Modified Activated Carbon for Copper Ion Removal from Aqueous Solution

Abstract

Because of increasing environmental awareness, it is becoming more important to remove harmful elements from water solutions. This study used activated carbon (AC) derived from waste wood-based panels as the base material, oxidized with nitric acid (OAC), and grafted with iminodiacetic acid (IDA-OAC) to improve the adsorption capacity and affinity for metals. The characterization of AC, OAC, and IDA-OAC was conducted via FTIR, SEM, N₂ adsorption and desorption analysis, elemental analysis, Boehm titration, and point of zero charge (PZC). The instrument studies proved the modified increasing of the functional groups of the adsorbents. Moreover, batch and column experiments were conducted to evaluate the ability of the three adsorbents to remove copper ions from aqueous solution. In batch sorption, IDA-OAC had the highest adsorption capacity (84.51 mg/g) compared to OAC (54.74 mg/g) and AC (24.86 mg/g) at pH 5. The breakthrough point (C_t/C_i = 0.05) of copper ions for IDA-OAC occurred much later than AC in the column experiment (AC = 19 BV, IDA-OAC = 52 BV). The Langmuir isotherm and pseudo-second-model kinetics modeling could better fit with the data obtained from the batch sorption of AC, OAC, and IDA-OAC. The significant capacity and reusability of IDA-OAC displayed high applicability for water treatment.

1. Introduction

US EPA has reported that metal water pollution is a severe worldwide problem due to the rapid development of industry and technology [1]. Some specific metal compounds are toxic, nonbiodegradable, persistent, bioaccumulated, and cause cancer, so treating metal pollutants in aqueous solutions is a significant issue [2,3]. Among many metals, copper is commonly found in industrial wastewater [4]. It has been widely used in semiconductors, electronic product manufacturing, and electroplating. Copper poisoning can cause nausea, diarrhea, liver, and kidney failure due to long-term exposure to copper through contaminated food and water sources [5]. For these reasons, many techniques have been developed to effectively remove metals from wastewater to meet the discharge standard of water pollutants, such as ion exchange [6], electrochemical treatment [7], chemical precipitation [8], reverse osmosis [9], and adsorption [5,10,11].

In these methods, adsorption by activated carbon (AC) is considered as a prospective approach to eliminate copper from wastewater, because of its easy implementation, high efficiency, low initial cost, and reusability [5,12]. It has widely been used in the removal of various contaminants from wastewater due to its high porosity parameter, great surface area, surface functional groups, and insensitivity to toxic environments [13,14,15]. On account of its many advantages, there have been many biowastes used for the fabrication of activated carbon materials, such as sawdust [16], paulownia wood [17], rice straw [18], and waste wood-based panels [19]. These biowastes also contain lignin and celluloses as commercial activated carbon precursors that can be a considered choice and low-cost sources to produce activated carbon [3].

In addition, with effluent standards becoming stricter in order to control pollution impacts, the modification of carbon materials has attracted extensive attention in recent years. The adsorption capacity of carbon materials is significantly relative to their pore structure and surface chemistry [13]. The surface modifications of a material can enhance the adsorption capacity and removal efficiency by increasing the active functional groups with a high affinity for metals on an adsorbent surface [20]. For example, HNO₃ oxidized biochar showed remarkably higher adsorption performance than the unmodified carbon via introducing functional groups [10]. Zuo et al. functionalized biochar with hydrogen peroxide, which caused several oxygen-containing groups on the material surface, enhancing the affinity for copper [14]. Among the many surface modifiers, fixing iminodiacetic acid (IDA) chelating functional group into materials and its use as an adsorbent can be helpful for wastewater restoration [15]. Katarzyna et al. modified graphene oxide with IDA for effectivity preconcentration and removal of Cu(II) from water samples (108.4 mg/g) [21]. Razak et al. grafted kenaf fiber with IDA and increased the adsorption capacity by about 200% for Cu(II) removal [22]. Both oxygen and nitrogen on IDA can provide electron pairs to form coordination with transition metals. This endows the adsorbent with the ability to effectively attract copper to remove metals from the water [23].

Therefore, activated carbon derived from waste wood-based panels has been oxidized with HNO₃ to enhance the number of oxygen-containing functional groups on the carbon material in this study. Afterwards, we grafted IDA to enhance the adsorption ability, affinity, and removal efficiency. A batch experiment was conducted to examine the influence of the solution pH, reaction time, initial concentration, and temperature on adsorption. The data from the batch sorption were verified with equilibrium and kinetic adsorption models to identify the adsorption mechanisms from the adsorption procedure. The revitalization experiment was carried out to make the adsorbent more economical. Lastly, the column system was also used to study AC, OAC, and IDA-OAC.

2. Materials and Methods

2.1. Chemicals and Materials

The H₃PO₄ (≥85.0%), nitric acid (≥65.0%), hydrochloric acid (≥37%), iminodiacetic acid (IDA) (≥98%), epichlorohydrin (EPI) (>99%), NaHCO₃ (≥99.7%), Na₂CO₃ (≥99.8%), NaOH (≥98%), NaCl (99.9%), NaNO₃ (>99%), and Cu(NO₃)₂·3H₂O (99%) were purchased from Uni-Onward Corp. Chemicals used in this research were all of analytical quality. N₂ (99.5%) was purchased from Yun Shan Gas Co. Waste wood-based panels (WWP) were collected from the local recycling center. They were cut into small pieces (1~4 mm) and then washed several times with DI water. They were then dried in the oven at 333 K for 24 h and stored in a scintillation vial for subsequent usage.

2.2. Preparation of Adsorbents

2.2.1. Fabrication of Activated Carbon from WWP

Activated carbon was fabricated via chemical activation. Specifically, WWP was impregnated with H₃PO₄ (85.0% w/w) at 298 K and placed in an oven at 383 K for 24 h. The impregnation ratio was 3:1 (H₃PO₄/WWP mass ratio). After that, a weighed amount of the dried mixture was put in the porcelain boat placed into a furnace, and heated up to 823 K for 2 h under continuous N₂ flow (150 mL/min STP) at a constant heating rate (10 K/min). The activated carbon was cooled to room temperature and washed with distilled water until constant pH. This resulting sample was dried at 333 K for 24 h and sieved to a uniform size fraction of 0.595 mm–0.149 mm.

2.2.2. Activated Carbon Oxidation

To increase the bond with the metal and the subsequent grafting site, we oxidized the activated carbon to increase oxygen-containing groups (such as hydroxyl, carboxyl) on the surface with HNO₃. For this, the 1 g of dried AC was impregnated in 10 mL of 7 N nitric acid solution for three hours at 353 K. After treatment, the residual material was filtered with filter paper and washed with distilled water until constant pH, and dried at 333 K for constant weight.

2.2.3. Synthesis of IDA-OAC

For fixing iminodiacetic acid on OAC, epichlorohydrin was reacted with primary hydroxyl on the OAC through electrophilic substitution. Afterward, nucleophilic substitution occurred between the amino groups on IDA and the epoxy rings on the OAC. Specifically, 1.0 g of oxidized activated carbon (OAC) was dispersed in aliquots of ethanol (20 mL), 1 M of NaOH (10 mL), and epichlorohydrin (10 mL). The mixture was agitated for 3 h at 313 K. After that, it was cooled to room temperature and collected by filtration, and washed with DI water dried at 333 K for 24 h, and abbreviated as EPI-OAC. Next, EPI-OAC (1.0 g), IDA (4.0 g), 100 mL of distilled water were mixed and stirred at 333 K for 10 h. The system was controlled to maintain the pH of the mixture higher than 10 during the reaction by adding NaOH solution. Finally, it was dried at 333 K for 24 h after the mixture solution was collected, and washed with diluted acetic acid and water, and abbreviated as IDA-OAC.

2.3. Characterization

The concentrations of Cu(II) ions were measured by ICP-OES (Varian, Palo Alto, CA, USA, Vista-MPX). The characteristics of the AC, OAC and IDA-OAC adsorbents were determined as follows: FTIR spectra for assessing the functional group’s presence were recorded within a range from 4000 to 500 cm⁻¹ using potassium bromide pallet in a Perkin Elmer, Spectrum one spectrometer. The changes of element content of C, N, H, and S were analyzed by an elemental analyzer (Unicube, Elementar Analysensysteme GmbH, Hanau, Germany). The surface morphology was determined with the Scanning Electron Microscopy (SEM) (EFE-SEM; SU-5000, HITACHI, Chiyoda ku, Japan). The BET surface area (Brunauer–Emmett–Teller) and pore structure were analyzed by adsorption and desorption with nitrogen at 77 K (Micromeritics ASAP 2020 specific surface analyzer). Before the gas adsorption measurement, the samples were degassed at 105 °C for 8 h. The Boehm titration method was performed to determine the acidic surface functional groups on the materials [24]. The pH drift method was used to determine the adsorbent’s pH point of zero charges (pH_PZC) [25].

2.4. Batch Sorption of Copper

In the batch adsorption process, Cu(NO₃)₂·3H₂O were used to prepare Cu(II) ions. A series of sorption was studied by adding 0.02 g of AC, OAC, IDA-OAC into 20 mL of a specific concentration of Cu(II) solution and agitated at a rate of 110 rpm in a shaker incubator. The temperature and the time factors were adjusted in the experiment. The influence of pH on adsorption experiments was processed at 298 K, and the HNO₃ or NaOH (0.01–1.0 M) solutions were used to adjust the pH value from 2 to 6. The effect of cations on the removal of Cu(II) was determined by adding 1000 to 5000 mg/L NaNO₃ with a Cu(II) concentration of 300 mg/L, and the mixture was shaken for 24 h at 298 K. For the determination of the impact of the different initial concentrations (5, 10, 30, 50, 80, 100, 150, and 200 mg/L), the solution was agitated for 24 h at a suitable pH value (pH = 5). The factor of contact time (4, 8, 16, 32, 60, 120, 180, 240, and 300 min) was determined at 298 K at optimum pH with a Cu(II) concentration of 200 mg/L. Further, the influence of temperature (298, 308 and 318 K) was analyzed. After each adsorption process, the filtrate was collected and analyzed by ICP-OES to measure the Cu(II) concentration. The adsorption capacity (q_e, mg/g) of the copper and removal efficiency (R%) were calculated using the following equation [11]:

$$q_e=\frac{\left(C_0-C_e\right)V}{W}$$

(1)

$$\mathrm{R}(\%)=\frac{\left(C_0-C_e\right)}{c_0}$$

(2)

where C₀ is the initial concentration and C_e is the equilibrium concentration of the copper solution (mg/L), and V(L) and W(g) are the volume of the Cu(II) solution and the weight of the adsorbent usage, respectively.

2.5. Equilibrium Isotherms, Adsorption Kinetics, and Thermodynamic Studies

To better understand the adsorption reactions with the primary mechanism and to investigate how copper ions interacted with adsorbents, the adsorption results with different initial concentrations were fitted with Langmuir isotherm (Equation (3)) and Freundlich isotherm (Equation (4)) models [15,26].

$$\frac{C_e}{q_e}=\frac{C_{\mathrm{e}}}{q_{max}}+\frac{1}{K_L{q}_{max}}$$

(3)

$$\ln \left(qe\right)=\ln K_F+\frac{1}{n}\ln C_e$$

(4)

where q_max (mg/g) signifies the maximum adsorption capacity. q_e (mg/g) is the concentration of Cu(II) solution under equilibrium. K_L is a Langmuir constant related to the adsorption energy (L/mg). C_e (mg/L) is the concentration of Cu(II) solution in equilibrium. K_F (mg/g) represents the Freundlich constants relative adsorption capacity of the adsorbent, and 1/n is the Freundlich coefficient about heterogeneity.

Adsorption kinetics of Cu(II) on adsorbent used experimental data about the effect of contact time to fit separately by pseudo-first (Equation (5))- and second (Equation (6))-order kinetic models [27].

$$\ln \left(q_e-q_t\right)=\ln q_e-k_{f}t$$

(5)

$$\frac{t}{q_t}=\frac{t}{q_e}+\frac{1}{k_s{q}_e^2}$$

(6)

where q_t (mg/g) is the quantities of Cu(II) adsorbed at the time, and q_e (mg/g) is the adsorbed amounts of Cu(II) under equilibrium, while k_f (1/min) and k_s (g/ (mg·min)) are the corresponding rate constants of pseudo-first- and second-order kinetic models, respectively.

The data from the effect of temperature on the adsorption process were used for determining three thermodynamic parameters: change in free energy (ΔG°), change in the enthalpy (ΔH°) and entropy variation (ΔS°). These parameters were calculated from the van’t Hoff equation [28]:

$$\Delta {\mathrm{G}}^{°}=-RT\ln K_d$$

(7)

$$\ln K_d=\frac{\Delta {\mathrm{S}}^{°}}{R}-\frac{\Delta {\mathrm{H}}^0}{RT}$$

(8)

$$K_d=\frac{C_0-C_e}{C_0}\times \frac{V}{M}$$

(9)

where R (8.314 J/(mol K)) is the universal gas constant, K_d (L/mol) is the adsorption coefficient, T is the absolute temperature in Kelvin. Using the slope and intercept of the plot of ln K_d versus 1/T, one can obtain the value of the ΔS° and ΔH°.

2.6. Reusability of IDA-OAC

To make the IDA-OAC adsorbent more economical and practical, regeneration and reusability experiments were carried out. In the regeneration experiment, the adsorbent which loaded copper ion was eluted (solid/liquid ratio of 1 g/L at 298 K for 24 h) with 0.1 M HCl, 0.1 M HNO₃, and 0.1 M H₂SO₄, respectively. After regeneration, the adsorbent was collected, washed, and dried for the subsequent three adsorption/desorption experiments.

2.7. Column Sorption of Copper

The column-scale experiments were evaluated in continuous adsorption. About 0.2 g of the AC, OAC and IDA-OAC was wet-packed in a plexiglass column which was 4 mL in volume and 11.2 mm in diameter. The effect of initial Cu(II) concentration (50 mg/L) was analyzed. Before feeding the influents into the column, a peristaltic pump was pumped downward through the column with distilled water for about 3 h. The flow rate for fixed-bed experiments was 1 mL/min at pH 5 (optimum value from batch-scale studies) and 12 BV/h. The samples were collected from the exit with a fraction collector until a saturation state occurred. The following equations were used for data analysis of fixed-bed adsorption [29].

$$q_{tot}=\frac{Q_V\mathrm{A}}{1000}=\frac{Q_V}{1000}{{\displaystyle \int }}_{t=0}^{t=t_{tot}}\left(C_i-C_t\right)dt$$

(10)

$$m_{tot}=\frac{C_i{Q}_V{t}_{tot}}{1000}$$

(11)

$$\mathrm{R}\%=\frac{q_{tot}}{m_{tot}}\times 100$$

(12)

where q_tot is the total mass of the adsorbent in the column, Q_v has been determined as the flow rate (mL/min), C_i (mg/L) and C_t (mg/L) are the inlet and outlet of Cu(II) concentration, the m_tot (mg) and R% present the total quantity of adsorbate flow through the column and the removal rate, respectively. The area under the breakthrough curve is marked as A and the plots of C_t/C_i against bed volume are called the breakthrough curves. C_t/C_i = 0.05 and 0.95 are signed as the breakthrough points (p_b) and exhaustion points (p_e), respectively.

3. Results and Discussion

3.1. Characterization of Adsorbents

The FT-IR spectra of possible functional groups on adsorbents are presented in Figure 1. For AC, because these carbons were activated by phosphoric acid, the peaks at 1156 cm⁻¹ and 1060 cm⁻¹ could be assigned to bending vibrations in C-OH bonds and vibration of the polyphosphate chain, respectively [30]. The peak around 1617 cm⁻¹ could be attributed to C=C stretching vibration from the aromatic ring and conjugated C=O bond [31]. Furthermore, the board band between 3250 to 3700 cm⁻¹ represent the overlapped stretching and vibration from amine groups(-NH) and hydroxyl groups(-OH) [32]. This observation was found in OAC and IDA-OAC also. After the nitric acid treatment, the peak was observed at 1700 cm⁻¹ due to the C=O stretches of carboxyl or carbonyl groups [33], and the C-O stretching at 1216 cm⁻¹ [34] proved that oxidation generates more oxygenated functional groups on the activated carbon. With the iminodiacetic acid grafted, the absorption bands at 1224 cm⁻¹ and 1060 cm⁻¹ related to C-O epoxyl and alkoxyl groups on EPI-OAC disappeared [21]. Then, the characterization of peaks related to bending vibration of N-H or stretching vibration of -C=O was shown at 1615 cm⁻¹ [30,32]. The peaks at 1384 cm⁻¹ and 1140 cm⁻¹ corresponded to C-N stretching [35], indicating the IDA was successfully grafted on OAC [36].

Elemental analysis was used to observe the change in contents of the AC, OAC, and IDA-OAC. From

Table 1. Element analysis of AC, OAC, and IDA-OAC.

Sample	AC	OAC	IDA-OAC
C (wt%)	63.911	55.104	52.803
N (wt%)	1.490	2.080	2.410
H (wt%)	2.251	2.986	2.397
S (wt%)	N.D.	N.D.	N.D.

N.D. < 0.01%.

, after the nitric acid treatment and iminodiacetic acid was grafted, the nitrogen content of OAC and IDA-OAC increased from 1.490% to 2.080%, and 1.490% to 2.410% compared to AC, respectively. The nitrogen on the AC was from the adhesives of the waste wood-based panels [19]. Moreover, the content of carbon decreased when the N% increase. This change indicates that nitric acid and iminodiacetic acid successfully introduce the functional groups on the surface of activated carbon [37].

The surface morphology information was obtained through the SEM technique. The SEM images (Figure 2) of AC, OAC, and IDA-OAC reveal the difference between the materials before modifying and after. As illustrated in Figure 2a, the activated carbon fabrication from waste wood-based panels had some open pores on the surface. In Figure 2b, homogenous porosity was observed when the magnification was enlarged [24]. After treating with the nitric acid, Figure 2c–f displayed the open pores obviously and exhibited a heterogeneous surface with porosity. This could be attributed to nitric acid destroying the pore wall and causing the pore structure to collapse [38]. In addition, although Figure 2c,e was not much different, Figure 2d,f demonstrated that in OAC after grafting with iminodiacetic acid, the surface of the adsorbent became coarser and fluffier. This phenomenon confirms that the functional ligand bonding with the OAC surface provides more active sites to the adsorbate [39].

To understand more surface physicochemical characteristics, the surface area, pore capacity, pore width, and contents of surface functional groups of adsorbents are shown in

Table 2. Physicochemical parameters of AC, OAC, and IDA-OAC.

Sample	AC	OAC	IDA-OAC
Surface area (m2/g)	1464.0757	996.0884	611.2244
Pore volume (cm3/g)	1.1731	0.5488	0.3082
Pore width (nm)	3.2051	2.2039	2.0167
Total acidity groups (mmol/g)	2.25	3.72	3.93
Carboxyl (mmol/g)	1.05	2.03	2.22
Lactone (mmol/g)	0.74	1.02	0.86
Phenolic (mmol/g)	0.46	0.67	0.85
pHpzc	3.21	2.68	4.94

. Initially, the AC exhibited much higher pore properties. After nitric acid oxidation and grafting, the surface area, pore volume, and pore width were lower in the AC. This situation was due to the introduction of the functional groups inside the pores of activated carbon, and the lower stability of the aliphatic being oxidized, causing the destruction of the porous structure [28,40]. Although there was a decrease in the pore width, the average size was still contained in the mesopore (2–50 nm). The adsorbate having a larger radius could be due to the pores also [41]. The number of surface acidic functional groups was determined through the Boehm titration. The results displayed an increment of total acidic groups after modifying AC and iminodiacetic acid grafting on OAC (increase from 2.25 to 3.72 mmol/g and 3.72 to 3.93 mmol/g, respectively). This proved that the nitric acid and iminodiacetic acid effectively introduced the functional group on AC through oxidization and grafting [42].

3.2. Effect of pH Value

Because the different solution pH strongly affects the form of the surface charge on the adsorbent and the state of the copper for adsorption capacity, the pH value is a significant factor for the adsorption process [15]. As seen in Figure 3, the phenomenon can be observed that more copper adsorption on the three kinds of adsorbent follows the increasing pH value (2 to 6). Junior et al. used chelating resin with the iminodiacetic acid group to recover Cu²⁺, and found that the adsorption of the metal increases with the higher pH, although the adsorbent was more selective for metals at low pH value [23]. The lowest adsorption quantity was found at pH 2 due to more hydrogen ions being competitive with copper ions for the active sites in the solution [5]. At pH 6, more OH⁻ ions might exist in the solution, causing hydrolysis or the precipitation of copper, affecting the adsorbent capacity [27,42]. Thus, the optimum pH was 5 for this study. In addition, through the measurement of point of zero charges, the surface charge of adsorbents is shown in Table 1. The surface of the adsorbent was more positively charged when the pH is <pH_pzc; this could cause electrostatic repulsion between the adsorbent and the metal. On the contrary, if the solution pH > pH_pzc, the functional group on the adsorbent is negatively charged because of the deprotonation [21]. This phenomenon enhances the affinity to copper ions. The AC, OAC, and IDA-OAC of pH_pzc indicated that adsorbents present a weakly acidic characteristic; they efficiently operate at higher pH values. Xie et al. presented the same result in which the adsorption capacity for copper became higher when pH was increased by using the acidic adsorbent [42]. For the above reasons, a solution of pH 5 was used in the following experiments.

3.3. Effect of Ion Strength

The ionic strength study is significant for the adsorbents in practical operations. Therefore, we investigated the effect of AC, OAC, and IDA-OAC on adsorption with various concentrations of NaNO₃ (1000~5000 mg/L). As shown in Figure 4, the adsorption capacity decreased with the increase in ionic strength. This could be attributed to competition between Na⁺ and Cu²⁺ for the adsorption sites [26]. In addition, the IDA-OAC exhibited a relatively stable adsorption capacity in high ion strength. It could also adsorb 69.7 mg copper ions per gram in the environment containing 5000 mg Na⁺. This demonstrates that the iminodiacetic acid prefers to combine with Cu²⁺ than Na⁺ and that providing a ligand for inner-sphere surface complexation reduces the influence of the variation of ionic strength [23,28]. Li et al. used an adsorbent with a dithiocarbamate functional group to uptake lead in high concentrations of sodium, which maintained high adsorption capacity because the sulfur atoms could provide ligands for the metals [28].

3.4. Effect of Initial Concentration and Equilibrium Isotherms

The effect of variation in the initial concentration of Cu(II) on AC, OAC, and IDA-OAC uptake amount and removal rate is presented in Figure 5. When the solutions reached equilibrium, it was revelated that the adsorption capacities rose with metal ion concentration (5 to 200 (mg/L)). The main reason is that more Cu(II) in the aqueous solution causes a higher driving force to overcome the mass transfer resistance for the adsorbent to uptake adsorbate [20]. At optimum conditions, IDA-OAC revealed the highest adsorption capacity (84.51 mg/g) compared to OAC (54.74 mg/g) and AC (24.86 mg/g). Compared to modifying the silicon dioxide with ethylenediaminetetraacetic acid (Cu 23.9 mg/g), this result proved that the AC through the oxidized and grafted IDA could efficiently enhance the adsorption ability [43]. In addition, although the removal rate of an adsorbent relies on the initial concentration, the OAC and IDA-OAC perform a high removal rate for copper ions at low concentrations, especially IDA-OAC. IDA-OAC removed about 100% of Cu(II) for the concentration at 50 ppm. The tridentate ligand on the IDA exhibited a high affinity to metal ions [21]. This could ensure that the adsorbate has been completely removed from the aqueous solution.

The Langmuir and Freundlich isotherm models have usually simulated the adsorption result with a different initial concentration at a constant temperature [26]. This is useful in order to know how the adsorbates interact with adsorbents. The two isotherm model plots of AC, OAC, and IDA-OAC are illustrated in Figure 6. The adsorption parameter is presented in

Table 3. The fitting results of Langmuir and Freundlich isotherm models.

Sample	qe (mg/g)	Langmuir Isotherm			Freundlich Isotherm
		qm (mg/g)	KL	R2	1/n	KF	R2
AC	24.86	25.04	0.74	0.9993	0.21	10.38	0.8745
OAC	54.74	53.99	2.69	0.9996	0.10	35.21	0.6742
IDA-OAC	84.51	83.75	5.74	0.9998	0.09	59.27	0.6667

. The results showed that the Langmuir isotherm was more fitted than the Freundlich model according to the regression coefficient (R²). For all the three adsorbents, the correlation coefficient of the Langmuir model was more significant than 0.99. This indicated that the copper ions tended to adsorb onto adsorbents homogeneously through monolayer adsorption [5]. Waly et al. used the AC and OAC to adsorb metals derived from water hyacinth and found the same results [39]. Xie et al. also observed that the copper interacted with activated carbon and oxidized carbon, which was well explained by the Langmuir adsorption model [42]. Moreover, the mechanism for the transition metals’ adsorption on grafted IDA material was also reported by Fu et al. [27]. The copper ion commonly occurs in the monolayer with adsorption by a chelating functional group [44]. The experimental data were almost close together, with the q_m (mg/g) values calculated from the Langmuir model being 25.04 mg/g (AC), 53.99 mg/g (OAC), and 83.75 mg/g (IDA-OAC), respectively. Moreover, the K_L value for IDA-OAC was higher than other adsorbents, demonstrating that the higher binding energy is favorable to copper [45].

Table 4. Comparison of studies on copper ion removal.

Adsorbent	pH	Capacity (qmax (mg/g))	Ref
PN-Fe3O4-IDA	pH = 5	47.66	[26]
PVDF-g-G3 PAMAM membrane	pH = 5	153.8	[46]
Fe3O4@SiO2-EDTA	pH = 5.3	36.86	[43]
SBA-TETA	pH = 4	23.9	[47]
GO-IDA	pH = 6.5	108.4	[21]
PEI-WS	pH = 6	52.2	[48]
IRC748 chelating resin	pH = 5	107.39	[36]
IRC86 cation-exchange resin	pH = 5	47.21	[49]
waste wood-based panels derived AC	pH = 5	25.04	Present study
OAC	pH = 5	53.99	Present study
IDA-OAC	pH = 5	83.75	Present study

is shown the different adsorbents maximum adsorption capacity for copper.

3.5. Effect of Contact Time and Adsorption Kinetics

To assess the adsorption rate and the equilibrium time between adsorbate and copper ions, the result of contact time on the adsorption capacity is displayed in Figure 7. In the beginning, the removal of Cu(II) rapidly increased for AC, OAC, and IDA-OAC as the contact time increased. In 60 min, most of the adsorbates were attracted to IDA-OAC (more than 80% of the adsorption capacity). The reaction became slow until it finally reached equilibrium at almost 120 min for the three adsorbents, and the adsorption capacity depended on different materials. The fact that adsorbents can uptake copper ions quickly at first might be attributed to a higher driving force and the amount of uncovered active sites on the adsorbents [39]. Subsequently, the adsorption rate slows for the adsorption sites after saturation. Aryee et al. reported that the copper adsorption on modified peanut husk went through two stages and reached equilibrium by three hours [26]. Laconica et al. used triethylenetetramine to modify mesoporous silica particles and removed copper ions in eight hours [47].

The experimental data about the effect of contact time were fitted by a pseudo-first-order kinetic model and pseudo-second-order kinetic model for this study. Two kinds of classical models can examine the controlling mechanism for the adsorption process. The pseudo-first model considers that the adsorbate undergoes sorption by the physical adsorption process. The pseudo-second model is controlled by chemical interaction [50]. Through the kinetic model plots and adsorption parameters for Cu(II) adsorption presented in Figure 8 and

Table 5. The fitting results of pseudo-first order and pseudo-second order kinetic models.

Sample	Pseudo-First Order		Pseudo-Second Order
	kf (1/min)	R2	Ks (1/min)	R2
AC	0.0083	0.6913	0.0053	0.9976
OAC	0.0142	0.7952	0.0012	0.9963
IDA-OAC	0.0139	0.8007	0.0009	0.9981

, it can be determined that the correlations between the pseudo-second model for AC, OAC, and IDA-OAC were greater than 0.99. The result from Razak et al. also found that the pseudo-second-order kinetic model was better fitted than the pseudo-first-order one by IDA-modified fiber sorption [22]. Neto et al. researched the kinetics model of copper interacted with a chelating group found the correlation factor of pseudo-second-order was 0.986 [51]. The ligand from the oxygen and nitrogen could donate ions for transitional metals. This proved that the primary interaction in the adsorption process was the exchanging or sharing of electrons.

3.6. Thermodynamics of Adsorption

The data from the effect of temperature on the adsorption process were used in the van’t Hoff equation for determining the three thermodynamic parameters ΔG°, ΔH°, and ΔS°. The positive sign of ΔH° from

Table 6. Thermodynamic parameters for the AC, OAC, and IDA-OAC.

Sample	Temperature (K)	ΔG° (kJ/mol)	ΔH° (kJ/mol)	ΔS° (J/mol K)
AC	298	−11.96	4.25	54.36
	308	−12.50
	318	−13.04
OAC	298	−13.87	4.36	61.13
	308	−14.45
	318	−15.09
IDA-OAC	298	−14.95	3.62	62.32
	308	−15.58
	318	−16.20

indicates that the adsorption process was endothermic for AC, OAC, and IDA-OAC. The negative value of ΔG° showed that the reaction process was spontaneous and decreased as the temperature increased [29]. This implies that the higher temperature is suitable for adsorption. Moreover, the ΔS° of the IDA-OAC was larger than OAC and AC. This phenomenon proved the high random adsorption between the adsorbents and copper ions to obtain more affinity to the adsorbate [30].

3.7. Reusability of IDA

In the reusability experiments, to use the 0.1 M HCl, 0.1 M H₂SO₄, and 0.1 M HNO₃ were conducted in the regeneration of IDA-OAC, respectively. The results revealed 0.1 M HCl had higher desorption efficiency (96.89%) than 0.1 M HNO₃ (86.47%) and 0.1 M H₂SO₄ (82.02%). Therefore, the 0.1 M HCl was the eluent for desorption of IDA-OAC. Figure 9 presents the four adsorption–desorption cycles. The adsorption efficiency decline could be because some copper ions were stuck in the adsorbents because the IDA-OAC had high porosity [12]. Or perhaps, the Cu²⁺ occupied the active site and had not been released during the desorbing process [44]. Although the adsorption capacity decreased gradually, it could also maintain high adsorption capacity (77.56 mg/g) after four cycles, which means IDA-OAC is an economical and efficient adsorbent for water treatment.

3.8. Column Sorption of Cu(II)

To enhance the application of the AC, OAC, and IDA-OAC in practice, Figure 10 illustrates the different adsorption abilities for the adsorbents in the column scale. The breakthrough curve can provide better awareness of the adsorbents characteristic to control the effluent from industry in practical applications. For AC, the breakthrough points (C_t/C_i = 0.05) and the exhaustion points (C_t/C_i = 0.95) are seen at 19 BV and 32 BV, respectively. Relatively, the OAC and IDA-OAC had higher bed volumes for breakthrough points (37 BV and 52 BV) and exhaustion points (66 BV and 77 BV). This means oxidized, activated carbon and grafted functional groups can also enhance the performance of sorption copper ions for adsorbents in the column scale. Further, the total removal efficiency for IDA-OAC was 83.54%, clearly higher than OAC (74.63%) and AC (73.53%). This result can ensure that the adsorbate is removed more effectively from the aqueous solution by IDA-OAC.

4. Conclusions

In this study, the nitric acid and iminodiacetic acid functional group successfully modified the activated carbon derived from waste wood-based panels. With the introduction of the oxygen-containing group on the AC, the adsorbents exhibited a high affinity for copper ions, especially the IDA-OAC. In the batch experiment, the adsorption data from AC, OAC, and IDA-OAC were well-explained by Langmuir isotherm and pseudo-second models. The adsorption capacity data q_m (mg/g) for IDA-OAC (83.75 mg/g) from the Langmuir isotherm model were higher than AC (25.04 mg/g) and OAC (53.99 mg/g). Through the oxidized and grafted AC, adsorption capacity increased by about 220% and 340% from the equilibrium adsorption result. Because of the high affinity between IDA and metal ions, the IDA-OAC could efficiently remove copper ions from the low-concentration solution and retain high adsorption capacity in high ion strength. The result of the column experiment demonstrated that grafting AC made the breakthrough point occur later (from 19 BV to 52 BV). The test of the IDA-OAC regeneration proved the good reusability and high stability for the sorption of Cu²⁺. This reveals that the AC and the modified carbon material have great characterization and are more cost-effective as highly potential adsorbents for water treatment.