Skip to main content

Degradation of low density polyethylene by Bacillus species


Since its invention, polyethylene (PE) has brought many conveniences to human production and life. In recent years, however, environmental pollution and threats to human health caused by insufficient PE recycling have attracted widespread attention. Biodegradation is a potential solution for preventing PE pollution. In this study, Bacillus subtilis and Bacillus licheniformis, which are widespread in the environment, were examined for their PE degradation abilities. Biodegradation of low-density polyethylene (LDPE) was assessed by weight loss, Fourier transform infrared spectroscopy (FTIR), and high performance liquid chromatography (HPLC) analyses. Weight losses of 3.49% and 2.83% were observed for samples exposed to strains B. subtilis ATCC6051 and B. licheniformis ATCC14580 for 30 days. Optical microscopy revealed obvious structural changes, such as cracks, pits, and roughness, on the surfaces of the microorganism-exposed LDPE sheets. Oxidation of the LDPE sheet surfaces was also demonstrated by the FTIR-based observation of carbon-unsaturated, –OH, –NO, –C=C, and –C–O bonds. These results support the notion that B. subtilis ATCC6051 and B. licheniformis ATCC14580 can degrade PE and could potentially be used as PE-biodegrading microorganisms. Further research is needed to examine potential relevant degradation mechanisms, such as those involving key enzymes.


Plastics were invented in the 1850s and replaced commonly used materials such as glass, metal, and wood. In current, plastic materials are widely used in all aspects of human production and life, due to their low manufacturing cost, good durability, and high strength [1]. The most widely used plastics are polyethylene (PE), polyethylene terephthalate (PET), polychlorinated vinyl (PVC), polypropylene (PP), polystyrene (PS), and polyurethane (PU) [10, 33, 37].

Among them, PE has the highest yield, more than 100 million tons each year globally [10]. PE-based materials are used in various industries, including transportation, construction, agriculture, machine building, and packaging [14]. However, a large proportion of PE products are not subjected to proper disposal after use. Published statistics indicate that less than 20% of PE waste is recycled each year [3]. In the natural environment, the accumulation of large amounts of PE waste severely impacts animals, plants, and microorganisms on land [25]. Consequently, PE waste flows into the ocean and affects marine ecology via toxicity exerted on organisms through consumption and suffocation [23, 30].

Conventional disposal methods for PE waste include landfilling, thermal treatment, and chemical treatment [17, 31, 35, 52, 58]. The management and recycling of waste through these traditional methods has been improved to a certain extent over time. However, such methods may cause secondary pollution of the environment. For example, burning PE waste can cause air pollution and excessive emissions of greenhouse gases. Toxic compounds released from PE waste can eventually be consumed by the human body through the food chain, threatening human health [4, 36].

Given some of the shortcomings of traditional methods, the advantages of recycling and degrading PE waste by biological methods have gained increasing interest [1]. Biodegradation has the advantages of low cost, strong operability, and low risk for releasing toxic fumes and/or harmful compounds to the environment. In recent years, researchers have isolated microorganisms with PE degradation potential from landfills, seawater, soil, and other sources [13, 20, 40, 46, 55]. For example, Anabaena spiroides, Bacillus sp., Lysinibacillus sp., Pseudomonas sp., and Aspergillus flavus were identified as good candidate strains [15, 20, 21, 29, 40, 43, 55, 57]. Invertebrates can also degrade PE, such as Tenebrio molitor, Galleria mellonella, Achroia grisella, and Lumbriculus variegatus [5, 28, 34, 45].

In this study, we selected five kinds of Bacillus species, which are widely present in natural soil, as potential strains to degrade LDPE. Their biodegradation of LDPE was assessed by weight loss, high performance liquid chromatography (HPLC), and attenuated total reflection Fourier transform infrared spectroscopy (ATR-FTIR) analyses. Furthermore, we identified some relevant chemical bond changes in LDPE.

Materials and methods


LDPE film was obtained from Goodfellow (9002884, Huntingdon, England). The chemical composition of the product was further characterized using FT-IR IS50 (Thermo Fisher, Waltham, USA). Bacterial cells were cultured in Luria Bertani (LB) broth composed of sodium chloride (10 g/l), tryptone (10 g/l), and yeast extract (5 g/l). The pH of LB broth was adjusted to 7.4 with NaOH. In the assay for microbial degradation of LDPE, mineral salt medium, Bushnell-Haas (BH) broth was used. BH broth contained K2HPO4 (1 g/l), KH2PO4 (1 g/l), NH4NO3 (1 g/l), CaCl2 (0.02 g/l), MgSO4 (0.20 g/l), and FeCl3 (0.05 g/l): pH was adjusted to 7 with NaOH [51]. Organic solvents such as acetone, chloroform, and ethanol were used for sample processing and analysis (Daejung, Siheung, Korea).

Microbial strains

Microbial strains used in this study were obtained from Korean Collection for Type Cultures (KCTC): Bacillus subtilis ATCC6051, Bacillus licheniformis ATCC14580, Bacillus pumilus ATCC7061, Bacillus amyloliquefaciens ATCC23350 and Bacillus velezensis KCTC13012.

LDPE film

Polythene film was cut into approximately square pieces with a dimension of 3 × 3 cm. The cut pieces were soaked in 70% ethanol solution for 30 min and washed with sterile distilled water. Subsequently, the PE sheets were dried at 60 °C for 1 h and weighed separately. The dried LDPE film samples were stored in glass desiccators until further use.

LDPE biodegradation in flasks

To see if PE could be decomposed by bacterial strains, Bacillus strains were cultured in 250 ml flasks containing 100 ml of BH broth along with LDPE film (3 × 3 cm) [27]. For inoculum preparation, 10 ml of overnight-culture Bacillus cells were collected by centrifugation at 12,000 rpm for 2 min at 4 °C, and resuspended in distilled water. The same process was further repeated twice times to remove LB medium. The final cells were inoculated into 100 ml BH broth and incubated at 37 °C with constant shaking at 135 rpm. LDPE film in BH broth without bacterial inoculation was used as a negative control, which was incubated under the same conditions as the sample group. As a blank, the LDPE film was used as received without culturing. All experiments were performed independently in triplicate.

Determination of cell counts during LDPE biodegradation

Once every 2 days, the absorbance of culture broth was measured at 600 nm (OD600). In addition, the number of viable cells was also determined by the colony counting method. For determination of colony counts, 100 µl of culture broth was spread on LB plates. Then, plates were incubated at 37 °C for 24 h. Viable cell counts were expressed in colony forming units (CFU) per milliliter.

Determination of weight loss

Once every 10 days, the LDPE film was taken from the cultures and washed with 2% sodium dodecyl sulfate (SDS) solution for 30 min, 70% ethanol solution for 30 min, and distilled water for 30 min in turn to remove the bacterial biomass. Then, the film was dried at 60 °C for 1 h and weighed. The weight loss of LDPE was calculated by using Eq. 1.

$${\text{Weight loss}}\, \left( \% \right) = \frac{{{\text{initial weight}} - {\text{final weight}}}}{{\text{initial weight}}} \times 100\% .$$

Optical microscopic analysis

Surfaces and edges of LDPE film were observed using an optical microscope. Optical microscopic analysis was performed with LDPE film specimens, indicating the blank (as-received), the negative control cultured without microbe, and the samples cultured with bacterial cells, at 1000 × magnification.

High-performance liquid chromatography (HPLC) analysis

Supernatant taken from the 30-day culture was filtered and applied to HPLC, Agilent 1100 series (Agilent Technologies, CA, USA) equipped with the RI-101 refractive index detector (Shodex, Denmark) [32, 44]. The flow rate was controlled at 500 µl per minute through a MetaCarb 87H column (Agilent Technologies, USA) at 25 °C using 5 mmol/l sulfuric acid as a single mobile phase.

Attenuated total reflection-Fourier transform infrared spectroscopy analysis

Samples were analyzed in the same conditions in attenuated total reflection (ATR) mode using an FT-IR IS50 (Thermo Fisher, Waltham, USA) [50]. All LDPE film specimens, including blank (as-received), negative control, and samples, were washed with 2% SDS, 70% ethanol, and distilled water sequentially. The PE specimens from the negative control was incubated under the same conditions as the sample group. In the final step, the LDPE film specimens were fully dried. IR spectra of all specimens were recorded in the 4000–400 cm−1 range at room temperature [38]. There were no significant differences between the three scans of each specimen.

Results and discussion

Growth of Bacillus cells in the medium containing LDPE as a sole carbon source

In this study, as potential strains to degrade LDPE, we selected five kinds of Bacillus species, including B. subtilis ATCC6051, B. licheniformis ATCC14580, B. pumilus ATCC7061, B. amyloliquefaciens ATCC23350 and B. velezensis KCTC13012. The five Bacillus strains were cultured for 30 days at 37 °C in the mineral salt medium supplemented with PE film fragments for the preliminary screening. As a result, B. subtilis ATCC6051 and B. licheniformis ATCC14580 showed cell growth by absorbance measurement at 600 nm after 30 days of culture, while the other strains didn't (data not shown).

Thus, for these two strains B. subtilis and B. licheniformis, the bacterial culture was monitored for 30 days with a 2-day sampling interval to see the detailed growth profiles in the salt medium supplemented with LDPE as the sole carbon source (Fig. 1a, b). Immediately after inoculation with B. subtilis and B. licheniformis, the absorbance values were similar, at 0.10 and 0.11, respectively. These values dropped sharply over the next 6 days (Fig. 1a, b). We speculated that this might reflect the hysteresis of Bacillus strains when using LDPE as the only carbon and energy source, due to the removal of the original medium during inoculation. However, viable count analysis revealed that the viable cell counts decreased significantly only in the first 2 days, from 1.29 × 104 CFU/ml (B. subtilis) and 5.62 × 104 CFU/ml (B. licheniformis) at the time of inoculation to 9.77 × 102 CFU/ml and 4.67 × 103 CFU/ml at day 2 post-inoculation, respectively (Fig. 1c, d). Thereafter, the trend flattened. This difference was presumed to reflect that the mineral salt medium contains a small amount of precipitate, leading to a pronounced decrease in absorbance caused by its early bacterial consumption [47]. For B. subtilis, bacterial growth significantly increased starting at day 6 of culture; the growth rate reached a plateau at day 12 and remained at that level to day 30 (Fig. 1a). The OD600 value reached the highest point of 0.062 at day 14. The viable cell counts of B. subtilis also showed the same patterns, reaching 1.95 × 104 CFU/ml at day 16 (Fig. 1c). Comparison of the results for each strain revealed that the absorbance of B. licheniformis showed a longer lag time than that of B. subtilis, and B. subtilis showed a stronger increase in viable cells in the presence of LDPE as the sole carbon source (Fig. 1b, d).

Fig. 1
figure 1

Growth profiles of B. subtilis and B. licheniformis strains in a minimal salt medium supplemented with LDPE as a sole carbon source. a, c B. subtilis; b, d B. licheniformis; a, b cell density at 600 nm (OD600); and c, d viable cell count as CFU/ml. All experiments were performed independently in triplicate

The average weight loss of LDPE films was determined every 10 days during incubation with B. subtilis or B. licheniformis (Fig. 2). Cultures without inoculation of microorganisms were incubated as negative controls. The weight of the LDPE film steadily decreased over 30 days in the presence of the tested Bacillus strains, while that of the negative control was almost unchanged (Fig. 2). After 30 days, LDPE weight losses of 3.49% and 2.83% were observed for films exposed to B. subtilis and B. licheniformis, respectively. The weight losses of LDPE and the increases in viable cell counts indicate that both Bacillus strains utilized the polymer as a carbon source for growth. Meanwhile, when the bacteria entered the stationary phase (12–30 days), LDPE was still being gradually degraded. At this time, the Bacillus strains may be in a viable but not culturable (VBNC) state, which is a survival state exhibited in response to adverse growth conditions [48]. Interestingly, the VBNC state of bacteria was reported to have a positive effect on the degradation of LDPE [12]. To determine the degradation status of LDPE in our experimental setting during this period, further examination in combination with more methods would be required.

Fig. 2
figure 2

Weight loss of LDPE film samples. Symbols are: filled circle, LDPE samples incubated with B. subtilis; open circle, LDPE samples incubated with B. licheniformis; and filled triangle, negative control, indicating LDPE specimens incubated in the flask in which bacterial cells were not inoculated. All experiments were performed independently in triplicate. See the Methods section for the details on calculating the weight loss of LDPE film samples

In earlier reports, Bacillus sp. SM1 generated an 18.9% weight loss in LDPE sheets within 180 days [3]. Harshvardhan and coworkers reported 1.50% and 1.75% of LDPE weight loss due to a 30-day exposure to B. pumilis M27 and B. subtilis H1584, respectively [19]. Bacillus sp. ISJ55 isolated from plastic-contaminated soil reduced the weight of LDPE by 1.50% at 60 days [18]. In another study, 3.5% and 10% weight losses were reported in HDPE and LDPE degradation tests using B. sphaericus strain over 1 year [49].

When seeking to degrade plastics in the natural environment, it may be more effective to employ a microbial community composed of various microorganisms rather than using a single strain. In a recent study, Gao and Sun suggested an artificial community containing Idiomarina sp., Marinobacter sp., and Exiguobacterium sp. to degrade PE effectively [13]. In this aspect, future development of B. subtilis within microbial communities and further studies on the interaction of various enzymes in B. subtilis during degradation could be needed.

LDPE morphology

To assess the morphology of the LDPE film specimens after 30 days of incubation, the films were washed and dried. Polymer samples were analyzed using an optical microscope (Fig. 3). Freshly prepared LDPE film without any treatment was observed as a blank (Fig. 3a, e). In the comparisons with the blank, after 30 days of incubation, there was no noticeable change on the surface of the negative control group (Fig. 3b). However, the surfaces of LDPE samples cultured with B. subtilis (Fig. 3c) or B. licheniformis (Fig. 3d) were roughened and exhibited some cracks. We speculate that these changes occurred because the bacteria formed a biofilm on the LDPE surface.

Fig. 3
figure 3

Morphologies of LDPE film under the optical microscope. For morphological analysis, all LDPE specimens were taken after 30-day incubation except for blank (fresh film). Surfaces (ad) and edges (eh) were analyzed separately. a, e Blank group, indicating fresh LDPE film; b, f negative control, indicating LDPE specimens incubated in a flask in which bacterial cells were not inoculated; c, g LDPE film incubated with B. subtilis; and d, h LDPE film incubated with B. licheniformis

Microscopic observation of the LDPE film edges (Fig. 3e–h) revealed that after 30 days of culture, the edges of negative control LDPE (Fig. 3f) were more rounded and flatter than those of the blank (Fig. 3e). This suggests that the sample experienced friction during the culture process, however the data on weight loss indicate that this friction was insufficient to significantly decrease the weight of the LDPE film (Fig. 2). In contrast, fine cracks with peeling were observed at the edges of LDPE cultured with B. subtilis (Fig. 3g) or B. licheniformis (Fig. 3h). Taken together, these results indicate that LDPE is degraded to a certain extent by the two Bacillus strains tested in this study.

LDPE decomposition products

Because PE can be structurally classified as a hydrocarbon, it might follow the terminal oxidation, double terminal oxidation, or subterminal oxidation metabolic pathway. PE molecules that undergo one of the above processes are eventually carboxylated and structurally similar to fatty acids upon carboxylation [26]. Thus, we hypothesized that low-molecular-weight organic acids would be produced from the decomposition of LDPE. To determine the decomposition products of LDPE, supernatants taken from 30-day cultures of the two Bacillus strains were subjected to HPLC analysis (Fig. 4). The Bacillus-inoculated samples each revealed three distinct new peaks, found at 21.8, 24.5, and 29.7 min (Fig. 4). Identification for these peaks was not conducted in this study, but it seems that the peak at 21.8 min indicates butyrate, based on retention time of the standard. We were also unable to confirm the component of the other two peaks due to a lack of standards. More specifically, after 30 days of culture, the peak at 21.8 min (estimated as butyrate) was detectable in both bacteria-containing culture supernatants (Fig. 4b, c) but not the negative control (Fig. 4a). Alkane oxidase and laccase, present in Bacillus species, are predicted to be involved in the degradation of PE [22]. Polyethylene molecules are converted to alcohols by the action of monooxygenases, and these alcohols are further oxidized to aldehydes by alcohol dehydrogenase [7]. The aldehydes are converted to fatty acids by aldehyde dehydrogenases [11] and, finally, the fatty acids are metabolized through the β-oxidation pathway and finally converted into CO2 and energy [6, 8]. Butyrate estimate (the peak at 21.8 min) in HPLC analysis, as one of the typical volatile lower fatty acids, indicates that Bacillus strains can utilize LDPE as the sole carbon source for metabolic activities to produce organic acids and other products, further verifying that Bacillus can degrade LDPE.

Fig. 4
figure 4

Determination of LDPE decomposition products using HPLC. For HPLC analysis, the broth was taken after 30-day culture. a In the negative control, the LDPE specimens were incubated in a flask without bacteria; b, c LDPE samples were incubated with b B. subtilis and c B. licheniformis

Surface functional groups on LDPE

The analysis of surface functional groups can be used as an indicator of PE degradation [2]. In this study, the functional groups on LDPE were determined by ATR-FTIR (Fig. 5). All four LDPE specimens, including blank, negative control, two samples incubated with B. subtilis or B. licheniformis, exhibited peaks at wavelengths of 700 cm−1, 1390 cm−1, 1485 cm−1, 2851 cm−1, and 2922 cm−1, which indicated C–H, –CH3 (methyl, C–H asymmetric/symmetric bend), =CH2 (methylene, C–H bend), =CH2 (methylene, C–H asymmetric/symmetric stretch) and =CH2 (methylene, C–H asymmetric/symmetric stretch) bonds, respectively [9, 24].

Fig. 5
figure 5

ATR-FTIR spectra of LDPE film. For ATR-FTIR analysis, all LDPE specimens were taken after 30-day incubation except for blank (fresh film). The colors indicate: blank (fresh LDPE film; cyan); negative control (LDPE specimens incubated in a flask without bacteria; yellow-green); LDPE film samples incubated with B. subtilis (blue) or B. licheniformis (red)

There were a number of peak differences between negative control (or blank) and LDPE samples incubated with bacterial strains, as follows: On the surface of LDPE incubated with B. subtilis, a new peak was observed at 1030.65 cm−1 (Fig. 5), indicating C–O stretching and the presence of alcohol, carboxylic acid, ester, and ether groups [53]. This phenomenon was also reported in LDPE biodegradation using B. siamensis [16].

On the other hand, the LDPE incubated with B. subtilis also exhibited a new peak at 1538.86 cm−1 indicating N–O stretching. In recent studies for PE degradation, it has been reported that the N–O stretching was found in PE samples [39, 41, 50]. For example, it has been reported that the corrosive gas NOx can cause PE degradation [39]. Furthermore, nitric oxide synthase (NOS), ubiquitous in Bacillus, can generate nitric oxide gas in an enzymatic reaction, which is thought to be responsible for the formation of nitro groups on LDPE [41]. Another study speculated that bacteria might secrete nitro and surfactants [50]. Although the partial pressure of NOx produced by Bacillus strains during culture was much lower than the reaction conditions of Oluwoye and coworkers’ study, the NOx-induced LDPE free radical reaction deserves further investigation.

Additional new peaks at 1646.10 cm−1 and 3281.24 cm−1 were observed in LDPE incubated with B. subtilis, suggesting the existence of C=C stretching and an –OH group, respectively. These results indicate that the B. subtilis-exposed LDPE underwent oxidation under our experimental conditions. Hydroxylation is generally considered to be an important step in PE biodegradation, because an hydroxyl group is necessary for the formation of carbonyl groups [54], which can be converted into esters for eventual cleavage by lipase or esterase [56].

Finally, LDPE incubated with B. subtilis exhibited decreases in the peaks at 2851 cm−1 and 2922 cm−1, indicating the weakening of =CH2 stretching. In a previous study on the biodegradation of LDPE, similar results were obtained using Acinetobacter baumannii [42].

The results obtained for surface functional groups of LDPE incubated with B. licheniformis were consistent with those obtained for LDPE incubated with B. subtilis, but of a lesser degree (Fig. 5). Collectively, these findings on the changes in surface functional groups support the notion that LDPE films are degraded by the two Bacillus strains tested herein. In this study, we tested two Bacillus strains, B. subtilis ATCC6051 and B. licheniformis ATCC14580, and reveal that they both exhibit potential for the colonization and biodegradation of LDPE. B. subtilis could form biofilms on untreated LDPE films and grow using PE as the sole carbon source. After 30 days, it effectively degraded 3.49% of the input LDPE. The LDPE degradation ability of B. licheniformis was slightly lower than that of B. subtilis, effectively degraded by 2.83%. This is the highest rate reported so far for LDPE degradation using a single Bacillus strain. Morphological changes seen by microscopic observations, differences in peaks on HPLC analysis, changes in peak intensities on ATR-FTIR, and the generation of new absorption peaks all confirmed the microbial-induced degradation of the PE film. Biofilm development and PE film degradation were observed by incubating LDPE films with each microbe as the sole carbon source. The study highlights that B. subtilis and B. licheniformis, the most common bacteria in soil, can be candidate microorganisms for bioremediation of plastic pollution. Various enzymes or microbial communities can be developed for polymer degradation. It will be a safe and environmentally friendly method. However, as aerobic bacteria, Bacillus has obvious limitations for plastic degradation in anaerobic environments (such as deep soil, and inside landfills), and it is necessary to further develop microbial communities composed of various microorganisms to cope with complex natural environments.

Availability of data and materials

The datasets used and/or analyzed during the current study are available from the corresponding author on reasonable request.


  1. Ahmed N, Zeeshan M, Iqbal N, Farooq MZ, Shah SA (2018) Investigation on bio-oil yield and quality with scrap tire addition in sugarcane bagasse pyrolysis. J Clean Prod 196:927–934.

    Article  CAS  Google Scholar 

  2. Ayeni TO, Arotupin DJ, Ayo OE (2022) Biodegradation of polyethylene by indigenous fungi from waste recycling site, South West, Nigeria. Bull Natl Res Cent 46(1):1–9.

    Article  Google Scholar 

  3. Biki SP, Mahmud S, Akhter S, Rahman MJ, Rix JJ, Al Bachchu MA, Ahmed M (2021) Polyethylene degradation by Ralstonia sp. strain SKM2 and Bacillus sp. strain SM1 isolated from land fill soil site. Environ Technol Innov 22:101495.

    Article  CAS  Google Scholar 

  4. Bishop G, Styles D, Lens PN (2020) Recycling of European plastic is a pathway for plastic debris in the ocean. Environ Int 142:105893.

    Article  CAS  Google Scholar 

  5. Bombelli P, Howe CJ, Bertocchini F (2017) Polyethylene bio-degradation by caterpillars of the wax moth Galleria mellonella. Curr Biol 27(8):R292–R293.

    Article  CAS  Google Scholar 

  6. Cha T-Y, Yong Y, Park H, Yun H-J, Jeon W, Ahn J-O, Choi K-Y (2021) Biosynthesis of C12 fatty alcohols by whole cell biotransformation of C12 derivatives using Escherichia coli two-cell systems expressing CAR and ADH. Stand Genom Sci 26(3):392–401.

    Article  CAS  Google Scholar 

  7. Chen Y, Zhao M, Hu L, Wang Z, Hrynsphan D, Chen J (2021) Characterization and functional analysis of Bacillus aryabhattai CY for acrylic acid biodegradation: Immobilization and metabolic pathway. Biotechnol Bioprocess Eng 26(6):910–922.

    Article  CAS  Google Scholar 

  8. Cho IK, Seol JU, Rahman M, Lee D-G, Son H, Cho H (2021) Laboratory studies of the algaecide GreenTD: stability, algaecidal activity and reduction of microcystin production. Appl Biol Chem 64(1):1–8.

    Article  CAS  Google Scholar 

  9. Coates J (2000) Interpretation of infrared spectra, a practical approach. Citeseer, London

    Google Scholar 

  10. Danso D, Chow J, Streit WR (2019) Plastics: environmental and biotechnological perspectives on microbial degradation. Appl Environ Biotechnol 85(19):e01095-e1119.

    Article  CAS  Google Scholar 

  11. Elahi A, Bukhari DA, Shamim S, Rehman A (2021) Plastics degradation by microbes: a sustainable approach. J King Saud Univ Sci 33(6):101538.

    Article  Google Scholar 

  12. Fida TT, Moreno-Forero SK, Breugelmans P, Heipieper HJ, Röling WF, Springael D (2017) Physiological and transcriptome response of the polycyclic aromatic hydrocarbon degrading Novosphingobium sp. LH128 after inoculation in soil. Environ Sci Technol 51(3):1570–1579.

    Article  CAS  Google Scholar 

  13. Gao R, Sun C (2021) A marine bacterial community capable of degrading poly(ethylene terephthalate) and polyethylene. J Hazard Mater 416:125928.

    Article  CAS  Google Scholar 

  14. Geyer R (2020) Production, use, and fate of synthetic polymers plastic waste and recycling, vol 2020. Academic Press, London, pp 13–32

    Book  Google Scholar 

  15. Ghatge S, Yang Y, Ahn J-H, Hur H-G (2020) Biodegradation of polyethylene: a brief review. Appl Biol Chem 63(1):1–14.

    Article  CAS  Google Scholar 

  16. Gong G, Kim S, Lee S-M, Woo HM, Park TH, Um Y (2017) Complete genome sequence of Bacillus sp. 275, producing extracellular cellulolytic, xylanolytic and ligninolytic enzymes. J Biotechnol 254:59–62.

    Article  CAS  Google Scholar 

  17. Grigore ME (2017) Methods of recycling, properties and applications of recycled thermoplastic polymers. Recycling 2(4):24.

    Article  Google Scholar 

  18. Gupta KK, Devi D (2019) Biodegradation of low density polyethylene by selected Bacillus sp. Gazi Univ J Sci 32(3):802–813.

    Article  Google Scholar 

  19. Harshvardhan K, Jha B (2013) Biodegradation of low-density polyethylene by marine bacteria from pelagic waters, Arabian Sea, India. Mar Pollut Bull 77(1–2):100–106.

    Article  CAS  Google Scholar 

  20. Jeon JM, Park SJ, Choi TR, Park JH, Yoon JJ (2021) Biodegradation of polyethylene and polypropylene by Lysinibacillus species JJY0216 isolated from soil grove. Polym Degrad Stab 191:109662.

    Article  CAS  Google Scholar 

  21. Jeong JW, Singhvi M, Kim BS (2022) Improved extracellular enzyme-mediated production of 7,10-dihydroxy-8 (E)-octadecenoic acid by Pseudomonas aeruginosa. Biotechnol Bioprocess Eng.

    Article  Google Scholar 

  22. Jin CE, Kim MN (2017) Change of bacterial community in oil-polluted soil after enrichment cultivation with low-molecular-weight polyethylene. Int Biodeterior Biodegradation 118:27–33.

    Article  CAS  Google Scholar 

  23. Jung JW, Kang JS, Choi J, Park JW (2020) Chronic toxicity of endocrine disrupting chemicals used in plastic products in Korean resident species: implications for aquatic ecological risk assessment. Ecotoxicol Environ Saf 192:110309.

    Article  CAS  Google Scholar 

  24. Jung MR, Horgen FD, Orski SV, Rodriguez V, Beers KL, Balazs GH, Jones TT, Work TM, Brignac KC, Royer S-J (2018) Validation of ATR FT-IR to identify polymers of plastic marine debris, including those ingested by marine organisms. Mar Pollut Bull 127:704–716.

    Article  CAS  Google Scholar 

  25. Kaseem M, Hamad K, Deri F (2012) Thermoplastic starch blends: a review of recent works. Polym Sci A 54(2):165–176.

    Article  CAS  Google Scholar 

  26. Kawai F, Watanabe M, Shibata M, Yokoyama S, Sudate Y, Hayashi S (2004) Comparative study on biodegradability of polyethylene wax by bacteria and fungi. Polym Degrad Stab 86(1):105–114.

    Article  CAS  Google Scholar 

  27. Kumar AG, Hinduja M, Sujitha K, Rajan NN, Dharani G (2021) Biodegradation of polystyrene by deep-sea Bacillus paralicheniformis G1 and genome analysis. Sci Total Environ 774:145002.

    Article  CAS  Google Scholar 

  28. Kundungal H, Gangarapu M, Sarangapani S, Patchaiyappan A, Devipriya SP (2019) Efficient biodegradation of polyethylene (HDPE) waste by the plastic-eating lesser waxworm (Achroia grisella). Environ Sci Pollut Res 26(18):18509–18519.

    Article  CAS  Google Scholar 

  29. Kunlere IO, Fagade OE, Nwadike BI (2019) Biodegradation of low density polyethylene (LDPE) by certain indigenous bacteria and fungi. Int J Environ Stud 76(3):428–440.

    Article  CAS  Google Scholar 

  30. Lahive E, Walton A, Horton AA, Spurgeon DJ, Svendsen C (2019) Microplastic particles reduce reproduction in the terrestrial worm Enchytraeus crypticus in a soil exposure. Environ Pollut 255:113174.

    Article  CAS  Google Scholar 

  31. Lamnii H, Abdelaziz MN, Ayoub G, Colin X, Maschke U (2021) Experimental investigation and modeling attempt on the effects of ultraviolet aging on the fatigue behavior of an LDPE semi-crystalline polymer. Int J Fatigue 142:105952.

    Article  CAS  Google Scholar 

  32. Lee JS, Paje LA, Kim MJ, Jang SH, Kim JT, Lee S (2021) Validation of an optimized HPLC–UV method for the quantification of formononetin and biochanin A in Trifolium pratense extract. Appl Biol Chem 64(1):1–7.

    Article  CAS  Google Scholar 

  33. Li D, Zhou L, Wang X, He L, Yang X (2019) Effect of crystallinity of polyethylene with different densities on breakdown strength and conductance property. Materials 12(11):1746.

    Article  CAS  Google Scholar 

  34. Li Y, Jie G, Liu Y, Zhuang G, Peng X, Wu WM, Zhuang XL (2020) Biodegradation of expanded polystyrene and low-density polyethylene foams in larvae of Tenebrio molitor Linnaeus (Coleoptera: Tenebrionidae): broad versus limited extent depolymerization and microbe-dependence versus independence. Chemosphere 262:127818.

    Article  CAS  Google Scholar 

  35. Liu K, Wang X, Wei N, Song Z, Li D (2019) Accurate quantification and transport estimation of suspended atmospheric microplastics in megacities: implications for human health. Environ Int 132:105127–105127.

    Article  CAS  Google Scholar 

  36. Lwanga EH, Vega JM, Quej VK, de los Angeles Chi J, Del Cid LS, Chi C, Segura GE, Gertsen H, Salánki T, van der Ploeg M (2017) Field evidence for transfer of plastic debris along a terrestrial food chain. Sci Rep 7(1):1–7.

    Article  CAS  Google Scholar 

  37. Makhlouf A, Satha H, Frihi D, Gherib S, Seguela R (2016) Optimization of the crystallinity of polypropylene/submicronic-talc composites: the role of filler ratio and cooling rate. Express Polym Lett 10(3):237–247.

    Article  CAS  Google Scholar 

  38. Mohamed AE, Elgammal WE, Dawaba AM, Ibrahim AG, Fouda A, Hassan SM (2022) A novel 1,3,4-thiadiazole modified chitosan: synthesis, characterization, antimicrobial activity, and release study from film dressings. Appl Biol Chem 65(1):1–18.

    Article  CAS  Google Scholar 

  39. Oluwoye I, Altarawneh M, Gore J, Bockhorn H, Dlugogorski BZ (2016) Oxidation of polyethylene under corrosive NOx atmosphere. J Phys Chem C 120(7):3766–3775.

    Article  CAS  Google Scholar 

  40. Park SY, Kim C (2019) Biodegradation of micro-polyethylene particles by bacterial colonization of a mixed microbial consortium isolated from a landfill site. Chemosphere 222(May):527–533.

    Article  CAS  Google Scholar 

  41. Pinto C, Sousa S, Froufe H, Egas C, Clément C, Fontaine F, Gomes AC (2018) Draft genome sequence of Bacillus amyloliquefaciens subsp. plantarum strain Fito F321, an endophyte microorganism from Vitis vinifera with biocontrol potential. Stand Genom Sci 13(1):1–12.

    Article  CAS  Google Scholar 

  42. Pramila R, Ramesh KV (2015) Potential biodegradation of low density polyethylene (LDPE) by Acinetobacter baumannii. Afr J Bacteriol Res 7(3):24–28.

    Article  Google Scholar 

  43. Ramach RVK, Kanna GR, Elumalai S (2017) Biodegradation of polyethylene by green photosynthetic microalgae. J Bioremediat Biodegrad 8(381):2.

    Article  CAS  Google Scholar 

  44. Seong HJ, Jang Y-S (2021) Effect of deregulation of repressor-specific carbon catabolite repression on carbon source consumption in Escherichia coli. Appl Biol Chem 64(1):1–6.

    Article  CAS  Google Scholar 

  45. Silva CJ, Silva ALP, DianaCampos SAM, Pestana JL, Gravato C (2021) Lumbriculus variegatus (oligochaeta) exposed to polyethylene microplastics: biochemical, physiological and reproductive responses. Ecotoxicol Environ Saf 207:111375.

    Article  CAS  Google Scholar 

  46. Spina F, Tummino ML, Poli A, Prigione V, Ilieva V, Cocconcelli P, Puglisi E, Bracco P, Zanetti M, Varese GC (2021) Low density polyethylene degradation by filamentous fungi. Environ Pollut 274:116548.

    Article  CAS  Google Scholar 

  47. Stafilov T, Čundeva K (1998) Determination of total thallium in fresh water by electrothermal atomic absorption spectrometry after colloid precipitate flotation. Talanta 46(6):1321–1328.

    Article  CAS  Google Scholar 

  48. Su X, Sun F, Wang Y, Hashmi MZ, Guo L, Ding L, Shen C (2015) Identification, characterization and molecular analysis of the viable but nonculturable Rhodococcus biphenylivorans. Sci Rep 5(1):1–12.

    Article  CAS  Google Scholar 

  49. Sudhakar M, Doble M, Murthy PS, Venkatesan R (2008) Marine microbe-mediated biodegradation of low-and high-density polyethylenes. Int Biodeterior Biodegradation 61(3):203–213.

    Article  CAS  Google Scholar 

  50. Tarafdar A, Lee J-U, Jeong J-E, Lee H, Jung Y, Oh HB, Woo HY, Kwon J-H (2021) Biofilm development of Bacillus siamensis ATKU1 on pristine short chain low-density polyethylene: a case study on microbe-microplastics interaction. J Hazard Mater 409:124516.

    Article  CAS  Google Scholar 

  51. Tarafdar A, Sinha A, Masto RE (2017) Biodegradation of anthracene by a newly isolated bacterial strain, Bacillus thuringiensis AT. ISM. 1, isolated from a fly ash deposition site. Lett Appl Microbiol 65(4):327–334.

    Article  CAS  Google Scholar 

  52. Tennakoon A, Wu X, Paterson AL, Patnaik S, Pei Y, LaPointe AM, Ammal SC, Hackler RA, Heyden A, Slowing II, Coates GW, Delferro M, Peters B, Huang W, Sadow AD, Perras FA (2020) Catalytic upcycling of high-density polyethylene via a processive mechanism. Nat Catal 3(11):1–9.

    Article  CAS  Google Scholar 

  53. Vimala P, Mathew L (2016) Biodegradation of polyethylene using Bacillus subtilis. Procedia Technol 24:232–239.

    Article  Google Scholar 

  54. Yao Z, Seong HJ, Jang Y-S (2022) Environmental toxicity and decomposition of polyethylene. Ecotoxicol Environ Saf 242:113933.

    Article  CAS  Google Scholar 

  55. Yin CF, Xu Y, Zhou NY (2020) Biodegradation of polyethylene mulching films by a co-culture of Acinetobacter sp. strain NyZ450 and Bacillus sp. strain NyZ451 isolated from Tenebrio molitor larvae. Int Biodeterior Biodegradation 155:105089.

    Article  CAS  Google Scholar 

  56. Yoon YR, Jang YS (2021) Potential of Baeyer–Villiger monooxygenases as an enzyme for polyethylene decomposition. J Appl Biol Chem 64:433–438.

    Article  Google Scholar 

  57. Yoshida K-i, van Dijl JM (2020) Engineering Bacillus subtilis cells as factories: enzyme secretion and value-added chemical production. Biotechnol Bioprocess Eng 25(6):872–885.

    Article  CAS  Google Scholar 

  58. Zhang F, Zeng M, Yappert RD, Sun J, Lee Y-H, Lapointe AM, Peters B, Abu-Omar MM, Scott SL (2020) Polyethylene upcycling to long-chain alkylaromatics by tandem hydrogenolysis/aromatization. Science 370:437–441.

    Article  CAS  Google Scholar 

Download references


This work was supported by the Technology Development Program to Decompose Agricultural Polyethylene Wastes Based on Systems Metabolic Engineering of Microorganisms from Cooperative Research Program for Agricultural Science and Technology Development (Project No. PJ01492601), Rural Development Administration, Republic of Korea.


This work was supported by the Technology Development Program to Decompose Agricultural Polyethylene Wastes Based on Systems Metabolic Engineering of Microorganisms from Cooperative Research Program for Agricultural Science and Technology Development (Project No. PJ01492601), Rural Development Administration, Republic of Korea.

Author information

Authors and Affiliations



Project design, YSJ; experiment, ZY; analysis, ZY, HJS, and YSJ; writing-original draft, ZY and YSJ; writing-review and editing, ZY and YSJ. All authors read and approved the final manuscript.

Corresponding author

Correspondence to Yu-Sin Jang.

Ethics declarations

Competing interests

The authors declare that they have no competing interests.

Additional information

Publisher's Note

Springer Nature remains neutral with regard to jurisdictional claims in published maps and institutional affiliations.

Rights and permissions

Open Access This article is licensed under a Creative Commons Attribution 4.0 International License, which permits use, sharing, adaptation, distribution and reproduction in any medium or format, as long as you give appropriate credit to the original author(s) and the source, provide a link to the Creative Commons licence, and indicate if changes were made. The images or other third party material in this article are included in the article's Creative Commons licence, unless indicated otherwise in a credit line to the material. If material is not included in the article's Creative Commons licence and your intended use is not permitted by statutory regulation or exceeds the permitted use, you will need to obtain permission directly from the copyright holder. To view a copy of this licence, visit

Reprints and Permissions

About this article

Verify currency and authenticity via CrossMark

Cite this article

Yao, Z., Seong, H.J. & Jang, YS. Degradation of low density polyethylene by Bacillus species. Appl Biol Chem 65, 84 (2022).

Download citation

  • Received:

  • Accepted:

  • Published:

  • DOI:


  • Polyethylene
  • Biodegradation
  • LDPE
  • Environmental pollution
  • Bacillus