Nickel Cobalt Manganese Hydroxide

Adsorption / desorption

Key value for chemical safety assessment

Other adsorption coefficients

Type:

log Kp (solids-water in soil)

Value in L/kg:

2.86

at the temperature of:

20 °C

Other adsorption coefficients

Type:

log Kp (solids-water in suspended matter)

Value in L/kg:

4.41

at the temperature of:

20 °C

Other adsorption coefficients

Type:

log Kp (solids-water in raw sewage sludge)

Value in L/kg:

3.94

at the temperature of:

20 °C

Other adsorption coefficients

Type:

log Kp (solids-water in settled sewage sludge)

Value in L/kg:

3.94

at the temperature of:

20 °C

Other adsorption coefficients

Type:

log Kp (solids-water in activated sewage sludge)

Value in L/kg:

3.94

at the temperature of:

20 °C

Other adsorption coefficients

Type:

log Kp (solids-water in effluent sewage sludge)

Value in L/kg:

3.94

at the temperature of:

20 °C

Other adsorption coefficients

Type:

log Kp (solids-water in sediment)

Value in L/kg:

3.85

at the temperature of:

20 °C

Additional information

KD- freshwater suspended particulate matter (SPM)

Reported KD-values between water and suspended particulate matter range

from 692 to 309,030 l/kg (Log KD: 2.84-5.49). The data are extracted from studies reporting water/suspended matter partitioning coefficients for the Netherlands, UK, France, Czech Republic, and Italy.

 Reported log KD, suspended particulate matter (SPM) values for Ni in freshwater surface waters in Europe 

Location	Log KD(L/kg)	Remarks	Reference
Four Dutch lakes Dintel Lake Hollandsch Diep Lake Volkerak Lake Zoom	3.91 4.20 3.98 3.94	Median Median Median Median	Koelmans and Radovanovic 1998
Trent river, UK Upper Swale river, UK	3.8 4.9	Modelled value Modelled value	Tipping et al.1998
Calder river, UK Nidd river, UK Swale river, UK Trent river, UK	4.00 - 5.09 3.69 - 5.32 4.24 - 5.49 2.84 - 4.45	min-max range min-max range min-max min-max range	Lofts and Tipping 2000
Rhône, France	4.51	NA	Elbaz-Poulichet et al.1996
Humber river, UK	3.8	NA	Comber et al.(1995; in Tipping et al., 1998)
Po river, Italy	4.87	median value	Pettine et al., 1994
Czech lakes (n=119)	4.26	Median value	Veselý et al., 2001
Conwy river, UK	4.33	NA	Zhou et al., 2003
Scheldt(salinity: 1.5 g/L)	3.9	Single value	Nolting et al., 1999
Tweed – Teviot Tweed – Boleside Tweed – Norham Wear Swale – Catterick Swale –Manor Nidd Ure Ouse – Ouse – Acaster Derwent Wharf Aire Calder Don Trent Great Ouse Thames	4.26 4.55 4.36 4.74 4.96 4.78 4.65 4.72 4.69 4.64 4.95 4.80 4.38 4.53 4.15 3.93 4.29 4.33	median value median value median value median value median value median value median value median value median value median value median value median value median value median value median value median value median value median value	Neal and Robson, 2000
Dutch freshwater	3.90	mean	Crommentuijn et al., 1997
RANGE	2.84 – 5.49

NA: not available

 

The partitioning coefficients between water and SPM was fitted to a cumulative distribution function (CDF) (Heijerick and P. Van Sprang, 2004; European Nickel Risk Assessment). The 10th, 50th and 90th percentiles of the CDF were selected as final suspended solids distribution coefficients for the local/regional exposure analysis:

 

KD,susp = 26,303 l/kg (log KD,susp= 4.42 L/kg) (50th percentile)

KD,susp,min = 5,754 (log KD, susp,min = 3.76 L/kg) (10th percentile)

KD,susp,max = 117,490 (log KD,susp,max = 5.07 L/kg) (90th percentile)

 

The 50th percentile value of the distribution function represents a typical suspended matter partition coefficient for EU waters and will be used for the derivation of local and typical regional.

 

KD-freshwater sediment

Reported Kp-values between water and sediment are presented in the first table below (data extracted from studies reporting water/sediment partitioning coefficients for theand) and in the second table below (river sediment data compiled by Gunn et al., 1992). The Kp values reported by Gunn et al. (1992) represent the individual or mean value of British - German rivers. Individual data that were used for the determination of mean data were not reported. The observed values range from 770 to 24,300 l/kg (Log Kp: 2.89-4.39).

 

Overview of KD-values on sediment

Water body, location	log KD L/kg	Remarks	Reference
Mersey river,	3.71	Modelled value	Turner et al. 2002
Dutch freshwater	3.72	Modelled value	Stortelder et al. 1989; in Crommentuyn et al. 1997
Dutch freshwaters: Nieuwe Merwede Rijn - Hagestijn Nieuwe Waterweg Oude Maas Waal Rijn – Lobith Ketelmeer Maas- Eijsden Ijsselmeer Haringvliet	3.79 3.86 3.88 3.88 3.89 3.92 3.96 4.04 4.06 4.34	Mean value Mean value Mean value Mean value Mean value Mean value Mean value Mean value Mean value Mean value	Van Der Kooijet al.1991
Range	3.71-4.34

 

 

Mean KD values for nickel in river sediments (Gunn et al. 1992)

Site – river / estuarine sediments	Number of measurements	Mean Kp value l/kg	Log Kp sed	Reference
Trent (Althorpe)	3	2750	3.44	Comber et al. 1995
Mersey (Howley weir)	1	7690	3.89	Comber et al. 1995
Rhine (Lauterbourg, Fr/Ger border)	8	24300	4.39	Kern et al.1998*
Ythan (Scotland)	1	770	2.89	Comber et al. 1995
Ouse (Selby)	1	1000	3.0	Comber et al. 1995
Mean		7300	3.9

 

The partitioning coefficients between water and sediment were fitted to a cumulative distribution function (CDF) (Heijerick and P. Van Sprang, 2004; European Nickel Risk Assessment). The 10th, 50th and 90th percentiles of the CDF were selected as final sediment distribution coefficients for the local/regional exposure analysis:

 

KD,sed = 7,079 L/kg (log KD,sed = 3.85) (50th percentile)

KD,sed,min = 2,138 L/kg (log KDsed,min = 3.33) (10th percentile)

KD,sed,max = 16,982 L/kg (log KD,sed,max = 4.23) (90th percentile)

 

The 50th percentile value of the distribution function represents a typical suspended matter distribution coefficient for EU waters and will be used for the derivation of local and typical

regional.

 

It should be noted that the distribution in the above tables is based on data that, with the exception of one value, only represent surface waters located in The Netherlands and the United Kingdom. The representativity of this distribution for the general case is evaluated using the distribution functions of ambient Ni-concentrations in water and sediments that were generated using extensive EU-monitoring data sets (European Union Nickel Risk Assessment, 2008/2009). Based on the 5th/95th, 50th/50th, and 95th/5th percentiles of the distributions of Ni in water/sediment, respectively, a range of theoretical KD-values was defined, with a median log KD of 4.07 and an estimated 10/90th percentile range of 3.62-4.56. These percentiles are in line with the values given and indicate that the natural variability of KD sediment is well covered in this distribution. Studies conducted after the completion of the EU RA were not included in this analysis. Data and analysis from the conclusion i) sediment program will be included after the evaluation and subsequent discussions are completed by DEPA.

KD-Marine (SPM and Sediment)

Marine partitioning coefficients for sediment and SPM are based on the study by Stuer-Lauridsen et al (1996). The following table represents the data used to derive the marine partitioning coefficients:

Partitioning coefficients KD in Danish brackish coastal water:

Location (1995)	Sediment	Suspended matter	Total water	Filtrate	Porewater	Sediment/total water	SPM/filtrate	Sediment/ porewater
	Mg Ni/Kg dw	Mg Ni/kg dw	ug Ni/L	ug Ni/L	ug Ni/L	KD, L/kg	KD, L/kg	KD, L/kg
Roskildefjord l	16.40	2.97	0.52	0.79	26.47	15710	3070	620
Roskildefjord ll	15.80	5.60	0.66	0.45	2.04	23910	8840	7680
Øresund	18.07	7.40	2.56	1.06	0.53	7070	6960	34260
Mean						15563 (log 4.2)	6290 (log 3.8)	14190 (log 4.2)

In Danish coastal waters (Table above) three locations KD,susp ranged 3070 to 8840 L/kg with a mean value 6290, i.e. log KD,susp,marine of 3.8.

In the Danish study on coastal water, the range from three locations had KD values from 7070 to 23910 L/kg with the average 15560 (Tableabove), i.e. log KD,sed,marine of 4.2.

KD- aquatic to STP:

Partitioning coefficients for aquatic to STP are based on the studies by Moriyama et al. (1998), Comber and Gunn (1992, 1994) and Gould and Genetelli (1992). The table below represents the data used to derive the aquatic to STP partitioning coefficient of Log KD of 3.4

Partition coefficients KD for STP:

STP	Coefficient	Range, L/kg	Value, L/kg	Log value	Reference
KDrs	solids-water in raw sewage sludge (m^3/m^3)	1720 – 2569	2333 ***	3.4	Moriyama et al.1989, Comber and Gunn 1994
KDa	solids-water in activated sewage sludge (m^3/m^3)	126 – 1259 453 – 1935	1000	3	Gould and Genetelli 1982 Comber and Gunn 1992

*** No published data available om KD for raw sewage – data obtained from combination of total Ni in raw sewage and Ni in faeces, assuming 100 mg/l SS

Nickel removal rates used for determining the STP removal parameter were limited to those reported after 2000 because removal rates increased with time for Denmark and the Netherlands. Ni removal rates in sewage treatment plants from recent years (2000-2002) are situated between 41% (DEPA, 2002) and 50% (CBS, 2004). Based on the available data, the value 40% removal represents a reasonable worst case removal of Ni in STP in the EU.

KD- Soil:

The variation observed in the American log KD soil values may relate to the variation in pH values. The log KD average was 2.08 in 11 soils with a pH range 4.3 to 4.85 (Buchter et al 1989) whereas the log KD average was 0.77 in 15 soil with a pH range 4.2 to 6.5 (King 1988). Anderson et al. (1988) reported log KD values in spiked Danish agricultural soils varying between 1.0 and 3.0. As the equilibration times in the Buchter et al. (1989) and King (1988) studies were relatively short, the studies performed by Janssen et al. (1997), De Groot et al. (1998) and Sauvé et al. (2000), describing field-derived partitioning coefficients, are more relevant to the risk assessment. The Janssen et al. (1997) study on 20 contaminated Dutch soils found a median value log Kp 3.17. This value is close to the log KD value of 2.86 (Aqua regia digestion) found by De Groot et al. (1998). Sauvé et al. (2000) reported a median log KD value of 3.37 for a wide range of soil types. However, since it is clear that the KD levels derived in this study are high compared to other studies and it is unclear what type of extraction techniques exactly are used, it is assumed that stronger digestion methods such as HF extraction or X-ray fluorescence -determining the metal fraction built into the crystal structure of the soil minerals, and hence not relevant for RA purposes- may be incorporated in these results.As the De Groot et al. (1998) study covered 46 European soils, although mainly Dutch soils, and aqua regia extraction was used as digestion method, this value is preferred for the risk assessment. The partition coefficient determined by aqua regia extraction is selected since for environmental purposes, the absolutely maximum fraction that may be released in time-determined through aqua regia digestion- is of interest (FOREGS Geochemical Baseline Programme – Analytical Manual, 2001). This digestion method is harmonised as an International Standard (ISO 11466) and is applied in most EU-countries. This extraction method is also applied in the ongoing scientific research program on Ni toxicity and bioavailability in soils. The log KD,soil of 2.86 (Aqua regia extraction) is used as input value for the exposure modelling.