Competitive Adsorption of Cadmium ( II ) and Mercury ( II ) Ions from Aqueous Solutions by Activated Carbon from Xanthoceras sorbifolia Bunge Hull

This paper presents low-cost and recyclable activated carbon (XLAC) derived from Xanthoceras sorbifolia Bunge hull for highefficiency adsorption of Cd(II) and Hg(II) ions in industrial wastewater. XLAC was prepared through H3PO4 activation and was characterized using N2 adsorption-desorption, scanning electron microscopy (SEM), energy-dispersive spectroscopy (EDX), and Fourier transform infrared (FTIR) spectroscopy. In single-metal-system adsorption experiments, the maximum adsorption capacities for Cd(II) and Hg(II) obtained under different experimental conditions were 388.7 and 235.6mg⋅g, respectively. All adsorption equilibrium data fit perfectly with the Langmuir isotherm model. In a binary metal system, competitive studies demonstrated that the presence of Cd(II) significantly decreased the adsorption of Hg(II), but the adsorption of Cd(II) showed a little change in the presence of Hg(II). In addition, XLAC can be regenerated with a 0.01mol⋅L HNO3 solution and reused at least four times. The FTIR spectra revealed that a chemical interaction occurs between functional groups containing lone electron pairs in XLAC and metal ions. Overall, these results suggest that XLAC may be suitable as an adsorbent for heavy metal removal from wastewater streams.


Introduction
Water pollution by heavy metal ions is a crucial environmental issue worldwide [1,2] because these ions are acutely toxic, nondegradable, and bioaccumulative.Cadmium(II) and mercury(II) are the most important toxic elements in the liquid wastes of several industries, including those that produce fertilizers, batteries, electronics, textiles, and petrochemicals, as well as tanneries and pesticide mills [3].The toxicity of Hg(II) and Cd(II) may lead to carcinogenesis, renal dysfunction, lung damage, and various syndromes in humans.The maximum permitted levels of Cd(II) and Hg(II) in livestock wastewater are 2 and 5 g⋅L −1 , respectively [4].Consequently, effectively controlling the levels of Hg(II) and Cd(II) before their disposal into the environment is of great importance [5][6][7].At present, conventional technologies widely used to remove heavy metals from industrial effluents and reduce their toxicity include chemical precipitation, liquid extraction, electrolysis, membrane separation, crystallization, and reverse osmosis [8].Owing to its technical feasibility and cost-effectiveness, adsorption has been universally recognized as an effective and economical method for treating wastewater containing toxic metals [9].Among the various carbonaceous materials commonly applied for water purification, activated carbon is a promising candidate in the adsorption process owing to its developed porosity, high surface area, large mesopore volume, and low cost and the presence of various functional groups on the surface and its relatively high adsorption rates for heavy metals.The widespread industrial use of activated carbon produced from agricultural waste for the removal of heavy metal contaminants renders activated carbon a high-addedvalue and "green" product that is strongly recommended.Therefore, many studies concerning the preparation of cheap and renewable activated carbon from nut shells, fruit stones, biochar, and bamboo culms have been reported [10][11][12][13][14].
In this study, the hull of Xanthoceras sorbifolia Bunge (XL), which is widely distributed in northern China, was utilized in the production of activated carbon (XLAC) because it is an inexpensive and accessible raw material; also, XL has rarely been used as a precursor for activated carbon.XLAC is expected to provide an excellent, highly porous structure and surface functional groups for binding metal ions in wastewater.Industrial contaminants consist of more than one heavy metal ion; thus, by understanding the competition between various metals for adsorption sites on the adsorbents and the interactions under particular conditions during the adsorption process, one can develop applications for real wastewater treatment.Therefore, in the present work, the agricultural-metal-binding XLAC was adopted for the removal of both Cd(II) and Hg(II) ions from aqueous solutions.
This study aimed to develop XLAC via H 3 PO 4 chemical activation and examine its practicality as an adsorbent for the removal of Cd(II) and Hg(II) ions from single-metal and binary metal solutions in batch and continuous modes.The physicochemical characteristics of XLAC were investigated using nitrogen adsorption isotherms, scanning electron microscopy (SEM), energy-dispersive X-ray spectroscopy (EDX), and Fourier transform infrared (FTIR) spectroscopy and compared with those of its precursor.The influences of the operating factors were examined to optimize the removal process variables such as the solution pH, initial Cd(II) and Hg(II) concentrations, and adsorption temperatures.The results demonstrated that XLAC has great adsorption capacity for both Cd(II) and Hg(II) ions.Additionally, isotherm equilibrium parameters were calculated by applying models to the experimental data.Furthermore, the novelty of this paper lies in its evaluation of the competitive adsorption of Cd(II) and Hg(II) from a binary system; both ions are categorized in the II Deputy Group, in the fifth and sixth periods of the periodic table, respectively, but have different ionic radii and valence electron arrangements.The results showed that XLAC can remove Cd(II) ions from solution more efficiently than it can remove Hg(II).XLAC was evaluated for its applicability.Additionally, the potential adsorption amounts and possible mechanisms of Cd(II) and Hg(II) ion uptake in XLAC were investigated.

Materials and Methods
2.1.Materials.X. sorbifolia Bunge hull (XL) was obtained from the solid waste disposal site of a marketplace located in Chifeng, China; it was then dried and screen-sieved.The portion with particle diameters in the 0.50-0.80mm range was selected for the preparation of activated carbon.Cd(NO 3 ) 2 ⋅4H 2 O and Hg(NO 3 ) 2 ⋅H 2 O were purchased from Beijing Chemical Works, Beijing, China.Calibration curves of the examined ions were established using standard solutions of Cd(II) and Hg(II) prepared in 0.5 mol⋅L −1 HNO 3 by diluting initial stock solutions (1000 mg⋅L −1 ).All of the other chemicals used in this study were of analytical grade, were used without further purification, and were supplied by Tianjin Bodi Chemical Reagent Co., Ltd., China.All of the solutions were prepared with deionized redistilled water.

Buffer Solution.
First, 3.4 g (0.025 mol) of sodium acetate trihydrate (NaOAc) and 1.5 mL (0.025 mol) of glacial acetic acid (HOAc) were mixed and placed in a 2 L volumetric flask.The mixture was diluted to scale with deionized redistilled water to prepare a buffer of pH 4.84.Furthermore, the NaOAc/HOAc buffer solution and NaOH (0.1 and 0.01 mol⋅L −1 ) were used to adjust the pH values of the solutions.

Preparation of XLAC.
The XL was washed to neutrality with deionized redistilled water and sun-dried for 12 h until all of the moisture evaporated.Next, the sample was oven-dried at 100 ∘ C for 24 h.The dried mass was mixed with a 45 wt.% H 3 PO 4 solution at a ratio of 2.6 : 1 (g H 3 PO 4 /g XL) and the mixture was magnetically stirred (500 revolutions⋅min −1 ) for 1 h.Afterwards, the impregnated sample was allowed to carbonize at 500 ∘ C in a tube furnace (FSX2-12-15N, Tianjin, China) for 1 h.After cooling to room temperature under nitrogen atmosphere, the sample was rinsed with deionized redistilled water until neutral pH was attained.The sample was then oven-dried overnight at 120 ∘ C to a constant weight, and the yield was evaluated.Yields of 34% were attained.The developed X. sorbifolia Bunge hull activated carbon is hereafter denoted as XLAC.Finally, the XLAC was ground, sieved at 200 mesh by standard sieves (Model Φ200), and kept in an airtight packet for batch experiments.

Properties of XLAC.
The Brunauer-Emmett-Teller (BET) surface area of the XLAC was determined from nitrogen adsorption-desorption isotherms measured at −196 ∘ C using a surface area analyzer (Micromeritics ASAP 2020, USA).The pore structure of the XLAC was assessed from the isotherms according to conventional procedures.The surface area ( BET ) and total pore volume ( tot ) were determined using the manufacturer's software.The micropore surface area ( mic ) and mesopore surface area ( meso ), as well as the mesopore volume ( meso ), were evaluated using the t-plot method.The density functional theory pore size distribution of the XLAC was obtained using the Autosorb software package with medium regularization.SEM was performed to visualize the morphological changes and to analyze the surface of the XLAC, and elemental analysis of the XLAC was performed using EDX coupled with SEM (Hitachi S-3400, Japan).The surface functionalities of the XL and XLAC were identified using FTIR spectroscopy (Thermo Nicolet, NEXUS, TM, USA).The spectra were recorded using the transmission method.Each sample was ground in KBr at a mass ratio of 1 : 200, and the resulting mixture was pressed.

Batch Adsorption Experiments.
Stock solutions with concentrations of 0.01 mol⋅L −1 were prepared by dissolving the necessary amounts of Cd(II) and Hg(II) ions in deionized redistilled water and diluting to the desired concentrations.
A series of adsorption experiments were conducted by combining 50 mg of XLAC with 50 mL of Cd(II) and Hg(II) solutions at different initial concentrations ranging from 0.0035 to 0.0065 mol⋅L −1 and pH values ranging from 2.5 to 6.0.Each metal ion solution was added to capped Erlenmeyer flasks that were placed in a thermostatic shaker (SHA-C, Jiangsu, China) and shaken at a constant speed of 200 revolutions⋅min −1 at 40 ∘ C for 300 min until equilibrium.Next, the pH of the suspension was adjusted with a certain amount of buffer solution and monitored using a pH meter (PB-10, Sartorius, Germany).Afterwards, all of the samples were centrifuged at 6000 revolutions⋅min −1 for 10 min.The initial and residual Cd(II) and Hg(II) concentrations were measured using an ultraviolet-(UV-) visible spectrophotometer [15] (TU-1901, Beijing, China).The Cd(II) and Hg(II) ion concentrations were calculated from the measured absorbance in the upper fluid at their corresponding maximum absorption wavelengths ( max of Cd(II) = 578 nm and  max of Hg(II) = 490 nm).Spectroscopic grade standards were periodically checked during the experiment and used to calibrate the instrument ( 2 ≥ 0.9990).Taking experimental errors into consideration, each determination was repeated three times in parallel under the same conditions, and the average values are given in this manuscript.The adsorption capacities for Cd(II) and Hg(II) were calculated from [16] where  ,1 and  ,2 (mg⋅g −1 ) represent the adsorption capacities for Cd(II) and Hg(II) at time  (min),  0,1 and  ,1 (mol⋅L −1 ) represent the initial and final concentrations of Cd(II) at time  (min), and  0,2 and  ,2 (mol⋅L −1 ) represent the initial and final concentrations of Hg(II) at time  (min), respectively. 1 and  2 (mL) represent the volumes of the Cd(II) and Hg(II) solutions. 1 and  2 (g) are the masses of the adsorbents.In the calculations of  ,1 and  ,2 , no losses of Cd(II) and Hg(II) to any other mechanism (e.g., volatilization, sorption to the glassware, or degradation) were assumed.

Adsorption Isotherms.
Equilibrium adsorption experiments were performed by combining 50 mg of XLAC with 50 mL of heavy metal solutions at different initial concentrations (0.0035-0.0065 mol⋅L −1 ) and different temperatures (35 ∘ C, 40 ∘ C, and 45 ∘ C) until adsorption equilibrium was reached.The Langmuir and Freundlich isotherm models for single-metal systems were used to determine the adsorption equilibrium [17].

Competitive Adsorption.
In this step, 50 mg of XLAC was added to synthetic mixtures of primary and secondary Cd(II) and Hg(II) solutions.Adsorption equilibrium experiments were conducted as described previously to measure the adsorption capacity for Cd(II) ions at equilibrium (initial Cd(II) concentration ranged from 0.0035 to 0.0065 mol⋅L −1 ) in the presence of 0.005 mol⋅L −1 Hg(II) ions in solution; likewise, the adsorption capacity for Hg(II) ions at adsorption equilibrium (initial Hg(II) concentration ranged from 0.0035 to 0.0065 mol⋅L −1 ) was determined in the presence of 0.005 mol⋅L −1 Cd(II) ions in solution.The binary metal solutions were agitated at a constant speed of 200 revolutions⋅min −1 at pH 5.5 for 300 min until equilibrium.The Cd(II) and Hg(II) concentrations in the individual binary solutions were determined using a UV-visible spectrophotometer.

Regeneration Studies.
The studies on the regeneration of Cd(II) and Hg(II) ions from XLAC were performed in 100 mL flasks using 0.01 mol⋅L −1 HNO 3 .The metal-ion-loaded XLAC reacted with the HNO 3 eluent solution for 120 min, and then the mixture was filtered; then, the XLAC was washed with deionized water to neutral pH, dried, and reused for the next adsorption process.Adsorption-desorption experiments were performed five times consecutively.

Results and Discussion
3.1.Characterization of XLAC.N 2 adsorption-desorption isotherms for XLAC and the precursor, XL, are displayed in Figure 1(a), and they reveal that XLAC shows a mixture isotherm characteristic of type I and type IV [18].The adsorption volume of XLAC increased with the relative pressure until / 0 ≈ 0.45, with a wider hysteresis loop at relatively high pressures, indicating the presence of many mesopores.The textural parameters of XLAC in Table 1 show that its surface area and total pore volume were higher than those of XL, at 688.62 m 2 ⋅g −1 and 0.377 cm 3 ⋅g −1 , respectively.These results imply that the contribution of the mesopores to the total pore volume (66.8%) became dominant and that the porous structure of XLAC was well developed.As reported for the activation process of XLAC, there may have been some reactions between H 3 PO 4 and the internal functional groups of XL, causing pore volume enhancement and expansion [19].Figure 1(b) shows the pore size distribution of XLAC.XLAC has pore sizes between 0.5 and 5.5 nm and shows a wide pore size distribution with a low pore volume.Table 1 also shows that the mesopore surface area increased notably.Thus, a significant amount of micropores became mesopores.
Elemental analysis was conducted for XLAC and XL using EDX.As indicated in Table 2, the carbon, oxygen, nitrogen, and phosphorus contents of XLAC were 80.26%, 12.92%, 4.62%, and 2.20%, respectively.Additionally, XLAC prepared from XL using the activating reagent, H 3 PO 4 , during the treatment process showed a higher carbon content (80.26%) than XL (59.41%).Moreover, the appearance of elemental phosphorus (2.20%), due to the introduction of H 3 PO 4 to be reacted with XL during the activation process, was confirmed by EDX analysis.
The surface morphologies of XLAC and XL were investigated using SEM and are shown in Figure 1.For XL (Figure 1(c)), the surface was irregular in nature, with many small sheets or layers with large pores.XLAC (Figure 1(d))   exhibited a coarse and microporous structure comprising a considerable amount of small cavities on the surface [20].This morphology suggests a rearrangement of the structure during the activation process, indicating a higher surface area and successful pore development in the XLAC.FTIR spectroscopy was employed to evaluate the changes in the major functional groups of XLAC and XL, and the results are shown in Figure 1(e).In contrast to XL (Figure 1(e)(A)), the broad overlapping absorption band at 3300-3500 cm −1 was due to the stretching vibration of the hydroxyl (-OH) and amine (-NH) groups on XLAC, with a maximum at 3422 cm −1 (Figure 1(e)(B)); this peak shifted to 3417 and 3410 cm −1 after the adsorption of Cd(II) and Hg(II), respectively, and shrank (Figure 1(e)(C and D)).These changes in the absorption bands illustrate that the -OH and -NH on a multimer differed from those on a monopolymer or even in a dissociative state, indicating that the states of -OH and -NH were affected by binding with Cd(II) and Hg(II).The peaks at 2384 and 2265 cm −1 were related to the C-H stretching in the methyl groups (Figure 1(e)(B)) and shifted after adsorption (Figure 1(e)(C and D)).A new intense peak at approximately 1620 cm −1 , which was assigned to the -C=O stretching vibration in the carboxyl groups, appeared (Figure 1(e)(B)) and was shifted significantly to 1612 and 1609 cm −1 and shrank (Figure 1(e)(C and D)).The peak appearing at 1192 cm −1 (Figure 1(e)(B)) was assigned to P=O because H 3 PO 4 was used as the activating agent, leading to the formation of phosphate acid esters.Furthermore, the peak at 1075 cm −1 corresponded to the C-O stretching in saturated aliphatic groups, and the -C-O and -O-C=O stretching of the carboxyl groups broadened, shrank, and shifted to 1071 cm −1 after Hg(II) adsorption (Figure 1(e)(C)) and 1063 cm −1 after Cd(II) adsorption (Figure 1(e)(D)).The peaks at approximately 964, 802, and 729 cm −1 were assigned to the -C-H of the benzene ring and aromatic alcohols, and the band at 558 cm −1 may be assigned to the out-of-plane bending of C-O bonds of alcohols and C-N bonds of amides; these peaks shrank after adsorption (Figure 1(e)(C and D)).These changes in the absorption peaks indicate that the free carboxyl groups became carboxylates, which appeared during the adsorption reaction between the metal ions and XLAC.Additionally, ion exchange occurred, and chemical bonds were formed between the metal ions and the -OH, -NH, -C=O, and -O-C=O groups of the XLAC.Generally, the bands show that the XLAC surface was provided with a certain amount of activated functional groups in the adsorption process [21,22].

Effect of pH.
The pH value of the heavy metal solution plays a major role in the adsorption process.The influence of pH on the adsorption capacity of XLAC was studied over the 2.5-6.0 pH range in the single-metal system, and the results are shown in Figure 2(a).The adsorption capacity of XLAC increased from 106.3 to 375.2 mg⋅g −1 for Cd(II) and from 81.2 to 228.7 mg⋅g −1 for Hg(II) when the pH was increased from 2.5 to 6.0.When the pH value was low, the overall surface charge of the activated sites became positive, and H + could compete with metal ions for exchangeable cations, resulting in lower uptake of Cd(II) and Hg(II) [23].The XLAC surface became more negatively charged as the pH increased, and because of the weak competition effect of the pH, more positively charged metal ions were adsorbed.Decreases in the adsorption capacity at higher pH values were related not only to the formation of Cd(OH) 2 and Hg(OH) 2 , but also to the ionized nature of the functional groups on the XLAC surface.The maximum adsorptions were observed at 5.1 for Cd(II) and 4.5 for Hg(II) ions; therefore, the pH value was adjusted to 5.5 for the remaining adsorption experiments.

Effect of Initial Concentrations.
To evaluate the adsorbability of Cd(II) and Hg(II) on XLAC, the adsorption capacities towards Cd(II) and Hg(II) ions were determined in single-metal solutions.Figure 2(b) shows the effects of the concentration of each metal, which ranged from 0.0035 to 0.0065 mol⋅L −1 at pH 5.5, on the adsorption capacity of XLAC.The adsorption capacity of XLAC increased from 264.3 to 381.1 mg⋅g −1 for Cd(II) and from 206.2 to 235.6 mg⋅g −1 for Hg(II) ions with an increase in the metal ion concentration, gradually reaching adsorption equilibrium.When the initial concentration was low, the activated adsorption sites on XLAC were sufficient.Afterwards, as the concentration of Cd(II) and Hg(II) increased, more available functional sites became occupied until saturation, causing the adsorption capacity to remain nearly constant.Nevertheless, the adsorption capacities for Cd(II) and Hg(II) differed, as shown in Figure 2(b); for a given XLAC dosage, a higher adsorption capacity was shown for Cd(II) (381.1 mg⋅g −1 ) than for Hg(II) (235.6 mg⋅g −1 ).The results revealed that Cd(II) was adsorbed because Cd(II) ions have greater affinity for XLAC.

Adsorption Isotherms. Adsorption isotherms can elucidate how the heavy metal ions interact with XLAC, enabling
the study of the practical application of XLAC in wastewater treatment.The adsorption parameters were determined using the Langmuir and Freundlich isotherm models.The linear forms of the Langmuir and Freundlich isotherms are represented, respectively, by [24] ln where   is the concentration of the metal ions at equilibrium (mol⋅L −1 ),   is the amount adsorbed (mg⋅g −1 ),   is the complete monolayer adsorption capacity (mg⋅g −1 ),  is the Langmuir constant related to the adsorption capacity (L⋅g −1 ), and  and   are the Freundlich constants.
Data on the Cd(II) and Hg(II) adsorption capacities of XLAC at different temperatures were evaluated and are shown in Figure 3(a); the adsorption parameters of the Langmuir and Freundlich isotherm models for each heavy metal are presented in Figures 3(b) and 3(c) and Table 3. Figure 3(a) shows that an increase in temperature enhanced the adsorption capacities for Cd(II) and Hg(II) ions.These results can be attributed to a swelling effect within the internal structure of XLAC caused by an elevated temperature in a certain range, facilitating the penetration of metal ions binding with functional groups on the surface and the overcoming of the energy barrier of adsorption.As observed in Table 3, the  2 Cd(II) value of 0.9912 ((1.856× 10 −5 ) < 0.01) for the Langmuir model is higher than that for the Freundlich model of 0.7347 ((0.0018)< 0.01), and there was no significant difference in the adsorption of Cd(II) ions.The  2 Hg(II) value of 0.9882 ((3.340× 10 −5 ) < 0.01) for the Langmuir model is also higher than that for the Freundlich model of 0.8460 ((0.0059)< 0.01), and no significant difference was found in the adsorption of Hg(II) ions.The experimental data for both Cd(II) and Hg(II) ion adsorption had better coefficient values and better fits with the Langmuir isotherm model than with the Freundlich isotherm model (Figures 3(b) and 3(c)).Additionally, comparison of the goodness-of-fit measures between the two different models showed that the Langmuir model yielded the lower standard error (SE) values, and the higher SE values of the Freundlich model indicated low predictive ability to describe Cd(II) and Hg(II) adsorption processes (Table 3).Therefore, the results for the single-metal-system solutions revealed that XLAC displayed higher affinity for Cd(II) than for Hg(II) ions [25].
The maximum monolayer adsorption capacity,   (mg⋅g −1 ), derived from the experimental data reached 388.7 mg⋅g −1 for Cd(II) and 235.6 mg⋅g −1 for Hg(II) ions.The adsorption capacities of XLAC for Cd(II) and Hg(II) ions were found to be comparable and moderately higher than those of other  similar reported adsorbents [26].XLAC has considerable potential for the removal of Cd(II) and Hg(II) ions from wastewater, with stronger affinity for Cd(II) ions.

Competitive Adsorption.
The competitive adsorption characteristics of Cd(II) and Hg(II) ions in binary metal solution systems were investigated, and the results are shown in Figure 4.When Hg(II) ions were added to the system at an initial concentration of 0.005 mol⋅L −1 , the adsorption capacity for Cd(II) increased with increasing initial Cd(II) concentration and gradually reached adsorption equilibrium (Figure 4(a)).These results imply that the Cd(II) adsorption capacity of XLAC was similar in single-metal and binary metal systems and did not experience competition after the addition of Hg(II).In contrast, the Hg(II) ion adsorption capacity of XLAC was affected by the presence of Cd(II) at an initial concentration of 0.005 mol⋅L −1 (Figure 4(b)).This finding indicates that activated sites for Cd(II) on XLAC may be partially occupied by the added Hg(II) in binary systems, but when the concentration of Cd(II) ions in solution was increased, Cd(II) was adsorbed preferentially at the adsorption sites on the XLAC surface, particularly in the case of insufficient activated sites [27].At low metal concentrations, the number of available adsorption sites was sufficient.Hence, the adsorption capacity of XLAC was not influenced by the presence of other heavy metal ions.However, when the concentration of metals exceeded the adsorption capacity, Cd(II) was adsorbed preferentially in the binary metal solution over the Hg(II) ions.This phenomenon suggests that Cd(II) ions have higher affinity for XLAC, which may be attributed to the fact that a longer ionic radius (Cd(II) (97 pm) < Hg(II) (110 pm)) corresponds to a shorter hydrated ionic radius, resulting in the higher affinity for metal ions of the activated sites of XLAC.Furthermore, the arrangements of the extranuclear electrons of Cd(II) and Hg(II) ions are 4d 10 5s 0 and 5d 10 6s 0 , respectively.According to Xu Guangxian's Approximate Rule of Electronic Configuration [28], the energy level of the nuclear track of 5s 0 is lower than that of 6s 0 ; thus, as the -OH, -C=O, and -NH functional groups on XLAC reacted with metal ions, the lone-electronpair electron clouds around the O and N atoms could first fill the lower energy level, 5s 0 .Hence, the adsorption capacity of XLAC for Cd(II) remained the same as that in the single-metal solutions, but the competitive adsorption had a negative influence on Hg(II) ions.Similar results have been observed in other studies [29].
3.6.Regeneration Studies.The regeneration of XLAC after adsorption is one of the key factors for its economic viability in practical applications for wastewater treatment.Reusability studies were conducted to regenerate heavy metals loaded on XLAC [30].HNO 3 at a concentration of 0.01 mol⋅L −1 was selected as the eluent for desorption of Cd(II) and Hg(II) ions from XLAC. Figure 5 shows the adsorptiondesorption results for the two metals and the regeneration of XLAC for five consecutive cycles.The reusability results for XLAC suggest that the adsorption capacities for Cd(II) and Hg(II) ions were almost unaffected, even after four cycles.The decrease in the adsorption capacity for the two metals was determined to be 20 mg⋅g −1 before the fifth use.This trend might be responsible for the negligible amount of materials lost during the regeneration cycles.In summary, XLAC can be used repeatedly for four cycles with little loss of initial adsorption capacity and possesses good regenerative properties towards Cd(II) and Hg(II) ions in wastewater.

Conclusions
XLAC was developed through H 3 PO 4 activation from X. sorbifolia Bunge hull and in 34% yields.XLAC was characterized using BET, SEM, EDX, and FTIR analysis.
The maximum adsorption capacities were 388.7 mg⋅g −1 for Cd(II) and 235.6 mg⋅g −1 for Hg(II) under the optimum conditions of adsorbent dosage of 50 mg, pH of 5.5, and temperature of 45 ∘ C. The adsorption equilibria of both Cd(II) and Hg(II) ions were described successfully by Langmuir isotherm models.Competitive adsorption results revealed that Cd(II) ions had higher adsorption affinity than Hg(II) ions did with activated sites on the XLAC surface.FTIR spectroscopic analysis of metal-loaded XLAC confirmed that the adsorption process occurred through chemical ion exchange.
XLAC was effectively regenerated using 0.01 mol⋅L −1 HNO 3 as the agent and was reused and showed high performance after four adsorption-desorption cycles.XLAC can be used as a low-cost, alternative adsorbent for the treatment of wastewater containing Cd(II) and Hg(II) ions.

Table 2 :
Global surface composition as determined by EDX analysis.