Starting from their introduction in the early 1900s, the use of plastics has grown exponentially, and currently, plastics have become widespread and essential in almost every society on earth to the point that life without plastics is unimaginable for most of us. None of the commonly used plastics are considered biodegradable (meaning that they cannot be dissolved or decomposed by natural agents). As a result, they accumulate, rather than decompose, in landfills or the natural environment. The continued widespread use of plastics, which does not seem to be decreasing anytime soon, has led to plastic pollution becoming an environmental hazard for which an efficient, easily employable and environmentally-friendly solution is yet to be found. The main plastic polymers that are produced worldwide are polyurethane, polyethylene, polyamide, polyethylene terephthalate, polystyrene, polyvinyl chloride, and polypropylene. These and other plastics have become ubiquitous throughout the world, present even in the deepest parts of the world’s oceans such as the Mariana Trench. Plastic pollution in oceans continues to increase with plastic debris being found in all major ocean basins, and an estimated 4 to 12 million metric tons of plastic waste generated on land entering the marine environment in 2010 alone.
It has been conjectured that the great abundance of plastics has led to the evolution of plastic degrading enzymes such as PETase (PET or polyethylene terephthalate-digesting enzyme) in bacteria. For a long time, much of the plastics that were being produced (basically, all of the plastics mentioned above) were thought to be impossible to degrade via natural agents as the polymers are designed to be durable and stable. Furthermore, no enzymes or organisms capable of breaking them down had been identified until 1977, when some lipases (extracellular enzymes that usually cleave esters in oils and fats) were reported to be able to attack ester bonds in some aliphatic polyesters and depolymerize such materials. In recent years, a lot of discoveries later, removal of plastics from the environment using microbes and their enzymes has become a focus of much research.
For the purposes of this page, plastic-eating bacteria are defined as bacteria that can break down and digest plastics such as polyethylene terephthalate (PET), polyethylene (PE) or polyurethane (PU). The recent discovery of Ideonella sakaiensis, which can use the plastic PET as a carbon and energy source, and the following modifications to its genome which have enhanced its degrading capabilities have given new hope for the management of plastic pollution through the utilization of microbes and their enzymes. A number of other plastic-eating bacteria/microbes have also garnered much attention as the number of enzymes and microorganisms that are capable of breaking down several different types of plastics keeps growing. But, however exciting the applications of these organisms and their enzymes may seem, their capabilities are still limited and require further investigation and modification so that their potential can be fully exploited.
By Meheret Ourgessa
Ideonella sakaiensis was first discovered in 2016 by Japanese researchers who isolated the novel species from outside a bottle-recycling plant. The authors identified the species by screening 250 environmental samples at the polyethylene terephthalate (PET) bottle recycling site.  At the time, it was the first and only known bacteria species that had naturally evolved to be capable of breaking down and digesting plastic as a carbon and energy source. Earlier work had shown that the mesophilic fungus Fusarium oxysporum could also produce an enzyme that is able to break down PET into its constituent monomers. The discovery of I. sakaiensis was more exciting, however, as bacteria are much easier to harness for industrial uses compared with fungi and other eukaryotes. Furthermore, it was shown that the enzyme involved in hydrolyzing PET in I. sakaiensis had as much as 88 times more activity compared to the enzyme found in F. oxysporum. A hydrolase enzyme isolated from the actinomycete Thermobifida fusca was also shown to effectively depolymerize PET. But T. Fusca bacteria do not use this enzyme to catabolize PET and the activity of this enzyme is about 120 times lower than that of I. sakaiensis.
I. sakaiensis stain Gram-negative and are aerobic bacteria belonging to the phylum Proteobacteria. The cells are non-spore forming and rod-shaped. The genus Ideonella belongs to the family Comamonadaceae of the class Betaproteobacteria. I. sakaiensis was identified as a representative of a novel species in the genus Ideonella on the basis of its physiological, biochemical, and phylogenetic data, including DNA–DNA relatedness. The DNA–DNA relatedness of I. sakaiensis with its closest phylogenetic neighbors was well below the 70 % cut-off point recommended for the assignment of the strains to the same genomic species. The bacteria grow within the pH range 5.5–9.0 (optimally between pH 7–7.5) and temperature range 15–42 ºC (optimally between 30–37 ºC) and cannot grow with 3% NaCl. The cells of the species are motile and use a polar flagellum to move. They attach to PET films using appendages which can also grow longer to connect the cells to each other. Appendages connecting the cell to PET films might also assist in the delivery of secreted enzymes onto the film. I. sakaiensis can degrade and assimilate PET as a major carbon source for growth. 
The researchers who discovered I. sakaiensis identified two enzymes produced by the bacteria that are involved in PET degradation - PETase and MHETase (MHET stands for mono(2-hydroxyethyl) terephthalic acid, the monoester of terephthalic acid and ethylene glycol) - which catabolized PET into its monomers terephthalic acid and ethylene glycol. These monomers are then used for bacterial metabolism. Although the PETase enzyme has been described in other bacterial species (mostly belonging to the phylum Actinobacteria), MHETase seems to be unique to the genome of I. sakaiensis. Originally, the degradation of PET by I. sakaiensis was relatively slow; complete degradation of a small PET film took 6 weeks. Recently, researchers were able to genetically modify I. sakaiensis to break down PET faster and also degrade PEF(polyethylene-2,5-furandicarboxylate) which is an emerging bioderived PET replacement with improved properties. The newly modified PETase enzyme is active on the aromatic polyesters (PET and PEF), but not aliphatic polyesters. The researchers who engineered this new enzyme concluded that it is likely that significant potential remains for improving its activity through similar protein modifications further.
PET was only patented roughly 80 years ago and put into widespread use in the 1970s. It is likely that the enzyme system for PET degradation and catabolism in I. sakaiensis appeared only recently, demonstrating the remarkable speed at which microbes adapt and evolve to exploit new substrates. In this case, the new substrate was waste from an industrial PET recycling facility. It is thought that a limited number of mutations in a hydrolase, such as PET hydrolytic cutinase, that inherently targets the natural aliphatic polymer cutin (waxy polymer that is one of two main components of the plant cuticle) may have resulted in enhanced selectivity for PET and led to the evolution of the PET degradation pathway in I. sakaiensis. Genomic analysis has shown that a genomic basis to support the metabolism of MHET analogs was established much earlier than when ancestral PETase proteins were incorporated into the pathway. PET enrichment in the habitat of I. sakaiensis is thought to have potentially promoted the selection of a bacterium that might have obtained the necessary set of genes for PET catabolism through lateral gene transfer.
Other Plastic-Eating Bacteria
Plastics have mainly been introduced since the 1960s. Given the relatively few decades since these polymers became available and widespread, nature has only had a very short time to evolve highly active enzymes. In general, it is thought that the microbial degradation of human-made polymers is a very slow process. The difficulty with the degradation of plastics by microbes mainly stems from the high molecular-weight of the polymers, strong Carbon-Carbon bonds and the extremely hydrophobic surface of plastics, which is very difficult to attack by enzymes. Nonetheless, a number of bacteria and other microbes have been reported to be able to degrade a variety of plastics(polymers and/or oligomers) or contain enzymes that can.
As discussed earlier, researchers have discovered and characterized enzymes from bacteria other than I. sakaiensis that are capable of breaking down PET. Currently, only a few bacteria (and fungi) have been described to be able to partially degrade PET to oligomers or monomers and all known PET hydrolases have relatively low turnover rates. PETases (PET hydrolases - PET hydrolyzing enzymes) represent the best-studied class of enzymes with respect to the hydrolysis of synthetic polymers. Interestingly, the trait for PET degradation appears to be limited to a few bacterial phyla and is mostly found in bacterial isolates that are members of the Gram-positive phylum Actinobacteria. Bacteria that have been found to contain PET hydrolases enzymes include Thermobifida fusca, Bacillus subtilis and species from the genera Thermomonospora. However, none of them have been reported to contain MHETase, the enzyme that breaks down the monomers of PET after it is degraded by a PETase. Overall, the I. sakaiensis PETase and MHETase enzymes are the best-studied models for PET degradation and it seems that they are the most potent and possibly useful as well.
Another plastic polymer bacteria have been shown to degrade is polyurethane(PUR/PU). There are a number of different types of polyurethane polymers, but microbes act on only those that have ester links. Although ether linked polyurethane plastics exist, it seems that no enzymes capable of acting on polyurethane ethers have been described. With respect to bacteria capable of degrading PUR, Gram-negative Betaproteobacteria from the genus Pseudomonas have been most frequently linked with PUR activities. One Pseudomonas species that has been studied for its PUR-degrading activity is able to grow on a PU-diol solution, a polyurethane oligomer solution, and use it as its sole source of carbon, energy and nitrogen. This bacterial strain was obtained from soil samples and is capable of degrading both, an oligomeric PU and a PU building block(monomer). While the list of PU-active bacteria is steadily increasing, various fungal species have also been identified as PU degraders.
Polyethylene(PE) has also been associated with microbial degredation. Research performed in polyethylene biodegradation, both with pure strains and complex microbial communities has proved that biodegradation of this material, although slow, is actually happening in nature. Possible PE degradation has been affiliated with a surprisingly large number of bacterial genera among which are the Gram-negative species in the genera Pseudomonas, Ralstonia, and Stenotrophomonas and also many Gram-positive taxa. A few studies have also linked PE-degrading microbes with the complex gut microbiomes of invertebrates. One such study indicated that during short-term exposure, the intestinal microbiome of the larvae of G. mellonella (a greater wax moth) is intricately associated with polyethylene biodegradation in Vivo. The study identified microorganisms in the genus Acinetobacter that appeared to be involved in this biodegradation process. A number of fungal genera have also been affiliated with assumed PE degradation.
Yet Another plastic that has been targeted for bacterial degradation is polyamide. Polyamide(PA) is a polymer of repeating units of aliphatic, semiaromatic, or aromatic molecules linked via amide bonds. Because the monomers for making this polymer can be very versatile, there are many different types of synthetic polyamides, with the most popular being nylon and Kevlar. Although no microorganisms capable of fully degrading the intact high-molecular-weight polymers have been reported, several studies are available on bacteria acting on either linear or cyclic nylon oligomers with short chain lengths. Examples include Arthrobacter sp. and Pseudomonas aeruginosa. The only enzyme that has been reported to act on high-molecular-weight nylon fibers so far originated from a white rot fungus. Some Pseudomonas species have also been reported to utilize 6-aminohexanoate-dimers, oligomers of polyamide, as a sole carbon and nitrogen source.
Polystyrene(PS), a synthetic polymer widely used for packaging industries and many daily use articles, has also been a target of possible bacterial degradation. Unfortunately, much like polyamide, there is no known bacterial enzyme that can degrade the high molecular-weight polystyrene polymer. Styrene itself is able to be used as a carbon source for growth by some microorganisms. Styrene degradation in bacteria is well studied in Pseudomonas, Xanthobacter, Rhodococcus, Corynebacterium, and others. It appears to be a widespread metabolism. Rhodococcus ruber has been shown to form biofilms on PS and partially degrade it. A biofilter consisting of Brevibacillus sp. has been shown to remove a surprising 3 kg of styrene in a day. In addition, Several bacteria have been reported to form either alone or as members of consortium biofilms on polystyrene films and particles, thereby degrading the polymer.
In sharp contrast to the huge global production rates of polypropylene and polyvinyl chloride(PVC), hardly any information is available on microbial degradation of either of these important polymers. Though there are a very few reports that describe the degradation of these polymers based on weight loss and using mixed species microbial communities have been published, it is likely that these reports were in part misled by the degradation of the chemical additives rather than the polymer in their cultures. As a result, no defined enzymes or pathways that are responsible for the degradation of either of these two high molecular-weight polymers are yet known.
Arctic microorganisms may have unique potential for biodegradation of plastics due to the environmental conditions of polar oceans, which differ from other marine ecosystems. Bacteria from these regions respond quickly to changing environmental patterns. Although there isn’t much research conducted on the interactions between plastic and marine microbiota, the growing amount of plastic waste might force the microorganisms in these environments to adapt to new substrates. Thus, these organisms and their metabolism are prime area for future research on biodegradation of plastics. The table to the right lists some microorganisms isolated from cold environments and able to degrade synthetic polymers(plastics).
Mechanisms of Degradation
Understanding the mechanisms by which bacteria and other microbes or their enzymes degrade plastic polymers or oligomers can lead to the identification of important enzymes involved in the processes which can be targeted for biotechnological engineering to lead to greater efficiency in microbial degradation of plastics, recycling of plastics and other possible applications for these microbes and their enzymes.
One of the most well-studied mechanisms of biodegradation of plastics is the pathway for PET catabolism in I. sakaiensis. It is thought that I. sakaiensis first excretes PETase enzymes (classified as esterase) from the cells onto PET surfaces. Appendages that grow extracellularly might be involved in the delivery of PETase onto PET surfaces. Extracellular PETase then hydrolyzes PET to produce MHET(monoester of ethylene glycol and TPA, both monomers of PET) as the major product and TPA(terephthalic acid) as a minor. The PET hydrolysis products are then transported into the periplasmic space through an outer membrane protein such as porin. MHETase, predicted to be an outer membrane-anchored lipoprotein, hydrolyzes MHET into TPA and EG(ethylene glycol). TPA is taken up into the cytoplasm through the TPA transporter coupled with TPA-binding protein and then integrated via protocatechuic acid (PCA) to the tricarboxylic acid (TCA) cycle. Ethylene glycol is metabolized via glyoxylic acid to the TCA cycle.
Interestingly, the expression of the PETase gene was dramatically upregulated in the presence of PET (but not TPA) in a culture of I. sakaiensis, raising the question of which molecule(s) induces its expression. However, TPA does upregulate the expression of a gene cluster that is highly identical with two TPA degradation gene clusters identified in Comamonas sp. strain E6. In other bacteria acting on PET,
Researchers have also proposed a degradation pathway for the oligomers of polyurethane by a Pseudomonas strain. This proposed pathway is summarized in the figure to the right. There a number of enzymes involved in this pathway. One of the first enzymes identified to act on PUR was the PueB lipase from Pseudomonas chlororaphis, a different Pseudomonas species. This organism codes for at least one additional enzyme active on PU, which was designated PueA. Both enzymes are lipases (which usually catalyze the ester-linked lipids in other cells) and similar to PET degradation with microbes, PU is degraded by the secreted hydrolases, and the degradation is tightly regulated. As mentioned previously, enzymes and microbes described as capable of degrading organisms were all acting on ester-linked PU. There have yet to be enzymes described to act on polyurethane ethers in the scientific literature.
To date, no microorganisms capable of degrading the intact high-molecular-weight polyamide polymer have been reported, but there are many bacteria that act on the oligomers of polyamide. Three main enzymes have been reported as essential for the initial hydrolysis of cyclic and linear 6-aminohexanoate oligomers. The first one is a cyclic-dimer hydrolase (NylA), the second a dimer hydrolase (NylB), and the third an endo-type oligomer hydrolase (NylC). Once the oligomers are hydrolyzed, the monomers are metabolized by different aminotransferases.
As with polyamides, there are no known microorganisms capable of degrading the high-molecular-weight polystyrene polymer and neither are there any enzymes, but there are many microbes that degrade the oligomers of the plastic. Under aerobic conditions, styrene is oxidized by two different pathways. The first one involves attacking the vinyl side chain and the second one is through attacking a rather nonspecific aromatic ring, thereby forming primarily the intermediates 3-vinylcatechol, phenylacetic acid, and 2-phenylethanol. These intermediates are channeled into the Krebs cycle after ring cleavage. The degradation of the vinyl side chain involves the action of three key enzymes, a styrene monooxygenase complex(styA and styB), a styrene oxide isomerase(styC), and a phenylacetaldehyde dehydrogenase(styD). The respective genes for side-chain oxygenation are frequently located in a single conserved gene cluster, often designated styABC(D). The styrene monooxygenase attacks the vinyl side chain to release epoxystyrene, which is then subjected to isomerization to form phenylacetaldehyde. Phenylacetaldehyde is then oxidized to phenylacetic acid through the involvement of a dehydrogenase. In P. putida, the phenylacetic acid is activated to phenylacetyl-coenzyme A (CoA) and then subjected to β-oxidation to yield acetyl-CoA, which is directly fed into the Krebs cycle. The expression of the conserved cluster is regulated through either a two-component regulatory system or LysR-type regulators.
Research performed on PE degradation by microbes so far is mainly of descriptive nature, with a few studies devoted to polyethylene degradation mechanisms or the isolation of enzymes belonging related to this process. However, these findings are limited and further evidence is required to identify the complete mechanisms for polyethylene degradation. Similarly, the few studies that describe the degradation of polyvinyl chloride and polypropylene by microbial communities do not detail the enzymes and pathways involved in the process.
Significance, Possible Applications and Limitations
There are many different ways plastic-degrading bacteria can be applied to improve plastic recycling or decomposition and decrease or curb pollution. Current possible applications of microbial degradation of plastics are limited, but these microbes may eventually be used to completely degrade certain plastic polymers or their oligomers and monomers. For example, The assimilation of PET by I. sakaiensis bacteria may be advantageous for removing this plastic material from the environment. Plastic-degrading microbes could also be applied in the recycling process. In PET degradation, if the terephthalic acid could be isolated and reused, this could provide huge savings in the production of new polymer without the need for petrol-based starting materials.
Another potential route of application is the isolation of the genes encoding enzymes for biodegradation which can then be integrated into common production strains via metabolic engineering or the use of enzyme cascade systems. Alternatively, genetic sequences of these enzymes could be used to mass-produce the enzymes themselves and use them to directly degrade plastic polymers. Furthermore, engineering microorganisms that would produce high-value compounds from plastic waste is a future challenge and would contribute to an improved circular use of plastics. Monomers and oligomers formed after the degradation could be used to build value-added products or even new polymers that are biodegradable. In addition, the development of highly active enzymes to be used textile industries and in detergents(cellulase is already currently used as one of the additives to detergents for cotton fibers) could already significantly reduce annual plastic pollution.
The uniquely cold-adapted enzymes of polar microorganisms provide numerous opportunities for biotechnological exploitation and give new insights into a wide range of applied issues such as plastic pollution. Currently, enzymes from psychrophilic microorganisms are raising interest for many industrial applications due to ongoing attempts to decrease energy demand. The lower temperature needed for growth at which enzymatic activity is maintained may be a huge advantage in the degradation process due to reduction of electric energy usage for heating.
There are many limiting factors in the application of plastic-degrading bacteria. Firstly, microbial plastic degradation of intact high-molecular-weight polymers seems to be limited to only polyethylene terephthalate. The microbial mechanisms that degrade other plastics are only limited to breaking down oligomers and monomers. And even with PET degradation the crystallinity and durability of the intact polymer limits the process. This is also often true for many other bacterial mechanisms for breaking down plastics. Another limiting factor that needs to be improved upon is bacterial survivability in plastic polluted environments. With I. sakaiensis, headway has already been made as genetic engineering has enabled the bacterial to survive in usual areas where plastic waste is located so that the bacteria can degrade the plastic waste optimally. The turn over rate of enzymes involved in plastic degradation and the overall rate of plastic degradation by microorganisms also needs to be improved before microbes and their enzymes can be applied to curb plastic pollution. Currently, the majority of bacteria that degrade plastics take as much as several weeks to fully or substantially break down small amounts of plastic films. Again, important headway is being made on this front with the bacterium I. sakaiensis of which the PETase enzyme was recently genetically modified to increase degradation activity by 14-fold at 40 °C.
It is important to note that since commercially available polymers and films are often used as substrates, they contain additives, plasticizers, and other biodegradable impurities (for example, phthalates), which are much more easily broken down than the actual backbone. This, therefore, interferes with the results studies show for plastic degradation by microbes or their enzymes and frequently leads to the identification of false positives. Also, often the enzyme activities that are reported are based on clearing zones in agar plates. However, these assays are not fully reliable. For these reasons, the overall methodology linked to the analysis of microbial plastic degradation needs to be standardized and optimized.
All this information about plastic-degrading bacteria points to the untapped potential of bacteria and their enzymes in curbing and decreasing plastic pollution in different natural environments. More research needs to be done to identify the enzymes, mechanisms, and especially microbial interactions involved in biodegradation. This can go a long way to improve the microbial degradation of plastics and lead to refined processes for applications. Currently, possible prime research areas include investigation of the degradation of plastics by polar microbes, elucidating microbial interactions involved in the degradation of different plastic polymers, and developing better methods to properly measure the amount of plastics broken down. Another area of future research that looks promising is the genetic modification of I. sakaiensis’ PETase enzyme to yield a more efficient hydrolase. At this time, the most effective way to break down plastics involves exposure to UV light together with mechanical disruption caused by waves and winds or grinding on marine rocks and sediments, which eventually breaks larger plastics into smaller pieces of micro- and nanoplastics. This method has its own limitations (including not being environmentally friendly) and microbial degradation of plastics may well be the method of choice in our future endeavors to recycle and/or break down the substantial amount of plastics already polluting almost all of the world’s natural environment.
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