TECHNOLOGY REPORT article
Volume 4 - 2016 | https://doi.org/10.3389/fenvs.2016.00068
Application of Biotests for the Determination of Soil Ecotoxicity after Exposure to Biodegradable Plastics
- Department of Sciences and Technological Innovation, University of Piemonte Orientale “A. Avogadro”, Alessandria, Italy
Biodegradable plastics are mostly applied in packaging materials (e.g., shopping bags), waste collection bags, catering products, and agricultural applications. In this last case, degradation takes place directly in soil where biodegradable plastic products are intentionally left after use (e.g., mulch films for weeds control). Due to the growing volumes of biodegradable polymers and plastics, interest in their environmental safety is increasing and more research is carried out. Some attempt has been made to apply biotests, used in other sectors of environmental sciences, in the assessment of biodegradable plastics safety. In this work, the quality of soils after biodegradation of the bioplastics Mater-Bi has been assessed with a large array of biotests based on model organisms representative of the different trophic levels in the food chains of the edaphic and aquatic ecosystems. Mater-Bi was degraded under controlled conditions for 6 months at a 1% concentration. The selected organisms included bacteria and protozoa (Vibrio fischeri and Dictyostelium discoideum, respectively), the green alga Pseudokirchneriella subcapitata, plants (the monocotyledon Sorghum saccharatum and the dicotyledon Lepidium sativum), and invertebrates animals (Daphnia magna, a freshwater crustacean, and the Oligochaeta earthworm Eisenia andrei), using both acute and chronic endpoints. The results of the applied ecotoxicological tests showed that the Mater-Bi materials tested at very high doses did not affect the soil quality. Soil exposed to Mater-Bi has no noxious effects on edaphic organisms; in particular, mono and dicotyledon plants results, indicate that Mater-Bi plastic products are innocuous for agricultural uses. The use of more sensitive chronic endpoints allows to exclude possible effects at population level. This is the first time that such a comprehensive approach is applied to the assessment of possible ecotoxicity effects induced by biodegradable plastics in soil and represents a possible starting point for improved standardized testing schemes.
Biodegradable plastics are mostly applied in packaging materials (e.g., shopping bags), waste collection bags, catering products, and agricultural applications (Shen et al., 2009). At the end of their commercial life these products are expected to degrade into harmless end products. Degradation takes place in composting plants or in anaerobic digestion plants (van der Zee, 2014) together with the bio-waste (food and yard waste) to give rise to compost. Compost is applied to soil as a fertilizer in order to increase organic matter. Degradation can also take place directly in soil where biodegradable plastic products are intentionally left after use (e.g., mulch films for weeds control). Since the agricultural soil is the medium for the production of food for humans and feed for farm animals, the absence of negative effects linked to applications of biodegradable plastics is of great concern to the interested parties. That is why all the testing protocols developed to characterize the biodegradable plastics and packaging include the assessment of ecotoxicity potentially originated from the biodegradation. Standards have been developed to specify the requirements for biodegradable plastics and packaging in composting (i.e., organic recycling), in home composting, and in soil. The most relevant standards on plastics that are biodegradable in different environments are shown in Table 1. All standards require (i) full biodegradation levels as a first tier of testing that prevents accumulation in soil and (ii) ecotoxicity testing as a second tier of testing in order to show environmental safety. The testing approach is similar in all cases: the plastic material is exposed to the matrix of interest (e.g., compost, soil) in a very high dose and let biodegrade. After a given time, a sample of the matrix is tested with biotests for ecotoxicity together with a control sample not exposed to the plastic item and a control sample exposed to a GRAS (Generally Recognized As Safe) substance, such as cellulose. No significant difference must be found between the test samples and control samples.
The standards on compostability (e.g., EN 13432) requires ecotoxicity assessment on compost samples where plastic material added at a 10% concentration has been composted for 3 months. The biological test is based on a germination and growth assay with two plant species and derives from the OECD 208 Guidelines for testing of chemicals (OECD, 2006).
Ecotoxicity requirements are also enforced by the standards on biodegradability in soil (the Italian and French national standards and the “OK Biodegradable soil” certification programme). Ecotoxicity tests must be carried out on soil samples where plastic material added at a 1% concentration has been degraded for 3 months. The prescribed concentration of plastics is much higher of the amount that is expected to end up normally in the environment. A 1% loading is much higher than the expected application loading of biodegradable plastics in soil. For example: a typical biodegradable plastic film for mulching is 1.5 × 10−5 m thick and has a density of 1250 kg m−3. This means 1.88 × 10−2 kg m−2 for one application. The soil depth where the plastic is typically used or remains after use is presumed to be 0.20 m, in agreement with the normal depth of soil tillage. Therefore, 1 m2 of plastic film covering 1 m2 of soil surface will typically be mixed with a volume of soil equal to 0.2 m3. This amount of soil weighs ~300 kg, considering a soil bulk density of 1500 kg m−3. Therefore, the typical loading of the plastic film in normal use will be ~0.0063% (1.88 × 10−2 kg/300 kg × 100).
The ecotoxicity biotests required by the different standards are shown in Table 2.
Table 2. Bio-tests for ecotoxicity considered by the different standards on biodegradable plastics and packaging.
The current approaches to the standardization of composting and soil biodegradation are considered satisfactory and suitable for the assessment of the environmental safety of biodegradable plastics (Fritz, 2014). The reason lies in the very high mineralization threshold levels (90%) required by these standards, which can be considered as an indication of total biodegradation and of no remaining residues (De Wilde, 2014). Additionally, the ecotoxicity tests applied to the compost or to the soil after the biodegradation of the plastic, make sure that products of biodegradation do not affect environment.
However, due to the growing volumes of biodegradable polymers and plastics, interest in their environmental safety is increasing and more research is carried out (Kapanen, 2012). A strong concern of the public opinion is about the environmental impact of persistent substances possibly released during polymer biodegradation and composting which could subsequently be spread into the environment during fertilization with compost, or directly diffused during their biodegradation in soil. It is therefore of interest for all the stakeholders to extend the range of the applied ecotoxicity tests in order to dispel any doubt and assure a smooth development of this promising industrial sector. This is the reason why some attempt has been made to apply biotests, used in other sectors of environmental sciences, in the assessment of biodegradable plastics safety.
The so-called “Flash test,” based on the kinetic measurement of bioluminescence by Vibrio fischeri, has been applied on compost (Tuominen et al., 2002) and on vermiculite (Degli-Innocenti et al., 2001) exposed to plastic materials. The conclusion of the studies was that the Flash test could be reliably used to verify the ecotoxicity of extracts from the biodegradation matrices (either vermiculite or compost).
A nitrification inhibition test was applied to soil extracts (Bettas Ardisson et al., 2014) after a biodegradation test based on the standard ISO 14238 (2012) for the measurement of nitrification activity. The conclusion was that the test approach was suitable for reaching conclusions on the effects of biodegradable plastics on soil.
No other biotests have been applied to our knowledge in this sector. The intention of this work was to verify the applicability of a larger number of bioassays for the determination of the potential ecotoxicity of soil after the biodegradation of plastics. In particular, the organisms included bacteria and protozoa (Vibrio fischeri and Dictyostelium discoideum, respectively), the green alga Pseudokirchneriella subcapitata, plants (the monocotyledon Sorghum saccharatum and the dicotyledon Lepidium sativum), and invertebrates animals (Daphnia magna, a freshwater crustacean, and the Oligochaeta earthworm Eisenia andrei). The array of ecotoxicological tests, including those routinely adopted by the Italian Institute for Protection and Environmental Research (ISPRA) and applied by territorial Environmental Agencies, was employed on soils where samples of biodegradable plastics had been biodegraded for 6 months. These tests are based on the OECD Guidelines or on other recognized protocols.
Materials and Methods
The test materials were three Mater-Bi plastic films provided by Novamont S.p.A.: Mater-Bi DF04A (internal denomination RIC 1362); Mater-Bi EF04P (internal denomination RIC 1619), Mater-Bi AF05S0 (internal denomination RIC 1620). These materials are biodegradable and compostable plastics, tested according the European standard EN13432 (Packaging. Requirements for packaging recoverable through composting and biodegradation. Test scheme and evaluation criteria for the final acceptance of packaging). They are based on the following constituents: corn starch; bio-based aliphatic polyester; bio-based aliphatic- aromatic copolyester; natural plasticisers. The elemental composition and the concentration of regulated metals is shown in Tables 3, 4 (source: Novamont). The films were powdered by means of cryogenic grinding with liquid nitrogen using an IKA M20 grinder.
The reference material was pure micro-crystalline cellulose (Merck) in powder.
The standard soil was prepared and supplemented as described in Table 5, following the ISO 17556 (2012). The water content was adjusted by adding deionized water in order to reach a total holding capacity between 40 and 60%. The final water content of wet soil used in the experiment was 16.9%.
The total solids were determined after drying in an oven at 105°C until constant weight was achieved. The volatile solids were determined after calcination at 550°C until constant weight was achieved. The pH was determined by diluting the soil in distilled water. A 10 g sample of soil was mixed with 25 ml of deionized water, stirred for 15 min and left unstirred for 30 min before measuring the pH with a Hanna Instruments pH meter model pH 211 (Violante and Adamo, 2000).
According to ISO 17556 (2012), the pH of the inoculum should be between 6 and 8 and the C/N ratio should be at least 40:1. Both conditions were met.
Fifteen 3-L glass flasks were each filled with a 800.0 g sample of soil. Three flasks were supplemented with 10.0 g of RIC 1362; three flasks were supplemented with 10.0 g of RIC 1619; three flasks were supplemented with 10.0 g of RIC 1620; three flasks were supplemented with 10.0 g of cellulose; three flasks were not supplemented (control soil). Each flask was carefully mixed with a spatula in order to mingle soil and test material and then incubated at 28°C ± 2°C. Pressurized air was sent over a gas flow controller and an air flow rate of about 6 L/h was supplied at the bottom of each reactor (dynamic conditions). The incubation lasted 6 months. The soil of each reactor was mixed at regular intervals and the water content was maintained constant by adding deionized water during the incubation period. The soil replicates were analyzed separately in ecotoxicity tests.
Soils (elutriates and whole soil) were analyzed applying a set of acute and chronic bioassays with bacteria, protozoa, algae, plants, crustaceans, and earthworms. In addition to the control soil (i.e., soil without Mater-Bi/cellulose degradation products), it was also used a (negative) lab control that allowed to demonstrate the normal state of the animals, and to verify the good quality of the control soil (Wallace Hayes and Kruger, 2014). The characteristics of the lab controls are specified in the standardized methodologies and reported here in the description of the different bioassays. Elutriates were obtained by diluting each soil sample with 3 parts of deionized water (dilution 1: 4 w/v). A volume of 300 ml of water was added to 100 g of soil (dry weight) in a 500 ml glass jars. The samples were subjected to continuous stirring (about 170 rpm) for 60 min and allowed to settle for 24 h at 4°C. Subsequently, the liquid phase (water extract) was centrifuged at 4000 rpm at 4°C for 15 min and filtered with a 0.45 μm filter in order to obtain a clear solution. The water extracts (elutriates) thus obtained were used for following testing.
V. fischeri Bioluminescence Inhibition (Microtox®) Test
The bioassay with the luminescent bacterium V. fischeri was performed following the standard ISO 11348-3 (2007) [Water quality—determination of the inhibitory effect of water samples on the light emission of V. fischeri (luminescent bacteria test)—part 3: method using freeze-dried bacteria]. The reduction of light emitted by bacteria after exposure for 15 min to elutriate samples was measured with a Microtox® luminometer detecting the light intensity at 490 nm, the wavelength emitted by the bacteria. The test requires the use of a lab control (2% NaCl in Milli-Q water), as well a positive control consisting of a 3,5-dichlorophenol (C6H4Cl2O) solution (6 mg/L). The test is considered valid if the bioluminescence inhibition induced in organisms exposed to the positive control is ≥50%.
The amoebic cells of D. discoideum (AX-2 strain) were cultured as described by Watts and Ashworth (1970), until their concentration reached 2–4 × 106 cells/mL. After centrifugation, the cells (0.75 × 106 cells/mL) were incubated for 3 and 24 h in the elutriate samples (25% AX-2 medium with 50 μM CaCl2 and 10 μg/mL tetracycline) as well in the lab control (25% AX-2 medium and 75% Page's Amoeba Saline with 50 μM CaCl2 and 10 μg/mL tetracycline) for the evaluation of vitality and reproduction rate, respectively.
Cell viability was evaluated essentially as described by Dondero et al. (2006), incubating the cells with SYBR Green™ (Invitrogen Molecular Probes, Eugene, OR, USA), that in alive amoebae is a cell membrane impermeable DNA-binding dye; cells were observed at 200 × magnification (Zeiss Axiovert 100M) using a FITC emission filter and transmission light simultaneously, a combination allowing a clear discrimination of dead cells (cells with a brightly fluorescent nucleus) from alive cells (with still intact biological membranes). For the reproduction rate, cells were counted with the use of a hemocytometer chamber (Bürker) (Dondero et al., 2006).
The determination of the inhibition of germination was conducted following the method UNICHIM N. 1651 (2003), using seeds of sorghum (S. saccharatum), a monocotyledon plant species, and of cress (L. sativum), a dicotyledonous species.
Before the test, the seeds were soaked with distilled water and left in agitation for 40 min. An amount of 10 g (dry weight) of soil, for each sample, was placed in a Petri dish (90 cm diameter) and a about 6.5 ml of distilled water. A filter paper Whatman #1 was then positioned on the wet soil and on this 10 seeds per plate. The plates were incubated for 72 h in the dark at a temperature of 25 ± 2°C. Quartz sand was used as lab control. Two replicates were set up for each sample of soil (replication) and for each plant species for a total of six replicates for each tested soil. After incubation the germinated seeds were counted (with root length ≥1 mm) and the results expressed as % of sprouted seeds. The test is considered valid if, at the end of the incubation period, the seed germination in the lab control is >90%.
P. subcapitata Growth Inhibition Test
The green algal bioassay was performed following the standard ISO 8692, 2004 (Water quality—freshwater algal growth inhibition test with unicellular green algae). Algal cultures in exponential growth phase were used (1 × 106 cells/mL). Growth inhibition was measured after exposure to elutriate samples for 72 h using a cell counting chamber (Bürker). The test requires the use of a standard solution (ISO 8692, 2004) as a lab control; the cell density after 72 h of incubation in the lab control has to be at least 67 times higher than the initial concentration (1 × 104 cells/mL) so that the test to be valid.
D. magna Immobilization Test and Reproduction
The acute crustacean bioassay was performed following the standard ISO 6341 (2012) [Water quality—determination of the inhibition of the mobility of D. magna Straus (Cladocera, Crustacea)—acute toxicity test]. In the experiments, neonates <24 h old were exposed to elutriate samples for 24 h at 20 ± 2°C, with a 16/8 h light-dark cycle. As laboratory control, we used a standard solution (ISO 6341, 2012). At the end of the period of exposure, the test containers were subjected to gentle agitation and the organisms immobilized, i.e., those animals not able to swim within 15 s, were counted. The test is valid if, in the lab control, the immobilized organisms are <10%.
The chronic test was carried out in ventilated crystallizers testing neonates <24 h old per tested soil, following the indications of OECD (2012). Each daphnid, individually held, was fed with 1 μl of algal cells of P. subcapitata (1 × 108 cells / ml) per day. Each sample was topped up every 7 days with water extract/control water. The incubation, for the chronic assay, was conducted for 21 days under the conditions described above, at the end of which the rate of parental vitality and the total number of living offspring (counted and removed daily from the crystallizers) generated from each parent. The chronic test is considered valid if, after 21 days of exposure, in the lab control parental mortality does not exceed 20%.
E. andrei earthworms (Bouché, 1972) were cultured as described in the OECD guidelines (OECD, 2004). Organisms were selected from a synchronized culture with a homogeneous age structure. Adult worms with clitellum of similar size and weight (400–500 mg) were utilized in the experiments.
Exposure to Soil Samples
For each soil replicate, ten worms were kept in 500 g of soil placed in glass test containers (OECD, 2004). At least three replicates per soil sample were used. The test containers were maintained in a climate-controlled chamber at 20 ± 1°C and maintained under controlled light-dark cycles (16 h light, 8 h dark) with illumination of 800 lx for a period of 28 d.
At the end of the 4 weeks of incubation the living adult worms and cocoons were removed from the test vessels and counted. The cocoons were repositioned in soil samples and incubated for further 28 days under the same conditions. At the end of the second incubation period, the number of juveniles hatched from the cocoons were recorded.
The soils after biodegradation of three Mater-Bi plastic films (i.e., RIC 1362, RIC 1619, and RIC 1620—see Section Materials and Methods), named for simplicity “Mater-Bi soil,” of cellulose (“cellulose soil”) and the control soil were all tested in parallel.
The results concerning the possible toxicity of the Mater-Bi soils and cellulose soils on Bacteria and Protists are reported in Figures 1, 2. All the elutriates obtained from the Mater-Bi soils and cellulose soils stimulated the light emission of the bacterium V. fischeri when compared with the lab control, although the enhancement never reach the value +20% indicative of a biostimulation effect (Figure 1). However, no changes were observed among the values from the control soil and Mater-Bi soils or cellulose soil.
Figure 1. Light emission of V. fischeri after exposure to the elutriate samples. Data are expressed as % variation with respect to lab control and represent the mean ± SD of at least five replicates. *Indicates statistically significant differences with respect to lab control values (p < 0.05 Mann–Whitney U-test). RIC 1362, RIC 1619, RIC 1620, Mater-Bi soils; Cellulose, soil containing cellulose reference material.
Figure 2. Survival (A) and reproduction rate (B) of D. discoideum amoebae after exposure to the elutriate samples. Data, expressed as % variation (A) and % variation with respect to lab control (B), represent the mean ± SD of at least five replicates. *Indicates statistically significant differences with respect to lab control values (p < 0.05 Mann–Whitney U-test). RIC 1362, RIC 1619, RIC 1620, Mater-Bi soils; Cellulose, soil containing cellulose reference material.
Figure 2 shows the effects of the Mater-Bi soils and cellulose soil on the survival and reproduction rate of the social amoeba D. discoideum. The elutriates did not cause negative effects on the survival of the organisms (Figure 2A) but induced a slight decrease of the reproduction rate (Figure 2B). Such decrease was significant, with respect to lab control, for the amebae exposed to the elutriates of the soil RIC 1620 (Mater-Bi containing soil) and of the cellulose soil; however, the effects never reach the decrease of 20% with respect to the lab controls, a value usually considered as an indication of weak toxicity.
The results presented in Figures 3–5 concern the evaluation of the possible effects of Mater-Bi and cellulose soils on autotrophic organisms.
Figure 3. Germination of S. saccharatum after exposure to the soil samples. Data are expressed as % variation and represent the mean ± SD of at least five replicates. *Indicates statistically significant differences with respect to lab control values (p < 0.05 Mann–Whitney U-test). RIC 1362, RIC 1619, RIC 1620, Mater-Bi soils; Cellulose, soil containing cellulose reference material.
The data related to the effects on a monocotyledon S. saccharatum and the dicotyledon L. sativum demonstrate that the seeds of both plants correctly germinate in the Mater-Bi soils and cellulose soils without differences in the germination rate with respect to the control soil or lab controls (Figures 3, 4).
Figure 4. Germination of L. sativum after exposure to the soil samples. Data are expressed as % variation and represent the mean ± SD of at least five replicates. *Indicates statistically significant differences with respect to lab control values (p < 0.05 Mann–Whitney U-test). RIC 1362, RIC 1619, RIC 1620, Mater-Bi soils; Cellulose, soil containing cellulose reference material.
In the same way, when the alga P. subcapitata was growth for 72 h in the elutriates obtained from the different soils no negative effects were observed on its replication rate (Figure 5).
Figure 5. Growth of the alga P. subcapitata after exposure to the elutriate samples. Data are expressed as % variation with respect to lab control and represent the mean ± SD of at least five replicates. *Indicates statistically significant differences with respect to lab control values (p < 0.05 Mann–Whitney U-test). RIC 1362, RIC 1619, RIC 1620, Mater-Bi soils; Cellulose, soil containing cellulose reference material.
Figure 6 shows the results of the acute and chronic toxicity tests using D. magna as model organism. The data reported in Figure 6A clearly demonstrate that there were no effects on the motility rate of the organisms after 24 h of exposure to the elutriate containing the Mater-Bi and cellulose soils. These results were confirmed by the data on the effects of the elutriate on the reproduction rate of D. magna (Figure 6B): no effects were found in organisms exposed to the elutriates from Mater-Bi soils; however, the elutriates containing cellulose soils determine an increase in the reproduction rate of this cladoceran, although in very variable extent.
Figure 6. Motility (A) and reproduction (B) of D. magna after exposure to the elutriate samples. Data, expressed as % variation (A) and % variation with respect to lab control (B), represent the mean ± SD of at least five replicates. *Indicates statistically significant differences with respect to lab control values (p < 0.05 Mann–Whitney U-test). RIC 1362, RIC 1619, RIC 1620, Mater-Bi soils; Cellulose, soil containing cellulose reference material.
Finally, in Figures 7, 8 are reported the results concerning the exposure of the earthworm E. andrei to the Mater-Bi soils and cellulose soils. The results obtained in earthworms exposed to the control soil were comparable to an standardized artificial soil (OECD, 2004) during the period of exposure (data not shown).
Figure 7. Effects on vitality of the oligochaete E. andrei exposed to the soil samples. Data are expressed as % variation and represent the mean ± SD of at least three replicates. *Indicates statistically significant differences with respect to control values (p < 0.05 Mann–Whitney U-test). RIC 1362, RIC 1619, RIC 1620, Mater-Bi soils; Cellulose, soil containing cellulose reference material.
Figure 8. Effects on reproduction of the oligochaete E. andrei exposed to the soil samples: (A) cocoons; (B) offspring; (C) number of juveniles hatched from each cocoon. Data are expressed as % variation with respect to soil control and represent the mean ± SD of at least three replicates. *Indicates statistically significant differences with respect to control values (p < 0.05 Mann–Whitney U-test). RIC 1362, RIC 1619, RIC 1620, Mater-Bi soils; Cellulose, soil containing cellulose reference material.
The data demonstrate that there are no toxic effects of the studied soils on the survival rate of worms (Figure 7). Data concerning the number of the cocoons produced (Figure 8A) and the value of the number of juveniles earthworms (Figure 8B) demonstrate that the reproduction rate (Figure 8C) is similar to the value observed in the animals maintained in the control soil.
Plastic contamination of terrestrial and aquatic ecosystems is nowadays considered one of the major environmental issues. In fact, the plastic global production was about 299 million tons in 2013 (PlasticsEurope, 2015) and while efforts to proper recovery and recycling are increasing still a fraction of plastic waste is not recovered and represents a contamination to some environments (UNEP, 2014). Due to the important role of plastic products in our society, in the last two decades different biodegradable plastics were produced with the aim to substitute, at least in part, the plastic products; this, together with a substantial effort toward recovery and recycling, should allow to reduce the negative environmental effects due to plastic waste accumulation in the different ecosystems (World Economic Forum, 2016).
However, not all the biodegradable plastics are “environmental friendly” and this depends on their chemical composition: in some case it was found that degradable plastics were toxic for edaphic and/or aquatic organisms (Fritz, 2014), thus their use no giving all the expected environmental advantages. In particular, few studies have been devoted to investigate the possible biological effects of plastic degradation products in organisms characteristic of the different trophic levels in the food chains of the edaphic and aquatic ecosystems.
In this research, the environmental compatibility of the biodegradable plastic Mater-Bi was studied evaluating the potential toxicity of its degradation products on a wide range of model organisms using well known standardized guidelines or, in some cases, scientific literature protocols.
Mater-Bi is a plastic material based on corn starch and biodegradable polyesters widely used for package (Bastioli, 2005). Same Mater-Bi grades are certified as “OK Biodegradable Soil” by Vinçotte (Belgium). The certification programme established by Vinçotte requires a biodegradation level of more than 90% after 2 years in soils (under controlled physical-chemical and microbiological conditions) and no ecotoxicity in soil exposed to the test material.
Ecotoxicity is assessed in soil samples after degradation of the plastic material introduced at high concentration in comparison with control soils. The ecotoxicity test is a seedling and plant growth test based on the OECD 208 (OECD, 2006) standard test method.
These characteristics have encouraged a wider employ of this biodegradable plastic also for other uses such as in the agricultural field as mulch films (Kyrikou and Briassoulis, 2007).
For this reasons it was considered of great importance to clarify the possible toxicity of this new biodegradable plastic with a larger array of biotests.
With the aim to clarify this important aspect, Mater-Bi was degraded in soils under controlled conditions for 6 months at a 1% concentration, following the Vinçotte certification programme testing scheme.
The selected model organisms for the evaluation of soil quality were bacteria and protozoa (V. fischeri and D. discoideum, respectively), the green alga P. subcapitata, plants such as the monocotyledon S. saccharatum and the dicotyledon L. sativum, and invertebrates animals such as the D. magna, a freshwater crustacean, and the Oligochaeta earthworm E. andrei.
The ecotoxicological tests on the alga and plants demonstrated that the Mater-Bi biodegradation products are not harmful for these autotrophic organisms. It should be noted that a large part of the bioassays used are chronic tests i.e., the more sensitive at organism level.
Similarly, no effects were found when the soil toxicity was evaluated using as model organisms two invertebrates such as D. magna and the earthworm E. andrei: also in this case the endpoints evaluated, both mortality (acute toxicity) and reproduction (chronic toxicity) ensured the higher sensitivity of the employed bioassays.
The data concerning the possible effects of the plastic degradation products on the bacterium V. fischeri using the Microtox test indicated that there are no negative effects on these organisms. These results are in line with previously reported data indicating that the Mater-Bi degradation products in soils do not affect the nitrification process depending on the microbiological activity (Bettas Ardisson et al., 2014).
Finally, an extremely sensitive bioassay using as model organism the social amoeba D. discoideum was used. This amoeba lives in the soil pore water and it is cultivated in lab in an aqueous medium. This ecotoxicological test is therefore adequate to study the biological effects of contaminants present in the soil using the elutriate extracts. This test was found to be more sensitive than the classical bioassays used by the environmental agencies as demonstrated in previous studies devoted to investigate the toxicity of waters and sediments of a freshwater ecosystem (Sforzini et al., 2008). Our results demonstrated no effects on the survival rate of the protozoa but the chronic test on the reproduction, that in 24 h analyses the second/third amoebae generation, shown a slight decrease up to 10% with respect to controls, a value that, being lower than 20%, is not usually considered an indication of toxicity.
The variability of the data observed in some biotests (in particular in the reproduction tests of D. magna and E. andrei) should suggest to use more replicates in future application of these bioassays to biodegradable plastics testing.
Altogether, the data obtained in this study demonstrate that the soils exposed to high amount of Mater-Bi have no noxious effects on edaphic organisms; in particular, mono and dicotyledon plants results, indicate that Mater-Bi plastic products are innocuous for agricultural uses. It should be noted that the bioassay using as model organism the earthworm E. andrei is a 28 d test for the evaluation of the survival rate but it lasts 56 d when the endpoint is the reproduction. This latter chronic test evaluates the number of cocoons produced but also the number of newborn worms that develop in the soils; this ecotoxicological test has proved to be sensitive to the effects of low concentrations of different toxic chemicals (Van Gestel et al., 1992; Spurgeon et al., 1994). The use of this test confirmed that Mater-Bi degradation poses no risk for edaphic biodiversity.
In this study, we have used four bioassays for aquatic model organisms i.e., bacteria, algae, protozoa, and crustacean. The elutriates obtained from the Mater-Bi soils were no toxic for the organisms used for freshwater ecotoxicological analysis: these results are of great relevance from an ecotoxicological point of view. In fact, these data indicate that there is no risk that toxic chemicals possibly released during plastic degradation may contaminate surficial or underground waters with the consequence to enlarge the environmental problems.
The importance to use an adequate control for the different bioassays should be also emphasized. It appears relevant to associate to the usual “lab control” and to the control soil without plastic item an additional control soil in which an amount of a natural, no toxic product with a composition similar to the bioplastics is added to the sample. In this case cellulose, a sugar polymer, sharing similar molecular characteristics with Mater-Bi, a bioplastic with a relatively high biodegradability, and sugar content due to the presence of starch. This cellulose sample could show some differences from the control due to the high amount of nutrient compounds (in this case sugar) added to the matrix. It is known that eutrophic conditions could cause negative effects directly to the different model organisms used in the tests. Moreover, the excess of sugar and other nutrients in the soils may change, during the experiment, the structure of the community, that may alter the survival/reproductive capacity of a particular organism. Our study demonstrates that when limited changes in the performance of the organisms exposed to Mater-Bi soils were found, these effects were similarly observed in the organisms exposed to the soil added with cellulose.
When considered altogether these data suggest that the ecotoxicological approach used in this study could represent a standard for future investigation on the environmental impact of plastic degradation products by means of (i) the use of a standardized, detailed protocol for bioplastic degradation, (ii) the evaluation of a large battery of ecotoxicological tests using acute and chronic endpoints, (iii) the use of microorganisms, plants, and animals, (iv) the use of model organisms suitable to test the toxicity of soils and elutriates following international accepted protocols. These rules adopted in this study may represent the basis for the lab analysis of the environmental compatibility of new bioplastics and other biotechnological materials.
The results reported in this study demonstrate that Mater-Bi is a bioplastic that seems to meet an adequate standard of environmental safety. Although a large battery of ecotoxicological tests, using both acute and chronic end points, was used no noxious effect was found. The use of model organisms typical of soil and freshwater allows us to exclude possible negative effects on the biodiversity of the edaphic ecosystem and of the related freshwater (both groundwater and surficial) compartments.
SS was the responsible of the research activity and expert of soil ecotoxicological tests; LO was the responsible of the freshwater ecotoxicological tests; SC supported the different aspects of the research activity i.e., from soil and elutriate preparation to the test performance; AV was the research coordinator.
Conflict of Interest Statement
The authors declare that the research was conducted in the absence of any commercial or financial relationships that could be construed as a potential conflict of interest.
This study was supported financially by a Novamont research grant (10/09/2014).
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Keywords: biodegradable plastics, ecotoxicological tests, edaphic organisms, Mater-Bi, soil quality
Citation: Sforzini S, Oliveri L, Chinaglia S and Viarengo A (2016) Application of Biotests for the Determination of Soil Ecotoxicity after Exposure to Biodegradable Plastics. Front. Environ. Sci. 4:68. doi: 10.3389/fenvs.2016.00068
Received: 28 July 2016; Accepted: 07 October 2016;
Published: 28 October 2016.
Edited by:Weiwen Zhang, Tianjin University, China
Reviewed by:Uwe Strotmann, Westfälische Hochschule, Germany
Luciano Takeshi Kishi, Universidade Estadual Paulista UNESP/FCAV, Brazil
Copyright © 2016 Sforzini, Oliveri, Chinaglia and Viarengo. This is an open-access article distributed under the terms of the Creative Commons Attribution License (CC BY). The use, distribution or reproduction in other forums is permitted, provided the original author(s) or licensor are credited and that the original publication in this journal is cited, in accordance with accepted academic practice. No use, distribution or reproduction is permitted which does not comply with these terms.
*Correspondence: Aldo Viarengo, firstname.lastname@example.org