Influence of application techniques on the ecotoxicological effects of nanomaterials in soil
© Hund-Rinke et al.; licensee Springer. 2012
Received: 8 June 2012
Accepted: 10 October 2012
Published: 17 October 2012
In terrestrial ecotoxicological tests, the availability and ecotoxicity of solid nanomaterials may depend on the application technique. We compared five spiking procedures using solid uncoated TiO2 and Ag nanoparticles in standardized OECD tests with earthworms, plants and soil microflora: dry spiking of soil by applying soil or silica sand as a carrier; dry spiking of food without a carrier; and wet spiking of soil and food with an aqueous nanoparticle dispersion.
The effects of the nanomaterials were influenced by the application technique. The differences were independent of the test organism (which represented different habitats and exposure pathways) and the specificity of the effect (stimulation or inhibition). Wet spiking resulted in stronger effects than dry spiking, but the bioavailability of the particles appeared to be limited when highly-concentrated nanoparticle suspensions were used for wet spiking. The availability of the nanoparticles was slightly lower when silica sand rather than soil was used as the carrier for dry spiking, but the matrix itself (soil or food) had no effect.
There are indications that the concentrations of the stock suspensions influence the test results, so dry spiking is preferred for solid TiO2 and Ag nanoparticles. We achieved satisfactory spiking homogeneity with Ag nanoparticles using soil as a solid carrier. Further experiments with other carriers and soil types are required to confirm that the observed differences are universal in character. There was no difference in effect when TiO2 nanoparticles were applied via food or soil. The spiking of soil instead of food is preferred for TiO2 nanoparticles, as is the case for conventional chemicals.
The increasing use of nanotechnology means that nanomaterials will inevitably enter the environment. Ecotoxicological data are required for risk assessments, and a preliminary review concerning the application of OECD guidelines to manufactured nanomaterials stated that the basic practices recommended by these guidelines are suitable for the testing of nanomaterials. However, guidelines for the delivery of substances to test systems, the quantitation of exposure, and the dose metrics, need to be adapted for the testing of nanomaterials. The guidance for sample preparation and dosimetry for the safety testing of manufactured nanomaterials does not provide detailed instructions for the application of nanomaterials in aqueous or non-aqueous media, but principal procedures are listed.
The guidance also state that nanomaterials applied to solid test media such as soils and sediments can be introduced by dispersion or in solid form, although the application method should be carefully chosen to avoid damaging the test substance. For example, the use of high-energy ultrasonication to achieve homogenous aqueous dispersions, or the use of a mortar and pestle to mix solid material with a solid carrier such as silica sand or soil, may damage or modify the surface, coating or crystalline structure of the nanomaterial. The water-based dispersion of nanomaterials is recommended to provide comparability between aquatic, terrestrial and sediment tests.
Several application methods have been proposed, including the application of nanomaterial suspensions to the soil[3–8] or to food which is then added to the soil[8, 9], and the application of nanoparticle powder directly to the soil[5, 10–12]. The details of the methods may vary in terms of the substrate, e.g. application to dry or wet soil, or the dispersion technique, e.g. TiO2 can be dispersed by vortexing in water before adding to air-dried soil or by vigorous stirring for 10 min and sonicating for 30 min, followed by drop wise addition to the soil with no further homogenization. The nanomaterial concentrations in the suspensions can also vary widely, e.g. nominal concentrations between 600 mg/L and 20 g/L have been reported in the case of TiO2. Solvents may be added to increase the stability and homogeneity of the suspensions before spiking soil with carbon-based nanomaterials such as fullerene[3, 4]. For TiO2, sodium hydroxide may be added to the stock suspension to increase the pH to 10[5, 6].
It is well known that nanomaterial properties such as the zeta potential, agglomeration size, deposition and resuspension behavior depend on environmental conditions[13–17]. The application technique may therefore affect the behavior and availability of nanomaterials and consequently their overall effect on soil organisms. Although application methods have been compared systematically for aquatic tests[18–20], equivalent comparisons have not yet been carried out for soil tests.
Applied spiking procedures
Principle of spiking
To ensure the clarity of presentation, we first describe the effects achieved with different application methods within each test system, and then summarize the results focusing on the application methods.
Effects of different application methods in individual ecotoxicological tests
We used nanoparticle concentrations of up to 200 mg/kg soil dry mass (dm) for dry spiking, and concentrations of 100 and 200 mg/L for wet spiking dispersions, resulting in soil concentrations of 10 and 20 mg/kg dm. The maximum concentrations used for wet spiking were limited by the maximum water holding capacity (WHCmax) of the soil and by the maximum concentrations suitable for the stock dispersions. The WHCmax limits the maximum amount of water that can be added to achieve a water content suitable for ecotoxicological testing. Dispersions with nanoparticle concentrations higher than the maximum 200 mg/L we used were considered unsuitable because this resulted in immediate sedimentation, reflecting the formation of large agglomerates. We investigated the effects of wet and dry spiking with soil as the carrier in tests using plants, earthworms and microbes (nitrogen transformation). We also compared dry spiking with soil and silica sand carriers by considering the potential ammonium oxidation activity.
TiO 2 (P25) – Plant test: fresh weight of the shoots
Test concentration [mg/kg]1
Avena sativa Fresh weight ± SD2[g/kg]
2.591 ± 0.286
Application via powder [mg TiO2/kg]
2.571 ± 0.487
2.461 ± 0.279
2.567 ± 0.391
2.382 ± 0.329
2.200 ± 0.185
1.803 ± 0.204 *
Application via dispersion
2.130 ± 0.201 *
2.286 ± 0.368
Nitrogen transformation test
TiO 2 (P25) – Nitrogen transformation: nitrate content and nitrogen transformation rate
Test concentration [mg/kg]1
Mean nitrate concentration ± SD2[mg/kg]1
Mean nitrate concentration ± SD2[mg/kg]1
Nitrogen transformation rate ± SD2[mg/(kg * 28 d)]1
27.3 ± 1.1
32.6 ± 3.4
5.4 ± 2.7
Application via powder
27.2 ± 2.8
35.9 ± 2.9
9.6 ± 2.7
24.7 ± 1.7*
35.8 ± 2.0
11.1 ± 1.5*
21.7 ± 2.6*
36.8 ± 4.0
15.1 ± 4.3*
21.5 ± 3.4*
39.3 ± 2.5*
17.8 ± 5.7*
Application via dispersion
27.8 ± 2.8
36.2 ± 4.9
8.3 ± 2.3
26.0 ± 4.1
34.1 ± 1.3
8.1 ± 3.9
Earthworm reproduction test
Effects of TiO 2 (P25) in the earthworm reproduction test
Test concentration [mg/kg]1
Mean biomass per vessel at test start ± SD2[g]1
Biomass per vessel at test end ± SD2[g]1
Increase in biomass of adult worms after 28 d [%]3
Number of juveniles per test vessel ± SD2
3.29 ± 0.24
5.47 ± 0.36
212 ± 46
Application via powder on soil
3.37 ± 0.43
5.80 ± 0.15
295 ± 44 *
3.49 ± 0.13
5.47 ± 0.10
299 ± 74
3.45 ± 0.14
5.47 ± 0.11
315 ± 42
Application via powder on food
3.36 ± 0.25
5.48 ± 0.32
280 ± 84
3.17 ± 0.26
5.41 ± 0.33
309 ± 67 *
3.29 ± 0.27
5.37 ± 0.33
333 ± 71 *
Application via dispersion on soil
3.25 ± 0.12
5.15 ± 0.12
326 ± 74 *
3.33 ± 0.25
5.69 ± 0.15
321 ± 14 *
Application via dispersion on food
3.23 ± 0.09
5.04 ± 0.10
280 ± 52
3.21 ± 0.16
5.26 ± 0.13
279 ± 12
Most TiO2 concentrations resulted in a statistically-significant increase in the number of juveniles compared to control vessels, but the difference was not significant in some tests because of comparable large standard deviations between replicates. For example, the dry application of 100 mg TiO2 per kg dm to the soil did not yield a significant difference to the control because the standard deviation was 25% (number of juveniles: 299 ± 74) whereas the application of 50 mg/kg resulted in a statistically significant difference, reflecting the smaller standard deviation of 15% (number of juveniles: 295 ± 44).
Effect of TiO 2 and silver nanoparticles on microbial ammonium oxidation activity
Test concentration [mg/kg]1
Ag nanoparticles Microbial ammonium oxidation activity ± SD2[ng/(g * h)]1
TiO2nanoparticles Microbial ammonium oxidation activity ± SD2[ng/(g * h)]1
50.9 ± 8.3
25.7 ± 5.6
10 mg/kg via soil
47.0 ± 3.6
23.6 ± 1.0
10 mg/kg via silica sand
50.4 ± 6.3
24.5 ± 1.8
100 mg/kg via soil
3.0 ± 0.9 *
18.8 ± 2.7 *
100 mg/kg via silica sand
15.9 ± 3.7 *
26.1 ± 7.3
The effect of different spiking procedures
Homogeneity of spiking – mean values of six samples taken at different locations of the soil spiked with Ag nanoparticles (dry application with soil as the carrier)
Measured concentration [mg/kg]1
Standard deviation [%]
Solid Ag - 100 mg/kg
80.4 ± 3.1
Solid Ag - 10 mg/kg
7.5 ± 0.8
In our tests, we applied TiO2 and Ag nanoparticles at concentrations higher than those expected in the environment based on a published model predicting soil concentrations of 1.28 μg/kg TiO2 and 22.7 μg/kg Ag in Europe. Risk assessment is based on NOEC and/or EC50 values, which are reduced by assessment factors to compensate for the limited number of test organisms. The use of assessment factors means that the consideration of test concentrations above environmental values is justified. Therefore, it is essential to develop procedures that allow the application of comparably high test concentrations for subsequent risk assessment.
We compared dry and wet spiking using water as dispersant. Our results clearly show that the application method can affect the ecotoxicological impact of nanomaterials, and that wet spiking can cause stronger effects than dry spiking. The wet application of 10 mg/kg nanoparticles resulted in a statistically-significant differences to the control in the plant test, whereas the dry spiking approach did not. We used 10 and 20 mg/kg TiO2 concentrations for wet spiking in the earthworm tests, and the stimulatory effect was comparable to or higher than that obtained for the lowest concentration used for dry spiking (50 mg/kg). The differences in the bioavailability of the test substance may therefore reflect the different agglomeration and sorption behavior of the nanomaterial under dry and wet spiking conditions. The characterization of nanomaterials in soil is still an important field of research and the state of the art has been recently reviewed[27, 28]. Unless we are able to characterize nanomaterials in soil, it may be difficult to explain their differing effects and to interpret the results of spiking studies.
No concentration-effect dependence was observed when wet application methods were used, although there was a statistically significant difference between experimental and control vessels. This agrees with previous reports showing that the application of 0.5, 1 and 2 g/kg dm TiO2 induces statistically significant but not concentration-dependent effects on microbial soil respiration. Stock TiO2 concentrations of up to 20 g/L were used in the investigation discussed above. McShane et al. avoided this by using an application method based on the required nanoparticle concentration in the soil. TiO2 dispersions were used only for soil concentrations up to 200 mg/kg. The maximum concentration in the aqueous stock suspension was 600 mg/L. Higher test concentrations were achieved by the dry application of TiO2, which was justified by the physical limitations of the dispersion method (i.e. the large amounts of nanomaterials needed to create the dispersions with nominal concentrations ≥ 1000 mg/kg).
For tests in aqueous media, the nanoparticle concentration in the dispersion affects the size of the resulting agglomerates, which reduces the toxicity of the nanoparticles[29, 30]. Tests using Caenorhabditis elegans on agar plates resulted in the steady-state inhibition of survival despite the increasing test concentrations of Ag nanoparticles. Therefore, we propose that the statistically-significant but concentration-independent effects of nanoparticle dispersions we observed reflect the comparable bioavailability of nanoparticles with different total concentrations due to the agglomeration behavior of nanoparticles in the stock preparation. We tested the two nanoparticle concentrations (10 and 20 mg/L) based on different stock suspensions (100 and 200 mg/L) and observed ecotoxicological effects on plants, earthworms and nitrogen-transforming microorganisms. We observed statistically-significant differences between experimental and control vessels in terms of plant growth and earthworm reproduction, although the mean values of the relevant parameters (plant fresh weight, number of juvenile earthworms) did not correspond to the differing concentrations. For example, the higher test concentrations had a lower impact on plant biomass, and the number of juvenile earthworms was similar at both test concentrations. It is possible that concentration-effect relationships could be revealed by repeating the tests at lower concentrations based on less-concentrated stock suspensions.
Ploeg et al. and Kool et al. observed concentration-dependent effects for C60 and ZnO even at high soil concentrations (C60: up to 154 mg/kg; nano-ZnO: up to 6400 mg Zn/kg dm) after applying the nanomaterials to soil using soil extracts instead of deionized water. Natural stabilizers (e.g. dissolved organic matter) in soil extracts may improve the stability and reduce the agglomeration of nanomaterials resulting in higher bioavailability. The recommendation of soil extracts for standardized tests means that the soil types and preparation methods must also be standardized, e.g. using guideline ISO 21268-1, which recommends a soil to water ratio of 1:2 and 24 h shaking.
Johansen et al. avoided highly-concentrated C60 stock suspensions by the repeated application of a weaker suspension until the desired test concentration was achieved. Between individual applications, the soil was dried in a vacuum oven to reduce the water content before the next dose was added. However, this may promote the aging of the nanomaterial in situ, modifying the sorption and hence the availability to test organisms. For example, Schreck et al. studied the effect of lead-enriched particulate matter by comparing freshly spiked, aged and long-term polluted soils. The ecotoxicity and bioavailability of the contaminated particulate matter was strongly influenced by complex interactions with the soil, and ageing was shown to reduce the toxicity of the test substance. Donner et al. investigated the aging of zinc applied as ZnSO4 in field soils, and found that 65Zn radioisotope dilution declined over time providing evidence of Zn fixation. This effect was not obvious in the ecotoxicological tests and was attributed to the strong regulatory impact of abiotic properties. Unless we are able to characterize nanomaterials in soil, it may be difficult to consider their effects and interpret the results of spiking studies using repeated drying/wetting cycles.
Dry application produced concentration-effect relationships in all the test systems. The nanomaterials were applied using a carrier. Inert carriers such as silica sand, for chemicals that are insoluble in water and organic solvents, are already described in the OECD test guidelines. We compared dry test soil and silica sand and found that effects were higher when the TiO2 and Ag nanoparticles were applied using dry test soil instead of silica sand. We assume that the bioavailability of the particles is reduced by silica sand. We only tested one soil, but this fulfilled all the criteria in the test guidelines for natural soils used as a test medium. The soil is characterized by a high content of sand (71%), low levels of organic carbon (0.93%) and a pH in the range 5.5–7.5. The use of different soil types will determine whether silica sand always reduces the bioavailability of nanomaterials compared to natural soil (indicating that the observed difference is a universal characteristic) or whether the effect is specific to particular soil types.
The homogeneity of Ag nanoparticle powder following the spiking of carrier soil was determined by chemical analysis and we observed a low standard deviation at both test concentrations (4% at 100 mg/kg dm and 11% at 10 mg/kg dm). The homogeneity of TiO2 spiking could not be demonstrated due to the high background level of TiO2 in the applied soil (1.3 g/kg). To include biological variability, we selected 68 results (mean values and standard deviations) with either TiO2 or Ag nanoparticles from randomly-selected tests with different test organisms and test parameters, including earthworm reproduction, plant growth and microbial nitrogen and carbon transformation. All tests were carried out according to the appropriate OECD guidelines. Furthermore, we applied the same criteria to tests with conventional chemicals (60 test results, mean values and standard deviations). Every standard deviation was expressed as a percentage of the respective mean value. We calculated the 90% percentile of the standard deviations for both sets of tests (nanomaterials and conventional chemicals) and found that 90% of the standard deviations in the nanomaterial tests were in the range 2–17% compared to 3–24% in the conventional chemical tests. The variability of the chemical analysis results for Ag was comparable to the variability of the ecotoxicological test results with Ag and TiO2 nanomaterials. Furthermore, the variability of the nanomaterial tests based on dry spiking using soil as the carrier was comparable to the variability of the conventional substance tests spiked with aqueous solutions. We therefore concluded that the dry spiking procedure using soil as the carrier achieves adequate spiking homogeneity, at least for Ag and uncoated TiO2 nanoparticles.
Earthworms were exposed to the test substances via spiked soil or food using wet and dry application methods. The wet application of nanomaterials to soil had a marginal stimulating effect on reproduction compared to wet application in food, but none of the differences between the matrices was statistically significant. For dry application no obvious difference was observed. Lapied et al. also compared the effect of earthworm exposure via spiked food and via soil, and attributed the absence of effects in the tests with spiked food to avoidance behavior. We did not observe avoidance of spiked food in our experiments, even though the substance concentrations in the spiked food were higher (1272 mg/kg dm for wet application compared to 100 mg/kg dm in the study discussed above). Feeding was implemented by spreading dung on the soil surface as recommended in the test guideline, thus the removal of dung by feeding was easy to verify. The biomass increase in adult worms was also a useful indicator of food uptake, and this was comparable for our spiked food and spiked soil experiments. The behavioral differences may reflect the use of uncoated particles in our experiments and Al2O3-coated particles in the previous investigation. Avoidance behavior has also been reported for earthworms exposed to Ag nanoparticles indicating perception of the contaminants.
Pros and cons for wet and dry spiking
· High concentrations independent of test material
· Higher bioavailability at least at lower test concentrations
· Procedure independent of test concentration
· Reduced bioavailability
· Functionalization of surface by stirring / sonication
· Test concentrations comparably low (limitation: WHCmax, sedimentation of nanomaterials in stock dispersion)
· Agglomeration at higher concentrations of stock suspension can limit bioavailability; behavior differs according to material
The nature of the ecotoxicological effect of the nanomaterials was inhibitory in the case of plants (reduced growth) but stimulatory in the case of earthworm reproduction and microbial nitrogen transformation. In contrast, McShane observed no impact on earthworm reproduction in tests using artificial and natural soils. The stimulation of earthworm reproduction and its seasonal dependency have been comprehensively discussed.
A transient reduction in microbial activity is often observed following an environmental insult and the subsequent overstimulation and return to normal activity reflects an adaptive response in the microbial population. As specified in the test guideline, we determined the nitrate concentration in the incubation vessels at only two time points, i.e. 3 h and 28 days after application. Nitrate generated in the incubation vessels is not consumed under the test conditions, thus a net increase at the test end-point indicates an increase in microbial nitrification activity during the 4-week incubation period. It is unclear whether there is still a difference in microbial activity between experimental and control vessels after the incubation period of 28 days. More detailed data on the effects of nanomaterials on microbial nitrification activity in the soil were outside the scope of this investigation, and would require additional sampling time points that are not currently mandated for the testing of non-agrochemicals. Additional data could also be produced by including modified tests, such as the determination of potential ammonium oxidation activity.
Our experiments using uncoated TiO2 and Ag nanoparticles showed that the application technique influences the severity of the effects observed in standardized ecotoxicity tests. The differences we detected were not dependent on either the direction of the effects (inhibition or stimulation) or on the test organisms, which represented different habitats and exposure pathways.
Wet and dry spiking
The most significant difference in ecotoxicological impact was observed when comparing wet and dry spiking methods. Wet spiking resulted in stronger effects than dry spiking. The effects caused by dry spiking were concentration-dependent for the selected test concentrations (3-6 concentrations, depending on the test) whereas there was no such relationship for the two test concentrations when wet spiking methods were applied using water as the carrier. Lower wet spiking concentrations than those reported here may have resulted in concentration-effect curves. Higher test concentrations do not seem to be appropriate because the bioavailability of the particles appeared to be limited when highly-concentrated nanoparticle suspensions were used for wet spiking. Therefore, concentration-dependent effect curves are more difficult to obtain for wet application methods compared to dry spiking because the appropriate range of test concentrations has to be selected. The use of highly-concentrated stock suspensions could generate false negative results and incorrect hazard assessments. Limit tests investigating a single high test concentration are therefore inappropriate for wet spiking. Dry spiking is the preferred application method for solid, uncoated TiO2 and Ag nanoparticles to ensure the effects are not dependent on the particle concentration used for spiking, even though the bioavailability is reduced by the dry spiking method. Satisfactory test substance homogeneity can be achieved using a solid carrier, at least for Ag. If wet application is necessary, then further experiments will be required to establish parameters for successful use, e.g. the use of dispersants that are more suitable than water or recommendations on the procedure to select suitable test concentrations.
Silica sand and air dried soil as solid carriers
Silica sand reduced the bioavailability of the test substances compared to dried soil, but a wider range of carrier materials (different grades of silica sand and different soil types) will need to be tested to determine whether the observed differences are universal in character.
Spiking soil and food
We found no significant difference in earthworm reproduction when the test substances were applied in spiked soil and spiked food. The bioavailable concentrations of uncoated TiO2 for earthworms seem to be comparable regardless of whether exposure is via food or soil. The standardized test guidelines recommend soil spiking and this is also the method of choice for the testing of nanomaterials because the soil is distributed throughout the test vessel whereas the food is concentrated at the surface. The use of spiked soil prevents the extent of exposure being influenced by avoidance behavior. However, exposure via food is recommended if specific information on this pathway is required.
Physicochemical properties of RefeSol 01A soil
WHCmax2 [ml H2O/kg]
Most experiments were performed with P25, which is used in the Sponsorship Programme on the Testing on Manufactured Nanomaterials launched by the Working Party on Manufactured Nanomaterials (WPMN), which was established by the Chemicals Committee of the Organisation of Economic Cooperation and Development (OECD). The WPMN agreed on a priority list of nanomaterials and a list of endpoints relevant for environmental safety testing. A detailed description of P25 is presented by Schlich et al. but major characteristics include anatase/rutile crystal structure, a primary particle size of 21 nm, a composition > 99% TiO2, a Brunauer Emmet-Teller (BET) surface of 60 m2/g and no coating. The TiO2 nanoparticles we used have photocatalytic properties but these are not likely to affect their toxicity in soil because the energy input from illumination is missing. Additional experiments were carried out using commercially-available silver nanoparticles (Sigma-Aldrich silver nanopowder, catalog number 576832). The particle size was <100 nm, the purity 99.5% metal, and the surface area 5.0 m2/g. In contrast to TiO2, silver nanoparticles release ions that are highly reactive and avidly bind to organic structures such as proteins, DNA and RNA, causing structural changes or inhibiting replication.
Almost all ecotoxicological tests were carried out using spiked soils. A small number of earthworm tests were carried out with spiked food.
Spiking soil with solid nanoparticles using soil as the carrier
The TiO2 and Ag nanoparticles were applied by mixing the powdered test material and air-dried carrier soil with the same physicochemical properties as the test soil (Table8). Enough TiO2 powder was added to the carrier so that the correct final test concentration was achieved when 1% carrier soil and 99% test soil were mixed to homogeneity (see below). The soil was mixed with a spoon rather than a pestle to avoid modifying the TiO2 crystalline structure. Untreated soil (at 20–30% WHCmax) was spread on a plate and the spiked carrier soil was evenly distributed over the test soil before manual mixing. The mixed soil was adjusted to 55% WHCmax using deionized water. Different test concentrations were applied depending on the test organism:
Plants (Avena sativa; oat) – TiO2: 10, 20, 30, 44, 67 and 100 mg/kg soil dry mass (dm).
Soil microflora (nitrogen transformation) – TiO2: 9.3, 21, 45 and 100 mg/kg soil dm.
Soil microflora (ammonium oxidation activity) – Ag: 10 and 100 mg/kg soil dm.
Earthworms (Eisenia fetida) – TiO2: 50, 100 and 200 mg/kg soil dm.
Spiking soil with solid nanoparticles using silica sand as the carrier
We used the procedure described above, replacing the air-dried soil with silica sand as used in the building trade, with a particle size of up to 0.5 mm and a specific surface area of 89 cm2/g. The same silica sand has been used for tests with artificial soil as described e.g. in OECD test guideline 222. The procedure was used to measure microbial ammonium oxidation activity with Ag concentrations of 10 and 100 mg/kg soil dm.
Spiking soil with aqueous nanoparticle dispersions
A dispersion of TiO2 nanoparticles was prepared by homogenizing a specific mass of particles in deionized water with a magnetic flea (900 rpm for 1 min) followed by ultrasonication (3 min) in a bath sonicator. The test soil was dried to ~10% WHCmax and spread on a plate. The full dose of TiO2 dispersion (enough to achieve the required test concentration in one application) was sprayed onto the soil using a syringe coupled to a cannula, and mixed thoroughly. Following the application of the dispersion and additional water used to clean the syringe, the test soil was adjusted to 55% WHCmax. The concentrations of the dispersions were made up to 95 and 187 mg/L in a total volume of 500 mL deionized water. Approximately 262 ml of test dispersion was added to 2.5 kg of test soil dm to increase the WHC from ~10% to 55%, corresponding to 10 and 20 mg/kg dm doses. For tests with soil microflora (nitrogen transformation), the final concentrations were 9.3 and 21 mg/kg soil dm.
Spiking food with solid nanoparticles
We mixed 40 g of air-dried, ground cow manure from an organic farm (enough for four replicates per test concentration) with the appropriate amount of TiO2 powder to achieve 50, 100 and 200 mg/kg final test concentrations, and divided the homogeneous mixture into four aliquots of 10 g. The mixture was moistened with 120 ml deionized water and 40 g of moist food was placed on the soil surface in 1-L test containers. The total amount of TiO2 per test vessel was the same in the spiked food and spiked soil experiments.
Spiking food with aqueous nanoparticle dispersions
We mixed 40 g of air-dried, ground cow manure with 120 ml concentrated TiO2 dispersions (212 and 424 mg/L in deionized water, in a total volume of 500 mL, prepared by stirring at 900 rpm for 1 min and ultrasonication for 3 min). The dung was applied to 2.5 kg dm soil, corresponding to soil concentrations of 10 and 20 mg/kg soil dm.
All tests were carried out as recommended in the corresponding OECD test guidelines. The earthworm reproduction test with Eisenia fetida permits the use of Eisenia fetida or Eisenia andrei as test organisms. We used Eisenia andrei which has been cultured in our laboratory for more than 15 years. The earthworms were acclimated to the test soil for 7 days prior to testing. We filled polypropylene containers (Bellaplast GmbH, Alf) to a depth of ~5 cm with 640 g dry mass of soil (55% WHCmax) and then spread 40 g wet cow manure (10 g air-dried cow manure, ground and moistened before application) onto the surface. The cows were kept in an ethical husbandry. The tests comprised eight replicates for the control and four replicates for each TiO2 concentration.
Ten earthworms weighing between 300 and 450 mg were added to each container, and the containers were incubated at 20 ± 2°C with a light/dark cycle of 16/8 h (~700 lux). Once per week, the water content was checked gravimetrically and evaporated water was replaced. Every 7 days, 20 g (wet weight corresponding to 5 g dry weight) of uncontaminated food was spread on the soil surface in each container. After 28 days, the adult earthworms were removed and weighed, and after 56 days the number of juveniles in each test container was counted.
Oat seedlings (Avena sativa) were cultivated in round nonporous plastic containers 85–95 mm in diameter. A glass fiber wick drew water from a reservoir through the bottom of the container to ensure consistent soil moisture. The water contained 1 mL/L fertilizer (Floragard Vertriebs GmbH, Oldenburg, Germany). The nutrient content of the fertilizer was ammonium 23 mg/L, iron (chelate) 0.50 mg/L, nitrate 23 mg/L, copper (chelate) 0.30 mg/L, phosphate 30 mg/L, manganese (chelate) 0.30 mg/L, potassium oxide 60 mg/L, molybdenum 0.01 mg/L, zinc (chelate) 0.05 mg/L and boron 0.10 mg/L. The containers were filled with approximately 280 g of moist soil (about 55% of WHCmax). Five seeds of the same size were planted in each replicate container immediately after spiking, and 24 h later the wicks were connected to the reservoir to moisten the soil. The test was carried out in a plant growth chamber at 20 ± 2°C, 70 ± 25% humidity and with a 16-h photoperiod (light intensity >7000 lux, color 25 universal white).
The 14-day growth phase started when 50% of the seedlings in the control group had emerged (growth day 1). The number of emerged seedlings was recorded in all containers. Emergence and visual signs of phytotoxicity and mortality were recorded throughout the exposure period. On growth day 14, all seedlings were counted and the aboveground wet biomass of the plants was measured immediately after harvesting.
For the nitrogen transformation test with soil microflora we augmented sieved and spiked soil with powdered plant material (lucerne-grass-green meal) at a plant/soil ratio of 5 g plant per kilogram of soil (dry mass). Three incubation containers per treatment were filled with 658 g of spiked soil along with three matching controls. The test was carried out in darkness at 20 ± 2°C for 28 days, during which the moisture content of the soil was maintained at 40–60% of WHCmax with a maximum range of 5%. The mass in the test vessels was measured weekly. Evaporated water was replaced with deionized water.
Samples of each treated and control vessel were analyzed for nitrate content at the beginning (3 h after application, day 0) and at the end of the exposure period (28 days). Nitrate was extracted from soil by shaking samples (20 g dm) with 0.1 M KCl solution at a ratio of 5 mL of KCl solution per gram dry weight for 60 min at 150 rpm. The mixtures were filtered and the liquid phases were analyzed for nitrate photometrically (Spectroquant® NOVA 400) immediately after preparing each extract. The nitrate concentration on days 0 and 28 was used to calculate the nitrogen transformation rate.
The short-term potential ammonium oxidation test was carried out using sieved and spiked soil. Four 250-mL Erlenmeyer flasks per treatment were filled with 25 g dm of spiked soil along with four matching controls. The vessels were incubated in darkness at 20 ± 2°C for 24 h and then mineral test medium was added to make up the volume to 100 mL. The medium consisted of KH2PO4 (0.56 mM), K2HPO4 (1.44 mM), NaClO3 (5 mM), (NH4)2SO4 (1.50 mM). The slurries were incubated on an orbital shaker at 25 ± 2°C, and 10-mL samples were removed after 2 and 6 h, supplemented with 10 mL 4 mol/L KCl, filtered and nitrite levels in the filtrate were determined photometrically.
Statistical analysis was carried out using ToxRat® Pro v2.10 software for ecotoxicity response analysis (ToxRat® Solutions GmbH, Alsdorf, Germany).
Determination of Ag levels
Digestion was carried out according to standardized guidelines[41, 42] using soil dried at 105°C for at least 12 h until it reached a constant weight. Approximately 3 g of the homogenized material was mixed with 28 g of aqua regia and incubated at room temperature for 16 h without agitation. The mixture was then heated under reflux for 2 h with glass chips and 1-octanole added to avoid overboiling and foaming. The mixture was cooled to room temperature, carefully made up to 100 mL and filtered (0.45 μm syringe filter, polyethersulfon membrane, Pall Corporation, New York). The concentration of silver was determined by inductively coupled plasma optical emission spectrometry (ICP-OES) using an IRIS Intrepid II (Thermo Electron, Dreieich, Germany) with a matrix-adjusted calibration carried out before each measurement. Silver was detected at 328.068 nm and compared to the certified reference material TMDA-70 (certified with 10.9 μg/L Ag) as a quality assurance sample. According to the quality assurance requirement, the silver recovery was in the range of ± 15% of the certified value. However, regarding Ag concentrations measured by ICP-OES, the mean recovery (accuracy) and precision of the non-digested CRM TMDA-70 measurements was 101 ± 2.9% (n = 4). The recovery for Merck IV standard solution samples containing 50 μg/L was 101 ± 2.7% (n = 4) and 94.7 ± 0.7% for 500 μg/L. Silver concentrations in reagent blanks were always below the limit of detection in the corresponding measurement series.
This study was developed in the context of the OECD Sponsorship Programme for the safety testing of nanomaterials. It was carried out on behalf of the German Federal Environment Agency (FKZ 3709 65 416) and financed by federal funds.
- ENV/JM/MONO(2009)21 (10-Jul-2010): Preliminary Review of OECD Test Guidelines for their Applicability to Manufactured Nanomaterials. OECD Environment, Health and Safety Publications Series on the Safety of Manufactured Nanomaterials. 15th edition. 2009. [http://www.oecd.org/document/53/0,3746,en_2649_37015404_37760309_1_1_1_1,00.html] Google Scholar
- ENV/JM/MONO(2010)25) (31-May-2010): Preliminary Guidance Notes on Sample Preparation and Dosimetry for the Safety Testing of Manufactured Nanomaterials. 24th edition. [http://www.oecd.org/document/53/0,3746,en_2649_37015404_37760309_1_1_1_1,00.html] 
- Tong Z, Bischoff M, Nies L, Applegate B, Turco RF: Impact of fullerene (C60) on a soil microbial community. Environ Sci Technol 2007, 41: 2985–2991. 10.1021/es061953lView ArticleGoogle Scholar
- Johansen A, Pedersen AL, Jensen KA, Karlson U, Hansen BM, Scott-Fordsmand JJ, Winding A: Effects of C 60 fullerene nanoparticles on soil bacteria and protozoans. Environ Toxicol Chem 2008, 27: 1895–1903. 10.1897/07-375.1View ArticleGoogle Scholar
- McShane H, Sarrazin M, Whalen JK, Hendershot WH, Sunahara GI: Reproductive and behavioral response of earthworms exposed to nano-sized titanium dioxide in soil. Environ Toxicol Chem 2012, 31: 184–193. 10.1002/etc.714View ArticleGoogle Scholar
- Whitfiel Aslund ML, McShane H, Simpson MJ, Simpson AJ, Whalen JK, Hedershot WH, Sunahara GI: Earthworm sublethal responses to titanium dioxide nanomaterial in soil detected by 1 H NMR metabolomics. Environ Sci Technol 2012, 46: 1111–1118. 10.1021/es202327kView ArticleGoogle Scholar
- Ge Y, Schimel JP, Holden PA: Evidence for negative effects of TiO 2 and ZnO nanoaprticles on soil bacterial communities. Environ Sci Technol 2011, 45: 1659–1664. 10.1021/es103040tView ArticleGoogle Scholar
- Lapied E, Nahmani JY, Moudilou E, Cjaurand P, Labille J, Rose J, Exbrayat J-M, Oughton DJ, Joner EJ: Ecotoxicological effects of an aged TiO2 nanocomposite measured as apoptosis in the anecic earthworm Lumbricus terrestris after exposure through water, food and soil. Environ Int 2011, 37: 1105–1110. 10.1016/j.envint.2011.01.009View ArticleGoogle Scholar
- Scott-Fordsmand JJ, Krogh PH, Schaefer M, Johansen A: The toxicity testing of double-walled nanotubes-contaminated food to Eisenia veneta earthworms. Ecotox Environ Safety 2008, 71: 616–619. 10.1016/j.ecoenv.2008.04.011View ArticleGoogle Scholar
- Hu CW, Li M, Cui YB, Li DS, Chen J, Yang LY: Toxicological effects of TiO 2 and ZnO nanoparticles in soil on earthworm Eisenia fetida . Soil Biol Biochem 2010, 42: 586–591. 10.1016/j.soilbio.2009.12.007View ArticleGoogle Scholar
- Coleman JG, Johnson DR, Stanley JK, Bednar AJ, Weiss CA, Boyd RE, Steevens JA: Assessing the fate and effects of nano aluminium oxide in the terrestrial earthworm, Eisenia fetida . Environ Toxicol Chem 2010, 29: 1575–1580. 10.1002/etc.196View ArticleGoogle Scholar
- Du W, Sun Y, Ji R, Zhu J, Wu J, Guo H: TiO 2 and ZnO nanoparticles negatively affect wheat growth and soil enzyme activities in agricultural soil. J Environ Monit 2011, 13: 822–828. 10.1039/c0em00611dView ArticleGoogle Scholar
- French RA, Jacobson AR, Kim B, Isley SL, Penn RL, Baveye PC: Influence of ionic strength, pH and cation valence on aggregation kinetics of Titanium Dioxide nanoparticles. Environm Sci Technol 2008, 43: 1354–1359.View ArticleGoogle Scholar
- Boncagni NT, Otaegui JM, Warner E, Curran T, Ren J, Cortalezzi MM: Exchange of TiO 2 Nanoparticles between Streams and Streambeds. Environm Sci Technol 2009, 43: 7699–7705. 10.1021/es900424nView ArticleGoogle Scholar
- Mukherjee B, Weaver JW: Aggregation and charge behavior of metallic and nonmetallic nanoparticles in the presence of competing similarly charged inorganic ions. Environm Sci Technol 2010, 44: 3332–3338. 10.1021/es903456eView ArticleGoogle Scholar
- Ottofuelling S, von der Kammer F, Hofmann T: Commercial titanium dioxide nanoparticles in both natural and synthetic water: comprehensive multidimensional testing and prediction of aggregation behavior. Environm Sci Technol 2011, 45: 10045–10052. 10.1021/es2023225View ArticleGoogle Scholar
- Cumberland SA, Lead JR: Particle size distributions of silver nanoparticles at environmentally relevant conditions. J Chromatogr A 2009, 1216: 9099–9105. 10.1016/j.chroma.2009.07.021View ArticleGoogle Scholar
- Hund-Rinke K, Schlich K, Wenzel A: TiO 2 nanoparticles - Relationship between dispersion preparation method and ecotoxicity in the algal growth test. Umweltwiss Schadst Forsch 2010, 22: 517–528. 10.1007/s12302-010-0147-0View ArticleGoogle Scholar
- Römer I, White TA, Baalousha M, Chipman K, Viant MR, Lead JR: Aggregation and dispersion of silver nanoparticles in exposure media for aquatic toxicity tests. J Chromatogr A 2011, 1218: 4226–4233. 10.1016/j.chroma.2011.03.034View ArticleGoogle Scholar
- Manier N, Garaud M, Delalain P, Aguerre-Chariol O, Pandard P: Behaviour of ceria nanoparticles in standardized test media – influence on the results of ecotoxicological tests. J. Phys.: Conf. Ser. 304th edition. 2011, 012058.Google Scholar
- OECD Guideline for the Testing of Chemicals Test No. 222, 2004. Earthworm Reproduction Test (Eisenia fetida/Eisenia andrei). 2004.Google Scholar
- OECD Guideline for the Testing of Chemicals Test No. 208, 2006. Terrestrial Plant Test: Seedling Emergence and Seedling Growth Test. 2006.Google Scholar
- OECD Guideline for the Testing of Chemicals Test No. 216, 2000. Soil Microorganisms: Nitrogen Transformation Test. 2010.Google Scholar
- ISO 15685, 2004. Soil quality - Determination of potential nitrification and inhibition of nitrification - Rapid test by ammonium oxidation. 2004.Google Scholar
- Gottschalk F, Sonderer T, Scholz RW, Nowack B: Modeled Environmental concentrations of engineered nanomaterials (TiO2, ZnO, Ag, CNT, Fullerenes) for different Regions. Environ Sci Technol 2009, 43: 9216–9222. 10.1021/es9015553View ArticleGoogle Scholar
- European Chemicals Agency (ECHA): Guidance on information requirements and chemical safety assessment: Chapter R.10: characterisation of dose [concentration]-response for environment. 2008. [http://echa.europa.eu/documents/10162/17224/information_requirements_r10_en.pdf] Google Scholar
- Fareé M, Sanchís J, Barceló D: Analysis and assessment of the occurrence, the fate and the behavior of nanomaterials in the environment. Trends Anal Chem 2011, 30: 517–527. 10.1016/j.trac.2010.11.014View ArticleGoogle Scholar
- Von der Kammer F, Ferguson PL, Holden PA, Masion A, Rogers KR, Klaine SJ, Koelmans AA, Horne N, Unrine JM: Analysis of engineered nanomaterials in complex matrices (environment and biota): General considerations and conceptual case studies. Environ Toxicol Chem 2012, 31: 32–49. 10.1002/etc.723View ArticleGoogle Scholar
- Lee WM, Ha SW, Yang CY, Lee JK, An YJ: Effect of fluorescent silica nanopartilces in embryo and larva of Oryzias latipes : Sonic effect in nanoparticle dispersion. Chemosphere 2011, 82: 451–459. 10.1016/j.chemosphere.2010.09.055View ArticleGoogle Scholar
- Gaiser BK, Fernandes TF, Jepson MA, Lead JR, Tyler CR, Baalousha M, Biswas A, Britton GJ, Cole PA, Johnston BD, Ju-Nam Y, Rosenkranz P, Scown TM, Stone V: Interspecies comparsons on the uptake and toxicity of silver and cerium dioxide nanoparticles. Environ Toxicol Chem 2012, 31: 144–154. 10.1002/etc.703View ArticleGoogle Scholar
- Kim SW, Nam SH, An YJ: Interaction of silver nanoparticles with biological surfaces of Caenorhabditis elegans . Ecotox Environ Safety 2012, 77: 64–70.View ArticleGoogle Scholar
- van der Ploeg MJC, Baveco JM, van der Hout A, Bakker R, Rietjens IMCM, van den Brink N: Effects of C60 nanoparticle exposure on earthworms ( Lumbricus rubellus ) and implications for population dynamics. Environ Pollut 2011, 159: 198–203. 10.1016/j.envpol.2010.09.003View ArticleGoogle Scholar
- Kool PL, Ortiz MD, van Gestel CAM: Chronic toxicity of ZnO nanoparticles, non-nano ZnO and ZnCl2 to Folsomia candida (Collembola) in relation to bioavailability in soil. Environ Pollut 2011, 159: 2713–2719. 10.1016/j.envpol.2011.05.021View ArticleGoogle Scholar
- ISO 21268–1, 2007: Soil quality – Leaching procedures for subsequente chemical and ecotoxicological testing of soil and soil materials – Part 1: Batch test using a liquid to solid ration of 2 l/kg dry matter. 2007.Google Scholar
- Schreck E, Foucoult Y, Geret F, Pradere P, Dumat C: Influence of soil ageing on bioavailability and ecotoxicity of lead carried by process waste metallic ultrafine particles. Chemosphere 2011, 85: 1555–1562. 10.1016/j.chemosphere.2011.07.059View ArticleGoogle Scholar
- Donner E, Broos K, Heemsbergen D, Warne MSJ, McLaughlin MJ, Hodson ME, Nortcliff S: Biological and chemical assessments of zinc ageing in field soils. Environ Pollut 2010, 158: 339–345. 10.1016/j.envpol.2009.06.034View ArticleGoogle Scholar
- Shoults-Wilson WA, Zhurbich OI, McNear DH, Tsyusko OV, Bertsch PM, Unrine JM: Evidence for avoidance of Ag nanoparticles by earthworms ( Eisenia fetida ). Ecotoxicology 2011, 20: 385–396. 10.1007/s10646-010-0590-0View ArticleGoogle Scholar
- Schlich K, Terytze K, Hund-Rinke K: Effect of TiO 2 nanoparticles in the earthworm reproduction test. Environ Sci Eur 2012, 24: 5. 10.1186/2190-4715-24-5View ArticleGoogle Scholar
- IME RefeSol. [http://www.refesol.de] 
- ISO 18512, 2007. Soil Quality - Guidance on Long and Short Term Storage of Soil Samples. 2007.Google Scholar
- DIN ISO 11466, 1997. Extraction of trace elements soluble in aqua regia. (ISO 11466:1995). 1997.Google Scholar
- DIN EN 13346, 2001. Characterization of suldges - Determination of trace elements and phosphorus - Aqua regia extraction methods. (EN 13346:2000). 2001.Google Scholar
This article is published under license to BioMed Central Ltd. This is an Open Access article distributed under the terms of the Creative Commons Attribution License (http://creativecommons.org/licenses/by/2.0), which permits unrestricted use, distribution, and reproduction in any medium, provided the original work is properly cited.