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EC number: 236-671-3 | CAS number: 13463-41-7
- 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
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Endpoint summary
Administrative data
Description of key information
Additional information
The information contained within this robust summary document comes from studies which are in the ownership of Arch Chemicals Inc. and which are protected in several regions globally. This information may not be used for any purpose other than in support of the Chemical safety Report submitted by Arch Chemicals Inc. under RegulationEC 1907/2006.
Adsorption and desorption in soil and sediment
In a study of the adsorption and desorption of zinc [pyridine-2,6-14C]pyrithione in two sediments and two terrestrial soils (Wysocky & Reynolds, 1996) conducted according to U.S. EPA Pesticide Assessment Guidelines, Subdivision N, §163-1, it was shown that zinc pyrithione has a high affinity for soil and sediment with adsorption Koc values ranging from 784 to 10,633. The corresponding desorption Koc values were even higher. The Koc values were not proportional to the percent organic matter in the soils and sediments, indicating other mechanisms for adsorption. Mobility was classified as low and slight in the two soils and slight and immobile in the two sediments. This was consistent with the results from a soil column leaching study discussed below (Ritter, 2001), in which zinc pyrithione was found to be immobile in four different soil types.
In a study on the soil sorption and desorption of zinc pyrithione in five European soils by Haberhauer (2002) (Ritter, 2001) conducted according to OECD Guideline 106, very high sorption (Kd > 550) was obtained for a clay loam. Similar sorption (Kd of 20 to 79) was determined for the other soils. Desorption is much less favoured than sorption, with desorption coefficients of one order of magnitude greater than that of sorption. The mobility of the test substance in soil is therefore low. .
Soil column leaching study
A soil column leaching study(Ritter, 2001)according toU.S. EPA Pesticide Assessment Guidelines, Subdivision N, §163-1, was conducted to further study and evaluate the mobility of zinc pyrithione in soils. The leaching potential of zinc pyrithione by four different soils types was investigated using the radiolabelled test substance. The leaching potential of pyrithione degradation products was also investigated after aging zinc pyrithione in sandy loam soil for a period of approximately one half-life (13 - 15.5 hours).
Most of the radioactivity in the unaged soil was retained in the top 6-cm soil segment. In the aged soil columns, most of the radioactivity remained in the top 0.6-cm layer of aged soil. Degradation of zinc pyrithione in the soil was extensive during the period over which the columns were leached.
The data from this study confirm the large Kadsvalues found in the batch equilibrium studies on zinc pyrithione. Zinc pyrithione binds strongly to soil and is immobile.
In summary, zinc pyrithione is adsorbed and rapidly degraded under conditions presented in a broad range of soil types. The half-life for pyrithione during aging in sandy loam was calculated as 13 - 15.5 hours. Significant degradation also occurred in unaged soil on the soil columns. The major terminal metabolites are humic-fraction incorporated bound residues, pyrithione sulfinic acid, and pyrithione sulfonic acid.
The leaching behavior of zinc pyrithione in four soils shows pyrithione to be immobile, which is consistent with the results from the adsorption/desorption study in two soils and two sediments.
Table 4.8: Adsorption and desorption of zinc pyrithione
Guideline / Test method |
Soil/sediment |
Adsorbed a.s. [average %] |
Ka1 |
KaOC2 |
Kd3 |
KdOC4 |
Ka/ Kd5 |
Degradation products Name [%] of a.s. |
Reference |
|
U.S. EPA Pesticide Assessment Guidelines, Subdivision N, §163‑1 |
sandy loam loam Saltwater sediment Freshwater sediment |
92.2 69.3 46.2 37.8 |
50.37 11.37 98.68 47.99 |
2347 784 10633 3597 |
70.67 12.66 202.45 87.04 |
3293 873 21814 6524 |
0.71 0.90 0.49 0.55 |
OMSiA |
nd - 22.3 % |
Wysocky, Reynolds (1996) Unpublished study |
OECD Guideline 106 |
Silty loam |
28.7 |
21 |
860 |
2300 |
97000 |
Not reported in study |
Degradants not identified |
Haberhauer (2002) Unpublished study |
|
U.S. EPA Pesticide Assessment Guidelines, Subdivision N, §163‑1 |
Sandy loam |
71.5 |
Not calculated |
Not calculated |
Not calculated |
Not calculated |
Not calculated |
OMSiA |
7.5 – 22.8 % |
Ritter (2005) Unpublished study |
1Ka= Adsorption coefficient
2KaOC= Adsorption coefficient based on organic carbon content
3Kd= Desorption coefficient
4KdOC= Desorption coefficient based on organic carbon content
5Ka/ Kd= Adsorption / Desorption distribution coefficient
Conclusion
Zinc pyrithione are slightly (Koc=784) or very slightly (Koc=2347) mobile in soils and very slightly mobile (Koc= 3597-10633) in sediments.
Volatilisation
Henry’s Law constant
The calculated Henry’s Law constant of <5 x 10-5Pa-m3-mol-1indicates that volatilisation from surface waters is not expected to be an important process.
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Reproduction or further distribution of this information may be subject to copyright protection. Use of the information without obtaining the permission from the owner(s) of the respective information might violate the rights of the owner.
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