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Hydrothermal Modification of Activated Carbon Enhances Acetaminophen Adsorption: Experimental and Computational Evidence of π–π Interaction Dominance

A peer-reviewed version of this preprint was published in:
Molecules 2025, 30(21), 4295. https://doi.org/10.3390/molecules30214295

Submitted:

15 September 2025

Posted:

17 September 2025

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Abstract
Acetaminophen (APAP) is a widely used pharmaceutical increasingly detected as a contaminant in aquatic environments due to its persistent nature and incomplete removal by conventional wastewater treatment. This study investigates the adsorption performance and mechanisms of commercial activated carbon (M) and its hydrothermally modified form (MH) for APAP removal. Characterization via elemental analysis, X-ray photoelectron spectroscopy (XPS), and N2 adsorption isotherms revealed that hydrothermal treatment reduced oxygen content and enhanced micro- and mesopore volumes, resulting in a more homogeneous and carbon-rich surface. Batch adsorption experiments conducted under varying pH (5–7) and temperature (30–40 °C) conditions showed that MH achieved up to 94.3% APAP removal, outperforming the untreated carbon by more than 15%. Kinetic modeling indicated that adsorption followed a pseudo-second-order mechanism (R² > 0.99), and isotherm data fitted best to the Langmuir model for MH and the Freundlich model for M, reflecting their differing surface properties. Adsorption was enhanced at lower pH and higher temperatures, consistent with an endothermic and pH-dependent mechanism. Complementary density functional theory (DFT) simulations confirmed that π–π stacking is the dominant interaction between APAP and the carbon surface. The most favorable configuration involved coplanar stacking with non-oxidized graphene (ΔG = −33 kJ/mol), while oxidized graphene models exhibited weaker interactions. Natural Bond Orbital (NBO) analysis further supported the prevalence of π–π interactions over dipole interactions. These findings suggest that surface deoxygenation and improved pore architecture achieved via hydrothermal treatment significantly enhance APAP adsorption, offering a scalable strategy for pharmaceutical pollutant removal in water treatment applications.
Keywords: 
activated carbon
;  
hydrothermal treatment
;  
acetaminophen/paracetamol adsorption
;  
pharmaceutical contaminants
;  
DFT modeling
;  
π–π interactions
Subject: 
Chemistry and Materials Science  -   Surfaces, Coatings and Films

1. Introduction

Acetaminophen (APAP), also known as paracetamol or N-(4-hydroxyphenyl)acetamide, is a widely used over-the-counter and prescription non-steroidal analgesic and antipyretic. Its primary pharmacological action involves the inhibition of prostaglandin synthesis through cyclooxygenase (COX-1 and COX-2) pathways, thereby alleviating pain and reducing fever. Global consumption of APAP is substantial, estimated at nearly 1.5 tons annually [1,2,3]. China and India currently lead global production, accounting for over 70% of the total supply [4,5].
Despite its therapeutic benefits, APAP has been increasingly recognized as a persistent and ubiquitous contaminant in aquatic environments, posing a pressing environmental and health concern. Its widespread usage, combined with incomplete removal in conventional wastewater treatment plants (WWTPs), contributes to its frequent detection in wastewater effluents, surface waters, groundwater, and even seawater. Reported concentrations range from nanograms to milligrams per liter. [1,6,7]. With a solubility of 305 mg/L at 25 °C and a Log Kow of 0.46, APAP is relatively hydrophilic and poorly adsorbed onto organic matter, contributing to its mobility in aquatic systems. Following administration, approximately 90% of APAP is excreted via urine in both unchanged and conjugated forms [8]. Additional pathways of environmental contamination include discharge from pharmaceutical manufacturing and improper disposal of expired or unused medications [1]. The direct release of untreated or partially treated wastewater, a significant source of APAP, can have severe ecotoxic effects on aquatic species and carcinogenic and mutagenic effects on humans [9].
The environmental occurrence of APAP has consequences. It has been documented in surface water, groundwater, and drinking water sources across 29 countries, with reported concentrations averaging 0.161 μg/L and reaching a maximum of up to 230 μg/L. These concentrations, even at the lower end of the range, are significant and indicate the widespread presence of APAP in our water sources, posing potential risks to both the environment and human health [10].
Human health risks associated with APAP include severe hepatotoxicity, oxidative stress, DNA damage, and liver failure in overdose scenarios. Environmentally, it is classified as a high-risk pollutant, particularly to aquatic organisms [11,12,13]. Aquatic invertebrates such as Daphnia magna, as well as fish species like Danio rerio and trout, exhibit sensitivity to APAP even at trace levels, manifesting in oxidative stress, enzyme inhibition, and developmental impairments [14,15]. Notably, paracetamol was identified as the NSAID (nonsteroidal anti-inflammatory drugs) that disrupted the most significant number of oxidative stress biomarkers, underscoring its ecotoxicological relevance [16]. Plants also experience phytotoxic effects, including reduced concentrations of photosynthetic pigments and inhibited root growth [13].
While the challenges are significant, the potential of advanced treatment solutions beyond conventional methods is promising. A recent survey of 20 WWTPs in China revealed APAP in 19 of the samples, with concentrations ranging from 0.06 to 29.2 nM. However, despite high removal rates reported for APAP during secondary treatment [3,17,18], more toxic metabolites such as p-aminophenol have been detected post-treatment at elevated concentrations (23.93–108.68 nM), indicating the existence of metabolic bottlenecks in existing treatment processes [19]. This highlights the need for advanced treatment solutions beyond conventional methods, along with continuous monitoring strategies to mitigate potential environmental and health risks [8,20,21].
Several advanced remediation technologies have been explored for the removal of APAP. Among these, Advanced Oxidation Processes (AOPs) have garnered considerable interest due to their ability to generate highly reactive radicals, particularly hydroxyl (•OH), capable of mineralizing organic pollutants into benign by-products [3,22]. In AOPs, hydroxyl radicals play a key role in breaking down organic pollutants, including APAP, into simpler, less harmful compounds, thereby reducing their environmental impact. However, AOPs face limitations, including incomplete mineralization and the formation of toxic intermediates—especially during photocatalytic oxidation. Additionally, UV-based systems are energy-intensive, and their efficiency can be diminished by background organic matter or radical-scavenging ions present in complex water matrices. Membrane technologies, including microfiltration, ultrafiltration, nanofiltration, and reverse osmosis, provide an advanced treatment pathway. While these systems offer high separation efficiencies, they are often hindered by membrane fouling, increased energy consumption, and high operational costs, particularly in pressure-driven applications such as reverse osmosis [23,24]. Additionally, high energy consumption is a notable drawback, particularly in pressure-driven systems, such as reverse osmosis, which require substantial energy inputs to maintain optimal performance.
Electrochemical methods, particularly Electrochemical Advanced Oxidation Processes (EAOPs), provide a flexible alternative for degrading pharmaceutical pollutants through redox reactions [25]. Recent innovations in nanostructured electrodes and catalytic coatings have significantly improved performance [26]. Integration with biological and membrane-based technologies has also demonstrated synergistic potential in complex treatment scenarios.
Biological remediation approaches, including phytoremediation and microbial biodegradation, have shown promise due to their sustainability and cost-effectiveness. Phytoremediation relies on specific plant species—often hardy or invasive—to absorb and transform pharmaceuticals through enzymatic pathways [27,28]. Similarly, microbial biodegradation utilizes bacteria, fungi, and microalgae capable of enzymatically degrading APAP via pathways involving amidases, oxygenases, and deaminases [13]. The low operational cost and environmental compatibility of biological methods make them an attractive option for sustainable water treatment. However, these methods are sensitive to environmental factors such as temperature, pH, and the presence of co-contaminants, which can impair microbial activity and overall efficiency.
Among the various remediation technologies, adsorption has emerged as one of the most promising strategies for removing emerging contaminants, including pharmaceutical contaminants from water systems [29,30,31,32,33]. Adsorbents, such as activated carbon and biochar, capitalize on their high surface area, porosity, and tunable surface chemistries to effectively capture organic contaminants [34]. Activated carbon, available in both granular (GAC) and powdered (PAC) forms, is particularly valued for its cost-effectiveness, chemical stability, and high adsorption capacity. Surface modifications, including oxidation and amination, further enhance its performance by introducing reactive functional groups that improve affinity toward ionizable or polar compounds such as APAP [20,35,36,37]. Advanced materials such as metal-organic frameworks (MOFs), carbon nanotubes (CNTs), and graphene derivatives exhibit even higher adsorption capacities. However, their high production costs and limited scalability remain significant barriers to widespread application [38,39]. In contrast, activated carbon offers a practical and scalable solution, especially for large-scale water treatment applications. Despite its advantages, adsorption-based remediation is not without challenges. Regeneration of spent adsorbents via thermal or chemical means is often energy-intensive and can degrade material integrity over time [40]. Moreover, safe disposal or recycling of exhausted adsorbents is critical to prevent secondary contamination. Nonetheless, continued advancements in adsorbent materials and system design underscore the viability of adsorption, particularly using activated carbon, as a cornerstone strategy for APAP remediation.
Enhancing the yield and performance of activated carbons can be effectively achieved through modifications to their surface chemistry and porous structure. In this context, we have explored hydrothermal modification as a viable strategy to improve the physicochemical properties of activated carbon. This approach has yielded promising results in previous studies, where the modified materials demonstrated high adsorption capacities for contaminants such as thorium [41], uranium [42], and acetamiprid [43]. Additionally, these materials have shown catalytic activity in reactions relevant to the synthesis of fine chemicals [44], further highlighting their versatility and potential for multifunctional applications.
In this context, the present study explores the use of activated carbon for the adsorption and removal of acetaminophen from contaminated water. Particular emphasis is placed on elucidating the adsorption mechanisms, evaluating key performance parameters, and assessing the practical feasibility of applying this approach in real-world water treatment systems.

RESULTS AND DISCUSSION

Characterization of Carbonaceous Materials

The proximate analysis (heating program detailed in the Supplementary Material) yielded comparable results for both materials, with a slight reduction in fixed carbon content and a corresponding increase in volatile matter in the hydrothermally treated sample (MH), as shown in Table 1. Both samples exhibit high fixed carbon content, indicative of a significant degree of carbonization, characteristic of activated carbons.
The elemental composition of the organic phase (excluding ash content) is summarized in Table 2. Hydrothermal treatment results in an increase in carbon, nitrogen, and sulfur content, and a reduction in hydrogen and oxygen. The former three elements are typically embedded within the graphene basal plane and thus exhibit lower reactivity. Conversely, hydrogen and oxygen, commonly located at the edges or defects of the carbon matrix, are more susceptible to removal under hydrothermal conditions.
X-ray photoelectron spectroscopy (XPS) further confirms these trends. Atomic and mass-based compositions are reported in Table 3 and Table 4, respectively. Both samples display surfaces enriched in carbon, with MH showing a more uniform composition and detectable nitrogen content, not detected in M.
Deconvolution of the C 1s peak (Figure 1, Table 5) reveals that hydrothermal treatment significantly reduces the proportion of moderately oxidized carbon species (285.7 to 286.5 eV) and strongly oxidized carbon species (288.6 to 289.6 eV), associated with hydroxyl/ether/carbonyl and carboxylic/ester groups, respectively. In contrast, the signal at 284.8 eV, corresponding to sp² carbon or C–H/C–C bonding, increases in MH.
The deconvolution of the O 1s peak, while limited due to overlap and complexity of functional groups, reveals the emergence of a secondary component at 536.8 eV in MH in addition to the only one showed by M (533 eV), suggesting structural rearrangements during treatment (Figure S4). Other elemental peaks did not present sufficient resolution for further analysis.
The point of zero charge (PZC) increased from 7.51 (M) to 8.06 (MH), indicating a reduction in surface acidity. This is consistent with the XPS results showing a decrease in oxygenated groups following hydrothermal treatment.
The FTIR spectra of both samples is shown in Figure 2. There are some small differences between them.
Some of the main bands observed are: 3450 cm-1 (O-H), 1700 cm-1 (C=O), 1550 cm-1 (C=C), 1140 cm-1 (C-O). It is observed that the 1700 cm-1 band only appears (weakly) in the MH sample. The band near 1140 cm-1 has a maximum in M and a double peak in MH. This indicates that changes have occurred in the functional groups possessing C-O single bonds as discussed in the XPS analysis. In addition, in the region between 1500 and 1300 cm-1 carbon backbone of these materials there is a decrease in the intensity at MH while the relative intensity of the 1550 cm-1 band increases. This implies that there are also changes in this part of the structure.
Nitrogen adsorption–desorption isotherms (Figure 3) demonstrate that both samples exhibit type IV isotherms with H4 hysteresis loops [45], typical of micro-mesoporous carbonaceous materials. MH displays a higher total N2 uptake.
Although MH shows a slight decrease in surface area, it exhibits higher micropore and mesopore volumes, which contribute to its improved adsorption performance. The pore size distribution (Table 6, Figure 4) further indicates a broader and slightly larger distribution in MH. In contrast, SEM micrographs (Figures S1 and S2, Supplementary Information) do not reveal any substantial morphological alterations.

Adsorption Experiments

The adsorption kinetics of acetaminophen (APAP) were evaluated using both adsorbent materials, M and MH, under varying pH (5, 6, and 7) and temperature conditions (30 °C and 40 °C). These parameters were selected to simulate hospital wastewater discharge scenarios, where APAP concentrations might be elevated. At these pH levels, APAP (pKa = 9.5) [46], predominantly exists in its neutral molecular form.
As shown in Figure 5(a) and 5(b), adsorption equilibrium was reached within 180 minutes for both adsorbents. MH consistently exhibited a significantly higher adsorption capacity than M across all conditions, with differences exceeding 15 percentage points. This enhanced performance is attributed to improved pore accessibility and surface chemistry introduced by hydrothermal treatment, which likely increases the availability of active sites. These conditions facilitate stronger adsorbate–adsorbent interactions, such as, π–π stacking, particularly relevant at pH values where APAP remains neutral. The sharper initial removal rates for MH suggest reduced diffusion resistance and improved mass transport properties.
To elucidate the adsorption mechanism, the kinetic data were fitted to pseudo-first order and pseudo-second-order models:
  • Pseudo-first-order model:
(1) l o g q e − q t = log q e − k 1 2.303 t
  • Pseudo-second-order model:
(2) t q t = 1 k 2 2 q e 2 + 1 q e t Where qt is the amount of adsorbate adsorbed at time t (mg/g); qe is the amount of adsorbate adsorbed in equilibrium; ki is the kinetic constant of the model (pseudo-first order: min -1 pseudo-second order: g/mg min); t is the time (min).
The pseudo-second-order model provided a significantly better fit across all experimental conditions (R² > 0.99). For example, under the MH_40_pH5 condition, an R² of 0.9995 was obtained, with a rate constant k = 0.2413 min⁻¹ and a calculated equilibrium removal of 94.3%. The kinetic parameters obtained are shown in Table 7.
Equilibrium adsorption isotherms were obtained at pH 5, 6, and 7, and at 30 °C and 40 °C, for both materials (Figure 6, Figure 7 and Figure 8). MH consistently outperformed M, with adsorption efficiency increasing by up to 19.9%. Higher temperature favored adsorption, consistent with an endothermic process.
The equilibrium data were modeled using the Langmuir and Freundlich isotherms (Table 8):
  • Langmuir equation:
(3) C e q e = 1 K L S m + C e S m Where K L is the Langmuir constant and S m is the adsorption capacity of a monolayer on the adsorbent.
  • Freundlich equation:
(4) log q e = log K F + 1 n log C e Where K F is the Freundlich constant that increases with the capacity of the adsorbent.
Carbon M fits the Freundlich model more closely, suggesting a heterogeneous surface with multiple active site types. In contrast, MH adheres better to the Langmuir model, indicating a more uniform surface chemistry and monolayer adsorption behavior. Despite similar monolayer capacities, experimental adsorption was consistently higher for MH. The Freundlich parameter n, which reflects adsorption favorability, was lower for MH, yet experimental results contradicted this, further supporting that different materials may align with different mechanistic models. As they respond to different mechanisms, the comparison of these parameters may not be correct.
To assess performance at higher concentrations, the effect of initial APAP concentration was evaluated. Table 9 summarizes these results. At low concentrations (100 mg/L), MH removed >93% of APAP across all conditions. Even at 500 mg/L, MH maintained a removal efficiency >57%, significantly outperforming M.
In conclusion, MH exhibits superior adsorption performance primarily due to changes in textural and chemical properties induced by hydrothermal treatment. The influence of temperature and pH, while present, is comparatively secondary. Adsorption is slightly more favorable at lower pH due to speciation effects and is enhanced at higher temperatures, suggesting an endothermic mechanism.

Computational Study

To gain further insight into the adsorptive interactions between APAP and the carbonaceous materials, a computational study was conducted using graphene and oxidized graphene models (see Supplementary Information, Figure S3). Geometry optimization was performed as outlined in the Experimental section. The oxidized graphene model included representative hydroxyl, carbonyl, and carboxylic functional groups.
The most stable configuration (model M3a) corresponded to a coplanar π–π stacking interaction between APAP and non-oxidized graphene, with a calculated free energy of adsorption of −33.0 kJ/mol (Figure 9(a)). In comparison, the analogous interaction with oxidized graphene (model M3b) yielded a less favorable ΔG of −25.7 kJ/mol (Figure 9(b)). This result is consistent with experimental findings, in which MH (lower oxygen content) exhibited higher adsorption capacity than M. However, it is noteworthy that this trend is not universal; for instance, prior simulations with phenol demonstrated enhanced adsorption on oxidized graphene [47].
Natural Bond Orbital (NBO) analysis revealed four significant interactions (>0.5 kcal/mol) in M3a versus two in M3b. These were primarily π–π stacking interactions, although one donor–acceptor interaction between APAP hydroxyl groups and graphene aromatic carbons is present as well. The stability of M3a suggests that π–π stacking dominates the adsorption mechanism.
To isolate the role of dipolar interactions, additional models (M4-1 to M4-6) were constructed in which APAP functional groups (hydroxyl or acetamide) were positioned near oxygenated groups on graphene (hydroxyl, carbonyl, or carboxyl), intentionally avoiding initial π–π stacking. During optimization, some systems (M4-2, M4-5) evolved into π–π stacked conformations, indicating a thermodynamic preference for these interactions. This can be better appreciated in Figure 10. The APAP molecule is initially facing a graphene’s carbonyl group (model M4-5), yet as geometry optimization develops, it keeps moving to find the most stable position located in a parallel plane above the graphene model. Others (M4-1, M4-3) retained dipolar contact but exhibited positive or near-zero ΔG values, suggesting less favorable adsorption. Finally, in the other two cases (M4-4 y M4-6), an intermediate situation was reached. Figure 11 shows the optimized geometries for all these models.
These results suggest that although dipole interactions may contribute to adsorption under certain conditions, the dominant interaction mechanism for APAP on carbonaceous materials is π–π stacking. The relatively small energy differences among various binding sites further support the experimental observation that surface structure and chemical homogeneity critically influence adsorption behavior.

MATERIALS AND METHODS

Materials

Acetaminophen was purchased from Sigma-Aldrich (Merck Group, Darmstadt, Germany). Commercial activated carbon granular 1.5 mm extrapure (Ref. 1.02514) was acquired also from Merck. Distilled water was used as a solvent in all determinations.

Synthesis of the Hydrothermal Carbon

MH Preparation

The commercial carbon material M (4 g) was treated with distilled water (50 mL) in a Teflon® vessel reinforced with a duraluminium outer jacket at a temperature of 180 ºC during 20 h. The content was filtered in a funnel with a filter plate and washed with 200 mL of distilled water. Then, it was dried in an oven at 110 °C for 24 h.

Characterization of the Activated Carbons

Textural characterization was performed by N2 adsorption isotherms at 77 K in an Anton Paar GmbH (Graz, Austria) Quantachrome Quadrasorb Evo equipment with prior degassing at 200 °C for 24 h , and the specific surface area was calculated by applying the BET method [48]. Elemental analysis (C, H, N, S, O) was performed using a Leco (St. Joseph, MI, USA) CHMS-932 elemental analyzer. C, H, N, and S were analyzed, and the difference was assigned to ash and oxygen content. Ash quantification was carried out in a Netzsch (Selb, Germany) STA 449 F3 Jupiter thermobalance (see heating program in Table S1). The point of zero charge (PZC) values were determined using the method proposed by Valente Nabais and Carrott [49]. A Hitachi (Tokyo, Japan) field emission scanning electron microscope (SEM) S-4800 and a FEI (Hillsboro, OR, USA) field emission scanning electron microscope (SEM) Quanta 3D FEG, were used to explore the surface morphological characteristics of all samples. The sample analysis was performed under high-vacuum conditions. X-Ray photoelectron spectra (XPS) were recorded on a SPECS (Zürich, Switzerland) FlexPS-ARPES-E SPECS instrument using monochromatic Al Kα radiation at 1486.68 eV. Fourier-transform infrared spectra were recorded in a Bruker (Billerica, MA, USA) Vertex70 spectrometer in the 400–4000 cm−1 range, with a DLaTGS detector and a 0.4 cm−1 spectral resolution. A KBr tablet was prepared with 1/250 dilution.

Adsorption Experiments

Adsorption Kinetics

In Erlenmeyer flasks, 200 mL of a 100 mg/L acetaminophen (APAP) solution at pH 5, 6, and 7 were placed, the pH was adjusted by adding dropwise 0.01M HCl and NaOH buffer solutions, then 200 mg of Merck (M) or Merck hydrothermal (MH) carbon were added. The experiments were placed in a constant shaking bath at 30 °C and 40 °C, where 3 mL of sample were taken at 5, 10, 20, 30, 60, 120, 180, 240, 300, 360, 420, 480, and 1440 min.

Adsorption Isotherm

40-mL solutions containing 200, 300, 400, 500, and 600 mg/L of APAP at pH 5, 6, and 7 were placed in Erlenmeyer flasks, followed by the addition of 40 mg of adsorbent. The tests were stirred for 24 h at 30 °C and 40 °C. The studies were performed in triplicate. After this time, an aliquot of the APAP solution was taken after 24 h, and the residual concentration was quantified.
The adsorption capacity of the materials was determined using equation 5.
(5) q e = C i − C f V m Where qe is the adsorption capacity at 24 h (mg/g), Ci is the initial concentration of APAP (mg/L), Cf is the concentration of APAP at 24 h (mg/L), V is the volume of APAP placed in the tests (L) and m is the mass of adsorbent placed during the experiments (g).

Analytical Determinations

Samples were analyzed using a UV-Vis spectrophotometer Shimadzu (Kyoto, Japan) at a wavelength of 249 nm.

Computational Details

The computational study was performed using the Gaussian16 (Revision A.03) package [50] with the PW6B95D3/Def2SVP DFT level of theory. The calculations were carried out in water (SMD model) [51].
The thermodynamic parameters for the two-molecule models were calculated by subtracting the calculated data of the individual molecules from the joint model result.
To study which are the most important interactions between APAP and graphene we have used NBO Analysis. This method transforms the wave functions used in the DFT calculation into localized forms (bonds and orbitals). It is often used to determine the Lewis structure of a compound but, in our case, we have used the second order perturbation theory to calculate the donor-acceptor interactions and estimate the energetic importance of each one.

CONCLUSIONS

Hydrothermal modification of commercial activated carbon significantly enhanced its physicochemical properties by increasing carbon and nitrogen content, reducing surface oxygen functionalities, and improving micro- and mesoporosity. The modified material (MH) exhibited superior adsorption performance for acetaminophen (APAP), achieving up to 94.3% removal under optimal conditions. Adsorption kinetics were best described by the pseudo-second-order model, while equilibrium data indicated that MH follows the Langmuir isotherm and M aligns more closely with the Freundlich model, reflecting differences in surface homogeneity. The adsorption process was only slightly favored at lower pH and higher temperatures. Density functional theory (DFT) calculations supported these findings, revealing that π–π stacking interactions dominate the adsorption mechanism and are strongest on non-oxidized carbon surfaces. Together, the experimental and computational results demonstrate that hydrothermal treatment is a promising and scalable strategy for enhancing the performance of activated carbon in the removal of pharmaceutical contaminants from water.

Supplementary Materials

The following supporting information can be downloaded at the website of this paper posted on Preprints.org, Figure S1. SEM images of M; Figure S2. SEM images of MH; Figure S3. Models of APAP (M1), graphene (M2a) and oxidized graphene (M2b); Figure S4. O 1s XPS spectra for (a) M and (b) MH; Table S1. Heating program.

Author Contributions

Conceptualization, C.J.D.V. and M.A.P.; methodology, C.J.D.V. and M.A.P.; formal analysis, A.G.C.C. and I.M.L.C.; investigation, A.G.C.C. and M.A.P.; resources, C.J.D.V. and I.M.L.C.; writing—original draft preparation, I.M.L.C., A.G.C.C. and M.A.P.; writing—review and editing, C.J.D.V. and I.M.L.C.; visualization, C.J.D.V., M.A.P., A.G.C.C. and I.M.L.C.; supervision, C.J.D.V.; project administration, C.J.D.V.; funding acquisition, C.J.D.V. and I.M.L.C. All authors have read and agreed to the published version of the manuscript.

Funding

This research was funded by European Union (European Regional Development Fund (85%)) and the Junta de Extremadura grant number GR24050 and the Ministerio de Ciencia e Innovación of Spain, grant number PID2021-124021OB-I00.

Institutional Review Board Statement

Not applicable

Data Availability Statement

The data will be provided upon request to the authors..

Acknowledgments

The authors would like to thank the members of the Servicio de Apoyo a la Investigación at the Universidad de Extremadurafor their work.

Conflicts of Interest

The authors declare no conflicts of interest.

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Preprints 176794 g001
Figure 1. C 1s XPS spectra for (a) M and (b) MH.
Figure 1. C 1s XPS spectra for (a) M and (b) MH.
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Figure 2. FTIR spectra of M and MH.
Figure 2. FTIR spectra of M and MH.
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Figure 3. N₂ adsorption isotherms at 77 K.
Figure 3. N₂ adsorption isotherms at 77 K.
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Figure 4. Pore size distribution (DFT method).
Figure 4. Pore size distribution (DFT method).
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Figure 5. APAP removal kinetics for (a) M and (b) MH. Numeric data from pH 5, 40 ºC experiment.
Figure 5. APAP removal kinetics for (a) M and (b) MH. Numeric data from pH 5, 40 ºC experiment.
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Figure 6. Adsorption isotherm for APAP onto M and MH at pH 5, 30 °C and 40 °C.
Figure 6. Adsorption isotherm for APAP onto M and MH at pH 5, 30 °C and 40 °C.
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Figure 7. Adsorption isotherm for APAP onto M and MH at pH 6, 30 °C and 40 °C.
Figure 7. Adsorption isotherm for APAP onto M and MH at pH 6, 30 °C and 40 °C.
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Figure 8. Adsorption isotherm for APAP onto M and MH at pH 7, 30 °C and 40 °C.
Figure 8. Adsorption isotherm for APAP onto M and MH at pH 7, 30 °C and 40 °C.
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Figure 9. Optimized geometries of APAP interaction with (a) non-oxidized (M3a) and (b) oxidized graphene (M3b).
Figure 9. Optimized geometries of APAP interaction with (a) non-oxidized (M3a) and (b) oxidized graphene (M3b).
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Figure 10. Optimization trajectory of model M4-5 showing APAP shifting into π–π stacked conformation.
Figure 10. Optimization trajectory of model M4-5 showing APAP shifting into π–π stacked conformation.
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Figure 11. Optimized geometries of APAP with oxidized graphene in models M4-1 through M4-6, with corresponding ΔG values.
Figure 11. Optimized geometries of APAP with oxidized graphene in models M4-1 through M4-6, with corresponding ΔG values.
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Table 1. Proximate analysis (dry basis, wt%) of the carbon materials.
Table 1. Proximate analysis (dry basis, wt%) of the carbon materials.
Sample Fixed Carbon (%) Volatile Matter (%) Ash (%)
M 92.62 3.41 3.97
MH 90.78 5.13 4.09
Table 2. Elemental composition of the organic fraction (wt%).
Table 2. Elemental composition of the organic fraction (wt%).
Sample C (%) H (%) N (%) S (%) O a (%)
M 81.54 2.12 0.77 0.71 14.86
MH 92.17 0.81 1.33 0.78 4.90
a Oxygen content determined by difference.
Table 3. Surface elemental composition (atomic %) by XPS.
Table 3. Surface elemental composition (atomic %) by XPS.
Sample C 1s (%) O 1s (%) N 1s (%) S 2p (%) Si 2p (%) Al 2p (%)
M 94.05 5.01 n.d. 0.13 0.61 0.20
MH 94.22 4.12 0.78 0.30 0.58 n.d.
Table 4. Surface elemental composition (wt%) by XPS.
Table 4. Surface elemental composition (wt%) by XPS.
Sample C 1s O 1s N 1s S 2p Si 2p Al 2p
M 91.36 6.48 0.00 0.34 1.39 0.44
MH 91.68 5.34 0.88 0.78 1.31 0.00
Table 5. Components of the C 1s peak obtained by deconvolution.
Table 5. Components of the C 1s peak obtained by deconvolution.
B.E., eV (%)
M 284.8 (52.75 %) 285.7 (23.95 %) 288.6 (23.3 %)
MH 284.8 (74.69 %) 286.5 (16.2 %) 289.6 (9.11 %)
Table 6. Textural properties from N₂ isotherms.
Table 6. Textural properties from N₂ isotherms.
SBET VDR Vme Vtotal
m2/g cm3/g cm3/g cm3/g
M 839.10 0.336 0.103 0.448
MH 808.26 0.384 0.130 0.533
model BET DR DFT
Table 7. Kinetic parameters for APAP adsorption on M and MH.
Table 7. Kinetic parameters for APAP adsorption on M and MH.
M MH
30 °C 40 °C 30 °C 40 °C
pH 5 pH 6 pH 7 pH 5 pH 6 pH 7 pH 5 pH 6 pH 7 pH 5 pH 6 pH 7
P-first order qe 28.65 28.44 29.78 32.34 28.99 31.06 29.15 29.64 30.01 28.67 28.53 79.97
k 0.0981 0.1004 0.0693 0.0702 0.0797 0.0769 0.0785 0.0758 0.0721 0.0864 0.0797 0.0267
R2 0.7293 0.7393 0.6019 0.6139 0.6339 0.6599 0.5487 0.5391 0.5202 0.5860 0.5446 0.4169
P-second order qe 34.01 33.33 29.41 34.25 34.13 31.95 51.02 50.51 49.50 52.63 51.55 50.51
k 0.1882 0.1882 0.2058 0.1960 0.2067 0.1781 0.2489 0.2456 0.2608 0.2413 0.2640 0.2623
R2 0.9976 0.9975 0.9975 0.9979 0.9983 0.9937 0.9995 0.9994 0.9996 0.9995 0.9997 0.9995
Table 8. Isotherm model parameters for APAP adsorption.
Table 8. Isotherm model parameters for APAP adsorption.
Langmuir Freundlich
T, °C Carbon pH R2 Sm KL R2 KF n
30 M 7 0.9615 298.5 1.08·10-3 0.9930 1.96·10-3 0.4574
30 MH 7 0.9945 307.7 1.81·10-3 0.9184 2.13·10-6 0.3125
40 M 7 0.9654 302.1 1.01·10-3 0.9960 1.57·10-3 0.4507
40 MH 7 0.9952 309.6 1.62·10-3 0.9168 1.28·10-6 0.3050
30 M 6 0.9670 296.7 1.02·10-3 0.9903 1.65·10-3 0.4521
30 MH 6 0.9930 308.6 1.70·10-4 0.9100 1.64·10-6 0.3086
40 M 6 0.9676 294.1 9.25·10-4 0.9915 7.96·10-4 0.4276
40 MH 6 0.9951 311.5 1.49·10-4 0.8982 1.22·10-6 0.3055
30 M 5 0.9729 302.1 9.54·10-4 0.9918 1.60·10-3 0.4538
30 MH 5 0.9931 308.6 1.55·10-4 0.8881 1.87·10-6 0.3125
40 M 5 0.9732 295.0 8.43·10-4 0.9950 5.28·10-4 0.4162
40 MH 5 0.9956 311.5 1.35·10-4 0.8766 1.21·10-6 0.3074
Table 9. Influence of initial APAP concentration on adsorption performance.
Table 9. Influence of initial APAP concentration on adsorption performance.
Material Temperature (°C) Adsorption capacity (mg/g) Removal efficiency (%)
pH 5 pH 6 pH 7 pH 5 pH 6 pH 7
[APAP] 100 mg/L
M 30 79.44 78.70 78.15 75.30 74.60 74.10
40 83.33 81.48 79.63 79.00 77.30 75.50
MH 30 98.89 98.70 98.33 93.80 93.60 93.30
40 99.44 99.26 99.07 94.30 94.10 94.00
[APAP] 500 mg/L
M 30 242.35 238.15 236.98 46.4 45.60 45.40
40 244.63 240.74 239.88 46.90 46.10 45.90
MH 30 300.00 297.84 295.19 57.50 57.00 56.50
40 302.04 300.62 297.90 57.80 57.60 57.10
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