application of the pesticide. Belmark 300
(30% fenvalerate EC formulation) had been sprayed at a
rate of 188-500 ml/ha (one to three times per year) for
more than three years. To obtain initial concentration,
organic litter samples were sprayed at a rate of 450 ml/ha
and samples were collected 2 h later. While the initial
concentration thus obtained in the litter was 0.214 mg/kg
(average value), orchard litter samples contained
0.30-0.63 mg/kg while samples from a non-treated block
contained < 0.002 mg/kg. Orchard soil samples (0-15 cm
depth) in two orchards contained fenvalerate residues of
< 0.0035-0.006 mg/kg and 0.0063-0.024 mg/kg [188].

4.2 Photodecomposition^a

In studies by Holmstead et al. [78], fenvalerate (5),
at a concentration of 0.01 mol/litre in methanol, hexane,
or acetonitrilewater (60:40), underwent rapid photodegra-
dation under the action of UV light (290-320 nm) with a
half-life of 16-18 min (Fig. 2). With 90-95% conversion
after 60 min, 2-(3-phenoxyphenyl)-3-(4-chlorophenyl)-4-
methyl-pentanenitrile (31) (decarboxy-fenvalerate) was the
major photoproduct, amounting to 54-57% of the total reac-
tion mixture. There were smaller amounts of the dechlori-
nated analogue (32) of decarboxy-fenvalerate and the dimer
(8) of 2,2-dimethyl-4-chlorostyrene. 3-Phenoxybenzoyl cy-
anide (4), 3-phenoxybenzaldehyde (18) (PBald), 4-chloro-
isobutylbenzene (6), and 2,2-dimethyl-4-chlorostyrene (7)
were detected in small amounts in hexane or methanol. 3-
Phenoxybenzyl cyanide (28), its dimer (26), and 1,2-bis-
(phenoxyphenyl)ethane (27) were found only in hexane, and
methyl 3-phenoxybenzoate (12) was detected only in meth-
anol. Products found uniquely in acetonitrile-water were
2-(4-chlorophenyl)-3-methylbutyric acid (17) (CPIA), 3-
phenoxybenzoic acid (22) (PBacid) and 1-(4-chlorophenyl)-
2-methylpropanol (9). Several unknown compounds were ob-
served in the remaining 5-10%. Fenvalerate, in a thin film

(1 mg/cm²) on glass, decomposed in sunlight with a half-
life of approximately 4 days. About 10% of the applied
material remained after 43 days. In addition to the photo-
products formed in solution, small amounts of 3-phenoxy-
benzyl alcohol (19) (PBalc) and isopropyl 4-chlorophenyl-
ketone (10) were detected.

On exposure to autumn sunlight in Japan, the
[2S, alphaS] isomer of fenvalerate in distilled water
decomposed with a half-life of approximate 10 days. This
isomer photodecomposed via pathways that included decar-
boxylation, hydration of the CN group to a carbamoyl
(CONH₂) group, hydrolysis of the CONH₂ group to a car-
boxyl (COOH) group, and cleavage of the ester or diphenyl
ether linkage. Cleavage of the ester linkage was a major
photochemical reaction and led to the formation of 2-(4-
chlorophenyl)-3-methylbutyric acid (17) (17.3% of the
applied ¹⁴C, 10 days after exposure). There was no sig-
nificant difference between fenvalerate and the [2S, alphaS]
isomer in the rates and routes of photodegradation [179].

The photodegradation of fenvalerate (0.3-0.4 ng/cm²)
on two kinds of soil in natural sunlight was compared with
that of the [2S, alphaS] isomer. Fenvalerate and its isomer
photodecomposed with half-lives of 1.4-2.4 days and 1.1-
2.5 days, respectively. The pathways included hydration
of the cyano group to the carbamoyl group (19.2-48.4% at
10 days) with subsequent hydrolysis to the carboxyl group
(0.9-2.0% at 10 days), ester-bond cleavage (3.4-4.5% at 10
days), and decarboxylation (0.3-0.9% at 10 days). Little
2S/2R and alphaS/alphaR isomerization (as determined by
HPLC) occurred on the soils. There was no significant
difference between the two compounds in the rates and
pathways of photodegradation [89].

Holmstead & Fullmer [77] investigated the photodecar-
boxylation of several cyanohydrin esters in methanol and
hexane under artificial light as models for pyrethroid
photodecomposition. The cyanohydrin esters gave rise to
decarboxylated products, to a greater or lesser extent,
whereas the analogous compounds without the cyano group
did not produce the photodecarboxylated compounds.
alpha-Cyanobenzyl phenylacetate, which yielded the stable
benzyl radical, gave substantially larger amounts of the
decarboxylated product than alpha-cyanobenzyl benzoate,
which produced the unstable phenyl radical.

The photodegradation of fenvalerate in water and on
soil was investigated using compounds labelled with ¹⁴C
at the following positions: carbonyl group (CO-fenval-

----------------------------------------------------------------
^a The numbers in brackets following chemical names refer to the
numbers given in Fig. 2.

erate), alpha-carbon in the benzyl group (Calpha-fenvale-
rate), and cyano group (CN-fenvalerate) [118]. On exposure
to sunlight, fenvalerate in very dilute solution in distil-
led water, in 2% aqueous acetone, in filter-sterilized
river water, or in sea water underwent rapid photolysis
with half-lives of approximately 4 days in summer and 13-
15 days in winter. The quantum yield was calculated at
6.6 x 10^-3 (at 313 nm in water) and the half-life of dis-
appearance at latitude 40°N was calculated at 4.1 days in
summer and 12.4 days in winter, values which were close to
the experimental ones. Photodegradation of ¹⁴CN-fenval-
erate resulted in the formation of greater amounts of
¹⁴CO₂ than ¹⁴CN-. After 6 weeks irradiation, ap-
proximately 30% (in aqueous acetone or river water) or
approximately 55-60% (in distilled water or sea water) of
the ¹⁴C was recovered as ¹⁴CO₂, while the correspond-
ing figures for ¹⁴CN- were 5% and 30%. One of the major
photodegradation products was decarboxy-fenvalerate (31),
which increased to approximately 20% (in distilled water)
in summer after 1 week and decreased thereafter. In win-
ter, the amount was approximately 20% after 6 weeks. Other
major products were PBacid (22) and CPIA (17), derived
from the ester bond cleavage, amounting to 43% and 58%,
respectively, of the applied radioactivity after 6 weeks
in winter. In addition, small amounts of alpha-carbamoyl-
3-phenoxybenzyl-2-(4-chlorophenyl)-3-methylbutyrate (33)
(CONH₂-fenvalerate), alpha-carboxy-3-phenoxybenzyl-2-(4-
chlorophenyl)-3-methylbutyrate (34) (COOH-fenvalerate), 3-
phenoxybenzyl cyanide (28), 3-phenoxyphenylacetamide (29),
3-phenoxyphenylacetic acid (30), PBalc, and PBald were
detected.

Fenvalerate, as a deposit (5.5-5.9 µg/100 cm²) on
Kodaira light clay, Azuchi sandy clay loam, and Katano
sandy loam soil from Japan, was decomposed by autumn sun-
light with the respective half-lives of 2, 6, and 18 days
[118]. The major product was CONH₂-fenvalerate (33),
which amounted to 7.9-25.7% of the applied radioactivity
after 10 days; it was formed in greatest amounts in sun-
light but also formed in the dark. Smaller amounts of
decarboxy-fenvalerate (31), the desphenyl analogue of
CONH₂-fenvalerate (35), COOH-fenvalerate (34), PBacid,
and PBalc were also detected. Of the applied radiocarbon,
3-10% remained unidentified.

4.3 Decomposition in Plants

Fenvalerate (2.4% emulsifiable concentrate (EC)),
permethrin (2% EC), and deltamethrin (25 g/litre) were
sprayed onto cotton fields in Arizona, USA, at respective
rates of 0.11, 0.11, and 0.23 kg/ha, and dislodgeable
residues of the insecticides on cotton foliage were exam-
ined. Of the original deposits of fenvalerate, 65%
remained at the end of 96 h (there were two rains between
24 and 48 h), compared with 47% and 32% for permethrin and
deltamethrin, respectively [57].

Fenvalerate deposits on cotton plants (0.8 mg/plant)
disappeared rapidly, with only half the material remaining
after 8 days of exposure. After 23 days, decarboxy-fenval-
erate and ester-cleavage products such as PBacid, PBald,
PBalc, and CPIA were detectable, but not quantifiable.
Decarboxy-fenvalerate was considerably more stable to UV
light than fenvalerate, but it decomposed at a somewhat
faster rate than p,p'-DDT, yielding mainly the dechlori-
nated analogue [78].

The metabolism of fenvalerate in kidney bean plants
has been studied under laboratory conditions by Ohkawa et
al. [136]. Fenvalerate labelled with ¹⁴C at the cyano
group and the [2S, alphaRS] isomer labelled separately at
the cyano, carboxy, and benzylic carbon atoms were used to
treat individual bean leaves of 14-day-old seedlings at a
rate of 10 µg per leaf. After 60 days, 85-86% of the
applied ¹⁴C was recovered from plants treated with the
carboxy and benzyl labels, whereas 67% was recovered from
plants treated with the cyano label. Only limited translo-
cation was observed and only very low levels of radioac-
tive residues (2-9 µg/kg) were detected in seeds.
Fenvalerate and the [2S, alphaRS] isomer disappeared at a
similar rate from the treated leaves with an initial half-
life of 14 days.

The metabolism of racemic fenvalerate and of its
[2S, alphaS] isomer was examined in cabbage plants grown
under laboratory conditions and treated (20 µg per leaf)
with [¹⁴C]-chlorophenyl- and [phenyl-¹⁴C]-benzyl-labelled
preparations of the two compounds. Both compounds disap-
peared from the treated leaves with similar half-lives of
approximately 12-14 days. They underwent ester cleavage
to a significant extent, together with some hydroxylation
at the 2- or 4-position of the phenoxy ring and hydrolysis
of the nitrile group to amide and carboxyl groups. Most of
the carboxylic acids and phenols thus produced occurred as
glycoside conjugates. In a separate experiment, the uptake
and metabolism of CPIA (17) was examined in the laboratory
using abscised leaves of kidney bean, cabbage, cotton, cu-
cumber, and tomato plants. The acid (17) was found to be
readily converted, mainly into glucose or 6-O-malonylglu-
cose esters in kidney bean, cabbage, and cucumber, into
glucosylxylose, sophorose, and gentiobiose esters in
cotton, and into two types of triglucose esters with dif-
fering isomerism in tomato. One of the acetyl-derived
glucoside conjugates was identical with the authentic
deca-acetyl derivative of the [1-6]-triglucose ester
[121].

In studies by Ohkawa et al. [136], fenvalerate was
metabolized or degraded in bean plants via several routes.
A minor route was hydrolysis of the cyano group leading to
the formation of the amide (33) and carboxylic acid (34)
derivatives of fenvalerate. The 3-phen-oxybenzyl moiety

underwent metabolism to yield PBacid, 3-(2'-hydroxy-
phenoxy)benzoic acid (23) and PBalc, which occurred mainly
as sugar conjugates. In addition, glucoside conjugates
of alpha-carboxy-3-phenoxybenzyl alcohol (36) were detected
to a lesser extent. The presence of alpha-cyano-3-phenoxyben-
zyl alcohol (16) conjugates was inferred since PBald was
released upon treatment with beta-glucosidase. A major
metabolite of the acid moiety was CPIA (17), which also
occurred mainly as glucoside conjugates. The decarboxy
derivative (31) of fenvalerate, presumably formed by
photochemical reaction on plant foliage as discussed pre-
viously, was detected in leaf extracts. When bean plant
seedlings were planted and left for 30 days in light clay
and sandy loam soils treated with ¹⁴C-fenvalerate at
1 mg/kg, the roots retained fairly large amounts of radio-
carbon. However, only limited radiocarbon was found in
the shoots (0.02 mg/kg), pods and seeds (0.01 mg/kg), and
there was no parent compound in the shoots.

Additional studies were carried out to investigate the
fate of 3-phenoxybenzoic acid (an important metabolite of
fenvalerate and most other pyrethroids) in plants. Using
abscised leaves of cabbage, cotton, cucumber, kidney bean
and tomato plants, ¹⁴C-3-phenoxybenzoic acid was shown to
conjugate with a complex range of sugars [120].

4.4 Decomposition in Soils

The degradation of fenvalerate in soils has been
studied under various conditions (aerobic or anaerobic
conditions, laboratory or field conditions, using radioac-
tive or non-radioactive material).

Samples of ¹⁴C-fenvalerate labelled separately in the
carboxy and cyano groups were used for soil studies by
Ohkawa et al. [133]. When several types of soil were
treated at a rate of 1 mg/kg and stored at 25°C under
aerobic conditions, the initial half-life of fenvalerate
ranged from 15 days to 3 months. As with other
pyrethroids, hydrolysis at the ester linkage was a major
degradation route, and ring hydroxylation in the 4'-pos-
ition (25), together with hydrolysis of the cyano group to
the amide and carboxyl groups, occurred to smaller ex-
tents. The degradation route unique to fenvalerate was
ether-bond cleavage yielding alpha-cyano-3-hydroxybenzyl-
1-2-(4-chlorophenyl)-3-methylbutyrate (14), which could be
produced through hydroxylation at the 2'7-position (13) in
the alcohol moiety. No H¹⁴CN released during ester-bond
cleavage was detected owing to its rapid conversion to
¹⁴CO₂. The amount of ¹⁴CO₂ was greater with the
cyano label than the carboxy label. For example, after
30 days in Katano sandy loam soil, 47.5% and 38.2% of the
applied radiolabel was evolved as ¹⁴CO₂ from the cyano
and carboxyl groups, respectively. In a laboratory soil-
leaching study, less than 1% of the applied radiocarbon
appeared in the effluent when leaching was started

immediately after treatment of the soil. Even after a
30-day incubation, only a trace amount of CPIA (17) was
detected in the effluent from soil columns treated with
¹⁴C-carbonyl-fenvalerate. In a separate experiment, the
degradation of ¹⁴C-fenvalerate was studied in a soil-
nutrient liquid suspension system. Separate cultures of
bacteria and fungi were used for the system. After 2 weeks
of incubation, larger amounts of ¹⁴CO₂ (35-42% of the
applied radiolabel) were formed from both culture media
when the ¹⁴CN-labelled compound was used than when the
¹⁴CO-labelled compound was used (1.1-2.3%). In the
latter case, the main degradation product was CPIA, which
amounted to 34-69% [133].

Studies using ¹⁴C-fenvalerate, labelled separately in
the chlorophenyl and benzyl groups, confirmed the degra-
dation pathways mentioned above. These studies also showed
that the labelled aromatic rings were also readily de-
graded to ¹⁴CO₂ (up to 66%). In addition, it was found
that any "bound residues" formed could be further de-
graded to ¹⁴CO₂ by admixture with fresh soils [119].

The rate of degradation of the individual isomers of
fenvalerate has been investigated. In one soil, the half-
lives of the RR, RS, SR, and SS isomers were shown to be
178, 89, 155, and 108 days, respectively [105]. Different
rates for the various isomers were similarly obtained in
loam and sandy loam soils [160].

Under flooded conditions fenvalerate degrades more
slowly than under aerobic conditions. In sterile soil,
degradation is minimal, indicating that microbial activity
is the major cause of this degradation [102]. Ohkawa et
al. [133] reported similar findings.

Studies in which crops were sown in soils containing
aged residues of ¹⁴C-fenvalerate (aging periods of 30,
120, and 345 days) showed that residues from fenvalerate
should not carry over into rotated crops [102].

The persistence of fenvalerate in Lethbridge (Canada)
soil has been studied under field and laboratory con-
ditions [74]. Formulated fenvalerate (30% emulsifiable
concentrate) was applied once to soil microplots in the
field at a dose rate of 600 µg/plot (150 g/ha) or to
soil in pots at a dose of 88.7 µg/pot (10 g/ha). The
treated pots were maintained at a daily temperature regime
of 20°C for 16 h and 10°C for 8 h in the environmental
chamber. Fenvalerate was found mainly in the top 2.5 cm
of the field soil, and 16 weeks later, 15% of the applied
fenvalerate remained. The initial half-lives were 5.9
weeks for the [2S, alphaR] [2R, alphaS] enantiomeric pair
and 6 weeks for the [2R, alphaR] [2S, alphaS] pair. The
spring soil samples, taken 45 weeks after application, con-
tained 11% of the total fenvalerate. Limited degradation
occurred during the winter. The degradation of fenvalerate

in soil incubated in the environmental chamber was similar
to the field results. The [2S, alphaR] [2R, alphaS] enant-
iomeric pair had a half-life of 5 weeks while the [2R,
alphaR] [2S, alphaS] pair had a half-life of 5.3 weeks.
These results were comparable to the average half-life of
7 weeks for fenvalerate incubated in British Columbia soils
[198].

In studies by Harris et al. [69], the persistence of
fenvalerate in subtropical field soil (average soil tem-
perature, 20-30°C) was investigated after applying 20%
emulsifiable concentrate at a rate of 1 kg active ingredi-
ent (ai)/ha twice a year (spring and autumn) over a 2.5-
year period. Residues in the top 15 cm of soil were moni-
tored for up to one year after the final application.
Fenvalerate levels declined rapidly after the spring
application and relatively slowly after the autumn appli-
cation. There was no carry over of the insecticide from
year to year, and after 2.5 years of application only 2%
of the total fenvalerate remained. The rate of disappear-
ance became slightly slower when fenvalerate application
ceased [181]. The degradation of fenvalerate (14.9 mg/kg)
in plainfield sand (5% moisture) at 25°C was relatively
slow, with an initial half-life of 2 months, as compared
with initial half-lives of 0.5, 1, and 2 months for
fenpropathrin (7.1 mg/kg), permethrin (8.8 mg/kg), and
cypermethrin (7.3 mg/kg), respectively, under laboratory
conditions.

A 2-year field study on the relative persistence of
permethrin, cypermethrin, fenpropathrin, and fenvalerate
in soils was carried out by Chapman & Harris [25]. The
pyrethroids were applied as emulsifiable concentrates at a
rate of 280 g ai/ha or 140 g ai/ha to duplicate plots in
Ontario, Canada, containing either sand or organic soil.
For plots treated at the higher rate, the insecticide was
immediately raked into the soil, while the plots receiving
the lower rate were left undisturbed and the upper 4-5 cm
of soil was subjected to gas-liquid chromatography (GLC)
analyses. The concentrations of the four pyrethroids
incorporated in both soils or remaining on the upper soil
layer decreased to less than 50% of the initial values
within one month. Again, fenvalerate was slightly more
persistent, with 7% of the initial application remaining
in organic soil 28 months after treatment.

Reed et al. [157] demonstrated that when fenvalerate
was applied to soil, adsorption prevented significant
leaching of the pesticide. Soil metabolites produced
either by photolytic or microbial degradation did not
accumulate to a significant level or present a problem in
subsequent rotation crops (lettuce, beets, and wheat)
planted at 30 days, 60 days, 120 days, or 1 year after
soil treatment. Although fenvalerate has intrinsically

high toxicity to a variety of aquatic organisms, these
field studies demonstrated that the toxicant was unavail-
able to non-target organisms. Therefore, it had little or
no impact in this test system following its use at the
maximum allowed rate of 2.24 kg/ha per year.

4.5 Decomposition in Water

The hydrolysis of racemic fenvalerate in buffered
aqueous solutions at pH 5.0, 7.0, and 9.0 was compared by
Katagi et al. [90] with that of the [2S, alphaS] isomer.
Both compounds were fairly stable at pH 5.0 and 7.0 (half-
lives of 130-220 days), while at pH 9.0 they underwent
hydrolysis (half-lives of 64.6-67.2 days) mainly via ester
bond cleavage. The main product was 2-(4-chlorophenyl)-3-
methylbutyric acid (17), which amounted to 14.9% of the
applied ¹⁴C after 28 days. As the [2S, alphaS] isomer
underwent alphaS/alphaR epimerization in the alcohol moiety
at pH 7.0 and 9.0, its rate of hydrolysis appeared to be
rather faster than that of fenvalerate. However, the half-
life estimated from the total amounts of [2S, alphaS] and
[2S, alphaR] epimer was close to that of fenvalerate, which
indicates no significant difference in hydrolysis rate.

The persistence of fenvalerate has been evaluated
in water and sediment contained in open trenches
(3 m x 1 m x 30 cm) lined with alkathene sheet [1]. Insec-
ticide emulsion was sprayed on the surface of the water at
the normal rate and at twice the recommended dosage. The
dissipation of the insecticide from water was rapid. About
74-80% of the pesticide was lost within 24 h at both ap-
plication rates. However, residues were found to be ad-
sorbed onto sediment, and these persisted beyond 30 days.

In soil, persistence was moderate, lasting around
30 days.

5. KINETICS AND METABOLISM

Appraisal

The metabolic fate of fenvalerate in rats, mice, and cows
has been studied using variously labelled racemic fenvalerate
(acid moiety or benzyl or cyano groups labelled).

From oral administration studies, fenvalerate appears to be
absorbed rapidly through the gastrointestinal wall.

Following a single oral administration of labelled fenval-
erate to rats, the excretion of radiocarbon from the acid or
benzyl moieties was fairly rapid. However, the excretion of
radiocarbon originating from the cyano group was relatively
slow, the rest of the radioactivity being retained in various
tissues, particularly in hair and stomach as thiocyanate. The
major routes of metabolism were ester cleavage, hydroxylation
at the 4'position of the alcohol moiety, and thiocyanate
formation from the cyano group. Major metabolites were 2-(4-
chlorophenyl)isovaleric acid (Cl-Vacid) and 3-OH-Cl-Vacid (Cl-
Vacid hydroxylated at the 3 position) from the acid moiety, and
the sulfate conjugate of 3-(4'-hydroxyphenyl)benzoic acid and
thiocyanate from the alcohol moiety. A lipophilic metabolite,
cholesteryl-[2R]-2-(4-chlorophenyl)isovalerate, which was related
to granuloma formation, was detected in the adrenals, liver,
and the mesenteric lymph nodes of rats, mice, and some other
species. The excretion of fenvalerate in the milk from orally
dosed cows was very low (0.44-0.64% of the total dose).

The metabolic fate of fenvalerate in mammals is sum-
marized in Fig. 3.

5.1 Metabolism in Mammals

5.1.1 Rat

Following the single oral administration of fenval-
erate, labelled with ¹⁴C in the carbonyl of the acid
moiety (¹⁴CO) and the benzylic carbon (¹⁴Calpha), to
male rats (7-30 mg/kg body weight), the radiocarbon from
the acid and alcohol moieties was rapidly and completely
excreted [86, 134]. The tissue residues were generally
very low, except for those in the fat. The total recovery
of ¹⁴C in urine, faeces, and expired air was 93-99% in
6 days. However, on dosing with ¹⁴CN-labelled fenval-
erate, the radiocarbon derived from the CN group was
excreted relatively slowly into the urine and faeces, and
a considerable amount (10%) of the radiocarbon was also
excreted as CO₂. Total recovery of ¹⁴C in urine,
faeces, and expired air was 75-81% in 6 days in this case.
The tissue residue levels were generally higher than those
from the acid and alcohol moieties. Hair, skin, and

stomach contents showed high residue levels, due to reten-
tion as ¹⁴C-thiocyanate. These excretion and tissue resi-
due patterns for the radiocarbon from the CN group were
similar to those with ¹⁴C dosed as KCN and KSCN in male
rats [134].

It was shown in the same study that fenvalerate under-
went oxidation at the 2'and 4'positions of the alcohol
moiety, as well as at the 2 and 3 positions of the acid
moiety, ester cleavage, and the conjugation of resultant
phenols and carboxylic acids with glucuronic acid, sul-
furic acid, and glycine. Cleavage of fenvalerate and its
ester metabolites appeared to release cyanohydrins, which
were, however, unstable under physiological conditions and
decomposed easily to cyanide and aldehydes (Fig. 3). The
cyanide ion was converted mainly to thiocyanate and
CO₂, and 2-iminothiazolidine-4-carboxylic acid, a metab-
olite detected with other pyrethroids containing a cyanide
group, was not positively identified [134]. The major fae-
cal metabolites from ¹⁴CO-, ¹⁴Calpha-, and ¹⁴CN-fenval-
erate were unchanged fenvalerate (5) and two ester metab-
olites of 2'-hydroxy-(13) and 4'-hydroxy-fenvalerate (25).
The major metabolites in 0- to 2-day pooled urine (50-55%
of the dosed radioactivity) from the acid-labelling were

2-(4-chlorophenyl)isovaleric acid (17) (Cl-Vacid), 2-(4-
chlorophenyl)-3-hydroxymethylbutyric acid (37) (3-OH-Cl-
Vacid), and its lactone (38) (3-OH-Cl-Vacid-lactone).
Other minor metabolites were 2-(4-chlorophenyl)-2-hydroxy-
3-hydroxymethylbutyric acid (39) (2,3-OH-Cl-Vacid) in the
free, the lactone (40) (2,3-OH-Cl-Vacid-lactone), and the
conjugated forms, 2-(4-chlorophenyl)- cis-2-butenedioic
acid anhydride (41) (Cl-BDacid anhydride), and 2-(4-
chlorophenyl)-3-methyl-2-butene-4-olide (42) (Cl-B-acid-
lactone). On the other hand, the predominant urinary
metabolite from the alcohol moiety was the sulfate conju-
gate of 3-(4'-hydroxyphenoxy)benzoic acid (23) (4'-OH-
PBacid), accounting for approximately 40% of the dose.
Other major metabolites were 3-phenoxybenzoic acid (22)
(PBacid) in the free (6%), the glucuronide (2%), and the
glycine (2%) conjugated forms, 4'-OH-PBacid in the free
(5%) and the glucuronide (2%) forms, and the sulfate of 3-
(2'-hydroxyphenoxy)benzoic acid (24) (2'-OH-PBacid) (3%).
With ¹⁴CN-fenvalerate, the major urinary metabolite was
thiocyanate (43) [134].

Pydrin insecticide (Y-rich) is an isomerically
enriched form of fenvalerate containing an excess ratio of
the active diastereomers SS and RR (designated Y) over the
less active diastereomers RS and SR (designated X) at a
ratio of approximately 85:15. Fenvalerate contains Y:X in
a ratio of 45:55. Following a single oral dose of the Y-
rich insecticide (8.4 mg/kg) to male and female Sprague-
Dawley rats, more than 90% of the administered radioac-
tivity from the acid moiety (chlorophenyl-¹⁴C) and the
alcohol moiety (phenoxyphenyl-¹⁴C) was eliminated within
the first 24 h. There was no major difference between the
two different fenvalerate preparations in either the elim-
ination rate or the metabolites distribution profile.
Cleavage of the ester linkage was the primary metabolic
pathway. The acid and alcohol portions of the parent mole-
cule underwent hydroxylation, oxidation, and conjugation.
These metabolic reactions were not dependent on the iso-
meric composition of the test material. Tissue residue
data showed that ¹⁴C residues were not retained in the
various organs [104].

The fate of sugar conjugates, which may be formed as
plant metabolites, has been investigated by Mikami et al.
[122]. Upon single oral administration to male Sprague-
Dawley rats at a concentration of 3.8 mg/kg, the mono-,
di-, and tri-glucose conjugates of [¹⁴C]-3-phenoxybenzyl
alcohol (19) and the mono-glucose conjugate of [¹⁴C]-3-
phenoxybenzoic acid (22) were rapidly hydrolysed and
extensively eliminated in the urine, mostly as the sulfate
conjugate of 3-(4-hydroxyphenoxy)benzoic acid (24).
Faecal elimination was a minor route, whereas biliary
excretion was responsible for about 42% of the dose, and
the glucuronide conjugates of (19), (22), and (24) were
common major metabolites. The biliary glucuronides were
metabolized in the small intestine to the respective

aglycones, which were reabsorbed, metabolized further, and
excreted in the urine as the sulfate conjugate of (24).
Although small amounts of the mono-, di-, and tri-gluco-
sides were found in the 30-min blood and liver samples
following oral administration of the tri-glucoside of
(19), they were not detected in the urine, bile, or fae-
ces. Similarly, the sulfate conjugate was one of the major
urinary metabolites in germ-free male rats, when dosed
with the ¹⁴C-glucosides at a rate of 9 µmol/kg via the
oral or intraperitoneal route, although certain amounts
were excreted unchanged in the urine and faeces. The glu-
cose conjugates were metabolized in vitro by intestinal
microflora and in various rat tissues including blood,
liver, small intestine, and small intestinal mucosa. The
tissue enzymes showed a different substrate specificity in
hydrolysing the glucosides. However, they were not metab-
olized in gastric juice, bile, pancreatic juice, or
urine.

5.1.2 Mouse

In mice, fenvalerate is metabolized in a similar way
to that in rats, but the following significant species
differences were found by Kaneko et al. [86]: (a) the
taurine conjugate of PBacid was found in mice but not in
rats; (b) 4'-OH-PBacid sulfate occurred to a greater
extent in rats than in mice; and (c) a greater amount of
thiocyanate was excreted in mice than in rats. No sig-
nificant sex differences were observed in rats and mice.
The metabolism of the stereoisomers of fenvalerate,
([2S, alphaRS] and [2S, alphaS]) was apparently similar to
that of racemic fenvalerate.

Following a single oral administration of the four
chiral isomers of [¹⁴C-chlorophenyl]-fenvalerate to
Sprague-Dawley rats and ddY mice (2.5 mg/kg body weight),
the [2R, alphaS] isomer showed, in both rats and mice, rel-
atively greater residues in the analyzed tissues (except
fat), particularly in adrenal glands, compared with the
other three isomers. Similarly, this isomer showed
higher tissue concentrations than the other isomers when
mice were fed a diet containing 500 mg/kg of the
[2S, alphaS], [2R, alphaS], or [2R, alphaR] isomers for
two weeks. The greater amount of radioactive residues from
the administration of [2R, alphaS] isomer, as compared
with those of other isomers, was explained by the
preferential formation of a lipophilic metabolite from the
[2R, alphaS] isomer found in all examined tissues, which
was not easily excreted. The amounts of the lipophilic
metabolite differed among tissues, being higher in adrenal,
liver, and mesenteric lymph nodes. This metabolite was
identified as cholesteryl [2R]-2-(4-chlorophenyl)isoval-
erate. The presence of the same metabolite was also indi-
cated in rat tissues [87].

5.1.3 Domestic animals

Two 3-month-old lambs were fed a diet containing
45 mg/kg fenvalerate for 10 days and then killed to deter-
mine the concentrations of fenvalerate in the kidney,
liver, leg muscle, and renal fat [210]. Among the analyzed
tissues, fat showed the highest fenvalerate level (3.6-4.4
mg/kg dry weight) while other tissues contained less than
0.3 mg/kg. Fenvalerate gave two gas chromatographic peaks
and each peak contained a pair of its enantiomers. In all
cases, the ratio of the areas of these peaks (peak 1
(RS,SR)/peak 2 (SS,RR)) was 1.08 both for fenvalerate in
the diet and for fenvalerate recovered from the fortified
control fat. In contrast, the fenvalerate isolated from
lamb fat had a peak area ratio of 0.76-0.78. Thus, one or
both of the first eluting enantiomers appeared to be
metabolized more rapidly than the other enantiomers.

In a study by Wszolek et al. [209], two Holstein cows
were fed fenvalerate at 5 and 15 mg/kg diet for 4 days and
were then given a clean diet for 6 days. Total excretion
of fenvalerate in milk amounted to 0.44 and 0.64% of the
total dose for the 5 and 15 mg/kg levels, respectively,
whereas about 25% of the dose was eliminated in the
faeces.

A lactating Holstein cow was fed grain fortified with
227 mg fenvalerate daily for 4 days and the urine was ana-
lysed. Intact fenvalerate was not detected in any samples
of the urine excreted by the cow during the 10-day feeding
study, nor was the acid metabolite (Cl-Vacid) (17) ident-
ified. The in vitro study on fenvalerate degradation in
rumen fluid indicated that no significant degradation of
fenvalerate was observed during the 6-h incubation [211].

Saleh et al. [161] gave a single oral dose of fenval-
erate (10 mg/kg body weight) to chickens and monitored the
persistence and distribution of the insecticide over 15
days. A concentration of 4.7 mg/litre in blood after 24 h
fell to 0.05 mg/litre after 7 days. Levels in other tis-
sues reached maxima of less than 1.0 mg/kg and fell rap-
idly. However, brain residues rose to a level of 4.0 mg/kg
over 7 days and persisted for the 15 days of the exper-
iment. Concentrations in eggs reached a maximum of
0.3 mg/kg yolk after 4 to 5 days, and a maximum of
0.24 mg/kg egg white. By day 6, levels had returned to the
pre-dosing level.

5.2 Enzymatic Systems for Biotransformation

The [2R, alphaRS] isomer of fenvalerate has been found
to be more rapidly hydrolysed by mouse liver esterase than
the [2S, alphaRS] isomer, but less rapidly metabolised than
the [2R, alphaRS] isomer with an oxidase system. A similar
correlation was observed with the [2S] and [2R] isomers of
S-5439 (3-phenoxybenzyl-2-(4-chlorophenyl)isovalerate) [165].

In an in vitro study on the metabolism of the four
chiral isomers of fenvalerate using homogenates from vari-
ous tissues of mice, rats, dogs, and monkeys, only the
[2R, alphaS] isomer yielded cholesteryl-[2R]-2-(4-chloro-
phenyl)isovalerate (CPIA-cholesterol ester) as a major
metabolite. Mouse tissues exhibited a higher rate of CPIA-
cholesterol ester formation than those of other animals.
Of the mouse tissues tested, the kidney, brain, and spleen
showed the greatest ability to form this ester, the rel-
evant enzyme activity being mainly localized in the
microsomal fractions. Carboxyesterases for mouse kidney
microsomes hydrolyzed the [2R, alphaS] isomer only of
fenvalerate to give CPIA and yielded the corresponding
cholesterol ester in the presence of artificial liposomes
containing cholesterol. It appears that the CPIA-
cholesterol ester resulted from the stereoselective
([2R, alphaS] only) formation of the CPIA-carboxyesterase
complex, which subsequently reacted with cholesterol to
yield the CPIA-cholesterol ester [128].

Hydrolysis of the four chiral isomers of fenvalerate
by microsomes of various mouse tissues has been investi-
gated by Takamatsu et al. [180]. The kidney, spleen and
brain hydrolyzed only the [2R, alphaS] isomer. Liver hydro-
lyzed the [2R, alphaS] and [2R, alphaR] isomers to a great-
er extent than the [2S, alphaR] and [2S, alphaS] isomers,
while plasma hydrolysed the [2S, alphaR] and [2R, alphaR]
isomers more rapidly than the [2S, alphaS] and [2R, alphaS]
isomers. The stereoselectivity of hydrolysis of the four
isomers by mouse liver microsomes was found to be same as
that in vivo. Of the four isomers, the [2R, alphaS] isomer
alone was transformed to cholesteryl-[2R]-2-(4-chlorophenyl)
isovalerate (CPIA-cholesterol ester) by microsomes of the
brain, kidney, spleen, or liver but not by plasma. The
rate of CPIA-cholesterol ester formation was lower in the
liver than in other tissues. The optimum pH (7.4-9.0) for
the formation of this ester was nearly the same as that
for hydrolysis of the [2R, alphaS] isomer to form CPIA in
mouse kidney microsomes.

The substrate specificity of microsomal carboxyester-
ase(s) responsible for the formation of cholesteryl-[2R]-
2-(4-chlorophenyl)isovalerate from fenvalerate was inves-
tigated by incubating mouse kidney microsomes with ¹⁴C-
cholesterol and fenvalerate or its analogues. Of the four
isomers of fenvalerate, only the [2R, alphaS] isomer yielded
a cholesterol ester. This specificity of cholesterol ester
formation was the same as that in the in vivo study. Some
of the fenvalerate analogues also produced similar choles-
terol esters. Steroids other than cholesterol were also
investigated as acceptors of the acid moiety of the
[2R, alphaS] isomer by incubating egg lecithin and several
steroids with the [2R, alphaS] isomer in the presence of
solubilized carboxyesterase(s). Dehydroisoandrosterone and
pregnenolone reacted with the [2R, alphaS] isomer to give the
corresponding ester conjugates [88].

One or more carboxyesterases located in the soluble
fraction of mouse brain homogenates hydrolyzed several
pyrethroid esters with a substrate specificity different
from that of the hepatic esterases. In particular,
fenvalerate and fluvalinate were hydrolyzed by brain
esterases at rates equal to or greater than that measured
for trans-permethrin. The results suggest that hydrolysis
in the brain may contribute to the detoxication of some
pyrethroids in mammals [64].

6. EFFECTS ON ORGANISMS IN THE ENVIRONMENT

The acute toxicity data of fenvalerate to aquatic and
terrestrial non-target organisms are summarized in Tables
5, 6, and 7.

6.1 Aquatic Organisms

6.1.1 Toxicity to aquatic invertebrates

Non-target invertebrates, except molluscs, are more
susceptible to the insecticide than fish, the LC₅₀
ranging from 0.08 to 2 µg/litre.

Fenvalerate is relatively non-toxic to oysters and
algae (LC₅₀ >1000 µg/litre) over short exposure periods.
Snails (Heliosoma trivolvis) exposed for 28 days to 0.79
µg/litre, the highest concentration tested, showed no
change in behaviour or survival [4].

Day & Kaushik [32] conducted short-term toxicity
tests on three species of cladoceran and one species of
calanoid (Diaptomus oregonensis). The 48-h LC₅₀ values
for daphnids were: 2.52 µg/litre for adult Daphnia magna,
0.83 µg/litre for D. magna aged 48 h (or less);
0.29 µg/litre for adult Daphnia galeata mendotae;
0.21 µg/litre for adult Ceriodaphnia lacustris; 0.16
µg/litre for D. galeata mendotae aged 48 h (or less).
Diaptomus oregonensis was the most sensitive species with
a 48-h LC₅₀ of 0.12 µg/litre. No toxicity was found with
the emulsifiable concentrate from which fenvalerate was
omitted (EC control). Rates of filtration of algae were
reduced at sub-lethal concentrations of fenvalerate.
Ceriodaphnia lacustris was the most sensitive species,
with rates of filtration significantly decreased at
fenvalerate concentrations of 0.01 µg/litre. Rates of
assimilation of algae were decreased at fenvalerate con-
centrations of 0.05 µg/litre or more.

Day & Kaushik [33] conducted life-cycle studies on the
toxicity of fenvalerate to Daphnia galeata mendotae.
Lifetable methods were used to generate statistical
comparisons between treatments. At a concentration of
0.005 µg/litre, fenvalerate increased the longevity of
the daphnids significantly from 37.6 to 51.6 days. How-
ever, at the same concentration, production of young was
decreased. Higher concentrations of fenvalerate caused
reduced survival of the adults. The intrinsic rate of
natural increase in the population was reduced at a con-
centration of 0.5 µg/litre. At 0.01 µg/litre, the net
reproductive rate decreased from 126 to 73 offspring per
female and the generation time from 20.3 to 17.3 days.

Table 5. Acute toxicity of fenvalerate to non-target freshwater organisms
--------------------------------------------------------------------------------------------------------------------------------------------
Species Size^a Parameter Toxicity Formu- System^c Temperature pH Hardness^d Reference
(µg/litre) lation^b (° C)
--------------------------------------------------------------------------------------------------------------------------------------------
Arthropods
Gammarus pseudolimnaeus adult-juv 96-h LC₅₀ 0.03 T F 15 7.6-7.8 46-48 4
Gammarus pseudolimnaeus 1-3 mm, juv 96-h LC₅₀ 0.05 T R 17 7.6-7.8 46-48 4
Waterflea 1st instar 96-h LC₅₀ 0.032 T S 17 7.4 44 115
(Daphnia magna)
Midge 3rd instar 48-h LC₅₀ 0.43 T S 22 7.4 44 115
(Chironomus pulmosus)
Mayfly larva 9-day LC₅₀ 0.08 T F 15 7.6 46-48 4
(Ephemerella sp.)
Rhagionid fly larva 28-day LC₅₀ 0.03 T F 15 7.6-7.8 46-48 4
(Atherix)
Stonefly naiad 72-h EC₅₀ 0.13 T F 15 7.6-7.8 46-48 4
(Pteronarcys dorsata)
Stonefly 3-6 weeks old 96-h LC₅₀ 1.9 EC S 20-22 7.8 7% 107
(Nitocra spinipes)

Fish
Atlantic salmon 6.2 cm, 5.3 g 96-h LC₅₀ 1.2 T R 10 110
(Salmo salar)
Rainbow trout 5-6 cm 48-h LC₅₀ 3.0 EC S 12-25.5 129
(Salmo gairdneri)
Rainbow trout 6 cm, 3 g 24-h LC₅₀ 76 T S 10 7.5 110 28
(Salmo gairdneri)
Rainbow trout 6 cm, 3 g 24-h LC₅₀ 21 EC S 10 7.5 110 28
(Salmo gairdneri)
Mosquitofish 4-5 cm 48-h LC₅₀ 15.0 EC S 8.8-16 129
(Gambusia affinis)
Mosquitofish 3-days old 72-h LC₅₀ 2.6 T S 24-27 124
(Gambusia affinis)
Desert pupfish 4-5 cm 48-h LC₅₀ 25.0 EC S 11-16.6 129
(Cyprinodon macularis)
Tilapia mossambica 5-6 cm 48-h LC₅₀ 200.0 EC S 15-21.4 129
Bluegill sunfish adult 96-h LC₅₀ 0.76 T S 22 7.4 40 115
(Lepomis macrochirus)
Fathead minnow adult 96-h LC₅₀ 2.35 T S 22 7.1 49 115
(Pimephales promelas)
--------------------------------------------------------------------------------------------------------------------------------------------
^a juv = juvenile.
^b T = Technical, EC = Emulsifiable concentrate.
^c R = Renewal, S = Static, F = Flow-through.
^d expressed as mg CaCO₃ per litre.

Table 6. Acute toxicity of fenvalerate to non-target estuarine & marine organisms
---------------------------------------------------------------------------------------------------------------------------------------
Species Size^a Parameter Toxicity Formul- System^c Temper- pH Salinity Reference
(µg/litre) ation^b ature ^o/_oo
(° C)
---------------------------------------------------------------------------------------------------------------------------------------
Algae
Skeletonema costatum 96-h EC₅₀ > 1000 T 20 30 212
Isochrysis galbana 96-h EC₅₀ > 1000 T 20 30 212
Thalassiosira pseudonana 96-h EC₅₀ > 1000 T 20 30 212
Nitzschia angularum 96-h EC₅₀ > 1000 T 20 30 212

Molluscs
Eastern oyster 2-h larva 48-h EC₅₀ >
1000 T S 25 20 212
(Crassostrea virginica)

Arthropods
Lobster (Homarus americanus) 450 g 96-h LC₅₀ 0.14 T R 10 30 110
Shrimp (Crangon septemspinosa) 1.3 g 96-h LC₅₀ 0.04 T R 10 110
Shrimp (Mysidopsis bahia) 1-day juv 96-h LC₅₀ 0.021 T S 25 20 212
Shrimp (Mysidopsis bahia) newly hatched 96-h LC₅₀ 0.008 T F 25.4 25.3 163
Shrimp (Penalus duorarum) adult 96-h LC₅₀ 0.84 T F 24.8 24.9 163
California grunion 3-day larva 96-h LC₅₀ 0.29 T F 26 25 114
(Leuresthes tenuis)
California grunion juv 96-h LC₅₀ 0.60 T F 25 22 114
(Leuresthes tenuis)
Inland silverside 26-day larva 96-h LC₅₀ 1.00 T F 24 20 114
(Nenidia beryllina)
Tidewater silverside juv 96-h LC₅₀ 1.00 T F 25 20 114
(Menidia peninsulae)

Fish
Sheepshead minnow 28-day fry 96-h LC₅₀ 121 T S 25 20 212
(Cyprinodon variegatus)
Sheepshead minnow adult 96-h LC₅₀ 5 T F 30 26.5 163
(Cyprinodon variegatus)
Bleak (Alburnus alburnus) 8 cm 96-h LC₅₀ 2-3 EC S 10 7.8 7 107
Atlantic silverside adult 96-h LC₅₀ 0.31 T F 24.1 25 163
(Menidia menidia)
Striped mullet adult 96-h LC₅₀ 0.58 T F 25.9 25.8 163
(Mugil cephalus)
Gulf toadfish adult 96-h LC₅₀ 5.4 T F 30 24.8 163
(Opsanus beta)
---------------------------------------------------------------------------------------------------------------------------------------
^a juv = juvenile.
^b T = Technical, EC = Emulsifiable concentrate.
^c R = Renewal, S = Static, F = Flow-through.

Table 7. Acute toxicity of fenvalerate to non-target terrestrial organisms
-------------------------------------------------------------------------------------------------------------------------
Species Size Application Parameter Toxicity Temper- Reference
ature
(°C)
-------------------------------------------------------------------------------------------------------------------------
Bird
Broiler chicks 8-12 weeks old, oral LD₅₀ 12 590 (mg/kg) 31-32 155
0.99-2.2 kg
Hen oral LD₅₀ > 1500 (mg/kg) 123

Arthropods
Insect parasite
Ichneumoid adult male film 24-h LC₅₀ 1760 (ng/vial) 152
(Campoletis sonorensis)
Insect predators
Lacewing adult 2.74 mg topical LD₅₀ 4.3 (mg/kg) 15 176
(Austromicromus tasmaniae) larva 2.52 mg topical LD₅₀ 67 (mg/kg) 20 176
Lacewing (Chrysopa carnea) 3rd instar, topical 72-h ED₅₀ > 25 (mg/g) 28 164
larva 9.9-10 mg topical ED₅₀ ~ 1 (mg/g) 28 164
one generation
Lacewing (Chrysopa carnea) larva film LC₅₀ 0.073 (mg/vial) 25 151
5-6 days old

Beetle 11.2 mg topical LD₅₀ 0.38 (mg/kg) 15 164
(Coccinella undecimpunctata)
Earwig (Labidura riparia) mature soil 0.11 kg ai/ha mortality 6% 205
0.22 kg ai/ha mortality 25% 205
0.44 kg ai/ha mortality 50% 205
Honey bee (Apis mellifera) adult topical LD₅₀ 410 ng/bee - 5

Predaceous mite species
Amblyseius fallacis adult female slide dip method LC₅₀ 2.6 (mg ai/litre) 27 158
Amblyseius fallacis adult female slide dip method LC₅₀ 7.0 (mg ai/litre) 26 199
Typhlodromus pyri adult female slide dip method LC₅₀ 8.1 (mg ai/litre) 26 199
Typhlodromus occidentalis adult female slide dip method LC₅₀ 2.1 (mg ai/litre) 26 199
-------------------------------------------------------------------------------------------------------------------------
McKenney & Hamaker [109] exposed the estuarine grass
shrimp Palaemonetes pugio to fenvalerate, in a flow-
through system to maintain constant exposure, throughout
20 days of larval development. The study was conducted
under optimal salinity conditions (20 ^o/oo). A nominal
concentration of 3.2 ng/litre significantly reduced the
percentage of larvae successfully completing metamor-
phosis. Exposure to 1.6 ng/litre prolonged larval develop-
ment. Larvae were also found to be less capable of
responding successfully to osmotic stress after exposure
to fenvalerate at 0.1 or 0.2 ng/litre.

6.1.2 Toxicity to fish

Fenvalerate is toxic to fish, LC₅₀ values being
0.29-200 µg/litre (Tables 5 and 6). The LC₅₀ value for
rainbow trout obtained with an emulsifiable concentrate
was 3.6 times lower than that for the technical product
[28]. The toxicity of fenvalerate to adult bluegill sun-
fish (Lepomis macrochirus) was unaffected by changes in
water hardness and pH [115].

The acute toxicities (96-h LC₅₀) of fenvalerate to
juvenile steelhead trout were 172 ng/litre and 88
ng/litre, respectively, under continuous and intermittent
exposure (approximate peak concentration: 460 ± 40
ng/litre for 4.5 h). Prolonged intermittent exposure
(70 days) of the early life-stage resulted in marked
lethality (32%) and reduced terminal weight (50% of con-
trol) (mean concentration: 80 ng/litre, peak concen-
tration: 461 ng/litre). However, continuous exposure to
80 ng/litre for 70 days did not effect these parameters
[31].

Fenvalerate has narrow safety margins for fish
(LC₅₀ of fish : LC₅₀ of mosquito larvae is in the ratio
of 1:24) when the insecticide is used against mosquitoes
[129].

Four rainbow trout (Salmo gairdneri) died within 11
hours when exposed to 412 µg fenvalerate/litre. Visible
signs of poisoning included elevated cough rate, tremors,
and seizures. Ventilatory and cardiac activity stopped
during the seizures. Histopathological examination of
gill tissue showed damage consistent with irritation, and
Na⁺ and K⁺ excretion rates were elevated. Fenvalerate
concentrations in brain, liver, and carcass at death were
0.16, 3.62, and 0.25 mg/kg, respectively. The study
suggested that, apart from effects on the nervous system,
effects on respiratory surfaces and renal ion regulation
may be associated with fenvalerate toxicity in fish [15].

When sheepshead minnows (Cyprinodon variegatus) were
studied during 28 days for early-life-stage toxicity,
3.9 µg fenvalerate/litre significantly reduced the sur-
vival of hatched fish and 2.2 µg/litre reduced both
length and weight, but no effects were detected at
0.56 µg/litre [68].

6.1.3 Field studies and community effects

Caplan et al. [23] applied fenvalerate at concen-
trations of 0.2 and 1.0 mg/kg to sediment in a tidal marsh
sediment model ecosystem. No adverse effects were seen on
the heterotrophic microorganisms in the sediment after a
7-day exposure to either concentration. Plate counts to
assess numbers of organisms and measurements of substrate
degradation were not different from those of controls. The
half-life of fenvalerate was 6.3 days for the treatment at
0.2 mg/kg and 8.9 days at 1.0 mg/kg.

In the field, fenvalerate was applied to ponds at
rates of 28-112 g ai/ha as a mosquito larvicide [124].
Populations of plankton, crustaceans, and mayfly nymphs
decreased but recovered quickly. Corixids, notonectids,
and aquatic beetle populations decreased slightly and the
effects remained throughout the study. Chironomid larval
populations were suppressed and emergence was inhibited.
However, no deleterious effects were observed on rotifer
populations.

When fenvalerate was applied to ponds at rates of
11.2-56 g ai/ha for mosquito control, the insecticide
produced complete mortality of mayfly naiads [130]. A
single treatment by fenvalerate at 28 g/ha controlled
mosquito larvae for more than 7 days, and it also affected
populations of mayfly naiads, dragonfly naiads, and diving
beetle larva, but not ostracods or damselfly naiads
[131].

Studies into the effects of fenvalerate on estuarine
benthic communities were conducted in a flow-through
system for 8 weeks and 1 week for laboratory- and field-
colonized communities, respectively. Technical grade
fenvalerate (100%), dissolved in a stock solution con-
sisting of 15% acetone and 85% triethylene glycol, was
metered by syringe pump into, and mixed with, the sea
water entering the centre of the constant-head box of each
apparatus receiving fenvalerate. The same amount of
carrier solvent (10 ml/day, 5 mg/litre) was metered into
the control apparatus. Nominal concentrations of fenval-
erate in sea water were 0.01, 0.1, and 1.0 µg/litre.
Samples of water were taken from the constant-head boxes
once a week for chemical analyses for fenvalerate concen-
tration. Community structure was altered significantly in
both cases by fenvalerate at 0.1 or 1 µg/litre, but not

by 0.01 µg/litre. The groups most sensitive to the
insecticide were chordates (Branchiostoma caribaeum) and
amphipods, while annelids and molluscs tolerated concen-
trations up to 10 µg/litre [177].

Tagatz et al. [178] placed boxes containing sand,
either uncontaminated or contaminated (nominal concen-
tration of fenvalerate of 0.1, 1.0, or 10 mg/kg), in an
estuary for 8 weeks, and the community structure of
benthic organisms colonising the boxes was assessed. The
average number of species colonising the sand at the
highest treatment level was significantly less than for
the controls (35.6 compared to 47.8); lower concentrations
had no effect on species diversity. Colonisation by
annelids, molluscs, and arthropods was unaffected even at
the highest dose. The only organisms deterred by the
fenvalerate were chordates (primarily lanceolets).

6.2 Terrestrial Organisms

6.2.1 Toxicity to soil microorganisms

In laboratory trials for effects on soil algae,
Megharaj et al. [116] applied fenvalerate to a black
cotton soil, taken from a fallow cotton field. Fenvalerate
applied once at a dose equivalent to 0.5 or 1.0 kg/ha had
no inhibitory effect on soil algae, but two applications
of fenvalerate, at concentrations of 0.75 or 5.0 kg/ha,
resulted in increased algal populations.

6.2.2 Toxicity to beneficial insects

Fenvalerate is highly toxic to honey bees (Apis
mellifera) with a topical LD₅₀ of 0.41 µg/bee. However,
in field tests at a normal application rate of 0.22 kg/ha,
the hazard is low because the residue repels bees for
about 10 h following application and decreases to non-
toxic levels within one day. During the first 5 days after
application, fenvalerate caused only light bee mortality.
At higher application rates (0.44 kg/ha), however, mor-
tality remained high 8 hours after application [5, 63, 84,
85].

Fenvalerate is toxic to the tobacco budworm (Heliothis
virescens) and to its predator green lacewing (Chrysopa
carnea) as well as to the parasite (Campoletis sonorensis)
of the tobacco budworm. But, it is more toxic to the pest
than to either the predator or the parasite. Comparison of
the LC₅₀ value for the parasite (C. sonorensis) with that
for the host (H. virescens) indicated similar toxicity,
the value for the host being 1.5 times that for the para-
site [152]. However, in the case of the predator (C.
carnea), the insecticide was much less toxic to the pred-
ator than to the pest, the selectivity ratio being 0.037
[151].

When third instar larvae of C. carnea were topically
dosed with 250 µg/insect, they exhibited marked toler-
ance during a 72-h period. The ED₅₀ value (paralysis,
failure to pupate, knockdown, and mortality) for fenval-
erate through one generation (larva to larva) was approxi-
mately 1000 µg/g [164].

Syrett & Penman [176] compared LC₅₀ values for
fenvalerate when applied topically to lucerne-infesting
aphids (Acyrthosipho kondoi and A. pisum) and to their
predators, namely the brown lacewing ( Austromicromus
tasmaniae, adult and larva) and the ladybird (Coccinella
undecimpunctata). The values were 0.071, 0.033, 4.3, 67,
and 0.38 mg/kg, respectively. From these data, the lady-
bird was slightly (5-10 times) more tolerant than the
aphid species, but lacewing adults were 60-120 times as
tolerant as the aphids. Furthermore, the larvae were 15
times more tolerant than the adults. There was a negative
temperature coefficient for A. tasmaniae, with greater
toxicity (approximately 3 times) at 10 °C than at 25 °C
[176].

When fenvalerate was applied to loamy sand and then
striped earwigs (Labidura riparia), a predator of the
cabbage looper (Trichoplusia ni), were added to the soil,
fenvalerate was of low toxicity at rates giving good
looper control [205].

Laboratory studies of the activity of fenvalerate on
spider mites and their predators showed that the spider
mite (Tetranychus urticae) was considerably more (67-548
times) resistant to fenvalerate than were its predators
(Amblyseius fallacis, Typhlodromus pyri, and Typhlodromus
occidentalis) [199]. The LC₅₀ value for T. urticae was
approximately 25 times greater than that for the predator
(A. fallacis) [158].

In the field, the predatory mite (T. pyri) disappeared
during the first 4-6 weeks after fenvalerate was sprayed
at 25 mg/litre to drip-off, and then small numbers were
found 7 weeks after spraying. The insecticide had no
appreciable toxicity for spider mites (Panonychus ulmi).
The virtual elimination of the predatory mite led to a
marked population increase of P. ulmi later in the same
season [3].

In apple and pear orchards, dramatic increases in the
populations of spider mites (T. urticae, Tetranychus
mcdanieli, or P. ulmi) were seen after the application of
fenvalerate at rates of 7.5 and 15 mg ai/litre. This was
due to a reduction in the numbers of the predatory mite
(Mataseiulus occidentalis) to zero or near zero [80].

From these results, it was suggested that the rec-
ommended application rates for fenvalerate would sometimes
be detrimental to integrated mite control programs in or-
chards, and these would require careful reconsideration.

6.2.3 Toxicity to birds

The toxicity of fenvalerate to birds is very low. The
acute LD₅₀ for the chicken is more than 12 g/kg
(Table 7). The toxicity to the bobwhite quail (Colinus
virginianus) and American kestrel is similarly low.

Bradbury & Coats [13] measured the toxicity of
fenvalerate for the bobwhite quail. Acute oral dosing
yielded an LC₅₀ in excess of 4 g/kg body weight for adult
birds and 1.785 g/kg body weight for 5-week-old juveniles.
Dietary dosing of 2-week-old chicks for 5 days (with a
further 3 days of observation) indicated an LC₅₀ of
> 15 g/kg diet.

Rattner & Franson [156] dosed American kestrels with
fenvalerate (1-4 g/kg body weight) and examined the birds
for toxic effects over 10 h after dosing. Some birds were
kept at temperatures of 22 °C and others under cold stress
at -5 °C. Fenvalerate, at exposures far greater than could
be expected in the environment, caused mild intoxication
and elevated plasma alanine aminotransferase activity.
Cold did not increase the toxicity of the pyrethroid.

6.3 Uptake, Loss, and Bioaccumulation

Fenvalerate is taken up readily by aquatic organisms
and rapidly reaches, within the organism, a plateau level
related to the water concentration of the pyrethroid. Loss
of fenvalerate from organisms is rapid when they are
transferred to uncontaminated water. There is no sugges-
tion of biomagnification in food chains.

Under laboratory conditions, the half-life of fenval-
erate in sea water containing 100 g sediment per litre sea
water was 34 (27-42) days in foil-covered samples and 8
8 days in sunlight-exposed ones. Eastern oysters
(Crassostrea virginica) kept for 28 days in sea water
containing 24 µg fenvalerate/litre gave a steady state
bioconcentration factor of 4700. After treatment ceased,
fenvalerate was depurated by the oysters to non-detectable
concentrations within a week [163].

Snails exposed for 28 days to fenvalerate (0.79 µg
per litre) did not show any changes in behaviour or
survival. The bioaccumulation ratios ranged from 356 to
1167 [4].

In a study by Spehar et al. [166], embryonic, larval,
and early juvenile stages of fathead minnows (Pimephales
promelas) were exposed to fenvalerate in a continuous-flow

system for 30 days. At 0.33 µg/litre the only effect was
a temporary initial impairment of swimming in some larvae.
This was more marked at 0.43 µg/litre at which level
survival of the larvae was also reduced. The 30-day bio-
concentration factor was 3000 ± 1500, but 25 days after
transfer to clean water the fenvalerate had again been
eliminated.

Rainbow trout (Salmo gairdneri) were used to evaluate
the gill uptake and toxicokinetics of [³H]-fenvalerate.
Fish (weight between 0.64 and 0.97 kg) were exposed in a
respirometer-metabolism chamber to technical grade
fenvalerate (0.28 or 23 ng/litre) or an emulsifiable-
concentrate formulation (16 ng/litre) at 11.0-11.5 °C for
36 to 48 h. No significant effects of emulsifiers or
fenvalerate concentration on uptake were observed. The
overall mean gill uptake efficiency was 28.6 ± 4.4%. After
8- to 48-h depuration periods, carcass and bile contained
80-90% and 10-20% of the gill-absorbed material, respect-
ively. Urine, faeces, and blood each contained less than
2% of the dose. Significant excretion and blood transport
of fenvalerate equivalents were completed within 8-12 h
after exposure ceased. Specific tissues from trout exposed
to 0.28 ng/litre were analyzed for fenvalerate equival-
ents. After a 48-h depuration period, bile contained the
highest concentration of fenvalerate equivalents (7 ng/g),
followed by fat (0.2 ng/g). Remaining tissues contained
0.015-0.045 ng/g. Analysis of biliary metabolites indi-
cated that the glucuronide of 4 -OH-fenvalerate was the
only significant degradation product. Results from the
present study suggest that efficient gill uptake does not
explain the sensitivity of fish to fenvalerate. Instead,
a low rate of biotransformation and excretion may play a
significant role in the susceptibility of rainbow trout
[14].

When juvenile Atlantic salmon were exposed to static
water containing 0.8-9.3 µg fenvalerate/litre for 16-96 h,
the concentration of fenvalerate in dead fish ranged from
0.16 to 0.43 mg/kg. The insecticide was not detected (de-
tection limit: 5 µg/kg) either in dead lobster hepatopan-
creas or in dead shrimps [110].

When carp (Cyprinus carpio) was exposed to [¹⁴C-CN]-
[2S, alphaRS]-fenvalerate (0.8 µg/litre) under semi-static
conditions for 7 days, the radioactivity in fish increased
to a level of 922 µg/kg. Once the fish were transferred
to fresh water, the levels of radioactivity in the fish
decreased with an initial half-life of 5 days [135].

In studies by Ohkawa et al. [135], carp, snails,
Daphnia, and algae were exposed to fenvalerate in an
aquatic model ecosystem where ¹⁴C-[2S, alphaRS] fenval-
erate (0.3 mg/kg) was applied to the bottom sandy loam

soil. During a 30-day run, concentrations of fenval-
erate in the water were 0.35-0.63 µg/litre and 0.14-
0.21 µg/litre on days 7 and 30, respectively. The bio-
concentration factors for fenvalerate were 122, 617, 683,
and 477 on day 7 (162-300, 993-1110, 629-829, and 714-1180
on day 30) in carp, snails, Daphnia, and algae, respect-
ively. In carp, large amounts of CP-Vacid (17) and
3-phenoxybenzoic acid (22) were detected, together with
small amounts of alpha-cyano-3-(4'-hydroxyphenoxy)benzyl-2-
(4-chlorophenyl)-3-methylbutyrate (4'-OH-Fen) (25). Small
amounts of alpha-carbamoyl-3-phenoxybenzyl-2-(4-chlorophe-
nyl)-3-methylbutyrate (CONH₂-Fen) (33), alpha-carboxy-3-
phenoxybenzyl-2-(4-chlorophenyl)-3-methylbutyrate (COOH-
Fen) (34), and 4 -OH-Fen (25) were detected in snails.
CPIA was specifically present in both Daphnia (prey) and
carp (predator). CONH₂-Fen (33) and alpha-carboxy-3-phenoxy-
benzyl alcohol (36) were common to algae (prey) and carp
(predator). Based on the products identified, degradation
pathways were proposed for this aquatic model ecosystem
(Fig. 4).

In a 28-day early-life stage study (see section
6.1.2), the mean bioconcentration factor in whole fish was
570 [68].

7. EFFECTS ON EXPERIMENTAL ANIMALS AND IN VITRO TEST SYSTEMS

7.1 Single Exposures

Table 8 shows the results of acute toxicity tests with
technical grade fenvalerate in various animal species.

The acute toxic signs in rats were restlessness,
tremors, piloerection, occasional diarrhoea, and an abnor-
mal gait. Following oral administration, surviving rats
recovered rapidly from acute clinical signs of poisoning
and were asymptomatic within 3-4 days [20].

Table 9 shows the results of an acute intraperitoneal
toxicity study of fenvalerate metabolites in mice [96].
All the compounds were dissolved in corn oil except
3-phenoxybenzoic acid, which was dissolved in DMSO. The
acute intraperitoneal toxicity in mice of the proposed
decarboxylated photo-products was found to be similar to,
or greater than, that of fenvalerate [78].

In a study by Blair and Roderick [12], groups of four
male and four female rats were exposed by inhalation (head
only) to an aerosol formulation (77-µm particle size)
generated from an aqueous suspension containing 3 g/litre.
Following a single administration (4 h) of this non-
inhalable particulate, acute signs of poisoning were noted
for a short period, presumably from oral ingestion of the
large particles. There was no mortality and all animals
appeared normal within 3 days following exposure.

7.2 Short-Term Exposures

7.2.1 Oral administration

Groups of Carworth Farm E rats (12 of each sex per
group) were fed fenvalerate in the diet at dose levels of
0, 125, 500, 1000, and 2000 mg/kg for 90 days [72]. Mor-
tality (11/12 male, 9/12 female) was observed at the
highest concentration. Body weight gain and food consump-
tion were decreased and blood urea nitrogen concentrations
were increased at 1000 and 2000 mg/kg. There were no
treatment-related changes in any groups of rats in the
haematological parameters examined. Increases in liver to
body weight ratios and kidney to body weight ratios were
observed at 500 mg/kg or more. Gross and microscopic
examinations revealed no compound-related changes in any
groups. The NOEL was 125 mg/kg diet.

Table 8. Acute toxicity of fenvalerate (technical grade) administered to various species
-------------------------------------------------------------------------------------------------
Species Route Sex Vehicle^a LD₅₀ (mg/kg) Reference
-------------------------------------------------------------------------------------------------
Rat oral DMSO 451 195
oral PEG:water > 3200 168
dermal 5000 (24 h) 140
inhalation M, F water > 101 mg/m³ (3 h) 94
intraperitoneal