Pectin functionalized with Cu/Fe nanoparticles for enhanced degradation of methylene blue from wastewater

Introduction: In the present study, citrus pectin-stabilized copper/iron bimetallic nanoparticle (NP) catalyst has been used for the degradation of methylene blue (MB) dye in wastewater produced from the food industry.

Methods: The P@Cu/Fe composites were synthesized by co-precipitation and the sol–gel methods.

Results and discussion: The characterization of the composites was carried out using UV, FTIR, SEM, and XRD techniques, revealing that P₁@Cu/FeNPs synthesized through co-precipitation had a particle size of 150–35 nm with an irregular spherical and hexagonal shape. P₂@Cu/FeNPs, synthesized using the gel combustion method using triethylamine as fuel, proved to be a better nanocatalyst with spherical particles having a uniform structure and size distribution of 105–23 nm. The mean zeta potential value of P₁@Cu/FeNPs was found to be between 0 and 5mv, showing the composite to be less stable and 13 mv for more stable P₂@Cu/FeNPs. The degradation of MB by P₁@Cu/FeNPs was recorded up to 23.57% after 35 min and the nanocomposite synthesized by the sol–gel method exhibited 97.28% degradation in 30 min. The P₂@Cu/FeNPs performed the best degradation due to their synergistic impact. In essence, this research represents a step toward the synthesis of bimetallic NPs using a biomaterial (citrus pectin) with improved synergistic photocatalytic potential that can induce different features in nanomaterials. Pectin-functionalized NPs using different metals should be synthesized and tested for different catalytic applications.

1 Introduction

In recent years, due to the rapid growth of industry, a huge amount of industrial waste are found to contain toxic dyes, heavy metals, and other harmful compounds that are being released into the environment. It has now become critical to remove dyes and heavy metals from wastewater in order to reduce the harmful effects of such effluents. The adsorption methods have currently received a lot of attention as a quick, inexpensive method (Zeinali et al., 2014). One refractory contaminant that is frequently found in the effluent of various industries is MB (Mengting et al., 2020). According to the latest data, for 100,000 commercially dyed products, 7 × 10⁵ tons of annually produced dyestuff are being released into aquatic environments. MB is a heterocyclic molecule identified as a cyanide and carbon monoxide antidote that is being used in the food industry for the testing of milk and dairy products. The presence of MB as a contaminant in water bodies has been reported to have detrimental effects on human health including irritation, nausea, diarrhea, dizziness, fever, and vomiting (Hamad and Idrus, 2022; Abuzeyad et al., 2024). MB prevents sunlight from entering the water body, which induces long-term effects on the ecosystem, harming aquatic life, and other living things. The basic structure of this particular dye consists of thiazine (Begum et al., 2017; Uddin et al., 2024). Such refractory pollutants have recently been investigated, and attempts have been made to remove these contaminants from wastewater using a variety of environmental technologies. The methods including Fenton’s oxidation, electrochemical treatment, ion exchange, biological treatment, and adsorption have been reported for the degradation of dyes (Yanyan et al., 2018; Zhou et al., 2022).

Due to their distinct porous properties, activated carbon (Mercier et al., 2014), zeolites, and metal–organic frameworks have been reported to adsorb dyes in water treatment (Hamad and Idrus, 2022). Additionally, pectin or pectin-containing substances, such as fruit waste and macroalgae, can remove coloring agents (Bardakçı et al., 2014). The most promising and understudied field of research in the 21st century is nanotechnology. In many reports, the ability of nanomaterials has been reported for the treatment of wastewater containing dyes and nano-adsorbents, and NPs have shown great potential to advance wastewater treatment (Kumari et al., 2019; Abuzeyad et al., 2024). These nano-adsorbents have gained popularity because they are made of magnetic cores and polymeric shells that not only have a large specific surface area but can also be easily adjusted by an external magnetic field for separation convenience. The demands of removing significant volumes of dyes, however, cannot be achieved by simple adsorption. Adsorption combined with photocatalytic degradation is said to be a more successful dye removal method (Sarkar et al., 2012; Biftu et al., 2020). Pectin is a hydrocolloid polysaccharide formed by the binding and polymerization of galacturonic acid (GalA) with natural sugars by a glycoside bond (1–4) that is the main constituent of the cell walls of the plant. Most materialistic (commercial/industrial) pectin is extracted from the peels of citrus and the residue of apples, each of which is a byproduct of juice production (Wang et al., 2021). Its major applications are as a stabilizers in shampoo and a thickener in cosmetics and personal care products (Picot-Allain et al., 2022).

Pectin molecules are flexible and open for modification purposes. The molecules carry a polyanion negative charge because of the ionization of the carboxyl group in their structure (Attallah et al., 2016). NPs of pectin are formed by the formation of intra-molecular and inter-molecular physical crosslinks and the existence of electrostatic interactions with the positively charged groups. Many divalent cations, such as BaCl₂, MnCl₂, and ZnCl₂, could be used for the pectin’s gelation, and spherical-shaped NPs are formed. Pectin structure stabilizes this shape (form) by the electrostatic interaction of the carbonate (CO₃) anions with the crosslinking cations (Ergin et al., 2021). Due to their unique properties, such as high specific surface area, low thermal conductivity, high porosity, and relative density, pectin-based nanocomposites represent a novel approach in advanced food packing materials as they could be used as drug delivery systems, inner layers, and sensors (Ahmadzadeh et al., 2018; de Oliveira et al., 2019). It has been demonstrated through results that the bonding of carboxy groups of pectin with Cu⁺² increased its adsorption capacity. The process was the preparation of pectin hydrogel with a low degree of esterification, which is why the adsorption capacity was strong on both Cu⁺² and water. In addition to Cu⁺², the adsorption behavior of pectin hydrogel has been investigated kinetically and thermodynamically (Shen et al., 2022). Physical and chemical adsorptions were the results of the Cu⁺² adsorption of hydrogel that was endothermic under natural conditions and favorable spontaneous adsorption led by the higher temperature (Saraf et al., 2016). Pectin has been used as an adsorbent, and NPs (CuS and CdS) served as the photocatalyst for the photocatalytic degradation of MB dye from wastewater under sunlight and lamp sources (Zhao and Zhou, 2016). The pectin@zirconium (IV) silicophosphate nanocomposite (Pc/ZSPNC) ion exchanger was synthesized by the sol–gel process, and a fine particle size was obtained. In the presence of sun radiation, Pc/ZSPNC displayed enhanced capacity and catalytic activity for the degradation of the MB dye. After 60 min of radiation exposure, 97.02% of the MB dye was found to be removed (Pathania et al., 2015). Pectin, a natural biopolymer, was used for the synthesis of PdNPs. Size-controlled PdNPs with a smaller size of 27.9 nm were generated at 70°C. Estimating catalytic efficiency in the discoloration of azo dye confirmed the catalytic potency of PdNPs prepared from pectin due to their greater surface area. Only 15 min were necessary for the degradation of the dye (Emam et al., 2020). A biopolymer pectin-graphene oxide (Pc/GO) nanocomposite was synthesized, and its effectiveness in photocatalytically degrading organic pollutants, including MB and methyl orange (MO) dyes, as well as the adsorptive removal of Cr (III) ions, was examined (Kaushal et al., 2020). A cross-linked copolymer network (Pec-g-PAMPS) was produced by free radical polymerization of a combination of 2-acrylamido-2-methylpropanesulfonic acid and pectin in the presence of N,N-methylenebisacrylamide. Using trisodium citrate to reduce silver nitrate inside the gel network, silver NPs were prepared and stabilized. MB removal from an aqueous solution using the hydrogel and the nanocomposite hydrogel was assessed using various methodologies (Baran, 2018). It has been found that Ag NPs significantly improve the Pec-g-PAMPS gels’ capacity to swell. After 3 cycles, the nanocomposite hydrogel maintained 80% of its efficiency, demonstrating its reusability for wastewater treatment (Babaladimath and Badalamoole, 2019).

Using a simple chemical precipitation method, pectin-MnO₂ and pectin SnO₂ nanocomposites were created. Under various experimental circumstances, the prepared nanocomposite was used as a catalyst for the oxidative breakdown of calmagiten, an azoic dye. Under various conditions, the pectin-MnO₂ nanocomposite/H₂O₂ system completely degraded the calmagite solution (Jabli et al., 2023). The Cu/FeNPs in the presence of hydrogen peroxide (H₂O₂) can catalyze a Fenton-like reaction. Fe₂O₃ and H₂O₂ combine in this process to form hydroxyl radicals (•OH), which are extremely reactive and capable of breaking down organic contaminants such as MB (Wang et al., 2016; Yang et al., 2019). Natural polysaccharide pectin offers functional groups (such as carboxyl and hydroxyl) that improve MB molecule binding onto the NPs’ surface. As a result, the MB concentration around the reactive sites increases. In addition to helping with adsorption, pectin stabilizes the NPs, keeping them from aggregating and preserving their high surface area and reactivity (Khodamorady and Bahrami, 2019).

Herein, the formation of novel hybrid composites of pectin has been carried out using cost-effective and eco-friendly precipitation and sol–gel methods. The main objective was to synthesize pectin biopolymer-based nanocomposites with a suitable pore size and the ability to maximize the degradation of MB dye. To the best of our knowledge, this study showed good results. Hence, this study will be an addition to the field of nanocomposite formation and an upgrade to the industrial use of their applications.

2 Materials and methods

2.1 Materials

Citrus pectin (98%), ferric chloride (FeCl₃) (99%), copper sulfate (CuSO₄) (99%), ethanol (98%), triethylamine (TEA) (98%), and sodium hydroxide (NaOH) (98%) were purchased from Sigma Aldrich. Wastewater samples containing MB were collected from the local food industry.

2.2 Synthesis of P₁@Cu/FeNPs

In order to fabricate P₁@Cu/FeNPs, an already reported co-precipitation method has been used (Figure 1). For this purpose, 0.4 M citrus pectin solution was made with 200 mL of distilled water, 0.1 M FeCl₃ (15 mL), and 0.1 M CuSO₄ (15 mL) were added in a conical flask, and stirred for 30 min at 60°C in the hot plate using a magnetic stirrer. NaOH solution was added to the mixture to obtain pH 3.5–4. As a result, the solution became concentrated, and a light greenish-brown jelly-type solution formed, indicating the formation of P₁@Cu/FeNPs nanocomposite (Doustkhah et al., 2018). The precipitates were kept in a drying oven for 6 h in a glass crucible for drying at 100°C. After drying, the precipitates were calcinated above 100°C (300–500°C) for 3 h (Younas et al., 2021).

Figure 1

Figure 1. Synthesis of Cu/Fe bimetallic nanoparticles with citrus pectin (the co-precipitation method).

2.3 Synthesis of P₂@Cu/FeNPs using the sol–gel method

An already reported sol–gel method was used for the synthesis of P₂@Cu/FeNPs (Figure 2). Shortly, 50 mL of triethylamine, 50 mL of ethanol, 200 mL of 0.4 M citrus pectin, 0.1 M of CuSO4 (50 mL), and 0.1 M solution of FeCl₃ (50 mL) were added in a conical flask and heated on a magnetic stirrer at 60°C for 30 min, with constant stirring. A very pungent odor was produced during this process. On removing from the hot plate and magnetic stirring, the solution was kept at room temperature to cool it down. A light brown colored gel was formed (Khashei et al., 2020; Bagherzade et al., 2021). The product was taken in a petri dish and heated at 300°C till the gel became brittle. The resulting material was crushed to fine particles with pestle mortar, and it resulted in P₂@Cu/FeNPs nanocomposite (Mehmood et al., 2022).

Figure 2

Figure 2. (A) Synthesis of Cu/Fe bimetallic nanoparticles with citrus pectin (the sol–gel method). (B) The mechanism of the formation of pectin functionalized Cu/FeNPs.

2.4 Characterization

The presence of different functional groups in P₁@Cu/FeNPs and P₂@Cu/FeNPs was evaluated with FTIR (BRUKER ALPHA-2). Crystallinity and phase composition of both composites were evaluated with X-ray diffraction (Bruker D8 Advance Eco) and morphology with field-emission scanning electron microscope (FE-SEM) (FEI Nova 450 NanoSEM). The catalytic performance results of samples were obtained with the help of a UV–visible spectrophotometer (CECIL 7400CE AQUARIUS).

2.5 Catalytic activity of P₁@Cu/FeNPs and P₂@Cu/FeNPs

The catalytic activity of P₁@Cu/FeNPs and P₂@Cu/FeNPs was investigated by a UV–visible spectrophotometer (CECIL 7400 CE AQUARIUS) in the scanning range of 200–800 nm. Each synthesized nanocomposite was sonicated in distilled water by using PG-215-Sonicator-017 for half an hour. Then 1 mL of the solution was taken in the test tube and covered the test tube with an aluminum foil sheet. The amount of MB measured in the wastewater solution was 0.03 mM. A dye sample was introduced into the test tube containing nanocomposite. The dye solution along with the nanocomposite sample was taken out from the solution mixture, and then the initial readings of the sample were recorded. After fixed intervals of time, readings were taken again (Nazir et al., 2022; Hassan et al., 2023). The degradation efficiency of the nanocomposites for the dye was determined with the help of the formula given below:

% Degradation = (A₁⁻A_t)/A₁ × 100.

Here, A₁ shows the initial absorbance of the solution containing dye along with the nanocomposite, and A_t shows absorbance at time “t” (Kaushal et al., 2020).

3 Results and discussion

3.1 Ultraviolet–visible spectroscopy

The absorbance of synthesized P₁@Cu/FeNPs by precipitated and P₂@Cu/FeNPs by the sol–gel method was recorded by UV–visible spectrophotometer (CECIL 7400 CE AQUARIUS) in the range of 200–800 nm. UV–vis spectrum P₁@Cu/FeNPs indicated λ_max value at 288 nm, which confirmed the presence of Fe metal (Latha and Gowri, 2014). The λ_max at 418 nm indicated the presence of citrus pectin, while λ_max at 578 nm confirmed Cu metal attachment to the nanostructure (Figure 3A). The spectrum for P₂@Cu/FeNPs shown in Figure 3B indicated a slight shift in the values of the λ_max with much sharper peaks but the ranges proved the presence of the same metals and groups, i.e., λ_max at 286 nm for Fe metal, 414 nm for citrus pectin, and 586 nm for Cu metal attached to the nanostructure (Rahman et al., 2019; Ghamari Kargar et al., 2022).

Figure 3

Figure 3. UV–vis spectrum of P₁@Cu/FeNPs (A) and P₂@Cu/FeNPs (B).

3.2 FTIR spectroscopy

The presence of functional groups and association with NPs were assessed in our samples by FTIR spectrophotometer (BRUKER ALPHA-2), and the results for both synthesized nanocomposite P₁@Cu/FeNPs and P₂@Cu/FeNPs are presented in Figures 4A–C. Mostly, the acid -OH broad peak overlapped with the -CH peak, which identified the acid. FTIR spectrum of citrus pectin can be seen in Figure 4A, which indicates the broad hydroxyl group peak for acids at 3322.51 cm⁻¹ that is closely spaced to -CH stretching vibrational band located at 2940.22 cm⁻¹. The stretching peaks related to the carbonyl group (C=O) in the free carboxylic acid group are indicated at 1609.33 cm⁻¹ (asymmetric stretching) and 1436.33 cm⁻¹ (symmetric stretching). The band at 1730.75 cm⁻¹ ascribes the esterified carboxyl group (C=O) of COOCH₃. The C-O stretching band can be seen at 1049.52 cm⁻¹ (Chylińska et al., 2014).

Figure 4

Figure 4. FTIR spectrum of pure Citrus Pectin (A), P₁@Cu/FeNPs (B), and P₂@Cu/FeNPs (C).

The FTIR spectrum of P₁@Cu/FeNPs, as seen in Figure 4B, the broadband at 3255.24 cm⁻¹ shows the hydroxyl group stretching of the acidic group, which is partially overlapped with the -CH stretching band (Sawant et al., 2016). The band is relatively stronger and weaker at 1615.85 cm⁻¹ and 1437.11 cm⁻¹, which describes the carbonyl group (C=O) of the free carboxylic group. The band at 1733.07 cm⁻¹ indicates the esterified carbonyl group of COOCH₃. The C-O stretching band was observed at 1012.17 cm⁻¹ (Sharma and Jeevanandam, 2013). The shifting of the band from 3322.51 cm⁻¹ to 3255.24 cm⁻¹ shows evidence for the attachment of Cu- metal, and the appearance of a band at 632.42 cm⁻¹ is due to the attachment of Fe metal to the pectin (Xue et al., 2021).

The FTIR spectrum of P₂@Cu/FeNPs is shown in Figure 4C. The band at 2978.44 cm⁻¹ is mainly ascribed to the -CH stretch of -CH, -CH_2, and -CH₃ groups in the pectin structure, while the vibrational broadband at 3339.94 cm⁻¹ describes the hydroxy group stretching of the acidic group, which is closely related to the -CH stretch band (Rana et al., 2019). The band attributed at 1625.76 cm⁻¹ is associated with the asymmetric vibration of the carbonyl group, while the weaker band at 1475.15 cm⁻¹ describes the symmetric vibration of the carbonyl group in the free carboxylic group. The peak at 1035.04 cm⁻¹ indicates the C-O stretching. The appearance of bands at 3339.94 cm⁻¹ and 807.02 cm⁻¹ proved the formation of Fe-Cu bimetallic NPs of pectin (Xue et al., 2021). Finally, all the vibrational stretching bands of both samples are closely related to the reference pure citrus pectin (Khorasani and Shojaosadati, 2019).

3.3 X-ray diffractometry

The crystalline structures of both synthesized nanocomposites were determined by powder XRD. As shown in Figure 5B, it can be seen that the characteristic broad diffraction peaks for P₂@Cu/FeNPs shown in wide-angle XRD patterns can be indexed to the cubic spinal magnetite Fe crystal structure, which shows diffraction peaks; the patterns indicated a crystalline structure at 2θ: 32.3^ο, 43.6^ο, 54.8^ο, and 62.7^ο, which are assigned to (101), (220), (311), and (440) (Rana et al., 2019). Furthermore, the XRD pattern of the CuO can be seen in Figure 5A, indicating the peaks at 2θ: 36.82^ο, 46.73^ο, 58.02^ο, 62.47^ο, and 71.32^ο corresponding to the (110), (111), (202), (202), (220), and (222) crystallographic phases in the XRD pattern that are related to CuO. Much sharper and more prominent peaks at values approximately the same as in Figure 5B were observed in Figure 5A.

Figure 5

Figure 5. XRD pattern of P₁@Cu/FeNPs (A) and P₂@Cu/FeNPs (B).

Low-angle XRD pattern of the P₁@Cu/FeNPs is also investigated and depicted in Figure 5A. The XRD pattern of both nanocomposites showed pronounced diffusion peaks from 20 to 30 that appeared due to pectin (Khashei et al., 2022). The XRD patterns of Fe and Cu immobilized on P₂@Cu/FeNPs show characteristic peaks whose relative intensities match well with the reported XRD of Fe₃O₄ magnetite and CuO (Nešić et al., 2018).

3.4 Scanning electron microscopy

The morphology of synthesized pectin-based nanocomposite by the precipitation method was analyzed by SEM and is shown in Figure 6A. SEM images of the sample represent the crystal structure of P₁@Cu/FeNPs as aggregated cubic-shaped particles. The particles with different diameters can be seen at a resolution of 200 nm, respectively. The diameter of pectin-based NPs was found to be 150 nm, 56 nm, and 32 nm. The results of the present study also agreed with the results of some previous studies (Zhang et al., 2013; Kurniawan et al., 2020). Similarly, the SEM images for P₂@Cu/FeNPs in Figure 6B represent the rhombic structured particles for ‘Cu, as well as spherical particles for ‘Fe’ in large agglomerates of pectin-based nanocomposites (Lu, 2019; Li et al., 2022). The nanocomposites synthesized by the sol–gel method showed a clear size reduction with a diameter of 105 nm, 45 nm, and 23 nm at a resolution of 200 nm.

Figure 6

Figure 6. SEM images of P₁@Cu/FeNPs (A) and P₂@Cu/FeNPs (B) at 200 nm.

3.5 Photocatalytic activity

It has been demonstrated in recent research that natural polysaccharides can interact with dyes to provide a better binding capacity, which can be advantageous for the environment in the treatment of dye wastewater (Khodamorady and Bahrami, 2019). It can be seen in Table 1 that chitosan, cellulose, and pectin are the best adsorbents among other classes of polysaccharides. Chitosan doped with multiwalled carbon nanotubes and ZnO showed maximum %age degradation of MB (Malekkiani et al., 2022) in the case of chitosan-based adsorbents. Similarly, for cellulose, cellulose-carbon-doped TiO₂ (Habibi and Jamshidi, 2019) and for pectin, pectin-GO nanocomposite (Kaushal et al., 2020) showed the best results for the degradation of MB. The current study showed approximately the same results but in less time.

Table 1

Table 1. Adsorption capacity of polysaccharide-related adsorbents for MB.

3.5.1 Photocatalytic activity of P₁@Cu/FeNPs

The spectrum for P₁@Cu/FeNPs (Figure 7A) confirmed that the wastewater containing dye was degraded by the synthesized NPs, and the decrease in absorbance proved the degradation of the dye (Gupta et al., 2015). The absorbance value of the reaction mixture containing synthesized NPs and MB (0.03 mM) at 664.5 nm was found to decrease after 15 min and 35 min. The decrease in absorbance confirmed the degradation of the dye and the percentage decrease was 14.86% after 15 min and 23.57% after 35 min (Ahmad and Ansari, 2021).

Figure 7

Figure 7. (A) Photocatalytic activity spectrum of P₁@Cu/FeNPs. (B) Photocatalytic activity spectrum of P₂@Cu/FeNPs.

3.5.2 Photocatalytic activity of P₂@Cu/FeNPs

It can be noticed that from Figure 7B, for P₂@Cu/FeNPs, sharp peaks were obtained for the degradation process. Initially, P₂@Cu/FeNPs were allowed to react with MB (0.03 mM) wastewater sample, and the absorbance was recorded in terms of full wavelength scan. After 10-, 20-, and 30-min intervals, the value of absorbance was found to be continuously decreasing. The decrease in the value of absorbance at the same wavelength confirmed the degradation process for wastewater containing MB dye (Gupta et al., 2015). The percentage degradation of the dye in terms of absorbance was 20.81% after 10 min, 71.79% after 20 min, and 97.28% after 30 min. The maximum degradation of MB was observed in the case of P₂@Cu/FeNPs as compared to P₁@Cu/FeNPs.

As compared to the previous literature, P₂@Cu/FeNPs showed approximately the same percentage degradation as MWCNTs/ZnO/Chitosan (Malekkiani et al., 2022), cellulose-carbon doped TiO₂ (Habibi and Jamshidi, 2019), and pectin-GO nanocomposite (Kaushal et al., 2020), but in a very short time.

The Cu/FeNPs bonded to the citrus pectin’s surface. When exposed to UV–vis light, the pollutant absorbs photons and becomes excited. The excited MB molecules then inject electrons into the NPs’ conduction band, producing positive carbon radicals. ·O₂^_ and ·OH are formed when the electrons injected into the band interact with the O₂ adsorbed on the surface of CuO and iron oxide NPs (Kaushal et al., 2020). Positive carbon radicals in the dyes are attacked electrophilically by the reactive oxygen species (·O₂^_), resulting in the formation of hydroxylated oxidation byproducts. The MB is then broken down into biodegradable oxidation byproducts, which are then adsorbed on the surface of citrus pectin (Nsom et al., 2019).

Cellulose-carbon doped TiO₂ (Habibi and Jamshidi, 2019), MWCNTs/ZnO/Chitosan (Malekkiani et al., 2022), and pectin-GO nanocomposite (Kaushal et al., 2020) showed enhanced degradation potential, as did the P₂@Cu/FeNPs, but in lesser time.

3.6 Zeta potential

The zeta potential of synthesized P₁@Cu/FeNPs by precipitated and P₂@Cu/FeNPs by the sol–gel method was recorded using Litesizer^™ 500 particle analyzer in the range of −200 to +200 mv zeta potential distribution. The zeta potential for P₁@Cu/FeNPs in Figure 8A shows a distribution from −80 mv to +60 mv with the mean zeta potential at zero, which confirmed the formation of electrical charges but was not very stable due to the mean value of 0 mv (Hodoroaba et al., 2019), and the value of +60 mv shows the stability of nanocomposites (Kumar et al., 2023). The zeta potential distribution for P₂@Cu/FeNPs shown in Figure 8B from −60 mv to 100 mv and a mean zeta potential of 13 mv indicated the formation of stable composites with variable charge distribution and dominance of positive charge of pectin-based Cu/FeNPs (Tabrizian et al., 2019). The larger the absolute value of ZP, the more chances there are for nanocomposite and nanoemulsion to repel and resist aggregate formation (Kumar et al., 2023).

Figure 8

Figure 8. Zeta potential of P₁@Cu/FeNPs (A) and P₂@Cu/FeNPs (B).

3.7 Statistical data analysis

The adsorption experiments were repeated in triplicate. All the obtained data were analyzed. The data analyses were performed using Origin software (Table 2).

Table 2

Table 2. Percentage degradation of MB and kinetics of the reaction.

4 Conclusion

Cu/Fe bimetallic NPs were synthesized with citrus pectin through precipitation and the sol–gel methods successfully. The Cu/Fe was integrated into the surface of citrus pectin, and the association was confirmed from the UV–vis and FTIR spectra. The crystallinity of the citrus pectin was found due to the attachment of Cu/Fe and confirmed by XRD, and the change in morphology of both nanocomposites was proved by SEM analysis. Pectin-functionalized Cu/FeNPs promote the breakdown of MB through a combination of adsorption, catalytic degradation (Fenton-like and other redox processes), synergistic electron transfer, and surface complexation mechanisms. While the Cu and Fe components offer catalytic activity and effective electron transfer processes, the pectin coating boosts adsorption capacity and stability. Together, these mechanisms result in efficient and enhanced degradation of MB in wastewater treatment applications. Changes in the concentration of the dye were recorded in terms of absorbance, and wastewater containing MB became clear in the presence of the nanocomposite. It was further proved that the nanocomposites prepared through the sol–gel method gave better results as compared to those prepared by the co-precipitation method. In comparison with the previously reported studies, P₂@Cu/FeNPs showed a very good percentage for the absorbance of MB dye in a short time. Studies proved that nanocomposite synthesized by the sol–gel method can be an excellent candidate for the removal of organic dyes from food and textile industry wastewater.

Data availability statement

The original contributions presented in the study are included in the article/supplementary material, further inquiries can be directed to the corresponding authors.

Author contributions

FH: Conceptualization, Investigation, Methodology, Supervision, Writing – original draft. UT: Investigation, Writing – original draft. SS: Investigation, Writing – original draft. PA: Data curation, Resources, Writing – review & editing. FA: Validation, Writing – review & editing. MA: Data curation, Writing – review & editing. UY: Software, Writing – review & editing. KA: Investigation, Writing – original draft. SA: Investigation, Writing – original draft. QZ: Conceptualization, Investigation, Writing – review & editing.

Funding

The author(s) declare financial support was received for the research, authorship, and/or publication of this article. The authors sincerely acknowledge the Researchers Supporting Project number (RSP2024R194), King Saud University, Riyadh, Saudi Arabia.

Conflict of interest

The authors declare that the research was conducted in the absence of any commercial or financial relationships that could be construed as a potential conflict of interest.

Publisher’s note

All claims expressed in this article are solely those of the authors and do not necessarily represent those of their affiliated organizations, or those of the publisher, the editors and the reviewers. Any product that may be evaluated in this article, or claim that may be made by its manufacturer, is not guaranteed or endorsed by the publisher.

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