908. Fenarimol (Pesticide residues in food: 1995 evaluations Part II Toxicological & Environmental)

FENARIMOL

Summary
Environmental transport, distribution, and transformation
Environmental levels and human exposure
Effects on organisms in the environment
Terrestrial vertebrates
Aquatic organisms
Bees and other arthropod species
Earthworms
Microorganisms
Environmental effects
Identity, physical and Chemical properties, mode of action,
and use
Identity
Physical and chemical properties
Formulations
Mode of action
Use
Environmental transport, distribution, and transformation
Volatilization and aerial transport
Water
Hydrolysis
Photolysis
Persistence in surface water
Degradation by microorganisms
Bioaccumulation and biomagnification
Soil
Adsorption and desorption
Photolysis
Biotransformation
Degradation by microorganisms
Persistence
Bioaccumulation and biomagnification
Environmental levels
Air
Water
Soil
Effects on other organisms in the laboratory and the field
Laboratory and field experiments
Microorganisms
Aquatic organisms
Terrestrial organisms
Risk assessment based on agricultural use
Microorganisms
Aquatic organisms
Terrestrial organisms

Evaluation of effects on the environment
Risk assessment
Further research
Previous evaluations by international bodies
References

1. Summary

1.1 Environmental transport, distribution, and transformation

Fenarimol is persistent in soil in laboratory studies but less so
in the field under mid-European conditions. Photolysis was shown to
occur on surfaces, but the rate was not quantified. As fenarimol is
likely to be applied where a crop canopy exists, photolysis is not
considered to be a significant mechanism for subsequent degradation in
soil

Fenarimol is not mobile and is therefore unlikely to reach water
through the soil. Should it reach water by other means, it is stable
to hydrolysis but susceptible to rapid photolysis. It also partitions
rapidly into sediment, and this is likely to be the major process for
removal from the water column. Once it is in the sediment, its
degradation is slow.

1.2 Environmental levels and human exposure

No data on levels in air or water were provided, but levels in
soil reached 0.1-0.4 mg/kg (averaged over the top 20 cm) directly
after application of 270 g/ha. In laboratory experiments, the level in
fish exposed to 0.1 mg/litre was 14.1 mg/kg tissue, and those in
earthworms exposed to 1 and 10 mg/kg soil were 1.0 and 9.6 mg/kg
tissue, respectively.

1.3 Effects on organisms in the environment

1.3.1. Terrestrial vertebrates

Birds and mammals are thought to be exposed to fenarimol mainly
from feeding, either directly on grass or fruit treated with fenarimol
or by eating contaminated insects or earthworms present in
fenarimol-treated crops. As fenarimol generally has low toxicity for
birds (LD₅₀ > 2000 mg a.i./kg bw) and mammals (LD₅₀2500 mg
a.i./kg bw), the toxicity:exposure ratios (TERs) were above the
threshold for unacceptable effects set by the European Plant
Protection Organisation (EPPO) (1993), indicating that use of
fenarimol should present a low acute risk to wild birds and mammals.

Reproducing birds are thought to be exposed to fenarimol only
when multiple applications are made in orchards throughout the year.
On the basis of a revised NOEC of 50 mg/litre for reproductive
toxicity, the TERs for this end-point were above the EPPO threshold
for unnacceptable effects and indicate that the risk to reproducing
birds of use of fenarimol in orchards should be low.

1.3.2 Aquatic organisms

Technical-grade fenarimol and fenarimol-containing products had
moderate acute toxicity to aquatic organisms, with LC₅₀ and EC₅₀
values of 0.82 mg a.i./litre for the most sensitive fish species
tested, 0.18 mg a.i./litre for aquatic invertebrates, and 0.76 mg
a.i./litre for algal species. On the basis of these data, formulations
of fenarimol are classified as 'harmful to fish or other aquatic
life'. Worst-case assessments for over-spraying indicated that there
is an acute risk (TER < 100) to all three aquatic groups from the use
of fenarimol, particularly its use on turf and in orchards. An
assessment of spray drift indicated, however, that the risk to aquatic
life from use on turf was acceptable, particularly when a dissipation
half-life (DT₅₀) of < seven days for fenarimol in the aqueous phase
of water and sediment systems was taken into account. Although this
assessment indicates that the acute risk to fish and algae from the
remaining agricultural and horticultural uses is also acceptable,
aquatic invertebrates are at acute risk from contamination arising
from air-assisted spray application, such as used in orchards.

Fenarimol was also of moderate long-term toxicity to fish and
aquatic invertebrates, with NOECs of 0.43 and 0.113 mg a.i./litre,
respectively. After overspraying on turf and in agricultural and
horticultural uses of fenarimol, fish and aquatic invertebrates have a
high long-term risk (TER < 10), particularly from use on turf and in
orchards. An assessment of spray drift after use on turf indicated,
however, that the long-term risk to fish and aquatic invertebrates was
acceptable, when a DT₅₀ of < 7 days for fenarimol in the aqueous
phase of water-sediment systems was taken into account.

Although fenarimol was rapidly removed from the aqueous phase of
natural water-sediment systems, it partitioned and persisted in the
sediment phase. Sediment-dwelling invertebrates (Daphnia magna) may
be at long-term risk from the use of fenarimol by air-assisted spray
application to tree and bush crops, such as in orchards.

1.3.3 Bees and other arthropod species

Fenarimol had little acute toxicity to honey bees, the acute oral
LD₅₀ being > 10 µg a.i./bee and the contact LD₅₀ being > 100 µg
a.i./bee. Although the hazard ratio for turf use, < 150, may have
exceeded the EPPO threshold of 50, the risk to bees from this use was
considered to be low, as application was done mainly in autumn or
winter when bees are unlikely to forage. The hazard ratios for the
remaining uses were < 50, indicating low risk to bees.

As the recommended European Standard Characteristics of
Beneficial Regulatory Testing for non-target arthropods were not
satisfied, the data that were submitted could not be used to assess
the risk to non-target arthropods from agricultural use of fenarimol.

1.3.4 Earthworms

Fenarimol had little toxicity for earthworms, with an acute
LC₅₀ of 200-300 mg a.i./kg soil and a reproductive NOEC of 1890 g
a.i./ha. In a number of overspray assessments, the acute and sublethal
risks to earthworms of application to turf and multiple applications
in orchards at maximal rates were considered to be low.

1.3.5 Microorganisms

Fenarimol had no effect on soil respiration and nitrification
processes at application rates up to 28 times the recommended maximum.
Representative 'worst-case' multiple overspraying of turf and orchards
at the maximal application rate resulted in a low risk to soil
microorganisms from the use of fenarimol. Concentrations up to
102.4 mg/litre had no effect on sewage treatment processes, indicating
a low risk.

1.4 Environmental effects

Fenarimol is not mobile but is persistent. Under normal
conditions of use on foliage, the amount that actually reaches the
soil is likely to be significantly reduced. As the potential risk to
aquatic invertebrates can be reduced by introducing a buffer zone, use
of fenarimol should present a low risk to non-target organisms.

2. Identity, physical and chemical properties, mode of action,
and use

2.1 Identity

ISO common name: fenarimol
Chemical name

IUPAC: (±)-2,4-dichloro-alpha-(pyrimidin-5-yl)
benzhydryl alcohol

Chemical Abstracts: (±)-alpha-(2-chlorophenyl)-alpha-
(4-chlorophenyl)-5-pyrimidinemethanol

CAS Registry No: 60168-88-9 (unstated steriochemistry)

CIPAC No: 380

Synonyms: compound 5732; development code EL-222

Structural formula:

Molecular formula: C₁₇H₁₂Cl₂N₂O

Relative molecular mass: 331.2

2.2 Physical and chemical properties

Pure active ingredient

Vapour pressure: 6.5 × 10^-5 Pa at 25°C (99.7% pure)

Hydrolysis At 25, 37 and 52°C:

(no purity stated)pH 3 no hydrolysis
pH 6 no hydrolysis
pH 9 no hydrolysis

After reflux at 100°C for 40 h

pH 3 30% hydrolysis
pH 6 no hydrolysis
pH 9 13% hydrolysis

Photolysis (no purity stated)

Natural sunlight: half-life in 2 mg/litre aqueous solution
in summer sun, 12h
half-life in water in
laboratory-simulated sunlight, < 1 h
half-life on silica gel plates in
sunlight approx. 14 h

Laboratory irradiation:
half-life in distilled water, 0.6 h
half-life in 2% acetone-water, 2.0 h

No information was submitted on melting-point, octanol-water partition
coefficient, solubility, or specific gravity.

Technical material

Purity: typically > 97%, with certified limits
of 95-101% to allow for assay and
production variability.

Impurities < 0.5%, except for 2,2'-, 2,3'-, and
4,4'-dichloro isomers, total max. 3%

Colour: off-white to buff

Physical state: crystalline solid

Odour: slightly aromatic

Melting point: 117-119°C

Octanol-water partition log K_ow = 3.69
coefficient:

Solubility (mg/litre at 25°C; purity either 95.4% or unspecified)

water at pH 3 14.6
water at pH 7 13.7
water at pH 10 13.8
acetone >250
acetonitrile 40-45
benzene 100-125
chloroform > 500
cyclohexanone > 500
ethyl cellulosolve > 250
heavy aromatic naphtha 40-45
hexane 1.1
methanol 100-125
methyl cellulose > 250
xylene 40-45 (A 09 & A 14)

Packed bulk density: 0.7-0.8 kg/m³

2.3 Formulations

Fenarimol is formulated mainly as wettable powders, emulsifiable
concentrates (EC) or suspension concentrates (SC).

2.4 Mode of action

Fenarimol inhibits ergosterol biosynthesis by inhibing C14
demethylation.

2.5 Use

Fenarimol is a systemic fungicide, which protects, cures, and
eradicates. It is usually applied to leaves and moves apoplastically
through the leaf towards the tip. Movement from treated to untreated
leaves is not significant enough to control disease. Application to
roots and seeds results in translocation to all of the aerial parts of
the plant.

Fenarimol is registered in many countries for use on a wide range
of fruits, vegetables, hops, and wheat, at application rates of
0.005-0.2 kg/ha on fruit with up to 14 applications per season,
0.002-0.06 kg/ha on vegetables with 1-10 applications per season, <
1.5 kg/ha on turf with one to four applications per season, and
0.04-0.06 kg/ha on cereals and hops with one to four applications per
season.

3. Environmental transport, distribution, and transformation

3.1 Volatilization and aerial transport

The dimensionless Henry's law constant (air-water partition
coefficient) for fenarimol is 2.83 × 10^-7, indicating that it has
moderately low volatility. The volatilization of fenarimol from plant
and soil surfaces was investigated by Day (1993). Formulated fenarimol
was sprayed onto Borstel soil at 60% maximal water-holding capacity or
onto stands of French beans about 30 cm high covering 70-80% of the
soil, at a rate of 70 g a.i./ha. The temperature was maintained at
20°C, with a relative humidity of 40% and an air velocity of 1.2 m/s.
Less than 0.2% radioactivity was volatilized from the soil and 1.5%
from the plants.

3.2 Water

3.2.1 Hydrolysis

Fenarimol in sterile buffer solutions at pH 3, 6 or 9 was
incubated in the dark at 25, 37, or 52°C for four weeks. No
degradation occurred. When the solutions were refluxed at 100°C for
40 h, about 30% hydrolysis occurred at pH 3 and 13% at pH 9 (Anon.,
undated). Thus, fenarimol is stable to hydrolysis.

3.2.2 Photolysis

Aqueous solutions of fenarimol and silica plates coated with
fenarimol were subjected to artificial light or natural summer
sunlight at 40° N in the USA. The first-order half-lives were < 13 h
under all conditions. Similar results were obtained by Mosier &
Saunders (1976) and Smith & Saunders (1982a), who also reported that
the major metabolite is 2'-chloro-2-(5-pyrimidyl)-4-chloro-benzo-
phenone. Saunders (1991) calculated the quantum efficiency of
photolysis and predicted half-lives ranging from 0.93 days in summer
at 30° N to 5.3 days in winter at 50° N. Fenarimol is thus susceptible
to rapid photolysis, but the significance of this process in turbid
waters is uncertain.

3.2.3 Persistence in surface water

Fenarimol may reach surface waters by spray drift, direct
overspray, or erosive run-off of water or particulate matter. Rapid
photolysis is a possible mechanism of degradation, but this may not
occur in turbid waters. In natural water-sediment systems in the dark,
fenarimol partitioned rapidly into the sediment (75-80% within seven
days), with a partition DT₅₀ of < 7 days, a DT₉₀ of < 14 days
(re-calculated from raw data), and no appreciable degradation over 80
days (Jackson & Lewis, 1994a). In a study conducted outdoors in the

USA, a slower rate of partitioning from water to sediment was seen
(DT₅₀, 18 days; re-calculated from raw data) (Althaus & Goebel,
1981). This value does not agree with the probable photolysis rate or
the results of the previous study; since the study was conducted in
1981, the result is considered to be less reliable. In general,
irrespective of the route of entry of fenarimol into surface water, it
will be adsorbed onto sediment and persist, as its degradation is
slow.

3.2.4 Degradation by microorganisms

No data were submitted on the degradation of fenarimol by
microoganisms in aqueous systems. It was not degraded during a
semi-continuous, 28-day study of aerated sewage sludge (Kline & Knox,
1981).

3.2.5 Bioaccumulation and biomagnification

In a 14-day study of bioaccumulation under static conditions,
bluegill sunfish (Lepomis macrochirus) were exposed for seven days
to a mean measured concentration of 0.083 mg/litre fenarimol (Althaus
& Beaty, 1981; Althaus, 1983). The maximal plateau concentrations were
5.1 mg/kg fenarimol in muscle after one day, 14.1 mg/kg in carcass
after four days, and 9.1 mg/kg in whole fish after two days,
equivalent to bioconcentration factors of 60,175, and 113 for muscle,
carcass, and whole fish, respectively. Depuration after transfer to
uncontaminated water was biphasic, with DT₅₀ values of 0.6 day for
the first three days of depuration and 5.5-6.1 days for the last four
days. Overall, > 95% of radioactivity was eliminated within four
days.

3.3 Soil

3.3.1 Adsorption and desorption

The K_oc values for fenarimol in four soils with 0.3-1.2%
organic carbon, pH 5.7-7.7, and a clay content of 5-32%, were 500-992
for adsorption and 482-2468 for desorption (re-calculated from the raw
data, since organic matter content was not converted to organic carbon
content in the original report) (Saunders & Powers, 1987).

In studies of four representative soils, with organic carbon
contents of 0.6-2%, pH 5.6-8.1, and clay contents of 4-28%,
radiolabelled fenarimol was applied to 30-cm dry soil columns, which
were then leached with 64 cm water for two to four days. Only 0-0.4%
of the total radiolabel was found in the leachate, and 91-100%
remained in the top 10 cm of soil. For comparison, 3.4-43% of atrazine
was found in the leachate from the same soils and the compound was
spread evenly throughout the soil (Sullivan & Saunders, 1976).

When soil (organic carbon, 0.6-1.8%; pH 6.4-8.1; clay content,
4-33%) containing fenarimol was aged for 30 days and then placed on
the tops of four columns which were then leached with 51 cm water,
unidentified radiolabel in the leachate accounted for 0.24-0.32%, and
essentially all of the radiolabel was in the top 12 cm of soil
(Saunders et al., 1983).

After 50 h photolysis of fenarimol in soil in natural sunlight,
46% of the radiolabel was identified as fenarimol. Portions of the
treated soil (organic carbon, 1.7-2.5%; pH 5-7.5; clay content, 4-21%)
were placed on two columns which were then leached with 30 cm water
over three days. The leachate contained 1.7-9% of the radiolabel, and
80-92% remained in the top 5 cm of the column. The main component of
the leachate was ortho-chlorobenzoic acid (34-50% of the
radiolabel); the remainder was a complex mixture of very polar
compounds (Vonk & van den Hoven, 1981).

3.3.2 Photolysis

Conflicting results have been obtained with regard to the
photolysis of fenarimol in soil, perhaps due to differences in
incident light or the nature of the surface. The fate of a thin film
of fenarimol in a pan in sunlight for 18 h and of a dry deposit under
the same conditions for 200 h was studied in Indiana, USA, at a
maximal temperature of 37°C: 62% of the fenarimol remained after 18 h
and only 4% after 200 h. Numerous minor degradation products were
found; the primary breakdown pathways were reported to be oxidation of
the chlorobenzene rings and the carbinol carbon. Secondary pathways
were ring closure, ring migration, and reduction of the carbinol
carbon (Althaus & Bewley, 1978a). In a study of the photolysis of a
dry deposit of fenarimol in a pan in natural winter sunlight in
Indiana, USA, with a maximal temperature of 18°C), 33-38% remained
after 100 days, and the major metabolite was ortho-chlorobenzoic
acid (Althaus, 1984).

In a further study of the photolysis of fenarimol on a soil film
in natural sunlight in Indiana, USA, for up to 32 h, no degradation
was observed (Smith & Saunders, 1982b).

3.3.3 Biotransformation

Three agricultural soils and one standard soil (organic carbon,
0.8-2.5%; pH 5.2-7.7; clay content, 6-39%) were incubated with
fenarimol at 0.05 or 0.25 mg/kg, 40% maximal water-holding capacity,
and 20°C. Fenarimol degraded very slowly, with DT₅₀ values of
436-1833 days, according to first-order kinetics (Jackson & Lewis,
1994b). Similar results were obtained in a study in which a single
metabolite, alpha-(2-chlorophenyl)-alpha-(4-chlorophenyl)-1,2-
dihydro-2-oxo-5-pyrimidinemethanol, was identified (Rainey, 1990).

In a brief comparison of aerobic and anaerobic degradation, both
aerobic and anaerobic metabolism were found to be slow, in keeping
with other results (Althaus & Beaty, 1982). Slow anaerobic degradation
had been observed previously (Althaus & Bewley, 1978b).

3.3.4 Degradation by microorganisms

Microbial degradation has not been addressed directly, but given
the very slow degradation of fenarimol under aerobic and anaerobic
conditions, a significant change in degradation rate is unlikely to be
seen in sterile soil.

3.3.5 Persistence

As discussed above, the degradation of fenarimol incubated in the
laboratory at 20°C is very slow, and the half-lives apparently vary
widely. The wide range is probably due to inaccuracies in
calculations, owing to the degree of extrapolation required to reach a
half-life. Nevertheless, the compound is clearly very persistent in
soil under laboratory conditions. Studies of dissipation at
agricultural sites in Germany gave much shorter DT₅₀ values (18-140
days), but the DT₉₀ values were still in excess of one year.

3.3.6 Bioaccumulation and biomagnification

In a 21-day study of bioaccumulation in earthworms, Lumbricus
terrestris were exposed to technical-grade fenarimol for 14 days in
a mixture of soil and rabbit faeces (for food source) at concen-
trations of 0, 1, or 10 mg/kg soil, followed by a seven-day clearance
period in uncontaminated soil. The mean concentrations of fenarimol in
soil were 111-150% of the nominal level. The concentrations in the
earthworms never exceeded the surrounding soil concentration, with
levels of 0.027 mg/kg bw after 1 h, 0.957 mg/kg bw after seven days,
and 1.037 mg/kg bw (to a maximum of 69% of the measured soil concen-
tration) after 14 days of exposure to a nominal soil concentration of
1 mg/kg soil. Similarly, the concentrations of fenarimol in earthworms
exposed for 1 h or seven or 14 days to a nominal soil concentration of
10 mg/kg soil were 0.105, 8.26, and 9.645 mg/kg bw (to a maximum of
89% of the measured soil concentration), respectively. These results
indicate that fenarimol was not bioaccumulated in earthworms at
concentrations above that in the soil. Earthworms rapidly eliminated
residues of fenarimol on transfer to uncontaminated soil, with a
clearance DT₅₀ of five days (Hoffman et al., 1981).

4. Environmental levels

4.1. Air

No data were available.

4.2 Water

No data were available.

4.3 Soil

An EC formulation of fenarimol was sprayed at a rate of 270 g
a.i./ha onto bare soil containing 1.2-4.9% organic carbon, pH 5.6-7.3,
and 9-26% clay, at four German agricultural field sites in May 1990,
and fenarimol was analysed in a 0-20-cm deep segment. The DT₅₀ was
14-123 days and the DT₉₀, 120-> 610 days (recalculated from the
observed raw data rather than by curve fitting); however, uncertainty
about the results obtained at the early sampling times reduces the
confidence that can be placed in the DT₅₀ value (Perkins, 1993).

In a further trial in which an EC formulation of fenarimol was
sprayed at a rate of 270 g a.i/ha onto bare soil containing 0.9-1.1%
organic carbon, pH 4.8-5.7, and 12-21% clay) at two German
agricultural field sites in May 1992, the concentrations in the
0-20-cm layer on clay 0 were 0.076-0.082 mg/kg. The resulting
dissipation DT₅₀ value was 60-130 days and the DT₉₀ was 489-> 609
days (recalculated from the observed raw data rather than by curve
fitting) (Butcher & Rawle, 1994).

The effect of surface application or incorporation of fenarimol
onto or into a silt loam soil was studied in Indiana, USA. When
fenarimol was applied to the surface, the dissipation DT₅₀ was 112
days and 35% remained after 511 days. When fenarimol was incorporated
into soil, none was dissipated from the 0-15-cm soil layer, and 65% of
the applied fenarimol remained after 903 days. Fenarimol is generally
applied to foliage, however, and hence dissipation rates after soil
incorporation are probably of little practical relevance (Althaus &
Bewley, 1978b).

5. Effects on other organisms in the laboratory and the field

5.1 Laboratory and field experiments

5.1.1 Microorgansims

(a) Water

In a semi-continuous, 28-day study of aerated sewage, the effect
of technical-grade fenarimol at concentrations up to 102.4 mg/litre on
microorganisms and the effect of microorganisms on fenarimol were
investigated (Kline & Knox, 1981). Fenarimol had no effect on
biological oxygen demand, viable cell count, pH, or accumulation of
solids in sewage inoculum, and it was not significantly degraded.
Fenarimol at these concentrations therefore had no effect on sewage
treatment processes.

(b) Soil

In a 14-week study, the effect of fenarimol at 240 mg/kg soil was
studied on respiration and microbial populations in a loam, a sandy
loam, muck, and a greenhouse mixture (Kline & Knox, 1976). Slight
reductions in comparison with controls were seen in carbon dioxide
production in the loam (about 22% reduction) and greenhouse soils
(about 40% reduction), but no effect was seen in the sandy loam or
muck soils. There was no difference in the number of colony forming
units in treated and control soils, except for an initial reduction in
the number of soil fungi in the treated loam and sandy loam, both of
which recovered to control levels within four to six weeks.

In a 15-day study, the effect of technical-grade fenarimol at 0,
0.4, 2, or 10 mg/litre was observed on nitrifying microorganisms
(Peloso & Kline, 1982). Oxidation of ammonium to nitrite by Nitro-
somonas europaea was nearly complete at all test concentrations and
in the control by day 25. There was a slight enhancement of nitrif-
ication at 0.4 and 2 mg/litre fenarimol, whereas at 10 mg/litre there
was either no effect or slight enhancement of nitrification of
ammonia. Complete oxidation of nitrite to nitrate by Nitrobacter
winogradskyi had occurred by day 12 after treatment with 0, 0.4, or
2.0 mg/litre fenarimol; at 10 mg/litre, a further three days were
necessary to achieve the same level of nitrification.

In a 28-day study conducted according to German Biologische
Bundesanstalt fur Landund Forstwirtschaft (BBA) Guideline VI 1-1, the
effect of a 120 g/litre EC formulation of fenarimol on soil microflora
activity in a loamy sand and silty loam soil was investigated at
application rates equivalent to 36 or 504 g/ha (Todt et al., 1988).
After 14 days, the dehydrogenase activity of all treated soils was
lower (2.4-2.5 mg triphenyl formazene per 100 g dry soil weight) than
that in the untreated control (3.5-4.3 mg triphenyl formazene per
100 g dry soil weight). The decrease was thus not dependent on the

application rate. The dehydrogenase activity of both soils returned to
control levels by day 28. There was no significant difference between
control and fenarimol-treated soils in nitrification activity, as
measured by soil nitrite content; however, the amount of newly formed
nitrate in both soils was twice that expected from the nitrite
depletion. As this effect was also reported in the control, it was
considered not to be related to treatment.

5.1.2 Aquatic organisms

(a) Plants

The acute toxicity of fenarimol to aquatic green algae is
summarized in Table 1. In addition, McCowen (1982) reported that
technical-grade fenarimol at concentrations up to 10 mg/litre had no
effect on cultures of Chlorella pyrenoidosa, Scenedesmus obliquus,
or Anacystis nidulans. The highest concentration had a moderate
effect on Raphidocellis subcapitata.

(b) Invertebrates

The acute toxicity of fenarimol to aquatic invertebrates is
summarized in Table 2.

In a 21-day life cycle test under static conditions, Daphnia
magna were exposed to technical-grade fenarimol at nominal
concentrations of 0.113-1.084 mg/litre, giving actual concentrations
of 107-113% of the nominal value. Parental survival was 90-100% in
water controls and at 0.113-0.331 mg/litre fenarimol but dropped to
70% at 0.643 mg/litre and 10% at 1.084 mg/litre. Statistically
significant reductions were seen in the numbers of broods, of 4.8-4.9
in controls to 0-4.0 at > 0.219 mg/litre fenarimol, in the total
number of young per female, from 103.2-105.2 in controls to 0-86.1 at
> 0.331 mg/litre fenarimol, and in mean body length, from 4.13-
4.24 mm in controls to 3.4-3.82 at > 0.643 mg/litre fenarimol. The
NOEC, in mean measured test concentrations, was therefore 0.113
mg/litre (Hoffman et al., 1987).

The acute toxicity of fenarimol to fish is summarized in Table 3.
The chronic toxicity of technical-grade fenarimol to fathead minnows
(Pimephales promelas) was investigated in a 33-day test during the
early life stage in a flow-through system. By the end of the study,
97-99% of eggs had hatched and 92-97% of fish in all groups were
alive. There were no physical or behavioural signs of toxicity and no
significant effects on fish length or weight throughout the study at
any concentration. The actual test concentrations were reported to be
92-100% of the nominal value. The NOEC as a mean measured test
concentration was 0.98 mg/litre, the highest dose tested (Hoffman
et al., 1982a).

Table 1. Acute toxicity of fenarimol to aquatic green algae

Organism Study type Exposure (% of End-point, result Test Reference
nominal concn) (mg/litre) guideline

Value 95% CI

Raphidocellis Static 76-100% a.i.; 14 days LC₅₀ = 1.48^a 0.63-20.0 None (broadly Hoffman &
subcapitata (32% at 1.5 mg/litre) in line with Cocke (1988)
OECD 210)
Scenedesmus Static 94-104%; a.i ErC₅₀ 24-48 h = 3.8 3.5-4.2 OECD 201 Douglas et al.
subspicatus EbC₅₀, 72 h = 3.0 2.7-3.3 (1991)
EbC₅₀, 96 h = 5.1 4.5-5.9
NOEC = 0.59
Raphidocellis Static 94-106% at 24 h; Eb₅₀, 72 h = 0.76 0.59-0.96 OECD 201 Bell (1994a)
subcapitata 120 g/litre EC NOEC = < 0.12
formulation Er₅₀, 72 h = 1.32 1.14-1.44
NOEC = 1.2

CI, confidence interval; EbC, effective concentration for effect on biomass; ErC, effective concentration for effects on growth rate
^a Based on measured test concentrations

Table 2. Acute toxicity of fenarimol to aquatic invertebrates

Organism Study type Exposure (% of End-point, result Test Reference
nominal concn) (mg/litre) guideline

Value 95% CI

Daphnia magna Static A.i.; not measured None (broadly Karnak et al.
24 h LC₅₀ = > 10 in line with EC (1978a)
48 h LC₅₀ = 6.8 method C2)
NOEC = < 2.75
Daphnia magna Static 92-110%; 120 g/litre EC method C2 Bell (1994b)
SC formulation (equivalent to
24 h LC₅₀ = 0.32 0.29-0.37 OECD 202)
48 h LC₅₀ = 0.18 0.12-0.26
NOEC = 0.12
Daphnia magna Static 86-109%; 120 g/litre EC method C2 Douglas et al.
SC formulation (equivalent to (1993)
24 h LC₅₀ = 5.6 4.6-7.1 OECD 202)
48 h LC₅₀ = 1.4 1.2-1.7
NOEC = 0.2

CI, confidence interval; SC, suspension concentrate
In a 69-day test during the early life stage in a flow-through
system with rainbow trout (Oncorhynchus mykiss) exposed to technical-
grade fenarimol, 96-100% of the eggs hatched and 92-100% of the fish
were still alive 30 days after hatching. Survival 59 days after
hatching was reduced to 86% at 0.97 mg/litre (the highest concen-
tration), but this was not statistically significant. No behavioural
signs of toxicity were reported at any concentration. The mean lengths
of fish 30 days after hatching were statistically significantly lower
than those of controls in solvent or in water or at 0.43 mg/litre
fenarimol. These effects were not considered to be dose-related,
however, since there was no statistically significant difference at
the same doses 59 days after hatching. The mean lengths of fish at
0.87 mg/litre fenarimol were significantly lower than those of
controls 30 and 59 days after hatching, and this effect was considered
to be treatment related as it was associated with a statistically
significant drop in mean body weight. The NOEC as a mean measured test
concentration was 0.43 mg/litre, on the basis of the statistically
significant reduction in both mean length and weight at the highest
dose. The actual concentrations were reported to be 88-140% of the
nominal value (Hoffman et al., 1982b).

5.1.3 Terrestrial organisms

(a) Plants

No data were available.

(b) Invertebrates

Bees: Technical-grade fenarimol had little toxicity, with a
48-h oral LD₅₀ of > 10 µg/bee and a 48-h contact LD₅₀ of >
100 µg per bee (Bell, 1994d). Mortality at these doses was < 1% after
contact, 23% after 24 h oral exposure, and 25% after 48 h; however,
higher oral doses should have been tested. As both the oral and
contact LD₅₀ values for fenarimol are > 10 µg per bee, all
fenarimol-containing products should remain unclassified in terms of
their hazard to honey bees.

Other non-target arthropod species: No standard laboratory
tests on the toxicity of technical-grade or formulated fenarimol to
non-target arthropods were submitted. Primary data on the insecticidal
properties of technical-grade fenarimol formulated in an acetone-
ethanol mixture diluted with distilled water containing 0.25% Tween 20
(a surfactant), administered as one spray of 400 mg a.i./litre or two
sprays of 50 or 400 mg/litre, were, however, submitted (Hertlein
et al., 1994). No effect was reported on cotton aphid (Aphis gossypii)
or spider mites (Tetranychus urticae) when fenarimol was applied
directly to infested plants. Similarly, application of fenarimol to a
substrate, followed immediately by a drying period before introduction

Table 3. Acute toxicity of fenarimol to fish

Organism Study type Exposure (% of End-point, result Test Reference
nominal concn) (mg/litre) guideline

Value 95% CI

Lepomis Flow through 55-86%; a.i.; 186 h 2.74-5.17 (chronic None Kehr et al. (1978a)
macrochirus toxicity)
Lepomis Static, not 88-95%; a.i. None (broadly Hoffman (1980)
macrochirus aerated 24 h > 4.0 in line with
48 h 2.0 1.7-2.5 OECD 203)
72 h 1.8 1.5-2.4
96 h 1.8 1.5-2.4
NOEC = 0.86
Static, aerated 24 h 9.6 5.8-16
48 h 5.7 3.4-9.6
72 h 5.7 3.4-9.6
96 h 5.7 3.4-9.6
NOEC = < 2.1
Oncorhynchus Static, not 92-109% a.i. None (broadly Hoffman (1980)
mykiss aerated 24 h > 2.4 in line with
48 h 2.4-4.1 OECD 203)
72 h 2.4-4.1
96 h 3.1 2.4-4.1
NOEC = 0.53
Static, aerated 24 h 4.1 3.2-5.3
48 h 4.1 3.2-5.3
72 h 4.1 3.2-5.3
96 h 4.1 3.2-5.3
NOEC = < 1.1

Table 3. (cont'd)

Organism Study type Exposure (% of End-point, result Test Reference
nominal concn) (mg/litre) guideline

Value 95% CI

Oncorhynchus Semi-static 81-109%; 120 g/litre OECD 203 Bell (1994c)
mykiss SC formulation
(67.4% at 72 h)
24 h 1.8 1.2-2.6
48 h 1.2 0.8-1.7
72 h 0.9 0.7-1.3
96 h 0.8 0.6-1.2
NOEC = 0.3
Oncorhynchus Semi-static 89-102%; 120 g/litre OECD 203 Douglas (1993)
mykiss SC formulation
(74% at 100 mg/litre)
24 h 6.1 4.9-7.4
48 h 5.0 3.8-6.7
72 h 5.0 3.8-6.7
96 h 5.0 3.8-6.7
NOEC = 0.12

CI, confidence interval
of test insects, had no effect on tobacco budworm (Heliothis
virecscens), beet armyworm (Spodoptera exigua), German cockroach
(Blattella germanica), southern corn rootworm (Diabrotica 11-punctata
howardi), or a free-living non-plant parasitic nematode (Pelodera
sp). Conflicting results were obtained for the aster leafhopper
(Macrosteles severini) in two trials: In the first, one application
of fenarimol at 400 mg/litre to the test substrate followed by a
drying period resulted in the deaths of all aster leafhoppers, whereas
in the second, two similar applications of fenarimol at 50 or 400
mg/litre had no effect. The effect of fenarimol on aster leafhoppers
in the first trial may therefore not have been treatment related.
Applications of fenarimol at spray concentrations up to 400 mg/litre
were thus generally of low toxicity to insects.

Fenarimol formulated as a 120 g/litre EC formulation and applied
as a 0.014% spray was classified as 'harmless' (< 50% effect in
laboratory tests) to beneficial parasites such as Encarsia formosa,
Aphidius matricariae, Leptomastix dactylopii, Phygdeuon trichops, and
Coccygomimus turionellae, to predatory mites and spiders such as
Phytoseiulus persimilis, Amblyseius potentillae, Amblyseius
finlandicus, Typhlodromus pyri, and Chiracanthium mildei, and to
predatory insects such as Syrphus corollae, Harmonia axyridis,
Anthocoris nemoralis, Bembidion lampros, and Pterostichus cupreus.
'Slightly harmful' effects (50-79%) were reported in tests with the
parasitoid Trichogramma cacoeciae and the predatory insects
Chrysoperla carnea and Semiadalia 11-notata. In semi-field and
field studies, the same formulation was classified as 'harmless' (<
25% effect in semi-field tests) for the predatory insects Chrysoperla
carnea and Aleochara bilineata and the predatory mites Phyto-
seiulus persimilis and Typhlodromus pyri but 'moderately harmful'
(51-75%) for the predatory mite Amblyseius finlandicus (Hassan
et al., 1988).

In a field study conducted in a Belgian orchard, the number of
arthropods falling onto plastic sheets in replicate tree plots after
treatment with a 120 g/litre EC formulation of fenarimol at a spray
concentration of 0.033% (0.5 litre of product in a water volume of
1500 litres/ha) and an application rate of 60 g/ha was compared with
the total population in the plots, as the number present on plastic
sheets after treatment with dichlorvos. The percentage change in
populations of Heteroptera, Dermaptera, Chrysopidae (larvae),
Chrysopidae (adults), Coccinellidae (larvae), Coccinellidae (adults),
Syrphidae (adults), and Hymenoptera parasitica was reported using
'Steiner's formula'. The highest percentage change was 13.8% for
Dermaptera (mainly earwigs); the remaining values were either negative
or < 10. Fenarimol at an application rate of about 59.4 g/ha was thus
considered to be 'harmless' to the beneficial arthropod fauna of
orchards. This study was not conducted according to any recognized
standard protocol (Anon., 1991).

Earthworms: In a 14-day study, Lumbricus terrestris was
exposed to technical-grade fenarimol in a mixture of soil and rabbit
faeces (for food source) at concentrations up to 100 mg/kg soil
(Karnak et al., 1978b). Fenarimol had little toxicity, since no
deaths were reported. Body weight was reduced during the last seven
days of the study at all concentrations including the control. This
was not considered to be treatment related and was probably due to
exhaustion of the food source.

In a 14-day test in artificial soil, Eisenia foetida was
exposed to a 120 g/litre EC formulation of fenarimol. Little toxicity
to compost worms was seen, with an LC₅₀ of 200-300 mg/kg soil, in
both the preliminary range-finding and the definitive test. In the
preliminary test, no deaths occurred after 14 days' exposure at a
concentration of < 100 mg/kg soil, but there was 100% mortality at
500 and 1000 mg/kg. In the final test, 0, 5, 75, 100, and 100% of
earthworms died after 14 days' exposure to 100, 200, 300, 400, and
500 mg/kg, respectively. Mean weight losses of 47-62 mg per worm were
reported after exposure to concentrations of 100-300 mg/kg, but as a
weight loss of 47 mg was reported in the controls and the soil
moisture content for all groups fell below the recommended 35%, the
body-weight losses were not considered to be treatment-related but
probably due to dehydration of the worms. The 14-day NOEC was
100-200 mg/kg soil on the basis of mortality. The study was conducted
according to the OECD 207 test guideline (Kühner, 1992).

In a 56-day test in artificial soil, the effect of a 120 g/litre
EC formulation of fenarimol was observed on the reproduction of the
earthworm Eisenia foetida (Bauer & Dietze, 1993). Earthworms were
exposed to soil that was sprayed directly with fenarimol at an
application rate of 378 or 1890 g/ha. After 28 days, 2.5% mortality
was seen at both test concentrations but was not considered to be
treatment related. The mean biomass of treated earthworms was not
significantly different (3.8-4.4% difference) from that of the control
group at day 0 or 28 after treatment. Similarly, the numbers of
offspring per surviving adult after 56 days (6.5 and 6.4 at 378 and
1890 g/ha) were not significantly different from that of the control
group (6.3). No morphological or behavioural symptoms of toxicity were
reported during the trial. Application of this formulation of
fenarimol at rates up to 1890 g/ha thus had no effect on the
reproduction of Eisenia foetida. The study was conducted according
to a draft BBA guideline.

Birds: Fenarimol had low acute oral toxicity to bobwhite quail
(Colinus virginianus), with an LD₅₀ of > 2000 mg/kg bw and an
NOEC of 2000 mg/kg bw (the highest dose tested) (Kehr et al.,
1978b). In a poorly reported study of oral toxicity, fenarimol was
found to have little acute toxicity to mallard ducks (Anas

platyrynchos) or bobwhite quail, with an LD₅₀ of > 200 mg/kg bw
(the only dose tested) for both species (Hoffman et al., 1975).
Fenarimol was found to have an eight-day LC₅₀ for mallard ducks of
> 6250 ppm (Kehr et al., 1978c). The NOEC was reported to be
1250 ppm, on the basis of reduced body weight gain during a three-day
recovery phase at the highest dose; however, as reduced food consump-
tion resulting in statistically significantly reduced body-weight gain
was reported at all concentrations during the five-day exposure
period, the NOEC is < 50 ppm (the lowest concentration tested). The
eight-day LC₅₀ for bobwhite quail was > 6250 ppm (Kehr et al.,
1978d). The NOEC was again reported to be 1250 ppm on the basis of
reduced feed intake and a consequential statistically significant
reduction in body-weight gain during both the exposure and recovery
period at 6250 ppm; however, as a statistically significant reduction
in body-weight gain was also reported during the recovery period after
1250 ppm, perhaps indicating a dose-response relationship, the NOEC is
250 ppm fenarimol.

In a one-generation study of reproductive toxicity, which was not
conducted according to any recognized standard protocol but which
broadly conformed to OECD test guideline 206, fenarimol was reported
to have little toxicity to mallard ducks, with 4, 16, 4, and 4% of
adults dying at 0,10, 50, and 250 ppm fenarimol, respectively (Fink,
1977). As all of the deaths were in females, no dose-response
relationship was evident, and no signs of gross abnormalities were
seen at necropsy, the effects were considered not to be related to
treatment but to the stress of egg laying. No statistically
significant effects were seen on reproductive parameters, such as the
numbers of eggs laid and cracked, eggshell thickness, viable embryos,
live three-week embryos, normal hatchling, and 14-day survivors, at
any dose tested. The NOEC was stated to be 250 ppm (the highest dose
tested), but the number of eggs laid was reduced by 9.2% at 50 ppm and
27% at 250 ppm; this result may have been dose-related although not
statistically significant. As the raw data were not available to
confirm whether this reduction was dose-related, the NOEC is in fact
50 ppm, on the basis of the 27% reduction in the number of eggs laid
at the highest dose.

In a one-generation study of reproductive toxicity, which was not
conducted according to any recognized standard protocol but which
broadly conformed to OECD test guideline 206, fenarimol was also
reported to have low reproductive toxicity to bobwhite quail (Hoffman
et al., 1980). In this study, 13% of adults at 0 and 50 ppm died,
and this was attributed to trauma caused by aggressive male behaviour;
however, there was a further 13% adult mortality at 50 ppm (for a
total of 26%) for which the cause was not evident. As there were no
deaths at the next highest dose (125 ppm fenarimol), and the eight-day

dietary LC₅₀ for this species was reported to be > 6250 ppm, the
deaths at 50 ppm were not considered to be treatment-related. A
statistically significant reduction in the number of eggs laid was
seen at 50 ppm; however, as no such effect was reported at the next
highest dose, it is unlikely to be treatment-related. The NOEC was
125 ppm.

In a further one-generation study of reproductive toxicity in
bobwhite quail, conducted in accordance with EPA 71-4 test guideline
and which conformed to OECD test guideline 206, fenarimol was again
reported to have little reproductive toxicity to bobwhite quail, with
an NOEC of 300 ppm (Hoffman & Cochrane, 1987). No statistically
significant or dose-related effect was reported on any of the
reproductive parameters measured, including egg production, number of
eggs cracked, eggshell thickness, number of eggs set, fertility,
embryo survival, hatchability, and hatchling survival.

Mammals: No additional data were submitted on the toxicity of
fenarimol-containing products to terrestrial vertebrate species other
than those reported in Section 7.

5.2 Risk assessment based on agricultural use

The information on use and application rates used for this risk
assessment is derived from the agricultural use of fenarimol within
the European Union. It should be possible to extrapolate the
assessment to other agricultural uses at similar application rates
elsewhere in the world.

5.2.1 Microorganisms

The most significant routes of overexposure of soil micro-
organisms to fenarimol are from the high application rates made to
turf and the multiple applications made every season in orchards.

(a) Turf

The maximal rate of application of fenarimol to turf is 6 kg/ha,
as four applications of 1.5 kg/ha per year. As reported above, no
significant effect on soil respiration or soil microbial populations
was seen 98 days after application at a rate equivalent to 168 kg/ha,
which is 28 times the maximal recommended field rate. No effect on
soil nitrification processes was seen after 15 days at 100 ppm (7 kg
a.i./ha) in a growth medium or 28 days at 5 kg/ha in a soil test.
These results broadly meet the EPPO (1993) threshold for acceptability
of < 25% effect after 100 days, thus indicating that the risk to soil
microbial processes from use of fenarimol on turf is low.

(b) Orchards

The maximal rate of application of fenarimol in orchards is
1.1 kg/ha, from 14 applications of 0.076 kg/ha per year. The data on
microbial toxicity presented above indicate that it has no significant
effect on soil respiration or microbial processes 98 days after an
application equivalent to 168 kg/ha, which is two orders of magnitude
higher than the maximal recommended field rate. This result broadly
meets the EPPO (1993) threshold for acceptability of < 25% effect
after 100 days, thus indicating that the risk to soil microbial
processes from use of fenarimol in orchards is low.

5.2.2 Aquatic organisms

The first route of high water contamination considered in aquatic
risk assessment is overspray, and then the exposure assessment is
refined to reflect spray drift. The maximal rates of application
within the European Union in categories other than on turf do not
differ significantly: 0.12 kg a.i./ha in orchards, 0.06 kg a.i./ha on
grapes and hops, and 0.084 kg a.i./ha for other arable and horticul-
tural uses; furthermore, multiple applications should not result in an
accumulation in surface water, as fenarimol is rapidly removed from
the aqueous phase into the sediment phase, with a DT₅₀ of less than
seven days in the aqueous phase (see above). The categories orchards,
hops and grapes, and other arable and horticultural uses are therefore
grouped into a general 'arable and horticultural' category for the
purposes of aquatic risk assessment, and 'turf' uses are considered
separately, as follows:

- application to turf by tractor-mounted and -drawn arable sprayer
at 1.5 kg/ha, and

- arable and horticultural application by tractor-mounted and
-drawn arable sprayer at 0.084 kg/ha and air-assisted sprayer at
0.12 kg/ha.

The predicted environmental concentration (PEC) in surface water is:

(a) Acute risk to pelagic organisms

The acute LC₅₀ and EC₅₀ values for the most sensitive fish,
aquatic invertebrates, and algae reported in section 5.1.2 were
0.8 mg/litre for rainbow trout (Oncorhynchus mykiss), 0.18 mg /litre
for Daphnia magna, and 0.76 mg/litre for Raphidocellis subcapitata.
These values were used in the 'worst-case' risk assessment for acute
exposure of aquatic organisms.

Use on turf: Aquatic life may be exposed to fenarimol from its
use as the SC formulation on turf after contamination of surface water
by direct overspray, spray drift, leaching, or run-off. The 'worst-
case' acute surface water PEC for turf use has been calculated as
0.5 mg/litre fenarimol, based on direct overspray contamination of a
3-cm deep static water body at the maximal individual application
rate.

The TERs for overspray based on the acute PECs and data on
toxicity reported in section 5.1.2, were 1.64 for fish, 0.36 for
aquatic invertebrates, and 1.52 for algae, indicating a high risk
(i.e. lower than the 'acceptable' EPPO (1993) threshold of 10) for all
aquatic organisms.

Contamination of water by overspray is, however, the worst case,
and a more realistic route of contamination is spray drift. On the
basis of German BBA data on spray drift -- 5% spray drift at 1 m for
arable tractor-mounted and -drawn hydraulic sprayers -- the PEC would
be 0.025 mg/litre 1 m from the point of application to turf. If this
acute PEC is used, the TERs for spray drift would be revised to 32 for
rainbow trout, 7.2 for Daphnia, and 30 for algae, indicating a low
acute risk, although the value for Daphnia indicates an acute risk
for aquatic invertebrates. Since fenarimol is rapidly removed from the
aqueous phase (see section 4), however, the acute risk to fish,
aquatic invertebrates, and algae is probably low.

Arable and horticultural use: Aquatic life may be exposed to
fenarimol in arable and horticultural uses as a result of contam-
ination of surface water by direct overspray, spray drift, leaching,
or run-off. The 'worst-case' PEC for acute contamination of surface
water from this use has been calculated as 0.024 mg/litre for tractor-
mounted spray-boom applications and 0.04 mg/litre for air-assisted
applications in orchards, based on direct overspray contamination of a
30-cm deep static water body at the maximal individual application
rate.

For tractor-mounted spray-boom applications, the TERs for
overspray based on these acute PEC values and the data on toxicity
reported in section 5.1.2 were 34.2 for fish, 7.5 for aquatic
invertebrates, and 31.2 for algae. The values for fish and algae are
higher than the 'acceptable' EPPO (1993) threshold of 10, indicating
that the acute risk should be low. The TER for Daphnia indicates,
however, that there may be an acute risk for aquatic invertebrates.
Since fenarimol is rapidly removed from the aqueous phase (see section
4), the acute risk to fish, aquatic invertebrates, and algae should be
low.

For air-assisted spray applications in orchards, the TERs for
overspray based on the acute PEC values and the data on toxicity
reported in section 5.1.2, were 20.5 for fish, 4.5 for aquatic
invertebrates, and 19 for algae. These values are higher than the
'acceptable' EPPO (1993) threshold of 10, indicating that the acute
risk to fish and algae should be low; however, the TER for Daphnia
indicates that there may be an acute risk for aquatic invertebrates.
Since fenarimol is rapidly removed from the aqueous phase (see section
4), the acute risk to fish, aquatic invertebrates, and algae should be
low. The TER for spray drift based on 30% deposition at 3 m would
increase to 25, indicating a low risk for aquatic invertebrates.

(b) Long-term risk for aquatic organisms

The long-term NOEC values reported in section 5.1.2 for the most
sensitive aquatic species tested were 0.43 mg/litre in a 69-day study
of rainbow trout and 0.113 mg/litre in a 21-day study in Daphnia
magna. These values were used in the 'worst-case' risk assessment
for acute exposure of aquatic organisms.

Use on turf: Aquatic life may be exposed to fenarimol for long
periods due to its use on turf as a result of initial contamination
from overspray or spray drift from up to four successive applications
The 'worst-case' PEC for acute contamination of surface water from
this use has been calculated on the basis of initial direct contam-
ination from overspray of a 30-cm deep, static water body at the
maximal individual application rate (see (a) above). As fenarimol is
rapidly removed from the aqueous phase of natural sediment-water
systems by either photolysis or adsorption onto sediment, with a
DT₅₀ in the aqueous phase of less than seven days (see section 4),
the long-term PEC for surface water from overspray is unlikely to
exceed the acute PEC. With a DT₅₀ of one day, only 0.000003 mg/litre
fenarimol of an original 0.5 mg/litre is likely to remain after 14
days. Up to four applications can be made to turf, within a minimal
interval of 21-42 days. The mean concentration over 14 days after one
application of 1.5 kg/ha of 0.25 mg/litre on turf is used as the
'worst-case' long-term PEC for surface water. The long-term TERs based
on this PEC and the data on toxicity reported in section 5.1.2 were
1.72 for rainbow trout and 0.45 for Daphnia magna. These values are
lower than the 'acceptable' EPPO (1993) threshold of 10, indicating
that there may be a risk to fish and aquatic invertebrates from
long-term contamination of water from overspray on turf.

Contamination of water by overspray is, however, the worst case,
and a more realistic route of contamination is spray drift. On the
basis of German BBA data on spray drift-5% spray drift at 1 m for
arable tractor-mounted and -drawn hydraulic sprayers -- the PEC would
be 0.025 mg/litre for spray drift 1 m from the point of application to
turf, which would fall to about 0.0000015 mg/litre after 14 days (for
a DT₅₀ of one day), resulting in a mean PEC for exposure to spray
drift over 14 days of 0.0125 mg/litre. The TERs would be 34.4 for
rainbow trout and 9.04 for Daphnia The TER for fish is higher than
the EPPO (1993) threshold of < 10 for unacceptable effects,
indicating that the long-term risk for this species of use of
fenarimol on turf should be low. Although the TER for Daphnia is
9.04, the fact that fenarimol is rapidly removed from the aqueous
phase indicates that the long-term risk for free-swimming aquatic
invertebrates should also be low.

Arable and horticultural use: Aquatic life may be exposed to
fenarimol in arable and horticultural uses as a result of
contamination of water by multiple overspraying or spray drift. The
'worst-case' PEC for long-term contamination of surface water from
this use has been calculated on the basis of an initial contamination
by overspray of a 30-cm deep, static water body at the maximal
individual application rates of 0.084 kg/ha for tractor-mounted
spray-boom applications and 0.12 kg/ha for air-assisted applications
in orchards.

In tractor-mounted spray-boom applications, fenarimol is rapidly
removed from the aqueous phase of natural sediment-water systems by
either photolysis or adsorption onto sediment, resulting in a DT₅₀
in the aqueous phase of less than seven days (see section 4). The
long-term PEC in surface water from overspray is therefore unlikely to
exceed the acute PEC. With a DT₅₀ of one day, only 0.00019 mg/litre
of an original acute PEC of 0.024 mg/litre should remain after seven
days. As up to three applications can be made to crops with a minimal
interval of 10-14 days, the mean concentration of 0.012 mg/litre over
each 10-day period was used as the 'worst-case' long-term PEC in
surface water for multiple spray-boom applications of fenarimol in
agricultural and horticultural uses.

The long-term TERs derived from these PEC values and data on
toxicity reported in section 5.1.2 were 35.8 for rainbow trout and 9.4
for Daphnia magna. As the value for rainbow trout is higher than the
'acceptable' EPPO (1993) threshold of 10, the long-term risk to fish
is low; however, the value for Daphnia magna is just below the
threshold of 10, indicating that this risk should be investigated
further. This long-term PEC, based on multiple initial overspraying at
the maximal application rate and at the minimal spray interval, is,
however, the worst case. The value likely in the field may well be
lower, taking into consideration the rapid adsorption of fenarimol
onto sediment and its rapid photolysis. It was therefore considered
that the TER for Daphnia magna is acceptable and indicates a low
long-term risk for free-swimming aquatic invertebrates.

In air-assisted spray applications in orchards, fenarimol is
rapidly removed from the aqueous phase of natural sediment-water
systems by either photolysis or adsorption onto sediment, resulting in
a DT₅₀ in the aqueous phase of less than seven days (see section 4).
The long-term PEC in surface water from overspray is therefore
unlikely to exceed the acute PEC. With a DT₅₀ of one day, only
0.00032 mg/litre of an original acute PEC of 0.04 mg/litre should
remain after seven days. As up to four applications can be made to
crops with a minimal spray interval of 14 days, the mean concentration
of 0.02 mg/litre over each 14-day period was used as the 'worst-case'
long-term PEC in surface water for multiple air-assisted spray
applications of fenarimol in agricultural and horticultural uses. The
chronic TERs based on these PECs and data on toxicity reported in
section 5.1.2 were 21.5 for rainbow trout and 5.7 for Daphnia magna.

As the value for rainbow trout is higher than the 'acceptable' EPPO
(1993) threshold of 10, the long-term risk for fish is low; however,
the value for Daphnia magna is below the threshold of 10, indicating
that this risk should be investigated further.

Contamination of water by overspray is, however, the worst case,
and a more realistic route of contamination is spray drift. On the
basis of German BBA data on spray drift -- 30% spray drift at 3 m for
air-assisted sprayers -- the PEC would be 0.012 mg/litre for spray
drift 3 m from the point of application which would fall to 0.00000075
mg/litre after 14 days (for a DT₅₀ of one day), resulting in a mean
PEC for exposure to spray drift over 14 days of 0.006 mg/litre. On the
basis of this PEC, the TER for Daphnia would be 18.8, which is
higher than the EPPO (1993) threshold of < 10 for unacceptable
effects, indicating that the chronic risk to pelagic aquatic inverte-
brates from air-assisted applications of fenarimol in orchards should
be low.

It is reported in section 4 that 75-80% of fenarimol is
partitioned into the sediment phase of natural sediment-water systems
within seven days. Therefore, fenarimol entering water due to
overspraying, spray drift, leaching, or surface run-off may pose a
risk to sediment-dwelling invertebrates. Once fenarimol enters the
sediment, there is no appreciable degradation over 80 days, indicating
that there may be a long-term risk to sediment-dwelling invertebrates.

The PEC in pore water (between sediment particles), calculated by
equilibrium partitioning:

Use on turf: The total maximal amount of fenarimol applied to
turf in one year is about 6 kg/ha. On the basis of the assumptions of
overspraying made in the section on acute risk (overspraying of a
30-cm deep, static water body at the maximal application rate) and
assuming that overspraying occurs in all applications, the total
amount of fenarimol entering the surrounding water in one year would
be 2 mg/litre. Assuming further that all of this amount partitions
into a 5-cm layer of sediment (from a 30-cm water column) and a
sediment density of 1.5 g/cm³, the total concentration of fenarimol
in sediment would be 8 mg/kg. Using equilibrium partitioning, the
concentration of fenarimol in the pore water of these sediments,
assuming a K_oc of 500 (section 4) and an organic carbon content of
2%, would be about 0.8 mg/litre. On the basis of the long-term NOEC
for Daphnia magna of 0.113 mg/litre (section 5.1.2) as an indicator
of the toxicity of fenarimol to sediment-dwelling invertebrates, the
TER would be 0.14, indicating a risk from overspraying on turf.

Contamination of water by overspray is, however, the worst case,
and a more realistic route of contamination is spray drift. On the
basis of 5% drift at 1 m for application to turf (German BBA), the
concentrations of fenarimol in sediment pore water would be reduced to
about 0.04 mg/litre. On the basis of the long-term NOEC for Daphnia
magna of 0.113 mg/litre (section 5.1.2) as an indicator of the
toxicity of fenarimol to sediment-dwelling invertebrates, the TER
would be 2.8, indicating a long-term risk. The high application rate
is, however, essentially a 'spot' treatment on e.g. golf courses, and
such highly localized, small-scale applications would result in a low
risk for sediment-dwelling invertebrates.

Arable and horticultural use: The total maximal amount of
fenarimol applied to any one crop in one year is about 0.36 kg/ha (5 ×
0.072 kg/ha on ornamental plants) for tractor-mounted spray-boom
applications and 1 kg/ha (14 × 0.072 kg/ha in orchards) for air-
assisted applications. On the basis of the assumptions of overspraying
made in the section on acute risk (overspraying of a 30-cm deep,
static water body at the maximal application rate) and assuming that
overspraying occurs in all applications, the total amount of fenarimol
entering the surrounding water in one year could be 0.12 mg/litre by
tractor-mounted spray-boom application and 0.33 mg/litre by air-
assisted application. Assuming further that all of this amount
partitions into a 5-cm layer of sediment (from a 30-cm water column)
and a sediment density of 1.5 g/cm³, the total concentration of
fenarimol in sediment would be 0.48 mg/kg with spray-boom application
and 1.32 mg/kg with air-assisted application. Using equilibrium
partitioning, the concentration of fenarimol in the pore water of
these sediment, assuming a K_oc of 500 (section 4) and an organic
carbon content of 2%, would be about 0.048 mg/litre for spray-boom
application and 0.132 mg/litre for air-assisted application. On the

basis of the long-term NOEC for Daphnia magna of 0.113 mg/litre
(section 5.1.2) as an indicator of the toxicity of fenarimol to
sediment-dwelling invertebrates, the TERs would be 2.4 for spray-boom
application and 0.86 for air-assisted application. Sediment-dwelling
invertebrates may therefore be at risk from overspraying by either
route of application.

Contamination of water by overspray is, however, the worst case,
and a more realistic route of contamination is spray drift. On the
basis of 5% drift at 1 m for spray-boom application on arable land and
30% drift at 3 m for air-assisted application in orchards (German
BBA), the concentrations of fenarimol in sediment pore water would be
reduced to about 0.0024 mg/litre for spray-boom application and
0.04 mg/litre for air-assisted application. On the basis of the
long-term NOEC for Daphnia magna of 0.113 mg/litre (section 5.1.2)
as an indicator of the toxicity of fenarimol to sediment-dwelling
invertebrates, the TERs would be 47 for spray-boom application and 2.8
for air-assisted application, indicating a low risk from spray-boom
applications but a long-term risk from air-assisted application. Data
on the long-term toxicity of fenarimol to a sediment-dwelling species
such as Chironomus would be useful for refining this predicted risk.

5.2.3. Terrestrial organisms

(a) Plants

No data were available.

(b) Invertebrates

Bees: Honey bees may be exposed to fenarimol during e.g.
application to turf at a maximal rate or orchards with attractive
flowering trees. Fenarimol was reported to have low acute toxicity to
honey bees, with an oral LD₅₀ of > 10 µg/bee and a contact LD₅₀
of > 100 µg/bee (section 5.1.3).

Bees may be exposed to fenarimol while foraging on flowering
weeds during or after application. The hazard ratio for use of
fenarimol on turf -- application rate (g/ha) divided by the LD₅₀
(µg/bee) -- based on an application rate of 1.5 kg/ha and the data on
toxicity reported in section 5.1.3 is < 150 for acute oral exposure
and < 15 for acute contact. The hazard ratio for oral exposure is
lower than the EPPO (1993) threshold of 50 for 'acceptable' effects,
indicating that the acute risk for bees grazing treated turf is low;
however, the contact hazard ratio is higher than the EPPO threshold of
50, indicating that there may be a risk. Fenarimol is applied to turf
mainly in autumn and winter, however, when bees are unlikely to be
foraging. The risk of exposure, and therefore the risk, are thus
considered to be low.

Bees may also be exposed to fenarimol by foraging the flowers of
treated crops or flowering weeds present in the crops. The hazard
ratios for such use, based on a maximal application rate of 0.12 kg/ha
and the data on toxicity reported in section 5.1.3, are < 12 for
acute oral exposure and < 1.2 for acute contact. Both ratios are
below the EPPO threshold of 51) for 'acceptable' effects, indicating a
low risk for honey bees from these uses of fenarimol.

Non-target arthropods: Non-target arthropods may be exposed to
fenarimol e.g. from use on turf at the maximal rate or multiple
applications on orchards. Small water volumes (200-500 litres/ha) are
applied in northern Europe, whereas volumes up to an order of
magnitude higher (1500-2000 litres/ha) are used in southern Europe.

No data from standard laboratory tests were submitted for
non-target arthropod species. A 120-g/litre EC formulation of
fenarimol applied at 140 mg/litre was 'harmless' (< 50% effect) to
selected non-target arthropods, including the aphid-specific parasi-
toid Aphidius matricariae and the predatory mite Typhlodromus pyri
(see section 5.1.3). As the EPPO (1993) threshold for further testing
is > 30% effect in laboratory tests, it should be ascertained whether
the value' < 50% is above that threshold; however, data from semi-
field tests showed a < 25% effect on Typhlodromus pyri at a
concentration of 140 mg/litre fenarimol. As the concentrations sprayed
at a volume of 300 litres/ha ranged from 400 mg/litre in orchards to a
maximum of 5000 mg/litre on turf, these data do not fully address the
probable effects of fenarimol at relevant concentrations or appli-
cation rates, particularly in northern Europe where low-water-volume
applications are prevalent.

One spraying with a 120 g/litre EC formulation of fenarimol at a
concentration of 40 g/litre and an application rate of 60 g/ha in a
Belgian orchard had no adverse effect on populations of non-target
arthropods (see section 5.1.3); however, the maximal recommended
application rate (120 g a.i./ha) was used in a single application,
whereas fenarimol can be applied up to 14 times at intervals of 7-14
days.

The data indicate that the risk to non-target arthropods should
be low, but no results were available from standard laboratory tests
with the internationally agreed indicator species Typhlodromus pyri
and Aphidius rhopalosiphi (as recommended by Barret et al., 1994)
and with the approved maximal application rate and number of applica-
tions, particularly in orchards. Such data would be useful for
addressing fully the risk for non-target arthropods of exposure to
fenarimol.

Earthworms: The most significant sources of overexposure of
earthworms to fenarimol are due to the high rates of application to
turf and the multiple applications made each season in orchards.
Fenarimol was moderately toxic to earthworms, with a 14-day LC₅₀ of
200-300 mg/kg of soil for the EC formulation and a 56-day NOEC for
reproductive toxicity of 1890 g/ha (see section 5.1.3).

The PEC in the top 5 cm of soil after four successive applica-
tions of fenarimol at 1.5 kg/ha on turf is 8.57 mg/kg, assuming that
the soil density is 1.4 g/cm³, that all of the applied fenarimol
enters the soil, and that no degradation occurs between applications
(DT₅₀ in laboratory soil, 436-1833 days; section 4). The short-term
TER based on this PEC and LD₅₀ values would be 23-35, which is
higher than the EPPO (1993) threshold of 10 and indicates a low acute
risk for earthworms. When the short-term TER is < 100 and the active
substance persists in soil (DT₉₀ > 100 days), EPPO (1993) requires
that expert judgement be used to assess whether further data are
needed on sublethal toxicity.

The TER based on the 14-day NOEC of 100-200 mg/kg of soil would
be 12-23, indicating a low risk for sublethal effects. In addition, a
study of reproductive toxicity in earthworms with the EC formulation
showed a 56-day NOEC of 1890 g/ha, which is greater than the maximal
individual application rate to turf and 0.32 times the maximal
recommended seasonal application rate; this was the highest dose
tested. In a further study, earthworms did not bioaccumulate
technical-grade fenarimol over the concentration in the surrounding
soil (see section 4). The additional information that degradation of
fenarimol is faster in the field than in the laboratory (DT₅₀ in
soil in the field, 14-130 days; section 4) indicates that the risk (or
sublethal effects in earthworms from the use of fenarimol on turf
should be low.

The PEC in the top 5 cm of orchard soil after 14 successive
applications of fenarimol on apples at 0.072 kg/ha is 1.44 mg/kg of
soil, assuming that the soil density is 1.4 g/cm³, that all of the
applied fenarimol enters the soil, and that no degradation occurs
between applications (DT₅₀ in laboratory soil, 436-1833 days;
section 4). The short-term TER based on this PEC and LD₅₀ values
would be 139-208, which is higher than the EPPO (1993) threshold of
100 for unacceptable effects and indicates a low acute risk for
earthworms from use of fenarimol in orchards.

The risk for vertebrates is assessed for four broad categories of
use:

- in orchards, on apples, pears, peaches, and cherries, at maximal
application rates of 0.12 kg/ha of the wettable powder on peaches
and 0.06 kg/ha of the EC formulation on cherries;

- on hops and grapes, with a maximal application rate of 0.06 kg/ha
of the wettable powder on grapes;

- on turf, with a maximal application rate of 1.5 kg/ha on amenity
and sports turf; and

- other horticultural and arable uses, including cane fruit,
ornamental plants, and vegetables, with a maximal application
rate of 0.084 kg/ha of the EC formulation on strawberries.

Birds: LD₅₀ values of > 200 and > 2000 mg/kg bw were
reported in two studies of bobwhite quail (see section 5.1.3);
however, the first value was derived from a poorly reported study
conducted with insufficiently high doses. The value of > 2000 mg/kg
bw was therefore used to assess the risk for oral exposure of the most
sensitive species tested. The eight-day dietary LC₅₀ of > 6250 ppm
fenarimol for mallard duck and bobwhite quail was also used.

The examples used were:

- a small insectivorous bird, an 11-g blue tit (Parus caeruleus),
with a total daily food consumption of 8.25 g, based on 3.3 g dry
weight of food per day (Kenaga, 1973);

- a fruit-eating bird, an 80-g starling (Sturnus vulgaris), with
a total daily food consumption of 60 g, based on 24 g dry weight
of food per day (EPPO, 1993);

- a grazing bird, a 3-kg greylag goose (Anser anser), with a
total daily food consumption of 900 g (Owen, 1975); and

- an earthworm-eating bird, an 89-g song thrush (Turdus
philomelos), with a total daily food consumption of 22 g, based
on 8.8 g dry weight of food per day (Kenaga, 1973).

In orchards, birds are exposed from eating either oversprayed
insects or treated fruit contaminated with fenarimol residues. The
initial residues expected on insects oversprayed at the maximal
application rate of 0.12 kg/ha are 3.48 mg/kg of small insects (EPPO,
1993). The short-term dietary TER, based on a dietary eight-day LC₅₀
> 6250 ppm fenarimol, would therefore be > 1796. If the total daily
food of a blue tit were contaminated insects, it would take in
0.029 mg of fenarimol, or 2.61 mg/kg bw. The acute oral TER based on
the acute oral LD₅₀ of > 2000 mg/kg bw would therefore be > 766.
Both of these TERs are greater than the EPPO (1993) threshold of 100,
indicating that the acute risk for insectivorous birds in orchards
treated with fenarimol should be low.

The initial residues expected on cherries oversprayed at the
maximal application rate of 0.06 kg/ha is 0.078 mg/kg of fruit (EPPO,
1993). The short-term dietary TER, based on a dietary eight-day LC₅₀
> 6250 ppm fenarimol, would therefore be > 80 128. If the total
daily food of a starling were contaminated cherries, it would take in
0.005 mg of fenarimol, or 0.063 mg/kg bw. The acute oral TER based on
the acute oral LD₅₀ of > 2000 mg/kg bw would therefore be > 31
746. Both of these TERs are greater than the EPPO (1993) threshold of
100; however, residues in cherries before harvesting have been
reported to be as high as 0.89 mg/kg of fruit. As this residue is only
one order of magnitude higher than the predicted initial residues used
to calculate the TERs, those based on residues at harvesting will
still be far higher than the threshold value, and the acute risk for
fruit-eating birds in orchards treated with fenarimol should be low.

In hop gardens and vineyards, birds are exposed from eating
either oversprayed insects or treated fruit contaminated with
fenarimol residues. The initial residues expected on insects
oversprayed at the maximal application rate of 0.06 kg/ha is
1.74 mg/kg of small insects (EPPO, 1993). The short-term dietary TER,
based on a dietary eight-day LC₅₀ > 6250 ppm fenarimol, would
therefore be > 3592. If the total daily food of a blue tit were
contaminated insects, it would take in 0.014 mg of fenarimol, or
1.31 mg/kg bw. The acute oral TER based on the acute oral LD₅₀ of >
2000 mg/kg bw would therefore be > 1527. Both of these TERs are
greater than the EPPO (1993) threshold of 100, indicating that the
acute risk for insectivorous birds in hop gardens and vineyards
treated with fenarimol should be low.

The initial residues expected on grapes oversprayed at the
maximal application rate of 0.06 kg/ha is 0.078 mg/kg of fruit (EPPO,
1993). The short-term dietary TER, based on a dietary eight-day LC₅₀
> 6250 ppm fenarimol, would therefore be > 80 128. If the total
daily food of a starling were contaminated grapes, it would take in
0.005 mg of fenarimol, or 0.063 mg/kg bw. The acute oral TER based on
the acute oral LD₅₀ of > 2000 mg/kg bw would therefore be >
31 746. Both of these TERs are greater than the EPPO (1993) threshold
of 100. Residues in grapes before harvesting have been reported to be
as high as 0.04 mg/kg, which is lower than the predicted initial
residues used to calculate the TERs and indicates that the risk for
birds eating grapes around harvest time is less than that for birds
eating grapes immediately after application. The values indicate that
the acute risk to fruit-eating birds in vineyards and hop gardens
treated with fenarimol should be low.

When fenarimol is applied to turf, birds are likely to be exposed
either by grazing treated grass or eating earthworms contaminated with
fenarimol residues. The initial residue expected on short grass
oversprayed at 1.5 kg/ha is 168 mg/kg of grass (EPPO, 1993). The
short-term dietary TER, based on a dietary eight-day LC₅₀ of >

6250 ppm fenarimol, would therefore be > 37.2. If the total daily
food of a greylag goose were contaminated grass, it would take in
151 mg of fenarimol, or 50.3 mg/kg bw. The acute oral TER based on the
acute oral LD₅₀ of > 2000 mg/kg bw would therefore be > 39.7. Both
of these TERs are lower than the EPPO (1993) threshold of 100, which
requires that the risk be assessed further. As application is done
mainly in autumn and winter, the initial residues are unlikely to
remain for long before being washed off or diluted by rainfall. In
addition, the values for toxicity used in the risk assessment are
'greater than' values, and the actual TERs may well be significantly
higher than those currently reported. Furthermore, although the United
Kingdom has the highest application rate to turf within the European
Union, no incidents of bird poisoning involving fenarimol have been
reported in the UK Wildlife Incident Investigation Scheme. The risk to
grazing birds from the use of fenarimol on turf would therefore appear
to be low.

The expected residue of fenarimol in soil after application of
6 kg/ha, in four applications of 1.5 kg/ha per year with no signi-
ficant degradation in soil (DT₅₀ in field soil, 14-130 days; see
section 5.1.3), is 8.58 mg/kg of soil, assuming a soil depth of 5 cm
and bulk density of 1.4 g/cm³. As at an application rate equivalent
to 7 kg/ha (10 mg/kg of soil) earthworms did not accumulate residues
at concentrations greater than those in the surrounding soil, the
maximal concentration of fenarimol in the earthworms would be
8.58 mg/kg. The short-term dietary TER, based on a dietary eight-day
LC₅₀ of > 6250 ppm fenarimol, would therefore be > 728. If the
total daily food of a song thrush were contaminated earthworms, it
would take in 0.19 mg of fenarimol, or 2.12 mg/kg bw. The acute oral
TER based on the acute oral LD₅₀ of > 2000 mg/kg bw would therefore
be > 943. Both of these TERs are greater than the EPPO (1993)
threshold of 100, indicating that the acute risk for earthworm-eating
birds on turf treated with fenarimol should be low.

In other agricultural and horticultural uses of fenarimol, birds
are likely to be exposed by consuming either oversprayed insects or
treated produce (e.g. strawberries) contaminated with fenarimol
residues. The initial residues expected on insects oversprayed at
0.084 kg/ha is 2.44 mg/kg of small insects (EPPO, 1993). The short-
term dietary TER, based on a dietary eight-day LC₅₀ > 6250 ppm
fenarimol, would therefore be > 2561. If the total daily food of a
blue tit were contaminated insects, it would take in 0.02 mg of
fenarimol, or 1.83 mg/kg bw. The acute oral TER based on the acute
oral LD₅₀ of > 2000 mg/kg bw would therefore be > 1093. Both of
these TERs are greater than the EPPO (1993) threshold of 100,
indicating that the acute risk for insectivorous birds in other arable
and horticultural uses of fenarimol should be low.

The initial residues expected on strawberries oversprayed at
0.084 kg/ha is 0.12 mg/kg of fruit (EPPO, 1993). The short-term
dietary TER, based on a dietary eight-day LC₅₀ > 6250 ppm
fenarimol, would therefore be > 52 083. If the total daily food of a
starling were contaminated insects, it would take in 0.007 mg of
fenarimol, or 0.09 mg/kg bw. The acute oral TER based on the acute
oral LD₅₀ of > 2000 mg/kg bw would therefore be > 22 222. Both of
these TERs are greater than the EPPO (1993) threshold of 100; however,
residues in strawberries before harvesting have been reported to be as
high as 0.14 mg/kg of fruit. As this residue is within one order of
magnitude of the predicted initial residues used to calculate the
TERs, those based on residues at harvesting will still be far higher
than the threshold value, and the acute risk for these birds from the
use of fenarimol should be low.

NOEC values of 125 and 300 ppm fenarimol have been reported for
reproductive toxicity in bobwhite quail in two studies (see section
5.1.3); an NOEC of 250 ppm was reported tor mallard ducks but was
revised to 50 ppm. The last value was used in the risk assessment for
the most sensitive species tested. The main risk for reproducing birds
is during multiple applications throughout a season. The 'worst case'
of > 14 applications of a wettable powder tormulation of fenarimol
on apples and pears in orchards at 0.076 kg/ha in any one season was
investigated. In orchards, breeding birds are likely to be exposed
by eating oversprayed insects or treated fruit (e.g. cherries)
contaminated with fenarimol residues.

The expected initial residue on small :insects oversprayed with
fenarimol at 0.076 kg/ha is 2.2 mg/kg (EPPO, 1993). The TER for
reproductive toxicity, based on the NOEC of 50 ppm, would therefore be
22.7. This value is greater than the EPPO (1993) threshold of 10,
indicating a low risk to insectivorous birds in orchards treated with
fenarimol.

The expected initial residues on cherries oversprayed with
fenarimol at 0.06 kg/ha is 0.078 mg/kg of fruit (EPPO, 1993). The TER
for reproductive toxicity, based on the NOEC of 50 ppm, would
therefore be 642; however, residues in cherries before harvesting have
been reported to be as high as 0.89 mg/kg. Use of this residue value
would reduce the TER to 56. Both of these values are greater than the
EPPO (1993) threshold of 10, indicating that the risk for reproductive
toxicity to fruit-eating birds in orchards treated with fenarimol
should be low.

Mammals: An oral LD₅₀ for fenarimol of 2500 mg/kg bw was
reported in rats, the most sensitive species tested, and this value
was used in the risk assessment.

The examples used were:

- a small earthworm-eating mammal, an 18-g common shrew
(Sorex araneus), with a total daily food consumption of 18 g
(Churchfield, 1986);

- a small fruit-eating mammal, an 18-g wood mouse (Apodemus
sylvaticus), with a total daily food consumption of 7.5 g
food/day, based on 3 g dry weight of food per day (Corbet &
Harris, 1991); and

- a grazing mammal, a 1200-g rabbit (Oryctolagus cuniculus), with
a total daily food consumption of 500 g (Ross, personal
communication).

In orchards, mammals are likely to be exposed only by eating
earthworms contaminated with fenarimol residues. The expected residues
in soil treated with fenarimol at 1.1 kg/ha in 14 applications of
0.076 kg/ha and with no significant degradation in soil (DT₅₀ in
field soil, 14-130 days) is 1.57 mg/kg of soil, assuming a soil depth
of 5 cm and bulk density of 1.4 g/cm³. At application rates
equivalent to 7 kg/ha (10 mg/kg of soil), earthworms did not
accumulate residues at levels greater than the concentration of
fenarimol in the surrounding soil, so that the maximal concentration
in the earthworms would be 1.57 mg/kg. If the total daily food
consumption of a common shrew were contaminated earthworms, it would
consume 0.03 mg of fenarimol, or 1.57 mg/kg bw. The acute oral TER,
based on an acute oral LD₅₀ of 2500 mg/kg bw, would therefore be
1592, which is greater than the EPPO (1993) threshold of 100,
indicating that the acute risk to earthworm-eating mammals of use of
fenarimol in orchards should be low.

In hop gardens and vineyards, mammals are thought to be exposed
by eating oversprayed insects or treated fruit (e.g. grapes) contam-
inated with fenarimol residues. The initial residues expected on
insects oversprayed at the maximal application rate of 0.06 kg/ha is
1.74 mg/kg of small insects (EPPO, 1993). If the total daily food of a
common shrew were contaminated insects, it would take in 0.03 mg of
fenarimol, or 1.74 mg/kg bw. The acute oral TER based on the acute
oral LD₅₀ of 2500 mg/kg bw would therefore be 1437. This value is
greater than the EPPO (1993) threshold of 100, indicating that the
acute risk for insectivorous mammals in hop gardens and vineyards
treated with fenarimol should be low.

The initial residues expected on grapes oversprayed at 0.06 kg/ha
is 0.078 mg/kg of fruit (EPPO, 1993). If the total daily food of a
wood mouse were contaminated grapes, it would take in 0.006 mg of
fenarimol, or 10.33 mg/kg bw. The acute oral TER based on the acute
oral LD₅₀ of 2500 mg/kg bw would therefore be 7500. This value is

greater than the EPPO (1993) threshold of 100. Residues in grapes
before harvesting have been reported to be as high as 0.04 mg/kg of
fruit, a value below the predicted initial residues used to calculate
the TER, indicating that the risk to mammals eating grapes around
harvest time is less than that for mammals eating grapes immediately
after application. The TER therefore indicates that the acute risk for
fruit-eating mammals in vineyards and hop gardens from the use of
fenarimol should be low.

When fenarimol is used to treat turf, mammals are exposed by
grazing treated grass or eating earthworms contaminated with fenarimol
residues. The initial residues expected on short grass oversprayed at
1.5 kg/ha is 168 mg/kg of grass (EPPO, 1993). If the total daily food
of a rabbit were contaminated grass, it would take in 84 mg of
fenarimol, or 70 mg/kg bw. The acute oral TER based on the acute oral
LD₅₀ of 2500 mg/kg bw would therefore be 35.7. This value is lower
than the EPPO (1993) threshold of 100, which requires that the risk be
assessed further. As application is done mainly in autumn and winter,
the initial residues are unlikely to remain for long before being
washed off or diluted by rainfall. The actual TER may therefore well
be significantly higher than those currently reported. Furthermore,
although the United Kingdom has the highest application rate to turf
within the European Union, no incidents of mammalian poisoning
involving fenarimol have been reported in the UK Wildlife Incident
Investigation Scheme. The risk to grazing mammals from the use of
fenarimol on turf would therefore appear to be low.

The expected residue of fenarimol in soil after application of
6 kg/ha, in four applications of 1.5 kg/ha per year with no signi-
ficant degradation in soil (DT₅₀ in field soil, 14-130 days; see
section 5.1.3), is 8.57 mg/kg of soil, assuming a soil depth of 5 cm
and bulk density of 1.4 g/cm³. As at an application rate equivalent
to 7 kg/ha (10 mg/kg of soil) earthworms did not accumulate residues
at concentrations greater than those in the surrounding soil, the
maximal concentration of fenarimol in the earthworms would be 8.57
mg/kg. If the total daily food of a common shrew were contaminated
earthworms, it would take in 0.15 mg of fenarimol, or 8.57 mg/kg bw.
The acute oral TER based on the acute oral LD₅₀ of 2500 mg/kg bw
would therefore be 291. This value is greater than the EPPO (1993)
threshold of 100, indicating that the acute risk for earthworm-eating
mammals on turf treated with fenarimol should be low.

In other agricultural and horticultural uses of fenarimol,
mammals are likely to be exposed by consuming either oversprayed
insects or treated produce (e.g. strawberries) contaminated with
fenarimol residues. The initial residues expected on insects
oversprayed at 0.084 kg/ha is 2.44 mg/kg of small insects (EPPO,
1993). If the total daily food of a common shrew were contaminated
insects, it would take in 0.04 mg of fenarimol, or 2.44 mg/kg bw. The

acute oral TER based on the acute oral LD₅₀ of 2500 mg/kg bw would
therefore be 1025. This value is greater than the EPPO (1993)
threshold of 100, indicating that the acute risk for insectivorous
mammals in other arable and horticultural uses of fenarimol should be
low.

The initial residues expected on strawberries oversprayed at
0.084 kg/ha is 0.12 mg/kg of fruit (EPPO, 1993). If the total daily
food of a wood mouse were contaminated insects, it would take in 0.001
mg of fenarimol, or 0.05 mg/kg bw. The acute oral TER based on the
acute oral LD₅₀ of 2500 mg/kg bw would therefore be 50 000. This
value is greater than the EPPO (1993) threshold of 100; however,
residues in strawberries before harvesting have been reported to be as
high as 0.14 mg/kg of fruit. As this residue is within one order of
magnitude of the predicted initial residues used to calculate the
TERs, those based on residues at harvesting will still be far higher
than the threshold value, and the acute risk for these birds from the
use of fenarimol should be low.

6. Evaluation of effects on the environment

Fenarimol is a systemic fungicide used on a wide range of fruit,
vegetables, hops, and wheat. It is registered in a large number of
countries. It is rapidly adsorbed onto soil and sediments; in a series
of laboratory experiments it showed no tendency to leach and stayed in
the top few centimetres of soil. A persistence of several months in
soil was confirmed in the field. Photolysis has been shown to occur,
but because of factors including the type of use and its ready
adsorption on soil and sediments photolysis is not considered to be a
significant mechanism for degradation. Fenarimol was not biodegradable
in studies in the field or the laboratory under either aerobic or
anaerobic conditions. Hydrolysis has been shown to occur only at
extreme pH. The compound is therefore highly persistent and not
mobile.

It bioaccumulates to a very limited degree, and depuration of
contaminated tissues takes place within a few days in both aquatic and
terrestrial organisms (fish and earthworms). It had no effect on soil
respiration or nitrification processes at concentrations much higher
than the normal application rates; similar results were obtained in
sewage sludges.

The LC₅₀ and EC₅₀ values for fenarimol were 0.82 mg/litre for
the most sensitive fish, 0.1.8 mg/litre for the most sensitive aquatic
invertebrate, and 0.76 mg/litre for the most sensitive alga. In
long-term experiments, the NOEC values were 0.43 mg/litre for fish and
0.113 mg/litre for aquatic invertebrates. Fenarimol had low acute
toxicity for honey bees, with an acute oral LD₅₀ of > 10 and a
contact LD₅₀ of >100 mg per bee. Little toxicity was seen in
earthworms, with an acute LC₅₀ of 200-300 mg/kg and an NOEC for
reproductive effects of 1.89 kg/ha. It was also of little toxicity to
birds, with an acute oral LD₅₀ of > 2000 mg/kg bw and an NOEL of
2000 mg/kg bw; however, reduced body weight was observed, with an NOEC
of 250 mg/kg of food. Several studies of reproductive toxicity gave
NOEC values of 50-300 mg/kg of food for different birds. No data were
available on the toxicity of fenarimol to wild mammals, but the LD₅₀
for laboratory mammals was 2500 mg/kg bw.

Risk assessment

At application rates equivalent to 28 times the maximal
recommended rate for fenarimol (4 × 1.5 kg/ha on turf), there was no
significant effect on soil respiration or microbial processes. The
risk to aquatic organisms was assessed on the basis of the 'worst-
case' examples of contamination by spray drift or overspray during
tractor-mounted spray-boom application to turf at 4 × 1.5 kg/ha and
air-assisted spray application to orchards at 14 × 0.072 kg/ha (Tables
4 and 5). Details of the method for calculating the PEC are given in
the monograph on fenthion. The summaries of acute and long-term TERs

for aquatic organisms reported above indicate that fenarimol presents
a small risk to aquatic life, except in multiple applications in
orchards, which present a medium-high risk to sediment-dwelling
invertebrates.

Table 4. Acute risk to aquatic organisms from spray drift or overspray contamination
arising from use of fenarimol by boom- or air-assisted spray

Organism LC₅₀/EC₅₀ Application Acute PEC^a Acute TER Risk
(mg/litre) (mg/litre)

Fish 0.8 Tractor boom spray 0.025^b 32 Low
Fish 0.8 Air-assisted spray 0.04^c 20 Low
Aquatic invertebrates 0.18 Tractor boom spray 0.025^b 7.2 Present^d
Aquatic invertebrates 0.18 Air-assisted spray 0.04^b 25 Low
Algae 0.76 Tractor boom spray 0.025^b 30 Low
Algae 0.76 Air-assisted spray 0.04^c 19 Low

PEC, predicted environmental concentration; TER, toxicity:exposure ratio
^a Based on one application
^b Spray drift
^c Overspray
^d The risk is considered to be low owing to the small-scale, localized nature of turf applications.

The risk for bees was considered to be low, since the hazard
ratios reported for the highest recommended application rates (1.5
kg/ha) were < 150 for acute oral exposure and < 15 for acute contact
exposure. The recommended timing of application is when bees are
unlikely to be foraging. The limited data on non-target arthropods do
not allow a full assessment of the risk. On the basis of the high rate
of application to turf (1.5 kg/ha) and the multiple applications in
orchards (14 × 0.072 kg/ha), the 'worst-case' short-term TER for
earthworms was 23-35 and the long-term TER was 139-208, indicating a
low risk.

The risks to insectivorous, grazing, and fruit-eating birds and
mammals in the 'worst-case' situations of high application rates to
turf (1.5 kg/ha) and multiple applications in orchards (0.072 kg/ha)
or on strawberries (0.084 kg/ha) are shown in Tables 6 and 7. The TERs
shown in these tables indicate a low risk (i.e. > 100), except for
grazing birds and mammals, after heavy use of fenarimol on turf. No
poisoning incidents have been associated in wildlife monitoring in the
United Kingdom with such use, suggesting that the actual risk is low.
At the same levels of exposure, the TERs for reproductive toxicity
were 22.7 for insectivorous birds and 56 for fruit-eating birds,
indicating a low risk to reproducing birds.

Table 5. Long-term risk to aquatic organisms from spray drift or overspray contamination
arising from multiple applications of fenarimol by boom- or air-assisted spray

Organism NOEC Application PEC^a TER Risk
(mg/litre) (mg/litre)

Fish 0.43 Tractor boom spray 0.0125^b 34 Low
Fish 0.43 Air-assisted spray 0.02^c 21 Low
Aquatic invertebrates 0.113 Tractor boom spray 0.0125^b 9 Present^d
Aquatic invertebrates 0.113 Air-assisted spray 0.006^b 18.8 Low
Sediment invertebrates 0.113^e Tractor boom spray 0.04^b 2.8 Present^d
Sediment invertebrates 0.113^e Air-assisted spray 0.04^c 2.8 Present

PEC, predicted environmental concentration; TER, toxicity:exposure ratio
^a Based on maximal recommended application
^b Spray drift
^c Overspray
^d The risk is considered to be low owing to the small-scale, localized nature of turf applications.
^e Based on long-term toxicity to Daphnia

Table 6. Risks to insectivorous, grazing, and fruit-eating birds from the use of fenarimol on turf and in orchards

Organism Use Food type Food residue LC₅₀ TER Risk
(mg/kg food) (mg/kg food)

Grelag goose (Anser anser) Turf Vegetation 168^a > 6250 > 37.2 Low
Song thrush (Turdus philomelos) Turf Earthworms 8.58^b > 6250 > 728 Negligible
Starling (Sturnus vulgaris) Orchard Cherries 0.89^b > 6250 > 7022 Negligible

TER, toxicity:exposure ratio
^a Calculated from the vertebrate risk assessment scheme of the European Plant Protection Organisation/Council of Europe
^b Based on actual data on residue levels
7. Further research

Studies are required on the long-term toxicity of fenarimol-
contaminated sediment to sediment-dwelling invertebrates.

Table 7. Risks to insectivorous, grazing, and fruit-eating mammals from the use of fenarimol on turf and soft fruit

Organism Use Food type Food residue Expected daily LD₅₀ TER Risk
(mg/kg food) intake (mg/kg bw)

Shrew (Sorex araneus) Turf Earthworms 8.58^a 8.57 2500 291 Negligible
Rabbit (Oryctolagus cuniculus) Turf Grass 168^b 70 2500 35.7 Low
Wood mouse (Apodemus sylvaticus) Soft fruit Strawberries 0.14^b 0.06 2500 > 10 000 Negligible

TER, toxicity:exposure ratio
^a Based on actual data on residue levels
^b Calculated
8. Previous evaluations by international bodies

A monograph on fenarimol is available from the European
Commission (91/414/EEC).

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    See Also:
       Toxicological Abbreviations
       Fenarimol (Pesticide residues in food: 1995 evaluations Part II Toxicological & Environmental)