Application of the Biomass of the Leaves of Diospyros kaki L.f. (Ebenaceae) in the Removal of Metal Ions from Aqueous Media

1. Introduction

The persistent rise in environmental contamination due to noxious agents like pesticides, dyes, pharmaceutical products, and potentially harmful metal species is an alarming trend. This phenomenon can be ascribed to the heightened industrial and agricultural activities aimed at fulfilling the growing demands of the population, the indiscriminate utilization of fossil fuels, and the exploitation of mineral resources. Consequently, the adverse repercussions of these detrimental anthropogenic practices are increasingly evident in the environmental impact caused by effluents containing toxic substances. The non-sustainability of production and exploitation methods is primarily responsible for the contamination (CARNEIRO et al., 2010; MINELLO et al., 2009; GARCÍA- SÁNCHEZ et al., 2022). Among the various types of environmental pollutants, potentially toxic metal species (formerly known as heavy metals) are responsible for several deleterious effects on organisms (GUPTA and KHAN, 2020; ZHANG; WANG and YAO, 2021; ALMEIDA; SOARES; FIGUEIRA, 2018). After entering the environment, heavy metals like copper, cadmium, zinc, lead, chromium, and arsenic have the potential to spread through the lithosphere, hydrosphere, and atmosphere, causing contamination across a significant portion of the planet. One of the most common ways of dispersion is through water, as they become solubilized in liquid media and then discharged into bodies of water that carry them over long distances from their sources, or by infiltration into the ground, reaching the groundwater. They can also be dispersed in the atmosphere, becoming adsorbed onto solid particles resulting from the burning of materials containing such elements. In this case, they can deposit on soils, lakes, and rivers, reaching distant regions, or undergo precipitation along with rain, causing the contamination of large areas (REEVE, 2002; BAIRD and CANN, 2011). As environmental pollutants, potentially toxic metal species do not undergo degradation and can be converted into organometallic species by bacterial activity in the medium. These compounds interact with organisms and are introduced into the food chain, causing the bioaccumulation and biomagnification of heavy metals in the environment (MANAHAN, 2000; ALMEIDA; SOARES; FIGUEIRA, 2018; REEVE, 2002). Organometallic compounds tend to pose a higher level of harm compared to free metal cations. This elevated hazard stems from their heightened attraction to the fatty tissues of aquatic organisms, leading to significantly higher bioconcentration factors. As a consequence, we can observe intoxication in communities that depend on aquatic animals for food (MANAHAN, 2000; ALMEIDA; SOARES; FIGUEIRA, 2018; REEVE, 2002). Given the inherent risks associated with the contamination of drinking water by heavy metals, which has a direct impact on human health, it is of great importance to develop and apply techniques for remediating wastewater. These techniques aim to prevent the emission of toxic metal species and the contamination of rivers, lakes, and seas. Among the methods for removing metal species from aqueous samples, solid-phase extraction using adsorbent materials is widely used due to its low cost, simplicity, and the possibility of anchoring different molecular ligands on the surfaces of the materials (ALCÂNTARA et al., 2004; MADRAKIAN; ZOLFIGOL; SOLGI, 2008; MAHMOUD et al., 2010; FERREIRA et al., 2011; PRADO et al., 2011; FILHO et al., 2013; HAJIAGHABABAEI et al., 2013; JORGETTO et al., 2013). This technique takes advantage of the presence of chelating or complexing groups (such as amines, amides, carboxylic acids, and hydroxyls) on the surface of the adsorbent, which are capable of sequestering metal ions and allowing the removal of such species from aqueous solutions. The chemical process entails the creation of covalent coordinate bonds between metal cations, which act as Lewis acids, and chemical molecules or groups anchored to the adsorbent’s surface, acting as Lewis bases. Lewis bases, including organic groups containing elements like N, O, S, and P, possess unshared electrons that can form covalent bonds with electron-deficient species (in this scenario, the metal cations). This ensures the secure immobilization of the metal species on the adsorbent, facilitating their effective removal (JORGETTO et al., 2015). Over time, several adsorbents have been proposed for remediating metal-contaminated wastewater, such as modified silicas, activated carbon, zeolites, sand, clays, cellulose polymers, industrial and agricultural residues, among others (AHMAD and AHMAD, 2022; GUPTA et al., 2012; MELLAH; CHEGROUCHE; BARKAT, 2006; PENG et al., 2012; LIU; WANG; LI, 2005; LI et al., 2021; WALCARIUS; MERCIER, 2010; NAIYA; BHATTACHARYA; DAS, 2008; SINGHA and DAS, 2013). Nevertheless, certain materials necessitate an organic functionalization process to enhance their adsorption capacity prior to their use as adsorbents. During this stage, a complexing or chelating molecule is bonded to the material’s surface, enabling it to effectively extract metal ions from the solution (FILHO et al., 2013; JORGETTO et al., 2013; WALCARIUS and MERCIER, 2010; SOUZA et al., 2011). Organofunctionalized materials present a serious disadvantage in terms of their application, namely the use of expensive reagents and solvents, as well as the generation of toxic waste during their synthesis and functionalization, which makes large-scale production for environmental purposes impractical (FERREIRA et al., 2011; FILHO et al., 2013; JORGETTO et al., 2013; SOUZA et al., 2011). As an eco-friendly substitute for synthetic materials, a range of adsorbents can be created from abundant naturally occurring organic materials, making them suitable for use in solid-phase extraction methods. Biomaterials, in particular, possess inherent complexing groups within their chemical composition, obviating the necessity for additional functionalization processes. The adsorption capabilities of these natural materials are linked to the inclusion of N, O, P, and S atoms (which act as Lewis bases) in their complexing groups, enabling the formation of covalent bonds through electron pair sharing with the metal species present in the solution (CASTRO et al., 2011; MARTINS et al., 2013). These biomaterials can be readily gathered and undergo uncomplicated preparation using basic techniques like drying, milling, and sieving, enabling their transformation into a finely powdered form suitable for conducting solid-phase extraction of metal species from aqueous solutions (SAAD et al., 2021; SEPEHRI et al., 2023). Biomaterials emerge as a compelling and cost-effective option for producing adsorbents to remediate wastewater (JORGETTO et al 2014; JORGETTO et al., 2015). Several biomaterials, such as banana peels (CASTRO et al., 2011), castor leaves (MARTINS et al., 2013), cassava root husks (JORGETTO et al., 2014), sugarcane bagasse (GURGEL and GIL, 2009), orange peels (GÖNEN and SERIN, 2012), peanut shells (ZHANG; LI; ZHOU, 2021), coconut fibers (GONZALES et al., 2008), pine bark (GUNDOĞDU et al., 2009), grass biomass (HOSSAIN et al., 2012), rice husk ash (NAIYA; BHATTACHARYA; DAS, 2009), green coconut shells (SOUZA et al., 2010), and corn leaves (SILVA et al., 2015), have already been studied regarding their adsorption capacities, demonstrating their effective removal of metal species from aqueous solutions. In addition to their low cost and ease of preparation, some of these materials can be reused for several adsorption/desorption cycles (CASTRO et al., 2011; MARTINS et al., 2013; KOBYA, 2004). In order to gauge a material’s potential suitability as an adsorbent, it becomes crucial to delve into the fundamental facets of its physicochemical properties. This inquiry aids in ascertaining the attraction between the adsorbent and specific metal species, alongside understanding the impact of environmental conditions such as pH and contact time on the material’s adsorption capacity. In this current study, we assessed the viability of a powder derived from Diospyros kaki L.f. (persimmon) leaves as a promising biosorbent for the removal of Cu(II) and Cd(II) from aqueous samples. The choice of this material is based on sustainability, as the leaves of this tree naturally fall during a certain period of the year (when the tree enters a stage of senescence), generating a large amount of available biomass (MATSUMOTO and SATO, 1997). Biosorbents, in addition to originating from renewable sources, have become a promising material as they do not require chemical modifications, making them even more economically viable (VAGHETTI, 2009; DEMIRBAS, 2008; AHALYA; RAMACHANDRA; KANAMADI, 2003). Thus, several relevant parameters that influence the adsorption process of metal species were investigated to elucidate the biosorbent properties of persimmon leaves.

2. Materials and Methods

2.1. Solvents, solutions and reagents

The solutions of Cu(II) and Cd(II) were prepared by dissolving their respective high-purity chlorides (Sigma-Aldrich, Steinheim, Germany) in ultra-pure deionized water (18.2 MΩ·cm^-1, Direct-Q system, Millipore, France) to obtain stock solutions of approximately 500 mg L^-1 for both metals. Treatments involving Cu(II) and Cd(II) solutions of distinct concentrations were prepared through the process of dilution, starting from the stock solutions, to achieve the intended concentrations. The standard metal solutions used for calibration of the spectrometer were prepared by diluting their respective 1000 mg L^-1 stock solutions (Specsol, Brazil). For pH adjustment, dilute solutions of HNO₃ (Carlo Erba) and NaOH (Merck, Darmstadt, Germany) were used. All containers were washed with 10 % v.v. HNO₃ for at least 24 hours, rinsed with deionized water, and dried at room temperature or in an oven heated to 50 °C prior to use.

2.2. Preparation of the biosorbent

The persimmon leaves were collected in the city of Botucatu, Brazil, and thoroughly washed with ultrapure water. They were placed in paper bags and stored in a ventilated chamber heated to 100 °C for one week to ensure complete drying. The dried material was manually ground and processed in a knife mill, resulting in a crude powder with particles of varying sizes. Subsequently, the material was sieved using sieves with different pore diameters. The fraction with a diameter between 63 and 106 μm was selected for the adsorption tests. Prior to conducting the experiments, the material underwent a washing process in a Soxhlet system, employing 500 mL of distilled water, until the washing effluent achieved clarity. This procedure was performed with the objective of eliminating water-soluble organic compounds liberated from the powder, which might otherwise interact with the metal ions and potentially hinder their adsorption onto the persimmon leaf particles. Following this, the washed material was subsequently transferred to a heated oven set at 55 °C to facilitate the evaporation of any residual solvent.

2.3. Equipments

The material was characterized by Fourier Transform Infrared Spectroscopy (FTIR) using a Nicolet Nexus 670 spectrometer. The sample was scanned 200 times with a resolution of 4 cm^-1 in transmittance mode. A 200 mg KBr pellet containing 1 % by weight of the sample was prepared to collect the spectrum of the persimmon leaves. Nitrogen, hydrogen, and carbon contents were determined through elemental analysis of 2.0 mg of the persimmon leaf powder using a Thermo Finnigan Flash 1112 Series EA CHNS elemental analyzer (CE Instruments). The concentrations of Cu(II) and Cd(II) were obtained at their most sensitive resonance spectral lines (324.7 and 228.8 nm, respectively) using a Shimadzu AA 7000 atomic absorption spectrometer in flame atomization mode (air-acetylene mixture). The morphology of the particles was observed using a Quanta 200 scanning electron microscope (FEI Company), and elemental mapping of N, P, S, and O was performed using an X-Max accessory (Oxford equipment) coupled to the electron microscope. The sample particles were dispersed in isopropanol, and the suspension was poured onto a glass slide. After drying, the sample was coated with gold. High-resolution ¹³C-NMR experiments were conducted at a magnetic field of 5.9 T using a DD2 NMR Agilent spectrometer. Samples were spun at up to 5.0 KHz in 4 mm zirconium rotors under magic angle conditions. The ¹³C spectra were obtained from {¹H}-¹³C cross-polarization experiments by applying a π/2 pulse of 6.0 µs on ¹H, a contact time of 1.0 ms, and a recycle delay of 5.0 s. 20,000 signals were collected. High-power proton decoupling was applied during the acquisition period in the cross-polarization experiments. A solid adamantine sample was used as a secondary standard for ¹³C isotropic chemical shift (high-frequency resonance at 38.6 ppm relative to tetramethylsilane, TMS), as well as for calibration of the {¹H}-¹³C cross-polarization conditions.

2.4. Point of zero charge (pH_PZC)

To provide a more comprehensive characterization of the adsorbent’s surface, we determined the point of zero charge (pH_PZC) through the immersion method. In these experiments, 25.0 mg of the powdered material was transferred to several Falcon tubes and stirred with 50.0 mL aliquots of a 0.01 mol L^-1 NaCl solution using a simple batch method on an axial axial homogenizer. The initial pH of these aliquots ranged from 2.0 to 12.0. Their pH was adjusted by the addition of dilute solutions of HCl and NaOH. The mixtures containing the material were stirred for 24 hours. At the end of the agitation period, the final pH of the solutions was measured (TAN et al., 2008). A calibrated pH meter, PHS-3B (PHTEK, Brazil), was used to record the initial and final pH of the solutions.

2.5. Batch adsorption experiments

To gain insight into the adsorption capabilities of the persimmon leaves powder and assess its suitability as a biosorbent, we explored critical parameters including kinetic equilibrium, pH impact, and maximum adsorption capacity. Batch experiments were conducted by stirring 10 mg of the adsorbent powder with 1.80 mL of the metal solution within 2.0 mL Eppendorf tubes, using an axial homogenizer. The material was subsequently filtered under pressure (to minimize contact between the metal species and the paper filter), and the supernatant was collected for metal content analysis. The analysis of the metal concentration in the collected solutions was performed by flame atomic absorption spectrometry (FAAS), after appropriate dilutions of the supernatants (using diluted HNO₃ solution). In each experiment, parameters such as contact time, pH, and analyte concentration were individually adjusted. Kinetic tests were carried out to ascertain the minimum duration necessary for the material to attain equilibrium in adsorption kinetics. These experiments entailed the mechanical agitation of the material with the analyte solution, spanning a time range of 1 to 240 minutes, conducted at room temperature. The concentrations of Cu(II) and Cd(II) in the solutions were set at 50 mg L^-1 and 25 mg L^-1, respectively, while maintaining a pH of around 5.5. The specific influence of solution pH on the adsorption of copper and cadmium was evaluated. Adsorption experiments were conducted under different pH values to determine the optimal pH at which the material exhibits the highest adsorption capacity. These experiments involved mechanical agitation of Cu(II) and Cd(II) solutions with concentrations of 50 mg L^-1 and 20 mg L^-1, respectively. The pH values of the Cu(II) and Cd(II) solutions were adjusted within a range from 1 to 6, and the material was allowed to interact with the solutions for 120 minutes.

To determine the influence of the analyte concentration on the maximum adsorption capacity of the material, it was mechanically agitated with Cu(II) and Cd(II) solutions of different concentrations (1 to 400 mg L^-1). For these experiments, the pH of the Cu(II) and Cd(II) solutions was adjusted to around 5.5, and the stirring time of the material with these solutions was 120 minutes. All batch experiments were performed at a room temperature of approximately 25 °C. After determining the residual concentration of the metals in the diluted supernatants, the adsorption capacity for all experiments was calculated using equation (1):

$$N_f=\frac{n_i-n_s}{m}$$

(1)

where n_i is the initial number of millimoles of the metal ion in the solution, n_s is the number of millimoles of the metal ion in the supernatant after extraction, and m is the mass of the adsorbent used (in grams).

3. Results and Discussion

3.1. Characterization of the material

The morphology of the particles, their surface properties, and the chemical composition of the adsorbent were investigated using techniques such as scanning electron microscopy (SEM), energy-dispersive X-ray spectroscopy (EDX), elemental analysis of C, H, and N, ¹³C nuclear magnetic resonance (¹³C-NMR), infrared spectroscopy (FTIR), and point of zero charge (pH_PZC). In Figure 1 and 2, we can observe the spectra collected by FTIR and ¹³C-NMR techniques. In Figure 1, the infrared spectrum presents important bands related to the organic groups of the material, where it is possible to identify potential functional groups involved in the coordination of metal ions. The bands observed at 3405 and 2915 cm^-1 are attributed to the stretching vibration of the O-H and C-H bonds, respectively. Anticipated bands are likely to appear, as these clusters constitute the primary elements within cellulose, a significant component found in leaves.

The strong and broad O-H band is the result of this polymeric constituent. The C-H stretching band is derived from the primary and secondary carbons (CH₃ and CH₂). The prominent band at 1630 cm^-1 can be attributed to the twisting vibration of the primary N-H bonds present in amino acid structures. The infrared absorption bands observed at 1370 and 1320 cm^-1 are correlated with the stretching of the C-N bonds of aromatic amines found in the material. The absorption band located at 1030 cm^-1 can be attributed to the symmetric stretching vibrations of the C-O bonds in alcoholic groups. In the infrared spectrum, we cannot confirm the presence of carboxyl groups since the C=O stretching band generally observed in the wavelength range between 1760 and 1690 cm^-1 is not present.

Figure 2 shows the ¹³C-NMR spectrum of the pulverized material. The highest resonance, observed at 74.2 ppm, corresponds to the C-OH groups of flavonoid glycosides, which are the main non-structural constituents of persimmon leaves. This large resonance signal can also be assigned to the carbons of the C-O bonds present in the flavonoid and coumarin rings. The signal observed at 171.7 ppm can be attributed to COOH groups of fatty acids and terpenoids present in considerable amounts in the leaves (XIE et al., 2015). A high resonance peak, observed at 168.0 ppm, may be associated with the carbons of the guanidine and carbamoyl groups present in the amino acids arginine and citrulline, respectively (RYU et al., 2016). The observed resonances between 154.2 and 144.2 ppm may be related to the N=C-S groups found in thiamine (SILVA et al., 2015).

The signal seen at 129.2 ppm is attributed to the presence of unsaturated aliphatic compounds (alkenes). This signal is also correlated with the unsaturated carbons (C=C) present in aromatic compounds (RIBEIRO and SOUZA, 2007). There is little evidence of the presence of nitrile (C≡N) bonds due to the low characteristic signal observed around 120 ppm. The resonance signal observed at 103.2 ppm corresponds to the anomeric carbons (O-C-O) of aldoses and ketoses (RIBEIRO; SOUZA, 2007). The signal shown at 38.5 ppm is consistent with the S-CH₂ groups present in the amino acids methionine and cysteine (JORGETTO et al., 2014). A strong resonance can be observed at 30.3 ppm, attributed to the carbons (R₂CH₂) of saturated aliphatic compounds (alkanes), as well as the signal seen at 24.0 ppm. This large peak is expected in materials of vegetable origin, which have a wide amount of structural polysaccharides such as lignin and cellulose. We cannot verify the resonance of the carbons involved in the peptide bonds (C-N) since the characteristic signal around 60 ppm is not present.

The ground material was also analyzed by SEM to determine its particle size homogeneity and the morphology of the particles. According to Figure 3, the particle size is not homogeneous, and some have very irregular shapes. Furthermore, these particles exhibit a notably coarse microscopic texture characterized by irregular channels. This feature contributes to an increased surface area for the material and offers numerous adsorption sites for metal species.

The EDX analysis was performed to map the distribution of the elements of interest onto the surface of the particles, and the collected elemental maps enabled the construction of Figure 4. As can be seen, the EDX maps indicate that N, O, S, and P are homogeneously distributed on the surface of the particles, and these elements are the main constituents of the groups of interest for the complexation of metal cations.

Elemental analysis showed that the leaves contain 44.87 % C, 4.87 % H, and 2.59 % N (by weight). The presence of O and S atoms in the material was also evidenced by the results of ¹³C-NMR, which suggested the presence of molecules containing sulfur and oxygen.

An experiment was conducted to determine the point of zero charge (PZC) and the corresponding pH value at which the material has a net charge of zero (neutrality) on its surface (pH_PZC), as a function of the pH of the medium. Below the pH_PZC, the material’s surface becomes protonated, resulting in a positive charge (protonation of hydroxyl, carboxylic, and amine groups). On the contrary, when the medium’s pH surpasses the material’s pHPZC, certain organic groups on the material’s surface release their hydrogen ions, resulting in a negative charge. As a result, in the presence of metal cations at acidic pH levels, electrostatic repulsion occurs between the cations and the positively charged surface of the adsorbent, leading to a diminished adsorption of these metal species. Conversely, at elevated pH values, the adsorption of cations may be promoted due to the material’s negatively charged surface. Nonetheless, contingent upon the concentration of hydroxide ions in the medium, they can engage in solvation with metal cations, impeding their complexation by the organic groups present on the material’s surface. Then, we can conclude that the optimal pH for the adsorption of the metal cations is the pH at which the overall surface charge of the adsorbent is neutral, which is referred to as the point of zero charge (PZC). The data obtained from the PZC experiment were used to construct Figure 5, and the pH_PZC is determined by the point where the experimental curve (initial pH versus final pH) intersects the line represented by x = y (initial pH = final pH). From the graph, we can observe that the pH_PZC for the persimmon leaves powder is 5.1. As discussed earlier, when the pH of the medium is below 5.1, the particles’ surface will be positively charged, whereas at higher pH values, the surface of the adsorbent will exhibit a negative charge. Since the pH_PZC is slightly acidic, it indicates a prevalence of acidic groups on the material’s surface (JORGETTO et al., 2015).

3.2. Batch adsorption experiments

3.2.1. Adsorption kinetics

Through kinetic experiments, we were able to establish the minimum duration of dynamic contact necessary for the material to achieve equilibrium with the metal solution. As shown in Figure 6 (inset), the material exhibits rapid kinetics, and the adsorption equilibrium is reached within 5 minutes for both metals. This indicates that the structure of the leaves provides high accessibility for the metal cations to coordinate with its adsorption sites. It is important to note that rapid kinetics for an adsorbent is highly desirable, making the material very attractive for analytical and decontamination purposes.

According to the literature, it is incorrect to use simple kinetic equations such as first and second-order models to describe the adsorption process on heterogeneous surfaces (HO and MCKAY, 1999). Therefore, the experimental kinetic data obtained for Cu(II) and Cd(II) were applied to the linear kinetic model of pseudo-second order. This model suggests that the metal extraction process occurs through the covalent coordination of non-bonding electron pairs of the atoms present on the surface of the adsorbent. The linearized form of the pseudo-second order kinetic model is represented by equation (2):

$$\frac{t}{N_{ft}}=\frac{1}{{KN}_e^2}+\frac{1}{N_e}t$$

(2)

where N_ft represents the adsorption capacity as a function of time (mmol g^-1); N_e corresponds to the adsorption capacity at equilibrium (mmol g^-1); K is the kinetic constant of the pseudo-second order (g mmol^-1 min^-1), and t is the contact time in each experiment (minutes). By plotting t/N_ft vs. t, the linearized kinetic isotherms were generated for the studied metal species, as depicted in Figure 6. We can observe a great agreement between the experimental data and the pseudo-second-order kinetic model, as evidenced by the high coefficients of linear correlation obtained (r² = 0.9999 for Cu(II) and r² = 0.9996 for Cd(II)). Considering an equation of the form y = Bx + A, the linear equations obtained for Cu(II) and Cd(II) were y = 10.539x - 11.566 and y = 31.062x + 22.330, respectively, where y = t/N_ft and x = t. According to Eq. (2), B = 1/N_e and A = 1/(K N_e²); by substituting the respective angular and linear coefficients for both metals, it was possible to calculate N_e and K for each species, resulting in N_e = 0.0948 mmol g^-1 and K = -9.6031 g mmol^-1 min^-1 for Cu(II), and N_e = 0.0321 mmol g^-1 and K = 43.208 g mmol^-1 min^-1 for Cd(II). Another piece of evidence that confirms the good agreement with this model is the similarity between the experimental adsorption capacity values (observed when the kinetic isotherms reach the highest adsorption capacity) and the calculated values (obtained from the mathematical model).

3.2.2. Effect of the pH of the medium

The influence of pH on the adsorption process of Cu(II) and Cd(II) ions was investigated in solutions with pH values ranging from 1 to 6, as the concentration of H⁺ species can affect the reaction equilibrium due to the protonation of the adsorption sites. Solutions with pH values higher than 6 were not tested due to the risk of hydrolysis reactions involving metal cations, which could compromise the adsorption process. The data obtained were plotted in

Figure 7. Effect of the pH on adsorption of Cu(II) and Cd(II) in aqueous medium, at room temperature (25 °C). Initial concentrations of Cu(II) and Cd(II) solutions: 50 and 20 mg L^-1, respectively; stirring time: 120 minutes; mass of adsorbent used: 10.0 mg.

Figure 7. Effect of the pH on adsorption of Cu(II) and Cd(II) in aqueous medium, at room temperature (25 °C). Initial concentrations of Cu(II) and Cd(II) solutions: 50 and 20 mg L^-1, respectively; stirring time: 120 minutes; mass of adsorbent used: 10.0 mg.

Both metal species exhibit their lowest adsorption capacities at pH values of 2 or lower. However, as the pH of the medium increases, the adsorption becomes more effective. The highest metal adsorption can be observed at pH values of 4.0 for Cu(II) and 3.0 for Cd(II). Such behavior is commonly observed in metal adsorption processes. At low pH values, the concentration of hydronium ions (H₃O⁺) is sufficiently high for the H⁺ species to compete with the metal ions for the adsorption sites. This effect is intensified at the lowest pH values. The size of the H⁺ ions also plays a significant role in this competition, as their smaller size provides greater mobility in the medium. This property gives the H⁺ ions an advantage in reaching the adsorption sites compared to larger metal ions such as Cu²⁺ and Cd²⁺ (JORGETTO et al., 2015). Consequently, the surface of the material becomes positively charged, leading to the repulsion of the metal ions present in the medium. As a result, metal adsorption is significantly compromised in low-pH media. As the pH increases and approaches neutrality, this effect becomes less intense, as the concentration of hydronium ions decreases, allowing for the adsorption of the metal ions. As the material is capable of adsorbing metal ions over a wide pH range, it would be suitable for application in solid-phase extraction of Cu(II) and Cd(II) from effluents, as well as for the decontamination of drinking water.

3.2.3. Maximum adsorption capacity

Under optimal conditions of pH and contact time, an experiment was conducted to determine the maximum adsorption capacity of the material as a function of Cu(II) and Cd(II) concentrations. The adsorption isotherms were plotted using the analyte concentrations and their respective N_f values (Figure 8).

As observed, the graphical representation of the data shows maximum adsorption capacity (N_fmax) values of approximately 0.19 mmol L^-1 for Cu(II) and 0.21 mmol L^-1 for Cd(II). To further understand the adsorption process occurring on the material, the experimental data of the isotherms were also fitted to the linearized Langmuir and Freundlich models. The Langmuir model quantitatively describes the formation of an adsorbate monolayer on the surface of an adsorbent, representing the equilibrium of adsorbate distribution between the solid and liquid phases. The Langmuir isotherm is widely used in biosorption assays for pollutants from aqueous solutions (RANGABHASHIYAM et al., 2014). The linear form of the Langmuir isotherm is given by equation (3) (LANGMUIR, 1916; LANGMUIR, 1932).

$$\frac{C_s}{N_f}=\frac{C_s}{N_s}+\frac{1}{N_{s}b}$$

(3)

In this expression, C_s represents the equilibrium concentration of the supernatant (mmol L^-1); N_f is the amount of adsorbed metal ions on the material’s surface (mmol g^-1); N_s is the maximum amount of metal ions adsorbed per gram of adsorbent (mmol g^-1), which is related to the number of available adsorption sites; and b (L mmol^-1) is a constant that reflects the affinity of the metal ions with the solid matrix and the adsorption energy. On the other hand, the Freundlich model is applicable to adsorption on heterogeneous surfaces and considers that adsorption occurs in multilayers with interactions between the adsorbed molecules (RANGABHASHIYAM et al., 2014). The linearized form of the Freundlich isotherm is given by equation (4) (FREUNDLICH, 1906):

$$\log q_e=\log k_f+\frac{1}{n}\log C_e$$

(4)

Where C_e represents the equilibrium concentration of the metal species (mmol L^-1); q_e is the amount of metal ions adsorbed per gram of adsorbent at equilibrium (mmol g^-1); k_f (mmol^1-(1/n) L^1/n g^-1) is the Freundlich constant that relates to the adsorption capacity, and n is a dimensionless constant that describes the intensity of the adsorption process. The values of b and N_s can be determined from the slopes and intercepts of the linear plots of C_s/N_f versus C_s (Langmuir isotherm), while the values of k_f and n are calculated from the intercepts and slopes of the plot of logq_e versus logC_e. The values of the constants (b, k_f, and n), along with the correlation coefficients (r²) generated by the linearization of the experimental data, are listed in Table 1.

Based on the obtained linear correlation values (r²), the Langmuir linearized model has proven to be the most suitable for fitting the experimental data of both metal species. This model exhibited excellent agreement with the adsorption data, as indicated by the high coefficients of linear correlation. With the help of the best-fit straight-line equations, it was possible to calculate the maximum adsorption capacity of the material (N_s) for Cu(II) and Cd(II) based on their angular coefficients (B = 1/N_s). Considering the similarity between these N_s values and the N_fmax values determined in the adsorption isotherms, we can infer that a significant portion of the available adsorption sites on the material’s surface is involved in the coordination of the metal species. The maximum adsorption capacity of the persimmon leaves is very similar for Cu(II) and Cd(II). The high efficiency in metal removal can be explained by the significant presence of sulfur and nitrogen in the material in question. These elements play important roles as soft and intermediate Lewis bases, respectively, which means they have the ability to donate electron pairs to interact with metal ions in solution. This phenomenon has been consistently observed in previous studies, as mentioned by PEARSON (1963). The presence of these bases suggests that the material has great potential for use in the solid-phase extraction of a wide variety of metal species, making it a promising choice for applications in the purification and recovery of metals from aqueous solutions. Concentrations above 400 mg L^-1 were not evaluated due to the difficulty in preparing more concentrated solutions of copper and cadmium at pH levels above 6. Increased concentrations of these metal species result in hydrolysis reactions and the formation of precipitates.

To compare the performance of persimmon leaf powder with that of other adsorbents in terms of Cu(II) and Cd(II) adsorption, Table 2 was constructed. Despite having a similar adsorption capacity, persimmon leaves require a simple treatment prior to their application in solid-phase extraction. This results in low-cost procedures and aligns with the principles of green chemistry, as the production of this adsorbent does not generate any toxic waste. Furthermore, it is derived from a renewable source and can be utilized for environmental purposes.

The table showcases several materials that share similarities with persimmon leaves, the subject of the referenced study, with its data appearing in the final row. Persimmon leaves are noteworthy due to their abundant and easily obtainable nature. Unlike less available or more challenging-to-acquire materials, such as specific synthetic chemicals or other materials of rare origin, persimmon leaves are readily accessible in many regions. Moreover, the ease of procuring persimmon leaves renders them an attractive choice for applications involving the adsorption of metals in aqueous solutions. This is especially significant when considering the necessity for scalability in practical scenarios. The abundant supply of persimmon leaves can render this solution both economically and environmentally friendly, allowing for its extensive implementation in the removal of metals from liquid effluents or contaminated solutions. Therefore, the selection of persimmon leaves as an adsorbent in this study not only yields noteworthy outcomes in the context of copper and cadmium adsorption but also underscores a crucial facet of environmental research and metal removal technology. This facet revolves around harnessing naturally abundant and readily accessible resources to tackle intricate environmental challenges. This approach can be regarded as sustainable and economically viable, thereby contributing to the advancement of research and the development of more effective and accessible water and effluent treatment technologies.

4. Conclusions

Persimmon leaves represent a low-cost alternative adsorbent for removing toxic metals from aqueous media. This material is abundant and can be easily processed into a fine powder through simple procedures. Grinding and pulverizing the leaves result in a porous material that doesn’t require prior functionalization steps for the uptake of metal ions. It can be directly applied to remediate metal species in aqueous solutions. Characterization of the powdered leaves revealed the presence of functional groups that act as Lewis bases, playing a crucial role in the chemisorption of Cu(II) and Cd(II) ions. The material exhibited rapid kinetics and proved to be effective over a wide pH range (3-6). Its adsorption behavior was best described by the Langmuir adsorption model, and its maximum adsorption capacity was comparable to that of many other biosorbents.

Future prospects for persimmon leaves in the field of metal removal from aqueous media include further exploration of their potential in real-world applications. It is important to conduct long-term studies to assess their durability and performance under varying environmental conditions. Additionally, research could focus on optimizing the processing methods to further enhance their adsorption capacity and efficiency. Investigating the regenerability of persimmon leaf-based adsorbents and exploring their use in large-scale water treatment processes would be valuable areas of future research. Furthermore, the combination of persimmon leaves with other materials or modification techniques may offer opportunities to improve their selectivity for specific metal ions. Overall, persimmon leaves hold promise as a cost-effective and environmentally friendly solution for the removal of toxic metals from aqueous environments, and their continued exploration in various applications is justified.