Adsorption Mechanisms of Dodecylbenzene Sulfonic Acid by Corn Straw and Poplar Leaf Biochars

Biochar is an eco-friendly, renewable, and cost-effective material that can be used as an adsorbent for the remediation of contaminated environments. In this paper, two types of biochar were prepared through corn straw and poplar leaf pyrolysis at 300 °C and 700 °C (C300, C700, P300, P700). Brunaer–Emmett–Teller N2 surface area, scanning electron microscope, elemental analysis, and infrared spectra were used to characterize their structures. These biochars were then used as adsorbents for the adsorption of dodecylbenzene sulfonic acid (DBSA). The microscopic adsorption mechanisms were studied by using infrared spectra, 13C-nuclear magnetic resonance spectra, and electron spin resonance spectra. The surface area and pore volume of C700 (375.89 m2/g and 0.2302 cm3/g) were the highest among all samples. Elemental analysis results showed that corn straw biochars had a higher aromaticity and carbon to nitrogen (C/N) ratio than the poplar leaf biochars. High temperature caused the increase of carbon content and the decrease of oxygen content, which also gave the biochars a higher adsorption rate. Pseudo-second order kinetic provided a better fit with the experimental data. Adsorption isotherm experiments showed that the adsorption isotherm of C300 fit the linear model. For other biochars, the adsorption isotherms fitted Langmuir model. Biochars with high temperatures exhibited enhanced adsorption capacity compared with ones at low temperatures. The qmax values of biochars to DBSA followed the order of P700 > C700 > P300. The adsorption mechanisms were complex, including partition, anion exchange, the formation of H bonds, covalent bonds, and charge transfer. The adsorption by covalent bonding might be the key mechanism determining the adsorption capacity of P700.


Introduction
Linear alkylbenzene sulfonates (LAS) are popularly used in detergents and cleaning products. They can cause environmental hazards after entering into surface waters by household and industrial sewage [1]. Some techniques have been applied for the removal of surfactants from water or soils. Adsorption is a superior method for water treatment or soil remediation due to its low cost, easy operation, and high efficiency. Mineral oxides, clays, activated carbon, and polymers can be used as the adsorbents for the adsorption of surfactants [2], but the sorption capacity of sodium dodecyl sulfate on Fluvisol soil was very low [3]. Renewable bioenergy technologies can convert biomass feedstock into biochar, accompanied with the production of bio-gas and bio-oil [4,5]. Biochar is a carbonaceous material created through thermal pyrolysis of biomass without oxygen condition. The yield of biochar will decrease in the pyrolysis process, due to the dehydration and thermal degradation of cellulose and lignin structures [6]. The type of feedstock and pyrolysis temperatures can also influence the physical, chemical and adsorption properties of biochars. Wheat straw biochar had higher carbon and nitrogen contents and lower ash materials, as compared with corn straw biochar [7]. Pine sawdust biochar also had a higher adsorption capacity than that of green waste and corncob biochars [8]. Higher pyrolysis temperature could cause the increase of C content and the adsorption affinity of organic contaminants on biochars. At the same time, H, O, N and S contents decreased [9,10]. Biochars have strong adsorption capacities for contaminants, such as carbaryl [11], naphthalene [9], fluoroquinolone antibiotics [12], hexavalent chromium [5], and so on. There is very little information on the adsorption properties of LAS on biochars.
Westall et al. had studied the sorption of LAS on the sediment materials, and the results showed that Freundlich and virial equations fitted the isotherms well [1]. The sorption mechanisms included hydrophobic interaction, specific chemical interaction, or electrostatic interaction. Sodium dodecyl sulfate could also be adsorbed by hydrophobic interaction with organic matter of the soil and by ligand exchange or electrostatic attraction with kaolinite [13]. Sodium dodecylbenzene sulfonate (SDBS) is an anionic surfactant that is used extensively worldwide. Many papers had reported its adsorption behaviors and adsorption mechanisms. It could be adsorbed onto the organophilic bentonites or activated carbon by the monolayer adsorption with a relatively fast process [14,15]. However, the adsorption of SDBS on kaolinite was a two-stage process with an apparent multilayer formation [16].
Dodecylbenzene sulfonic acid (DBSA) is the acid form of SDBS. DBSA could be adsorbed on humic acids (HAs) by H bonds, hydrophobic interactions, and electron donor-acceptor mechanisms. Alluvial soil HA had a higher sorption capacity than that of Mollisol soil HA [17]. The adsorption behaviors of DBSA on biochars have been seldom reported. Corn straw and poplar leaf are commonly seen in China, and they are attractive feedstocks for biochar production. Therefore, we chose corn straw and poplar leaf as the biomass feedstocks to produce biochars in this study. The objective of the study was to obtain a deeper investigation of the influence of the pyrolysis temperature and biomass feedstocks on the physicochemical properties of biochars, and the adsorption behaviors of DBSA on different types of biochars. Further, infrared (IR) spectra, 13 C-nuclear magnetic resonance (NMR) spectra and electron spin resonance (ESR) spectra were applied to study the adsorption mechanisms. The application of ESR provides a new insight into the adsorption mechanism of DBSA on biochars.

Materials
Dodecylbenzene sulfonic acid (95%) was purchased from TCI (TCI, Shanghai, China). Its critical micelle concentration (CMC) is 0.4134 g/L [18]. The biomasses of corn straw and poplar leaf were collected from Inner Mongolia and Beijing, China. Before the pyrolysis, corn straw and poplar leaf were washed to remove the ash. Then, the dried biomass feedstocks were put into stainless steel reactors (cylindrically shaped with a height of 10.5 cm and an inner diameter of 7.5 cm) and pyrolyzed in a Sx2-4-10 digital laboratory muffle furnace (Zhonghuan Lab Furnae Co., Ltd., Tianjin, China) at 300 • C and 700 • C for two hours with a heating rate of 10 • C/min. These products were mixed with 1 M HCl and 3 M HF to remove the ash materials. After washing with deionized water, the corn straw biochar and poplar leaf biochar were crushed and sieved to 0.25 mm. The obtained biochars were referred to as C300, C700, P300 and P700. HCl and HF (Sinopharm Chemical Reagent Co., Ltd., Shanghai, China) were all of analytical grade.

Biochar Characterization
Scanning electron microscope (SEM) images of the biochars were recorded by a Hitachi S-4800 scanning microscope (Hitachi, Tokyo, Japan). The Brunauer-Emmett-Teller (BET) nitrogen specific surface areas of biochars were determined by N 2 adsorption-desorption at 77 K with a Tristrar II 3020 surface area analyzer (Micromeritics, Norcross, GA, USA). The contents of C, N, and H were determined in a Vario EL III elemental analyzer (Elementar, GmbH, Hanau, Germany). The O content was calculated based on the equation: O% = 100% − C% − H% − N% − ash content. The micro IR spectra were recorded in the range of 4000-600 cm −1 with a resolution of 4 cm −1 using a Nicolet Nexus-470 FTIR spectrometer (Thermo Nicolet, San Diego, CA, USA). The solid-state 13 C-NMR spectra were acquired on a Bruker DSX2300 spectrometer (Bruker, Faellanden, Switzerland) operated at 100.37 MHz. The sample was packed in a 4 mm rotor with a contact time of 3000 µs. The scan times were more than 20,000. ESR spectra were undertaken using a Bruker ESP300 spectrometer (Bruker BioSpin, Billerica, MA, USA) and operated at 100 kHz modulation and 9.75 GHz microwave frequency.

Batch Adsorption Experiments
The adsorption kinetics of DBSA at a constant concentration (120 mg/L, 20 mL) onto 60 mg biochars were examined at different sampling times (0, 1, 2, 5, 10, 16, 24, 36, 48, 60, and 72 h). The temperature was 25 ± 2 • C. After shaking at the speed of 130 rpm, the solution was centrifuged at 5000 rpm for 12 min, and filtered through a 0.22 µm membrane. The concentration of DBSA was measured at 223 nm using the UV757 spectrophotometer (Shanghai Accurate Scientific Instrument Co., Ltd., Shanghai, China). Each point containing the blank and control samples was conducted in triplicate.
Different concentrations of DBSA solution (15 mg/L-360 mg/L, 20 mL) were mixed with 60 mg biochars in a 50 mL flask and shaken for 48 h to reach adsorption equilibrium for obtaining the adsorption isotherms. Then the mixtures were treated as described above.

Data Analysis
The amount of DBSA adsorbed was calculated by the following equation: where V is the volume of the solution (mL), C and C e are the initial and equilibrium concentrations (mg/L), m is the weight of the biochars (g), and R% represents the removal efficiency. The relationships between the adsorption rate constants and the chemical compositions of biochars were examined using the Pearson correlation coefficient.

Characteristics of Biochars
C700 and P700 samples exhibited larger surface areas (375.89 m 2 /g and 105.88 m 2 /g) and pore volumes (0.2302 cm 3 /g and 0.0721 cm 3 /g) than that of C300 and P300. Corn straw biochars also had higher surface areas and pore volumes by comparing with that of poplar leaf biochars. The average pore sizes of the biochars ranged from 3.98-12.27 nm ( Table 1). The SEM micrographs of the biochars were demonstrated in Figure 1. C300 and P300 samples had fewer pores and more smooth appearances. At low temperature, amorphous carbons were the main carbons, and pores were not well developed. C700 and P700 presented uniform tunneling macropore structures in Figure 1b,d. C700 also had some smaller pore structures inside the tunneling macropores. Due to the high temperature, the tunneling structures had been crushed. The adsorption and desorption isotherms for biochars are shown in Figure 2. The similar isotherms of C700 and P700 suggested that the adsorption of N 2 on biochars may follow similar kinetics [19] because of their similar pore structures. For C300 as well as for P300, the isotherms are characteristic of non-porous materials or materials with large macropores, indicating no porous structure. The elemental compositions and atom ratios of biochars are shown in Table 2. The C contents and C/N ratios of corn straw biochars were higher than those of poplar leaf biochars. The low ratios of H/C (0.21 and 0.38) indicated the high aromatization of biochars [20], because some of the amorphous carbon would be transformed into aromatic carbon at 700 • C [21]. The C contents, ash materials, and C/N ratios of the biochars were also greater at a higher pyrolyzing temperature. O/C was indicative of surface hydrophilicity, and (O + N)/C was recognized as the indice of polarity [22,23]. H, N, O, O/C, and (O + N)/C decreased with the pyrolyzing temperatures, due to the dehydration, decarboxylation, and decarbonylation in the pyrolysis process [24]. The distinct surface and structure characteristics of biochars, regulated by the biomass feedstock and pyrolytic temperatures, could significantly influence the adsorption of DBSA on biochars. Table 1. BET-N 2 surface area, pore volume, and average pore size of biochars.

Samples
Surface Area (m 2 /g) Pore Volume (cm 3 Table 2. Elemental composition (on a dry mass basis) and atomic ratios of biochars. for biochars are shown in Figure 2. The similar isotherms of C700 and P700 suggested that the adsorption of N2 on biochars may follow similar kinetics [19] because of their similar pore structures. For C300 as well as for P300, the isotherms are characteristic of non-porous materials or materials with large macropores, indicating no porous structure. The elemental compositions and atom ratios of biochars are shown in Table 2. The C contents and C/N ratios of corn straw biochars were higher than those of poplar leaf biochars. The low ratios of H/C (0.21 and 0.38) indicated the high aromatization of biochars [20], because some of the amorphous carbon would be transformed into aromatic carbon at 700 °C [21]. The C contents, ash materials, and C/N ratios of the biochars were also greater at a higher pyrolyzing temperature. O/C was indicative of surface hydrophilicity, and (O + N)/C was recognized as the indice of polarity [22,23]. H, N, O, O/C, and (O + N)/C decreased with the pyrolyzing temperatures, due to the dehydration, decarboxylation, and decarbonylation in the pyrolysis process [24]. The distinct surface and structure characteristics of biochars, regulated by the biomass feedstock and pyrolytic temperatures, could significantly influence the adsorption of DBSA on biochars.

Adsorption Kinetics and Isotherm
In Figure 3, results from studying the adsorption kinetics of DBSA on biochars are shown. The results indicated that the adsorption of DBSA on C700, P300, and P700 was relatively slow. However, it was faster than the adsorption of DBSA on soils and Mollisol soil HA [17]. Within 5 h of solution/biochar contact, 89.67%, 78.34%, and 83.09% of the initial DBSA amount were removed by C700, P300, and P700, respectively. After 10 h, the adsorption of DBSA almost reached its equilibrium with 91.05%, 81.69%, and 85.28% removal efficiencies. For C300, the adsorption seemed to approach equilibrium in 48 h, with a removal efficiency of 89.50%. Kinetic equation parameters for the adsorption of DBSA on biochars are listed in Table 3. Pseudo-second order kinetic was more suitable in describing the adsorption kinetics of DBSA on biochars (R 2 , 0.992-0.999). It was confirmed that chemical adsorption was the rate-limiting mechanism [22]. From the adsorption rate constant, it appears that DBSA adsorbed more quickly to the biochars prepared at high temperature than to the biochars made at low temperature.

Adsorption Kinetics and Isotherm
In Figure 3, results from studying the adsorption kinetics of DBSA on biochars are shown. The results indicated that the adsorption of DBSA on C700, P300, and P700 was relatively slow. However, it was faster than the adsorption of DBSA on soils and Mollisol soil HA [17]. Within 5 h of solution/biochar contact, 89.67%, 78.34%, and 83.09% of the initial DBSA amount were removed by C700, P300, and P700, respectively. After 10 h, the adsorption of DBSA almost reached its equilibrium with 91.05%, 81.69%, and 85.28% removal efficiencies. For C300, the adsorption seemed to approach equilibrium in 48 h, with a removal efficiency of 89.50%. Kinetic equation parameters for the adsorption of DBSA on biochars are listed in Table 3. Pseudo-second order kinetic was more suitable in describing the adsorption kinetics of DBSA on biochars (R 2 , 0.992-0.999). It was confirmed that chemical adsorption was the rate-limiting mechanism [22]. From the adsorption rate constant, it appears that DBSA adsorbed more quickly to the biochars prepared at high temperature than to the biochars made at low temperature.    Pseudo-Second Order Kinetic 1/q t = 1/K 2 × q e 2 + t/q e = 1/v 0 + t/q e K 1 (h −1 ) q e (mg/g) R 2 K 2 (g/(mg·h)) q e (mg/g) v 0 (mg/(g·h)) R 2 q e is the adsorbed amount at equilibrium, q t is the amount of DBSA adsorbed at time t, K 1 and K 2 are the pseudo-first order rate constant and pseudo-second order rate constant, K 2 q e 2 (v 0 ) is the initial rate [25,26]. Values are mean ± standard errors.
The adsorption isotherms of DBSA on biochars were demonstrated in Figure 4. DBSA adsorption capacity on biochars increased with the increasing pyrolysis temperature. Linear, Freundlich, and Langmuir models were applied to fit the isotherms, and the parameters of the isotherm equations were listed in Table 4. The linear model fit well for the adsorption of DBSA on C300, which indicated that the DBSA was partitioning into the non-carbonized organic matter of C300 [9]. The adsorption of DBSA on C700, P300, and P700 were best fit to the Langmuir isotherm under the concentration range studied, which confirmed that the adsorption occurred on a homogenous surface by monolayer adsorption [28]. It also indicated that a strong adsorption affinity existed between biochars and DBSA, and it was the anion exchange interaction that made the sulfonate ion adsorbed onto poplar leaf biochars and C700 [29]. Interestingly, the surface area of C700 was the biggest among four samples (Table 1), approximately 3.6 times that of P700 (Table 1), but q max of DBSA on P700 (155.9 mg/g) was the highest. Furthermore, P300 had the highest average pore size (12.27 nm), but the lowest q max . Therefore, surface area and average pore size were not the factor governing the adsorption capacity. This suggests that P700 has great potential in pollution control of surfactants.
In Table 5, the K 2 values were analyzed as a function of some of the characteristics of the biochars (Tables 1, 2, 6 and 7). A strong positive relationship was observed between the values of these adsorption rate constants and surface area, pore volume, and organic free radical concentrations of biochars. At the same time, K 2 was negatively related to the content of O and (O + N)/C. The statistical analyses reported here have suggested the involvement of these structural parameters in the adsorption process. q e is the adsorbed amount at equilibrium, K P , K, and K F are the partition coefficient, adsorption coefficient and Freundlich affinity coefficient, respectively. C e is the equilibrium solution concentration, q max is the Langmuir maximum capacity, and n is the Freundlich linearity constant [27]. Values are mean ± standard errors.

Adsorption Mechanisms
As can be seen from the Fourier transform infrared (FTIR) spectra in Figures 5 and 6, the broad band at 3365 cm −1 was ascribed to the O-H stretching vibration of hydroxyl functional groups [30]. The peaks at 2927 cm −1 and 2856 cm −1 were attributed to symmetric C-H stretching of alkyl groups [31]. P300 contained more alkyl groups than the other biochars, due to the stronger adsorption at 2927 cm −1 . The bands at 1707 cm −1 and 1612 cm −1 were assigned to C=O vibrations [32]. The band at 1212 cm −1 was indicative of C-O stretching vibration in phenol and alcohol [33]. The peaks in 831-884 cm −1 corresponded to an aromatic C-H stretching vibration [34]. As can be seen from the FTIR results of C300, C700, P300, and P700, higher pyrolysis temperature caused the decrease of the aliphatic C-H groups, and the disappearance of the peaks at 1707 cm −1 . These results were consistent with the elemental analysis results of lower ratios of H/C and O/C. The obvious changes of the structural characters might be the reason for the different adsorption sites and adsorption mechanism. The FTIR spectra of biochars after the adsorption of DBSA are also presented in Figures 5 and 6. In Figure 5, the adsorption intensities at 1707 cm −1 and 1212 cm −1 in the FTIR spectrum of C300-DBSA became higher than that of the pristine C300 after the adsorption, which indicated that the adsorption took place in C=O and C-O groups, and H bond formed. H bond may be formed between the H atom in hydroxyl functional groups of phenol or carboxyl, and the O atom of DBSA. The presence of aromatic C-H groups at 884 cm −1 in the C700-DBSA sample confirmed that the aromatic C-H groups of DBSA were adsorbed on C700.

Adsorption Mechanisms
As can be seen from the Fourier transform infrared (FTIR) spectra in Figures 5 and 6, the broad band at 3365 cm −1 was ascribed to the O-H stretching vibration of hydroxyl functional groups [30]. The peaks at 2927 cm −1 and 2856 cm −1 were attributed to symmetric C-H stretching of alkyl groups [31]. P300 contained more alkyl groups than the other biochars, due to the stronger adsorption at 2927 cm −1 . The bands at 1707 cm −1 and 1612 cm −1 were assigned to C=O vibrations [32]. The band at 1212 cm −1 was indicative of C-O stretching vibration in phenol and alcohol [33]. The peaks in 831-884 cm −1 corresponded to an aromatic C-H stretching vibration [34]. As can be seen from the FTIR results of C300, C700, P300, and P700, higher pyrolysis temperature caused the decrease of the aliphatic C-H groups, and the disappearance of the peaks at 1707 cm −1 . These results were consistent with the elemental analysis results of lower ratios of H/C and O/C. The obvious changes of the structural characters might be the reason for the different adsorption sites and adsorption mechanism. The FTIR spectra of biochars after the adsorption of DBSA are also presented in Figures 5 and 6. In Figure 5, the adsorption intensities at 1707 cm −1 and 1212 cm −1 in the FTIR spectrum of C300-DBSA became higher than that of the pristine C300 after the adsorption, which indicated that the adsorption took place in C=O and C-O groups, and H bond formed. H bond may be formed between the H atom in hydroxyl functional groups of phenol or carboxyl, and the O atom of DBSA. The presence of aromatic C-H groups at 884 cm −1 in the C700-DBSA sample confirmed that the aromatic C-H groups of DBSA were adsorbed on C700.
The peaks at 2926 cm −1 and 2854 cm −1 became stronger, which indicated that the aliphatic C-H groups of DBSA were adsorbed on P300 [2]. The shape of the adsorbing peak of 1612 cm −1 became wider and the peak intensity increased, which could be ascribed to the adsorption on C=O groups. The appearance of an additional band at 831 cm −1 was the consequence of the interaction of aromatic C-H groups of DBSA with P300. The FTIR spectra of P700-DBSA showed no significant change in comparison to P700, which indicated that the adsorption of DBSA on P700 did not alter the structure. The structural carbon distribution of the biochars and their complexes was calculated according to the 13 C-NMR spectra, and is shown in Table 6. With the increase of the temperature, the contents of aliphatic carbon, heteroaliphatic carbon, and acetal carbon all decreased. At the same time, the contents of aromatic carbon, carboxyl carbon, and carbonyl carbon increased. Poplar leaf biochars had higher contents of aliphatic carbon and carboxyl carbon than corn straw biochars. In Figure 6, after the adsorption of DBSA on P300, the band at 3365 cm −1 shifted to the lower frequency 3333 cm −1 , which suggested the strong interaction formed through the H bond [35]. An increase in the intensity of the band at 1225 cm −1 could also confirm the formation of a H bond [33]. The peaks at 2926 cm −1 and 2854 cm −1 became stronger, which indicated that the aliphatic C-H groups of DBSA were adsorbed on P300 [2]. The shape of the adsorbing peak of 1612 cm −1 became wider and the peak intensity increased, which could be ascribed to the adsorption on C=O groups. The appearance of an additional band at 831 cm −1 was the consequence of the interaction of aromatic C-H groups of DBSA with P300. The FTIR spectra of P700-DBSA showed no significant change in comparison to P700, which indicated that the adsorption of DBSA on P700 did not alter the structure. Figures 7 and 8 are the 13 C-NMR spectra of biochars and biochars-DBSA complexes, respectively. The structural carbon distribution of the biochars and their complexes was calculated according to the 13 C-NMR spectra, and is shown in Table 6. With the increase of the temperature, the contents of aliphatic carbon, heteroaliphatic carbon, and acetal carbon all decreased. At the same time, the contents of aromatic carbon, carboxyl carbon, and carbonyl carbon increased. Poplar leaf biochars had higher contents of aliphatic carbon and carboxyl carbon than corn straw biochars.      For C300, the content of aromatic carbon changed the most, from 35.98% before the adsorption to 42.22% after the adsorption. The change rate was the biggest (17.34%), which suggested that adsorption took place on aromatic carbon. The change rate of the aliphatic carbon of C700 was up to 4190%, and the presence of the long chain polymethylene carbon (28 ppm) implied that adsorption happened on long chain polymethylene carbon [36]. The adsorption mainly happened on carbonyl carbons of poplar leaf biochars due to the biggest change ratios of 78.13% and 77.89% for P300 and P700, respectively. After the adsorption of DBSA, the hydrophobicity of C700, Y300, and Y700 hardly changed.
Organic free radicals in humic acid or biochars have attracted considerable attention because of their potential for the adsorption and degradation of organic contaminants [37,38]. The g values observed for the biochars-DBSA complexes were the same as the g values of original biochars, thus indicating that no additional free radical species were generated [39]. Organic free radical concentrations increased in the interaction products of biochars and DBSA, relative to the original biochars, in the order: P700 > P300 > C300. These results could be the reason for the formation of charge-transfer between the electron donating carbonyl groups of biochars and the electron acceptor benzene ring of DBSA [40]. The enlargement of the line width in the interaction product of P700-DBSA was the consequence of the formation of covalent bonds between DBSA and P700 [39]. The covalent bonds might play a more important role in making the adsorption capacity of P700 higher than that of other biochars.

Conclusions
In this study, biochars from crop straw and poplar leaf have been prepared at 300 °C and 700 °C, respectively. The differences within the pyrolysis temperatures resulted in noticeable changes in the surface morphologies and structural characteristics of biochars derived from different biomass feedstocks. The adsorption kinetics of crop straw and poplar leaf biochars obeyed the pseudo-second order rate model. The study also investigated the adsorption abilities and adsorption mechanisms of DBSA on two different biochars. Isotherm analysis showed that the linear model fit well with the experiment data of C300, and the Langmuir model fit well with the data of C700, P300, and P700. The adsorption mechanisms of DBSA on crop straw biochars included partition, H bonds, and charge-transfer bonds. The adsorption sites were C=O, C-O, aromatic C, aromatic C-H groups, and long chain polymethylene carbon. IR spectra and ESR spectra also confirmed that H bonds, chargetransfer, and covalent bonds were the main adsorption mechanisms between DBSA and poplar leaf biochars. The adsorption mainly took place on the aliphatic C-H, C=O, C-O and aromatic C-H groups. For C300, the content of aromatic carbon changed the most, from 35.98% before the adsorption to 42.22% after the adsorption. The change rate was the biggest (17.34%), which suggested that adsorption took place on aromatic carbon. The change rate of the aliphatic carbon of C700 was up to 4190%, and the presence of the long chain polymethylene carbon (28 ppm) implied that adsorption happened on long chain polymethylene carbon [36]. The adsorption mainly happened on carbonyl carbons of poplar leaf biochars due to the biggest change ratios of 78.13% and 77.89% for P300 and P700, respectively. After the adsorption of DBSA, the hydrophobicity of C700, Y300, and Y700 hardly changed.
Organic free radicals in humic acid or biochars have attracted considerable attention because of their potential for the adsorption and degradation of organic contaminants [37,38]. The g values observed for the biochars-DBSA complexes were the same as the g values of original biochars, thus indicating that no additional free radical species were generated [39]. Organic free radical concentrations increased in the interaction products of biochars and DBSA, relative to the original biochars, in the order: P700 > P300 > C300. These results could be the reason for the formation of charge-transfer between the electron donating carbonyl groups of biochars and the electron acceptor benzene ring of DBSA [40]. The enlargement of the line width in the interaction product of P700-DBSA was the consequence of the formation of covalent bonds between DBSA and P700 [39]. The covalent bonds might play a more important role in making the adsorption capacity of P700 higher than that of other biochars.

Conclusions
In this study, biochars from crop straw and poplar leaf have been prepared at 300 • C and 700 • C, respectively. The differences within the pyrolysis temperatures resulted in noticeable changes in the surface morphologies and structural characteristics of biochars derived from different biomass feedstocks. The adsorption kinetics of crop straw and poplar leaf biochars obeyed the pseudo-second order rate model. The study also investigated the adsorption abilities and adsorption mechanisms of DBSA on two different biochars. Isotherm analysis showed that the linear model fit well with the experiment data of C300, and the Langmuir model fit well with the data of C700, P300, and P700. The adsorption mechanisms of DBSA on crop straw biochars included partition, H bonds, and charge-transfer bonds. The adsorption sites were C=O, C-O, aromatic C, aromatic C-H groups, and long chain polymethylene carbon. IR spectra and ESR spectra also confirmed that H bonds, charge-transfer, and covalent bonds were the main adsorption mechanisms between DBSA and poplar leaf biochars. The adsorption mainly took place on the aliphatic C-H, C=O, C-O and aromatic C-H groups.