Shorter lifetime of a soil invertebrate species when exposed to copper oxide nanoparticles in a full lifespan exposure test

Toxicity tests that last the all life duration of the organisms are not common, instead, long-term tests usually include one reproductive cycle. In the present study we optimized and propose a lifespan (all life) term test using Enchytraeus crypticus (Oligochaeta). The effect of copper oxide nanoparticles (CuO-NPs) was assessed in this lifespan test and compared to copper salt (CuCl2), using the same effect concentrations on reproduction (EC50). Monitored endpoints included survival and reproduction over-time (202 days). Results from survival showed that CuO-NPs caused shorter life of the adults compared to CuCl2 (control LT50: 218 days > CuCl2 LT50: 175 days > CuO-NPs LT50: 145 days). The effect was even more amplified in terms of reproduction (control ET50: 158 days > CuCl2 ET50: 138 days > CuO-NPs ET50: 92 days). Results suggest that CuO-NPs may cause a higher Cu effect via a trojan horse mechanism. The use of lifespan tests brings a novel concept in soil ecotoxicity, the longevity. This is a particularly important aspect when the subject is nanomaterials toxicity, where longer term exposure time is expected to reveal unpredicted effects via the current short/long-term tests. The present study confirms this higher effect for CuO-NPs.

and 1420 mg Ag/kg, respectively). Also, Waalewijn-Kool et al. 16 reported that the release of Zn ions to soil, from ZnO-NPs, continued over one year, which caused a decrease in toxicity to Folsomia candida at that time. In fact, the need of more long-term toxicity studies to obtain a better understanding of NMs effects is fully recognized and pointed out as a current gap and future priority in the knowledge on nanotoxicology 2,17,18 .
Copper oxide nanoparticles (CuO-NPs) are used in a wide range of industrial and commercial applications [19][20][21][22][23] . The increased production of CuO-NPs escalates the likelihood of their introduction into the environment. Currently, most of the information regarding the ecotoxicity of CuO-NPs is based on "short-term"/acute effects, mostly in the aquatic compartment (e.g. refs [24][25][26][27][28][29] and fewer in the soil compartment, e.g. on plants [30][31][32] and on soil dwelling invertebrates [33][34][35][36][37][38] . Therefore, NMs potential long-term toxicity, combined with a likely long residing time, should not be ignored and it is important to investigate the toxicity of these materials 39,40 . In the present study we propose a lifespan test i.e., all life duration for the soil living oligochaete E. crypticus, until it dies of age. E. crypticus is a model standard species where many endpoints can be assessed: survival and reproduction 3,41 , bioaccumulation 42 , embryo development 43 , or via a full life cycle with hatching, growth, maturity 44 (see further explanation in the discussion).
The procedures for a lifespan test using E. crypticus were optimized using control conditions (un-spiked soil) by monitoring the survival and reproduction of the organism over the entire time of its lifespan. Further, the developed assay was used to study the longevity effects of CuO-NPs in comparison to CuCl 2 , using similar 50% effect concentrations on reproduction (EC 50 = 1400 and 180 mg Cu/kg for CuO-NPs and CuCl 2 , respectively) 45 .

Results
Lifespan assay: optimization in control conditions. Results on survival at D1 and D20 are shown on  Table 1.
The lifespan at D1 is lower than at D20 (D1 LT 50 : 145 days, D20 LT 50 : 162 days). Results in terms of reproduction can be observed in Fig. 1B: the number of juveniles produced per adult at D1 is higher than at D20, during the first 101 days, but D1 has a reproduction EC 50 earlier than D20 (e.g. D1 ET 50 : 154 days, D20 ET 50 : 242 days, Table 1).
Lifespan assay: exposure to CuO-NPs and CuCl 2 . The effects of CuO-NPs and CuCl 2 on E. crypticus lifespan (survival) can be depicted in Fig. 2A and the ETx calculated are summarized in Table 2.
CuO-NPs exposure caused a more severe lifespan decrease than CuCl 2 : control LT 50 : 218 days > CuCl 2 LT 50 : 175 days > CuO-NPs LT 50 : 145 days. Results in terms of reproduction (Fig. 2B) show that CuO-NPs exposure caused higher effects on reproduction in E. crypticus, with a 50% reduction in reproduction occurring earlier than for CuCl 2 (e.g. control ET 50 : 158 days > CuCl 2 ET 50 : 138 days > CuO-NPs ET 50 : 92 days, Table 2). Comparing the survival and reproduction curves (Fig. 2) it seems that the variation around the model for survival is reflected in the variation around the model for reproduction.
In situ characterisation. The total Cu measured in the soil was ca. 100% of the added total concentration for both CuO-NPs and CuCl 2 . The total Cu in soil solution was less than 1% of the total for CuO-NPs and less than 3% for CuCl 2 . The free active Cu was less than 0.001% for both Cu forms exposure. For controls, the total Cu in soil solution was 0.07% and the active Cu was 0.004%.

Discussion
This is the first study where the entire lifespan of an enchytraeid was monitored in soil. Previous knowledge on enchytraeids' lifespan (in agar media) showed: 120 days for Enchytraeus albidus 46 , 127 days for Enchytraeus   48 . Westheide and Graefe 47 also reported an 85 days lifespan for E. crypticus which is considerably less than the 244 and 370 days we observed for D1 and D20, respectively. Possibly, the differences in terms of test media, soil (in our study) and agar media 47 influence the longevity, as the food source was the same (oats). Hence, this indicates that E. crypticus can live longer in soil compared to agar.
The experimental test design as proposed here can be used as draft for a lifespan test in soil for E. crypticus. Results showed that the selected sampling points to assess the survival and reproductive output over-time were adequate. Although it is a very long duration of the test, the associated material costs are relatively low, except in terms of time consumption and human resource, but the level of information is very high. The majority of the studies that assess endpoints like survival, reproduction, bioaccumulation or growth are based on shorter exposure periods, covering up to 6 weeks of duration 3,42 and cannot predict the effects on longevity.
Analysis of organisms' survival over time showed that at D1 enchytraeids died earlier compared to D20. The reproductive output (number of juveniles per adult) was higher for the D1 than for the D20, which is in agreement with results from a detailed density study using the same species 49 . This has also been observed in other studies: lower reproductive output at higher densities compared to lower densities, for instance in Lumbricus terrestris the cocoon production was 1.5, 0.6, 0.1, 0.06, 0.04 and 0.0 at D1, D2, D3, D4, D6 and D8, respectively 50   . Asterisks indicate significant differences between control and treatments at each sampling day (p < 0.05 Tukey Test or Dunn's method). The lines represent the model fit to data.
Regarding reproduction, the observed decrease in reproductive output over time is possibly age related. Changes in fertility in relation to age (reproductive senescence) have been reported in many organisms 51 . For example, in Caenorhabditis elegans the fast decline in the reproduction begins at young to middle age due to sperm depletion 52 whereas in Drosophila melanogaster is due to apoptosis of ageing egg chambers 53 . In E. crypticus the reproductive output showed a variation along the lifespan of the organisms and decreased with aging. This further reiterates the importance of using organisms with synchronized age in ecotoxicological testing as recommended for this species and implemented in the full life cycle test 44 .
Results showed that for the same reproduction EC 50 CuO-NPs were more toxic than CuCl 2 , i.e. exposure to CuO-NPs caused shorter longevity and lower reproduction. Please note that results reflect a comparison between reproduction EC50s (not the same or a range of soil concentrations) which will provide the most stable measure for the distance between the concentration curves. To test more concentrations would be very interesting to study as well, and would illustrate whether the steepness of the concentration-response curves are the same. However, the importance in the present study was the distance between the curves, hence to optimise time and resources we have selected this reduced design. Regarding the longevity (survival), maybe the mechanism is similar to what is reported in Mytilus galloprovincialis 54,55 , i.e. CuCl 2 was easily eliminated whereas CuO-NPs had slower elimination rate resulting in an increased accumulation with time of exposure. In short, even though Cu concentrations in the digestive gland of mussels were higher for CuCl 2 than for CuO-NPs in the first week of exposure, Cu accumulation decreased for CuCl 2 at the end of experiment (15 days) whereas it increased for CuO-NPs exposure. In the present work, the soil was spiked every 15 days, which means a continuous renewal or new pulse of Cu source. The following may be considered: (a) only dissolution and transformation of the NPs over 15 days is monitored and can have an effect in the test and (b) if NPs within the organism are refilled by this approach and we have NP-specific effects only in the early time of exposure because the NPs degrade quickly, then the refilling could be amplifying the NP effect compared to one long term exposure without renewal. Hence, the observed differences in terms of longevity (59-143 days period) could possibly be related with different accumulation/elimination rates between NPs and salt and less likely due to the decrease of Cu bioavailability by sorption to soil over time.
From day 157 onwards, effect levels became similar between CuO-NPs and CuCl 2 , which could mean that, after prolonged exposure, Cu elimination (from CuCl 2 ) was less efficient (also linked to the age of the organisms, note that from day 143 there is a reduction in reproduction, also in control) and the effects caused by CuCl 2 meet those caused by CuO-NPs. Alternatively or additionally, the reason could also be the general deteriorating health of the adults.
The mechanism of Cu uptake from CuO-NPs is not fully understood. Some authors explain the higher cytotoxicity of CuO-NPs (in comparison to CuCl 2 on a mass basis) via a trojan horse mechanism, i.e. NPs can release a boom of metal ions inside the cells, possibly due to lower pH which causes a higher dissolution 56, 57 . Shi et al. 30 reported higher toxicity of CuO-NPs (in comparison to CuCl 2 ) to Landoltia punctate due to the high uptake of ions released from the NPs, but question the intra-cellular form of Cu and if the CuO-NPs themselves are taken up into the cells. Pradhan et al. 27 suggest the intake of CuO-NPs in Allogamus ligonifer, and also state that the Cu ions released from the CuO-NPs may contribute to the toxicity of CuO-NPs. A study by Navratilova et al. 58 showed that it was possible to detect larger CuO-NPs by Single Particle ICP-MS, but due to the interaction with soil components it was very difficult (or impossible) to separate Cu + bound to small natural particles from CuO-NPs present in the sample. The CuO-NPs used in the present study were below the theoretical detection limit, so it was not possible to detect them. However, in their study Navratilova et al. 58  completely solubilize in the presence of soil components, i.e. organic matter. Hence, in the current work, the exposure was based on measurement of total and active Cu in the soil and soil solution. Nevertheless, it was not possible to directly explain the difference in toxicity based on the measured concentrations in soil solution, i.e. total and active ions. Although, it was observed that the ratio between the total Cu concentration in soil solution of the CuO-NPs and of the CuCl 2 was similar to the ratio between the LT 50 s for reproductive output of the two Cu-forms. For survival the same was true for the measured active ions i.e. a similar ratio. This however may be more a coincidence than a confirmation of a causative phenomenon, but deserve further consideration when broadly available and validated techniques for discrimination between ionic and particle based forms in solid media exist 59

Conclusions
A lifespan test was developed for the first time in soil organisms and includes longevity as an additional endpoint for ecotoxicology. The proposed lifespan term test will be extremely useful to assess the prolonged effects of toxicants, e.g. very relevant for nanomaterials. Results showed precisely that longevity was more affected for CuO-NPs compared to CuCl 2 exposure (when tested at a similar reproduction effect concentration, EC 50 ), which would not be predictable based on the current standard test. We understand that the test length may be an issue but highly recommend the performance of longevity test for selected cases and design, in particular for the testing of nanomaterials.

Materials and Methods
Test organisms. The test organism belongs to the species Enchytraeus crypticus, Westheide and Graefe, 1992.
Cultures were kept in agar plates fed ad libitum with grinded and autoclaved oats and maintained in laboratory under controlled conditions, e.g. photoperiod of 16:8 hours (light: dark) and temperature of 20 ± 1 °C. Juveniles of synchronized age (11 days) were used. For details on culture synchronization see Bicho et al. 44 .
Test soil. The standard natural soil LUFA 2.2 (Speyer, Germany) was used. Main properties of the soil can be summarised as follows: pH (0.1 M CaCl 2 ) of 5.5, 43.3% of maximum water-holding capacity (WHCmax), 1.61% organic carbon and a particle size distribution of 7.9% clay, 16.3% silt and 75.8% sand.
Test procedures. Development of the lifespan assay: control conditions. The development/optimization of the lifespan assay was done in un-spiked soil, moistened to 50% of the WHCmax. Juveniles of synchronized age (11 days) were randomly selected and placed in each well (of the 6-well plates) at two densities: 1 (D1) and 20 (D20) organisms per replicate, ten replicates were used. After 25 days (11 plus 14 days to allow growth and reaching maturity) adults' survival was recorded and the surviving adults (25 days old) were transferred to new test plates, in the same conditions, i.e. D1 or D20, respectively. To ensure that juveniles were not transferred together with the adults, prior the transference to the new test plates, the organisms were cleaned in a petri-dish with distilled water and checked under a stereo microscope (Zeiss Stemi 2000-C). Every 15 days, the survival of the adults was recorded and the surviving adults were transferred to new test plates as described above. After each transfer, the previous test plates were left during 11 more days to ensure that the cocoons laid have time to hatch; after that, the soil in the well plates was transferred to glass vials and fixated with 96% ethanol and Bengal rose (1% in ethanol) and the juveniles were counted using a stereo microscope (Zeiss Stemi 2000-C). Food (grinded and autoclaved oats) was added weekly (2 and 10 mg for D1 and D20 exposed organisms, respectively). Water was added every 3 days. The test was maintained at a photoperiod of 16:8 hours light:dark and at 20 ± 1 °C. The test ran until all the adults were dead (370 days).
Lifespan assay: exposure to CuO-NPs and CuCl 2 . For the test with CuO-NPs and CuCl 2 , organisms (juveniles of synchronized age) were exposed at density D1 following the procedures described above. Density D1 was chosen due to the increased power of traceability of results to one individual (compared to an average, etc.); besides, there is lower variability in terms of reproductive output compared to D20. Twenty (20) replicates per test condition were used, 2 mg of food was added weekly and water adjusted every 3 days. The test was maintained at a photoperiod of 16:8 hours light:dark and at 20 ± 1 °C. The test ran for 202 days (plus 11 more days to allow the cocoons to hatch); the test duration was selected based on the results from the optimization of the lifespan assay in control conditions (≈LT 80 ).
The schedule, test design and sampling days, as optimized, are presented in Fig. 3.
Test chemicals and spiking. Copper-salt (CuCl 2 •2H 2 O) and Copper Oxide Nanoparticles (FP7 SUN pristine materials) were used ( Table 3). The CuCl 2 was obtained from Sigma-Aldrich (CAS number 10125-13-0) with a purity of 99%. The tested concentrations were selected based on the EC 50 for reproduction effect (CuCl 2 = 180 mg Cu/kg and CuO-NPs = 1400 mg Cu/kg soil dry weight) as known from previous Enchytraeid Reproduction Test (ERT) results 45 . CuCl 2 was added to pre moistened soil (20% w/w) as aqueous solution. For CuO-NPs, the NPs were added as dry powder to the soil as recommend by OECD for the testing of insoluble substances 60 . In short, CuO-NPs were thoroughly mixed manually with the dry soil to obtain the corresponding concentration. After that, deionized water was added to reach 50% of the soil WHC. All soils were homogeneously mixed and allowed to equilibrate for 1 day before test start. Soil was spiked and renewed every 15 days during sampling. Controls correspond to un-spiked LUFA 2.2 soil moistened until 50% of WHC. Test vessels consisted of 6-well plates (35 mm ø), each well containing 5 g of moistened soil (50% of WHC). Treatments and replicates were distributed randomly in the test plates.
In situ characterisation. The amount of Cu was measured in the test soil and in soil solution (for method details see Gomes et al. 61 ) in a concurrent experiment over 28 days. In the soil the total Cu was measured (by Graphite Furnace Atomic Absorption Spectroscopy: AAS-GF). In soil solution, both the total Cu and free active form were measured by AAS-GF and by ion-selective electrode, respectively. The CuO present as nanomaterials was not determined in the soil, due to the technical difficulties e.g. that the particle size is below the theoretical detection limit of 15 nm (see Navratilova et al. 58 ).
Data analysis. To assess significant differences between treatments at each sampling day One-Way ANOVA (using Tukey Test or Dunn's method for multiple comparisons) was used (SigmaPlot 11.0).
Lethal Time (LTx) as time to reduce survival in x% and Effect Time (ETx) as time to reduce reproduction in x% calculations were performed for survival and reproduction, respectively, using the logistic equation or threshold sigmoid 2 or 3 parameters regression models (TRAP 1.30 software).   Table 3. Characteristics of the tested CuO-NPs (Source: FP7-SUN project).