Three commercial bioplastics and a non-biodegradable petrochemical plastic were used for this study. These plastics are commonly used to bind vegetables or fruits in agricultural fields. The commercial PBS (Showa Highpolymer, Tokyo, Japan), PBS-starch (Matsubara Shoji, Tokyo, Japan), and PLA (Mitsui Chemicals, Tokyo, Japan) were the bioplastics, while PA66 was the non-biodegradable petrochemical plastic used in this study. The thickness of each plastic was 2 mm. For a separate experiment, all of the three kinds of bioplastics (PBS, PBS- starch, and PLA) were powdered by using a Power Grinder (T-351, Rong Tsong Precision Technology, Taichung, Taiwan). Physical properties of the bioplastics are shown in Table 1. PBS-starch film is a blend of PBS (50%) and starch (50%).

Each of the non-sterilized bioplastics (PBS, PBS-starch, and PLA) and non-biodegradable petrochemical plastic (PA66) films (3 cm × 3 cm) were buried (5% (w/w)) in an agricultural soil (100 g-soil/pot, bacterial biomass 7.5 × 10⁸ cells/g-soil). The pots were kept under controlled condition (25˚C and 60% relative humidity) for 28 days. Moisture content of the soils was maintained around 35% to 40% throughout the experiment. The plastics films

^aProperties of PBS-starch was not determined.

were recovered from the soil every 7 days, and the residual weights were measured after washing using an ultrasonic washer. The degradation ratio was calculated by the weight loss of the plastics. In addition, the surface of each plastic was observed by a digital stereo microscope (VHX-1000, Keyence, Osaka, Japan) and scanning electron microscope (SEM, VE-8800, Keyence, Osaka, Japan) after sputtering of Pt-Pd.

PBS, PBS-starch, and PLA were powdered by using a Power Grinder until ca. 250 µm of diameter (T-351, Rong Tsong Precision Technology, Taichung, Taiwan). The surface area of the powdered-bioplastic was about 12 times larger than that of commercial bioplastic (the surface area of the plastics was estimated using a digital stereo microscope (VHX-1000, Keyence, Osaka, Japan). The powdered-bioplastics were buried (0.25% (w/w)) in the same agricultural soil (50 g soil/pot) used for burying the plastic films. The pots were kept under controlled condition (25˚C and 60% relative humidity) for 28 days. Moisture content of the soils was maintained around 35% to 40% throughout the experiment. The soil samples were recovered from the pots every 7 days, and the degradation of powdered-bioplastics was analyzed based on the decrease of the total carbon (TC) in the soil. TC in the soil was analyzed by using TOC-V_CPH equipped with a solid sample combustion unit of SSM-5000A (Shimadzu, Kyoto, Japan).

To investigate the effect of the bacterial biomass on the bioplastic degradation in the soil, PBS-starch film (3 cm × 3 cm) was buried in soils varying in bacterial biomass (7.5 × 10⁶, 7.5 × 10⁷, and 7.5 × 10⁸ cells/g-soil). The initial bacterial biomass in the original soil was 7.5 × 10⁸ cells/g. Other two levels of bacterial biomass was adjusted by mixing sterilized soil in the original soil. The sterilized soil was prepared by autoclaving (121˚C, 2 atm for 60 min).

In another experiment, three different soils were collected from a riverside, a mountain, and an agricultural farm around the city of Kusatsu (Shiga prefecture, Japan). Each soil was filled into pots (approximately three kg-soil/pot), and three sheets of PBS-starch film (3 cm × 3 cm) were buried in each pot.

In both experiments, the weight loss of the PBS-starch film was measured after 7 days of incubation at room temperature (25˚C), and the degradation ratio was calculated from the weight loss.

Three bioplastics (PBS, PBS-starch, and PLA) and a non-biodegradable petrochemical plastic (PA66) were buried in an agricultural field (field size was 1 m × 1 m). The plastics were recovered from the soil after 2 years, and the surface of each plastic was observed as described above by using a digital stereo microscope (VHX- 1000, Keyence, Osaka, Japan) and SEM (VE-8800, Keyence, Osaka, Japan).

For quantification of bacterial and fungal biomass, the soil adjacent to the plastics was sampled. The bacterial biomass in the soil was quantified by the environmental DNA (eDNA) extracted by slow stirring analysis method [16] . The fungal biomass in the soil was quantified by the plate-counting method [23] . For plate-counting, a soil suspension was spread onto PDA-AB-RB agar medium (200 g potato, 15 g glucose, 30 mg rose bengal, 50 mg chloramphenicol, 1 mg carbenicillin, 100 mg streptomycin, 10 mg tetracycline and 20g agar, per liter), and the agar plate was incubated at 30˚C. The fungal colony forming units (CFU/g-soil) were counted after 4 days of incubation.

The variable V3 region of bacterial 16S rRNA gene (corresponding to positions 341 to 926 in the Escherichia coli) was analyzed by denaturing gradient gel electrophoresis (DGGE). The eDNA was extracted from the soil samples by the slow-stirring method [16] . The extracted eDNA was purified by using GEL-M (Viogene, Taipei, Taiwan) and amplified by PCR (PC708, Astec, Fukuoka, Japan) with primers DGGE-F (5’-CGCCC GCCGC GCCCC GCGCC CGTCC CGCCG CCCCC GCCCG CCTAC GGGAG GCAGC AG-3’) and DGGE-R (5’- CCGTC AATTC CTTTG AGTTT-3’) [24] [25] . The PCR reaction included an initial denaturation step at 94˚C for 5 min, 30 cycles of a denaturation step at 94˚C for 30 sec, a primer annealing step at 60˚C for 30 sec, and an extension step at 72˚C for 1 min, followed by a final elongation step of 72˚C for 5 min. The denaturant concentration in 6% (w/v) polyacrylamide gel was from 20% to 60%, and electrophoresis was performed with the D-Code system (Bio-Rad Laboratories, CA, USA) for 10 hours at 60˚C, 80 V. After electrophoresis, the gel was stained by SYBR Gold (Invitrogen, CA, USA) and analyzed by Kodak 1D Image Analysis Software (Kodak, NY, USA). Cluster analysis (single linkage) was carried out by using the software FP Quest (Bio-Rad Laboratories, CA, USA).

To investigate the effect of bioplastics degradation on microbial activities, the nitrogen circulation activity was determined as described previously [20] [22] . Bacterial biomass, ammonium oxidation activity, and nitrite oxidation activity were used to analyze the nitrogen circulation activity. The bacterial biomass was estimated by eDNA analysis method [16] as mentioned above. To estimate the ammonium and nitrite oxidation activities, 2-g soil (moisture was adjusted to 60% water holding capacity) was taken into a 50 ml plastic tube, then 60 μmol of -N ((NH₄)₂SO₄) or -N (KNO₂) was added. After 3 days of incubation at 25˚C, decrease rates of -N and -N were measured. Each of the three properties (bacterial biomass, ammonium oxidation activity, and nitrite oxidation activity) was scored 0 - 100 points. Bacterial biomass of 6 × 10⁸ cells/g-soil was defined as 100 points. Similarly, complete reduction of added NH₄⁺ or NO₂⁻ during the incubation was defined as 100 points for ammonium or nitrite oxidation activities, respectively. Based on these 3 scores, a radar chart was constructed, and then the nitrogen circulation activity was calculated.

Bioplastics are degraded by many kinds of microorganisms in nature, and the bioplastics are converted into water and carbon dioxide by microbial metabolism. Non-biodegradable petrochemical plastics such as PA66, polypropylene and polyethylene remain in the environment for a long time because the plastics are resistant to invade by microorganisms. To analyze the biodegradability of each plastic in nature, 3 kinds of commercial bioplastics (PBS, PBS-starch and PLA) and a non-biodegradable petrochemical plastic (PA66) were buried in an agricultural soil (initial bacterial biomass: 1 × 10⁹ cells/g-soil), and the weight reductions of plastics were analyzed after 28 days. The weight reductions of PBS-starch and PBS were 7.2% and 1.2%, respectively, however PLA and PA66 remained undegraded (Figure 1). This result indicates that the degradation of bioplastics

in nature is closely related to the chemical component and bonding characteristics of the plastic.

To determine the influences of the degradation products from the bioplastics on the soil environment, time courses of microbial biomass in the soil were analyzed. The bacterial and fungal biomass in the soil samples did not change so much over the 28 days (Figure 2(a) and Figure 2(b)). These results suggest that the degradation products from PBS and PBS-starch do not affect the microbial biomass and diversity.

To analyze the biodegradability of each bioplastic clearly, the powdered bioplastics were added in soil and the rate of decrease in soil TC was measured after 28 days. The degradation ratios of PBS-starch, PBS, and PLA after 28 days were 24.4%, 16.8%, and 13.8%, respectively. These bioplastics were degraded faster than the commercial bioplastics (Figure 3). The enhancement of biodegradability of powdered bioplastics in the soil seemed to be caused by increase in the surface area. The tendency of the relative biodegradabilities of each powdered- bioplastics was similar to those of the commercial bioplastics.

In order to analyze the effect of bacterial biomass on the degradation of bioplastics in the soil, PBS-starch films were buried in 3 kinds of soils containing the same bacterial diversity but different levels of bacteria biomass (A: 7.5 × 10⁶, B: 7.5 × 10⁷ and C: 7.5 × 10⁸ cells/g-soil), and the reduction in the weight of bioplastic was measured. The soil samples were prepared by mixing different ratios of sterilized and non-sterilized soils (see Materials and Methods section). The degradation ratio was greater when the bacterial biomass was higher (Figure 4). This

result suggests that the degradation of bioplastic depends on the bacterial biomass in the soil.

In the next step, PBS-starch films were buried in 3 kinds of environmental soil samples differing in bacterial biomass and diversity. The degradation ratios of PBS-starch in the soils from a mountain (5.8 × 10⁷ cells/g-soil), from a riverside (1.0 × 10⁸ cells/g-soil), and from an agricultural farm (7.8 × 10⁸ cells/g-soil) were 8.0%, 23.4%, and 28.3%, respectively (Table 2). These results also indicate that PBS-starch degradation in the environmental soil samples is closely related to the bacterial biomass.

Three kinds of commercial bioplastics (PBS, PBS-starch and PLA) and a non-biodegradable petrochemical plastic (PA66) were buried in an agricultural field (initial bacterial biomass: 5.4 × 10⁸ cells/g-soil) for 2 years. The degradation of each plastic and the effect of the degradation on the soil bacterial biomass and diversity were analyzed. The surfaces of all bioplastics turned dark, however that of PA66 did not change. Of the bioplastics, the structures of PBS and PBS-starch were considerably more degraded than that of PLA. This result indicates that the degradation rate of PBS and PBS-starch in the environment is faster than that of PLA. This result was

similar to that from the short-term (28 days) degradation experiment. The bacterial biomass in PBS, PBS-starch, and PLA buried soils did not differ significantly to that in the control experiment (5.4 × 10⁸ cells/g-soil), however the bacterial biomass in the soil with PA66 decreased slightly (4.2 × 10⁸ cells/g-soil) (Figure 5).

PCR-DGGE analysis was carried out to investigate the bacterial diversity in each soil sample (Figure 6). The band patterns were divided into 3 clusters. The patterns from PBS and PA66 belonged to the same cluster, and those from PLA and PBS-starch belonged to the same cluster. The BSI (band similarity index) among the clusters was above 80%, therefore the degradation of bioplastics and PA66 in the soil for 2 years did not seem to

influence the bacterial diversity. These results indicate that the soil bacterial biomass and diversity were not influenced by the degradation of bioplastics.

The plastic samples which was buried in soil for 28 days and 2 years were observed by SEM, and changes in the plastic surfaces were analyzed (Figure 7). The surfaces of PBS and PBS-starch were drastically changed in both short- and long-term experiments, confirming the decay of these bioplastics. In the case of PLA, the surface structure changed slightly after 28 days, and the structure was further decayed after 2 years. On the other hand, PA66 did not change after 28 days or 2 years of degradation, thus the non-biodegradable petrochemical plastic seemed to be very recalcitrant to biodegradation in the soil environment. These results indicate that the structures of the bioplastics were degraded and decayed in the soil environment, though the degradation rates differed among the bioplastics. PBS and PBS-starch were easily degraded, but PLA needed a long time for a significant degradation.

Biodegradation of PLA, PBS, and PBS-starch in the agricultural soil did not significantly affect the bacterial biomass, however the bacterial diversity was slightly changed. In order to investigate the influences on the microbial activity in agricultural soils by the degradation of bioplastics, the nitrogen circulation activities in the soils buried with PBS, PBS-starch, or PLA were analyzed. The activity of the nitrogen circulation in the soil was measured based on the bacterial biomass, oxidation activity, and oxidation activity.

After 84 days of incorporation of bioplastics in soil, the oxidation activities of and and the bacterial biomass were decreased in the soils with PLA. Especially, the oxidation activity was significantly changed, which was 26% lower than that without bioplastic (control experiment). The nitrogen circulation activity (21.5 points) was almost half the level of the control experiment (40.0 points) (Figure 8(a)).

On the other hand, the nitrogen circulation activity in soil with PBS was almost the same level as the control experiment after 84 days of treatment (Figure 8(b)). The activities were 21.1 points in PBS-buried soil and 24.2 points in control experiment. The bacterial biomass and the oxidation activities of and in PBS- starch buried soil were not influenced by the degradation process (Figure 8(c)).

These results indicate that the degradation of PBS and PBS-starch did not affect on the nitrogen circulation activity, but that of PLA seemed to show a negative effect for the activities of both ammonium and nitrite-oxi- dizing bacteria.