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EC number: 266-972-5 | CAS number: 67711-95-9 A complex combination of insoluble compounds which precipitate during copper electrolytic refining.
- 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
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- Genetic toxicity
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- 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)
Description of key information
Key value for chemical safety assessment
Additional information
- Freshwater environment
Partitioning coefficient for Pb between the freshwater and suspended particulate matter (SPM) are summarized in the voluntary risk assessment of lead (LDAI, 2008). An overview of the selected data is provided in the Table below.
Table: Reported log KD,SPM values for Pb in freshwaters in Europe.
Location |
Log KD(L/kg) |
Remarks |
Reference |
Four Dutch Lakes |
6.0 |
average |
Koelmans and Radovanovic, 1998 |
Calder River, UK Nidd River, UK Swale River, UK Trent River, UK All rivers All rivers |
4.45 - 5.98 4.69 - 6.25 4.58 - 6.20 4.61 - 6.06 5.41 5.71 |
min-max range min-max range min-max range min-max range observed mean predicted mean |
Lofts and Tipping, 2000 |
Scheldt, Belgium |
5.3 |
salinity of 1.5 ppm |
Nolting et al., 1999 |
Po River, Italy |
5.5 |
median value |
Pettine et al., 1994 |
Dutch freshwater |
5.81 |
mean |
Stortelder et al., 1989; in Crommentuyn et al., 1997 |
Upland-influenced river water, UK Low-salinity water, UK |
4.6 5.5 |
modelled value modelled value |
Tipping et al., 1998 |
7 freshwater locations in The Netherlands |
5.93 |
|
Venema, 1994; in Crommentuyn et al., 1997 |
54 Czech rivers / 119 locations |
5.44 5.18 |
median KD median KA(1) |
Veselý et al., 2001 |
RANGE |
4.45 – 6.25 |
|
|
(1)KA: based on the acid soluble concentration
For the calculation of local and regional exposure concentrations the median log KD,SPM value of 5.47 is selected. This value corresponds with a KD,SPMof 295,121 l/kg.
For freshwater sediments, the selected KDvalue was 153,848 L/kg (Log KD: 5.19).
- Estuarine environment:
The next table summarizes the KD,SPM values for suspended particulate matter that were determined in estuarine water bodies. The lowest reported logKD (3.8) was found in a Texan estuary (Benoit et al, 1994). Other values are generally situated between 5.8 and 6.5 with a maximum value of 7.46 (Zhou et al, 2003). However, this value was calculated based on values of suspended particles derived from a graph. Also dissolved Pb was around or beneath detection level, the detection limit was used to calculate the partition coefficient. KD values for this study are thus unreliable estimates. These values were therefore not taken into account while calculating the probability distribution. The maximum value can be found in North Australian estuaries with a KD of 7.2 (Munksgaard and Parry, 2001).
Table: Reported KD,SPM values for Pb is estuarine surface waters.
Location |
Log KD(L/kg) |
Remarks |
Reference |
Seine estuary |
6.1-6.3 |
Min-max range |
Chiffoleau et al, 1994 |
Rhine estuary |
5.85-6.26 |
Min-max value |
Golimowski et al, 1990 |
Weser estuary, Germany |
5.87-6.27 |
Different metal extraction methods used |
Turner et al, 1992 |
Mersey estuary, UK |
4.7-5.0 |
Estimated KDfor river water |
Turner et al, 2002 |
Scheldt estuary, Belgium |
6.0-6.51 |
Min-max value |
Valenta et al, 1986 |
Scheldt estuary, Belgium |
5.4-6.0 |
Min-max value |
Baeyens, 1998 |
Penze estuary, France |
5.5-6.8 |
Min-max value |
Waeles et al, 2007 |
Mersey estuary, UK |
5.0-5.48 |
Min-max value with increasing salinity |
Hartnett & Berry, 2010 |
Conway estuary, Wales |
5.62-7.46 1 |
Min-max range |
Zhou et al, 2003 |
S. Baltic Sea |
6.67 |
Median value |
Sokolowski et al, 2001 |
N. Australia |
5.5-7.2 |
Min-max value |
Munksgaard and Parry, 2001 |
Lena estuary, Russia |
6.42 |
Median value |
Martin et al, 1993 |
Texas |
3.8-6.8 |
Min-max value |
Benoit et al, 1994 |
Danshuei estuary, Taiwan |
5.2-6.5 |
Min-max value |
Jiann et al, 2005 |
Nile estuary |
5.2-5.3 |
Min-max value |
Abdel-Moati, 1990 |
RANGE |
3.8-7.46 |
|
|
1 Values were calculated based on reported dissolved and particulate Pb-concentrations
For the calculation of local and regional exposure concentrations in estuarine environments, a median log KD,SPM value of 5.83 should be used. This value corresponds with a KD,SPM of 677,954 L/kg.
- Marine environment:
A median KD,SPM for Pb was calculated for suspended particulate matter in the marine environment, using the data given below. Four reported marine log KD,SPM values were below 5,0 and were representative for the Atlantic Ocean, the Adriatic Sea, the Greek coast near Lesbos and the Scheldt estuary (4.7, 4.8, 4.1 and 4.9, respectively). Log KD,SPM values for the North Sea are situated between 5.0 and 7.25. The maximum value is situated in the Adriatic Sea (log KD,SPMof 7.8). All reported log KD,SPM for other marine water bodies were situated between 5.0 and 7.8.
From a distribution (Triangular) that is fitted through all these data points a median log KD,SPM of 6.18 for Pb in the marine environment is derived. This corresponds with a KD,SPM of 1,518,099 L/kg.
Table: Reported log KD,SPM values for Pb in marine surface water
Location |
Log KD(L/kg) |
Remarks |
Reference |
Belgian coastal waters |
5.30-5.60 |
Min-max range |
Baeyens et al, 1987 |
North Sea coastal waters |
5.0-7.0 |
Min-max range |
Balls, 1989 |
Scottish Sea Loch |
6.47 |
Average value of 3 sampling stations |
Hall et al |
Southern North Sea |
5.9-7.12 |
Min-max range, NSP-data |
McManus and Prandle, 1996 |
Dover strait |
5.712 |
Summer/winter value |
|
Northern North Sea |
6.682 |
Late summer |
|
Humber/Wash, UK |
6.532 |
Winter/spring |
|
Humber/Wash, UK |
7.242 |
Summer |
|
Scheldt, Belgium |
4.9 |
Salinity of 30 ppm |
Nolting et al, 1999 |
Baltic Sea |
5.782 6.492 7.102 |
10thpercentile 50thpercentile 90thpercentile |
Pohl and Hennings, 1999 |
North Sea |
5.512 6.302 7.252 |
10thpercentile 50thpercentile 90thpercentile |
Tappin et al, 1995 |
Seawater, UK |
6.2 |
Modeled value |
Tipping et al, 1998 |
Oceans |
6.3-6.5 |
Min-max range |
Valenta at al, 1986 |
Mytilene, Greek coast |
4.1 |
Calculated value |
Angelidis et al, 2003 |
Adriatic Sea |
4.8-7.8 |
Min-max range |
Tankéré et al, 2001 |
Black Sea |
5.9-6.6 |
Min-max range |
Tankéré et al, 2001 |
Atlantic Ocean |
4.7-6.4 |
Min-max range |
Helmers, 1996 |
RANGE |
4.1-7.8 |
|
|
2Values and/or percentiles were calculated based on reported dissolved and particulate Pb-concentrations
For the marine environment, only one study has reported Pb partition coefficients between the aqueous phase (overlying water) and sediment (Yland et al, 1996). They reported for sediments from the North Sea and Wadden Sea a log KD of 5.66.
- Terrestrial environment
The best estimates of KDs to assess leaching losses of Pb from the soil are made by models based on in situ pore water concentrations. Adsorption KDs do not take into account ageing reactions while KDs measured in dilute salt extracts tend to underestimate the Pb concentrations in pore water as the ionic strength is usually lower in the extracts than in the pore water. Measurement of Pb concentrations in pore water overcomes these shortcomings. There are only two studies available where KDs are measured based on pore water Pb concentrations (de Groot et al., 1998; Smolders et al., 2000). If the regression models are applied to predict the KD of a “typical” soil with pH 6.5, 2 % organic matter content and 27.4 mg Pb/kg soil, the model of de Groot predicts a KD of 19 103L/kg (Al-ox = 34 mmol kg-1, %fraction 2-38 µm = 12) while the model of Smolders predicts a KD of 1.8 103L/kg. If the pH decreases to 3.5 the KDs decrease to 6.9 10² and 2.2 10² L/kg respectively, if the pH increases to 7.5 the KDs increase to 58 10³ and 3.5 10³ L/kg respectively. It is difficult to derive one “typical” realistic KD based on these two equations. Therefore the average of the median measured KDs (see Table below) by de Groot et al. (1998) and Smolders et al (2000), i.e. 6,400 L/kg, can be used as a realistic KD to calculate Pb leaching losses. A realistic low KD is 6.0 10² L/kg (10th percentile of the combined KD datasets of de Groot and Smolders), a realistic high KD is 43 10³ L/kg (90th percentile of the combined KD datasets).
Table: Regression models of KDas a function of soil parameters.
KDregression model |
Notes |
Reference |
logKD= -0.13 + 0.48 pH +0.16 log(%fraction 2-38 µm) + 0.73 log(Al-ox) |
r² = 0.84,in situKD, n=47, contaminated and uncontaminated soils from NL, B and D |
de Groot et al., 1998 |
logKD= 0.22 + 0.75 log[Pb]tot+0.30 pH |
r² = 0.94,in situKD, n=13, contaminated soils from B |
Smolders et al., 2000 |
logKD= 0.28 pH + log(%OM) + 1.0 |
r² = 0.38, adsorption KDin 0.005N salts, n=33, contaminated and uncontaminated soils from NL, UK and F |
Gerritse & Van Driel, 1984 |
log[Pb]s= -0.34 – 0.15 pH + 0.61 log(%OM*10) |
r² = 0.37, metal concentration in water extract, n=31, contaminated and uncontaminated soils from NL, UK and F |
McBride et al., 1997 |
log[Pb]tot- 0.988 log[Pb]s= 1.30 + 0.55 pH |
metal concentration in 0.005 M CaCl2+ 0.005 M Ca(NO3)2extract, n=100, contaminated soils from UK |
Jopony & Young, 1994 |
logKD= 0.37 pH + 0.44 log[Pb]tot+ 1.19 |
r² = 0.56, compilation of >70 studies, n=204 |
Sauvé et al., 2000 |
%OM: percentage organic matter in the soil; [Pb]s: Pb concentration in solution; [Pb]tot: total Pb concentration in the soil, Al-ox: amount of aluminum extracted by ammonium oxalate/oxalic acid, %OC: percentage organic carbon content.
The following information is taken into account for any environmental exposure assessment:
From the literature overview, the following partitioning coefficients have been derived for Pb:
- Aquatic compartment
Partition coefficient in freshwater suspended matter: Kdsusp= 295,121 L/kg
Partition coefficient in freshwater sediment: Kdsed,fw = 153,848 L/kg
Partition coefficient in marine sediment: Kdsed,mar = 457,088 L/kg
Partition coefficient in estuarine suspended matter: Kdsusp= 667,954 L/kg
Partition coefficient in marine suspended matter: Kd,susp= 1,518,099 L/kg
- Soil compartment
Partitioning coefficient: Kd value soil: 6,400 L/kgInformation 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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