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EC number: 200-662-2 | CAS number: 67-64-1
- Life Cycle description
- Uses advised against
- Endpoint summary
- Appearance / physical state / colour
- Melting point / freezing point
- Boiling point
- Density
- Particle size distribution (Granulometry)
- Vapour pressure
- Partition coefficient
- Water solubility
- Solubility in organic solvents / fat solubility
- Surface tension
- Flash point
- Auto flammability
- Flammability
- Explosiveness
- Oxidising properties
- Oxidation reduction potential
- Stability in organic solvents and identity of relevant degradation products
- Storage stability and reactivity towards container material
- Stability: thermal, sunlight, metals
- pH
- Dissociation constant
- Viscosity
- Additional physico-chemical information
- Additional physico-chemical properties of nanomaterials
- Nanomaterial agglomeration / aggregation
- Nanomaterial crystalline phase
- Nanomaterial crystallite and grain size
- Nanomaterial aspect ratio / shape
- Nanomaterial specific surface area
- Nanomaterial Zeta potential
- Nanomaterial surface chemistry
- Nanomaterial dustiness
- Nanomaterial porosity
- Nanomaterial pour density
- Nanomaterial photocatalytic activity
- Nanomaterial radical formation potential
- Nanomaterial catalytic activity
- Endpoint summary
- Stability
- Biodegradation
- Bioaccumulation
- Transport and distribution
- Environmental data
- Additional information on environmental fate and behaviour
- Ecotoxicological Summary
- Aquatic toxicity
- Endpoint summary
- Short-term toxicity to fish
- Long-term toxicity to fish
- Short-term toxicity to aquatic invertebrates
- Long-term toxicity to aquatic invertebrates
- Toxicity to aquatic algae and cyanobacteria
- Toxicity to aquatic plants other than algae
- Toxicity to microorganisms
- Endocrine disrupter testing in aquatic vertebrates – in vivo
- Toxicity to other aquatic organisms
- Sediment toxicity
- Terrestrial toxicity
- Biological effects monitoring
- Biotransformation and kinetics
- Additional ecotoxological information
- Toxicological Summary
- Toxicokinetics, metabolism and distribution
- Acute Toxicity
- Irritation / corrosion
- Sensitisation
- Repeated dose toxicity
- Genetic toxicity
- Carcinogenicity
- Toxicity to reproduction
- Specific investigations
- Exposure related observations in humans
- Toxic effects on livestock and pets
- Additional toxicological data
Endpoint summary
Administrative data
Description of key information
Additional information
There
are two reliable experimental studies for photo degradation in air. The
overall loss rate of acetone including photo dissociation and loss by
reaction with OH radicals and the corresponding lifetimes were
calculated for January, Equinox and July at 40 degree northern latitude.
Lifetimes were 18.6 - 114.4 days. This is in accordance with the
findings of the second study. The photo dissociation lifetime for
40°solar angle is 1/kdissoc = 14.8 days. Based on the weight of evidence
and on the molecular structure acetone is resistant to hydrolysis. In
water acetone may form the ketal by hydration, however ketal formation
is reversible.
According to several reliable studies, acetone is readily biodegradable.
In a modified OECD 301B screening test acetone was biodegraded to 90.9 ±
2.2 % after 28 days. The 10 days window was met. In a BOD-test according
to APHA Standard methods No. 219 (1971) acetone was degraded to 84%
based on ThOD in 5 days. In two further BOD-tests biodegradation of
acetone yielded 76% after 10 days (84% after 20 days) and 81% after 20
days, respectively. Therefore simulation testing on ultimate degradation
in surface water and sediment simulation testing do not need to be
conducted. There is one study available for sea water. In a BOD-test
acetone was biodegraded in synthetic salt water by a sea water adapted
inoculum to 76% in 20 days. The pass level of 60 % was barely failed.
This indicates that biodegradation of acetone may be somewhat slower in
sea water, but not significant.
Acetone is biodegradable under anaerobic conditions by adapted
microorganisms. After a lag phase of 5 days complete biodegradation was
observed
within 4 days by microorganisms previously cross-adapted with acetate.
Deduced as a weight of evidence from the physicochemical data (miscibility with water in all proportions, log Pow = -0.24) acetone should not sorb onto soils. Data for soil sorption are quoted in a reliable scientific study. Soil sorption Kd was 1.5 L/kg, at 20 °C. The soil sorption coefficient indicates that acetone is mobile in soil and may be transported by soil water. This study is supported by two other findings. In an adsorption/desorption study with the clay mineral sodium montmorillonite no adsorption of acetone was observed. Sodium montmorillonite is part of the clay fraction of soils. Therefore it can be concluded that acetone does not sorb on mineral fractions of soils. In a further study on anaerobic biodegradation of14C labelled acetone in landfill refuse, the soil was intensively extracted after the experiment. The study shows that acetone is able to percolate through landfill refuse caused by rainfall, despite anaerobic biodegradation occurred. Traces of14C were found in the humin fraction of the refuse, but nature and bonding of these residues were not studied. No physically adsorbed14C-acetone was found in the CH2Cl2-extracts of the samples percolated with water, and only traces of14C-acetone were found in the samples that were not percolated by water, indicating the low adsorption potential of14C-acetone.
No reliable experimental data on bioaccumulation are available. Based on the calculated BCF=3 (input parameter: measured log Kow value) no potential for bioaccumulation is to be expected. Furthermore, according to Annex IX, 9.3.2, testing of bioaccumulation is not necessary, if log Kow is less than 3 (acetone: log Kow=-0.24)
Several
reliable experimental studies and further reported values from reliable
sources for the Henry’s Law constant are available. According to
experimental studies (bubble column technique) the Henry’s Law constant
was determined for 2.929 Pa m3mol-1and 3.070 Pa m3mol-1at
25 °C, indicating a moderate volatility from water. The Henry's law
constant for sea water was determined for 3.311 Pa m3mol-1at
25 °C. A slight salting-out effect is to be observed by comparison of
the Henry's Law constants in fresh and sea water. In both media the
Henry's law constants rise with temperature.
Distribution modelling using a simple one-dimensional model of the
global circulation assuming a single pulse emission of acetone predicted
significantly high spatial ranges of 46.5% of the earth perimeter, which
are caused by their intermediate gas-phase stability and high
volatility. The persistence’s are predicted below 20 days, mainly due to
the degradation in water and soil. A generalised Fate Model based on a
steady-state mass balance model designed for primary and biological
reactors of a typical diffused air activated sludge system considering
the processes advection, sorption, volatilisation, air stripping, and
biotransformation was used to predict the fate of acetone in waste water
plants. The model calculations implicate that acetone is predominantly
in the aqueous phase and without biotransformation it would be
transferred to the effluent. Volatilisation is not relevant. In model
runs including biodegradation, removal is partly due to
biotransformation and to transport to the effluent.There are several
studies concerning other distribution data dealing with the partition of
acetone between air and water and the behaviour in soils. Air/water
partition coefficients range from 357 – 341:1, these data are in
accordance with the moderate volatility of acetone deduced from the
experimentally derived Henry’s Law constants. Other studies are dealing
with the diffusion of acetone in soil air. Soil diffusion coefficient at
0 °C was calculated for 8.8 x 10-3cm2/sec
(air: 0.109 cm2/sec). The diffusion coefficient for acetone
was found to be considerably lower than in air. Liquid acetone is able
to expand clay soils rapidly within 2-3 days to an extent of 3.5 – 8 %.
Environmental monitoring data are available for all compartments. Most
studies are from 1979 – 1990. In 2010, the occurrence of acetone in the
sludge of a stp receiving the wastewater of INEOS Phenol was
investigated. Further recent monitoring data are not available. Studies
on environmental concentrations are referring predominantly to
atmospheric concentrations. Acetone concentrations in remote areas (Pt
Barrow, Alaska, USA, 1967) are reported for 0.72 – 6.96 µg/m3.
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