Registration Dossier

Data platform availability banner - registered substances factsheets

Please be aware that this old REACH registration data factsheet is no longer maintained; it remains frozen as of 19th May 2023.

The new ECHA CHEM database has been released by ECHA, and it now contains all REACH registration data. There are more details on the transition of ECHA's published data to ECHA CHEM here.

Diss Factsheets

Environmental fate & pathways

Endpoint summary

Administrative data

Description of key information

Additional information

General discussion of environmental fate and pathways:

General summary of the information on environmental fate and pathways

Slag, copper smelting is a complex inorganic substance (UVCB). It mainly contains iron silicate and silicates of aluminum and calcium. Traces of metals exist in metal, mineral form or included in silicate phases. The physico-chemical characterization of the substance demonstrated that the trace metals are firmly built in and bonded into the glass/crystal structures of the silicate and other mineral phases. This resulted in limited release and low measured water-solubility of the trace metals present in the matrix.

Stability and Biodegradation

The classic standard testing protocols on hydrolysis, photo-transformation and biodegradation are not applicable to inorganic substance such as slag, copper smelting.

This was recognized in the Guidance to Regulation (EC) No 1272/2008 Classification, Labeling and Packaging of substances and mixtures (metal annex):“Environmental transformation of one species of a metal to another species of the same does not constitute degradation as applied to organic compounds and may increase or decrease the availability and bioavailability of the toxic species. However as a result of naturally occurring geochemical processes metal ions can partition from the water column. Data on water column residence time, the processes involved at the water – sediment interface (i. e. deposition and re-mobilisation) are fairly extensive, but have not been integrated into a meaningful database. Nevertheless, using the principles and assumptions discussed above in Section IV.1, it may be possible to incorporate this approach into classification. ”

Relevant fate aspects for copper slag in the environment have therefore been included in the section “Additional information on fate and pathways”.

As outlined in the CLP guidance (2009), understanding of the rate and extent of transformation /dissolution of the copper slag to soluble, potentially available metal species is relevant to the environmental hazard assessments and this is described below.

The uptake of copper slag by living organisms is related to the degree to which the metal mineral phases in the slag react with water / biological fluids and release soluble, potentially bio available ionic and other metal bearing species.

The release of metals from the slag is expected to involve transformation (eg oxidation of sulphide mineral phases) as well as dissolution of the original and transformed metal forms. Given the complex composition of copper slag, the solubility test data show that different metal transformation/dissolution processes occur simultaneously but at different rates.

Transformation/dissolution in standard medium

Standardized transformation/dissolution tests of copper slag were carried out to study its potential to release soluble available ionic and other metal-bearing species to the environment (Rodriguez et al.,2010). The rate of dissolution is expected to vary according to particle size, solid phase speciation, degree of crystalinity. Therefore transformation/dissolution tests were performed on 12 samples that are representative for alldifferent production processes, origin of the raw material (primary or secondary) and slag cooling rate (rapid cooling /granulation or slow cooling). All forms of the copper slags (stones, granules and powders) were assessed. Stones were grinded and/or sievedand particles of 1-2 mm were retained for testing. Granules and fines were tested in their original particle size as bulk material.

Considering the composition of this complex material, a 7days transformation / dissolution test at a loading of 100 mg/L was performed on one sample at pH 6 and at pH 8, following the release of a broad range of metals. (Rodriguez et al.,2010). The data clearly demonstrated higher release rates at pH 6 then at pH 8.

Transformation / dissolution tests for 7 days at pH 6 (worst case) and loading of 100mg/L were therefore performed on all samples (Rodriguez et al., 2010). The results of the 7 days test (pH6, 100mg/L) demonstrate low releases of Cu to the OECD media in the range of 0.6-6.6 μg Cu/l from granules and stones, up to 20 μg Cu /l from the fines. Low releases are recorded for some of the other metals: lead (0 – 3.9 μg/l), nickel (0 – 1.3 μg/l) and Zn (0 -18 μg/l). Release of As and Cd were below the detection limits.

Relative release rates (of Cu, Pb, Ni and Zn) were calculated as dissolved metal at pH 6 during 7 days transformation/dissolution divided by total metal content in the slag. This resulted in the following relative release rates:

-     Cu 0.1 - 0.67% for granules ans stones; 4- 4.59% for fines

-     Ni 0 - 1.92% for granules ans stones; 5.2 % for fines

-     Pb 0-0.56%                                           

-     Zn 0-1,51%                                           

The observed dissolution rates are important to quantify the amount of metal release, which is further used for acute and chronic environmental hazard assessment. They also serve as an indication of the lability of the solid phase in both chemical and physical terms.

Transformation/dissolution in mesocosm pond water

7 days transformation/dissolution tests (several loadings, pH around 8) were also carried out for a range of slags, using, as test medium water of the mesocosm ecotoxicity study carried out on one of the slag materials ( Schaefers et al, 2010).

Comparison between the 7 days transformation/dissolution tests in standard medium (Rodriguez et al., 2010) and mesocosm pond water (Schaefers et al., 2010) demonstrates, for all tested slag materials lower release rates in the classic T/D tests at pH6 . The observed metal release rates are related to differences in the test medium-specific characteristics (eg pH and DOC) as well as slag-specific characteristics (eg particle sizes and crystalline structure).

Attenuation of the released metal ions

Once released from the slag, the metal-ions will be sorbed to mineral and particulate organic matter surfaces in the water, sediment and soil and will bind to dissolved organic and sulphide materials present in water, soil and sediment compartments. Binding, precipitation and partitioning allows for a reduction of “bio-available metal species” and thus potential metal toxicity as a function of time.

The combination of metal release from the slag materials and subsequent removal of the released metal ions was assessed during the mesocosm enclosures (data for >4 months) with varying concentration of slag introduced as stones or particulates (1-2 mm). The data with metal releases from particulates (1-2 mm) demonstrated initial short term increase in copper and lead concentrations followed by a decrease and equilibration of the soluble metal concentrations. The data on the metal releases from the stones indicated more gradual increases and stabilization of the soluble metal concentration thereafter (H. Rüdel, 2010, Mesocosm study Analytical report). The data from the particulates therefore demonstrate that the released metals are removed from the water column and the data from the stones indicate that the released metals are removed from the water column and /or the metal releases rates from the slag surfaces decrease as a function of time (passivation of the slag surfaces).

Transport and distribution

Assessing the transport and distribution of the slags substance has no meaning.

The mechanisms of distribution over liquid/solid phase (adsorption /desorption, precipitation and removal from water column) of the different metals contained in the slag have been assessed in details for each single metal in respective risk assessments and/or Chemical Safety reports.

Partition coefficients for soil/water, sediment/water and suspended matter/water are available for different metals contained in the slag and further used for environmental exposure assessment. Cu, Pb, Ni, Zn, As and Cd are considered relevant. The data are summarized below.


Table 5: Overview of solid water partition coefficients (Kd) for the selected trace constituents of Copper slag and the fraction of emission directed to water by STP









Suspended matter (freshwater)


30 246

295 121

10 000

26 303

130 000

110 000

Suspended matter (marine)


131 826

295 121

10 000

26 303

130 000

110 000

Sediment (freshwater)


24 409

154 882

6 607

7 079

130 000

73 000



2 120

6 400





Fraction of STP emission directed to surface water











Crommentuyn et al. (1997)





Bioaccumulation and secondary poisoning

Copper slag is a complex metal containing substance. It contains a range of trace metals which have a great variation in their physico-chemical and toxicological properties (Cu Pb, Zn, Ni). The assessment of bio-accumulation and secondary poisoning for the slag as a whole therefore has no meaning.

Metal concentration in biota was assessed as part of the outdoor mesocosm with copper slag stones and fines (Hommen et al, 2012). In themesocosm study[FV1] , biota Cu concentration increased up to a factor of 5 compared to the controls while other metals showed usually no or a smaller increase in biota. No indication of biomagnification in the food chain was found.

Furthermore, accumulation data (BCF and BAF values) are available for all metal constituents in the slag (e.g. McGeer et al., 2003). According to CLP Guidance for complex substances (SectionIII.3.2), it is not recommended to estimate an average or weighted BCF value but identify one or more constituents for further consideration.

Metals like Cu, Zn are essential and well regulated in all living organisms and therefore the bio accumulative criterion is not applicable. Data for copper (Cu RA, 2008 and Cu CSR, 2010) demonstrate that copper is not biomagnified in the aquatic and terrestrial ecosystems and that there is no issue for secondary poisoning of copper.The copper Risk Assessment Report (2008) and REACH Chemical Safety Report (2010) have provided detailed information on (1) the essentiality of copper; (2) the homeostatic control of copper; (3) the mechanisms of action of copper ions; (4) the comparison between copper toxicity from dietary versus waterborne exposures. From this information, it has been concluded that the bio-accumulation criterion does not apply to the essential element copper. Similarly, in the zinc risk assessment and chemical safety report (2010), it has been concluded that the bio-accumulation criterion does not apply to the essential element zinc.

Secondary poisoning is however considered relevant for lead, nickel and cadmium, based on their known bioaccumulation potential.The bio-accumulation potential of lead and nickel has been assessed in the lead and nickel risk assessments (2007), REACH Chemical Safety Report (2010) and under the EU Water Framework Directive. These assessments concluded that both lead and nickel are not bio- magnified and do not pose a secondary poisoning concern.”Secondary poisoning of lead, nickel and cadmium contained in the copper slag is further taken into account in the environmental exposure assessment.

This assessment therefore concludes that copper and zinc are not bio-accumulative and that lead and nickel do not bio-magnify.

Other information on fate and pathways

Fiber-shaped particles might form during the use of copper slag as an abrasive medium in high-pressure abrasive blasting. Research showed that high concentrations of fibers are generated in the air and in the used abrasive medium during high-pressure abrasive blasting. According to research of the Berufsgenossenschaftliches Institut für Arbeitsschutz (BIGA)[[Occupational Cooperative Institute of Work Protec-tion]], the detected fibers are not asbestos fibers but fragments of the amorphous mass of the abrasive medium or newly-formed crystalline phases.

It is assumed that such fiber shape particles are typically formed during use of abrasives such as coal and steal slags, mineral abrasives (e. g., garnet, olivine)

Therefore a study has been conducted to assess the bio-persistence of fiber-shaped particles that are formed during use of copper slag as abrasive medium and the potential health hazards arising from inhalation or ingestion (Professor Dr. Ewers, 2010, Investigation of the bio-persistence of respirable fiber-shaped particles in copper slag after use as an abrasive medium) See Section 7.12, Additional toxicological information