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EC number: 208-883-6 | CAS number: 544-92-3
- 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
Adsorption / desorption
Administrative data
Link to relevant study record(s)
- Endpoint:
- adsorption / desorption: screening
- Type of information:
- experimental study
- Adequacy of study:
- key study
- Study period:
- from June 1989 to June 1990
- Reliability:
- 2 (reliable with restrictions)
- Rationale for reliability incl. deficiencies:
- study well documented, meets generally accepted scientific principles, acceptable for assessment
- Justification for type of information:
- Field research
- Qualifier:
- no guideline followed
- Principles of method if other than guideline:
- The study areas are shown in Fig. 1 together with more detailed insets of the estuaries indicating sampling locations. The survey period extended from June 1989 to June 1990. The Forth Estuary was sampled in June, August, November, January, March and May, the Tay in July, August, September, November, February, April and June. A small fast boat was used for sampling in the Tay Estuary and for the Forth Estuary west of the road and rail bridges, in the Firth of Forth a larger vessel was used (RS Forth Ranger). All surveys were undertaken at high water on spring tides. Samples were collected from a depth of 1 m using the sampler described by Balls & Laslett (1991). Only brief details of sampling and analytical procedures will be given here, further information s available elsewhere (Balls et al., 1994; Laslett & Balls, 1995). Trace metal samples were collected in acid cleaned polythene bottles and pressure filtered within 24 h onto preweighed acid washed 0.4 gm pore size polycarbonate membranes (Nuclepore). Membranes were washed free of salt with distilled water and air dried for SPM determination, they were subsequently digested with hot concentrated nitric acid for the determination of particulate trace metals. The precision of the method varied between metals but was generally in the range 10-15%.
In preparation for major element analysis by thin film X-ray fluorescence (XRF), aliquots of water were filtered through preweighed 37 mm diameter 0.4 gm pore size polycarbonate membranes (N clepore). The membranes were subsequently washed free of salt with distilled water and reweighed to assess their particulate loadings.
Samples for particulate organic carbon (POC) determination were collected in glass bottles and vacuum filtered through a 25 mm diameter Whatman GF/F filter in an all glass apparatus. Blanks were minimized by heating filters at 500°C for 2 h before use.
Filters were stored frozen and prior to the determination of POC (Perkin Elmer Elemental Analyser 240B) carbonate was removed by exposure to hydrochloric acid fumes. - GLP compliance:
- no
- Type of method:
- other: X-Ray Fluorescence
- Computational methods:
- The partition coefficient (Kd) is calculated as Kd = Cp / Cd
(Cp and Cd are respectively the solubility of the metal and the concentration of the fine particles) - Key result
- Type:
- log Kd
- Remarks:
- overall mean
- Value:
- 4.65 dimensionless
- % Org. carbon:
- 8.2
- Remarks on result:
- other: mean % org. carbon
- Remarks:
- Results for Tay
- Key result
- Type:
- log Kd
- Remarks:
- overall mean
- Value:
- 4.78 dimensionless
- % Org. carbon:
- 10.4
- Remarks on result:
- other: mean % org carbon
- Remarks:
- Results for Forth
- Validity criteria fulfilled:
- not applicable
- Conclusions:
- The log Kd median values for Forth and Tay were 4.76 and 4.65, respectively. It is considered to be a substance adsorbed on the soil through this.
- Executive summary:
The composition of dissolved and particulate trace elements was investigated in two North Sea estuaries (Forth and Tay). It was found that log Kd is higher than that of Forth in Tay, which may be related to the content of organic carbon in particulate matter. The log Kd median values for Forth and Tay were 4.76 and 4.65, respectively. It is considered to be a substance adsorbed on the soil through this.
- Endpoint:
- adsorption / desorption: screening
- Type of information:
- read-across from supporting substance (structural analogue or surrogate)
- Remarks:
- from the source substance copper
- Adequacy of study:
- supporting study
- Justification for type of information:
- REPORTING FORMAT FOR THE ANALOGUE APPROACH
1. HYPOTHESIS FOR THE ANALOGUE APPROACH
A read-across based on analogue approach has been performed for that endpoint.
The read-across hypothesis, according to Read Across Assessment Framework published by ECHA, is based on the fact that different compounds which have the same type of effect(s). It corresponds to the scenario 2 described as follows:
« This scenario covers the analogue approach for which the read-across hypothesis is based on different compounds which have the same type of effect(s). For the REACH information requirement under consideration, the effects obtained in a study conducted with one source substance are used to predict the effects that would be observed in a study with the target substance if it were to be conducted. The same type of effect(s) or absence of effect is predicted. The predicted strength of the effects may be similar or based on a worst-case assumption. ».
2. SOURCE AND TARGET CHEMICAL(S) (INCLUDING INFORMATION ON PURITY AND IMPURITIES)
The read-across has been performed between copper cyanide (CAS No. 544-92-3; target chemical) and copper (CAS No. 7440-50-8; source chemical).
3. ANALOGUE APPROACH JUSTIFICATION
Copper cyanide is decomposed into copper compounds and cyanide in water. Cyanide is decomposed at high velocity and distributed as hydrogen cyanide. Hydrogen cyanide is not adsorbed and desorbed on sediments or suspended adsorbents because of its high water solubility. As a consequence, it can be considered that it is the copper compound that has the greater influence on the adsorption/desorption properties of the substance copper cyanide. There is no data available on the registered substance copper cyanide for this endpoint. Therefore, the results of adsorption and desorption tests, which is a study on the environmental distribution of copper compounds, were used.
Based on these elements and to the fact that both target and source chemicals are inorganic substances with close physical-chemical properties, it can be assumed that copper cyanide and copper may have similar environmental fate. The read-across approach between copper cyanide and copper is therefore relevant for this endpoint. - Reason / purpose for cross-reference:
- read-across source
- GLP compliance:
- no
- Conclusions:
- Based on a read-across from the source substance copper, the target substance copper cyanide can be regarded as a substance adsorbed on the soil, with log Kd median values considered to be between 4.65 and 4.76.
- Executive summary:
The composition of dissolved and particulate trace elements was investigated in two North Sea estuaries (Forth and Tay). It was found that log Kd is higher than that of Forth in Tay, which may be related to the content of organic carbon in particulate matter. The log Kd median values for Forth and Tay were 4.76 and 4.65, respectively. It is considered to be a substance adsorbed on the soil through this.
A read-across has been performed between copper cyanide (CAS No. 544-92-3; target chemical) and copper (CAS No. 7440-50-8; source chemical).
Indeed, copper cyanide is decomposed into copper compounds and cyanide in water. Cyanide is decomposed at high velocity and distributed as hydrogen cyanide. Hydrogen cyanide is not adsorbed and desorbed on sediments or suspended adsorbents because of its high water solubility. As a consequence, it can be considered that it is the copper compound that has the greater influence on the adsorption/desorption properties of the substance copper cyanide. There is no data available on the registered substance copper cyanide for this endpoint. Therefore, the results of adsorption and desorption tests, which is a study on the environmental distribution of copper compounds, were used.
Based on these elements and to the fact that both target and source chemicals are inorganic substances with close physical-chemical properties, it can be assumed that copper cyanide and copper may have similar environmental fate. The read-across approach between copper cyanide and copper is therefore relevant for this endpoint.
Therefore, the registered substance copper cyanide can be regarded as a substance adsorbed on the soil, with log Kd median values considered to be between 4.65 and 4.76.
- Endpoint:
- adsorption / desorption: screening
- Data waiving:
- study scientifically not necessary / other information available
- Justification for data waiving:
- other:
- Justification for type of information:
- In accordance with column 2 of REACH Regulation (EC) No 1907/2006, Annex VIII, section 9.3.1, the test on adsorption/desorption screening does not need to be conducted as the substance copper cyanide can be expected to have a low potential for adsorption based on the octanol water partition coefficient. The theoretical, calculated (EPIWIN) log Pow is - 1.49, i.e. very low, as expected for an inorganic substance.
Referenceopen allclose all
Table 5.4.1.1: Distribution coefficient
|
KDin the Forth Estuary |
|
KDin the Tay Estuary |
June 1989 |
4.89 |
July 1989 |
4.64 |
August 1989 |
4.72 |
August 1989 |
4.51 |
November 1989 |
4.75 |
September 1989 |
4.66 |
January 1990 |
4.73 |
November 1989 |
4.67 |
March 1990 |
4.85 |
February 1990 |
4.66 |
May 1990 |
4.72 |
April 1990 |
4.73 |
June 1990 |
4.89 |
July 1990 |
4.64 |
Overall mean + range |
4.78 (4.72 - 4.89) |
|
4.65 (4.51 - 4.73) |
Table 5.4.1.2: Comparative results from other references
Area |
Log KD-range |
Reference |
Rhine |
4.1–5.0 |
Golimowskietal,1990 |
Waal |
3.7–5.3 |
Golimowskietal,1990 |
Maas |
4.7–5.8 |
Golimowskietal,1990 |
Weser |
4.1 |
Turner et al, 1992 |
Seine |
4.5–4.7 |
Chiffoleau et al, 1994 |
Mersey |
4.7–5.0 |
Comber et al, 1995 |
Humber |
3.8–3.9 |
Comber et al, 1995 |
Table 5.4.1.3: Suspended POC (%) in the Forth Estuary for individual surveys between June 1989 and June 1990
% POC | |||
Min | Median | Max | |
June 1989 | 3.0 | 8.0 | 18.5 |
August 1989 | 5.8 | 10.0 | 13.9 |
November 1989 | 6.6 | 10.4 | 26.7 |
January 1990 | 3.9 | 12.5 | 37.5 |
March 1990 | 6.3 | 10.3 | 22.9 |
May 1990 | 4.7 | 11.1 | 35.9 |
Table 5.4.1.4: Suspended POC (%) in the Tay Estuary for individual surveys between June 1989 and June 1990
% POC | |||
Min | Median | Max | |
July 1989 | 4.3 | 8.7 | 20.1 |
August 1989 | 4.7 | 8.9 | 23.2 |
September 1989 | 5.4 | 7.6 | 13.5 |
November 1989 | 4.2 | 10.5 | 19.4 |
February 1990 | 3.4 | 6.0 | 11.2 |
April 1990 | 2.7 | 6.5 | 8.2 |
June 1990 | 6.9 | 9.1 | 14.7 |
Description of key information
In accordance with column 2 of REACH Regulation (EC) No 1907/2006, Annex VIII, section 9.3.1, the test on adsorption/desorption screening does not need to be conducted as the substance copper cyanide can be expected to have a low potential for adsorption based on the octanol water partition coefficient. The theoretical, calculated (EPIWIN) log Pow is - 1.49, i.e. very low, as expected for an inorganic substance.
Key value for chemical safety assessment
- Koc at 20 °C:
- 575 877
Additional information
As additional information, a study on an analogue substance was available and was used for CSA purpose. Indeed, the composition of dissolved and particulate trace elements was investigated in two North Sea estuaries (Forth and Tay). It was found that log Kd for copper is higher in Forth than in Tay, which may be related to the content of organic carbon in particulate matter. The log Kd median values for Forth and Tay were 4.76 and 4.65, respectively. The source substance copper is therefore considered to be a substance adsorbed on the soil through this.
A read-across has been performed between copper cyanide (CAS No. 544-92-3; target chemical) and copper (CAS No. 7440-50-8; source chemical).
Indeed, copper cyanide is decomposed into copper compounds and cyanide in water. Cyanide is decomposed at high velocity and distributed as hydrogen cyanide. Hydrogen cyanide is not adsorbed and desorbed on sediments or suspended adsorbents because of its high water solubility. As a consequence, it can be considered that it is the copper compound that has the greater influence on the adsorption/desorption properties of the substance copper cyanide. There is no data available on the registered substance copper cyanide for this endpoint. Therefore, the results of adsorption and desorption tests, which is a study on the environmental distribution of copper compounds, were used.
Based on these elements and to the fact that both target and source chemicals are inorganic substances with close physical-chemical properties, it can be assumed that copper cyanide and copper may have similar environmental fate. The read-across approach between copper cyanide and copper is therefore relevant for this endpoint.
Therefore, the registered substance copper cyanide can be regarded as a substance adsorbed on the soil, with log Kd median values considered to be between 4.65 and 4.76.
Moreover, kd can be converted to koc with the following equation: kd = koc x foc (organic carbon fraction) <==> koc = kd / foc
In the study, the following organic carbon values have been reported:
Table 5.4.1.3: Suspended particulate organic carbon (POC, %) in the Forth Estuary for individual surveys between June 1989 and June 1990
% POC | |||
Min | Median | Max | |
June 1989 | 3.0 | 8.0 | 18.5 |
August 1989 | 5.8 | 10.0 | 13.9 |
November 1989 | 6.6 | 10.4 | 26.7 |
January 1990 | 3.9 | 12.5 | 37.5 |
March 1990 | 6.3 | 10.3 | 22.9 |
May 1990 | 4.7 | 11.1 | 35.9 |
Table 5.4.1.4: Suspended POC (%) in the Tay Estuary for individual surveys between June 1989 and June 1990
% POC | |||
Min | Median | Max | |
July 1989 | 4.3 | 8.7 | 20.1 |
August 1989 | 4.7 | 8.9 | 23.2 |
September 1989 | 5.4 | 7.6 | 13.5 |
November 1989 | 4.2 | 10.5 | 19.4 |
February 1990 | 3.4 | 6.0 | 11.2 |
April 1990 | 2.7 | 6.5 | 8.2 |
June 1990 | 6.9 | 9.1 | 14.7 |
Based on these tables, averaged POC values range betwwen 8.19% (Tay Estuary) and 10.38% (Forth Estuary).
Therefore, koc values are determined to be 539 440 L/kg (Tay Estuary) and 575 877 L/kg (Forth Estuary).
For CSA purpose, the most conservative value is used as the key koc value of the substance, i.e. 575 877 L/kg.
Information on Registered Substances comes from registration dossiers which have been assigned a registration number. The assignment of a registration number does however not guarantee that the information in the dossier is correct or that the dossier is compliant with Regulation (EC) No 1907/2006 (the REACH Regulation). This information has not been reviewed or verified by the Agency or any other authority. The content is subject to change without prior notice.
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