Adsorption of Perfluorooctanoic Acid from Aqueous Media Using an Engineered Sugarcane Bagasse Biochar–Chitosan Composite

Abstract

In the recent years, several studies from developing economies have reported the presence of per- and polyfluoroalkyl substances (PFAS) in water bodies, with perfluorooctanoic acid (PFOA) predominating, a potential endocrine disruptor. In this study, an engineered sugarcane bagasse biochar–chitosan composite (SBCT) was designed, synthesized, and evaluated as a novel adsorbent for the removal of PFOA from aqueous systems at concentrations up to 500 ppb. Batch adsorption experiments were conducted to investigate the effects of initial PFOA concentration, contact time, pH, adsorbent dosage, and temperature. Scanning electron microscopy (SEM) showed that SBCT has a significant porous structure. The composite showed over 90% of PFOA removal from water. Further, peaks corresponding to C–F bonds observed after adsorption by Fourier transform infrared (FTIR) spectroscopy confirms the adsorption of PFOA on SBCT. The protonated amine groups (NH₃⁺) in chitosan enhanced the adsorption of anionic PFOA through electrostatic attraction with carboxyl groups (COO⁻). The kinetic study revealed that pseudo-first-order best described the adsorption process, with an equilibrium adsorption capacity (q_eq) of 2.78 mg/g, suggesting that physisorption is the predominant mechanism. The Langmuir Isotherm model gave the best fit, establishing a maximum adsorption capacity (q_max) of 9.08 mg/g. Thermodynamic analysis revealed that the adsorption process was spontaneous and exothermic, consistent with physisorption. The regeneration capacity of the SBCT composite demonstrated exceptional reusability over five methanol adsorption–desorption cycles. The adsorption kinetics, equilibrium behavior, and regeneration efficiency suggest that SBCT is a viable low-cost adsorbent for batch adsorption-based treatment systems targeting PFOA removal, particularly in decentralized and resource-constrained water treatment applications.

1. Introduction

Perfluorooctanoic acid (PFOA), used as an anionic surfactant, is a long-chain perfluoroalkyl carboxylic acid (PFCA) within the broader class of per- and polyfluoroalkyl substances (PFAS) [1]. PFOA is utilized as a processing aid in making fluoropolymers for the production of non-stick cookware, waterproof clothing, and insulation, and in coatings, fire-fighting foams, and lubricants for their oil, water, and stain resistance [2,3,4]. The worldwide emissions resulting from commercial PFOA manufacturing were estimated between 90 and 970 tonnes from 1951 to 2002, 30–430 tonnes from 2003 to 2015, and are projected to reach 630 tonnes between 2016 and 2030, while emissions from fluoropolymer production were reported between 1220 and 6560 tonnes (1951–2002), 660–3870 tonnes (2003–2015), with an expected increase to 4520 tonnes (2016–2030) [5].

Owing to its remarkable chemical stability and surface activity ascribed to its strong carbon–fluorine (C–F) linkages, PFOA is resistant to biodegradation [6,7] and is listed as a persistent organic pollutant (POP) in Annex A of the Stockholm Convention since 2019 [1,8]. Despite its widespread utilization in industrial and domestic applications, multiple studies have reported its toxicological effects, including carcinogenicity, genotoxicity, endocrine disruption, liver toxicity, immunological dysfunction, and reproductive issues [3,9,10]. PFOA is defined as hydrophobic and oleophobic due to its low fluorine polarizability, but it has a robust and particular affinity for human serum albumin [11] and supported by molecular simulations [12], highlights its pronounced proteinophilic nature.

The hydrophobic and lipophobic characteristics of PFASs pose significant challenges in remediation efforts [13,14]. Wastewater treatment facilities are significant sources of PFAS, since PFOA concentrations in effluents (110 ng/L) surpass those in influents (100 ng/L) at a U.S. facility, demonstrating inadequate effectiveness in removal [15]. Wastewater PFOA concentrations were found predominant among PFASs in wastewater from developed countries such as Sweden [16], Japan [17], and Korea [18] span from tens to hundreds of ng/L, with values in Sweden reported up to 11.9 µg/L in Sagargatan pumping station [19]. Similarly, wastewater studies from developing and rapidly industrializing regions, China [20,21], and Kenya [22], report the dominance of PFOA concentrations, confirming its widespread presence in municipal and industrial wastewater systems. In developing economies, groundwater PFOA concentrations of up to 2.51 µg/L have been reported in industrial regions of China [23]. In China, elevated PFOA concentrations in drinking water are ascribed to upstream wastewater treatment plant discharges into source streams [6,24]. These findings highlight the growing burden of PFOA pollution in developing regions and underscore the need for cost-effective and decentralized remediation strategies. Common treatment procedures are typically inadequate for eliminating trace levels of PFOA from wastewater, while advanced technologies are sometimes prohibitively costly. Adsorption, especially with materials like activated carbon, provides a more cost-effective and efficient solution, delivering enhanced removal performance and less secondary pollution compared to methods such as coagulation, degradation, or filtration [7,25,26]. Adsorption is recognized as a simple, effective, and cost-efficient method for removing PFASs from water. The efficacy of diverse adsorbents in eliminating PFOA has been examined, encompassing nanomaterials, activated carbon, carbon nanotubes, ion exchange polymer resins, and different minerals [27,28,29,30]. Biochar, an economically carbon-dense substance generated through the pyrolysis of biomass under low-oxygen conditions, has emerged as a potential adsorbent for removing PFOA from water and wastewater [31,32,33]. Biochar is preferred over other adsorbents because of its cost-effectiveness, superior adsorption performance, and ecologically friendly properties. Additionally, one of the benefits of employing biochar is its ability to be customized for specific carbon sequestration [34]. Sugarcane bagasse, an agro-industrial byproduct, is considered a suitable raw material for extensive biochar production owing to its plentiful availability, economic viability, substantial mineral content, and inherently porous fibrous structure [35]. Again, Chitosan’s non-toxicity, hydrophilicity, biodegradability, and biocompatibility render it a cost-effective, renewable, and eco-friendly sorbent for effective water purification [36]. Chitosan-modified biochar has demonstrated improved efficacy in augmenting the adsorptive capacity for a wide range of contaminants, including arsenic (V) [37], Ofloxacin [38], and heavy metals [39].

Given the challenges with PFOA in wastewater particularly in developing economies, we have synthesized a novel engineered biochar in the form of sugarcane bagasse biochar/chitosan composite (SBCT) for effective removal of PFOA present even in trace levels in water. The SBCT composite material was characterized using FTIR methodology, SEM examination, and Brunauer–Emmett–Teller (BET) surface area methods. Adsorption kinetics and isotherm models were employed to evaluate the PFOA uptake capacity. We have further investigated the impact of initial PFOA concentration, adsorbent dosage, pH of the aqueous PFOA solution, and temperature on adsorption effectiveness. Additionally, the potential for reusing the exhausted adsorbent was examined using several regeneration agents. Finally, the effectiveness of SBCT has been compared with other adsorbents for PFOA removal.

2. Materials and Methods

2.1. Adsorbate

Perfluorooctanoic acid (PFOA), chitosan (deacetylated chitin), and epichlorohydrin (ECH) were sourced from Sigma Aldrich (St. Louis, MO, USA). Every additional reagent was of analytical grade. The stock solution was initially made with methanol, while Milli-Q water was used to formulate all subsequent working solutions. The concentrations of the prepared PFOA solutions were verified using Gas Chromatography–Electron Capture Detector (GC–ECD) (Agilent Technologies, Santa Clara, CA, USA) analysis after derivatization based on external calibration with derivatized PFOA standards, and the measured concentrations were within ±5% of the nominal values. The corresponding calibration curve is provided in Figure S1.

2.2. SBCT Preparation

The novel SBCT was synthesized utilizing a modified technique derived from established methods in the literature [38,40]. The raw material, sugarcane bagasse (SB), was procured from a local cane juice seller in Tamil Nadu (Chengalpattu, Indian) and divided into smaller pieces. The bagasse was thoroughly cleaned with Milli-Q water to eliminate the surface contaminants and subsequently dried in a hot air oven at 105 °C for 8 h to eradicate moisture content. The dried bagasse was powdered using a grinder and subjected to isothermal pyrolysis in an oxygen-limited environment in a preheated muffle furnace at 350 °C for 70 min. A lower pyrolysis temperature (350 °C) under slow pyrolysis conditions was chosen to retain surface functional groups and minimize ash formation in sugarcane bagasse biochar, facilitating effective chitosan modification and PFOA adsorption [41]. The residual ash and other contaminants from the biochar were removed by washing the biochar with Milli-Q water. The biochar was dried at 80 °C in a hot air oven, screened through a 150 µm nylon mesh, and stored in a sealed container within a desiccator to prevent moisture absorption. Preliminary experiments were carried out using different biochar–chitosan mass ratios (1:1 and 2:1). Based on adsorption performance and surface characteristics, the 2:1 ratio was selected for further study. The higher biochar content also improves economic feasibility, as biochar is a low-cost agro-waste material compared to chitosan. In this procedure, 2 g of chitosan powder was dissolved in 200 mL of a 3% (v/v) acetic acid solution while being magnetically stirred to obtain a homogeneous solution. Subsequently, 4 g of biochar derived from sugarcane bagasse was integrated into the 2 g chitosan solution in a 2:1 ratio (SB:CT) and stirred continuously for 2 h. To facilitate crosslinking, 300 mL of a 2% (v/v) epichlorohydrin (ECH) solution was introduced, and the mixture was stirred in a water bath shaker at 40 °C for 30 min. The pH was later adjusted to a range of 8.0–10.0 using a 1 mol/L NaOH solution. The resultant composite was meticulously cleaned to eliminate any remaining alkali before utilization.

2.3. Adsorbent Characterization

The chemical functionality and composition of the SBCT composite were examined by Fourier-transform infrared spectroscopy (FTIR) using a PerkinElmer ALPHA-FT-IR spectrometer (PerkinElmer Inc., Waltham, MA, USA) over the wavelength range of 400–4000 cm⁻¹. Surface morphology and structural properties were assessed using scanning electron microscopy (SEM) employing an FEI Quanta 200 instrument (FEI Company, Hillsboro, OR, USA). At the same time, the composition of the elements was analyzed through energy-dispersive X-ray spectroscopy (EDAX) using an FEI Nova SEM 450 (FEI Company, Hillsboro, OR, USA). The Brunauer–Emmett–Teller (BET) surface area was ascertained by nitrogen adsorption–desorption isotherms at 77 K utilizing a Quantachrome Autosorb IQ analyzer (Quantachrome Instruments, Boynton Beach, FL, USA). The point of zero charge (pZC) of the SBCT composite was ascertained using the specified methodology given elsewhere [42]. Briefly, a 50 mL solution of 0.1 M NaCl was mixed with 0.5 g of biochar and permitted to remain undisturbed for 24 h to reach equilibrium. A series of solutions with differing initial pH values (pHi) was generated by adjusting the pH using 0.1 M hydrochloric acid and sodium hydroxide solutions. After the equilibration interval, the final pH (pHf) was documented, and the pH difference (ΔpH = pHi − pHf) was calculated. A graph of ΔpH against pHi was constructed to determine the pZC. All measurements were conducted in triplicate to guarantee repeatability.

2.4. Batch Adsorption of PFOA

Adsorption studies were conducted in duplicate utilizing the SBCT composite as the adsorbent. Simulated wastewater with perfluorooctanoic acid (PFOA) concentrations between 0.5 and 4 mg/L was generated, and 30 mL of this solution was placed into 50 mL Nalgene tubes (Southern India Scientific Corporation (SISCON), Chennai, Tamil Nadu, India). Each tube was allocated 0.02 g of the SBCT material and underwent agitation at 150 rpm in an orbital shaker, sustained at ambient temperature (25 °C), for different contact times. After treatment, the suspensions were filtered through a 0.22 μm membrane to isolate the solid and liquid phases. Before analysis, the filtrate was subjected to derivatization, transforming PFOA into its anilide form through the use of 2,4-difluoroaniline (DFA) as the derivatizing reagent and N, N-dicyclohexylcarbodiimide (DCC) as the dehydrating agent. The derivatization of PFOA prior to GC–ECD analysis was performed following established protocols reported in the literature [43], with minor modifications to optimize sensitivity and peak resolution. PFOA was quantified in a GC-ECD system (Agilent 7890B, Agilent Technologies, Santa Clara, CA, USA) using an HP5 column (Agilent Technologies, Santa Clara, CA, USA) (30 m length, 0.32 mm internal diameter, 0.25 μm film thickness). Nitrogen was used as a carrier gas, with a total flow rate of 18.8 mL per minute. The temperature of the detector was maintained at 280 °C. Sample injections were conducted in splitless mode with a fixed injection volume of 1 μL.

The adsorption capacity at equilibrium, q_eq (mg/g), and PFOA removal efficiency, R_E (%), were estimated with Equations (1) and (2):

$${\mathrm{q}}_{\mathrm{e}\mathrm{q}}={\displaystyle \frac{\left({\mathrm{C}}_{\mathrm{i}\mathrm{n}}-{\mathrm{C}}_{\mathrm{e}\mathrm{q}}\right){\mathrm{V}}_{\mathrm{o}}}{{\mathrm{m}}_{\mathrm{o}}}}$$

(1)

$${\mathrm{R}}_{\mathrm{E}}\left(\%\right)={\displaystyle \frac{{\mathrm{C}}_{\mathrm{i}\mathrm{n}}-{\mathrm{C}}_{\mathrm{t}\mathrm{c}}}{{\mathrm{C}}_{\mathrm{i}\mathrm{n}}}}\times 100$$

(2)

C_in refers to the initial PFOA concentration, while C_eq (mg/L) represents the equilibrium state PFOA concentration. The variable C_tc (mg/L) indicates the concentration at a given time of contact, m_o represents the adsorbent’s mass in grams, and V_o denotes the PFOA volume in mL. Each of the experiments was conducted in duplicate under controlled temperature conditions.

2.5. Isotherm Modeling of Adsorption

The adsorption nature and behavior of PFOA on SBCT were evaluated by changing the initial PFOA concentrations between 0.5 and 4 mg/L. The amount of PFOA adsorbed at each concentration level was used to construct adsorption isotherms, which were then analyzed using the nonlinear plotting of the Langmuir model given in Equations (3) and (4), the Freundlich model in Equation (5), and the Temkin model in Equation (6) and Redlich-Peterson in Equation (7) as used elsewhere [44,45].

$${\mathrm{q}}_{\mathrm{e}\mathrm{q}}={\mathrm{q}}_{\mathrm{m}\mathrm{a}\mathrm{x}}{\mathrm{K}}_{\mathrm{L}\mathrm{q}}{\mathrm{C}}_{\mathrm{e}\mathrm{q}}/1+{\mathrm{K}}_{\mathrm{L}\mathrm{q}}{\mathrm{C}}_{\mathrm{e}\mathrm{q}}$$

(3)

$${\mathrm{R}}_{\mathrm{L}\mathrm{q}}=1/\left(1+{\mathrm{K}}_{\mathrm{L}\mathrm{q}}{\mathrm{C}}_{\mathrm{i}\mathrm{n}}\right)$$

(4)

$${\mathrm{q}}_{\mathrm{e}\mathrm{q}}={\mathrm{K}}_{\mathrm{f}\mathrm{d}}{\mathrm{C}}_{\mathrm{e}\mathrm{q}}^{1/n}$$

(5)

$${\mathrm{q}}_{\mathrm{e}\mathrm{q}}={\mathrm{B}}_{\mathrm{T}\mathrm{m}}\mathrm{l}\mathrm{n}\left({\mathrm{K}}_{\mathrm{T}\mathrm{m}}{\mathrm{C}}_{\mathrm{e}\mathrm{q}}\right)$$

(6)

$${\mathrm{q}}_{\mathrm{e}\mathrm{q}}={\mathrm{K}}_{R-P}{\mathrm{C}}_{\mathrm{e}\mathrm{q}}/1+{\mathrm{\alpha }}_{R-P}{\mathrm{C}}_{\mathrm{e}\mathrm{q}}^{\beta }$$

(7)

C_eq (mg/L) and q_eq (mg/g) denote PFOA concentration and SBCT adsorption capacity at the state of equilibrium, and q_max (mg/g) indicates the anticipated maximum monolayer adsorption capacity of PFOA. The ‘K_Lq’ (L/mg) is the Langmuir constant. The dimensionless separation factor R_Lq, calculated using Equation (4), elucidates the favorability of the adsorption process, where R_Lq > 1 indicates adsorption is not favorable, R_Lq = 1 denotes adsorption is linear, and R_Lq < 1 signifies adsorption is favorable. K_fd (mg/g) in Equation (5) is the Freundlich adsorption capacity constant, n indicates adsorption intensity, a 1/n value < 1 indicates favorable adsorption and surface heterogeneity; 1 < n < 10 also suggests favorability. 1/n > 1 implies phase agreement, while n = 1 denotes concentration-independent partitioning. K_Tm (L/g) denotes the Temkin equilibrium binding constant, and B_Tm is associated with the heat of sorption (J/mol). The constants ${\mathrm{K}}_{R-P}$ (L/g) and ${\mathrm{\alpha }}_{R-P}$ (L/mg) in Equation (7) represent the Redlich–Peterson adsorption capacity and affinity parameters, respectively, while the exponent $\beta$ (0 < $\beta$ ≤ 1) describes the degree of surface heterogeneity. When $\beta =1$, the R−P model reduces to the Langmuir isotherm, indicating monolayer adsorption on a homogeneous surface, whereas values of $\beta <1$ suggest heterogeneous adsorption behavior resembling the Freundlich model.

2.6. Kinetic Modeling of Adsorption

Kinetic models were used to elucidate the adsorptive mechanism of PFOA onto SBCT. The three kinetic models using nonlinear regression fitting applied were: the pseudo-first-order model (Equation (8)), the pseudo-second-order model (Equation (9)), and the Weber–Morris intra-particle diffusion model (Equation (10)) [45].

$${\mathrm{q}}_{\mathrm{t}\mathrm{c}}={\mathrm{q}}_{\mathrm{e}\mathrm{q}}(1-e^{-{\mathrm{K}}_1\mathrm{t}})$$

(8)

$${\mathrm{q}}_{\mathrm{t}\mathrm{c}}=\left({\mathrm{K}}_2{{\mathrm{q}}_{\mathrm{e}\mathrm{q}}}^2{\mathrm{t}}_{\mathrm{c}}\right)/(1+{\mathrm{K}}_2{\mathrm{q}}_{\mathrm{e}\mathrm{q}}{\mathrm{t}}_{\mathrm{c}})$$

(9)

$${\mathrm{q}}_{\mathrm{t}\mathrm{c}}={\mathrm{k}}_{\mathrm{i}\mathrm{p}\mathrm{d}}{\mathrm{t}}_{\mathrm{c}}^{1/2}+\mathrm{C}$$

(10)

K₁ (1/min) in Equation (8) is the equilibrium coefficient of pseudo-first-order kinetic uptake per minute. The parameters ‘q_eq’ and ‘q_tc’ represent the adsorption capacity at equilibrium and at contact time (t_c), respectively. in Equation (9), ‘K₂’ (1/min), the rate constant for pseudo-second-order kinetics. In Equation (10), ‘k_ipd’ is the intra-particle diffusion rate constant, and ‘i’ represents the boundary layer effect, and C is the intercept (mg/g).

2.7. Thermodynamic Studies

Temperature significantly affects both the rate and capacity of adsorption. To evaluate the impact on PFOA adsorption, experiments were carried out within the 20 °C to 40 °C range. The typical Gibbs free energy change (ΔG⁰) was calculated utilizing the Van’t Hoff equation [46].

$${∆\mathrm{G}}^0=-\mathrm{R}\mathrm{T}\ln \left({\mathrm{K}}_{\mathrm{v}}\right)$$

(11)

$$\ln {\mathrm{K}}_{\mathrm{v}}=-∆{\mathrm{H}}^0/\mathrm{R}\mathrm{T}+{∆\mathrm{S}}^0/\mathrm{R}\mathrm{T}$$

(12)

$${∆\mathrm{G}}^0={∆\mathrm{H}}^0-\mathrm{T}∆{\mathrm{S}}^0$$

(13)

Gibbs free energy (ΔG⁰, kJ/mol), enthalpy change (ΔH⁰, kJ/mol), and entropy change (ΔS⁰, kJ/mol) were evaluated by using Equations (11)–(13), where K_V represents the dimensionless equilibrium constant, R represents the universal gas constant, and T denotes the absolute temperature in Kelvin.

3. Results and Discussion

3.1. Novel Engineered SBCT

In general, engineered biochar augmented through physicochemical methods or biological modifications enhances the structural and surface characteristics, including increased surface area, improved ion exchange capacity, refined pore structure, and elevated functional group content [41,47]. It is to be noted that compared to activated biochar, pure, unmodified biochar often has a lower adsorption effectiveness, and its low density and small particle size make separation challenging, which limits its usefulness in water treatment [48,49]. Chitosan, a renewable organic polymer derived from chitin in crustacean shells and fungal mycelia, is valued for its versatile structure and eco-friendly applications, particularly in wastewater treatment [50]. The inclusion of protonated amine units (NH₃⁺) in chitosan is capable of enhancing the electrostatic interactions with the carboxyl groups (COO⁻) of PFOA [51]. However, the practical use of raw chitosan in water treatment is limited by its slow rate of adsorption and susceptibility to degradation in acidic environments [52]. Hence, we prepared engineered composites made of biochar of sugarcane bagasse and Chitosan (SBCT) to provide an effective substrate for enhancing sorption mechanisms, particularly for anionic pollutants like PFOA. The formation of the SBCT composite involves both physical incorporation and chemical interactions between biochar and chitosan. During composite preparation, chitosan is deposited on the biochar surface, partially altering the pore structure and leading to surface coating and pore modification [53]. The interaction between biochar and chitosan is mainly governed by hydrogen bonding and electrostatic attraction between oxygen-containing functional groups on the biochar surface and the amine and hydroxyl groups of chitosan [39]. Such a novel composite was prepared to investigate whether SBCT PFOA removal efficacy in aqueous media than either unmodified pristine biochar or raw chitosan.

3.2. SBCT Characterization

a. Surface morphology

SBCT samples were subjected to SEM and energy-dispersive X-ray spectroscopy (EDX) analysis before and after the adsorption process and are presented in Figure 1a,b. SEM images revealed that the SBCT surface showed wrinkles and groove-like structures, significantly increasing the available pore size for PFOA adsorption. The presence of a rough and porous surface contributes to enhanced adsorption efficiency. Additionally, post-adsorption SEM images showed increased surface roughness and thickness, indicating successful chitosan aggregation on the SBCT composite surface. Before adsorption, fluorine was present in SBCT only at trace levels (~0.76 wt%), as can be seen in the EDX results for light elements (Figure 1a). However, after adsorption, elemental analysis showed that the fluorine content raised to 5.3 wt%, confirming successful PFOA uptake onto SBCT (Figure 1b). The increase in oxygen content observed in EDX after adsorption is consistent with FTIR results, which show prominent hydroxyl, amide, and C–O functional groups and their shifts after adsorption, indicating surface interaction through oxygen- and nitrogen-containing groups. The N₂ adsorption–desorption isotherm (Figure 1c) exhibits a characteristic hysteresis loop, indicating the presence of mesoporous structures and capillary condensation behavior. The Barrett–Joyner–Halenda (BJH) pore size distribution (Figure 1d) shows that SBCT contains both micro- and mesopores. Micropores (<2 nm) contribute only slightly, while mesopores in the range of 2–50 nm dominate the pore structure. A clear peak at around 2–3 nm indicates that small mesopores provide most of the pore volume and internal surface area. The total pore volume is approximately 0.072 cm³/g, together with a surface area of 127.07 m²/g. This pore structure supports good accessibility of adsorption sites and facilitates the diffusion of PFOA molecules. A comparison of EDX results for various biochar–chitosan ratios (Figure S2) indicated that the 1:1 composite had elevated nitrogen content due to enhanced chitosan loading, while the 2:1 composite demonstrated a more balanced surface composition with increased exposed carbon and adequate surface-accessible amine groups. Excess chitosan in the 1:1 composite may lead to agglomeration and partial pore obstruction, but the 2:1 ratio maintains surface accessibility and good functionalization.

b. Point of zero charge (pZC)

The pZC of SBCT was measured as 6.1 (Figure S3). Below pH 6.1, the surface of SBCT acquires a positively charged character, enhancing electrostatic attraction with the anionic form of PFOA. Conversely, at pH above 6.1, electrostatic repulsion may hinder the adsorption efficacy of SBCT. These results indicate that SBCT can function as an effective adsorbent for removing PFOA from aqueous solutions in acidic pH.

c. Chemical Interactions with Functional Groups

The FTIR spectra of the SBCT composite before and after adsorption are represented in Figure 2a,b, respectively. The broad absorption bands observed near 3260 cm⁻¹ and 3450 cm⁻¹ are attributed to the overlapping vibrational modes of N–H and O–H groups. The increased intensity of the O–H band represents the presence of hydroxyl or amine functionalities on the SBCT surface [27]. The absorption band observed at 1580 cm⁻¹ is characteristic of the amide (CONH) group, consistent with findings reported [38]. The peak located between ~1150–1155 cm⁻¹ is attributed to the β-glycosidic linkage in chitosan [54]. Additionally, the band near 1600 cm⁻¹ corresponds to the stretching vibration of C=O groups, which are prevalent in carboxylic acids, amides, or ketones. The enhanced intensity of this peak following adsorption suggests effective interaction between PFOA and SBCT, likely facilitated by the carboxyl functional group of PFOA in aqueous media [51]. Peaks appear in this region of 1200–1140, corresponding to the C–F bonds in PFOA. This confirms PFOA adsorption [51]. The corresponding C–O Stretch in alcohols, esters, or ethers is given in the signals around 1050–1100 cm⁻¹ [55]. A shift in the N–H absorption peaks toward lower wavenumbers was observed, suggesting that N–H groups might have played a role in the adsorption of PFOA. Thus, the interaction between SBCT and PFOA was collectively confirmed by the spectral changes, supporting the effectiveness of the adsorption mechanism.

3.3. Factors Governing PFOA Adsorption

3.3.1. Contact Time

The SBCT composite at 0.02 g was added to a synthetic PFOA solution of 2 mg/L to evaluate the adsorption capacity of SBCT for PFOA, as illustrated in Figure 3. The adsorption capacity of 2.7 mg/g was attained at 240 min, with a maximum PFOA removal of 91%; a slight increase to 2.71 mg/g at 300 min indicates that equilibrium was effectively reached around 240 min. Therefore, all following batch adsorption studies were performed with a contact duration of 240 min. In comparison, unmodified pristine sugarcane bagasse biochar (SB) and pure chitosan (CT) demonstrated reduced adsorption capabilities of 1.59 mg/g and 2.05 mg/g, respectively. In comparison to the 1:1 composite, the optimized 2:1 SBCT exhibited approximately 13% more adsorption capacity, due to enhanced chitosan dispersion and improved accessibility to adsorption sites.

The SBCT composite was developed by integrating sugarcane bagasse biochar with chitosan at a 2:1 ratio, which most likely enhanced the adsorption capacity of PFOA through electrostatic interactions between protonated amine groups (NH₃⁺) in chitosan and carboxyl groups (COO⁻) in anionic PFOA. The increased surface area, functional groups, hydrophobicity, and synergistic adsorption mechanisms improved the performance of SBCT, as supported by studies showing that chitosan-modified biochar demonstrates significantly higher adsorption capacities than pristine biochar or chitosan alone [38].

3.3.2. pH

The effect of change in initial pH levels in the adsorption of PFOA, covering a range starting from acidic (pH 2) to alkaline (pH 12), is illustrated in Figure 4. The marked decline in PFOA adsorption with increasing pH is due to PFOA predominantly existing in its anionic form under aqueous conditions, bearing a carboxylate group. Hence, hydrogen bonding between the carbonyl functionalities (C=O) of PFOA and the positively charged –NH₃⁺ moieties on the composite surface at lower pH leads to pronounced adsorption due to strong electrostatic interactions with the PFOA molecule and SBCT [51,56]. The adsorption process is dominant under acidic conditions associated with this interaction. Our observations are in line with other studies showing higher adsorption of perfluorinated compounds, including PFOA, at acidic pH values, viz., pH 3 [57,58,59], pH 4 [60], and pH 2 [51]. As pH increased, these bonds might have begun to disrupt in alkaline conditions, leading to a decrease in adsorption capacity. When the pH reached 8, the alkaline environment became unfavorable for PFOA adsorption. At pH 10, the adsorption capacity was lowest, likely due to the abundance of OH⁻ ions in a strongly alkaline environment. The pZC of SBCT was around 6.1. Below this pH, in more acidic conditions, the surface became positively charged, promoting electrostatic attraction with anionic PFOA and enhancing adsorption. In contrast, at higher pH in alkaline conditions, the surface became negatively charged, thereby reducing adsorption efficiency [38].

3.3.3. Adsorbent Dosage and Initial Concentration

The adsorptive capacity of PFOA is significantly influenced by SBCT composite dosage and PFOA concentration. In this study, 0.01 g and 0.02 g of SBCT were used to evaluate the adsorbent dose effect on PFOA removal. PFOA showed a higher removal efficiency of 91% at 0.02 g, as illustrated in Figure S4. The PFOA concentration, ranging between 0.5 and 4 mg/L, was examined to reflect both common and severe environmental pollution levels. This concentration range falls within the range used in other studies [61,62] for PFOA removal. The results reflected that higher PFOA concentration led to a rise in the adsorption capacity. The maximum experimentally observed adsorption capacity (q_max) of 5.1 mg/g was observed at 4 mg/L of PFOA concentration, with a gradual increase with increasing concentrations. The maximum PFOA removal was observed at the lowest concentration tested (0.5 mg/L; Figure S5). The slight reduction in the removal efficiency at higher PFOA concentrations can be attributed to the increasing saturation tendency of active adsorption sites on the SBCT surface. This phenomenon is attributed to the aggregation of semi-micelles and micelles at higher concentrations, which can accumulate on the adsorbent surface and influence the adsorption process, as noted in other studies [59,60].

3.4. Adsorption Modeling of PFOA Using SBCT

3.4.1. Isotherm Study

Isotherm models were applied to evaluate the adsorption of PFOA in aqueous solution and SBCT at equilibrium concentrations (C_eq) at room temperature (25 °C). The data were evaluated using a nonlinear regression model as outlined [63], and the results were used to estimate model parameters and the correlation coefficient (R²). Experimental data and model values are presented in Figure 5, with detailed results in

Table 1. Parameters of adsorption isotherm models.

Nonlinear Isotherm Models	Key Parameters	R2	RMSE (mg/g)	χ2
Langmuir	qmax = 9.01 mg/g; KLq = 6.80 L/mg	0.95	0.19	0.12
Freundlich	Kfd = 7.28; n = 0.69	0.92	0.32	0.35
Temkin	BTm = 1.73; KTm = 25.51 L/mg	0.94	0.24	0.21
Redlich–Peterson	KR−P = 16.55; αR−P = 2.04; β = 1.30	0.95	0.23	0.21

. The Langmuir isotherm model assumes adsorption is a monolayer on a homogeneous surface with finite adsorption sites [63]. The model provided the best fit to the data (R² = 0.95), exhibited the lowest root mean square error (RMSE) (0.19 mg/g) and χ² (0.12) among all tested models, indicating superior agreement with the experimental data. The theoretically calculated maximum adsorption capacity (q_max) of SBCT is 9.01 mg/g, and the Langmuir constant (K_Lq) was 6.80 L/mg, indicating a strong affinity between SBCT and PFOA. The adsorption process is favorable, as confirmed by the separation factor R_Lq of 0.18, which falls between 0 and 1. The Freundlich model [64], suitable for heterogeneous surfaces, also fit the data reasonably well (R² = 0.92), with a Freundlich constant (K_fd) of 7.28 and a 1/n value of 0.318, reflecting favorable adsorption intensity. The Temkin model is based on the assumption that the adsorption energy decreases with increasing surface area [65]. With the SBCT composite, the Temkin constants B_Tm = 1.73 and K_Tm = 25.51 L/mg, fitted with an R² of 0.94, suggest substantial interaction between PFOA and SBCT. The Redlich–Peterson (R−P) isotherm model yielded a reasonably high correlation coefficient (R² = 0.95); however, the fitted exponent, β = 1.30, exceeded the theoretical upper limit of unity and was associated with large uncertainty. This phenomenon is well-documented in literature and is frequently attributed to parameter coupling and over-parameterization, particularly in systems with limited experimental data. Under these circumstances, nonlinear optimization may converge to theoretically acceptable solutions that lack clear physical significance, instead of providing an improved physical description of the adsorption mechanism [66,67]. Furthermore, the RMSE (0.23 mg/g) and χ² (0.21) values for the R–P model did not improve relative to those of the Langmuir model. Thus, the Langmuir model indicates that the adsorption properties of PFOA on the SBCT monolayer align with those of other adsorbents [24,68].

3.4.2. Kinetic Study

Three kinetic models were evaluated to understand the adsorption process of PFOA using SBCT. The parameters and the coefficient of determination were evaluated (Figure 6), and the values are summarized in

Table 2. Parameters of Kinetic Models.

Kinetic Models	First Order			Second Order			Intraparticle Diffusion Model
Parameters	qeq (mg/g)	K1 (min−1)	R2	qeq (mg/g)	K2 g/mg/min	R2	kipd mg g−1 min−0.5	C (mg/g)	R2
Value	2.784	0.014	0.992	3.477	0.004	0.981	0.166	0.167	0.90

. The pseudo-first-order model showed a strong correlation with the experimental data, with an R² value of 0.992 and a rate constant (K₁) of 0.014 min⁻¹, indicating a good fit. The equilibrium adsorption capacity (q_eq = 2.784 mg/g) closely matches the experimental value (q_exp = 2.727 mg/g). Thus, the adsorptive mechanism is primarily driven by physisorption because the model assumes that the adsorption rate is directly proportional to the number of adsorptive sites available [69]. The R² value of the pseudo-second-order model was 0.981, which is slightly lower than first-order kinetics with a rate constant (K₂) of 0.004 g/mg/min. The q_eq value of 3.477 mg/g derived from the second-order model is not close to the experimental values, suggesting that chemical interactions may be a contributing factor, though not a dominant mechanism [69]. The intraparticle diffusion rate constant (k_diff) was 0.166 mg/g/min^−0.5, and the non-zero intercept (C = 0.167 mg/g) indicates the presence of boundary-layer resistance. The Weber–Morris plot does not pass through the origin, suggesting that intraparticle diffusion is not the sole rate-limiting step. The mesoporous pore structure of SBCT, as evidenced by BET and BJH analyses, facilitates diffusion of PFOA molecules into internal adsorption sites, while surface adsorption and boundary-layer resistance together govern the overall adsorption kinetics. The observed multi-linearity implies that the adsorption process proceeds through multiple stages, including an initial surface adsorption followed by intraparticle diffusion [45]. The observations are in line with the findings of other studies using adsorbents such as magnetic carbonized fiber [68] and chitosan-based hydrogel [51], where the pseudo-first-order model provided a superior fit, signifying that physisorption played a significant role during adsorption. The adsorption capacity of SBCT as explained by the kinetic profile of PFOA removal from aqueous medium suggests it’s future application as a promising adsorbent for water purification.

3.4.3. Thermodynamic Parameters

The change in temperature impacting the adsorption process tested across the temperature range of 20 to 40 °C is presented in

Table 3. Parameters of adsorption thermodynamic models.

Parameters	ΔG° (KJ mol−1)					ΔH° (KJ/mol)	ΔS° (J/mol/K)
	293 K	298 K	303 K	308 K	313 K
Value	−6.65 ± 0.22	−6.67 ± 0.26	−6.09 ± 0.15	−5.95 ± 0.19	−5.72 ± 0.13	−21.8	−51.3

Note: All values denote mean ± standard deviation.

. The Gibbs free energy change (ΔG°) ranged between −6.65 kJ/mol and −5.72 kJ/mol, indicating that the adsorption process occurs spontaneously. The adsorption mechanism is consistent with physisorption rather than chemisorption, where the values of ΔG° are above −20 kJ/mol [46]. Further, the reaction is exothermic and physisorption-driven, supported by the low enthalpy change (ΔH°) of −21.8 kJ/mol, as chemisorption typically involves more significant heat changes (i.e., ΔH° < −80 kJ/mol). These thermodynamic results are consistent with kinetic data indicating a pseudo-first-order adsorption model representing physisorption. The negative entropy shift (ΔS° = −51.3 J/mol·K) indicates an increase in organized distribution at the solid–liquid interface during adsorption. Such systematic immobilization of PFOA molecules on the SBCT surface and the limited mobility of adsorbed species is a common phenomena in adsorption processes, when solute molecules move towards a more uniform surface layer. Similar thermodynamic behavior, characterized by negative ΔG° and ΔS°, has been reported for PFOA adsorption onto Chemically activated maize tassel [70] and iron-modified biochar [71].

3.5. Regeneration Experiments

The regeneration capability of the adsorbent is a very important factor in determining its long-term viability in practical use. The stability and reusability of the SBCT composite were assessed by performing five adsorption–desorption cycles using three different methanol concentrations of 50%, 75%, and 100% along with deionized water (DI). Following the initial cycle, the adsorption efficiency gradually dropped. The adsorption capacity declined by up to 8% in the fifth cycle for 100% methanol and by 65% for DI water, demonstrating more effective desorption and better regeneration with methanol than with DI water. Figure 7 depicts the gradual loss of active adsorption sites with repeated use of the adsorbent. A comparative summary of PFAS regeneration efficiencies using methanol, ethanol, and alkaline solutions reported in the literature is provided in Table S1 to contextualize the regeneration strategy employed for the SBCT composite in this study. Methanol-based regeneration is effective, yet its environmental and operational implications, such as solvent handling, recovery, and disposal, require meticulous management; however, the minimal solvent volumes needed and the practicality of solvent recovery and reuse can minimize the environmental impacts thereby making the composite more sustainable.

Hence, the regeneration study demonstrates that SBCT can retain a significant portion of its adsorption efficiency upon methanol regeneration. The composite material demonstrated its continued reusability, especially when regenerated using higher methanol concentrations, highlighting its potential for real-world practical applications [72].

3.6. Comparative Analysis with Other Studies

The comparison of PFOA removal using sugarcane Bagasse Biochar/Chitosan composite (SBCT) is provided in

Table 4. Comparison of adsorption kinetics and adsorption capacities of various adsorbents.

Adsorbent	C0 (mg/L)	pH	teq (h)	qeq (mg/g)	qmax (mg/g)	Reference
Rice husk BC	100–200	5	5	550	1085/Lq	[27]
Multi-walled carbon nanotubes (MWCNT)	10–500	5	4	12.4	5.4/Fe	[74]
Bamboo AC	20–250	5.0	24	576	544/Fe	[75]
Starch-stabilized Fe3O4 nanoparticles	0–4	6.8	0.5	15.53	62.5/Lq	[76]
Granular activated carbon(GAC)	0.5–10	5	120	12.6	52.8/Lq	[73]
Chitosan + hydrogel	100–2000	-	<24	1050.83	1275.9/Lq-Fe	[51]
Sulfur polymer support activated carbon	0.250–5	5	-	-	0.355/Lq-Fe	[62]
Magnetic carbonized fiber	25–250	3	2	41.85	204.7/Lq	[68]
Hierarchically microporous biochar (HMB)	50–150	2–10	0.5	423	1269/Lq	[77]
Calotropis Gigantea fiber	25–250	-	3	54.76	232.8/Lq	[78]
Polyurethane-modified magnetic sorbent	0.05–1	5.5	46	243.9 (µg/g)	2.480/Sips	[79]
Multi-walled carbon nanotubes @Molecular imprinted polymers (MWCNTs@MIPs)	0.10–20	5	2	1.44	12.4/Lq	[72]
Sugarcane bagasse biochar/Chitosan composite (SBCT)	0.5–4	4	4	5.1	9.01/Lq	Our study

Note: C₀—Initial concentration (mg/L); t_eq—equilibrium time (h); q_eq—Equilibrium adsorption capacity (mg/g); q_max—Maximum adsorption capacity (mg/g)/Isotherm model; L_q—Langmuir Isotherm; F_e—Freundlich Isotherm; L_q-F_e—Langmuir Freundlich Isotherm.

. The initial PFOA concentrations in the different studies vary, making it difficult to compare the adsorption capacities of the SBCT composite directly with different adsorption studies. The present study investigated the performance of SBCT under relatively low concentrations ranging between 0.5 and 4 mg/L. Rather than maximizing adsorption capacity at elevated concentrations, the SBCT composite is positioned as a sustainable and low-cost adsorbent that demonstrates effective PFOA removal at low concentrations, making it suitable for decentralized and resource-constrained treatment applications. The PFOA adsorption using adsorbents like Rice Husk Biochar [27] and Chitosan-Hydrogel [51] was evaluated at much higher concentrations of PFOA (100–2000 mg/L), naturally leading to higher adsorption capacities, which are not comparable with our results. The studies conducted at similar low initial PFOA concentrations, such as Granular activated carbon (GAC) ranges between 0.5 and 10 mg/L [73], Multiwalled carbon-nanotubes @ molecularly imprinted polymers (MWCNTs@MIPs) of 0.1 to 20 mg/L [72], and sulfur polymer-supported Powdered activated carbon (PAC) of 0.25 to 5 mg/L [62] is similar to our study. The SBCT developed in our study exhibited maximum adsorption capacity of 9.01 mg/g, which was comparable with MWCNTs@MIPs of 12.4 mg/g [72], and higher than sulfur-supported PAC of 0.355 mg/g [62], in addition, SBCT reached equilibrium within 4 h, significantly faster than GAC [73] for 120 h and comparable to MWCNTs@MIPs [72] of 2 h, with the advantages of low-cost, eco-friendly materials and simple synthesis without the need for complex modifications like molecular imprinting or sulfur polymer support. However, the maximum PFOA adsorption capacities will differ based on the testing conditions. The novel engineered SBCT composite stands out by combining environmental sustainability, fast kinetics, and effective PFOA removal even at low concentrations.

3.7. A Sustainable Technology for Water Treatment

Developed economies can afford advance techniques for removal of PFAS from water. However in developing countries, given the challenges of open drains or direct discharges releasing such persistent micropollutants in the water bodies, there is a basic need of a filtering medium using a low-cost adsorbent [25]. Cost-effective engineered SBCT composite can provide a solution for eliminating PFOA from wastewater or contaminated water bodies. This lab-scale study includes adsorption experiments using aqueous solutions, whereas real wastewater systems are far more complex. The presence of competing ions, dissolved organic matter, fluctuating pH, and variable contaminant loads may hinder adsorption efficiency and affect reproducibility under field conditions. It is to be noted, that the variability in the source, composition, and quality of raw materials, especially biochar precursors and biopolymer content, may affect the physicochemical properties and adsorption efficacy of the composite at larger scales. Consequently, the standardization of raw material selection and synthesis parameters will be crucial for ensuring uniform performance. Pilot-scale studies and long-term field trials using real wastewater matrices are required to validate the robustness and reliability of SBCT under realistic operating environments.

It is important to note that if not properly managed, saturated composites may pose environmental risks and serve as a secondary pollution source. The post-treatment of the adsorbent is necessary because the adsorption technology can only transfer PFOA from aqueous media to the solid phase. The application of advanced oxidation processes (AOPs) such as UV/H₂O₂ or ozone treatments or even bioremediation techniques can facilitate complete degradation of adsorbed contaminants by promoting sustainable reuse or safe disposal. Therefore, optimizing adsorbent recovery, integrating AOPs for contaminant destruction, and developing cost-effective regeneration protocols to ensure environmental safety and economic feasibility are necessary for the successful implementation of treatment. Our engineered SBCT composite can be modified based on the real-time conditions. From a scale-up perspective, the use of inexpensive raw materials from waste organic products, an uncomplicated synthesis pathway, and compatibility with decentralized treatment systems enhance the practical feasibility of SBCT for applications outside laboratory settings. Real-time application of our novel SBCT can contribute in advancing Sustainable Development Goals (SDG)—SDG 6 (Clean Water and Sanitation), SDG 14 (Life under water), and SDG 11 (Sustainable Cities and Communities).

4. Conclusions

We designed and prepared engineered biochar composite-SBCT for the effective removal of PFOA, which is effective even at a very low concentration (0.5 mg/L) from aqueous media. The SBCT composite achieved enhanced PFOA adsorption capacities under varied environmental conditions, outperforming many conventional materials. The removal of PFOA was effective under acidic pH conditions. The adsorption mechanism of PFOA on SBCT is further evaluated using an isotherm study and kinetic modeling, demonstrating favorable alignment with pseudo-first-order kinetics and the Langmuir isotherm model with a maximum adsorption capacity of 9.01 mg/g. Together with the kinetic analysis, our thermodynamic results confirm the physisorption phenomenon of SBCT engineered composite. In addition, it is evident that the electrostatic interactions enhanced PFOA affinity toward SBCT without altering the overall adsorption mechanism.

SBCT composite can be used as a low-cost and sustainable material with potential for further scale-up and process optimization.