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EC number: 237-048-9 | CAS number: 13597-46-1
- 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
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- Auto flammability
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- Endpoint summary
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- 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
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- Repeated dose toxicity
- Genetic toxicity
- Carcinogenicity
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- Specific investigations
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- Additional toxicological data
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Endpoint summary
Administrative data
Description of key information
In accordance with the EU risk assessment, and in a same approach as for aquatic ecotoxicity, the soluble zinc ion is considered as the toxic entity for zinc substances in this section on soil. Consequently, the analysis below is relevant for all zinc compounds.
It is noted that the scope of the terrestrial effect assessment under REACH is restricted to soil organisms in a narrow sense, i.e., non-vertebrate organisms living the majority of their lifetime within the soil and being exposed to substances via the soil pathway. Reliable chronic toxicity data are available for the long-term effect of zinc on 35 terrestrial species or microbial endpoints covering the 3 trophic levels (12 terrestrial plants, 10 invertebrates and 13 microbial endpoints). A total of 220 reliable EC10 and NOEC values, ranging between 31.2 and 8003.5 mg Zn/kg dry weight (dw), were selected for derivation of a PNEC value. All results were derived for soluble zinc substances (Zn(CH3COO)2, ZnCl2, Zn(NO3)2 or ZnSO4, including hydrated forms).
The bioavailability and toxicity of zinc to soil organisms was significantly affected by the equilibration time and the properties of the soils tested. Toxicity to soil organisms decreased with longer equilibration time, showing lower toxicity in field conditions compared to standard laboratory settings. Toxicity to terrestrial plants decreased with higher effective cation exchange capacity (eCEC = CEC at pH of the soil) and higher pH of the soil. Toxicity to terrestrial invertebrates decreased with higher eCEC and toxicity to microbial endpoints decreased with higher background Zn concentrations in soil. Toxicity data were only considered reliable and useful for derivation of a PNEC value when information was available on the relevant soil properties of the test soil, allowing normalization of the EC10 and NOEC. Geometric mean values were derived for the most sensitive endpoint per species or microbial process in case multiple data were available for one species or process. Species or process geometric mean values without correction for bioavailability vary between 37 mg Zn/kg for reproduction of the invertebrate Enchytraeus doerjesi and 1246 mg Zn/kg for microbial dehydrogenase activity. After correction for differences between lab and field conditions and normalization to the same soil properties of an example reference soil with pH 6, 2% organic carbon, 10% clay, eCEC of 10 cmolc/kg and 25 mg Zn/kg, species or process mean values vary between 79 mg Zn/kg for reproduction of the invertebrate Enchytraeus doerjesi and 8948 mg Zn/kg for microbial dehydrogenase activity.
Table1. Overview of the selected chronic soil toxicity values for zinc selected forthePNEC derivationfor toxicity of inorganic zincto terrestrial organisms (based on total Zn concentrations).
Test organism |
Taxonomic group |
Endpoint |
Original NOEC or EC10values, not corrected for bioavailability (mg Zn/kg dw) |
NOEC or EC10values corrected for differences between laboratory and field conditions and normalized to the same soil properties* (mg Zn/kg dw) |
||
|
|
Range (and amount) |
Species or process mean |
Range (and amount) |
Species or process mean |
|
Plants |
||||||
Allium cepa |
Amaryllidaceae(monocotyledon) |
Yield |
220 (n=1) |
220 |
328 (n=1) |
328 |
Avena sativa |
Poaceae(monocotyledon) |
Grain yield |
238 – 702 (n=4) |
374 |
447 – 1983 (n=4) |
1046 |
Brassica rapa |
Brassicaceae(eudicotyledon) |
First bloom |
546 – 549 (n=2) |
547 |
341 – 594 (n=2) |
450 |
Cucumis sativus |
Cucurbitaceae(eudicotyledon) |
Shoot yield |
179 – 5213 (n=10) |
782 |
326 – 7953 (n=10) |
1650 |
Hordeum vulgare |
Poaceae(monocotyledon) |
shoot yield |
91 (n=1) |
91* |
201 (n=1) |
201 |
root elongation |
937 – 1900 (n=3) |
1453 |
419 – 818 (n=3) |
548 |
||
Populus trichocarpa |
Salicaceae(eudicotyledon) |
root yield |
272 (n=1) |
272 |
571 (n=1) |
571 |
root elongation |
105 (n=1) |
105* |
219 (n=1) |
219 |
||
Lycopersicon esculentum |
Solanaceae(eudicotyledon) |
shoot yield |
174 (n=1) |
174 |
189 (n=1) |
189 |
root yield |
161 (n=1) |
161* |
174 (n=1) |
174 |
||
Trifolium pratense |
Fabaceae(eudicotyledon) |
shoot yield |
40 – 135 (n=6) |
65 |
111 – 335 (n=6) |
259 |
root yield |
40 – 115 (n=6) |
58* |
111 – 335 (n=6) |
227 |
||
Trigonella foenum graceum |
Fabaceae(eudicotyledon) |
yield |
150 (n=1) |
150 |
217 (n=1) |
217 |
Triticum aestivum |
Poaceae(monocotyledon) |
shoot yield |
245 – 5925 (n=14) |
612 |
528 – 16769 (n=14) |
1950 |
grain yield |
96 – 4779 (n=11) |
574 |
267 – 3187 (n=11) |
556 |
||
biomass yield |
56 – 2835 (n=8) |
362* |
105 – 1099 (n=8) |
346 |
||
Vicia sativa |
Fabaceae(eudicotyledon) |
shoot yield |
108 (n=1) |
108 |
327 (n=1) |
327 |
root yield |
40 (n=1) |
40* |
111 (n=1) |
111 |
||
Zea mays |
Poaceae(monocotyledon) |
shoot yield |
253 – 578 (n=2) |
382 |
887 – 908 (n=2) |
898 |
Invertebrates |
||||||
Aporrectodea caliginosa |
Lumbricidae(annelida) |
reproduction |
302 – 584 (n=2) |
420* |
352 – 643 (n=2) |
476 |
mortality |
1425 (n=1) |
1425 |
4034 (n=1) |
4034 |
||
Eisenia andrei |
Lumbricidae(annelida) |
reproduction |
431 (n=1) |
431 |
947 (n=1) |
947 |
Eisenia fetida |
Lumbricidae(annelida) |
reproduction |
99 – 1341 (n=30) |
306* |
255 – 1759 (n=30) |
719 |
growth |
439 – 736 (n=3) |
561 |
1078 – 1611 (n=3) |
1255 |
||
mortality |
752 – 932 (n=3) |
808 |
1570 – 2041 (n=3) |
1809 |
||
Enchytraeus albidus |
Enchytraeidae(annelida) |
reproduction |
90 – 182 (n=3) |
130 |
137 – 398 (n=3) |
252 |
Enchytraeus doerjesi |
Enchytraeidae(annelida) |
reproduction |
32 – 47 (n=3) |
37 |
69 – 103 (n=3) |
79 |
Lumbricus rubellus |
Lumbricidae(annelida) |
reproduction |
461 (n=1) |
461 |
575 (n=1) |
575 |
Lumbricus terrestris |
Lumbricidae(annelida) |
reproduction |
442 (n=1) |
442 |
533 (n=1) |
533 |
Folsomia candida |
Isotomidae(arthropoda) |
reproduction |
31 – 1261 (n=22) |
261 |
115 – 3055 (n=22) |
579 |
Proisotoma minuta |
Isotomidae(arthropoda) |
reproduction |
217 (n=1) |
217 |
1906 (n=1) |
1906 |
Sinella curviseta |
Entomobryidae(arthropoda) |
reproduction |
217 (n=1) |
217 |
282 (n=1) |
282 |
Microorganisms |
||||||
Natural soil microbial communities |
nitrogen transformation |
ammonification |
1057 (n=1) |
1057 |
1594 (n=1) |
1594 |
nitrogen transformation |
denitrification |
84 (n=1) |
84 |
102 (n=1) |
102 |
|
nitrogen transformation |
nitrification |
77 – 697 (n=19) |
179 |
101 – 955 (n=19) |
284 |
|
carbon transformation |
acetate mineralization |
346 (n=1) |
346 |
628 (n=1) |
628 |
|
carbon transformation |
glutamic acid induced respiration |
53 – 494 (n=5) |
126 |
91 – 585 (n=5) |
208 |
|
carbon transformation |
glucose induced respiration |
41 – 1393 (n=16) |
269 |
182 – 3075 (n=16) |
486 |
|
carbon transformation |
mineralization of dissolved organic carbon |
89 – 198 (n=4) |
130 |
134 – 346 (n=4) |
213 |
|
carbon transformation |
basal respiration |
55 – 313 (n=4) |
167 |
278 – 1179 (n=4) |
557 |
|
carbon transformation |
maize residue mineralization |
56 – 1144 (n=11) |
249 |
64 – 1393 (n=11) |
324 |
|
enzyme activity |
arylsulphatase |
120 – 8004 (n=5) |
862 |
188 – 5798 (n=5) |
1177 |
|
enzyme activity |
dehydrogenase |
1246 (n=1) |
1246 |
8948 (n=1) |
8948 |
|
enzyme activity |
phosphatase |
387 – 2727 (n=3) |
1128 |
130 – 5443 (n=3) |
1238 |
|
enzyme activity |
urease |
84 – 689 (n=2) |
241 |
296 – 352 (n=2) |
323 |
* pH 6, 2% organic carbon, 10% clay, eCEC 10 cmolc/kg and 25 mg Zn/kg
Additional information
A quality-screened database on the toxicity of zinc towards soil organisms has been compiled from the Zn RAR (Munn et al. 2010. European Union Risk Assessment Report - Zinc Metal. EUR 24587 EN. Luxembourg (Luxembourg): Publications Office of the European Union. JRC61245. https://op.europa.eu/en/publication-detail/-/publication/111d589d-8f52-442e-8720-c0ed745d2ed3/language-en) and updated with newly retrieved literature data (search 1995-2019). A total of 220 reliablechronic EC10 and NOEC values, ranging between 31.2 and 8003.5 mg Zn/kg dry weight (dw), were selected for derivation of a PNEC value. Reliable chronic toxicity data are available for the long-term effect of zinc on 35 terrestrial species or microbial endpoints covering the 3 trophic levels (12 terrestrial plants, 10 invertebrates and 13 microbial endpoints). Bioavailability corrections for zinc to soil organisms were derived from comprehensive research projects, where various toxicity assays were performed in a range of soils after various spiking treatments. The bioavailability corrections were discussed, agreed and applied in the EU risk assessment on zinc and 5 zinc compounds (Munn et al 2010).
Since the available ecotoxicity database for the effect of Zn to soil organisms is large, the use of the statistical extrapolation method is preferred for PNEC derivation. Based on an uncertainty analysis, and in particular the large toxicity database covering a representative range in plant and invertebrate species, microbial processes and soil conditions, the availability of normalization models, an extensive field validation, and the inherent conservatism resulting from the setting of the HC5,50%value with reference to realistic worst-case conditions of bioavailability (10th percentile of normalized HC5,50% values for 4130 soils representative for Europe), it can be concluded that the available database and models allow for the derivation of an HC5,50% that is protective for the terrestrial environment. The application of an AF = 1 is therefore proposed on the HC5,50% for the derivation of a robust and ecological relevant PNEC to be retained for the risk characterization.
The reasonable worst-case PNECsoil, based on the 10th percentile of the distribution of normalized HC5,50% values for an extensive, representative dataset of European soils, is 83.1 mg Zn/kg. If information on specific soil type and soil conditions is available, a soil-specific PNECsoil can be calculated, by applying the bioavailability corrections depending on soil properties. To this end, a tool is available that includes all data and bioavailability corrections for Zn, allowing derivation of site-specific PNEC values taking into account the local soil properties (https://www.arche-consulting.be/tools/threshold-calculator-for-metals-in-soil/).
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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