Biodegradation Capabilities of Paraquat-Degrading Bacteria Immobilized on Nanoceramics

The biodegradation of paraquat was investigated using immobilized microbial cells on nanoceramics fabricated from nanoscale kaolinite. Pseudomonas putida and Bacillus subtilis, which degrade paraquat, were immobilized separately on nanoceramics (respectively called ICnc−P and ICnc−B). The attachment of bacteria to nanoceramics resulted from electrostatic force interactions, hydrogen bonding, and covalent bonding (between the cells and the support materials). The initial 10 mg L−1 concentration of paraquat in water was removed by the adsorption process using nanoceramics at 68% and ceramics at 52%, respectively. The immobilized cells on the nanoceramics were able to remove approximately 92% of the paraquat within 10 h, whereas the free cells could only remove 4%. When the paraquat was removed, the cell−immobilized nanoceramics exhibited a significant decrease in dissolved organic nitrogen (DON). ICnc−B was responsible for 34% of DON biodegradation, while ICnc−P was responsible for 22%. Ammonia was identified as the end product of ammonification resulting from paraquat mineralization.


Introduction
Paraquat, widely used as a herbicide, is well−known as an extremely toxic chemical with a human median lethal dose (LD 50 ) of 3-5 mg kg −1 [1]. Environmental contamination from paraquat, especially in Thailand's soil and water has been reported [2]. Strong soil binding makes paraquat comparatively immobile. Approximately 0.1% of the applied paraquat will be present in the soil water. The half−life varies from 1.4 to 7.2 years, depending on the soil composition [3]. Paraquat can inhibit culturable soil bacteria, reduces hydrogenase activity, increases urease activity, and has a negative effect on soil fungi [4][5][6]. It can enter the food chain when animals forage for food [7]. Long−term exposure to paraquat will result in detrimental biomagnification for both humans and animals [8]. Paraquat can enter the body via the respiratory system, digestive tract, and mucosal absorption, causing varying degrees of toxicity [9].
Paraquat has been removed from the environment using a variety of techniques. Physico−chemical processes, particularly adsorption and advanced oxidation processes, are highly effective at removing toxic chemicals [10,11]. However, these techniques necessitate a relatively high initial investment and material expense [10]. Bioremediation has evolved into an attractive and effective method for removing toxic waste from polluted environments. It is highly involved in the degradation, elimination, immobilization, or detoxification of various chemical wastes and physical hazardous materials from the environment via the all−encompassing action of microorganisms. Therefore, bioremediation is the most efficient, cost−effective, and environmentally friendly method for managing a polluted environment [12]. Cell immobilization as an advanced bioremediation technique has been introduced for degrading toxic chemicals, including paraquat [13]. Specifically, the immobilization of microbial cells on adsorbent materials is well recognized as a combination technology between adsorption and biodegradation [14].
To remove paraquat from polluted water, clay minerals such as montmorillonite, nontronite, and kaolinite are among potent adsorbents [15][16][17][18][19]. Recently, many researchers have gained attention from clay−based nanomaterials with specific chemical and biological properties. Nanoclay is a very small dimension of a specific clay and has proven to be an excellent adsorbent in removing heavy metals and organics [20][21][22][23][24]. Due to the minute size and large amount of surface area per unit volume, and surface modification potential, nanoclay is more efficient as a sorbent for water contaminants than traditional clay [24]. Montmorillonite and kaolinite are the clays most used as nano−adsorbents. Taha and Mobasser (2015) [25] reported that montmorillonite was an exceptional adsorbent in dichlorodiphenyltrichloroethane (DDT) and polychlorinated biphenyl (PCB) removal from contaminated soil and solution. Ten percent of nanoclay (Cloisite ® Na + , which is a natural montmorillonite) adsorbed 75% of PCB after 16 h of equilibrium time [25]. Rezvani and Taghizadeh (2018) [24] studied the adsorption of nitrate, lead, arsenic, and turbidity from water using nanoclay granules. Comparatively, the investigated nanoclay materials (50% of nanoclay and 50% clay by mass) have higher ion exchange capacity and contaminant removal than the corresponding clay materials (100% clay). Yue et al. (2022) [26] also reported an environmentally friendly nanoclay/sodium algenate washing agent that can effectively decontaminate oiled sand.
To acquire a high efficiency in pollutant degradation and to maximize contaminant bioavailability in cell immobilization, many materials, such as polyvinyl alcohol [27], PVA-alginate-kaolin gel beads [15], alginate [28], and biochar [29,30], have been used to support the microorganisms for biodegradation purpose. A novel environmentally friendly risk−based remediation technology has emerged that uses clay minerals in integrating microorganisms [14]. The use of clay or nanoclay in conjunction with cell immobilization (i.e., PVA-alginate-kaolin gel beads) to enhance the removal of crystal violet (CV) in water was studied [15]. Entrapping Burkholderia vietnamiensis C09V in the PVA-alginate-kaolin gel beads provided 98% removal of CV, while the CV removal by the naked beads and free cells was only 77% and 94%, respectively [15].
Immobilization of appropriate microorganisms could enhance paraquat degradation efficiency [14]. The high biomass and strong resistance to toxic chemicals of the consortium of immobilized cells contribute to the high metabolic activity of pollutant degradation [31]. According to Huang et al. (2019) [32], some bacterial and fungal species can degrade paraquat in soils and slurry. These paraquat−degrading microbial strains are Pseudomonas putida [33]; Agrobacterium tumefaciens, Aerobacter aerogenes, Pseudomonas fluorescens, and Bacillus cereus [34]; Enterobacter cloacae PQ02 [35]; and Aeromonas veronii NK67 [36]. They can effectively degrade paraquat and utilize it as a carbon and/or nitrogen source to grow [34,37]. The biodegradation rate under controlled conditions is affected by multiple variables, including temperature, pH, nutrients, initial concentration, inoculum size, and bacterial or fungal strain characteristics [32].
To date, no study has reported on applying nanoclay in supporting microorganisms on pesticide degradation, especially paraquat. From past works, the immobilization of paraquat−degrading bacteria on nanoclay should enhance the paraquat removal from contaminated water. This work demonstrates for the first time the paraquat removal by nanoclay adsorption and the paraquat degradation by the immobilization of paraquat−degrading bacteria onto the nanoclay.
In this work, the nanoclays were used innovatively to make ceramic rings (called nanoceramics), and the paraquat−degrading microorganisms, Pseudomonas putida TISTR 1522 (or P. putida) and Bacillus subtilis TISTR 1248 (or B. subtilis), were individually immobilized onto the nanoceramics (called bio−nanoceramics) for paraquat removal from a synthetic medium. The nanoceramics played a role as an excellent adsorbent as well as a cell support material. As far as we know, this is the first research study to report nanoceramics' potential as immobilization supports for bacterial cells with a capability in paraquat adsorption and biodegradation, simultaneously.
This work focused on paraquat degradation and mineralization by bio−nanoceramics (cell−immobilized nanoceramics). The removal efficiency as well as the degradation kinetics of paraquat in a synthetic medium was examined. In addition, the reduction of dissolved organic nitrogen (DON) was used as a biomineralization efficiency indicator of paraquat.

Nanoceramic Synthesis
Nanoclay (kaolinite), biochar, and polystyrene foam were mixed at a weight ratio of clay:biochar:foam of 6:0.5:0.5. The mixture (200 g total) was added to 70 mL of tap water, mixed, then incubated at 28 • C overnight. Subsequently, the incubated mixture was slip cast into a ring−shaped ceramic, 1.9 ± 0.15 cm in diameter and 2.5 ± 0.22 cm in length, before drying under natural sunlight for 2-3 d. The ceramic rings were calcined at 800 • C for 2 h and sterilized by autoclave at 121 • C for 15 min before use.
For ceramic surface modification, 32 g of the sterile ceramics were dipped into 200 mL of 1M NH 4 F solution for 30 min, then washed with sterilized deionized (DI) water 3-4 times. After that, they were dehydrated at 80 • C for 4 h in an oven and then stored in a sterile box for further use. The obtained ceramics were called nanoceramics (labeled as C nc ). Furthermore, the regular kaolinite (non−nano size) following the same procedure as C nc and also calcinated at 800 • C and labeled as C c were used to produce the control ceramics.

Cell Immobilization on Ceramic Materials
The acclimatized cells with paraquat were used to prepare a cell suspension. The freeze−dried bacterial cells (B. subtilis or P. putida) were activated in a synthetic medium (0.057 g NH 4 PO 4 , 0.017 g K 2 HPO 4 , 0.043 g NaCl, and 0.043 g MgSO 4 .7H 2 O in 1 L of sterile distilled water), mixed with 10% LB broth and 10 mg L −1 paraquat, and incubated−shaken at 120 rpm, 28 • C, for 6 d. This cell solution was sub−cultured on a PCA plate that had been mixed with 10 mg L −1 paraquat and then incubated at 37 • C for 24-48 h. Prior to immobilization, 5 active colonies of the acclimated cells from the PCA were incubated in 500 mL of fresh LB broth on a shaker (120 rpm) at 28 • C for 18 h (called cell suspension). The initial cell adhesion was measured by the plate count technique. Briefly, 1 mL of the cell suspension was diluted in 9 mL sterile phosphate−buffered saline (PBS) and well mixed (labeled as 10 −1 ). A ten−fold serial dilution from 10 −1 to 10 −7 was conducted. After that, 0.1 mL of the sample was put on a PCA plate. Dilutions were duplicated and three dilutions at 10 −5 to 10 −7 were further used. All the sample plates were incubated for 24 h at 37 • C. The total number of colonies was counted, calculated, and reported (CFU mL −1 ) as in Equation (1) [38].
For cell immobilization, a ratio of C nc (g) and cell suspension (mL) of 1:10 was applied. Briefly, the sterile ceramics were dropped into the cell suspension (approximately 10 7 CFU mL −1 of the initial cell concentration) and incubated−shaken (100 rpm) at 28 • C for 2 h. The cell−immobilized ceramics, called bio−nanoceramics (labeled as IC nc ), were dried for 10 min at room temperature. Then, the first adhered cells on IC nc were enumerated using the plate count technique and reported (CFU g −1 ) as in Equation (2). Briefly, one loaf of sample (3.2 g) was mashed to powder. The powder sample was added to 9 mL sterile PBS (labeled as 10 −1 ). Then, a 10−fold serial dilution from 10 −1 to 10 −6 was performed and spread on PCA plates in the same manner as the cell suspension as described above [38].

Characterization of Nanoceramic and Bio−Nanoceramic
A scanning electron microscope (SEM) (Leo1455VP, Leo Electronics Co., Ltd., Tokyo, Japan) was used to examine the morphology of the cells and ceramic surfaces (of IC nc ). Sample preparation followed a slightly modified method from [39]. The sample size was 1.5 to 2 mm in diameter and 0.4 to 0.6 mm in height. Three steps of the sample preparation process are as follows. In the fixation step, 2.5% glutaraldehyde was dropped on the sample for 1 h, followed with 1% osmium tetroxide for 2 h. In the dehydration step, 30% ethanol was first dropped on the samples for 15 min prior, followed by a concentration of 50%, 70%, 90%, and 100%, respectively. Finally, for the drying step, the sample was soaked in hexamethyldisilazane for 5 h. All the steps were conducted in a chemical fume hood. The samples were mounted on stubs and coated with gold before being analyzed with the SEM.
A Zetasizer (Nano ZS90, Malvern Panalytical Malvern, UK) was used to measure the point of zero charge (pH pzc ) of the C nc and bacteria. The cell solution was prepared by mixing half of the colony in 5 mL of 10 mM NaCl solution [40]. The surface areas of the C nc and IC nc were examined using a Multipoint surface area analyzer (BET) (TriStar II 3020, Micromeritics Inc., Norcross, GA, USA).

Adsorption and Paraquat Biodegradation Using Ceramic, Nanoceramic and Bio−Nanoceramic
An amount of 30 g of C c (without cells), C nc (without cells), or IC nc was experimented on in a batch reactor, a 1500 mL beaker (Pyrex ® ) with an LED digital magnetic hotplate stirrer (TOPTION Instruments, China) under 28 • C for 24 h. The 1 L of investigated synthetic medium consisted of 0.057 g NH 4 PO 4 , 0.017 g K 2 HPO 4 , 0.043 g NaCl, and 0.043 g MgSO 4 . 7H 2 O in distilled water with 10 mg L −1 paraquat (5.6 mg L −1 as C, 1.1 mg L −1 as N). The liquid samples were withdrawn periodically during the 10 h experimental period. The samples were put through a 0.22 µm pore−size membrane filter (MF−Millipore™), and the filtrates were used for the residual paraquat concentration analysis. For dissolved inorganic nitrogen (DIN) species analysis, i.e., ammonium nitrogen, nitrite nitrogen, nitrate nitrogen, and total dissolved nitrogen, the solution samples were filtered using a 0.45 µm pore−size nylon syringe (EZFlow ® ). All experiments were triplicated, and the minimum and maximum values were reported. In addition, the amount of immobilized cells on IC nc and leaching cells in the synthetic solution at the initial and final treatment time (24 h) of the experiment were determined by the plate count technique [41].
Zero − order kinetics : First − order kinetics : ln where C 0 is the initial concentration, C is the concentration at time t, and k is the biodegradation rate constant.

DON Biodegradation Degree
The degradation experiment was conducted in the same manner as mentioned in Section 2.5. Free cells, IC nc −P, and IC nc −B were performed. Liquid samples were withdrawn periodically 30 mL/time for dissolved inorganic nitrogen (DIN) species analysis, i.e., ammonium nitrogen, nitrite nitrogen, nitrate nitrogen, and total dissolved nitrogen. The solution samples were separated through a 0.45 µm pore−size nylon syringe filter (EZFlow ®, VWR, Atlanta, GA, USA). All experiments were in triplicate, and both the minimum and maximum values are presented.

Analytical Methods
For the analysis of paraquat concentration, liquid chromatography−mass spectrometry, (LC−MS) (Agilent 6120, Santa Clara, CA, USA) was performed. Poroshell 120 HILIC−Z (Santa Clara, CA, USA), 2.1 × 100 mm, 2.7 µm (Agilent No.685775−924) was used for the chromatography column. The paraquat analysis was conducted following the USEPA 549.2 method from the U.S. Environmental Protection Agency for the analysis of paraquat and diquat with reversed phase/ion−pair extraction C8 SPE cartridges followed by ion−pair liquid chromatography. The paraquat retention time was 15 min and the detection limit of the paraquat was 0.01 mg L −1 .
Focusing on the concentrations of dissolved inorganic nitrogen (DIN) species, the cadmium reduction method was performed to measure NO 3 −N [43], and NO 2 −N and NH 3 −N were measured by the colorimetric and the phenate methods, respectively [44,45]. For TDN analysis, the persulfate chemical wet oxidation method was used [45]. dissolved organic nitrogen (DON) was calculated as the difference between measured total dissolved nitrogen (TDN) and the sum of measured DIN species using Equation (7) [41]. The DON biodegradation degree through the cell−immobilized ceramics was determined as in Equation (8) [41].
where DON i and DON t are DON before and after the paraquat treatment at time t, respectively. DON bi and DON bt are DON before and after paraquat treatment at time t for the control (sterile synthetic medium).

Statistical Analysis
To determine the reliability and significance of the findings, a statistical analysis was performed on the experiment results. All experiments were conducted in triplicate, and the results are presented as the mean standard deviation (SD). We used the coefficient of determination (R 2 ) and the residual sum of squares to evaluate the biodegradation kinetics models' fit (RSS). For the observed data, the model with the highest R 2 and the lowest RSS was deemed to be the best fit. The SPSS statistical software package was utilized for statistical analysis. Excel was used to construct graphs.

Characteristics of Ceramic and Cell−Immobilized Ceramic
The SEM images of the surface morphologies for C nc and IC nc are shown in Figure 1. The bacilli or rod shape of both P. putida and B. subtilis is clearly observed on the surface of the cell−immobilized nanoceramics with P. putida (labeled as IC nc −P) in Figure 1b, and B. subtilis (labeled as IC nc −B) in Figure 1c. The rod−shaped bacteria do not appear in C nc , as shown in Figure 1a. The surface area of nanoceramics without cells or C nc was 12.95 m 2 /g. In comparison with cell−immobilized nanoceramics, this value is lower due to the bacteria coverage on the ceramic surface. The surface areas of the cell−immobilized nanoceramics were 7.95 and 8.42 m 2 /g for IC nc −P and IC nc −B, respectively.
The pH pzc values of C nc , P. putida, and B. subtilis were 1.5, 2.4, and 0.4, respectively ( Figure S1a,b). With the immobilization of P. putida and B. subtilis on the nanoceramic surface, the pH pzc values of IC nc −P and IC nc −B are slightly changed to 2.6 and 1.0, respectively ( Figure S1c).
Apparently, at neutral pH (pH 7), the surface of C nc was negatively charged (negative zeta potential of −21.0 mV). Many negative charged sites are most likely caused by the deprotonation of hydroxyl groups at the edges of the nanoceramic surface, for example −Si−O−Al−O− [46]. This surface charge promoted a strong attachment between the nanoceramic surface and the bacterial cells. The ceramic surface was negatively charged and contained the hydroxyl group at the broken edges of the kaolinite clay [47]. The bacterial surface was dominated by a negative charge and many functional groups, (i.e., hydroxyl, carboxyl, phosphoryl, and amide groups) [48]. Thus, the attachment of immobilized cells on IC nc likely arose from the interactions of the electrostatic force and hydrogen and covalent bonding between the cells and nanoceramics.
Toxics 2023, 11, x FOR PEER REVIEW 6 of 17 determination (R 2 ) and the residual sum of squares to evaluate the biodegradation kinetics models' fit (RSS). For the observed data, the model with the highest R 2 and the lowest RSS was deemed to be the best fit. The SPSS statistical software package was utilized for statistical analysis. Excel was used to construct graphs.

Characteristics of Ceramic and Cell−Immobilized Ceramic
The SEM images of the surface morphologies for Cnc and ICnc are shown in Figure 1. The bacilli or rod shape of both P. putida and B. subtilis is clearly observed on the surface of the cell−immobilized nanoceramics with P. putida (labeled as ICnc−P) in Figure 1b The pHpzc values of Cnc, P. putida, and B. subtilis were 1.5, 2.4, and 0.4, respectively ( Figure S1a,b). With the immobilization of P. putida and B. subtilis on the nanoceramic surface, the pHpzc values of ICnc−P and ICnc−B are slightly changed to 2.6 and 1.0, respectively ( Figure S1c).
Apparently, at neutral pH (pH 7), the surface of Cnc was negatively charged (negative zeta potential of −21.0 mV). Many negative charged sites are most likely caused by the deprotonation of hydroxyl groups at the edges of the nanoceramic surface, for example −Si−O−Al−O− [46]. This surface charge promoted a strong a achment between the nanoceramic surface and the bacterial cells. The ceramic surface was negatively charged and contained the hydroxyl group at the broken edges of the kaolinite clay [47]. The bacterial surface was dominated by a negative charge and many functional groups, (i.e., hydroxyl, carboxyl, phosphoryl, and amide groups) [48]. Thus, the a achment of immobilized cells on ICnc likely arose from the interactions of the electrostatic force and hydrogen and covalent bonding between the cells and nanoceramics.

Paraquat Adsorption Using Nanoceramics
The efficiency of paraquat removal using Cnc at pH 7 is shown in Figure 2a. For comparison, the removal performance using ceramic formed by the kaolinite clay (labeled as Cc) was also investigated. The paraquat in the solution gradually decreased in both cases. Apparently, the Cnc provided a higher performance in paraquat adsorption than Cc. After 5 h, the paraquat removal reached 68% and 52% using Cnc and Cc, respectively. The results clearly indicated that using the nanoclay to produce the ceramic matrices positively influenced paraquat adsorption. Nanoclay made an excellent adsorbent to remove organics and heavy metals [20][21][22][23]. Rezvani and Taghizadeh (2018) [24] demonstrated that the nanoceramic granules provide excellent removal of several water pollutants such as lead, arsenic, and nitrate, and turbidity. The superb ability in paraquat adsorption of Cnc (12.95 m 2 /g) in this work is possibly due to a higher specific surface of this material than that of the Cc (7.35 m 2 /g).

Paraquat Adsorption Using Nanoceramics
The efficiency of paraquat removal using C nc at pH 7 is shown in Figure 2a. For comparison, the removal performance using ceramic formed by the kaolinite clay (labeled as C c ) was also investigated. The paraquat in the solution gradually decreased in both cases. Apparently, the C nc provided a higher performance in paraquat adsorption than C c . After 5 h, the paraquat removal reached 68% and 52% using C nc and C c , respectively. The results clearly indicated that using the nanoclay to produce the ceramic matrices positively influenced paraquat adsorption. Nanoclay made an excellent adsorbent to remove organics and heavy metals [20][21][22][23]. Rezvani and Taghizadeh (2018) [24] demonstrated that the nanoceramic granules provide excellent removal of several water pollutants such as lead, arsenic, and nitrate, and turbidity. The superb ability in paraquat adsorption of C nc (12.95 m 2 /g) in this work is possibly due to a higher specific surface of this material than that of the C c (7.35 m 2 /g). In addition, the surface charge of Cnc and Cc as measured by pHpzc and negative zeta potential was also another important factor influencing the adsorption efficiency of both ceramics. From this work, the pHpzc values of Cnc and Cc were 1.5 and 2.5, respectively. At experimented pH (pH 7) for paraquat adsorption, the negative zeta potentials of Cnc and Cc were −21.0 mV and −12.34 mV, respectively. Apparently, the negatively charged surfaces of nanoceramic can promote a stronger binding a achment between the nanoceramic surface and the paraquat than those occurred on the ceramic surface. This surface chemistry possibly resulted from the electrostatic force, and hydrogen and covalent bonding between paraquat and nanoceramics. To enhance the synergistic effect between adsorption and biodegradation, the nanoceramic material was chosen as the microbial support for paraquat degradation and mineralization by cell−immobilized nanoceramics, as discussed in the next section.
The solution's pH effect on the nanoceramics was also investigated. The residual par- In addition, the surface charge of C nc and C c as measured by pH pzc and negative zeta potential was also another important factor influencing the adsorption efficiency of both ceramics. From this work, the pH pzc values of C nc and C c were 1.5 and 2.5, respectively. At experimented pH (pH 7) for paraquat adsorption, the negative zeta potentials of C nc and C c were −21.0 mV and −12.34 mV, respectively. Apparently, the negatively charged surfaces of nanoceramic can promote a stronger binding attachment between the nanoceramic surface and the paraquat than those occurred on the ceramic surface. This surface chemistry possibly resulted from the electrostatic force, and hydrogen and covalent bonding between paraquat and nanoceramics. To enhance the synergistic effect between adsorption and biodegradation, the nanoceramic material was chosen as the microbial support for paraquat degradation and mineralization by cell−immobilized nanoceramics, as discussed in the next section.
The solution's pH effect on the nanoceramics was also investigated. The residual paraquat under the influence of pH using C nc adsorbent is illustrated in Figure 2b. When the solution pH increased from pH 1.0 to pH 11, paraquat removal performance obviously increased and the highest removal of paraquat by C nc occurred at a pH of 11.0. Because the solution pH was much more than the pH pzc (at 1.5), the negatively charged sites of the nanoceramic surface can lead to the electrostatic attraction with the positively charged sites of paraquat molecules. The small fraction of paraquat removal with the acidic solution pH could be ascribed by the electrostatic repulsion between the surface charge of the adsorbent and the cation of paraquat surface. The adsorption capacity (q e ) of paraquat from each pH is also included in Figure 3b. Apparently, the paraquat adsorption capacity decreased as the solution pH increased. At a high pH (in basic region), the increasing amount of negatively charged sites of the nanoceramic caused an increase in the adsorbed paraquat. This behavior was in good agreement with the previous work using modified bentonite clay for paraquat removal from an aqueous solution [49]. The paraquat adsorption onto the clay surface was an exothermic and a spontaneous process. The maximum value of the equilibrium amount of adsorbed paraquat on the nanoceramic at pH 11 at 65.8 µmol/g was slightly lower than the illite (72.3 µmol/g) and clay mineral (73.1 µmol/g) at the same pH [19,50].   Figure 3 shows paraquat removal in the synthetic medium by the ICnc. The paraquat removal readily occurred by both ICnc−P and ICnc−B, while the Cnanoceramic (without cells) could remove paraquat gradually. The 10 mg L −1 initial concentration of paraquat was decreased to approximately 1 mg L −1 within 6 h by both ICnc−P and ICnc−B. In contrast, after 6 h, the initial concentration of paraquat remaining in the synthetic medium treated  Figure 3 shows paraquat removal in the synthetic medium by the IC nc . The paraquat removal readily occurred by both IC nc −P and IC nc −B, while the Cn anoceramic (without cells) could remove paraquat gradually. The 10 mg L −1 initial concentration of paraquat was decreased to approximately 1 mg L −1 within 6 h by both IC nc −P and IC nc −B. In contrast, after 6 h, the initial concentration of paraquat remaining in the synthetic medium treated by C nc was approximately 28%. Cell immobilization on nanoceramics enhanced paraquat removal, compared to nanoceramics without immobilized cells (C nc ).

Role of Nanoceramics and Immobilized Cells on Paraquat Degradation
The paraquat removal efficiency of C nc , IC nc −P, and IC nc −B reached 30%, 29%, and 28%, respectively, within 30 min. Results show that the adsorption plays a more important role than biodegradation at the beginning of the paraquat removal. The adsorption process could explain the instant removal of paraquat by the IC nc −P and IC nc −B at the early stage of the experiment. The adsorption mechanism could refer to the attraction and repulsion of the paraquat molecule and the surface charge of the nanoceramics during the experiment. Recalling point of zero charge values of C nc , IC nc −P, and IC nc −B were 1.5, 2.6, and 1.0, respectively; negatively charged surfaces of nanoceramics are observed when the solution pH is higher than pH pzc . As the pK a of cationic paraquat was approximately 9-9.5 cationic [51], the positive charge of the molecule is prominent at neutral solution (pH 7). Consequently, the positive paraquat molecule promptly adsorbed on the negatively charged surface of the ceramic. Chen et al. (2013) [52] conducted cell immobilized on the calcium alginate beads impregnated with activated carbon fiber and concluded that the adsorption on the solid surface is associated with the removal of pollutant during the beginning stage, and this is in good agreement with our results in this study. Nanoceramics removed approximately 72% of paraquat within 10 h. The result echoes paraquat adsorption onto a ceramic surface through electrostatic interaction. The efficiency of clay minerals, such as kaolinite, zeolite, and montmorillonite, as an absorbent in removing paraquat from an aqueous solution has been reported in many studies [15][16][17][18][19].
The synergistic effect between the adsorption and biodegradation was clearly observed after 30 min (Figure 3). The paraquat concentrations in the reactors with IC nc -P and IC nc −B were more rapidly reduced than that with C nc . Interestingly, the immobilized cells on the nanoceramics could subsequently degrade the absorbed paraquat. A similar occurrence was observed in the removal of other pollutants by Lin et al. (2010) [53] and Massalha et al. (2010) [54]. Lin et al. (2010) [53] reported that the immobilization technique significantly enhanced the efficiency of pyridine degradation by Paracoccus sp. strain KT−5. The mixture of clay and AC contributes to the cell immobilization and enhances phenol at high concentrations, as shown by Massalha et al. (2010) [54].
To clearly illustrate the role of the microbial cells and nanoceramics in this process, the sterilized cells of P. putida (IC nc −P) and B. subtilis (IC nc −B) were applied for paraquat removal, as shown in Figures 3a and 3b, respectively. Among the three materials consisting of C nc , IC nc (Living cells), and IC nc (Sterilized cells), the sterilized cells provided the lowest efficiency in paraquat removal. With the dead cells occupying the nanoceramic surface, paraquat removal efficiency was less than that of the pristine nanoceramics. In addition, the paraquat adsorption ability of the nanoceramic with sterilized cells was also lower than the control nanoceramic (without cells). This result supports the significance of the synergistic effect between the physical adsorption from the nanoceramics and the biodegradation from the cell−immobilized nanoceramics.
The biodegradation performances of paraquat by the free cells of P. putida and B. subtilis in comparison with the immobilized cells on nanoceramics of the same microbial species are illustrated in Figure 3c. No biodegradation of free cells was clearly seen. Evidently, the solid phase (e.g., the C nc ), microbial phase (e.g., the immobilized bacteria), and aqueous phase (i.e., water or paraquat solution) influenced the degradation mechanism of ceramicbacteria-paraquat interaction. The nanoceramic was a superb support material, providing a habitat for the immobilized microbial cells, in addition to being a superior adsorbent for paraquat through the electrostatic force between the positive charge and negative charge of paraquat and nanoceramic surface, respectively. Thus, the paraquat−degrading bacteria could release the extracellular enzymes to degrade the adsorbed paraquat into smaller molecule(s). Kopytko et al. (2002) [33] also described paraquat degradation by P. putida with an activated carbon (AC) support material and the addition of nutrient broth. During 72 h, more than 95% and 47% of the paraquat was removed with and without AC support, respectively. The results of this study are in line with the previous work by Li et al. (2022) [55]. Li et al. (2022) [55] discovered that immobilized Stenotrophomonas acidaminiphila Y4B cells degraded glyphosate more effectively than their free counterparts. Initially, between 0 and 3 days, the glyphosate degradation rate of free cells was faster than that of immobilized cells; however, after 3 days, immobilized cells degraded glyphosate faster than free cells. Immobilized cells were unable to directly touch glyphosate at the beginning of the breakdown process, resulting in a delay. However, the immobilized cells were ultimately more effective than the loose cells [55].

Influence of Paraquat Toxic Stress on Immobilized Cells on Nanoceramic Surface
Toxic stress on the immobilized cells were obtained from the cell leaching test. The initial numbers of immobilized cells on the nanoceramics and free cells in the aqueous solution during the paraquat biodegradation experiments using IC nc −P are shown in Table 1. The leaching of initial immobilized cells in the aqueous solution was evaluated 24 h after the paraquat biodegradation experiment. Results showed that the initial amount of immobilized cells on IC nc −P was 9.7 × 10 6 CFU mL −1 , and the residual amounts remaining on the nanoceramics and the free cells in the paraquat aqueous solution after 24 h were 2.0 × 10 6 and 4.1 × 10 5 CFU mL −1 , respectively. The cell leaching from the IC nc −P in the aqueous solution (without paraquat) is also measured and compared in the same table. The percentages of cell leaching from the IC nc −P were 4.23 ± 0.78% and 2.37 ± 0.98% for with and without paraquat in aqueous solution, respectively. Table 1. Amount of cells on ceramics (CFU g −1 ) and in aqueous solution (CFU mL −1 ) during the paraquat biodegradation experiments.

Free Cells in Aqueous Solution
IC nc −P in aqueous solution (without paraquat) 7.6 × 10 6 0 6.0 × 10 6 1.8 × 10 5 IC nc −P in paraquat aqueous solution 9.7 × 10 6 0 2.0 × 10 6 4.1 × 10 5 IC nc −B in paraquat aqueous solution 7.2 × 10 5 0 6.5 × 10 5 2.2 × 10 4 Leaching percentage IC nc −P in aqueous solution (without paraquat) = 2.37 ± 0.98% IC nc −P in paraquat aqueous solution = 4.23 ± 0.78% IC nc −B in paraquat aqueous solution = 3.06 ± 1.12% The paraquat toxic stress demonstrated in this work tentatively occurred from the interaction between reducing agents such as ascorbic acid or oxidoreductase enzymes and the paraquat (PQ 2+ ). The paraquat−free radicals (PQ +• ) generated from the reduction of PQ 2+ can react with O 2 to form superoxide anion radicals (O 2 •− ), which can further be transformed to hydroxyl radicals (OH • ), as reported previously by Du (2005) [1]. These generated radicals (O 2 •− and OH • ) induced the oxidative stress to bacteria and caused microbial stress to the system. The toxic stress to the viable microbial cells (for both free cells and immobilized cells) from paraquat at a concentration of 10 mg L −1 was shown in this work. The presence of paraquat in the solution is greatly influenced by the biofilm structure and the cellular stress response. The leaching percentage of P. putida cells from nanoceramics was more pronounced from the effect of paraquat toxic stress. After 24 h of the paraquat biodegradation process, the leaching of initial immobilized cells of B. subtilis (3.06 ± 1.12%) in the aqueous solution was also detected.
Both the P. putida and the B. subtilis strains are renowned for their metabolic capabilities and environmental adaptability as well as their ability to degrade a wide variety of organic contaminants [32]. From Figure 3, the free cells of both strains restrict the biodegradation performance of paraquat. For the immobilized cells, the paraquat toxic stress affected the leaching of immobilized cells to the aqueous solution; however, the efficiency in paraquat biodegradation remained high. The superior biodegradation of paraquat using immobilized cells, derived from the best adsorbent characteristics of the nanoceramic surfaces, can minimize the direct interaction between paraquat and microbial cells. In addition, the immobilized cell can provide continuous biodegradation, thereby overcoming the disadvantage of limited adsorption capacity and enhancing the survival resilience of bacteria protected from the application environment [30]. Based on the removal of herbicide by immobilized cells by Li et al. (2022) [55], the immobilized cells are more effective in degrading the herbicide due to the fact that they are more protected from the complexity of the natural environment, which can inhibit their activity. Temperature, pH, and the existence of indigenous microorganisms were among these environmental parameters. Consequently, the immobile cells are less susceptible to being washed away by water and attacked by predators.
The paraquat biodegradation using immobilized cells on nanoceramics from this work is also in agreement with the phenol biodegradation using immobilized cells on alginate, clay, and powdered activated carbon from a previous work by Massalha et al. (2010) [54]. The tolerance of the immobilized microbial cells on these support materials allows for excellent mineralization at a phenol concentration that was 2000 mg L −1 higher than the maximum concentration mineralizable by the free cells. The biofilm adherence to the nanoceramic surface can provide high metabolic activity and strongly resist toxic compounds such as paraquat [31].

Kinetics for Paraquat Degradation Using Cell−Immobilized Nanoceramics
Three zero−, first−, and second−order kinetic models determined the trend of paraquat degradation. As shown in Table 2, the second−order model potentially explained the degradation kinetics of paraquat by both IC nc −P and IC nc −B with R 2 > 0.95. In addition, the second−order model very well fitted the paraquat removal using C nc with R 2 > 0.98. A reduction in the half−life of paraquat from 1.3 h to 0.5 h was observed when cell−immobilized nanoceramics were applied for paraquat removal in comparison with the nanoceramics. The initial degradation rate (r) of paraquat using C nc −B (0.0092 mg L −1 min −1 ) was slightly higher than the C nc −P (0.0090 mg L −1 min −1 ). Similarly, the degradation rate constant (k) of paraquat with C nc −B (0.2408 M −1 min −1 ) was marginally greater than the C nc −P (0.2126 M −1 min −1 ). The results show that both IC nc −P and IC nc −B exhibited a higher performance in paraquat removal in comparison with the same biodegradation kinetic models.

Determination of DON Biodegradation Degree Using Cell−Immobilized Nanoceramics
The DIN concentrations (NO 3 -N, NO 2 -N, and NH 3 -N) during paraquat biodegradation using P. putida (free cells), B. subtilis (Free cells), IC nc −P, and IC nc −B are demonstrated in Figure 4. Apparently, the DIN concentrations obtained from paraquat biodegradation between the free cells and immobilized cells of P. putida are substantially different. The relatively low performances in the transformation of paraquat to each inorganic nitrogen by the free cells of P. putida are presented in Figure 4a and Figure 4b for B. subtilis. Using cell−immobilized nanoceramics (ICnc−P and ICnc−B), the predominant species of inorganic nitrogen from paraquat biodegradation detected in the system was NH3−N. The appearance of NO3−N was detected after 8 h of the treatment, while the NH3−N concentration continuously decreased. The nitrification occurred in the system because both microbial cells (P. putida and B. subtilis) are heterotrophic nitrifying bacteria [28,56]. Daum et al. (1998) [56] and Wang et al. (2019) [28] previously demonstrated the ability of heterotrophic nitrifying bacteria (P. putida) in oxidizing ammonia to nitrite, then into nitrate, thus these results agree with this study.
The DON biodegradation degrees derived from paraquat degradation using the cell−immobilized nanoceramics for both ICnc−P and ICnc−B are illustrated in Figure 5. The DON biodegradation degrees using ICnc−P and ICnc−B were 22 ± 1.0% at 16 h and 34 ± 1.3% at 8 h, respectively. The ICnc−B provided a higher DON biodegradation degree than the ICnc−P. These immobilized cells were able to convert the organic nitrogen in the paraquat molecule to inorganic nitrogen (NH3−N and NO3−N) through the ammonification. The detection of inorganic nitrogen, especially ammonia, in this work is in good agreement with Dinis−Oliveira et al. (2008) [57]. The intermediate products from paraquat degradation were monoquat and 4−carboxy−1−methylpyridinium (MINA), which were degraded further to smaller molecules, including methylamine, formate, and oxalate, before carbon Apparently, the DIN concentrations obtained from paraquat biodegradation between the free cells and immobilized cells of P. putida are substantially different. The relatively low performances in the transformation of paraquat to each inorganic nitrogen by the free cells of P. putida are presented in Figure 4a,b for B. subtilis. Using cell−immobilized nanoceramics (IC nc −P and IC nc −B), the predominant species of inorganic nitrogen from paraquat biodegradation detected in the system was NH 3 −N. The appearance of NO 3 −N was detected after 8 h of the treatment, while the NH 3 −N concentration continuously decreased. The nitrification occurred in the system because both microbial cells (P. putida and B. subtilis) are heterotrophic nitrifying bacteria [28,56]. Daum et al. (1998) [56] and Wang et al. (2019) [28] previously demonstrated the ability of heterotrophic nitrifying bacteria (P. putida) in oxidizing ammonia to nitrite, then into nitrate, thus these results agree with this study.
The DON biodegradation degrees derived from paraquat degradation using the cell−immobilized nanoceramics for both IC nc −P and IC nc −B are illustrated in Figure 5. The DON biodegradation degrees using IC nc −P and IC nc −B were 22 ± 1.0% at 16 h and 34 ± 1.3% at 8 h, respectively. The IC nc −B provided a higher DON biodegradation degree than the IC nc −P. These immobilized cells were able to convert the organic nitrogen in the paraquat molecule to inorganic nitrogen (NH 3 −N and NO 3 −N) through the ammonifi-cation. The detection of inorganic nitrogen, especially ammonia, in this work is in good agreement with Dinis−Oliveira et al. (2008) [57]. The intermediate products from paraquat degradation were monoquat and 4−carboxy−1−methylpyridinium (MINA), which were degraded further to smaller molecules, including methylamine, formate, and oxalate, before carbon dioxide, ammonia, and water were obtained as the ultimate products [57]. Regarding to the DON biodegradation degree and the detected inorganic nitrogen species during the paraquat removal, both cell−immobilized nanoceramics (IC nc −P and IC nc −B) were able to ammonify paraquat, oxidize the ammonia generated, and mineralize the paraquat. the DON biodegradation degree and the detected inorganic nitrogen species during the paraquat removal, both cell−immobilized nanoceramics (ICnc−P and ICnc−B) were able to ammonify paraquat, oxidize the ammonia generated, and mineralize the paraquat.

Conclusions
This study showed the synergy of nanoceramic surface paraquat adsorption and immobilized cell biodegradation and mineralization. Two strains of P. putida (ICnc−P) and B. subtilis (ICnc−B) immobilized on nanoceramics removed paraquat be er than their free cells. The second−order model accurately describes paraquat degradation kinetics for ICnc−P and ICnc−B. ICnc−B degraded paraquat at 0.0092 mg L −1 min −1 , slightly faster than ICnc−P (0.0090 mg L −1 min −1 ). Paraquat with ICnc−B (0.2408 M −1 min −1 ) had a slightly higher degradation rate constant (k) than ICnc−P (0.2126 M −1 min −1 ). Both heterotrophic nitrifying bacteria possibly convert paraquat into inorganic nitrogen species, including NH3−N, NO3−N, and NO2−N. Approximately 20-35% of organic nitrogen in paraquat was biologically ammonified, demonstrating the strength of the cell−immobilized nanoceramics. For further research, the application of these cell−immobilized nanoceramics is recommended for pesticide removal in wastewater. Organic loading, pH, and dissolved oxygen concentration should be investigated to achieve the high capability of paraquat degradation.
Author Contributions: M.J. performed the experiments and analyzed the data; P.K. analyzed the data and wrote and edited the manuscript; E.K. reviewed and edited the manuscript. All authors have read and agreed to the published version of the manuscript.

Conclusions
This study showed the synergy of nanoceramic surface paraquat adsorption and immobilized cell biodegradation and mineralization. Two strains of P. putida (IC nc −P) and B. subtilis (IC nc −B) immobilized on nanoceramics removed paraquat better than their free cells. The second−order model accurately describes paraquat degradation kinetics for IC nc −P and IC nc −B. IC nc −B degraded paraquat at 0.0092 mg L −1 min −1 , slightly faster than IC nc −P (0.0090 mg L −1 min −1 ). Paraquat with IC nc −B (0.2408 M −1 min −1 ) had a slightly higher degradation rate constant (k) than IC nc −P (0.2126 M −1 min −1 ). Both heterotrophic nitrifying bacteria possibly convert paraquat into inorganic nitrogen species, including NH 3 −N, NO 3 −N, and NO 2 −N. Approximately 20-35% of organic nitrogen in paraquat was biologically ammonified, demonstrating the strength of the cell−immobilized nanoceramics. For further research, the application of these cell−immobilized nanoceramics is recommended for pesticide removal in wastewater. Organic loading, pH, and dissolved oxygen concentration should be investigated to achieve the high capability of paraquat degradation.