|Chemical Abstract Number (CAS #)||
|Synonyms||Aminocarb||Phenol, 4-(dimethylamino)-3-methyl-, methylcarbamate||Metacil||4-Dimethylamino-3-cresyl methylcarbamate
||EPA Method 632|
Link to the National Library of Medicine's Hazardous Substances
Database for more details
on this compound.
|Use|| 100% AS AN INSECTICIDE IN CONTROL OF FOREST PESTS INCL SPRUCE
WEBWORM & JACK PINE BUDWORM (1974) FORMER USE
Control of lepidopterous larvae and other chewing insects in cotton, field crops, and in forestry.
|Consumption Patterns|| 100% AS AN INSECTICIDE IN CONTROL OF FOREST PESTS INCL SPRUCE
WEBWORM & JACK PINE BUDWORM (1974)
|Apparent Color|| WHITE CRYSTALLINE SOLID ; TAN CRYSTALS
|Melting Point|| 93-94 DEG C
|Molecular Weight|| 208.26
|Environmental Impact|| Aminocarb may be released in the environment during its use as an insecticide. If released
to soil, aminocarb is expected to have a moderate high mobility in soils. Loss of aminocarb will
occur primarily by hydrolysis and biodegradation. Loss of aminocarb from soil due to
volatilization may not be important. The persistence of aminocarb in a forest soil was less than 8
days. In water, aminocarb appears to degrade as a result of hydrolysis, biodegradation and
photolysis. The half-life of aminocarb in a creek water with a pH of 6.52 was 11.5 days.
Aminocarb should not bioconcentrate in aquatic organisms. It should not volatilize from soil or
water. In the atmosphere, reaction with photochemically produced hxydroxyl radicals will be an
important loss processes for vapor phase aminocarb in the atmosphere. The half-life of aminocarb
due to this reaction has been estimated to be less than 1 hr. Partial removal of aminocarb will also
occur as a result of dry and wet deposition. Workers who apply the insecticide are the most likely
people to be exposed to aminocarb. Exposure would be expected via inhalation and dermal
|Environmental Fate|| TERRESTRIAL FATE: Based on degradation studies in water , both biodegradation
and hydrolysis may be the major processes for the degradation of aminocarb from soil.
Because of the inability of sunlight to penetrate beyond soil surface, photolysis will not be
important beyond the top layers of soil. Based on low estimated values for vapor pressure
(1.88X10-6 mm Hg) and Henry's Law constant (5.64X10-10 atm cu m/mole), volatilization of
aminocarb from dry and wet soil should not be important. The estimated Koc value of
100-210 indicates that aminocarb should exhibit high to moderate leaching in soil(4,SRC). The
persistence of aminocarb in soil will depend on the soil type, moisture content, pH and the
temperature of soil . In a conifer forest soil (sandy loam) of pH 6.2 and temperatures of 10-22.3
deg C, the persistence of aminocarb did not exceed 8 days .
AQUATIC FATE: Aminocarb will degrade by a combination of hydrolysis, photolysis and
biodegradation in water . The half-life of aminocarb in a creek water from Moncton, New
Brunswick, Canada with a natural pH of 6.52 was 11.5 days . The hydrolysis of aminocarb in
water will be faster at higher pH . In 14 days, 90% aminocarb degraded in Little Miami River
water from Ohio and it was totally degraded in less than 4 weeks . Under field application
conditions, residues of aminocarb disappeared rapidly (3-25 hrs) from water, sediment and fish .
The log BCF value of less than 5(4-6) indicates that bioconcentration of aminocarb in aquatic
organisms will not be important.
ATMOSPHERIC FATE: Based on a vapor pressure of 1.88X10-6 mm Hg estimated from
Henry's Law constant and water solubility , aminocarb may be present partially in the vapor
phase and partially in the particulate form in air(3,SRC). Based on an estimation method , vapor
phase aminocarb may be removed from the atmosphere with a half-life of less than 1 hr. due to
reaction with photochemically produced hydroxyl radicals. Partial removal of particulate
aminocarb from the air may occur by dry deposition. Both vapor and particle phase
aminocarb may be partly removed from the atmosphere by wet deposition.
|Drinking Water Impact|| SURFACE WATER: The concn range of aminocarb in a still lake water (directly
exposed) one hr. after spraying at a rate 52 g a.i./ha was less than 0.01 to 331 ug/l. The concn of
aminocarb in an exposed stream one hr. following spraying was less than 0.01 to 18.4 ug/l . The
median concn in both waters hardly exceeded 1 ug/l one hr. after spraying . The level will
decrease rapidly in water with time . Metabolites of aminocarb have never been detected in
natural water after aerial spraying .
Aminocarb applied to the surface of a stream dispersed throughout the water column within 100
m of the place of application. Concn in the water were first highest near the surface, later more or
less evenly distributed, and lingered longest near and within the stream bottom. Both oil and water
based formulations of Matacil 1.8F gave similar results. Aminocarb concn diminished
logarithmically downstream. Concn of aminocarb in suspended particles, sediments, periphyton,
higher plants, insects, and brook trout were not higher than ambient in water and dissipated
quickly. Aminocarb phenol was found consistently in measurable concn in water treated with the
aq formulation, but in much smaller concn in water treated with the oil formulation. It was also
found only as very small amt in 3 sediment samples in the stretch treated with the aq formulation.
A slight increase in drift of Chironomidae was probably caused by aminocarb. No effects on
survival, drift, or species composition of phytoplankton were noted.