Biocatalysis as a green route for recycling the recalcitrant plastic polyethylene terephthalate.

Biocatalysis can enable a closed-loop recycling of post-consumer PET waste.

Introduction

The global production of fossil‐based plastics has grown more than 20‐fold since 1964 to 322 million tons in 2015, and a slowdown of this rate is not expected (Ellen MacArthur Foundation and World Economic Forum, 2014; PlasticsEurope, 2016). Many materials derived from synthetic polymers have already replaced their natural counterparts in all areas of human life. The majority of plastics are short‐lived products which are disposed within 1 year after manufacture. However, only 14% of plastic packaging materials used worldwide is currently collected for recycling while another 14% is incinerated for energy recovery (Ellen MacArthur Foundation and World Economic Forum, 2014). The remaining 72% of plastic packaging is not recovered with 40% land filled and 32% estimated to completely escape the collection system. This part of plastic waste ends up in diverse natural habitats, especially in oceans where it can cause serious environmental damages (Andrady, 2015; Jambeck et al., 2015). Therefore, innovative technologies to improve the recycling of plastics and to reduce the consumption of non‐renewable fossil feed stocks are required.

Polyethylene terephthalate (PET) is the most widely used synthetic polyester. It is a thermoplastic of high‐molecular‐weight composed of terephthalic acid (TPA) and ethylene glycol (EG). PET can exist as both an amorphous and a semi‐crystalline polymer (Webb et al., 2013). Owing to its excellent physical and chemical properties, PET finds numerous applications as textile fibres, packaging materials and beverage bottles. PET is generally referred to as ′polyester′ in the textile industry which consumes the majority of the PET produced globally. In 2014, 49.2 million tons of PET fibres was produced worldwide (Fiber Economics Bureau, 2015). In 2015, the global production of PET resins was 27.8 million tons which was dominantly used for the manufacture of packaging materials and beverage bottles (Plastic Insight, 2016). Almost half of the postconsumer PET bottles worldwide are collected for mechanical recycling to produce polyester fibres (Ellen MacArthur Foundation and World Economic Forum, 2014).

Polyethylene terephthalate made from renewable biomass (bio‐PET) is becoming of industrial interest lately. EG derived from sugarcane ethanol (Tsiropoulos et al., 2015) and TPA derived from sugar beet paraxylene (Collias et al., 2014; Smith, 2015) can be utilized to replace their fossil‐based counterparts to produce bottle‐grade PET. Although fossil feedstocks can be saved by the commercialization of bio‐PET bottles, the challenges for their recycling remain as their recalcitrant properties are the same as those of petroleum‐derived PET bottles (Chen et al., 2016).

Microbial polyester hydrolases can degrade PET

Polyethylene terephthalate has been previously considered as recalcitrant to biological degradation. However, fungal and bacterial polyester hydrolases exhibiting hydrolytic activity against PET films and fibres have been reported recently (Zimmermann and Billig, 2011; Chen et al., 2013; Wei et al., 2014c; Wei and Zimmermann, 2017) (Table 1). Among the reported microbial polyester hydrolases, cutinases and their homologues have shown the greatest potential for PET hydrolysis (Müller et al., 2005; Ronkvist et al., 2009; Herrero Acero et al., 2011; Wei et al., 2014c). Cutinases are enzymes capable of hydrolysing cutin, an aliphatic polyester found in the plant cuticle (Kolattukudy, 1981; Heredia, 2003). Müller et al. (2005) first reported that low‐crystalline (lc) PET film with 10% crystallinity prepared by melt pressing of PET beverage bottles could be degraded by the polyester hydrolase TfH from Thermobifida fusca DSM43793 at 55°C. However, a reaction time of 3 weeks with an exchange of the enzyme solution every week was required to achieve a weight loss of approximately 50% of the PET film. Ronkvist et al. (2009) reported a 97 ± 3% weight loss of an lc PET film with 7% crystallinity within only 96 h of reaction at 70°C with the fungal cutinase HiC from Thermomyces (formerly Humicola) insolens. A comparable degradation performance with amorphous PET materials has been also demonstrated with LC‐cutinase at 70°C (Sulaiman et al., 2014), a polyester hydrolase homologous to TfH identified by a metagenomics approach (Sulaiman et al., 2012), and by a variant of TfCut2 at 65°C, derived from T. fusca KW3 differing only in two amino acid residues from TfH (Wei et al., 2016).

Table 1

Microbial polyester hydrolases reported to cause significant weight losses of PET materials

Enzyme	Source	Reaction conditions		Weight loss	Crystallinity of PET	PET source and preparation	References
		Temperature	Time
TfH	Thermobifida fusca DSM43793	55°C	3 weeks	≈ 50%	10%	Melt pressing of a beverage bottle (Granini AG, Nieder‐Olm, Germany)	(Müller et al., 2005)
TfH	Thermobifida fusca DSM43793	55‐65°C	48 h	≤ 14%	Not reported	Amorphous PET film (Goodfellow GmbH, Bad Nauheim, Germany)	(Then et al., 2015)
BTA‐2				≤ 4%
Tfu_0882	Thermobifida fusca YX	55‐65°C	48 h	≤ 5%			(Then et al., 2015)
TfCut1	Thermobifida fusca KW3	55‐65°C	48 h	≤ 11%			(Then et al., 2015)
TfCut2				≤ 12%
Variants of TfCut2	Thermobifida fusca KW3	65‐80°C	48 h	≤ 25%			(Then et al., 2015, 2016)
		65°C	50 h	≤ 45%			(Wei et al., 2016)
A double mutant of Cut190	Saccharomonospora viridis AHK190	63°C	3 days	13.5 ± 0.5%	Not reported	Amorphous PET film (Goodfellow Cambridge, Ltd., Tokyo, Japan)	(Kawai et al., 2014)
				27 ± 1%		Amorphous PET film (Sanwa Supply Inc., Okayama, Japan)
LC‐cutinase	Metagenome from plant compost	50‐70°C	24 h	≤ 25%	Not reported	Amorphous PET film (Sanwa Supply Inc., Okayama, Japan)	(Sulaiman et al., 2014)
HiC	Thermomyces (formerly Humicola) insolens	70°C	96 h	97 ± 3%	7%	Amorphous PET film (Goodfellow Cambridge, Ltd.)	(Ronkvist et al., 2009)

Microbial polyester hydrolases can enable a complete depolymerization of lc PET into its monomers TPA and EG that can be reused for the synthesis of virgin PET (Fig. 1). Recycled TPA can also be employed for the synthesis of products with significantly added value such as metal‐organic frameworks (MOF) (Manju et al., 2013). Enzymatically recycled PET monomers may also become substrates for Pseudomonas putida cell factories to produce biodegradable, value‐added bioplastics such as polyhydroxyalkanoates (PHA) (Wierckx et al., 2015).

Figure 1

Biocatalysis for a closed‐loop recycling of postconsumer PET. TPA, terephthalic acid; EG, ethylene glycol; MOF, metal‐organic framework; PHA, polyhydroxyalkanoate.

The PET hydrolases Thc_cut1 from T. cellulosilytica (Pellis et al., 2016a) and HiC (Hunsen et al., 2008a,b) have been shown to efficiently synthesize aliphatic polyesters as well as to catalyse a ring‐opening polymerization of lactones. These enzymes could therefore be also employed for the synthesis of polyesters from recycled monomers and open up avenues for novel closed‐loop recycling technologies of postconsumer PET waste based on biocatalysis (Fig. 1).

Chemical methods applied for the depolymerization of PET require high temperatures and the use of toxic chemicals (Awaja and Pavel, 2005). In contrast, a biocatalytic degradation of PET is providing a green technology performed at mild temperature and pH conditions in the absence of hazardous chemicals (Wei and Zimmermann, 2017). PET hydrolases show a high specificity for the ester bonds in PET. Hence, enzymatic degradation of PET in composite materials such as PET‐polyethylene blends, metallized PET‐based packaging films or in textiles containing PET could open up further opportunities to recover value from plastic waste using a biocatalytic approach (Gallagher, 2003).

Key challenges for biocatalytic PET recycling

The efficient enzymatic hydrolysis of PET by polyester hydrolases still presents a number of challenges for the further development of a biocatalytic PET waste recycling technology. The presence of the aromatic building block TPA in PET provides stiffness to the polymer chain and is a major reason for its low biodegradability (Marten et al., 2003, 2005). As a result, PET exhibits a glass transition temperature (T g) of above 70°C and a melting point (T m) of over 230°C (Alves et al., 2002). This prohibits the application of enzymes at the T m of PET. However, at its T g, the amorphous regions of PET become more flexible and accessible to enzymatic attack. Indeed, enzymatic hydrolysis performed at a reaction temperature close to its T g resulted in an efficient degradation of lc PET films (Ronkvist et al., 2009). As a consequence, polyester hydrolases for the degradation of PET need to exhibit thermal stability properties at elevated temperatures of ≥ 70°C.

Computational simulation using structural models of polyester hydrolases from Thermomonospora curvata DSM43183 revealed that their flexible catalytic triad is more prone to unfold at high reaction temperatures near T g of PET (Wei et al., 2014b). This unfolding process can be suppressed when Ca2+ or Mg2+ bind to the potential metal ion binding site of TfCut2, a homologous polyester hydrolase (Then et al., 2015). Indeed, the thermal stability and hydrolytic activity against PET of polyester hydrolases from T. alba AHK119 (Thumarat et al., 2012), T. fusca KW3, YX and DSM43793 (Then et al., 2015) as well as from Saccharomonospora viridis AHK190 (Kawai et al., 2014) showed a positive correlation with the presence of Ca2+ and Mg2+ in the reaction medium. The replacement of the metal ion binding site with a disulfide bridge allowed the hydrolysis of PET films by TfCut2 variants at reaction temperatures up to 80°C independent of Ca2+ (Then et al., 2016). Phosphate anions also had a stabilizing effect on bacterial polyester hydrolases and increased their PET degradation performance (Schmidt et al., 2016).

Among the bacterial polyester hydrolases, the metagenome‐derived LC‐cutinase has shown an outstanding thermal stability at 70°C and superior hydrolytic activity against lc PET (Sulaiman et al., 2014). Thus, the microbial biodiversity in environmental samples may allow the identification of further promising polyester hydrolases by metagenomic approaches. Moreover, protein engineering focusing on key amino acid residues involved in the thermostabilization of polyester hydrolases can be expected to provide further biocatalysts as candidates for industrial PET recycling processes. For these purposes, the availability of high‐throughput screening methods plays an important role for the rapid detection of novel PET‐hydrolysing enzymes from the environment and their variants created by genetic engineering (Wei et al., 2012).

Recently, a polyester hydrolase exhibiting PET‐hydrolysing activity at 30°C was identified from Ideonella sakaiensis 201‐F6, isolated from a PET bottle recycling site (Yoshida et al., 2016). However, due to the inertness of PET at this temperature as a result of its intrinsic polymer properties, a biocatalytic recycling at low reaction temperatures is unlikely to be feasible.

The enzymatic hydrolysis of PET is a surface erosion process (Müller, 2006). The interaction of the biocatalyst with the polymeric substrate therefore plays an essential role for an efficient hydrolysis performance. Crystal structural analysis of several bacterial polyester hydrolases revealed the location of the catalytic triad in a surface groove surrounded by several hydrophobic amino acids (Kitadokoro et al., 2012; Roth et al., 2014; Sulaiman et al., 2014). This structural feature has been considered as crucial for the accommodation of a large polymeric substrate with hydrophobic properties such as PET (Herrero Acero et al., 2011; Kitadokoro et al., 2012). The adsorption of the polyester hydrolases to the polyester surface could be augmented by the presence of exogenous binding modules. The fusion of the polymer binding module from a PHA‐hydrolysing enzyme or of fungal hydrophobins to Thc_cut1 resulted in a significantly enhanced adsorption and hydrolytic activity on the surface of PET films (Ribitsch et al., 2013, 2015).

Bis(2‐hydroxyethyl) terephthalate (BHET) and mono‐(2‐hydroxyethyl) terephthalate (MHET) are low‐molecular esters of TPA and EG that are released during the enzymatic degradation of PET (Vertommen et al., 2005; Wei et al., 2012). These intermediate hydrolysis products have been shown to inhibit the activity of the polyester hydrolases TfCut2 and LC‐cutinase (Barth et al., 2015a, 2016). MHET has a high affinity to the substrate binding pocket of TfCut2 and is hydrolysed at a very low rate. This inhibitory effect could be efficiently reduced using an ultrafiltration membrane reactor (Barth et al., 2015b). Thereby, inhibitory hydrolysis products did not accumulate in the enzyme reactor and could be easily collected together with TPA and EG. In another strategy to remove inhibitory intermediate hydrolysis products, the immobilized carboxylesterase TfCa from T. fusca KW3 (Billig et al., 2010; Oeser et al., 2010) with high activity against low‐molecular PET oligomers was employed together with the polyester hydrolases TfCut2 or LC‐cutinase in an enzyme reactor to hydrolyse lc PET films (Barth et al., 2016). As a result, an up to twofold increased yield in degradation products could be obtained. Similarly, lipase CalB also facilitated the degradation of PET catalysed by the fungal polyester hydrolase HiC (Carniel et al., 2016). A 7.7‐fold increase in the yield of TPA was obtained due to the removal of MHET hydrolysed by CalB. By these dual‐enzyme systems, PET monomers can be obtained in a one‐pot process in high purity simplifying their downstream processing.

The product inhibition of the polyester hydrolase TfCut2 by MHET could also be relieved by a single site substitution of a key amino acid residue involved in the interaction with an oligomeric PET model compound (Wei et al., 2016). A 2.7‐fold higher weight loss of lc PET films could be obtained with this enzyme variant than with the wild type TfCut2.

Beverage bottles and fibres with a high degree of crystallinity of above 30% represent the most abundant types of postconsumer PET materials and can presently not be efficiently hydrolysed in an enzymatic process (Wei and Zimmermann, 2017). Compared to a biaxially oriented PET film with 35% crystallinity, a lc PET film with 7% crystallinity was hydrolysed by HiC at a 25‐fold higher rate at 70°C (Ronkvist et al., 2009). While an approximately 42% weight loss of lc PET film was obtained with a TfCut2 variant within 50 h at 65°C, PET fibres with a higher degree of crystallinity of above 30% were only partially hydrolysed (Wei et al., 2016). Bottle‐grade PET also showed a low enzymatic degradability. About two orders of magnitude lower amounts of degradation products were released from this material compared to from amorphous PET with a degree of crystallinity of 1.9% at the same reaction conditions (Yoshida et al., 2016).

A mechanical pretreatment of postconsumer PET materials may also be necessary to enable a complete enzymatic hydrolysis by enlarging the available surface area for access to the enzymes. Reducing various PET materials to particles with a diameter of about 100 nm significantly increased their degradation by TfCut2 (Wei et al., 2014a). The Thc_cut1 catalysed degradation of lc PET powders also released higher amounts of degradation products than from PET films at the same reaction condition as a result of the increased surface area (Pellis et al., 2016b). PET particle sizes between 0.25 and 0.5 mm obtained by micronization of different postconsumer beverage bottles were shown to be more susceptible to an enzymatic hydrolysis by Thc_cut1 as a result of the increased accessible surface area for the enzyme (Gamerith et al., 2017).

Concluding remarks

Microbial polyester hydrolases have shown their potential in the biocatalytic depolymerization of PET. For an efficient degradation of postconsumer PET plastic waste in an industrial process, the performance of the enzymes still requires substantial improvements. The discovery and engineering of novel polyester hydrolases exhibiting specific catalytic properties towards high crystalline and bottle‐grade PET materials therefore remain key challenges. This can be achieved by applying microbial biotechnology methodologies for identifying novel enzymes from the environment exploiting microbial biodiversity and by generating powerful variants by protein engineering using rational design and enzyme evolution strategies. If successful, these enzymes can make an important contribution towards a future sustainable closed‐loop plastic recycling industry.

Conflict of interest

None declared.