NC State
Hubbe, M. A., Lavoine, N., Lucia, L. A., and Dou, C. (2021). "Formulating bioplastic composites for biodegradability, recycling, and performance: A Review," BioResources 16(1), 2021-2083.


Society’s wish list for future packaging systems is placing some daunting challenges upon researchers: In addition to protecting contents during storage and shipping, the material must not bio-accumulate, and it should be readily recyclable by using practical processing steps. This article considers strategies employing bio-based plastics and reviews published information relative to their performance. Though bioplastics such as poly(lactic acid) (PLA) and poly(hydroxybutyrate) (PHB) can be prepared from plant materials, their default properties are generally inferior to those of popular synthetic plastics. In addition, some bioplastics are not easily decomposed in soil or seawater, and the polymers can undergo chemical breakdown during recycling. This review considers strategies to overcome such challenges, including the use of biodegradable cellulose-based reinforcing particles. In addition to contributing to strength, the cellulose can swell the bioplastic, allowing enzymatic attack. The rate-controlling step in bioplastic degradation also can be abiotic, i.e. not involving enzymes. Though there is much more work to be done, much progress has been achieved in formulating bioplastic composites that are biodegradable, recyclable, and higher in strength compared to the neat polymer. Emphasis in this review is placed on PLA and PHB, but not to the exclusion of other bioplastic matrix materials.

Download PDF

Full Article

Formulating Bioplastic Composites for Biodegradability, Recycling, and Performance: A Review

Martin A. Hubbe,*,a Nathalie Lavoine,a Lucian A. Lucia,a and Chang Dou b

Society’s wish list for future packaging systems is placing some daunting challenges upon researchers: In addition to protecting contents during storage and shipping, the material must not bio-accumulate, and it should be readily recyclable by using practical processing steps. This article considers strategies employing bio-based plastics and reviews published information relative to their performance. Though bioplastics such as poly(lactic acid) (PLA) and poly(hydroxybutyrate) (PHB) can be prepared from plant materials, their default properties are generally inferior to those of popular synthetic plastics. In addition, some bioplastics are not easily decomposed in soil or seawater, and the polymers can undergo chemical breakdown during recycling. This review considers strategies to overcome such challenges, including the use of biodegradable cellulose-based reinforcing particles. In addition to contributing to strength, the cellulose can swell the bioplastic, allowing enzymatic attack. The rate-controlling step in bioplastic degradation also can be abiotic, i.e. not involving enzymes. Though there is much more work to be done, much progress has been achieved in formulating bioplastic composites that are biodegradable, recyclable, and higher in strength compared to the neat polymer. Emphasis in this review is placed on PLA and PHB, but not to the exclusion of other bioplastic matrix materials.

Keywords: Poly(lactic acid); Poly(hydroxybutyrate); Cellulosic reinforcement; Decomposition; Engineered biodegradation; Lipase; Cellulase

Contact information: a: Department of Forest Biomaterials, North Carolina State University, Campus Box 8005, Raleigh, NC, 27695-8005; b: Advanced Biofuels and Bioproducts Process Development Unit, Lawrence Berkeley National Laboratory, Berkeley, CA, 94720; * Corresponding author:



Plastic materials are playing an ever-increasing role in modern society. A plastic can be defined as a polymeric material that can be formed by flow, which often involves cycles of melting and then cooling in order to optimize the final product qualities. The most widely used plastics are petroleum-derived synthetic polymers, which are meltable and hydrophobic. They include polyethylene, polypropylene, polyamides, and polyesters. Environmental damage occurs when such plastics are discarded as litter after a single use (e.g., as food packaging). The non-biodegradable nature of typical synthetic plastics means that they tend to accumulate in ecosystems, including in the ocean, where they interfere with aquatic life (Cózar et al. 2014; Eriksen et al. 2014; Jambeck et al. 2015; The Pew Charitable Trust 2020).

This article reviews studies that explore potential ways to replace petroleum-based plastics with bio-based plastics. Emphasis here is on hard plastics that can be used for such items as bottles, cups, and components of various devices. Efforts to replace petroleum-based plastics in such applications face three serious challenges: first, bio-based systems will need to be biodegradable under typical conditions prevailing not only in soils, but also in the sea; second, public pressure will demand them to be recyclable multiple times, which may be achievable by melting and compounding, and third, the bio-based systems will need to meet rigorous performance standards related to strength, toughness, and resistance to fluids, etc. Costs of bio-plastics are a concern, since market forces are likely to be a major factor governing the potential volume of implementation.

Of the challenges just mentioned, the goal of full, undisputed biodegradability is perhaps the most daunting. Biodegradability will be defined here as the ability of a material to be broken down by living organisms into simple molecules such as water, carbon dioxide, methane, and other compounds that can be utilized by living organisms. Leja and Lewandowicz (2010), further defined biodegradation as involving the metabolism of microorganisms such as bacteria, fungi, and algae. According to ISO Standard 14855-1:2005, a biodegradable plastic is one that attains 90% mineralization of organic carbon when exposed to defined conditions. By contrast, thermal decomposition is an example of a breakdown mechanism of bioplastic that does not depend on microorganisms or the enzymes produced by them (Petinakis et al. 2010). As noted by Shen et al. (2009) and Lavoine and Bras (2016), there is a societal preference for packaging materials that are both biodegradable and derived from plant materials, i.e. bio-based.

The term biodegradability encompasses a wide variety of enzymatic and/or chemical processes induced by living organisms, whose efficiencies are influenced to a great degree by the state of the local environment of the living organism. For example, rates for biodegradation can vary widely because of water and soil conditions. These rates are therefore not a constant for a particular substrate. Furthermore, the path of biodegradation is dependent on oxygen, leading to aerobic or anaerobic processes (Jørgensen 2008). A series of biodegradation studies have been completed that collected data on the nature of the biodegradation for the most common synthetic plastics (Table 1). It should be noted that for each of the studies, there were numerous sources and types of plastics that greatly influenced the overall incubation times, weight losses, and degradation products. For example, Shah et al. (2008), found that the rate of biodegradation of polyurethane (PUR) under the same conditions as those by Stepien et al. (2017) could be significantly reduced to 28 days when using a cocktail of bacteria (Bacillus sp. AF8; Pseudomonas sp. AF9; Micrococcus sp. 10; Arthrobacter sp. AF11; Corynebacterium sp. AF12). Through a natural evolutionary process, microorganisms can adapt their cocktail of enzymes to enable the biodegradation of diverse food sources, including plastics. For instance, researchers discovered a natural enzyme in a Japanese waste recycling center; the bacterium was able to efficiently degrade poly(ethyleneterephthalate) (PET) as a food source (Austin et al. 2018).

Table 1. Biodegradation of Synthetic Plastics under Specified Conditions and Microorganism

Key: PE = polyethylene; LDPE = low-density polyethylene; PS = polystyrene; PP = polypropylene; PVC = poly(vinylchloride); PUR = poly(urethane)

Table 2. Biodegradation of Bioplastics under Specified Conditions

Key: PLA = poly(lactic acid); PHA = poly(hydroxyalkanoate); PHB = poly(hydroxybutyrate)

Research on bioplastic biodegradation also has been conducted, and some results are listed in Table 2. What is noteworthy to observe between the bioplastics versus the synthetic plastics is that the incubation periods were similar, while resultant weight losses were only a little bit higher for bioplastics.

The fact that a certain polymer has been prepared from plant-based source materials does not imply that it is readily biodegradable (Payne et al. 2019). Rather, there appears to be a perverse inverse relationship between the ability of polymers to achieve high elastic modulus and melting point vs. their susceptibility to degradation at ambient temperature (Bikiaris 2013; Elsawy et al. 2017). A prime example is poly(lactic acid) (PLA), which has received attention as a leading candidate to substitute for synthetic polymers in applications requiring stiffness (Farah et al. 2016). Though some studies support the biodegradability of PLA under ideal composting conditions at relatively high temperatures (Kale et al. 2007a; Rudnick and Birassoulis 2011; Siracusa 2019), unmodified PLA generally cannot be regarded as biodegradable at room temperature or in typical ocean conditions (Emadian et al. 2017; Chamas et al. 2020). On the other hand, studies have shown that the properties of various plastics can be improved by judicious use of cellulose-based reinforcements, especially if something is done to improve the compatibility between the surfaces of the reinforcing particles and various hydrophobic matrix polymers (Hubbe and Grigsby 2020).

As will be shown in this review article, progress in achieving each of the three main goals – biodegradability, recyclability, and performance – already has been demonstrated. Such success often has been achieved by the use of reinforcing particles and various additives. Each modification adds to the complexity of the formulation. Formulation of a complex composite structure, especially if it needs to contain multiple additives to optimize multiple aspects of its performance, can make it more difficult to adjust the process to meet quality requirements. Thus, as has been found in other fields, complexity itself can be regarded as an additional challenge faced by innovators (Place et al. 2009; Geraldi et al. 2011).

Working Hypotheses

The premise of this review article is that the three goals of biodegradability, recyclability, and performance might be best met, or at least approached, by formulation of a composite system having a blend of ingredients. The biodegradability can be measured by published assays and standards (which are specified later in the article). The word recyclability, for the present discussion, will mean that the material can be melt-reprocessed and formed into successive generations of plastic material that can serve a similar function as in the first cycle. The word “performance” will be considered relative to common petroleum-based plastics such as polyethylene, polypropylene, and polystyrene, which constitute a substantial portion of non-biodegradable litter.

The following hypotheses are proposed here as a means of focusing attention on certain issues that will be considered in this article. Published evidence supporting or not supporting the hypotheses listed below will be considered in this article.

  1. Fiber-like or fibrillated cellulosic reinforcements have the potential not only to strengthen bioplastic matrix materials, but they also can provide a conduit to allow moisture and enzymes, etc., to gain access within the structure, promoting the possibility of biodegradation.
  2. The manner in which the surfaces of cellulosic reinforcements are treated or derivatized can provide not only an enhancement of blend compatibility and strength properties, but it also can provide a strategic weak link by which the structure may be later degraded by natural microbes and/or enzymes.
  3. The physical properties of the composite, as well as its recyclability and/or biodegradability, can be optimized by the selection and concentration of additives such as plasticizers, surfactants, and other bio-based polymers such as starch and its derivatives.
  4. The biodegradation of crystalline domains of a bioplastic matrix polymer such as PLA can be enhanced by including ingredients that contain carboxylic acid groups. Such materials may need to become intimately mixed during casting or compounding of the material.

The hypothesis statements listed above all deal with aspects of sustainability. A sustainable material ought to fulfil a useful purpose with a minimum of adverse impact on the environment. Polymeric products based on the use of plant-based materials and eco-friendly processing have the potential to reduce society’s dependence on fossil fuels (Kobayashi 2017). The importance of direct recycling of plastics is highlighted by the work of Souroudi and Jakubowicz (2013) and Cosate de Andrade et al. (2016). Their life cycle assessment studies showed that in the case of PLA, simple recycling of the used plastic, by means of melting and reforming into new products, had a lower adverse environmental impact than either chemical recycling (for instance to obtain lactic acid) or composting. Composting is often discussed as a suitable end-of-life fate for bioplastics, since by that means their organic content theoretically can contribute to amendment of soils (Payne et al. 2019). However, composting is only adoptable if the “recoverable” materials are susceptible to biological attack without compromising the composting ecosystem in which they are present. A compostable material offers a digestible substrate that does not kill the microorganisms directly or indirectly by virtue of its by-products. A life cycle study by Hermann et al. (2011) concluded that favorable results in terms of energy recovery could be achieved if a bioplastic is anaerobically degraded with recovery of methane gas, which can displace the use of fossil fuels. Regardless of what is planned for the end fate of a new generation of bioplastic materials, given the huge amounts of plastics that are ending up in natural waters and soils around the world, they must be biodegradable under the conditions that they are likely to encounter in outdoor and aquatic environments.

Layout of the Article

The main sections of this article are reflective of the three societal expectations for bioplastics, as mentioned earlier. However, to make that discussion more understandable for a wide audience, some critical background information is presented in the next main selection. After that comes a section discussing factors that have been reported to affect the rates of biodegradation of bioplastics and their composites or blends. The next main section has to do with the recycling of bioplastics, with emphasis on recycling of the plastic material into new generations of plastic material. Then the attention is turned to how to improve the strength and other physical attributes of bioplastics and their composites.

Earlier Reviews

Because of widespread concern about the fate and properties of plastics, including bioplastics, many review articles and chapters have been written that illuminate aspects of the topic. Selected works of this type are listed in Table 3. The present article focuses on opportunities to apply a variety of strategies to optimize not only the biodegradation, but also recyclability and strength-related properties.

Table 3. Review Articles and Chapters Dealing with Aspects of Bioplastics


Bioplastics as a Potential Path Forward

Certain bioplastics, when used alone, already have advanced a lot towards meeting society’s needs for biodegradability, recyclability, and strength. According to Emadian et al. (2017), bioplastics in general tend to be more expensive and lower in strength than their petroleum-based alternatives. Their redeeming feature is that they are predominantly polyesters. Ester bonds, in general, are expected to be susceptible to cleavage by enzymatic action. Esterases have evolved to convert polyesters to monomeric compounds. Their catalytic power can be quantified in terms of their catalytic acceleration kcat/ku, where ku is the rate constant of a nonenzymatic ester hydrolysis. For example, the value of catalytic acceleration for acetylchoinersterase, the enzyme necessary for support proper neuronal communication pathways, is 1013 (Harel et al. 1996). Such values are consistent with a high level of molecular recognition playing an essential role in the hydrolytic process.

Din et al. (2020) provide a quite comprehensive review of the most widely available bioplastics, i.e. poly(lactic acid) (PLA), polyhydroxyalkanoates, including poly(hydroxyl-butyrate) (PHB), polycaprolactone, thermoplasticized starch, and cellulose. Emadian et al. (2017) tabulate many studies in which the extents of biodegradation were reported as a function of conditions and time of contact with soil, composting, or exposure floating on the sea. Panchal and Vasava (2020) emphasized that there is an essentially infinite range of variants of biodegradable polymer materials that can be achieved by making adjustments of composition and conditions during synthetic steps. Thus, even if the presently available biopolymers and their blends or composites do not yet meet all of the hoped-for goals, there is reason to be hopeful that better formulations will continue to emerge during the course of research.

Chemistries of Bioplastics

PLA basics

The first type of bioplastic to be considered here will be PLA. Lactic acid, from which PLA is ultimately derived, can be generated as a byproduct of polysaccharides or sugars. The polymerization can take place under water-free conditions to yield a polymer having the repeat unit shown in Fig. 1. The most promising synthetic route involves dimerization into lactide with the loss of two water molecules, followed by polymerization in anhydrous media in the presence of tin octanoate as a catalyst (Omay and Guvenilir 2013; Castro-Aguirre et al. 2016). As shown, PLA is a linear polyester. Because the repeating unit lacks any charged groups or –OH groups, PLA can be regarded as hydrophobic, though less so than polyolefins such as polyethylene, polypropylene, or poly(ethylene terephthalate (PET). Especially when PLA is prepared with relatively high molecular weight and pure stereochemistry (Reeve et al. 1994), a melting point as high as 175 C can be achieved, which is exceptionally high among biopolymers (Bikiaris 2013). Under favorable conditions, superior optical and physical properties can be achieved (Miyoshi et al. 1996). Potentially disadvantageous traits of PLA can be listed as its brittle nature, low resistance to heat, and a slow rate of crystallization, the last of which means that PLA tends to fall short of its potential elastic modulus values (Elsawy et al. 2017). The limited tolerance for heating can lead to loss of molecular weight during melt-preprocessing (Farah et al. 2016). Though PLA can be regarded as not very compatible with cellulosic surfaces, it is not the worst case. The development of contact with cellulosic reinforcements with PLA is better than that between cellulosic surfaces and polyethylene or polypropylene (Mofokeng et al. 2012; Hubbe and Grigsby 2020).

Fig. 1. Main synthesis routes and structure of poly(lactic acid)

Another limitation of PLA, which will be covered in the next main section, is the lack of, or very slow rate of biodegradation at ambient temperatures (Karamanlioglu and Robson 2013; da Silva et al. 2019). Slow biodegradation, especially of the crystalline zones of PLA, appears to be the flip side of successful preparation of a dense, well-organized nanostructure. Although this is a bonus for its use in mechanically demanding applications, the presence of crystalline zones makes PLA more recalcitrant against biodegradation. In addition, the hydrophobic nature of PLA discourages the diffusion of water, ions, or enzymes into the interior of PLA.

Because optically pure PLA, e.g. poly(L-lactic acid), generally can develop higher crystallinity, melting point, and modulus values, it can be advantageous to use a fermentation route to obtain the starting lactic acid of high L-enantiomer purity (Abdel-Rahman et al. (2013). Singhvi and Gokhale (2013) have reviewed aspects of production of PLA from biomass. Cubas-Cano et al. (2018) reviewed the microbial aspects of lactic acid production, with emphasis on metabolic pathways and purification steps. In addition, as shown by Chambon et al. (2011), lactic acid can be obtained by hydrothermal degradation of cellulose.

PHB and other polyalkanoates

When the overarching goal is to find a biopolymer that can serve as a substitute for common petroleum-based polymers, the next most often considered option, after PLA, appears to be poly(3-hydroxybutyrate) (PHB), along with its copolymer with valeric acid (PHB-co-valerate) (Reddy et al. 2003). Unmodified PHB has been reported to be quite brittle, making it difficult to reprocess during melting and reforming (Soroudi and Jakubowicz 2013; Seggiani et al. 2015). PHB is derived when bacteria are allowed to thrive in a glucose-controlled environment and later experience nutrient deprivation, leading to carbon assimilation in the course of PHB production. This biomaterial and associated manufacturing expenditures deliver a much smaller ecological footprint than the petroleum analogues.

The copolymer of PHB with valeric acid has more favorable processing ability and is more suitable for simple recycling (Ariffin et al. 2010; Soroudi and Jakubowicz 2013; Lagazzo et al. 2019). Valeric acid (CH3(CH2)3COOH), which is also known as pentanoic acid, is a straight-chain low MW carboxylic acid that can be easily degraded. Favorable adhesion to cellulosic fibers with PHB-co-valerate was reported in a study of melt-compounding (Sanchez-Safont et al. 2016). Lagazzo et al. (2019) showed that composites formed with the copolymer and sisal fibers could be successfully melt-reprocessed three times, and there was less embrittlement compared to the unreinforced copolymer. Losses in molecular mass have been reported, in the course of melt-reprocessing; however, such losses did not prevent multiple recycling of the copolymer (Zaverl et al. 2012; Vandi et al. 2019). Yu et al. (2011, 2014a) and Srithep et al. (2013) reported that composites formed from PHB-co-valerate and nanofibrillated cellulose (NFC) showed earlier onset of crystallinity of the matrix phase, which contributed to more favorable physical properties. Relative to PLA, PHB-co-valerate has been reported to have a faster rate of biodegradation in sludge and in soil (Avella et al. 2000; Arcos-Hernandez et al. 2012). Soil biodegradation of PHB-co-valerate was favorably affected by the presence of wood fibers (up to 50 wt%), as a composite (Chan et al. 2019). The same study evaluated wood-PLA composites, and the biodegradation results were not as promising as for PHB-co-valerate. Weng et al. (2011) reported more rapid biodegradation of PHB that had been blended with either PHB-co-valerate or isomeric forms of PHB.

The copolymer also can be hydrolytically degraded, though not as favorably as in the case of PLA (Bonartsev et al. 2012a,b). Hassaini et al. (2017) observed improved physical properties of PHB-co-valerate composites formed with olive husk flour that had been hydrophobized with trimethoxy-octadecylsilane to render the reinforcing fibers more hydrophobic. Yatigala et al. (2018) similarly showed that addition of maleic anhydride during compounding improved the properties of several kinds of bioplastics, including PHB-co-valerate, with wood fiber reinforcement.

As shown in Fig. 2, PHB can be obtained in different isomeric forms, depending on the starting material and the synthesis route (Sastri 2010).

Fig. 2. Synthesis reactions and structures of two isomeric forms of poly(hydroxybutyrate)

Starch products

Starch products deserve to be mentioned here because they have potential for blending with hydrophobic bioplastics such as PLA. In that way, starch can play a role in formulations that substitute for commercial, petroleum-derived plastics. In the presence of optimized moisture content and temperature, it is possible to extrude starch as a thermoplastic polymer (Kalambur and Rizvi 2006; Elsawy et al. 2017; Khan et al. 2017; Din et al. 2020). Blends of PLA and thermoplasticized starch have been widely studied (Martin and Averous 2001; Ganjyal et al. 2007; Thongtan and Sriroth 2011; Nair et al. 2012; Mihai et al. 2014; Masmoudi et al. 2016; Lv et al. 2017; de Macedo et al. 2019; Turco et al. 2019). An especially attractive feature of starch, as a candidate for blending with other biopolymers, is its generally rapid biodegradation by amylase enzymes (Ganjyal et al. 2007; Tokiwa and Calabia 2007; Lu et al. 2009; Leejarkpai et al. 2011; Narayan 2012; Lv et al. 2017; Sohn et al. 2019; Ferreira et al. 2020).

Researchers have wondered why it has been possible, given the generally hydrophilic and water-soluble nature of starch, to achieve effective blends with biopolymers such as PLA. Lawton (1995) reported a surface energy of extruded and jet-cooked starch films of about 40 dynes/cm, which is moderately hydrophilic. Averous and Fringant (2001) found that addition of 10% polyester in a blend with starch yielded a much more hydrophobic surface, which is consistent with a disproportionate amount of the more hydrophobic component diffusing to the air interface. Biresaw and Carrier (2001) did not find any consistent correlation between the ability of starch to be blended with various polymers and the wettability properties of the other polymers. More recently, Shrimali et al. (2018) presented evidence that a hydrophobic side of starch macromolecules is able to adsorb effectively onto hydrophobic mineral surfaces. In other words, depending on the conformation of starch, it can present a surface that is suitably hydrophobic to be compatible with a hydrophobic plastic phase. The effect was explained by Yamane et al. (2006), who considered analogous behavior of cellulose, which has the same chemical composition as amylose starch, but with different orientation at the glycosidic linkages. As shown in Fig. 3, depending on whether one is dealing with the axial or the equatorial face of cellulose, it can be alternatively hydrophobic or hydrophilic (Khazraji and Sylvain (2013). Thus, it would be reasonable to expect that a related mechanism can be important when thermoplasticized starch is being formulated in mixtures with more hydrophobic bioplastics.

Fig. 3. Molecular conformation of cellulose, redrawn from Yamane et al. (2006), who used the drawing to support their finding that cellulose can present surfaces of differing hydrophobic or hydrophilic character, depending on the solvent system present during regeneration of the polymer. In the figure, gray spheres represent carbon, pink spheres represent oxygen, and cyan spheres represent hydrogen.

A further example to highlight the dual affinity of starch is provided by cyclic forms of starch, which are known as cyclodextrins. Through the action of specialized enzymes, starch can be cyclized into various ring structures comprising 5 to 7 anhydroglucose units; these are known respectively as , , and (Roy et al. 2015). Figure 4 shows the molecular structure of a -cyclodextrin version (part A) and the conformational pattern of a -cyclodextrin version in which the hydrophobic nature is stereochemically amplified (part B). In the toroidal structure, the hydroxyl groups face outwards toward the bulk solution, hence imbuing the outer part of the ring with hydrophilicity (dissolves well in water). By contrast, the hydrophobic components (C-H bond) nest within the cavity of the toroid to endow that location with hydrophobicity.

Fig. 4. A representation of the hydrophobic-hydrophilic partitioning of starch when it adopts a cyclic (“cyclodextrin”) geometry. Green coloration represents a hydrophobic environment within the ring.

Composite Options for Bioplastics

The use of fibrous materials to enhance the properties of plastic matrix materials has become well established, both technically and commercially (George et al. 2001; Najafi 2013). Although other materials such as glass fibers and carbon fibers are more widely used as reinforcement in various plastics, cellulose-based reinforcements also are employed. The size of the reinforcements covers a huge range. At the high size end of the range, macroscopic wood pieces are used in various wood-plastic composites (Najafi 2013; Hubbe and Grigsby 2020). At the other extreme, cellulose nanocrystals, which are typically 3 to 50 nm in cross-section and 100 nm to several µm (depending on the biomass source) in length, have been used (Hubbe et al. 2008).

For industrial production, one of the most practical procedures to prepare a bioplastic composite involves dry-mixing, followed by melt-extrusion and compounding or injection-molding of the desired shape (Hubbe and Grigsby 2020). The relatively high temperatures and shear stress levels associated with such operations can adversely affect the resulting composites in two ways. One is a loss of molecular mass of the polymer; this issue will be considered more closely when discussing the recyclability of biopolymers and their composites. Another harm is the mechanical breakage of cellulosic reinforcement material (Teuber et al. 2016). As a strategy to avoid such adverse effects of high temperatures and shear stress, many studies have been carried out by dissolving the plastic in a solvent, followed by casting and evaporation (Arias et al 2015). The downside of solvent-casting processes can include concerns about solvent release, slower processing, and higher costs.

Compatibilization Options

Because of the generally hydrophilic nature of cellulosic surfaces, which contrasts with the hydrophobic character of PLA and other bioplastics most likely to be able to take the place of common petroleum-based plastics, it is important to consider the compatibility of the surfaces. A recent review article showed substantial increases in the strength of cellulose-reinforced plastic composites when the system contained at least one additive or surface treatment designed to improve melt-wettability or adhesion at such interfaces (Hubbe and Grigsby 2020). There are basically two approaches to achieving compatibility between a hydrophobic matrix polymer and a hydrophilic reinforcing particle – either treat the surface of the reinforcing particle or add something to (or modify) the matrix polymer. Surface modification of the cellulosic reinforcement will be considered first.

Surface derivatization

Esterification can be regarded as well suited for the modification of cellulose surfaces in the present context. Cellulosic surfaces are known have an abundance of –OH groups that will readily react with a number of modifying agents that include carboxylic acids, acid-anhydrides, or acid chlorides under suitable conditions of temperature and time. For example, it is possible to form an ester between cellulose surface –OH groups and lactic acid; such an approach has been shown to achieve better compatibility with a PLA matrix (de Paula et al. 2016; Hua et al. 2016). A related approach has been demonstrated by grafting PHB-co-valerate onto cellulose surfaces, resulting in higher mechanical performance of the PHB composites (Yu et al. 2014a). Even methyl esterification of cellulose surfaces has been shown to be helpful in increasing compatibility with a PHB matrix (Yu et al. 2014b). Zandi et al. (2019) showed related benefits when the cellulose surfaces were benzylated. Wei et al. (2017) carried out transesterification at nanocellulose surfaces with the methyl ester of canola oil fatty acids. Yin et al. (2020) recently demonstrated lipase-catalyzed derivatization of cellulose nanocrystal (CNC) surfaces with laurate esters, which improved the dispersion of the CNCs in PLA and increased the composite strength. Cui et al. (2020) treated cellulose with citric acid under conditions of 130 C and 15 h of exposure. The citrate-reacted cellulose contributed to higher strength compared to untreated cellulose when used as a reinforcement for PLA.

Another reason why ester linkages, as just described, are well suited to the present goals is that such linkages are susceptible to enzymatic cleavage (Hasan et al. 2006). In other words, they could function as a weak link when the time comes for the material to biodegrade upon exposure to the environment or composting. The process depicted in Fig. 5 is based on the type of surface treatment employed by Yin et al. (2020).

Fig. 5. Depiction of vulnerability of a class of ester bonds that were established by, and which also can be cleaved with the assistance of lipase-enzyme treatment

Other surface reactions have been reported to change the compatibility of cellulose with plastic matrix materials. These include long-chain alkyl trimethoxysilane (Orue et al. 2015; Hassaini et al. 2017; Yin et al. 2018; Lertphirun and Srikulkit 2019; Patwa et al. 2019), epoxy treatment (Kyutoku et al. 2019), triazine grafting (Yin et al. 2017), and physical coating of the cellulose with polyethylene oxide (Singh et al. 2020).

Reactions during compounding

As an alternative to surface derivatization, various additives or modifications can be done that involve the matrix or the mixture of reinforcing particles and bits of matrix material. A widely used version of this approach involves of adding something that is capable of reacting during melt-extruding and compounding. For instance, alkyl-trimethoxysilane has been added as an ingredient to a mixture of wood fiber and PLA prior to melt-extrusion (Pilla et al. 2009a,b). Quiles-Carrillo et al. (2018a,b) demonstrated the use of acrylated epoxidized soybean oil, which appeared to play a dual role as plasticizer and as a reagent. Maleic anhydride was used as a reagent during melt-extrusion (Rigolin et al. 2019). The reported results suggest that the additive reacted with the cellulose surfaces, thereby hydrophobizing the cellulose. However, a more promising version of that approach is to first react the maleic anhydride with low-molecular-mass PLA and then use the product as a compatibilizing additive (Wu 2009). The latter approach is analogous to the widespread use of maleic acid derivative of polyethylene (MAPE) as a compatibilizer for wood-polyethylene composites (Hubbe and Grigsby 2020).

Other additives

In addition to the matrix polymers, reinforcing fibers, and compatibilizing or surface-modifying treatments already considered, the processing and properties of reinforced plastic composites also can be greatly affected by such additives as plasticizers, surfactants, and polymer bends. Each of these will be considered in the main sections that follow, especially when considering how they can affect biodegradability. Even minor ingredients can be considered as potential weak links (Pillai 2014; Satti and Shah 2020), which might later be used to aid in biodegradability. For instance, when starch is used as a blend with PLA, the rate of biodegradation can be greatly increased (Leejarkpai et al. 2011; Mihai et al. 2014). In addition, hydrophobic groups appended to cellulose surfaces by means of ester linkages can serve as weak links (Wei et al. 2017; Patwa et al. 2019; Yin et al. 2020), since presumably such linkages can be enzymatically cleaved (Reetz 2002; Hasan et al. 2006).


Overview of Biodegradation Issues

Motivation for research and development of bioplastic products, such as PLA and PHB, rests partly upon a common understanding that such materials are biodegradable, and hence are likely to be more eco-friendly than synthetic polymers (e.g., polyethylene) (Tokiwa et al. 2009). That worldview becomes threatened when it is reported that these two biobased plastics, which have shown some of the greatest promise in terms of physical properties, have failed to degrade under some conditions of soil exposure and seawater exposure (Wan et al. 2019a). For instance, Wadsworth et al. (2013) reported that when PLA was placed into the ground in the form of agricultural mulch, there was little loss of molecular mass after 29 weeks, despite some loss of mechanical strength. Relatively hot conditions of composting, e.g. 60 C, have been found to give effective biodegradation of PLA, especially when employing a dialysis method (Panyachanakul et al. 2019). Camas et al. (2020) reported that seawater degradation of PLA is very slow and similar to that of high-density polyethylene (HDPE), which is well known as a persistent plastic in the environment. By contrast, on land PLA has been found to degrade about 20 times faster than HDPE.

To bring objectivity to the search for materials that biodegrade rapidly enough for practical use, governmental and international agencies have developed standards (Narayan 2012; Ruggero 2019). The following standards are for example related to compostability: ASTM D5338, ASTM D6400; ISO 14855-1, and ISO 17088:2012 (see Kale et al. 2007b). However, as noted by Muniyasamy et al. (2013), composting systems are inherently complex and difficult to standardize. For assessment of plastic biodegradation in soil, but not under composting conditions, ASTM D5988-18 or ISO 17556:2019 may be used. Biodegradability in an ocean environment can be assessed according to ASTM D6691-17. Non-floating plastic in an ocean sandy environment is covered by ISO 18830:2016 and ISO 19679:2020.

As a result of numerous studies, a general description of the main mechanistic steps of biodegradation of bioplastics can be stated (Tokiwa and Calabia 2007; Lucas et al. 2008; Bikiaris 2013; Muniyasamy et al. 2013; Wang et al. 2013; Pillai 2014; Elsawy et al. 2017; Emadian et al. 2017; Qi et al. 2017; Scaffaro et al. 2019; Chamas et al. 2020; Xu et al. 2020). One can envision the process happening as a series of three steps, namely (i) biodeterioration, (ii) biofragmentation, and (iii) assimilation. The last (iii) of these can include mineralization, whereby the material has been returned to the basic ingredients characteristic of soil. Qi et al. (2017) listed the main steps as being release of the enzyme from a microbe, followed by action of the enzymes and release of breakdown products. Factors affecting the rate of biodegradation of a bioplastic can include water uptake by the bioplastic, enzymatic attack, cleavage of ester groups, release of monomers and oligomers, diffusion of the solubilized entities, and ultimate breakdown to carbon dioxide and water (Bikiaris 2013). Hakkarainen et al. (2000) concluded that enzymatic degradation of PLA mainly proceeds from the chain ends rather than random scission; whereas hydrolytic degradation takes place at random locations along PLA chains. Unfortunately, the process of chain end scission or “peeling” is extremely slow and cumbersome to attain a favorable decomposition profile. In order to achieve much more effective degradation profiles, the strategy of chain cleavage is necessary. Laycock et al. (2017) reviewed publications suggesting that the rates of biopolymer degradation may involve both oxidative and hydrolytic mechanisms. As noted by Nair et al. (2017), the biodegradability of a plastic generally cannot be predicted based on its source material, such as whether it is petroleum-based or plant-based. Rather, biodegradability typically is more dependent on chemical structures, purity, and the degree to which the bioplastic forms into crystalline domains.

While most of the research attention has been focused on enzymatic routes of degradation of biopolymers, there is increasing evidence that some of the rate-limiting steps are abiotic, i.e. not controlled by enzymes. Already in 1998 it was observed that the rate of PLA decomposition in the temperature range of 40 to 60 C was almost completely dependent on temperature and moisture, with little influence that could be attributed to the presence or absence of microbial enzymes (Agarwal et al. 1998). Copinet et al. (2009) and Husarova et al. (2014) carried out parallel experiments with and without enzymes present and found very similar biodegradation rates of PLA. Further persuasive evidence comes from a study in which PLA/starch blended materials were subjected to parallel experiments either in composting conditions or in a pile of inert vermiculite. Again, near-equal degradation was obtained in the parallel conditions. Based on an analysis of rate data, Stloukal et al. (2015) concluded that enzymes are unable to break down PLA until the molecular mass has been first decreased by an abiotic mechanism. Strikingly contradictory evidence, relative to other citations in this paragraph, was presented by Satti et al. (2017), who observed much faster degradation of PLA in the presence of certain bacteria, even allowing degradation at ambient temperature. Abiotic hydrolysis becomes significant as the temperature becomes higher than the glass transition point of PLA, which often lies within the range of 55 to 62 C (Karamanioglu et al. 2014).

Though a majority of published articles have been focused on the need for more rapid biodegradation of biopolymers in the environment, it is important to maintain a balanced perspective. To perform its function, a typical polymeric material generally must remain intact for an optimized period, even when subjected to natural environments. Thus, one can use the word “tuning” to describe measures that are taken to promote or inhibit biodegradation (Gardella et al. 2017; Wei et al. 2017). For this reason, the discussion that follows will also include some findings – such as the incorporation of lignin – that often tend to slow down the biodegradation of bioplastics. Likewise, Laycock et al. (2017) discussed ways to determine the “safe working life” of biopolymers in diverse applications. In some applications, a persistent polymer that remains intact and can be recycled multiple times may be preferable to a biodegradable plastic, even in the case of bio-based plastics (Steinbuchel 2005).

Bioplastic Matrix Type

In the engineer’s toolkit of ways to manipulate the rate of biodegradation, perhaps the first strategy involves the selection of the type of bioplastic matrix. In general, the rates of biodegradation of the best-known bioplastics follow the order of PHB-co-valerate > PHB > PLA (Bonartsev et al. 2012a,b). The general rule is that greater enzymatic susceptibility can be expected for biopolyesters that have greater numbers of methylene groups within each repeating unit along the chain (Tokiwa and Calabia 2007). In addition, a higher molecular mass polymer is likely to be more durable and resistant to biodegradation (Bonartsev et al. 2012a). Recent work by Parisi et al. (2019) and Tournier et al. (2020) achieved very high rates of breakdown of the petroleum-based plastic poly(ethylene terephthalate) (PET) under aqueous conditions. In the case of PLA, both enantiomers are biodegradable, at least in their amorphous regions, but different enzymes are needed to initiate the biodegradation (Kawai 2010). As noted by Panchal and Vasava (2020), another option is to employ petroleum-derived monomers for the preparation of fully biodegradable plastics.

The preparation of copolymers offers additional opportunities to tune the biodegradation rates of biopolymers (Bikiaris 2013). There are innumerable opportunities to incorporate various alternative bio-based co-monomers during the synthesis (Sudesh et al. 2000; Kobayashi 2017). As a rule, copolymers are less likely to form highly crystalline solids, and biodegradability is generally favored by amorphous character of the thus-synthesized copolymers (Reeve et al. 1994; MacDonald et al. 1996; Tokiwa et al. 2009; Kawai 2010; Pantani and Sorrentino 2013; Luzi et al. 2015, 2019; Elsawy et al. 2017). For instance, Wang et al. (2011) described the incorporation of a weak-link monomer into polyurethane, based on the triblock oligomer PLA-poly(ethylene glycol)-PLA. Another approach, which will be considered in more detail later, is to prepare blends of different polymers (Bikiaris 2013).


An enzyme can be described as a relatively large protein or group of protein molecules that, on account of its structural and chemical details, is able to catalyze the cleavage or assembly of covalent bonds. Those that are relevant in terms of biodegradation of polyesters are enzymes that are excreted from the cell walls of certain fungi and bacteria (Kawai 2010). The enzymes of the greatest relevance can be classed as proteinases, lipases, esterases, and alcalases (Lee and Wang 2006; Lee et al. 2014; Roohi et al. 2018). It is important to match the enzyme with the materials and conditions. For industrial composting or bioreactors, thermophilic lipases are effective (Kawai 2010; Lee and Song 2011). Notably, poly(L-lactic acid) is mainly cleaved by proteases, whereas poly(D-lactic acid) is mainly cleaved by lipases.

Promoters of enzymatic biodegradation

Certain additives have been found to promote biodegradation of bioplastics. The list includes wood fibers (Chaiwutthinan et al. 2019), microcrystalline cellulose (Fortunati et al. 2012), sulfate-stabilized cellulose nanocrystals (s-CNCs) (Luzi et al. 2016), CNCs stabilized by the phosphate ester of nonylphenolethoxylate (Luzi et al. 2015), and benzoyl peroxide (Hu et al. 2018).

Inhibitors of enzymatic biodegradation

Cellulosic materials from plants, i.e. biomass, provides an inspiring example of achieving high strength while simultaneously being fully biodegradable in natural environments (Teeri et al. 2007). Cellulosic materials also will be considered in subsequent sections relative to its reported effects on the biodegradability, recyclability, and strength of bioplastic composites. Two well-known factors that tend to inhibit biodegradation of cellulose-based materials are increasing levels of lignin and increasing levels of crystallinity. An inhibiting effect of lignin on biopolymer degradation was reported by Anstey et al. (2014). The cited authors suggested that the slower degradation may be related to the contrasting mechanisms of degradation of the bioplastic and the lignin. Angelini et al. (2014, 2016) and da Silva et al. (2019) surprisingly found that incorporation of certain lignin types into PHB actually promoted biodegradation. However, another lignin-rich additive inhibited both hydrolytic and enzymatic degradation of the PHB (Angelini et al. 2014). There is widespread consensus that increasing crystallinity of the matrix polymer will slow and sometimes essentially stop the progress of biodegradation (Reeve et al. 1994; MacDonald et al. 1996; Tokiwa and Calabia 2007; Tokiwa et al. 2009; Bikiaris 2013; Pantani and Sorrentino 2013; Elsawy et al. 2017; Emadian et al. 2017; Seoane et al. 2017b).

Another type of inhibitor that affects many common enzymatic processes involves products of the hydrolysis reactions. For example, sufficiently high concentrations of lactic acid have been found to decrease rates of enzymatic hydrolysis of PLA (Panyachanakul et al. 2019).

In addition to favoring amorphous regions of bioplastics, hydrolytic enzymes also tend to favor attack on outer surfaces rather than bulk or internal action (Wang et al. 2003; Gutierrez-Wing et al. 2010; Arcos-Hernandez et al. 2012; Bikiaris 2013; Lee et al. 2014; Pillai 2014; Elsawy et al. 2017; Laycock et al. 2017; Ding et al. 2018; Chan et al. 2019; Chamas et al. 2020). Arcos-Hernandez et al. (2012) concluded that the rate of biodeterioration and depolymerization was dependent on the composition of the bioplastic, its degree of crystallinity, and its surface morphology.


Consistent with the previous discussion, it is logical to expect that rates of biopolymer biodegradation can be increased by increasing the accessibility of biopolymer surface area to enzymes. For instance, Finelli et al. (1998) proposed that a blended mixture of PHB and ethyl cellulose would provide a three-dimensional accessibility to degradation that would be inherently much more vulnerable to enzymatic attack than the PHB by itself. Various researchers have suggested that faster degradation can be achieved if something is added to the mixture to allow diffusion within the bioplastic material (Fortunati et al. 2013; Xie et al. 2014; Balart et al. 2018; Chan et al. 2019). Thus, the development of cracks in the course of biodegradation (Hakkarainen et al. 2000; Lee et al. 2014; Lu et al. 2014; Chan et al. 2019) would be expected to accelerate the degradation process.

It can be hypothesized that the hydrophobic nature of various biopolymers can serve as an impediment to biological degradation processes, which invariably involves aqueous conditions. Thus, the tendency of lignin to inhibit biodegradation in some cases could be explained by the finding that its addition to PLA increased the water contact angle (Gordobil et al. 2015). On the other hand, one might anticipate that biodegradation would be promoted by adding materials or particles that would make the biopolymer surface more water-wettable (Seoane et al. 2017a,b; Turco 2019). Yamano (2014) observed a correlation between biodegradability and hydrophilicity of a polyamide, the terminal groups of which had been modified with alkyl chains having different lengths. Though there is reason to expect a general correlation between hydrophilicity and susceptibility to enzymatic attack, it is usually difficult to separate potential effects of hydrophobicity from other factors in the experimental systems.

Cellulosic materials

Cellulosic fibers stand out as a promising candidate to provide access for moisture and microbial enzymes within bioplastic composites. For example, kraft fibers are known to provide an essential wicking within cellulose absorbent products that contain superabsorbent polymers (Hubbe et al. 2013). Several researchers have proposed that cellulosic materials play a related role when they are present in bioplastic composites (Seoane et al. 2017b; Balart et al. 2018; Gunti et al. 2018; Cinelli et al. 2019; Lertphirun and Srikulkit 2019). By allowing access to the enzymes and aqueous media access, the hydrolysis reactions are no longer limited to the exterior of a bioplastic phase. As a further contributing mechanism, cellulosic fibers can be expected to swell when moistened (Rowell 2007), and the swelling can be expected to open up cracks within the biopolymer. Accordingly, Chan et al. (2019) observed the opening of channels within PHA-wood composites, allowing access for enzymatic biodegradation. Gunti et al. (2016) observed substantial water absorption into jute fiber-filled PLA composites. Wang et al. (2014) observed increased water-swelling when PLA was filled with lignin-containing nanocellulose.

A possible mechanism by which cellulosic reinforcements can facilitate entrance of water into a hydrophobic polymer matrix, as a first step in bringing about decomposition of the matrix material, is illustrated in Fig. 6. As shown, the swelling of the cellulose material, which also allows passage of water deep into the bioplastic phase, can be expected to induce cracks, depending on the brittle nature of the matrix phase.

Fig. 6. Schematic diagram of (a) cellulose-based reinforcement within a hydrophobic polymer matrix; and (b) how the initial entrance of water via the reinforcements can lead to their swelling and possible crack formation in the matrix material

Various studies have reported positive correlations between cellulosic content in bioplastic formulations and biodegradation rates. Microcrystalline cellulose was shown to promote the biodegradation of PLA and poly(butylene adipate-co-terephthalate) (Fortunati et al. 2012; Giri et al. 2019). Lu et al. (2014) reported a more rapid biodegradation of PLA when formulated with distiller’s dried grains and solubles. Lv et al. (2017) and Chan et al. (2019) observed increasing rates of biodegradation of polyhydroxyalkanoates with increasing content of wood flour. Several researchers have reported accelerated biodegradation of various bioplastics when formulated with cellulosic fibers (Mathew et al. 2005; Hidayat and Tachibana 2012; Wu 2012; Gunning et al. 2013; Anstey et al. 2014; Mihai et al. 2014; Gunti et al. 2016, 2018; Popa et al. 2018; Chaiwutthinan et al. 2019; Zandi et al. 2019). Yang et al. (2016) reported enhanced degradation of PLA films that contained lignin and cellulose. Wan and Zhang (2018) and Wan et al. (2019b) demonstrated rapid biodegradation of PLA that had been reinforced with poly(methylmethacrylate)-derivatized cellulose fibers. Wu (2009) observed that PLA reinforced with coconut fibers was highly biodegradable when the mixture also included maleic anhydride.

However, some other research teams observed no positive effect of cellulosic fibers on biodegradation of bioplastics (Avella et al. 2000). Fazita et al. (2015) reported that bamboo fabric reinforcement decreased the rate of biodegradation of PLA. Likewise, Masmoudi et al. (2016) observed a slower rate of biodegradation of PLA when formulated with cellulose fibers. Mixed results were reported by Mofokeng et al. (2012), who reported lower rates of PLA biodegradation when reinforced with the low level of 1% sisal fibers, but higher levels of biodegradations for combinations of higher fiber levels and time exposures of 10 days or more. Mixed results were also reported by Way et al. (2013) who found somewhat faster and more extensive biodegradation when the filler was cotton fibers, but the opposite when the filler was wood fibers. In summary, though the hydrophilic nature a cellulosic reinforcements might help promote biodegradation, they might also have a net effect of holding the material together more securely, thus slowing biodegradation in some cases.

Nanocellulose also has been reported to affect biodegradation rates when used as a reinforcement in bioplastics, but there was not good agreement among different studies. Urbina et al. (2016) incorporated PLA into bacterial cellulose by solvent casting and observed a more rapid biodegradation compared to neat PLA films. Heidarian et al. (2018) observed that incorporation of CNCs into recycled PLA decreased the biodegradation rates. In contrast, Luzi et al. (2015, 2016) observed promotional effects of CNCs on degradation of blends of PLA or its blend with PHB. However, Luzi et al. (2019) did not observe any important effect of CNCs on biodegradability, relative to other factors considered. Arrieta et al. (2015, 2016, 2018) reported that incorporation of CNCs into PLA-PHB blends did not interfere with biodegradation. It is speculated that the disagreement among studies may be related to a balance between either strengthening of the composite structure or increasing the hydrophilic nature due to the presence of the CNC.

In addition to often promoting the biodegradation of the bioplastic, another potential advantage of employing cellulose for a biodegradable composite system is the fact that cellulose itself is biodegradable. Cellulases and other wood-degrading enzymes are abundantly available in natural environments (Bhat and Bhat 1997; Mohanty et al. 2000; Passardi et al. 2005; Sukumaran et al. 2005; Madhavi and Lele 2009; Sharma et al. 2016). None of the studies involving bioplastic composites cited in this work specifically considered effects due to wood-degrading enzymes, but over a longer timeframe such effects are expected to be important, especially in soil environments and composting. The biodegradation of lignocellulosic materials in the course of composting has been reviewed elsewhere (Hubbe et al. 2010; Hubbe 2014).

Foam structure

Besides the use of cellulosic reinforcements, another way to invite moisture and enzymes into the interior of a bioplastic material is by creating a solid foam with an open-cell structure. Such an approach might make sense in applications where a low-density, porous material is needed. Foams have been created from PLA (Bocz et al. 2016; Borkotoky et al. 2018a,b; Zhang et al. 2018; Zimmermann et al. 2018; Sungsee and Tanrattanakul 2019), and blends of PLA and starch (Ganjyal et al. 2007; Sohn et al. 2019). In some of these cited studies the foams were reinforced with sawdust (Sungsee and Tanrattanakul 2019), cellulosic fibers (Bocz et al. 2016; Zhang et al. 2018; Zimmerman et al. 2018), nanofibrillated cellulose (Zimmerman et al. 2018), or cellulose nanocrystals (Borkotoky et al. 2018a,b). However, none of these cited works provided a demonstration that the formation of a foam structure affected biodegradation rates. Sungsee and Tanrattanakul (2019) demonstrated slow degradation under in vitro physiological conditions. Ganjyal et al. (2007) observed faster biodegradation of PLA foams compared to mixed PLA-cellulose acetate foams.

Effects of Exposure Conditions

Conditions during exposure of bioplastics and their composites to composting, soil, and seawater, etc., have been shown to have various effects on biodegradation. Because cast-off or properly disposed plastic items can end up in widely diverse circumstances, the ideal would be to engineer suitably rapid biodegradation in each of the listed environments. Composting conditions will be considered first, since there is potentially more to learn from such studies. Not only are the conditions of composting generally better recorded than those associated with soil burial, but the effects are typically faster and more complete during the studied period.


Studies in which composting conditions were used to evaluate the biodegradation of bioplastics or their composites are listed in Table 4. As a general summary, successful composting was reported for most systems, among which PLA was by far the most widely studied. However, degradation rates appear to be sensitive to many details. One needs to keep in mind that temperature is a key variable. Successful composting under industrial conditions, which involve relative large compost piles and the generation of temperatures in the range of about 55 to 65 C, might not imply favorable results under lower or unknown temperature conditions that are likely to prevail during household composting (Hubbe et al. 2010; Gorrasi and Pantani 2013; Emadian et al. 2017).

Table 4. Studies in Which Composting was Used to Evaluate Biodegradability of Bioplastics or their Composites

Hakkarainen et al. (2000) achieved relatively rapid biodegradation of PLA under composting conditions at 30 C. The molecular mass decreased significantly during four weeks of enzymatic hydrolysis. Notably, insignificant degradation was observed in cases where sodium azide had been added to prevent biological processes.

Effects due to temperature during biodegradation were observed in several studies. It has been generally found that biodegradation increases with increasing temperature (Ho et al. 1999; Karamanlioglu and Robson 2013). Musiol et al. (2011) observed essentially complete degradation of PLA and other bioplastics at 70 C. Similar results were obtained when the bioplastics were placed in distilled water at the same temperature. In other cases the researchers observed optimum temperatures for the action of certain enzymes (Lee and Song 2011; Youngpreda et al. 2017).

Soil conditions

Table 5 lists studies that employed soil burial tests as a means of evaluating the biodegradation of bioplastics or their composites. Striking evidence of degradation during soil burial was reported by Balart et al. (2018). Weight loss was minimal during an initial 14 days of soil burial at 30 C, but thereafter there was an approximately linear loss of weight, resulting in about 80% to 95% weight loss after 42 days of burial. These results were not significantly affected by the presence of hazelnut shell flower in the PLA matrix at levels as high as 30%, though a content of 40% further accelerated the weight loss. As a general summary, many of the articles reported that biodegradation was slow, but it could be sped up by incorporating hydrophilic materials into the bioplastic. There appears to be a need for further enhancement in soil biodegradation rates of bioplastics.

Table 5. Studies in Which Soil Burial was Used to Evaluate Biodegradability of Bioplastics or their Composites

In comparison to composting, the conditions during realistic burial in soil are often at cooler temperatures. So it is worth noting that various researchers reported slow or negligible degradation in soil tests (Rudnick and Birassoulis 2011; Karamanlioglu and Robson 2013; Gunti et al. 2016). In particular, Wadsworth et al. (2013) noted little loss of molecular mass under soil conditions; PLA mulch fabrics remained largely intact after 10 to 29 weeks of exposure. In some studies it was observed that breakdown of the bioplastic was generally limited to surface effects (Arcos-Hernandez et al. 2012; Chan et al. 2019).

Though composting and soil burial conditions have been considered most often by researchers, it seems likely that the most effective biodegradation of bioplastics will be achieved in some kind of bioreactor. For instance, Panyachanakul et al. (2019) reported essentially complete breakdown of PLA at 60 C in a stirred tank with a selected enzyme and with dialysis to avoid the buildup of lactic acid byproduct. Anaerobic digestion of PHB in a mixture with municipal wastewater sludge has been reported (Gutierrez-Wing et al. 2010). Ruggero et al. (2019) recently reviewed the topic of biodegradation of bioplastics in aerobic composting and anaerobic digestion.


The ocean surface represents one of the most challenging venues for the biodegradation of plastics. Figure 7 illustrates at least two ways that plastic debris can reach the ocean, even when the initial disposal might be in the form of litter or flushed items. A disadvantage of the ocean surface relative to biodegradation of bioplastics is that the prevailing temperatures are always substantially lower than those associated with successful composting of such materials. A possible positive contribution of UV light has been shown to aid in the degradation of PLA (Pattanasuttichonlakul et al. 2018). However, there is circumstantial evidence that floating plastic on the ocean does not necessarily remain floating (Eriksen et al. 2014). Cózar et al. (2020) proposed that much of the plastic becomes incorporated into the ocean biosphere, possibly as micrometer-sized bits. Such bits, therefore, might no longer be subject to significant UV light exposure. Indeed, the problem with radiative induction of degradation is penetration depth. Most systems that respond to light generally do so at the topmost layers, and any propagation of the radicals generated is limited to no more than a few micrometers. Therefore, UV light as a potent bioremediative agent is limited to thin materials and optically transparent (clear water) systems located at the sea surface. On the other hand, biodegradation has been shown to occur in the case of poly(-caprolactone) even deep within the ocean (Sekiguchi et al. 2011).

Fig. 7. Schematic illustration of ways in which plastic litter and plastic items inadvertently introduced to sewage may eventually end up in the ocean. Inspiration for the figure can be credited to The content of the figure was greatly changed and all aspects were redrawn.


As an alternative to biodegradation, certain bioplastic formulations containing PLA, polyethylene terephthalate, and other ingredients can be effectively degraded in distilled water at 70 C (Musiol et al. 2011). The mechanism is abiotic hydrolysis, as mentioned earlier. In about a month of incubation, the two bioplastic formulations considered in the study lost about 40 to 55% of their molecular mass. Thus, one must continually keep both the abiotic and the enzyme-catalyzed pathways in mind, as well as their likely combined or synergistic effects.

Effects of Additives on Biodegradation

The formulation of a bioplastic can include many kinds of additives, and the objective of this subsection is to consider evidence of whether or not some of them tend to either promote or inhibit the biodegradation of bioplastics and related composites. Some potential additives may clearly fall into categories such as plasticizers, surfactants, coupling agents, or a component of a blended polymer matrix. However, at least some of them may straddle more than one such classification, and their roles may be described in the literature using different terms. Regardless of what category is used, the essential question is whether or not a certain additive might function as a weak link, somehow facilitating either enzymatic or abiotic degradation at the end of the material’s life.


Table 6 provides key information from studies that consider the effects of various additives that can be regarded as plasticizers for bioplastics. Briefly stated, the role of a plasticizer is to increase the ability of a plastic to stretch before it breaks (Wypych 2004). Typically a plasticizer will also reduce the glass transition temperature and decrease the elastic modulus. Poly-(ethylene glycol) (PEG), in addition to acting as a plasticizer, has been reported to promote degradation of PLA (Arrieta et al. 2014a). In the case of PLA, an assumed plasticizing role of PEG may explain observations of faster and more complete biodegradation (Arrieta et al. 2014a; Xie et al. 2014; Zhang et al. 2019). The more rapid biodegradation also has been attributed to its hydrophilic nature (Xie et al. 2014). Faster degradation in the presence of various other plasticizers also has been reported (Nair et al. 2012; Carofiglio et al. 2017; Gardella et al. 2017; Yu et al. 2019; Zhang et al. 2019).

Table 6. Plasticizers and their Effects on Biodegradation of Bioplastics


Because surface-active agents (surfactants) have contrasting affinities within the same molecule, it is reasonable to expect that some of them can be effective for improving the assembly process and properties of composites involving hydrophobic bioplastic matrices with cellulosic reinforcement. Bondeson and Oksman (2007) observed that an anionic surfactant helped to disperse nanocellulose (CNCs) within PLA, but the PLA matrix had lower strength as a result. Luzi et al. (2015) reported that addition of CNCs that had been treated with a phosphate ester of nonylphenolethoxylate promoted disintegration of PLA in compost. It is logical to expect that surfactants molecules can have the effect of increasing the amount of water molecules within a bioplastic phase, thus promoting various degradation mechanisms as already discussed.


A compatibilizer can be viewed as playing a role similar to that of surfactants, serving as a kind of bridge between otherwise non-interacting phases (Kim and Pal 2011). Often the term compatibilizer refers to polymeric species that have affinity characteristics intermediate between the main matrix polymer and the reinforcing particles (Takatani et al. 2008; Li et al. 2013). Table 7 shows cases in which use of compatibilizers (via, for instance, grafting of coupling agent, surface modification or use of additives) were reported to have effects on biodegradation of bioplastics and their composites. The general finding was that the additives gave rise to more rapid degradation. The effects were sometimes attributed to increased hydrophilic character of the mixture (Gardella et al. 2017) or faster diffusion of water (Fortunati et al. 2013).

Table 7. Compatibilizers and their Effects on Biodegradation of Bioplastics

Crosslinkers and coupling agents

Faster biodegradation with proteinase K of blends of PLA and poly(butylene succinate) was observed when benzoyl peroxide had been used to promote crosslinking during the composite preparation (Hu et al. 2018). However, it was also noted that the crosslinking appeared to resist complete degradation. Kido et al. (2014) likewise observed faster biodegradation of crosslinked PLA; they attributed this effect to the hydrophilic nature of the crosslinker. Lee and Wang (2006) observed lower enzyme degradability when PLA or polybutylene succinate bioplastics reinforced with bamboo fibers had been crosslinked with a lysine-based diisocyanate. Zenkiewicz et al. (2012) reported that physical crosslinking of PLA slowed enzymatic degradation.

Maleic anhydride, which can react during compounding, is often considered as a way to achieve better compatibility between phases in a composite. Mihai et al. (2014) observed high biodegradation of PLA-starch blends even with the use of maleic anhydride, which was reported to act as a coupling agent during reactive extrusion. Wu (2009) reported that PLA reinforced with coconut fibers could be degraded by bacteria at 35 C under composting conditions whether or not the formulation included maleic anhydride.

Carboxylic Acid-bearing Compounds as Additives

There is one more kind of potential additive to consider, beyond those just discussed. Since there does not seem to be an established term for this kind of additive, it will be described here simply as “carboxylic acid-bearing compounds”. Unlike the other additives already discussed, these compounds appear not to have a role in improving the processing of the material or its properties during active use. Rather, their apparent role is to promote either abiotic decomposition or a combination of abiotic and enzymatic decomposition of a biopolymer, such as PLA.

As noted by Bikiaris (2013) and Elsawy et al. (2017), hydrolysis of polyesters can be catalyzed by the presence of carboxylic acid groups. For instance, such groups might consist of the carboxylic acids at one of the ends of each PLA chain. Because there are more and more such groups as the molecular mass is reduced by degradation, the decomposition of PLA and related molecules can be described as autocatalytic (Tsuji and Ikada 2000; Paul et al. 2005; Zhou and Xanthos 2008; Elsawy et al. 2017). The effect was explained by Gatenholm and Mathiasson in 1994. They noted that crotonic acid released during the breakdown of PHB could lead to faster degradation of the PHB. It is possible to synthesize a PLA oligomer with pendant carboxylic acid groups and incorporate it into PLA (Stloukal and Kucharczyk 2017). The cited authors showed that at a level of just 5% in the PLA, the carboxylic acid compound was able to speed up the decomposition of PLA under both abiotic and enzyme-promoted decomposition conditions. Elsawy et al. (2017) suggested that the lower pH resulting from the newly formed carboxylic acid groups might be the ultimate cause of accelerated decomposition. Acidic conditions can be expected to promote the forward and reverse reactions of Fischer esterification (Vafaeezadeh and Fattahi 2015). Such an explanation is consistent with the findings of Vert et al. (1991). An alternative explanation might be that, on the contrary, the breakdown of PLA structure is facilitated by the deprotonation of the carboxylic acid groups, giving rise to ionized carboxylate species within and on the biopolymer. This possible mechanism is illustrated in Fig. 8. Due to the strong association between carboxylate groups and water, the bioplastic structure then would be prone to swell in water. Indeed, if the amount of carboxylation were high enough, it would be possible to prepare hydrogels from PLA-based materials (Munim and Raza 2019). An attractive aspect of this alternative explanation, if valid, is that such a mechanism would be able to work under near-neutral pH conditions, such as in the ocean (Marion et al. 2011) or during optimized composting (Hubbe et al. 2010).

Fig. 8. Depiction of water molecules associating with the charged and highly polar carboxylate group of a carboxylic acid species within a bioplastic phase. The mechanism may depend on the presence of microcracks to allow access to water and pH values high enough to bring about dissociation (e.g. pH > 3.5).

In view of the effects just described, some reported effects of plasticizers, as listed in Table 6, can be considered again. It is worth noting that faster rates of degradation were observed when using the following plasticizers: olive mill wastewater residues (Carofiglio et al. 2017), gum Arabic (Nair et al. 2012), and orotic acid (Yu et al. 2019). The first two of these plasticizers are known to be complex mixtures, and thus the presence of carboxylic acid compounds is likely. Orotic acid has a carboxylic acid group. The cited findings support the concept that carboxylic acid groups contained within the PLA promoted its degradation. However, not all studies agree. Luzi et al. (2019) did not observe important effects on biodegradation rates when oligomeric lactic acid, which would be expected to have a higher carboxylic acid content, was added to PLA as a plasticizer.

Biopolymer Blends

Blending with relatively hydrophilic polymers can be a promising approach to both lower the cost of bioplastics and also to render them more susceptible to biodegradation. For instance, blends of PLA with starch have been widely reported (Martin and Averous 2001; Kalambur and Rizvi 2006; Tokiwa and Calabia 2007; Tureckova et al. 2008; Lu et al. 2009; Sarasa et al. 2009; Thongtan and Sriroth 2011; Nair et al. 2012; Mihai et al. 2014; Masmoudi et al. 2016; Elsawy et al. 2017; Lv et al. 2017; Sohn et al. 2019; Turco et al. 2019). Similarly, a blend of PLA with chitosan or cellulose acetate also was shown to allow relatively rapid biodegradation (Claro et al. 2016). In many of these studies, the presence of starch was shown to speed up the rate or the extent of biodegradation (Tokiwa and Calabia 2007; Tureckova et al. 2008; Sarasa et al. 2009; Nair et al. 2012; Mihai et al. 2014; Masmoudi et al. 2016; Lv et al. 2017). Some authors have attributed such effects to an overall increased hydrophilicity of the material (Pillai 2014; Vasile et al. 2018; Turco et al. 2019).

As noted earlier, when introducing starch as a potential component in a bioplastic formulation, there is evidence that by changing its molecular conformation, starch is able to present a less hydrophilic character at interfaces with hydrophobic materials (Shrimali et al. 2018). This attribute may help to explain why starch has shown promise as a blend in combination with much more hydrophobic bioplastics. Analogous behavior has been reported for PEG (Chen et al. 2002), which likewise has been employed as an additive in bioplastics, despite its being quite soluble in water.

Blends of hydrophobic bioplastics such as PLA and PHB with polymers other than starch have been widely reported. A wide range of results can be expected because of the difficulty in predicting whether a given pair of polymers, under certain conditions, will form a homogeneous melt mixture, or whether there will be separate domains of each component at a micro- or nano-scale. If two contrasting polymers are mutually soluble, then it is reasonable to expect a suppression of crystal formation (Weng et al. 2011), i.e. amorphous character, which would then suggest greater susceptibility to enzymatic degradation (Kawai 2010; Elsawy et al. 2017). Table 8 lists studies that compared the biodegradability of bioplastics and their blends.

Some of the effects observed relative to the biodegradability of PLA when blended with other polymers might be explained based on changes in the overall hydrophobicity, as discussed earlier. The slow biodegradability of PLA has been attributed in part to its hydrophobicity (Agrawal and Bhalla 2003; Pillai 2014). Yamano et al. (2014) proposed that biodegradability would be correlated with hydrophilicity. This concept is consistent with a proposed acceleration of biodegradation by hydrophilic cellulosic materials in bioplastics (Yu et al. 2011). Moeini et al. (2020) reported increased wettability of PLA with the inclusion of -costic acid. This is an important finding because acid decomposition products during hydrolysis of bioplastics are expected to play an autocatalytic role in their abiotic decomposition, as discussed earlier. The opportunity to induce low pH in these biopolymeric media has a profound influence on the degradation profile, especially if given sufficient time and temperature. Acid is a vitally critical ally in the degradation possibilities because there is no means to buffer it in these types of polysaccharides.

Table 8. Blends among Hydrophobic Bioplastics and their Effects on Biodegradation

Inoculation with Microbes

Though bacteria and fungi, along with their excreted enzymes, are present throughout natural environments, it is reasonable to expect that enzyme-dependent biodegradation can be accelerated by intentional inoculation or enzyme addition (Tokiwa and Calabia 2006; Satti et al. 2017; Satti and Shah 2020). Slower degradation has been noted in some experiments where microorganisms have been excluded (Karamanlioglu et al. 2014). When the bioplastic is PLA, it has been shown that certain bacterial species are most suitable, e.g. Bacillus licheniformisPseudomonas geniculateActinomadura keratinilytica, and Sphingobacterium sp. (Fukushima et al. 2009; Pattanasuttichonlakul et al. 2018; Satti et al. 2018; Panyachanakul et al. 2019; Satti et al. 2019). Likewise, Nair et al. (2016) demonstrated the biodegradation of PLA by the following fungal species: Penicillium chrysogenumCladosporium sphaerospermumSerratia marcescens, and Rhodotorula mucilaginosa.

To achieve specificity in biodegradation reactions, or when conducting mechanistic studies, it can make sense to employ enzymes rather than exposing bioplastics to the bacteria or fungi that produce those enzymes (Urbanek et al. 2020). Table 9 lists some key results of studies involving lipase, which is especially noted as an effective agent for cleavage of the ester groups in triglyceride fats (Satti and Shah 2020). Lipase has also been reported to be efficient for cleaving ester groups in the poly-D-lactic acid form of PLA (Hegyesi et al. 2019). It should be noted that although Lee and Wang (2006) reported virtually complete breakdown of PLA, their study did not include control tests carried out without the enzymes at the same pH and temperature.

Table 9. Promotion of Bioplastic Degradation using Lipase Enzyme

Table 10 lists corresponding results for proteinase enzymes, especially proteinase K. This enzyme has been mentioned as being especially suited for PLA (Tokiwa and Calabia 2006).

Table 10. Promotion of Bioplastic Degradation using Proteinase Enzymes


Overview of Recyclability Issues

The term recyclability, when it is applied to bioplastics, can have more than one meaning. The major focus of this section will be on factors affecting the degree to which bioplastics can be melted and then formed into a next generation of plastic items. However, it is important to keep in mind that there are other alternatives, such as breaking down the materials to either oligomeric or monomeric building blocks that can be reused in some way that provides value. Various topics related to the recycling of bioplastics have been reviewed (Soroudi and Jakubowicz 2013; Niaounakis 2019; Tang and Chen 2019).

From the standpoint of overall environmental impacts, some studies have concluded that multiple recycling of bioplastics represents a favorable option, compared to other possibilities such as composting, landfilling, and incineration (Soroudi and Jakubowicz 2013; Cosate de Andrade et al. 2016). When the time comes that a plastic item no longer is suitable for continued use in its initial shape and dimensions, the best way to minimize usage of natural resources is to melt the plastic and reform it (Bhattacharjee and Bajwa 2017). However, Kale et al. (2007b) concluded that although recycling can be favorable from an energy standpoint, it is often impractical because of high requirements for cleaning and sorting. Niaounakis (2019) reported a lack of recent progress in recycling of biopolymers, although there has been patent activity, which is indicative of commercial interest in such processing of plant-derived plastics. Such activities need to be followed up by construction of suitable recycling facilities focused on bioplastics.

From a technical standpoint, it has been shown that the melt-reprocessing of PLA, PHB, and related bioplastics is feasible (Lopez et al. 2012; Åkesson et al. 2016; Lagazzo et al. 2019). However, there can be losses in properties of each succeeding generation of recycled bioplastic, depending on conditions of temperature, time, and shearing. The decrease of mechanical properties such as tensile strength, impact strength, and modulus, were observed in almost all studies of recycled bioplastics and composites. Two main aspects of degradation, which can take place during cycles of melting and reforming, are breakdown of the bioplastic matrix and breakdown of reinforcing particles, of which cellulosic particles are discussed in this article. Table 11 lists studies that have evaluated the properties during multiple generations of melt-reforming of bioplastics or their composites.

Table 11. Studies in Which Bioplastics or their Cellulose-Reinforced Composites Were Melt-reformed Several Times

Breakdown of Bioplastic during Recycling

Loss of molecular mass

With respect to biopolymer breakdown during melt-reprocessing, one of the clearest indications of degradation has been shown by evaluation of molecular mass.

Table 12. Studies Evaluating Molecular Mass Changes of Bioplastics or their Cellulose-Reinforced Composites that Were Melt-reformed Several Times

Chain scission during processing leads to reduction of molecular mass, thus weakening the mechanical properties of the recycled materials. The effect is dependent on reprocessing parameters, such as temperature, time, moisture content, and number of cycles. Table 12 lists studies that have considered such changes, along with key results.

Temperature effects

Thermal decomposition has been mentioned as a likely cause or contributor to bioplastic molecular breakdown during melt-reprocessing (Gatenholm and Mathiasson 1994; Ren et al. 2015; Cruz Sanchez et al. 2017). Indeed, as will be discussed, the depolymerization of PLA upon heating can be utilized as a way to recover the monomers (Dong et al. 2012). According to Cruz Sanchez et al. (2017), thermo-oxidative degradation is a mechanism that affects thermoplastics in general, especially if the reprocessing takes place at a high temperature relative to the thermal stability properties of the polymer. Gatenholm and Mathiasson (1994) proposed that frictional heating of the bioplastic during shearing was an immediate cause of depolymerization. Vandi et al. (2019) recently reported that although shear during reprocessing appeared to contribute to molecular mass loss of polyalkanoates, such losses could be minimized by reducing the time of shearing and melting.

Effects of Additives on Recyclability


Plasticizers, which can lower the softening temperature of bioplastics, offer a strategy to reprocess bioplastics with the prospect of lesser molecular damage. Lower glass transition temperatures of biopolymers have been observed when plasticizers were part of the formulation (Baiardo et al. 2003; Kulinski et al. 2006; Mekonnen et al. 2013; Fortunati et al. 2014; Ramos et al. 2014). A less brittle nature of the bioplastics in the presence of plasticizers (Jacobsen and Fritz 1999; Savenkova et al. 2000; Qiu and Zhou 2014; Arrieta et al. 2014b, 2015; Kamthai and Magaraphan 2015) also can be expected to contribute to successful processing during melt-reforming. According to Seggiani et al. (2015), PEG, which is a commonly used plasticizer for bioplastics, also can act as a lubricant during reprocessing.

Employment of enantiomeric pairs of biopolymers is another potential strategy that may be helpful in terms of reprocessing (Weng et al. 2011). This is because, especially in cases where the components are so similar that they can form an intimate mixture, the degree of crystallization within the blended matrix is likely to be less than that of a similar homopolymer. Reeve et al. (1994) and MacDonald et al. (1996) reported this kind of behavior for blends of L- and D enantiomers of PLA. Lower crystallinity generally implies greater elongation at break, i.e. a less brittle material. Although the cited work showed lower crystallinity in the case of blends, an opposite effect has often been reported when blending PLA with other biopolymers such as PHB (Arrieta et al. 2014b; 2015; 2017). In the latter cited cases, the enhanced crystallinity tends to imply that the blended components remained as separate phases, at least at a microscopic level.

Various additives during preparation of biopolymer films or composites have been shown to act as nucleating agents for the bioplastic matrix. Such effects have been reported for lignin (Mu et al. 2014), lignocellulose fibers (Hassaini et al. 2017), and nanocellulose particles (Srithep et al. 2013; Yu et al. 2014). Likewise, Yu et al. (2019) found that orotic acid can serve as a nucleating agent for poly(3-hydroxybutyrate-co-4-hydroxybutyrate). Thus, there will be a continual need for testing and research to better understand factors affecting the degree of crystallinity, and thus the modulus and elongational properties of bioplastics.

Strategy to repair bioplastics in the course of their recycling

In view of the expected loss of molecular mass accompanying typical melt-reprocessing of a bioplastic during its recycling, a proactive chemical approach can be used to increase the molecular mass during the processing. As shown by Beltran et al. (2019), the molecular mass of PLA can be increased by processing it with a chain extender and an organic peroxide. The pair of additives react with the PLA, leading to cross-linking, branching, and chain extension, which accompany some degradation reactions. Increased melt-viscosity was observed, consistent with a net increase in average molecular mass. Dhar et al. (2018) likewise observed increased melt-viscosity and favorable effects on properties when an organic peroxide was used during the recycling of PLA/CNC films.

Breakdown of Cellulosic Reinforcements

According to Rowell (2007), fiber breakage is a critical issue that affects the recycling of all plastic composites reinforced by cellulosic fibers. Conditions need to be selected that meet the needs for mixing while minimizing such damage. Cellulosic fiber breakage also has been observed as a result from the melt-reprocessing of biopolymer composites (Virtanen et al. 2016; Bhattacharjee and Bajwa 2017; Chaitanya et al. 2019). Figure 9 provides a pictorial representation of the expected length reduction of cellulosic reinforcing particles in the course of cycles of reprocessing.

Fig. 9. Representation of breakage of cellulosic particles on account of high shear stress encountered during recycling, especially when it entails melt-extrusion

Berzin et al. (2017) modeled the shear forces during a melt-extrusion process, providing a way to predict the breakage of reinforcing fibers. The model was compared to results obtained with flax, hemp, and sisal fibers. Different formats of twin-screw thread pattern were employed, and the average lengths, diameters, and aspect ratios of the fibers after the extrusion process were compared. Diameter reduction generally was associated with separation of cells within the multicellular fibers. Breakage generally could be predicted by cumulative strain imparted to a fiber.

Careful adjustment of the ingoing moisture content of cellulosic fibers can be used as a strategy to minimize fiber breakage during melt-extrusion. Virtanen et al. (2016) showed that it was important to avoid excessive moisture levels, which can cause hydrolytic decomposition of PLA during the processing. On the other hand, the heat during the process was able to evaporate the water from moist fibers. Possibly as a result of evaporative cooling, there was less fiber cutting, as well as minimum damage to the PLA.

Recycling to Monomers and Oligomers

To complete the discussion on the recyclability of bioplastics and their composites, additional studies reporting the recovery of monomers and oligomers from PLA and other biopolymers can be cited (Dong et al. 2012; Soroudi and Jakubowicz 2013; Hajighasemi et al. 2016; Zhu et al. 2018). In their review of the topic, Soroudi and Jakubowicz (2013) noted that chemical recycling of PLA can be done in two ways. High-temperature hydrolysis can be used when the goal is to obtain lactic acid. Thermal degradation can be used when the goal is to obtain L-L-lactide. As suggested in Fig. 10, the separation of the PLA from other plastics and non-plastic substances can be envisioned to happen in two steps. First, one would expect a gross separation of the waste items into different plastic types, as well as exclusion of non-plastic items from the stream to be devoted to PLA. At a later stage, after such processes as high-temperature hydrolysis or thermal degradation, the monomers (lactic acid or L-L-lactide) can be purified by known methods (Ghaffar et al. 2014; Komesu et al. 2017).

Fig. 10. Diagram suggesting two paths for the recycling of PLA by means of breakdown to monomers or oligomers followed by polymeric synthesis

Schliecker et al. (2003) observed that the rate of hydrolysis was influenced by the properties of PLA itself (e.g. molecular weight and crystallinity) as well as environmental conditions (e.g. temperature and pH of the reaction). Both acidic and basic conditions accelerate the hydrolysis reaction through chain-end cleavage and random ester cleavage, respectively. Studies have reported that selected catalysts (e.g. alkali earth metals, aluminum hydroxide, etc.) facilitate PLA depolymerization into L-L-lactide in thermal degradation, rendering an effective depolymerization at lower temperatures (Fan et al. 2003, 2004; Nishida et al. 2005). Alcohols were also used to break the ester bonds of PLA under mild conditions (Román-Ramírez et al. 2019, 2020). The products, alkyl lactates, are considered as valuable chemicals that can be converted into lactide and then back into PLA production. Dong et al. (2012) reported that the temperature required for depolymerization of PLA could be reduced by about 100 C by use of selected catalysts. Pedersen and Conti (2017) demonstrated such processing for polycarbonate and some other polymers using hydrothermal processing. In the presence of supercritical water, the plastics were converted to a mixture of crude oil, water-soluble organic compounds, gases, and solids. Nearly 100% of conversion was obtained in the case of polycarbonate. The yield for recovery of lactic acid from PLA, however, was near zero. Payne et al. (2019) characterized such systems as generally having high costs, but feasible in cases where recycling to obtain lactic acid is important. Liu and his colleagues (Song et al. 2013, 2018) performed a serial of studies using different types of ionic liquids to depolymerize biobased polyesters. They substantially improved the efficiency of depolymerization by selecting and tailoring the ionic liquid. Overall, chemical recycling is a promising strategy because it allows the breakdown of bioplastics into monomeric products at high purity. The main issue that remains to be resolved is the cost of the process. More work needs to be done to lower the costs before commercial application.

Alternative processing routes can be considered that involve enzymatic steps. The enzyme most often reported for PLA depolymerization is protease. Hajighasemi et al. (2016) pursued molecular recycling of PLA by an enzymatic approach carried out for three weeks at 30 C. In the most favorable system, about 90% of the PLA was converted to a mixture of monomers and oligomers. Tsuneizumi et al. (2010) showed that it was possible to separate blends of PLA and other polymers by taking advantage of differing solubilities of the components in toluene. Alternatively, the poly(butylene succinate) (PBS) in a mixture with PLA could be selectively removed by lipase, to make a cyclic oligomers that could then be reprocessed into pure PBS. Youngpreda et al. (2017) reported the multiple recycling of PLA using lipase at elevated temperature under nitrogen. The best results were obtained at 60 C. Though ecofriendly, the enzymatic strategy is slow and does not necessarily satisfy the speed and scale of industrial recycling processes. It thus needs further development.

Zhu et al. (2018) reported the preparation of a polymer based on g-butyrolacone (GBL), employing a trans-ring fusion at the alpha and beta positions. The material could be converted back and forth repeatedly between its polymeric state and its monomeric state. It was also possible to tune the crystallinity of the material by blending two enantiomers, with the mixture, giving a high level of crystallinity in this case.

As noted by Ariffin et al. (2010), molecular recycling of bioplastics is consistent with the concept of a biorefinery operation. In an analogous manner to the refining of petroleum, a biorefinery operation employs a series of separation and reaction steps to convert a crude mixture into a diversity of relatively pure compounds, from which polymers and structures can be formed. Thus, in the cited work, copolymers related to PHB were smoothly and selectively converted into crotonic acid and 2-pentenoic acid.

Work reported by Miyoshi et al. (1996) provides clues to a potential recycling strategy for PLA. The cited authors were concerned about the high price of high quality PLA, which needs to have a high molecular mass. They devised a process involving continuous melt-repolymerization, using a batch-type stirred reaction and a twin screw extruder. Such a process was able to achieve a high molecular mass of PLA starting with lactic acid. It would be logical to apply a related strategy when reprocessing PLA from other sources.


Overview of Strength Issues

The societal expectations for a fully successful bioplastic composite can be envisioned as a three-legged stool, of which the legs represent (1) high biodegradability, (2) suitability to be melt-pressed into recycled plastic products, and (3) strength properties that are competitive with widely used synthetic plastics. Regarding this third leg (i.e., the physical and mechanical properties), much of the needed discussion already has been included in a recent review article (Hubbe and Grigsby 2020). In addition, the topic has been reviewed with a focus on fracture toughness and impact strength (Al-Maharma and Sendur 2019), processing methods used to form the biocomposites (Fortunati et al. 2016), surface treatments for the cellulosic reinforcements in such composites (Verma and Jain 2017), and cellulosic nanocomposites (Moon et al. 2011). Accordingly, the present section can be relatively brief, and readers who want to go deeper can go to the cited sources.

Matrix Attributes and Strength

When one’s goal is to prepare a hard or stiff polymer that can substitute for such synthetic polymers as polystyrene or high-density polyethylene, then it makes sense to begin the process with a bioplastic having a high modulus of elasticity in its pure state. From this starting point, the final properties of the polymer can be tuned to meet a wide range of specifications, including various values of modulus, elongation at break, and other attributes, with the use of plasticizers and reinforcing particles. This situation is exemplified by PLA, the Young’s modulus of which can be as high as 3300 to 4500 MPa (Jacobsen and Fritz 1999; Baiardo et al. 2003; Mathew et al. 2005; Pillin et al. 2008; Haafiz et al. 2013; Mihai et al. 2014; Cruz Sanchez et al. 2017; Kyutoku et al. 2019). However, unmodified PLA lacks toughness when used alone (Cui et al. 2020).

Effects of Additives on Physical Properties

Plasticizing agents and physical properties

Plasticizing agents can promote greater molecular mobility of segments within a polymer, thereby decreasing its glass transition temperature (Bodaghi 2020; Moeini et al. 2020). Related effects can include decreases in elastic modulus and increases in elongation to breakage. Though the net effects of such changes can sometimes be hard to predict, plasticizers provide a tool by which technologists can adjust the properties of bioplastics to meet different goals, such as toughness and strength.

In the formulations of bioplastics, various plasticizers have been shown to decrease the glass transition temperature (Jacobsen and Fritz 1999; Baiardo et al. 2003; Mekonnen et al. 2013; Fortunati et al. 2014; Patwa et al. 2019; Moeini et al. 2020; Panaitescu et al. 2020). Likewise, increased elongation before breakage has been reported when adding plasticizing agents to PLA and other bioplastics (Jacobsen and Fritz 1999; Mekonnen et al. 2013; Cheng et al. 2014; Kamthai et al. 2015; Patwa et al. 2019). Jacobsen and Fritz (1999) reported that a large proportion of 10 wt% of PEG was required in order to achieve large increases in the elongation ability of PLA.

A surprising, but widely reported effect of certain plasticizers has been increases in the rate or extent of crystallinity of PLA and some other bioplastics. Because crystallinity implies a loss of polymer segment mobility, such an effect can be regarded as contrary to the classic functions of a plasticizer. Such behavior was reported in the following studies (Li and Huneault 2007; Arrieta et al. 2014a; 2018). Similarly, Arrieta et al. (2017) reported that PHB was able to act as a nucleating agent when blended with PLA. Li and Huneault (2007) reported that the addition of acetyl triethyl citrate and PEG as plasticizers made it possible to achieve good crystallinity within PLA even when cooling was rapid. The opposite tendencies of plasticization and inducement of higher crystallinity are illustrated schematically in Fig. 11. It would appear that an enhanced mobility of polymer segments at a critical stage in processing may be important to allow the crystallization process to occur, which is essentially the opposite of plasticization.

Fig. 11. Schematic description of two key effects on a typical stress-strain curve of plastic material: increases in crystallinity induced by the additive, vs. plasticizing effects

Polymer blends and strength

Typical plasticizing agents are monomers, and that fact can raise concerns related to leaching or uncontrolled/unwanted diffusion. In the case of the well-known plasticizer bisphenol-A, leaching from petroleum-based plastics has been tied to endocrine disruption effects (Rubin 2011). Leaching can be minimized by such means as increasing the molecular weight of the plasticizing agent, or even by covalently bonding it to polymer segments (Bodaghi 2020). Both toxicity and leaching issues need to be kept in view when formulating plasticization systems for the next generation of plastic materials, especially in food-contact and biomedical/pharmaceutical applications.

The ultimate manifestation in increasing the molecular weight of a plasticizer is to blend a bioplastic with another biopolymer. For example, Qiu and Zhou (2014) showed that poly(ethylene adipate) was very effective at the 20% level in increasing the elongation to breakage of PLA. Effects of PEG and poly(ethylene oxide) (PEO) (same polymer, but with a higher molecular mass and usually, a different route of production) likewise can be regarded as both plasticizers and potential blend components in bioplastics (Jacobsen and Fritz 1999). Oguz et al. (2019) achieved high toughness when recycled polyurethane was bended with PLA.

Effects of Cellulose Reinforcements

Cellulose fibers

As tabulated by Hubbe and Grigsby (2020), there is abundant evidence that cellulosic reinforcement in bioplastics can be used as a way to increase the elastic modulus. Published articles considered in the cited source clearly show that the effect was not sensitive to whether the reinforcing particles were large (e.g. cellulose fibers or wood particles) or very small (e.g. cellulose nanocrystals). In a broad sense, these results are consistent with a high elastic modulus of the crystalline regions of cellulose and the high aspect ratios of typical cellulose-based reinforcements, e.g. 138 GPa (Nishino et al. 1995). Some examples of cellulose fibers-reinforced PLA or PHB composites, with increased Young’s moduli, are given in the following articles (Huda et al. 2005a,b, 2006; Ludvik et al. 2007; Pilla et al. 2009a; Tawakkal et al. 2010; Mofokeng et al. 2012; Gunning et al. 2013; Way et al. 2013; Battegazzore et al. 2014; Lu et al. 2014; Mihai et al. 2014; Rapa et al. 2014; Ren et al. 2015; Gunti et al. 2016, 2018; Masmoudi et al. 2016; Liu et al. 2017; Sanchez-Safont et al. 2018; Wan and Zhang 2018; Dehghan et al. 2019; Vandi et al. 2019; Wan et al. 2019b; Panaitescu et al. 2020).


Because of the higher costs and additional processing steps required to prepare very small cellulosic reinforcing particles and to ensure their compatibility with the matrix polymer, it is important in each application to consider what might justify such costs and efforts. Nanocellulose can provide clear advantages if the product needs to be transparent or if the melted material needs to flow through extremely small nozzles. Relatively large cellulose particles might be expected to act sometimes as defects in a plastic film or structure, possibly providing a site for initiation of a crack or tear. On the other hand, as discussed in an earlier section, one needs to consider whether those same “defects” may play an important role in promoting more rapid biodegradation in cases where biodegradability is a recognized goal.

With respect to strength of plastic composites in general, the benefits of nanocellulose addition have been clearly shown in multiple studies (Hubbe and Grigsby 2020). However, relatively few studies have reported strength gains that could clearly be attributed to the presence of nanocellulose in a bioplastic matrix. Seoane et al. (2017a) prepared PHB-CNC composites using a solvent-casting procedure, which is an excellent way to avoid degrading cellulosic reinforcements. Higher strength was achieved. Srithep et al. (2013) reported nearly a two-fold increases in tensile modulus when poly(3-hydroxybutyrate-co-3-hydroxyvalerate) was reinforced by nanofibrillated cellulose. Wang et al. (2014) observed increases in tensile strength of PLA when composites were formed with lignin-containing cellulose nanofibers, using a solvent-casting method. Yu et al. (2014) achieved superior strength when CNCs were hydrophobized by the grafting of PHB-co-valerate onto their surfaces. In that form, they were able to increase the Young’s modulus of PHB-co-valerate by 95% at a 20% loading. Yin et al. (2017) achieved increases in both tensile strength and elongation to breakage when using lipase-mediated surface hydrophobization of CNCs to reinforce PLA.

Several authors have reported that nanocellulose was able to promote crystallization of the biopolymer during cooling. This is an important effect due to an expected relationship between the modulus of a polymer and its crystallinity (Humbert et al. 2011). The following studies reported evidence that nanocellulose was acting to promote crystallization of PLA or PHB-co-valerate (Yu et al. 2011; Srithep et al. 2013; Mu et al. 2014; Wang et al. 2014; Almasi et al. 2015; Arrieta et al. 2015; Hua et al. 2016; Hassaini et al. 2017; Borkotoky et al. 2018b; Seoane et al. 2019). Avella et al. (2000) reported a similar enhancement of crystallinity when ordinary wheat straw fibers were used during melt-extrusion of PHB-co-valerate.

Compatibilizers and strength

The importance of achieving compatibilization at the interface between cellulosic reinforcements and oleophilic polymers was one of the most consistent findings that emerged from an earlier review of the literature (Hubbe and Grigsby 2020). Such effects were observed with high statistical certainty in a large number of studies, spanning a wide range of sizes of reinforcing particles. The following studies showed such effects in the case of PLA and other oleophilic biopolymers (Yu et al. 2014; Almasi et al. 2015; Orue et al. 2015; de Paula et al. 2016; Hua et al. 2016; Wei et al. 2017; Yin et al. 2017, 2018, 2020; Kyutoku et al. 2019; Cui et al. 2020; Singh et al. 2020).


Based on the publications considered in this review, it is clear that considerable progress has been achieved in the preparation of bioplastic composites that have more rapid biodegradability at the end of life, melt-recyclability when recycled, and strength characteristics during their use. Strategies that have been demonstrated for different systems can be regarded as a tool set for future development work. An overall strategy to achieve the three goals of high biodegradability, retention of properties during melt-reprocessing, and improved strength characteristics during its use can be summarized briefly as follows:

  1. As a first step in any project aimed at achieving a biodegradable plastic that also meets high strength requirements, it is recommended to start with a high purity and high molecular mass biopolymer such as poly(lactic acid) or poly(hydroxybutyrate)-co-valerate having a sufficiently high elastic modulus to meet the overall needs for the intended application.
  2. Employ cellulosic reinforcing particles that have been selected to have a suitable size, depending on the needs of the final product. Cellulosic fibers of natural size can be used, except if the product requires very high smoothness, transparency, or ability to flow through tiny openings, etc.
  3. Use an effective chemical treatment to achieve sufficient compatibility between the surfaces of the cellulosic particles and the bioplastic matrix, especially in cases where the latter has a hydrophobic nature. For example, cellulosic fibers can be hydrophobized by esterification to be more compatible with PLA. Select a surface treatment system than can be readily reversed by enzymatic effects when the material is composited or if it ends up in a natural environment.
  4. Employ a “poison pill” strategy, at an optimized level, to help initiate an eventual autocatalytic breakdown of PLA or related biopolymers when placed into a natural environment or composting. For instance, this can be done by formulating PLA with PLA oligomers, the molecular mass of which determines the frequency of carboxylic acid groups.
  5. Employ a plasticizer during formulation of the material as a means of either promoting crystallization during cooling of the bioplastic or as a strategy to increase elongation before breakage. Because the two effects can work against each other, it is recommended to try several types of plasticizers over a range of dosages and processing conditions to seek optimized effects.


The authors thank the following volunteers who checked an earlier version of the document and suggested corrections and improvements: Muhammad Remanul Islam, Universiti Kuala Lumpur (UNIKL); Rakesh Kumar, Indian Inst Technol, Instrument Design Dev Ctr, Delhi, India; and Nurul Fazita Mohammad Rawi, Universiti Sains Malaysia, Division of Bioresource Technology, School of Industrial Technology.


Abdel-Rahman, M. A., Tashiro, Y., and Sonomoto, K. (2013). “Recent advances in lactic acid production by microbial fermentation processes,” Biotech. Advan. 31(6), 877-902. DOI: 10.1016/j.biotechadv.2013.04.002

Adhikari, D., Mukai, M., Kubota, K., Kai, T., Kaneko, N., Araki, K. S., and Kubo, M. (2016). “Degradation of bioplastics in soil and their degradation effects on environmental microorganisms,” J. Agric. Chem. Environ. 5, 23-34. DOI: 10.4236/jacen.2016.51003

Agarwal, M., Koelling, K. W., and Chalmers, J. J. (1998). “Characterization of the degradation of polylactic acid polymer in a solid substrate environment,” Biotechnol. Prog. 14(3), 517-526. DOI: 10.1021/bp980015p

Agrawal, A, K., and Bhalla, R. (2003). “Advances in the production of poly(lactic acid) fibers: A review,” J. Macromol. Sci. Polym. Rev. 43, 479-503. DOI: 10.1081/MC-120025975

Åkesson, D., Vrignaud, T., Tissot, C., and Skrifvars, M. (2016). “Mechanical recycling of PLA filled with a high level of cellulose fibres,” J. Polym. Environ. 24(3), 185-195. DOI: 10.1007/s10924-016-0760-0

Al-Maharma, A. Y., and Sendur, P. (2019). “Review of the main factors controlling the fracture toughness and impact strength properties of natural composites,” Mater. Res. Expr. 6(2), article no. 022001. DOI: 10.1088/2053-1591/aaec28

Almasi, H., Ghanbarzadeh, B., Dehghannya, J., Entezami, A. A., and Asl, A. K. (2015). “Novel nanocomposites based on fatty acid modified cellulose nanofibers/poly(lactic acid): Morphological and physical properties,” Food Packag. Shelf Life 5, 21-31. DOI: 10.1016/j.fpsl.2015.04.003

Angelini, S., Cerruti, P., Immirzi, B., Santagata, G., Scarinzi, G., and Malinconico, M. (2014). “From biowaste to bioresource: Effect of a lignocellulosic filler on the properties of poly(3-hydroxybutyrate),” Int. J. Biol. Macromol. 71, 163-173. DOI: 10.1016/j.ijbiomac.2014.07.038

Angelini, S., Cerruti, P., Immirzi, B., Scarinzi, G., and Malinconico, M. (2016). “Acid-insoluble lignin and holocellulose from a lignocellulosic biowaste: Bio-fillers in poly(3-hydroxybutyrate),” Eur. Polym. J. 76, 63-76. DOI: 10.1016/j.eurpolymj.2016.01.024

Anstey, A., Muniyasamy, S., Reddy, M. M., Misra, M., and Mohanty, A. (2014). “Processability and biodegradability evaluation of composites from poly(butylene succinate) (PBS) bioplastic and biofuel co-products from Ontario,” J. Polym. Environ. 22(2), 209-218. DOI: 10.1007/s10924-013-0633-8

Arcos-Hernandez, M. V., Laycock, B., Pratt, S., Donose, B. C., Nikolic, M. A. L., Luckman, P., Werker, A., and Lant, P. A. (2012). “Biodegradation in a soil environment of activated sludge derived polyhydroxyalkanoate (PHBV),” Polym. Degrad. Stabil. 97(11), 2301-2312. DOI: 10.1016/j.polymdegradstab.2012.07.035

Arias, A., Heuzey, M. C., Huneault, M. A., Ausias, G., and Bendahou, A. (2015). “Enhanced dispersion of cellulose nanocrystals in melt-processed polylactide-based nanocomposites,” Cellulose 22(1), 483-498. DOI: 10.1007/s10570-014-0476-z

Ariffin, H., Nishida, H., Hassan, M. A., and Shirai, Y. (2010). “Chemical recycling of polyhydroxyalkanoates as a method towards sustainable development,” Biotech. J. 5(5), 484-492. DOI: 10.1002/biot.200900293

Arrieta, M. P., Lopez, J., Hernandez, A., and Rayon, E. (2014a). “Ternary PLA-PHB-Limonene blends intended for biodegradable food packaging applications,” Eur. Polym. J. 50, 255-270. DOI: 10.1016/j.eurpolymj.2013.11.009

Arrieta, M. P., Lopez, J., Rayon, E., and Jimenez, A. (2014b). “Disintegrability under composting conditions of plasticized PLA-PHB blends,” Polym. Degrad. Stabil. 108, 307-318. DOI: 10.1016/j.polymdegradstab.2014.01.034

Arrieta, M. P., Fortunati, E., Dominici, F., Lopez, J., and Kenny, J. M. (2015). “Bionanocomposite films based on plasticized PLA-PHB/cellulose nanocrystal blends,” Carbohyd. Polym. 121, 265-275. DOI: 10.1016/j.carbpol.2014.12.056

Arrieta, M. P., Lopez, J., Lopez, D., Kenny, J. M., and Peponi, L. (2016). “Biodegradable electrospun bionanocomposite fibers based on plasticized PLA-PHB blends reinforced with cellulose nanocrystals,” Indust. Crops Prod. 93, 290-301. DOI: 10.1016/j.indcrop.2015.12.058

Arrieta, M. P., Samper, M. D., Aldas, M., and Lopez, J. (2017). “On the use of PLA-PHB blends for sustainable food packaging applications,” Mater. 19(9), article no. 1008. DOI: 10.3390/ma10091008

Arrieta, M. P., Peponi, L., Lopez, D., and Fernandez-Garcia, M. (2018). “Recovery of yerba mate (Ilex paraguariensis) residue for the development of PLA-based bionanocomposite films,” Indust. Crops Prod. 111, 317-328. DOI: 10.1016/j.indcrop.2017.10.042

ASTM D5338-98e1. “Standard test method for determining aerobic biodegradation of plastic materials under controlled composting conditions.”

ASTM D5988-18. “Standard test method for determining aerobic biodegradation of plastic materials in soil,”

ASTM D6400-04. “Standard specification for compostable plastics.”

ASTM D6691-17. “Standard test method for determining aerobic biodegradation of plastic materials in the marine environment by a defined microbial consortium or natural sea water inoculum,”

Austin, H. P., Allen, M. D., Donohoe, B. S., Rorrer, N. A., Kearns, F. L., Silveira, R. L., Pollard, B. C., Dominick, G., Duman, R., El Omari, K., Mykhaylyk, V., Wagner, A., Michener, W. E., Amore, A., Skaf, M. S., Crowley, M. F., Thorne, A. W., Johnson, C. W., Woodcock, H. L., McGeehan, J. E., and Beckham, G. T. (2018). “Characterization and engineering of a plastic-degrading aromatic polyesterase,” PNAS 115(19), E4350-E4357.  DOI: 10.1073/pnas.1718804115

Avella, M., Rota, G. L., Martuscelli, E., Raimo, M., Sadocco, P., Elegir, G., and Riva, R. (2000). “Poly(3-hydroxybutyrate-co-3-hydroxyvalerate) and wheat straw fibre composites: Thermal, mechanical properties and biodegradation behavior,” J. Mater. Sci. 35(4), 829-836. DOI: 10.1023/A:1004773603516

Averous, L., and Fringant, C. (2001). “Association between plasticized starch and polyesters: Processing and performances of injected biodegradable systems,” Polym. Eng. Sci. 41(5), 727-734. DOI: 10.1002/pen.10768

Baiardo, M., Frisoni, G., Scandola, M., Rimelen, M., Lips, D., Ruffieux, K., and Wintermantel, E. (2003). “Thermal and mechanical properties of plasticized poly(L-lactic acid),” J. Appl. Polym. Sci. 90(7), 1731-1738. DOI: 10.1002/app.12549

Balart, J. F., Montanes, N., Fombuena, V., Boronat, T., and Sanchez-Nacher, L. (2018). “Disintegration in compost conditions and water uptake of green composites from poly(lactic acid) and hazelnut shell flour,” J. Polym. Environ. 26(2), 701-715. DOI: 10.1007/s10924-017-0988-3

Battegazzore, D., Bocchini, S., Alongi, J., Frache, A., and Marino, F. (2014). “Cellulose extracted from rice husk as filler for poly(lactic acid): Preparation and characterization,” Cellulose 21(3), 1813-1821. DOI: 10.1007/s10570-014-0207-5

Beltran, F. R., Infante, C., Ulagares de la Orden, M., and Urreaga, J. M. (2019). “Mechanical recycling of poly(lactic acid): Evaluation of a chain extender and a peroxide as additives for upgrading the recycled plastic,” J. Cleaner Prod. 219, 46-56. DOI: 10.1016/j.jclepro.2019.01.206

Berzin, F., Beaugrand, J., Dobosz, S., Budtova, T., and Vergnes, B. (2017). “Lignocellulosic fiber breakage in a molten polymer. Part 3. Modeling of the dimensional change of the fibers during compounding by twin screw extrusion,” Composites Part A – Appl. Sci. Manufac. 101, 422-431. DOI: 10.1016/j.compositesa.2017.07.009

Bhat, M. K., and Bhat, S. (1997). “Cellulose degrading enzymes and their potential industrial applications,” Biotech. Adv. 15(3-4), 583-620. DOI: 10.1016/S0734-9750(97)00006-2

Bhattacharjee, S., and Bajwa, D. S. (2017). “Feasibility of reprocessing natural fiber filled poly(lactic acid) composites: An in-depth investigation,” Advan. Mater. Sci. Eng. 2017, article no. 1430892. DOI: 10.1155/2017/1430892

Bikiaris, D. N. (2013). “Nanocomposites of aliphatic polyesters: An overview of the effect of different nanofillers on enzymatic hydrolysis and biodegradation of polyesters,” Polym. Degrad. Stabil. 98(9), 1908-1928. DOI: 10.1016/j.polymdegradstab.2013.05.016

Biresaw, G., and Carriere, C. J. (2001). “Correlation between mechanical adhesion and interfacial properties of starch/biodegradable polyester blends,” J. Polym. Sci. Part B – Polym. Phys. 39(9), 920-930. DOI: 10.1002/polb.1067

Bocz, K., Tabi, T., Vadas, D., Sauceau, M., Fages, J., and Marosi, G. (2016.). “Characterisation of natural fibre reinforced PLA foams prepared by supercritical CO2 assisted extrusion,” Express Polym. Lett. 10(9), 771-779. DOI: 10.3144/expresspolymlett.2016.71

Bodaghi, A. (2020). “An overview on the recent developments in reactive plasticizers in polymers,” Polym. Advan. Technol. 31(3), 355-367. DOI: 10.1002/pat.4790

Bonartsev, A. P., Boskhomodgiev, A. P., Iordanskii, A. L., Bonartseva, G. A., Rebrov, A. V., Makhina, T. K., Myshkina, V. L., Yakovlev, S. A., Filatova, E. A., Ivanov, E. A., Bagrov, D. V., and Zaikov, G. E. (2012a). “Hydrolytic degradation of poly(3-hydroxybutyrate), polylactide and their derivatives: Kinetics, crystallinity, and surface morphology,” Molec. Crystals Liq. Crystals 556, 288-300. DOI: 10.1080/15421406.2012.635982

Bonartsev, A., Boskhomdzhiev, A., Voinova, V., Makhina, T., Myshkina, V., Yakovlev, S., Zharkova, I., Filatova, E., Zernov, A., Bagrov, D., Andreeva, N., Rebrov, A., Bonartseva, G., and Iordanskii, A. (2012b). “Degradation of poly(3-hydroxybutyrate) and its derivatives: Characterization and kinetic behavior,” Chem. Chem. Technol. 6(4), 385-392. DOI: 10.23939/chcht06.04.385

Bondeson, D., and Oksman, K. (2007). “Dispersion and characteristics of surfactant modified cellulose whiskers nanocomposites,” Composite Interfaces 14(7-9), 617-630. DOI: 10.1163/156855407782106519

Borkotoky, S. S., Chakraborty, G., and Katiyar, V. (2018a). “Thermal degradation behaviour and crystallization kinetics of poly (lactic acid) and cellulose nanocrystals (CNC) based micro7cellular composite foams,” Int. J. Biol. Macromol. 118, 1518-1513. DOI: 10.1016/j.ijbiomac.2018.06.202

Borkotoky, S. S., Dhar, P., and Katiyar, V. (2018b). “Biodegradable poly (lactic acid)/Cellulose nanocrystals (CNCs) composite microcellular foam: Effect of nanofillers on foam cellular morphology, thermal and wettability behavior,” Int. J. Biol. Macromol. 106, 433-446. DOI: 10.1016/j.ijbiomac.2017.08.036

Burlein, G. A., and Rocha, M. C. G. (2015). “LDPE/PHB blends filled with castor oil cake,” in: Proceedings of PPS-30: The 30th International Conference of the Polymer Processing Society, S. C. Jana (ed.), AIP Conf. Proc. 1664, article no. 030008. DOI: 10.1063/1.4918398

Carofiglio, V. E., Stufano, P., Cancelli, N., De Benedictis, V. M., Centrone, D., De Benedetto, E., Cataldo, A., Sannino, A., and Demitri, C. (2017). “Novel PHB/olive mill wastewater residue composite based film: Thermal, mechanical and degradation properties,” J. Environ. Chem. Eng. 5(6), 6001-6007. DOI: 10.1016/j.jece.2017.11.013

Castro-Aguirre, E., Iñiguez-Franco, F., Samsudin, H., Fang, X., and Auras, R. (2016). “Poly(lactic acid) – Mass production, processing, industrial applications, and end of life,” Adv. Drug. Del. Rev. 107, 333-366. DOI: 10.1016/j.addr.2016.03.010

Chaitanya, S., Singh, I., and Song, J. I. (2019). “Recyclability analysis of PLA/Sisal fiber biocomposites,” Composites Pt. B – Eng. 173, article no. UNSP 106895. DOI: 10.1016/j.compositesb.2019.05.106

Chaiwutthinan, P., Chuayjuljit, S., Srasomsub, S., and Boonmahitthisud, A. (2019). “Composites of poly(lactic acid)/poly(butylene adipate-co-terephthalate) blend with wood fiber and wollastonite: Physical properties, morphology, and biodegradability,” J. Appl. Polym. Sci. 136(21), article no. 47543. DOI: 10.1002/app.47543

Chamas, A., Moon, H., Zheng, J. J., Qiu, Y., Tabassum, T., Jang, J. H., Abu-Omar, M., Scott, S. L., and Suh, S. (2020). “Degradation rates of plastics in the environment,” ACS Sustain. Chem. Eng. 8(9), 3494-3511. DOI: 10.1021/acssuschemeng.9b06635

Chambon, F., Rataboul, F., Pinel, C., Cabiac, A., Guillon, E., and Essayem, N. (2011). “Cellulose hydrothermal conversion promoted by heterogeneous Bronsted and Lewis acids: Remarkable efficiency of solid Lewis acids to produce lactic acid,” Appl. Catal. B – Environ. 105(1-2), 171-181. DOI: 10.1016/j.apcatb.2011.04.009

Chan, C. M., Vandi, L. J., Pratt, S., Halley, P., Richardson, D., Werker, A., and Laycock, B. (2019). “Insights into the biodegradation of PHA/wood composites: Micro- and macroscopic changes,” Sustain. Mater. Technol. 21, article no. e00099. DOI: 10.1016/j.susmat.2019.e00099

Chen, C. Y., Even, M. A., Wang, J., and Chen, Z. (2002). “Sum frequency generation vibrational spectroscopy studies on molecular conformation of liquid polymers poly(ethylene glycol) and poly(propylene glycol) at different interfaces,” Macromol. 35(24), 9130-9135. DOI: 10.1021/ma020614j

Chieng, B. W., Ibrahim, N. A., Then, Y. Y., and Loo, Y. Y. (2014). “Epoxidized vegetable oils plasticized poly(lactic acid) biocomposites: Mechanical, thermal and morphology properties,” Molecules 19(10), 16024-16038. DOI: 10.3390/molecules191016024

Cinelli, P., Mallegni, N., Gigante, V., Montanari, A., Seggiani, M., Coltelli, M. B., Bronco, S., and Lazzeri, A. (2019). “Biocomposites based on polyhydroxyalkanoates and natural fibres from renewable byproducts,” Appl. Food Biotechnol. 6(1), 35-43. DOI: 10.22037/afb.v6i1.22039

Claro, P. I. C., Neto, A. R. S., Bibbo, A. C. C., Mattoso, L. H. C., Bastos, M. S. R., and Marconcini, J. M. (2016). “Biodegradable blends with potential use in packaging: A comparison of PLA/chitosan and PLA/cellulose acetate films,” J. Polym. Environ. 24(4), 363-371. DOI: 10.1007/s10924-016-0785-4

Copinet, A., Legin-Copinet, E., and Erre, D. (2009). “Compostability of co-extruded starch/poly(lactic acid) polymeric material degradation in an activated inert solid medium,” Materials 2(3), 749-764. DOI: 10.3390/ma2030749

Cosate de Andrade, M. F., Souza, P. M. S., Cavalett, O., and Morales, A. R. (2016). “Life cycle assessment of poly(lactic acid) (PLA): Comparison between chemical recycling, mechanical recycling and composting,” J. Polym. Environ. 24(4), 372-384. DOI: 10.1007/s10924-016-0787-2

Cózar, A., Echevarria, F., Gonzalez-Gordillo, J. I., Irigoien, X., Ubeda, B., Hernandez-Leon, S., Palma, A. T., Navarro, S., Garcia-de-Lomas, J., Ruiz, A., Fernandez-de-Puelles, M. L., and Duarte, C. M. (2014). “Plastic debris in the open ocean,” Proc. Nat. Acad. Sci. USA 111(28), 10239-10244. DOI: 10.1073/pnas.1314705111

Cruz Sanchez, F. A. C., Boudaoud, H., Hoppe, S., and Camargo, M. (2017). “Polymer recycling in an open-source additive manufacturing context: Mechanical issues,” Additive Manufac. 17, 87-105. DOI: 10.1016/j.addma.2017.05.013

Cubas-Cano, E., Gonzalez-Fernandez, C., Ballesteros, M., and Tomas-Pejo, E. (2018). “Biotechnological advances in lactic acid production by lactic acid bacteria: Lignocellulose as novel substrate,” Biofuels Bioprod. Biorefin. – BIOFPR 12(2), 290-303. DOI: 10.1002/bbb.1852

Cui, X. N., Ozaki, A., Asoh, T. A., and Uyama, H. (2020