Bacteriostatic Activity of LLDPE Nanocomposite Embedded with Sol–Gel Synthesized TiO2/ZnO Coupled Oxides at Various Ratios

Metal oxide-polymer nanocomposite has been proven to have selective bactericidal effects against the main and common pathogens (Gram-positive Staphylococcus aureus (S. aureus) and Gram-negative Escherichia coli (E. coli)) that can cause harmful infectious diseases. As such, this study looked into the prospect of using TiO2/ZnO with linear low-density polyethylene (LLDPE) to inactivate S. aureus and E. coli. The physical, structural, chemical, mechanical, and antibacterial properties of the nanocomposite were investigated in detail in this paper. The production of reactive species, such as hydroxyl radicals (•OH), holes (h+), superoxide anion radicals (O2•¯), and zinc ion (Zn2+), released from the nanocomposite were quantified to elucidate the underlying antibacterial mechanisms. LLDPE/25T75Z with TiO2/ZnO (1:3) nanocomposite displayed the best performance that inactivated S. aureus and E. coli by 95% and 100%, respectively. The dominant reactive active species and the zinc ion release toward the superior antibacterial effect of nanocomposite are discussed. This work does not only offer depiction of the effective element required for antimicrobial biomedical appliances, but also the essential structural characteristics to enhance water uptake to expedite photocatalytic activity of LLDPE/metal oxide nanocomposite for long term application.


Introduction
Microbial infection on polymer-based biomedical appliance appears to be a major threat within the healthcare industry, as it can cause infectious outbreaks and economic losses. Gram-positive Staphylococcus aureus (S. aureus) and Gram-negative Escherichia coli (E. coli) are the two major nosocomial pathogens that can lead to a wide spectrum of infections, including skin and soft tissue infections, surgical site infections (SSI), catheter-related infections, septic shock, pneumonia, endocarditis, bacteremia, and cellulitis [1,2]. Nevertheless, bacterial resistance towards antibiotics and

Materials
All chemicals used in this study were of analytical grade and purchased from Sigma Aldrich (Darmstadt, Germany). LLDPE pellets were obtained from Lotte Chemical Titan (M) Sdn. Bhd. (Kuala Lumpur, Malaysia). The chemicals were used as received without further purification.

Synthesis of TiO 2 /ZnO Nanocomposite
TiO 2 /ZnO nanocomposite prepared in different ratios (1:1, 1:3, 3:1) had been synthesized via sol-gel method. ZnO sol was prepared by adding 0.114 mole of zinc acetate dehydrate (ZAD) into ethanol and stirred at 70 • C for 5 min. Then, the mixture was stirred at room temperature for another 30 min. Subsequently, 2 mL of deionized water was added dropwise, and the stirring was continued for another 5 h. The suspension was centrifuged at 3000 rpm for 15 min. The precipitate was washed with deionized water for several times, and then dried in an oven overnight at 80 • C. The dried sample was pulverized with pestle and mortar and then calcined in air at 500 • C for 2 h. The sample was designated as 100Z.
As for TiO 2 sol, titanium isopropoxide (TTIP) was mixed in ethanol with a volume ratio of 1:4 and stirred for 30 min. Next, deionized water with a volume ratio of H 2 O:precursor solution = 1:100 was added dropwise into the TTIP mixture and stirred for 3 h. The suspension was centrifuged, washed, dried, and calcined. This sample was designated as 100T. In preparing TiO 2 /ZnO nanocomposite, ZnO and TiO 2 sols were synthesized separately by adhering to the aforementioned procedure, and then mixed according to their molar ratios (TiO 2 /ZnO = 1:3, 1:1, 3:1). The samples were designated as 25T75Z, 50T50Z, and 75T25Z for TiO 2 /ZnO ratios of 1:3, 1:1, and 3:1, respectively.

Fabrication of LLDPE/Metal Oxide Nanocomposite
The nanocomposites were prepared using the wet casting method. LLDPE pellets (1 g) were dissolved in 15 ml of 1,2-dichlorobenzene at 70 • C under continuous stirring for 10 min (solution A). After that, 5 wt % of metal oxide nanoparticles were added into 10 mL of 1,2-dichlorobenzene and sonicated for 3 min (solution B). Next, solution B was added dropwise into solution A under continuous stirring for 10 min. The mixture was poured into 90 mm diameter petri dish and oven dried at 80 • C for 18 h to generate LLDPE/metal oxide polymer film. Pure LLDPE polymer films were synthesized by adhering to the same procedure without including metal oxide. The samples were designated as LLDPE, LLDPE/100T, LLDPE/100Z, LLDPE/25T75Z, LLDPE/50T50Z, and LLDPE/75T25Z.

Characterization
The polymer nanocomposites had been characterized using multiple techniques. The morphology was observed using field emission scanning electron microscopy (FESEM, LEO GEMINI, Carl Zeiss, Oberkochen, Germany). The samples were gold-coated to avoid charging effect. The crystalline phases were analyzed using X-ray diffraction (XRD, X-Ray diffractometer D8 Advance BRUKER AXS GmbH, Karlsruhe, Germany). The degree of crystallinity (Xc) was calculated based on the following expression [36]; X c = (I c 110 + I c 220 )/(I a + I c 110 + I c 220 ) (1) where I a and I c hkl are the areas under the amorphous halo and the hkl reflections, respectively.
The melting temperature (Tm) and the enthalpy of fusion (∆H f ) were determined with a differential scanning calorimetry (DSC, Mettler Toledo, Kowloon, Hong Kong). Each nanocomposite with 10-15 mg was weighed and scanned from room temperature until 200 • C at a heating rate of 20 • C/min in an inert nitrogen (N 2 ) atmosphere (N 2 flow rate, 50 mL/min). The relative crystallinity was determined from the enthalpy value (∆H); the parameter value for 100% crystalline LLDPE was 276 J/g [37]. The relative crystallinity was calculated based on the following equation [38]: w = weight fraction of the filler or matrix in blends, ∆H f = apparent enthalpy of melting of the filler or matrix, ∆H • f 100% = extrapolated value of the enthalpy that corresponded to the melting of 100% crystalline sample (276 J/g for LLDPE). Next, the mechanical strength was examined using an Instron universal testing machine (Model TTC, Instron Corp., Buckinghamshire, UK). The metal ions released from the LLDPE nanocomposites were quantified using an inductively coupled plasma-optical emission spectrometer (ICP-OES Optima DV Perkin Elmer Inc., Branford, CT, USA). Each LLDPE nanocomposite film was (60 mm in diameter) immersed into a solution of 100 mL of deionized water, wherein 3 mL from the solution had been analyzed at 12,24,48,72, and 96 h. The role of reactive species from LLDPE nanocomposites was determined by testing the photocatalytic activity of the nanocomposite films to degrade methylene blue (MB) aqueous solution. The film was immersed in 10 ppm of 40 mL of MB and kept in dark for 1 h to attain an equilibrium adsorption state. In order to determine the photodegradation efficiency under sunlight, a number of experiments were performed from 11:00 until 14:00. At fixed time interval, the LLDPE film was removed, while the solution was withdrawn and measured using a UV-vis spectrophotometer at 644 nm. The photocatalytic experiments were repeated in the presence of radical scavengers (5 mmol/L) to assess the impact of various reactive species ( • OH, O 2 •− , h + ) on the photocatalytic reaction. Methanol (MeOH), acetonitrile (ACN), and benzoquinone (BQ) were selected as scavengers for h + , • OH radical, and superoxide anion radical O 2 •− , respectively.

Measurement of Antibacterial Ctivity
The antibacterial activity of LLDPE nanocomposites was determined using Gram-positive and Gram-negative strains. Standard ATCC (American Type Culture Collection) cultures, such as S. aureus ATCC 25923 and E. coli ATCC 25922, were employed in this study. The pathogens were grown aerobically in Luria-Bertani (LB) broth, (Merck, Darmstadt, Germany) for 24 h at 37 • C.
The antibacterial activity was assessed by adhering to the ASTM E2149-01 (ASTM Designation E 2149-01) standard. All glassware was sterilized before use. The bacterial culture was grown on a LB agar plate for 24 h. The grown culture was used to inoculate 50 mL of LB broth in a 100 mL Scott bottle. The culture was incubated at 37 • C with 115 rpm for 18-20 h. After that, the test cultures were diluted using sterilized buffer solution (pH 7.0) to reach a final concentration of (1.5-30) × 10 5 cfu/mL. In order to evaluate the antibacterial activity, the test sample was added into a 250 mL conical flask filled with 50 mL of the working bacterial dilution. The conical flasks were shaken (115 rpm) for 1, 6, 12, and 24 h at 37 • C using a mechanical shaker under visible light (electricity fluorescent fixture T5 8W). After 1 h, 100 µL aliquot of appropriate dilution was aseptically pipetted to determine the bacterial concentration via standard plate counting method. The obtained value was converted into colony forming units per millimeter (cfu/mL) and had been considered as bacteria concentration at the initial contact time (t 0 ). The bare LLDPE composite and the bacterial inoculum functioned as control. The colonies were counted and compared to those on the control plates to detect any change that might indicate inhibition of cell growth. The percentage of bacteria reduction (R%) was calculated using the following equation: where R is antibacterial rate (%), B is the average number of cell colony of sample (cfu/sample) at t 0 (1 h) contact time, and A is the average number of colonies of treated sample (cfu/sample) within specified contact time [39].

Surface Morphology of LLDPE Nanocomposites
FESEM images of bare and LLDPE nanocomposites are illustrated in Figure 1. The surface morphology of bare LLDPE ( Figure 1a) and nanocomposites with high TiO 2 content (100T, 50T50Z, and 75T25Z) (Figure 1b-d) displayed relatively similar smooth surfaces. The samples seemed to have a dense texture. On the contrary, LDPE nanocomposites with high ZnO content (100Z, 25T75Z) were rather rough with distinct voids (Figure 1e,f). This characteristic is important to increase the production and migration rates of Zn 2+ ions within the LLDPE matrix (refer to ICP analysis in Section 3.7), thus enhancing the antimicrobial activity. The nanoparticles were homogeneously distributed on the surface (inset Figure 1b a -f a and supporting Figure S1) as evident by small white dots and aggregation of several nanoparticles. The EDX analysis also revealed the presence of Zn, Ti, C and O ( Figure S2). The presence of nanoparticles on the surface is expected to enhance the antimicrobial activity rapidly.

Surface Morphology of LLDPE Nanocomposites
FESEM images of bare and LLDPE nanocomposites are illustrated in Figure 1. The surface morphology of bare LLDPE ( Figure 1a) and nanocomposites with high TiO2 content (100T, 50T50Z, and 75T25Z) (Figure 1b-d) displayed relatively similar smooth surfaces. The samples seemed to have a dense texture. On the contrary, LDPE nanocomposites with high ZnO content (100Z, 25T75Z) were rather rough with distinct voids (Figure 1e,f). This characteristic is important to increase the production and migration rates of Zn 2+ ions within the LLDPE matrix (refer to ICP analysis in Section 3.7), thus enhancing the antimicrobial activity. The nanoparticles were homogeneously distributed on the surface (inset Figure 1b a -f a and supporting Figure S1) as evident by small white dots and aggregation of several nanoparticles. The EDX analysis also revealed the presence of Zn, Ti, C and O ( Figure S2). The presence of nanoparticles on the surface is expected to enhance the antimicrobial activity rapidly.  Figure 2 portrays the XRD patterns of bare and LLDPE/metal oxide nanocomposites. As for bare LLDPE (Figure 2a), two distinct peaks were observed at 22.5° and 24.5°, which represented (110) and (220) reflections of orthorhombic LLDPE [40]. Meanwhile, for LLDPE/100T (Figure 2b), an additional anatase peak of TiO2 was noted at 2θ = 25.5° (JCPDS21-1272), indicating that most of the TiO2 nanoparticles were embedded in the polymer matrix, whereas some remained on the surface [41]. LLDPE/75T25Z seemed to share similar characteristics with LLDPE/100T as three distinctive diffraction peaks were clearly noticed (Figure 2c). Only characteristic peaks of LLDPE were recorded for LLDPE/50T50Z (Figure 2d), which can be ascribed to the existence of cubic Zn2Ti3O8 with lowdegree crystallinity [Supporting Table S1]. The characteristic peaks of LLDPE (22.5 and 24.5°) and the  Figure 2 portrays the XRD patterns of bare and LLDPE/metal oxide nanocomposites. As for bare LLDPE (Figure 2a), two distinct peaks were observed at 22.5 • and 24.5 • , which represented (110) and (220) reflections of orthorhombic LLDPE [40]. Meanwhile, for LLDPE/100T (Figure 2b), an additional anatase peak of TiO 2 was noted at 2θ = 25.5 • (JCPDS21-1272), indicating that most of the TiO 2 nanoparticles were embedded in the polymer matrix, whereas some remained on the surface [41]. LLDPE/75T25Z seemed to share similar characteristics with LLDPE/100T as three distinctive diffraction peaks were clearly noticed ( Figure 2c). Only characteristic peaks of LLDPE were recorded for LLDPE/50T50Z (Figure 2d), which can be ascribed to the existence of cubic Zn 2 Ti 3 O 8 with low-degree crystallinity [Supporting Table S1]. The characteristic peaks of LLDPE (22. (100), (002), and (101) planes, respectively) were observed for LLDPE/25T75Z and LLDPE/100Z composites [42]. Based on the outcomes derived from XRD, the main characteristic peaks of LLDPE appeared to have been retained in all samples, indicating that the incorporation of coupled TiO 2 /ZnO nanoparticles did not significantly alter the general structure of LLDPE matrix, while the interaction between oxide nanoparticles and LLDPE involved a physical process, as verified via FT-IR ( Figure 3). However, the crystallinity index of LLDPE decreased upon reaction with highly crystalline metal oxide (Table 1). It is testified that the incorporation of 100T, 75T25Z, 25T75Z, and 100Z metal oxides has appreciable influence on the crystallinity of LLDPE, in comparison to oxide with low-degree crystallinity (50T50Z). As noted, highly crystalline metal oxides reduced the degree of crystallinity of LLDPE and enhanced the water uptake through polymer matrix [43]. Hence, the antimicrobial properties of LLDPE nanocomposites were expected to enhance.  [42]. Based on the outcomes derived from XRD, the main characteristic peaks of LLDPE appeared to have been retained in all samples, indicating that the incorporation of coupled TiO2/ZnO nanoparticles did not significantly alter the general structure of LLDPE matrix, while the interaction between oxide nanoparticles and LLDPE involved a physical process, as verified via FT-IR ( Figure 3). However, the crystallinity index of LLDPE decreased upon reaction with highly crystalline metal oxide (Table 1). It is testified that the incorporation of 100T, 75T25Z, 25T75Z, and 100Z metal oxides has appreciable influence on the crystallinity of LLDPE, in comparison to oxide with low-degree crystallinity (50T50Z). As noted, highly crystalline metal oxides reduced the degree of crystallinity of LLDPE and enhanced the water uptake through polymer matrix [43]. Hence, the antimicrobial properties of LLDPE nanocomposites were expected to enhance.

FT-IR
FT-IR is one of the most widely used tools for polymer characterization due to its sensitivity towards molecular environment, as well as chain conformation and morphology, particularly concerning the detection of energy levels transition in macromolecules [44,45]. Figure 3 shows the FT-IR spectrum of bare and LLDPE/metal oxide nanocomposites. Bare LLDPE (Figure 3a) revealed characteristic peaks at 2914.63 and 2842.47 cm −1 , indicating C-H stretching vibrations of CH 2 and CH groups, respectively [46]. Another band recorded at 1642.67 cm −1 could be associated to CH 3 bonding deformation. The peaks at 1469.67 and 722.5 cm −1 are attributable to CH 2 bending deformation and rocking deformation, respectively. The FT-IR spectrum of LLDPE nanocomposites seemed to be similar to that of bare LLDPE, except for a shallow broad peak of O-H at 3400.21 cm −1 (red-dashed frame), which refers to a characteristic band for hydroxyl group at the surface of the metal oxides [47]. The presence of LLDPE characteristics in the nanocomposites were noted with slight reduction in terms of intensity, hence signifying that the chemical structures have been preserved without the formation of appreciable chemical bonds between LLDPE and nanoparticles. The peak intensity for LLDPE/50T50Z at 2914.63 and 2842.47 cm −1 was more intense, when compared to other LLDPE nanocomposites, which can be attributed to the intense stretching vibration of LLDPE matrix. Polymers 2018, 10, x FOR PEER REVIEW 8 of 18  Table 2 presents the findings obtained for Young modulus' tensile strength (TS) and percentage of elongation of bare and LLDPE nanocomposites. Bare LLDPE exhibited lower TS and Young modulus, but higher percentage of elongation, in comparison to those of nanocomposites. Upon integration of nanoparticles, TS and Young modulus seemed to increase, but reduction was recorded for the percentage of elongation, which is in agreement with other investigations [48,49]. The nanoparticles in LLDPE matrix displayed toughening and reinforcing effects that restricted the molecular motion of LLDPE polymer chains, thus enhancing the capability of LLDPE to withstand greater loads [41]. When inorganic nanoparticles were amalgamated into the LLDPE matrix, the percentage of elongation dropped drastically mainly because the nanoparticles hindered dislocation motion, thus decreasing the stress at break. On the contrary, bare LLDPE showcased sufficient space and time to orientate, especially when force was applied to the polymer chains. In order to evaluate the biocidal activity, samples that possessed more strength, moderate Young modulus, and elongation had been essential. This is because LLDPE matrix with more amorphous region may enhance the release of metal ion during water uptake.  Table 2 presents the findings obtained for Young modulus' tensile strength (TS) and percentage of elongation of bare and LLDPE nanocomposites. Bare LLDPE exhibited lower TS and Young modulus, but higher percentage of elongation, in comparison to those of nanocomposites. Upon integration of nanoparticles, TS and Young modulus seemed to increase, but reduction was recorded for the percentage of elongation, which is in agreement with other investigations [48,49]. The nanoparticles in LLDPE matrix displayed toughening and reinforcing effects that restricted the molecular motion of LLDPE polymer chains, thus enhancing the capability of LLDPE to withstand greater loads [41]. When inorganic nanoparticles were amalgamated into the LLDPE matrix, the percentage of elongation dropped drastically mainly because the nanoparticles hindered dislocation motion, thus decreasing the stress at break. On the contrary, bare LLDPE showcased sufficient space and time to orientate, especially when force was applied to the polymer chains. In order to evaluate the biocidal activity, samples that possessed more strength, moderate Young modulus, and elongation had been essential. This is because LLDPE matrix with more amorphous region may enhance the release of metal ion during water uptake.  Table 3 displays the parameters of thermal analysis (crystallization temperatures (Tc), melting temperatures (Tm), apparent enthalpy (H ), melting enthalpy (∆H o ), and degree of crystallinity (% X c )) for bare and LLDPE nanocomposites. A slight increment was noted in Tc and Tm for LLDPE nanocomposites, when compared to that for bare LLDPE. This can be ascribed to the high thermal stability of the nanocomposites from the physical hindrance of nanoparticles to the motion of LLDPE molecular chain. Nevertheless, the H value for all LLDPE nanocomposites, except for LLDPE/50T50Z, seemed to have slumped. In fact, a similar trend was noted for %X c . The crystallinity of LLDPE was influenced by the spherulitic growth. Meanwhile, in LLDPE nanocomposites, the growth of spherulites was hindered by the presence of crystalline nanoparticles between the LLDPE polymeric chains; hence, a retard in the nucleation of LLDPE crystal [50]. This is because crystalline inorganic nanoparticles do not co-crystallize with LLDPE, and thus inhibit LLDPE crystallization. Therefore, the degree of crystallinity for LLDPE nanocomposites was relatively lower than that for bare LLDPE, hence contributing to more amorphous region for better bactericidal effect. The %X c value of LLDPE/50T50Z was similar to that of LLDPE. This is attributable to the amorphous nature of nanoparticles, in which LLDPE crystallization did not decrease to a greater extend as that in LLDPE nanocomposites with crystalline nanoparticles.

Relative Production of Reactive Species (Hydroxyl Radicals, Superoxide Anion and Holes)
The photo-activated surface properties of LLDPE nanocomposites were considered for the ability of light-activated disinfection in TiO 2 /ZnO nanoparticles. Hence, the photocatalytic activity of LLDPE nanocomposites on degradation of organic dye (methylene blue, MB) was examined in the presence of radical scavengers to quantify the migration of reactive species ( • OH radical, superoxide anion, and h + ). Acetonitrile (ACN), benzoquinone (BQ), and methanol (MeOH) were selected as scavenger for • OH, O 2 •− , and h + , respectively. Figure 4 illustrates the percentage of photo-degradation of MB using LLDPE nanocomposites in the presence of radical scavengers. As observed, the photodegradation efficiency displayed by LLDPE composites with 100T, 75T25Z, 50T50Z, 25T75Z, and 100Z were 90%, 85%, 50%, 99%, and 95%, respectively, in the absence of radical scavengers; which revealed that 25T75Z had the highest release of reactive species. Upon the introduction of ACN, the photodegradation efficiency of 100Z and 25T75Z decelerated drastically by 50% and 60%, respectively ( which revealed that 25T75Z had the highest release of reactive species. Upon the introduction of ACN, the photodegradation efficiency of 100Z and 25T75Z decelerated drastically by 50% and 60%, respectively (Table 4). On the other hand, the efficiency of 100T, 75T25Z, and 50T50Z decreased marginally by 15%, 10%, and 5%, respectively. The outcomes reveal that • OH is the main reactive species in LLDPE nanocomposites. When BQ (a scavenger for O2 •− radical) was added to the reaction, the photodegradation of MB for 100T, 75T25Z, and 50T50Z remained constant, indicating zero participation of O2 •− in those samples rich with crystalline TiO2 and partially crystalline Zn2Ti3O8. Nonetheless, the efficiency of LLDPE with 100Z and 25T75Z changed by 20% and 10%, signifying that 100Z induced greater O2 •¯ from film, when compared to 25T75Z. With the addition of MeOH, the degradation of both samples (100T and 75T25Z) reduced by 50%, which demonstrated the major contribution of h + in photocatalytic reaction. Besides, the reduction in 25T75Z and 100Z by 40% and 25%, respectively, there was higher participation of h + in the photocatalytic reaction of 25T75Z, when compared to that in 100Z. Overall, the findings appear to confirm the photocatalytic activity for bacteriostatic effect of LLDPE nanocomposites rich with zincite phase (100ZnO and 25T75Z), which were primarily driven by three reactive species in a sequence of • OH > O2 •− > h + and • OH > h + > O2 •− , respectively. As for the photocatalytic activity of LLDPE nanocomposites rich with TiO2 (100T and 75T25Z), two reactive species contributed in a sequence of h + > • OH, whereas in 50Z50T, minor participation of • OH was involved.

Zinc Ion Release
The release of metal ion from LLDPE nanocomposites also has an integral role in determining the antibacterial properties of LLDPE nanocomposites. In this study, the release of zinc ions (Zn 2+ ) was evaluated by immersing LLDPE nanocomposites in water for 12 h until 96 h. After the immersion period, the water was analyzed to determine the dissolved Zn 2+ ions, as shown in Figure 5. For the entire LLDPE nanocomposites, the release of Zn 2+ increased with time, which is attributed to the disintegration of the existing intermolecular hydrogen bonding between LLDPE and water molecules. Water diffusion has an impact on the plasticity of LLDPE matrix and permits more favorable conditions for the release of Zn 2+ ions. The outputs demonstrate that the rate of Zn 2+ ion release differed for each LLDPE nanocomposite. The release of Zn 2+ ions was significantly higher for LLDPE/100Z, and followed by LLDPE/25T75Z. The other LLDPE nanocomposites, however, did not exhibit appreciable release within the fixed time. The high rate of Zn 2+ ion release showcased in LLDPE/100Z is ascribed to enhanced water diffusion characteristics and the amorphous nature of LLDPE nanocomposite. The voids in LLDPE/100Z (Figure 1f) may have accelerated the entry of water molecules and the migration of zinc ions. In light of this, LLDPE/25T75Z with steady increment could stand a better chance for long-term application, in comparison to LLDPE/100Z. This is yet to be proven and the related research is ongoing. Overall, the outcomes support low-degree polymer matrix, presence of ZnO phase, nanoparticles with hydrophilic nature, and void-controlled ion release.

Zinc Ion Release
The release of metal ion from LLDPE nanocomposites also has an integral role in determining the antibacterial properties of LLDPE nanocomposites. In this study, the release of zinc ions (Zn 2+ ) was evaluated by immersing LLDPE nanocomposites in water for 12 h until 96 h. After the immersion period, the water was analyzed to determine the dissolved Zn 2+ ions, as shown in Figure 5. For the entire LLDPE nanocomposites, the release of Zn 2+ increased with time, which is attributed to the disintegration of the existing intermolecular hydrogen bonding between LLDPE and water molecules. Water diffusion has an impact on the plasticity of LLDPE matrix and permits more favorable conditions for the release of Zn 2+ ions. The outputs demonstrate that the rate of Zn 2+ ion release differed for each LLDPE nanocomposite. The release of Zn 2+ ions was significantly higher for LLDPE/100Z, and followed by LLDPE/25T75Z. The other LLDPE nanocomposites, however, did not exhibit appreciable release within the fixed time. The high rate of Zn 2+ ion release showcased in LLDPE/100Z is ascribed to enhanced water diffusion characteristics and the amorphous nature of LLDPE nanocomposite. The voids in LLDPE/100Z (Figure 1f) may have accelerated the entry of water molecules and the migration of zinc ions. In light of this, LLDPE/25T75Z with steady increment could stand a better chance for long-term application, in comparison to LLDPE/100Z. This is yet to be proven and the related research is ongoing. Overall, the outcomes support low-degree polymer matrix, presence of ZnO phase, nanoparticles with hydrophilic nature, and void-controlled ion release.

Antibacterial Properties
Gram-positive (S. aureus) and Gram-negative (E. coli) were tested by adhering to the ASTM E 2149 test method. The results (Table 5) show that all LLDPE nanocomposites displayed remarkable efficacy against S. aureus. Nonetheless, only LLDPE nanocomposites with ZnO exhibited antibacterial activity against E. coli (Table 6). Figure 6 illustrates the bacterial reduction percentages for both S. aureus and E. coli with LLDPE nanocomposites immersed for 24 h in LB broth. LLDPE/100T and LLDPE/75T25Z inactivated S. aureus by approximately 77% and 95 %, respectively. Nevertheless, both were inactive against E. coli. LLDPE/50T50Z, LLDPE/25T75Z, and LLDPE/100Z showed exceptional bacteriostatic effect on S. aureus and E. coli. These outcomes signify that LLDPE nanocomposites rich in ZnO (LLDPE/25T75Z and LLDPE/100Z) nanoparticles could effectively destroy both pathogens.
Based on the scavenger and ion release analyses, two primary mechanisms were determined for the bacteriostatic effect: (1) inclusion of oxidative stress through the interaction of reactive species

Antibacterial Properties
Gram-positive (S. aureus) and Gram-negative (E. coli) were tested by adhering to the ASTM E 2149 test method. The results (Table 5) show that all LLDPE nanocomposites displayed remarkable efficacy against S. aureus. Nonetheless, only LLDPE nanocomposites with ZnO exhibited antibacterial activity against E. coli (Table 6). Figure 6 illustrates the bacterial reduction percentages for both S. aureus and E. coli with LLDPE nanocomposites immersed for 24 h in LB broth. LLDPE/100T and LLDPE/75T25Z inactivated S. aureus by approximately 77% and 95 %, respectively. Nevertheless, both were inactive against E. coli. LLDPE/50T50Z, LLDPE/25T75Z, and LLDPE/100Z showed exceptional bacteriostatic effect on S. aureus and E. coli. These outcomes signify that LLDPE nanocomposites rich in ZnO (LLDPE/25T75Z and LLDPE/100Z) nanoparticles could effectively destroy both pathogens.
Based on the scavenger and ion release analyses, two primary mechanisms were determined for the bacteriostatic effect: (1) inclusion of oxidative stress through the interaction of reactive species ( • OH radicals and h + ) with proteins, DNA, and lipids; and (2) release of Zn 2+ ions that may be responsible for antibacterial activity by binding to the cell membrane. The antibacterial effect of LLDPE/100T on S. aureus seemed to be mainly driven by • OH radicals and h + . Obviously, these outputs explain the superior bacteriostatic effect of LLDPE/25T75Z and LLDPE/100Z upon S. aureus, which generated more • OH radicals and h + , when compared to LLDPE/100T [51]. The presence of voids and relatively low crystallinity nature of LLDPE/25T75Z and LLDPE/100Z expedited water uptake through polymer matrix, which promoted the release of reactive species, when compared to that in compact LLDPE/100T. LLDPE/100T did not display any impact upon E. coli. This suggests that Zn 2+ may be the sole responsible species to destroy E. coli. Based on the XRD analysis, LLDPE/25T75Z and LLDPE/100Z revealed high content of ZnO phase that was hydrophilic in nature, so as to enhance water penetration via polymer matrix and consequently generate hydrated Zn 2+ ions. E. coli has a negative surface charge membrane with a layer of cytoplasm and multilayers of peptidoglycan polymer [26]. Therefore, the positively-charged Zn 2+ ion species can easily penetrate into the surface of E. coli cell wall membrane. The released Zn 2+ ions from the polymer matrix would accumulate in the cell due to electrostatic forces. This disrupts normal cellular activities, thus resulting in membrane disorder. Zn 2+ ions also have strong chemical affinity towards thiol groups of macro-biomolecules, which could inhibit protein synthesis, nucleic acid synthesis, and metabolic pathways. Interruption of trans-membrane electron transportation by Zn 2+ ions also can hamper microbial growth [26].
In this study, TiO 2 /ZnO nanocomposite (LLDPE/25T75Z) showcased better antibacterial performance against E. coli and S. aureus, in comparison to TiO 2 or ZnO nanocomposite. The discrepancy between the inactivation capabilities of these samples at 6 h and 12 h can be explained by the significant fact that TiO 2 /ZnO retained effective charge separation due to the formation of heterojunction between ZnO and c-Zn 2 Ti 3 O 8 (Supporting Figure S2), which aided the transfer of electron from conduction band (CB) of ZnO to CB of c-Zn 2 Ti 3 O 8 and h + from the valence band (VB) of c-Zn 2 Ti 3 O 8 to that of ZnO [27]. As a result, more e − and h + were made available for • OH radical formation, and were hence released from LLDPE nanocomposite to inactivate the pathogens (Figure 4). Figure 7 portrays that the release of Zn 2+ ions appeared to be greater in LLDPE nanocomposites with high ZnO weight ratio. Nevertheless, LLDPE/25T75Z displayed complete destruction of E. coli, although the release of Zn 2+ ions had been lower than that of 100Z. This is attributable to the minor effect of O 2 •− radicals generated by LLDPE/25T75Z (Figure 4) LLDPE/50T50Z appeared to be less effective below 24 h, and the reason is probably due to the dominant c-Zn 2 Ti 3 O 8 phase with low-degree crystallinity, which resulted in low photocatalytic reaction. Besides, the C-index of this sample was relatively higher, suggesting slow water uptake through the polymer matrix for ion or reactive species release. Figure 6 presents the findings for antibacterial mechanism of LLDPE nanocomposites against S. aureus and E. coli. Under sunlight illumination, a pair of negatively-charged electrons and a positively-charged electron hole had been created, as illustrated in reaction pathway (I). Upon contact with O 2 and H 2 O when they reached the surface, the O 2 •− and • OH radicals were generated, respectively (Equations (4) and (5)). These radicals are extremely reactive when in contact with bacteria. The initial oxidative damage occurs on the cell wall where LLDPE/25T75Z photocatalytic surface makes the first contact with the intact cell. With increment in contact time, the diffusion of H 2 O is also increased (pathway (II)), thus allowing O 2 •¯t o react with H + so as to generate HO 2 • radicals and subsequently produce HO 2 − (Equation (6)). These, in solution, can react with H + to form H 2 O 2 (Equation (7)). The generated H 2 O 2 is diffused into the inner membrane and causes cell membrane damage. Damage inflicted upon the cell membrane directly leads to leakage of minerals, proteins, and genetic materials, thus causing cell death. Concurrently, the leaching of Zn 2+ from LLDPE/25T75Z into the growth media that occurs in pathway (III) promotes cell death. Therefore, the toxicological mechanism of Zn 2+ plays an important role in rupturing the cell wall by degrading lipoprotein C-and N-terminals, which is the cause for the destruction of the outer membrane structure. react with H + so as to generate HO2 • radicals and subsequently produce HO2 − (Equation (6)). These, in solution, can react with H + to form H2O2 (Equation (7)). The generated H2O2 is diffused into the inner membrane and causes cell membrane damage. Damage inflicted upon the cell membrane directly leads to leakage of minerals, proteins, and genetic materials, thus causing cell death. Concurrently, the leaching of Zn 2+ from LLDPE/25T75Z into the growth media that occurs in pathway (III) promotes cell death. Therefore, the toxicological mechanism of Zn 2+ plays an important role in rupturing the cell wall by degrading lipoprotein C-and N-terminals, which is the cause for the destruction of the outer membrane structure.

Conclusions
LLDPE/metal oxide nanocomposites were synthesized through wet mixing method. The crystalline phases, the existence of metal oxide at the polymer matrix (bulk and/or surface), related voids, the degree of LLDPE crystallinity, the hydrophilic nature, the reactive species release ( • OH, h + , and Zn 2+ ion release), and the antimicrobial efficiency were studied in detail. This study discovered that LLDPE nanocomposite with high ZnO content displayed remarkable antibacterial efficiency against E. coli and S. aureus. The reactive species release ( • OH, h + , and Zn 2+ ion release) was enhanced by low crystalline LLDPE matrix with voids. Inactivation of E. coli was mainly driven by Zn 2+ ion release, whereas • OH contributed to the hampering of S. aureus. The formation of heterojunction also appears to be essential in charge carrier separation to inactivate the pathogens at a rapid rate.

Conclusions
LLDPE/metal oxide nanocomposites were synthesized through wet mixing method. The crystalline phases, the existence of metal oxide at the polymer matrix (bulk and/or surface), related voids, the degree of LLDPE crystallinity, the hydrophilic nature, the reactive species release ( • OH, h + , and Zn 2+ ion release), and the antimicrobial efficiency were studied in detail. This study discovered that LLDPE nanocomposite with high ZnO content displayed remarkable antibacterial efficiency against E. coli and S. aureus. The reactive species release ( • OH, h + , and Zn 2+ ion release) was enhanced by low crystalline LLDPE matrix with voids. Inactivation of E. coli was mainly driven by Zn 2+ ion release, whereas • OH contributed to the hampering of S. aureus. The formation of heterojunction also appears to be essential in charge carrier separation to inactivate the pathogens at a rapid rate.