Renewable Poly(Lactic Acid)Lignocellulose Biocomposites for the Enhancement of the Water Retention Capacity of the Soil

This manuscript details the preparation and characterization of a renewable biocomposite material intended as a soil conditioner based on low-molecular-weight poly(lactic acid) (PLA) and residual biomass (wheat straw and wood sawdust). The swelling properties and biodegradability of the PLA-lignocellulose composite under environmental conditions were evaluated as indicators of its potential for applications in soil. Its mechanical and structural properties were characterized by differential scanning calorimetry (DSC), thermogravimetric analysis (TGA), Fourier-transform infrared spectroscopy (FTIR), and scanning electron microscopy (SEM). Results showed that the incorporation of lignocellulose waste material into PLA increased the swelling ratio of the biocomposite by up to 300%. The application of the biocomposite of 2 wt% in soil enhanced its capacity for water retention by 10%. In addition, the cross-linked structure of the material proved to be capable of swelling and deswelling repeatedly, indicating its good reusability. Incorporating lignocellulose waste in the PLA enhanced its stability in the soil environment. After 50 days of the experiment, almost 50% of the sample had degraded in the soil.


Introduction
Growing water scarcity has emerged as the most limiting factor for crop production in agriculture, particularly in arid and semi-arid regions, and the world is searching for agricultural practices that promote water use efficiency [1]. Water-absorbing polymers are one way to enhance the water use efficiency of the soil and contribute towards conditions that are beneficial to plant growth [2]. This material is capable of absorbing large amounts of water without dissolving and desorbing the absorbed water into the soil when exposed to drought. As a soil conditioner, it improves the water retention ability of the soil and increases nutrient availability for plants. Water-absorbing materials can also act as an agent for slow-release fertilizers to minimize nutrient losses by leaching and thus decrease pollution with respect to the environment [1][2][3]. In addition, the application of such materials to soil improves soil structure, permeability, water infiltration and evaporation rates while reducing water run-off and erosion, which inversely improve crop productivity and feasible crop yields [2,4]. However, most of these materials available on the market are synthesized from petroleum-based polymers, and their high costs and hampered biodegradability have restricted applications at the agricultural scale [5]. As a direct result of the negative impact of synthetic polymers on the environment, researchers have focused on the development of a novel sustainable bipolymer based on renewable resources [6,7]. Using nature-sourced biopolymers such as proteins, polysaccharides or their combination has advantages over synthetic forms due to their low cost, inherent hydrophilicity, biodegradability, and environmental safety [4,8]. However, some bio-based hydrogels have shown poor mechanical A low-molecular-weight PLA (Mw~7 700) was synthesized from L-Lactic acid (L(+)-LA 80% (C 3 H 6 O 3 , Lach-Ner, Neratovice, Czech Republic) by a polycondensation reaction described below. Tin (II) 2-ethyl hexanoate (Sn(Oct) 2 , Sigma Aldrich, Milano, Italy) constituted the catalyst during synthesis, and acetone (C 3 H 6 O, VWR International, Stribrna Skalice, Czech Republic) was employed as the solvent of the resultant PLA. Methanol (CH 4 O, VWR International, Stribrna Skalice, Czech Republic) was used to clean the fabricated PLA, while citric acid (CA) in an anhydrous form (Lach-Ner, Neratovice, Czech Republic) was applied as a natural, non-toxic cross-linker of carboxylic groups in the given lignocellulosic materials supplementing the PLA. Chopped WS and SD were sourced as lignocellulosic waste products of agricultural activities and the wood industry in the territory of the Czech Republic.

Synthesis of PLA
The low-molecular-weight PLA was synthesized from lactic acid (LA) in accordance with a procedure by Kucharczyk et al. [22]. This commenced with LA at an amount of 400 mL that was dosed into a three-neck round-bottom flask equipped with a Teflon stirrer that was placed in an oil bath and heated at 160 • C for 3 h to remove water; for this purpose, a heating magnetic stirrer (Phoenix RSM-02 HP) was connected to laboratory apparatus for distillation under reduced pressure (20 kPa). The reaction vessel was disconnected from the vacuum pump, and 0.5 wt% of the Tin(II) 2-ethylhexanoate catalyst (related to the initial mass of the reactants) was dropwise added into it under continuous stirring at 300 rpm. The flask was then reconnected to the vacuum source at 100 Pa, and the reaction continued for 48 h at 160 • C. The resulting product was cooled to room temperature and dissolved in acetone. The polymer solution subsequently underwent precipitation in a mixture of chilled methanol and distilled water at a ratio of 1:1 (v/v) and was then filtrated by centrifugation at 13,000 rpm; this process of dissolution and precipitation was repeated twice more. The final product was washed with distilled water and dried at 45 • C for 48 h. The resultant pure PLA had a molecular weight of 7700 g/mol, as characterized by GPC analysis (Agilent PL-GCP 220 chromatographic system).

Preparation of the PLA/Lignocellulose Composite Material
The low-molecular-weight PLA in powder form was dissolved in acetone under continuous stirring at 45 • C for 30 min to obtain a PLA solution of 10 wt% (Solution 1). The cross-linking agent (CA, 10 wt% of polymer weight) was dissolved in distilled water under continuous stirring at 70 • C for 15 min (Solution 2). The WS and SD were ground in an IKA A11 B mixer and sieved to a particle size of ≤300 µm and the particle size distribution was determined on a test sieve shaker (HAVER EML 200 digital plus T). The relevant amount of WS or SD (15,35, and 60 wt%) was then added into Solution 2 at a mass ratio of 1:8 to enhance the dissolution of components, followed by thorough mixing for 30 min. This solution was heated at 100 • C, as such pre-treatment aids the reduction in hemicellulose levels in the straw, in turn heightening the compatibility of the lignocellulose material with the PLA and improving the water permeability of the PLA composite samples [23,24]. Solution 2 was then mixed with Solution 1 and gently stirred at 100 • C for 4 h until the solvent evaporated. The consequent product with plastic-like behavior was poured into molds (1.2 cm). The samples were stored at room temperature for 24 h to ensure the gradual evaporation of residual volatile solvents and avoid the rapid onset of shrinkage and fracture during the following curing process. The samples were subsequently dried at 90 • C for 2 h to enhance cross-linking points between the COOH groups of CA and cellulose. Designations of the samples and their composition as dry matter are given in Table 1, while a schematic diagram of the procedure is appended as Supplementary Data S1. * wt% related to the amount of PLA. ** wt% related to the amount of PLA solution. *** Pure PLA fabricated by a procedure described in the "PLA synthesis" section.

Structural Properties
Analysis of the cross-section morphology of samples, which had been thinly coated with a gold-palladium alloy, was carried out by scanning electron microscopy (SEM) on a Nova NanoSEM 450 unit set at an operating voltage of 10 kV. Changes in the physical structure of selected biocomposites that had been buried in soil were also evaluated. The samples were removed at predetermined intervals from the soil, cleaned and analyzed by SEM.
Alterations affecting the chemical structure of the biocomposite during degradation in soil were determined by Fourier transform infrared spectroscopy (FTIR) on a Thermo NICO-LET 6700 spectrometer, applying the attenuated total reflection (ATR) technique. Equipped with a diamond crystal, the unit was set to a resolution of 2 cm −1 and a wavenumber range of 4000-400 cm −1 . The samples were removed at predetermined intervals from the soil, cleaned and analyzed by FTIR.

Thermal Properties
The thermal stability of the hydrogels was studied by differential scanning calorimetry (DSC) and thermogravimetric analysis (TGA). DSC measurements were recorded under an inert nitrogen flow of 50 mL N2/min −1 using a DSC 1 STAR (Mettler Toledo, Belgium) Instrument. Samples of 5 mg were sealed in non-hermetic aluminum crucibles and were tested within the temperature range from −20 • C to 220 • C. The glass transition temperature (T g ) was determined as the midpoint of the initial change in slope. Melting (T m ) and cold crystallization (T cc ) temperatures were denoted as those for the peaks of the corresponding melting endotherm and crystallization exotherm, respectively, as determined during the second heating scan. The degree of crystallinity (X c ) was calculated according to the following Equation (1): where ∆Hm is melting enthalpy, ∆Hcc stands for cold crystallization enthalpy, ∆Hm0 represents the heat of fusion associated with pure crystalline PLA (93.1 J·g −1 ) and w corresponds to the weight fraction of PLA in the sample [25]. TGA analysis was performed on a Mettler-Toledo TGA/SDTA 851e instrument under nitrogen flow (10 mL/min −1 ). Samples of 5 mg were sealed in platinum crucibles, and a heating rate of 10 • C min −1 was applied at intervals, with temperatures ranging between 25 • C and 500 • C.

Swelling Ratio and Water Retention in Soil
Values for the swelling ratio (SR) of the PLA/lignocellulose biocomposite were assessed by the gravimetric method in distilled water. A dried sample was soaked in distilled water for 24 h at room temperature (24 • C). The kinetics of swelling were discerned by taking the soaking material out of the solution at defined intervals of time (1, 30, 60 and 1440 min.), removing excess media with filter paper and recording the weight. Values for SR were determined by weighing the samples before and after immersion in distilled water for 24 h by using the following Equation (2): where Ws and Wd are the masses of swollen and dried samples (g), respectively. The swelling capacity of the material was also evaluated in soil extracts, with the latter prepared according to the following procedure [26]. In brief, 100 g of air-dried commercial garden soil (pH 5.8-6.0) was dissolved in 500 mL of deionized water in an incubator shaker for 60 min at 165 rpm and centrifuged for 7 min at 1000 rpm. The supernatant was then separated out by filter paper (55 mm) from any remaining soil particles. The supernatant obtained was employed as a swelling medium, and values for SR were calculated according to Equation (2).
The efficiency of the prepared material for retaining water in soil was gauged as follows: 1 g of sample was thoroughly mixed with 50 g of dry soil and placed in a preweighted pot (W); soil without any sample present was applied as the control (W 0 ). In total, 30 mL of distilled water was added afterward, and the weight was recorded again (Wt). The extent of water retention in soil (WR, in percent) was calculated by the following Equation (3).
The above experiment for SR and WER was repeated to investigate the reusability of the material in the soil.

Degradation Studies
A soil burial test and GPC analysis of degraded samples were employed to characterize the absorbent material in order to study the effect of its composition on degradability in the soil environment. The degradation of the biocomposites in soil was assessed via a burial method under a controlled temperature (25 • C), whereby hydrogels were buried at a depth of 3 cm from the surface in a pot containing soil. Relative humidity was maintained at 40%. The samples were removed from the soil at 5-day intervals, washed gently with water to remove soil particles, cleaned and dried at 45 • C for 48 h in a vacuum oven. The degradation of the samples was calculated by the following Equation (4): where Wi is the initial weight of samples prior to any degradation, and Wf refers to the weight of a sample after specific periods of biodegradation. The average molecular weight (M w ) and molecular weight distribution of samples and the changes they underwent during degradation tests were analyzed by gel permeation chromatography (GPC) on an HT-GPC 220 system (Agilent) equipped with a dual detection system ("RI" refractive index and "VIS" viscosity detectors). The samples were dissolved in tetrahydrofuran (THF) (~2 mg.ml −1 ) overnight. Separation and detection took place using a series of mixed columns (1xB, 1xD and 1xE) (300 × 7.8 mm, Polymer Laboratories). Analysis was carried out at 40 • C in THF at a flow rate of 1 mL.min −1 and a loading volume of 100 µL. The GPC system was calibrated with narrow polystyrene standards ranging from 580 to 6,000,000 g.mol −1 (Polymer Laboratories Ltd., Church Stretton, UK). Values for mean molar mass or molecular weight (M w ), number of average molar mass (M n ) and polydispersity index (Ð = M w /M n ) for the tested samples were determined using peaks corresponding to the polymer fraction in accordance with the universal calibration method. All data were processed in Cirrus software (Agilent Technologies, Santa Clara, CA, USA) [27].

Statistical Analysis
All experiments were performed in triplicate at least three times. All data are expressed as the mean (± standard deviation (SD). Standard deviations were calculated for selected parameters according to Equation (5) and represented as error bars. Figure 1 shows that cross-section morphology was largely affected by an increase in the content of the lignocellulose-based filler. Samples with an increased amount of WS or SD possessed numerous voids and cavities, whereas those with 15% WS/SD appeared more homogeneous and compact, as the subsequent PLA that possessed greater solidity and cross-linking in the PLA-lignocellulose material was denser [24]. A simple heat-induced mechanism pertained to such cross-linking (the esterification of cellulose by citric acid), whereby citric acid dehydrated over two reactive anhydride stages, creating cross-links between adjacent cellulose chains [5]. The resultant material exhibited great strength and stability, albeit at the expense of reduced absorption capacity. However, a sample with a high amount of fillers had a porous structure with pore sizes of 100-200 microns, facilitating the absorption and retention of water molecules, which diffused into the framework of the material and heightened the swelling ratio and extent of water retention in the soil environment [28]. Differences in particle size potentially affect the structural properties and subsequent swelling capacity of a material. Particle size fractionation revealed that particles of the ground WS generally measured 2.0-2.5 mm (35%) and 3 mm (36%), while SD accounted for 35% of particles of 0.5-1.0 mm and 21% of those exceeding 1.0-1.5 mm in size as depicted in Figure 2. lose-based fillers; (A-C) samples containing 15, 35 and 60 wt% WS, respectively; (D-F) samples with 15, 35 and 60 wt% SD, respectively. Differences in particle size potentially affect the structural properties and subsequent swelling capacity of a material. Particle size fractionation revealed that particles of the ground WS generally measured 2.0-2.5 mm (35%) and 3 mm (36%), while SD accounted for 35% of particles of 0.5-1.0 mm and 21% of those exceeding 1.0-1.5 mm in size as depicted in Figure 2.

Structural Analysis
The typical FTIR-ATR spectra of the synthesized low-molecular-weight PLA, WS and PLA-WS and PLA-SD samples presented in Figures 3 and 4A,B are in agreement with results reported elsewhere [25,[29][30][31]. The positions of major absorption peaks and

Structural Analysis
The typical FTIR-ATR spectra of the synthesized low-molecular-weight PLA, WS and PLA-WS and PLA-SD samples presented in Figures 3 and 4A,B are in agreement with results reported elsewhere [25,[29][30][31]. The positions of major absorption peaks and corresponding functional groups for the straw are as follows: the one at 3370 cm −1 pertains to the stretching vibration of intermolecularly associated hydroxyl in the cellulose (-OH); 2920 cm −1 is the C-H stretching vibration of the saturated alkyl groups of the cellulose and hemicellulose; the peak at 1651 cm −1 correlates with the carbonyl group of the acetyl ester in the hemicellulose and carbonyl aldehyde in lignin [32]. The absorbance peak at 3280 cm −1 is assigned to the O-H stretching vibration of the hydroxy group of CA [33]. In Figure 4A,B, a broad peak between 3500 and 3000 cm −1 is attributed to the stretching vibration of the -OH groups of CA and lignocelluloses [34]. The absorbance band at 1755 cm −1 is attributed to a C=O stretching vibration of PLA [25] and is weaker for samples with a greater content of the lignocellulose filler. The weak band at 1650 cm −1 that occurred in WS correlates with the carbonyl group of the acetyl ester in the hemicellulose and carbonyl aldehyde in the lignin [32]. The broad weak band at 1610 cm −1 relates to the aromatic skeleton vibrations of lignin characteristics in biomass WS [35]. The peak at 1455 cm −1 typically denotes a CH 3band, and an asymmetric one appears at 1360 cm −1 [25]. The region between 1300 and 1050 cm −1 shows four intensive absorption peaks at 1184, 1132, 1089 (C-O-C stretching) and 1045 cm −1 (-OH band). The peak at 1055 cm −1 (WS sample) denotes the bending vibration of -OH and the stretching vibration of C-O in saccharide cellulose [30]. The peaks located at 869 and 755 cm −1 correspond to -C-C-stretching. The intensities of all such peaks diminished in relation to the concentration of PLA in the sample, as presented in Figure 4.
The absorbance band at 1626 cm −1 (Figure 4) indicated absorbed water in the samples. This band shows reduced intensity when citric acid was present, and this is probably caused by the involvement of hydrophilic groups in cross-links with CA; thus, the films absorbed less water [31].
Minor absorption peaks appear between 1500 cm −1 and 1400 cm −1 , reflecting unsaturated (C=C) in the molecules and potentially relating to waxes, extractives and lignin, and they are in agreement with those for lignocellulosic natural fibers. This region can also be characterized by aromatic ring vibrations and ring breathing associated with C-O stretching in the lignin [32]. absorbed less water [31].
Minor absorption peaks appear between 1500 cm −1 and 1400 cm −1 , reflecting unsaturated (C=C) in the molecules and potentially relating to waxes, extractives and lignin, and they are in agreement with those for lignocellulosic natural fibers. This region can also be characterized by aromatic ring vibrations and ring breathing associated with C-O stretching in the lignin [32].

Thermal Properties
The thermal properties of neat PLA and PLA composites were studied by DSC, and the data collected are summarized in Table 2. The DSC results revealed that increasing the concentration of WS and SD particles in the sample reduced the Tg and melting tempera-

Thermal Properties
The thermal properties of neat PLA and PLA composites were studied by DSC, and the data collected are summarized in Table 2. The DSC results revealed that increasing the concentration of WS and SD particles in the sample reduced the T g and melting temperature (T m ) of the matrix; the respective causes were the plasticizing influence of the lignin and the heightened formation of imperfect crystals during the accelerated crystallization process of biocomposites [6]. The crystallization temperature (T c ) of the biocomposites increased (106 • C ≥ 125 • C) in contrast with pure PLA (T c = 102 • C), revealing that nucleation by lignocellulose fibers hastened the PLA crystallization process [6]. The data given in Table 2 show that the presence of lignocellulose fillers raised the crystalline mass fraction (X c ) of samples. The greater X c of the PLA-WS and PLA-SD composites evidences the better compatibility of PLA macromolecules with the lignocellulose particles of WS or SD, directly resulting in an increase in accessible heterogeneous nucleation sites [36]. The increased crystallinity observed for all samples could also relate to the lower amount of amorphous lignin and hemicellulose present in untreated lignocellulose fibers [37].

Formulation
T 135  50  102  2  WS15  145  53  106  5  WS35  148  55  117  13  WS60  149  55  121  20  WSC  143  52  120  21  SD15  138  47  117  13  SD35  142  49  123  20  SD60  143  49  125  22  SDC  135  48  119  24 The thermal degradation of samples containing WS and SD at different concentrations were compared with neat PLA. As detailed in Figure 5A,C, the TGA curves for the loss in mass at 500 • C show that both lignocellulose fillers enhanced thermal stability by up to 21% and 28% in WS60 and SD60, respectively, compared to pure PLA; the likely causes are the strengthening properties of lignocellulose fibers and the cross-linking reaction of CA with the carboxylic groups of lignocellulosic materials, with the possible outcome of protecting WS60 composites against degradation by temperature. The highest thermal effect was observed for samples WS15 and SD15. Those supplemented with 15% of the lignocellulosebased fillers were stable without a significant loss in mass at up to 349 • C. In parallel with the increase in the amount of filler, a slight drop-off was observed in the maximum temperature for degradation. Findings showed that the primary effect of increasing the content of lignin reduced the degradation of PLA-WS and PLA-SD samples. The thermal stability of non-cross-linked WSC and WSD samples was slightly less than cross-linked composites, highlighting the influence of cross-linking on thermal degradation.
Compared to pure PLA, the T max of the biocomposite increased by up to 53 • C (15 wt% sample); however, increasing the content of the fillers led to a small reduction in T max , and this was probably due to the greater presence of less thermal stable components in WS or SD [37]. Taking samples with 60 wt% of filler as an example, the addition of WS reduced the maximum degradation temperature by up to 21 • C, which is over the degradation temperature observed with 15 wt% of the supplemented lignocellulose. Other authors have also reported a reduction in the thermal stability of biopolyesters by introducing cellulosic fibers [37,38]. The thermal degradation values are summarized in Table 3.
The TGA thermograms in Figure 5A,C plot the rate of change in mass and temperatures with the maximal loss in mass (T max ). The dTGA curves in Figure 5B,D depict the degradation process in three stages: the first stage (below 100 • C) primarily involves the removal of the absorbed moisture, the second stage (150-300 • C) relates to the degradation of cellulosic substances such as hemicellulose and cellulose and the final stage (310-400 • C) pertains to the degradation of non-cellulosic materials in fibers [36]. The findings demonstrate that the temperature for decomposition by biocomposites is higher than that for PLA, with a trend for a gradual decrease in temperature that is in parallel with the increase in WS and SD content.

Swelling Properties
The water absorption characteristics of the prepared biocomposites with different contents of lignocellulose fibers are given in Figures 6 and 7. The graphs show that the swelling ratios (SR) of biocomposites increase in line with the increase in WS or SD concentrations. Variances in the swelling kinetics of PLA-SW and PLA-SD materials are visible in Figure 6, and they are probably initiated by the interactions of hydrophilic lignocellulose fibers with the PLA matrix [39]. With the increase in the content of WS or SD in the composite, free -OH groups present in the cellulose and hemicellulose structure absorb water through hydrogen bonds that form between the water molecules and OH-groups on the surfaces of WS or SD particles [11]. Heating the lignocellulose biomass when preparing the biocomposites led to an increase in the porosity of the surface structure of the biomass through a partial degradation of hemicellulose and lignin, facilitating the penetration of composite materials by water molecules [24,40]. This resulted in high water ab-

Swelling Properties
The water absorption characteristics of the prepared biocomposites with different contents of lignocellulose fibers are given in Figures 6 and 7. The graphs show that the swelling ratios (SR) of biocomposites increase in line with the increase in WS or SD concentrations. Variances in the swelling kinetics of PLA-SW and PLA-SD materials are visible in Figure 6, and they are probably initiated by the interactions of hydrophilic lignocellulose fibers with the PLA matrix [39]. With the increase in the content of WS or SD in the composite, free -OH groups present in the cellulose and hemicellulose structure absorb water through hydrogen bonds that form between the water molecules and OHgroups on the surfaces of WS or SD particles [11]. Heating the lignocellulose biomass when preparing the biocomposites led to an increase in the porosity of the surface structure of the biomass through a partial degradation of hemicellulose and lignin, facilitating the penetration of composite materials by water molecules [24,40]. This resulted in high water absorption in samples with higher concentrations of WS or SD. As Figure 6 shows, a rapid increase in water absorption occurred during the initial stage of swelling, followed by a gradual course of absorption over 24 h until the samples reached an equilibrium. The highest SR was observed for samples WS60 (SR 240%) and SD60 (SR 233%).  The data presented in Figure 7 reveal that all samples were able to absorb and desorb water repeatedly, indicating their efficiency for water retention and reusability. The SR of PLA-WS/SD composites was evaluated during 10 cycles of swelling and drying. A lower capacity for water absorption was observed for samples supplemented with fewer lignocellulose fillers, with a slight increase in SR from 163 to 195% for WS15 and from 191 to 222% for SD15 in comparison to biocomposites with higher concentrations of fillers. This significant reduction in the ability to absorb water was caused by the hydrophobic nature of PLA. Samples with greater concentrations of lignocellulose fillers exhibited a slightly heightened capacity for water absorption, with WS35 and WS60 reaching SR values of 282% and 301% in the 10th cycle of swelling and drying, respectively. A similar trend was observed for PLA-SD composites, where SR increased with each swelling and drying cycle. The SR of SD35 slightly increased from 301% to 324% compared to the SR of SD60, which slightly decreased from 326% to 316% in the last such cycle. As observed in Figure  7, however, the SR of these PLA composites cross-linked with CA remained almost constant throughout the 10 cycles of swelling and drying, indicating good stability and reusability in soil. In contrast, a significant reduction in absorption capacity was observed for the non-cross-linked WSC (255 > 179%) and SDC samples, with the la er starting to disintegrate after the fifth cycle, probably due to its less stable structure and the breakup of particles during swelling tests. The samples blended with 35% and 60% of WS or SD showed far higher water absorbency as the cycles continued.

Water Retention in Soil
The results presented in Figure 8 show that adding PLA-WS/SD composite samples to the soil improved its water-holding capacity and slowed down the evaporation of irrigation water from the soil during drought conditions for at least 30 days. The soil containing PLA composites with lignocellulose fillers held and retained more water than pure soil (the control); soil samples designated as WS60 and SD60 retained over 85% of irrigated water compared to samples with low lignocellulosic content (WS15 and SD15), which demonstrated 72% and 74% in this regard at the beginning of the experiment. The water retention capacity of the control soil just equaled 66% at the initial phase of swelling, with The data presented in Figure 7 reveal that all samples were able to absorb and desorb water repeatedly, indicating their efficiency for water retention and reusability. The SR of PLA-WS/SD composites was evaluated during 10 cycles of swelling and drying. A lower capacity for water absorption was observed for samples supplemented with fewer lignocellulose fillers, with a slight increase in SR from 163 to 195% for WS15 and from 191 to 222% for SD15 in comparison to biocomposites with higher concentrations of fillers. This significant reduction in the ability to absorb water was caused by the hydrophobic nature of PLA. Samples with greater concentrations of lignocellulose fillers exhibited a slightly heightened capacity for water absorption, with WS35 and WS60 reaching SR values of 282% and 301% in the 10th cycle of swelling and drying, respectively. A similar trend was observed for PLA-SD composites, where SR increased with each swelling and drying cycle. The SR of SD35 slightly increased from 301% to 324% compared to the SR of SD60, which slightly decreased from 326% to 316% in the last such cycle. As observed in Figure 7, however, the SR of these PLA composites cross-linked with CA remained almost constant throughout the 10 cycles of swelling and drying, indicating good stability and reusability in soil. In contrast, a significant reduction in absorption capacity was observed for the noncross-linked WSC (255 > 179%) and SDC samples, with the latter starting to disintegrate after the fifth cycle, probably due to its less stable structure and the breakup of particles during swelling tests. The samples blended with 35% and 60% of WS or SD showed far higher water absorbency as the cycles continued.

Water Retention in Soil
The results presented in Figure 8 show that adding PLA-WS/SD composite samples to the soil improved its water-holding capacity and slowed down the evaporation of irrigation water from the soil during drought conditions for at least 30 days. The soil containing PLA composites with lignocellulose fillers held and retained more water than pure soil (the control); soil samples designated as WS60 and SD60 retained over 85% of irrigated water compared to samples with low lignocellulosic content (WS15 and SD15), which demonstrated 72% and 74% in this regard at the beginning of the experiment. The water retention capacity of the control soil just equaled 66% at the initial phase of swelling, with a decreasing trend during 30 days. A slight increase in water retention capacity was observed in soil samples containing the WS absorbent material (12%) in comparison with the PLA-SD (8%) and control soil samples (5.5%) at the close of the experiment.

Biodegradability
Although PLA has been verified as a naturally degradable plastic in soil or compo it has been shown to be less susceptible to microbial a acks and degradation in a natu environment than compared to other biodegradable biopolymers [6]. The biodegrada ity of PLA-WS and PLA-SD composites in soil was investigated using a soil burial t and the results are presented in Figure 9.

Biodegradability
Although PLA has been verified as a naturally degradable plastic in soil or compost, it has been shown to be less susceptible to microbial attacks and degradation in a natural environment than compared to other biodegradable biopolymers [6]. The biodegradability of PLA-WS and PLA-SD composites in soil was investigated using a soil burial test, and the results are presented in Figure 9.
Polymers 2023, 15, x FOR PEER REVIEW 15 of 20 [42]. Indeed, a PLA and wood powder/starch composite exhibited a rapid rate of degradation as the starch ratio went up, leading to effective degradation within only 75 days [42]. Introducing natural components such as fillers, therefore, could promote the biodegradability of PLA composites. It should be taken into account, though, that a variety of factors might influence the degradation of composites, e.g., particle size, the geometry of the sample, the degree of crystallinity and molecular weight, as well as environmental conditions such as temperature, pH and microbial activity [43]. Herein, samples WS60 and SD60 showed 52% and 50% degradation after 45 days of the study, respectively, within which time 63% WSC and 57% SDC had degraded. These results emphasize the more rapid biodegradability of the la er non-cross-linked materials with high lignocellulose content and make it evident that cross-linking with CA directly affects the biodegradation process. The SEM micrographs of the PLA-WS/SD composites in Figure 10 show the formation of cavities in the inner structure during the degradation process in soil. As visible in Figure 10B,C,E,F, the number of cavities in the materials increased over time, causing the disintegration of the samples during their degradation in the soil, with the probable causes being environmental conditions such as humidity, temperature and soil-related microbial activity [43]. The biodegradation of PLA-WS and PLA-SD composites took place over three distinct phases: water evaporation; the breakdown of side chains in the PLA/lignocellulosic network; and the decomposition of main chains, including cellulose and PLA [41]. When PLA/lignocellulose-based composites were buried in soil, it was observed that the crosslinking structure of the polymer network broke down, and small fragments were obtained after 45 days of the experiment. Changes in the visual appearance of the biocomposites during the soil burial test are depicted in Figure S2 in the Supplementary Materials.
The plots in Figure 9 show that the presence of the low-molecular-weight PLA slowed down the rate of the biodegradation of biocomposites, and this is probably because PLA is hydrophobic in nature, which makes it less susceptible to microbial attacks and degradation in a natural environment. The slow biodegradation process is also explained by the glass transition temperature (T g ) of PLA, as it exceeds ambient temperatures, and microorganisms capable of degrading PLA are scarce in the given environment [6]. The course record for sample WS15 was one of extended biodegradation, reaching almost 34% after 45 days in soil. The sample with the same content of SD was similar, achieving 37% of degradation by the close of a 45-day period. In contrast, samples with 35% and 60% of the same filler showed a trend of increase, and this was most likely caused by the hydrophilic lignocellulose that absorbed more water, resulting in high water evaporation and faster degradation.
A study in the literature describes the environmental degradation of paddy straw/PLA biocomposites, wherein a similar, considerable biodeterioration of the studied materials was observed, particularly those containing higher loadings of lignocellulosic fillers; the phenomenon was attributed to the hydrophilic nature of the straw, leading to high water uptake and relatively stronger colonization and activities of microorganisms [42]. Indeed, a PLA and wood powder/starch composite exhibited a rapid rate of degradation as the starch ratio went up, leading to effective degradation within only 75 days [42]. Introducing natural components such as fillers, therefore, could promote the biodegradability of PLA composites. It should be taken into account, though, that a variety of factors might influence the degradation of composites, e.g., particle size, the geometry of the sample, the degree of crystallinity and molecular weight, as well as environmental conditions such as temperature, pH and microbial activity [43].
Herein, samples WS60 and SD60 showed 52% and 50% degradation after 45 days of the study, respectively, within which time 63% WSC and 57% SDC had degraded. These results emphasize the more rapid biodegradability of the latter non-cross-linked materials with high lignocellulose content and make it evident that cross-linking with CA directly affects the biodegradation process.
The SEM micrographs of the PLA-WS/SD composites in Figure 10 show the formation of cavities in the inner structure during the degradation process in soil. As visible in Figure 10B,C,E,F, the number of cavities in the materials increased over time, causing the disintegration of the samples during their degradation in the soil, with the probable causes being environmental conditions such as humidity, temperature and soil-related microbial activity [43]. Alterations in the chemical structures of PLA-WS composites during biodegradation were also confirmed by FTIR analysis. Figure 11 shows the FTIR spectra for the WS35 sample after 35 and 50 days of biodegradation in soil. The FTIR spectra for degraded samples show peaks at 3420, 3370, 2996, and 2924, which potentially indicate the formation of the free hydroxyl groups of CA and lignocellulose during the microbial a ack of samples in soil. The intensity of some peaks for degraded PLA-WS composites was lower than those described above in Figure 4. For example, the region of 1755 cm −1 represents an expression of ester groups formed by the occurrence of cross-linking with citric acid. As the samples degrade, the strength of their carboxyl bonds diminishes. A new wide absorption band occurs at 1639 cm −1 for the degraded samples, a ributed to the water absorbed by cellulose during degradation [29]. The characteristic peaks of C-O stretching at 1213 cm −1 and 1184 cm −1 were also reduced, suggesting that disintegration takes place with respect to the aforementioned ester bonds in the cross-linked sample [44]. The peaks located at 871 and 750 cm −1 correspond to -C-C-stretching, while the peak at 871 cm −1 constitutes the amorphous phase, and the peak at 750 cm −1 constitutes the crystalline phase [25]. After 50 days of degradation, the peaks almost disappeared. Alterations in the chemical structures of PLA-WS composites during biodegradation were also confirmed by FTIR analysis. Figure 11 shows the FTIR spectra for the WS35 sample after 35 and 50 days of biodegradation in soil. The FTIR spectra for degraded samples show peaks at 3420, 3370, 2996, and 2924, which potentially indicate the formation of the free hydroxyl groups of CA and lignocellulose during the microbial attack of samples in soil. The intensity of some peaks for degraded PLA-WS composites was lower than those described above in Figure 4. For example, the region of 1755 cm −1 represents an expression of ester groups formed by the occurrence of cross-linking with citric acid. As the samples degrade, the strength of their carboxyl bonds diminishes. A new wide absorption band occurs at 1639 cm −1 for the degraded samples, attributed to the water absorbed by cellulose during degradation [29]. The characteristic peaks of C-O stretching at 1213 cm −1 and 1184 cm −1 were also reduced, suggesting that disintegration takes place with respect to the aforementioned ester bonds in the cross-linked sample [44]. The peaks located at 871 The degradation of samples in terms of change in molecular weight was gauged by GPC, as detailed in Table 4. Analyses took place at certain time intervals during degradation tests in soil. Molecular mass differed according to the content of lignocellulose, and biocomposites with 15% of WS/SD demonstrated the lowest values at the end of the experiment. Samples WS15 and SD15 degraded by approximately 50% after 50 days in soil. Within the same time frame, the molecular weight of cross-linked WS60 and SD60 samples dropped by up to 45-47%, compared to WSC (51%) and SDC (56%), evidencing the influence of cross-linking on the decomposition of materials in the soil. Another potential explanation was the presence of lignocellulosic materials due to cellulose possessing a high degree of crystallinity that hindered enzymatic actions, in addition to the association of cellulose and hemicellulose with lignin, whereby a natural barrier was created for the cellulosic portion against the a ack of microorganisms [30]. It is evident from these findings that GPC analyses provided greater objectivity for assessing the degradation of biocomposites than gauging a loss in mass by the burial test. The molecular weight of neat PLA reduced from 7700g/mol −1 to 6300 g/mol −1 after being buried in the soil for 50 days. The reason was probably the active microorganisms and moisture in the earth that could easily penetrate PLA molecules; this led to the disruption of the molecular architecture promoted by the random hydrolytic scission of ester bonds in the amorphous chains of the PLA during the degradation process [43]. Such degradations also caused an increase in the PDI of neat PLA from 1.6 to 2.4 and an increase from 1.5 to 4.0 for biocomposites. The degradation of samples in terms of change in molecular weight was gauged by GPC, as detailed in Table 4. Analyses took place at certain time intervals during degradation tests in soil. Molecular mass differed according to the content of lignocellulose, and biocomposites with 15% of WS/SD demonstrated the lowest values at the end of the experiment. Samples WS15 and SD15 degraded by approximately 50% after 50 days in soil. Within the same time frame, the molecular weight of cross-linked WS60 and SD60 samples dropped by up to 45-47%, compared to WSC (51%) and SDC (56%), evidencing the influence of cross-linking on the decomposition of materials in the soil. Another potential explanation was the presence of lignocellulosic materials due to cellulose possessing a high degree of crystallinity that hindered enzymatic actions, in addition to the association of cellulose and hemicellulose with lignin, whereby a natural barrier was created for the cellulosic portion against the attack of microorganisms [30]. It is evident from these findings that GPC analyses provided greater objectivity for assessing the degradation of biocomposites than gauging a loss in mass by the burial test. The molecular weight of neat PLA reduced from 7700 g/mol −1 to 6300 g/mol −1 after being buried in the soil for 50 days. The reason was probably the active microorganisms and moisture in the earth that could easily penetrate PLA molecules; this led to the disruption of the molecular architecture promoted by the random hydrolytic scission of ester bonds in the amorphous chains of the PLA during the degradation process [43]. Such degradations also caused an increase in the PDI of neat PLA from 1.6 to 2.4 and an increase from 1.5 to 4.0 for biocomposites.