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. 2021 Jun 25;6(26):17086–17094. doi: 10.1021/acsomega.1c02214

Enhanced Adsorption of Rhodamine B on Modified Oil-Based Drill Cutting Ash: Characterization, Adsorption Kinetics, and Adsorption Isotherm

Yuqing Zhao †,‡,§, Hang Yang †, Jianfa Sun ∥, Yi Zhang §,*, Shibin Xia †,*
PMCID: PMC8264943  PMID: 34250365

Abstract

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In this paper, phosphoric acid (H3PO4), hydrochloric acid (HCl), and hydrogen peroxide (H2O2) were employed for the modification of oil-based drill cutting ash (OBDCA) for the first time. The adsorption of rhodamine B (RhB) on modified oil-based drill cutting ash (MOBDCA) in an aqueous medium was investigated. H2O2-modified OBDCA had the optimal adsorption efficiency for RhB. The physical and chemical properties of MOBDCA were analyzed using X-ray diffraction (XRD), scanning electron microscopy (SEM), Fourier transform infrared spectroscopy (FTIR), ζ-potential, N2 adsorption–desorption isotherm, and pore size distribution. The effect of the pH value (3–11), reaction time (10–720 min), and initial RhB concentration (10–200 mg/L) on RhB adsorption was discussed. The adsorption kinetics highly fitted with the pseudo-second-order model (R2 > 0.99), which indicated that the adsorption process was dominated by chemisorption. The adsorption isotherm fitted well with the Langmuir and Freundlich models (R2 > 0.97), which indicated the monolayer adsorption process and the heterogeneous adsorption process, respectively. The theoretic adsorption capacity (50 mg/g) for RhB was achieved by H2O2-modified OBDCA. This paper provides a promising method of resource utilization of OBDCA to treat organic pollutants.

Introduction

With the rapid development of industry, more and more industrial wastewater is discharged into the environment without sufficient treatment, resulting in increasingly serious pollution of water resources.1,2 Common pollutants in the water environment include organic dyes, heavy metals, pesticides, antibiotics, and hormone drugs.3−5 Among them, dyes are the main source of water pollution, which are widely used in papermaking, textile, leather, printing, and dyeing industries.6−10 Rhodamine B (RhB), a xanthene-type cationic dye, is commonly used in rubber, paper, and plastic manufacturing industries.11−13 Insufficient treatment for RhB in water bodies could result in environmental pollution and cause harm to human health.14 Therefore, the removal of RhB is of great significance.

The main methods for treating dyes in wastewater include adsorption, flocculation, chemical oxidation, reverse osmosis, photocatalytic degradation, and so on.15−19 Among them, adsorption technology has attracted much attention due to its advantages such as simplicity, eco-friendliness, and recyclability of adsorbents.20,21 Traditional materials used to adsorb dyes usually include zeolite, biological materials, nanomaterials, carbonaceous materials, ion exchange resins, and so on.22−24

Oil-based drill cutting ash (OBDCA) is a solid waste that is produced from the pyrolysis product of oil-based drill cuttings (OBDC). In China, the yield of OBDCA is up to 200 thousand tons, which cannot be fully utilized due to the huge quantity. The main utilization method of OBDCA is as a raw material for brick and cement.25−27 In our previous study, OBDCA was developed as a novel material of environmental remediation for metal polluted soil and water.28,29 However, OBDCA is currently not used in the removal of organic matter due to the poor adsorption efficiency for organic matter. To enhance adsorption for organic matter, appropriate modification of OBDCA should be studied. Acid modifications have been widely used to improve the adsorption capacity of the material for pollutants. The possible reasons are that acid modification could remove soluble salts, introduce new functional groups, increase the pore volume, and enhance the specific surface area for the material.30−32 In this study, three common acids, H3PO4, HCl, and H2O2 were selected to modify OBDCA for improving the adsorption capacity for organic pollutants.

The main aims of this study were (1) to modify OBDCA using three acids; (2) to compare the characterization of modified OBDCA (MOBDCA) and OBDCA; (3) to investigate the effect of the modification method and pH value on RhB removal; and (4) to study the adsorption kinetics and adsorption isotherm of RhB on MOBDCA and OBDCA.

Characterization of OBDCA and MOBDCA

The morphology characterization of OBDCA and MOBDCA was analyzed using a scanning electron microscope (SEM) (Figure 1). OBDCA was an irregular particle with a relatively coarse surface structure, which indicated the presence of impurity on OBDCA. For M1-OBDCA, the morphology of M1-OBDCA had no obvious difference with OBDCA. For M2-OBDCA and M3-OBDCA, the morphology of the two samples was an irregular particle shape with a relatively smooth surface structure, which indicated less impurity on OBDCA. The change of morphology was due to the stronger oxidation and corrosion effect of HCl and H2O2 than H3PO4 for OBDCA modification.

Figure 1.

Figure 1

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SEM photographs of the samples: (a, b) OBDCA, (c, d) M1-OBDCA, (e, f) M1-OBDCA, and (g, h) M1-OBDCA.

The surface functional group of OBDCA and MOBDCA was analyzed using Fourier transform infrared spectroscopy (FTIR; Figure 2). For OBDCA, the obvious band appeared at 3436 cm–1 was attributed to the O–H stretching vibration peak;33 the band appeared at 1625 cm–1 was attributed to O–H bending vibration peak.34 The band appeared at 1087 cm–1 was attributed to the C–N stretching vibration peak.35 The bands appeared at 601–468 cm–1 were ascribed to C–C=O stretching vibration peaks.36 The FTIR spectra of the three modified OBDCA samples had no obvious difference compared with those of OBDCA, which indicated that modification had not changed the functional group for OBDCA.

Figure 2.

Figure 2

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FTIR spectra of MOBDCA and OBDCA.

The composition of OBDCA and MOBDCA was analyzed using X-ray diffraction (XRD) (Figure 3). For OBDCA, many mess peaks appeared in the XRD pattern of OBDCA, which indicated the complex composition of OBDCA. According to the index result, the main diffraction planes observed in OBDCA included quartz (SiO2, PDF 79-1907), barite (BaSO4, PDF 76-0213), and vaterite (CaCO3, PDF 74-1816).37−39 For M1-OBDCA and M3-OBDCA, the XRD pattern had no obvious difference compared with that of OBDCA. For M2-OBDCA, the diffraction planes corresponding to barite and vaterite disappeared. This was due to the reaction of CaCO3 with HCl to form CaCl2, which resulted in the reduction of vaterite in M2-OBDCA. In addition, although BaSO4 could not react with HCl, the solubility of BaSO4 increased in the presence of HCl, which also resulted in the reduction of barite in M2-OBDCA.

Figure 3.

Figure 3

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XRD patterns of MOBDCA and OBDCA.

Figure 4 shows the N2 adsorption/desorption isotherms and pore size distributions of OBDCA and MOBDCA. For OBDCA, according to the Brunauer–Deming–Deming–Teller (BDDT) classification, the N2 adsorption/desorption isotherms of OBDCA were irreversible approximate type II with no obvious hysteresis loop; the data of pore size distribution indicated the non-porous structure of OBDCA with a very small pore volume. For M1-OBDCA and M3-OBDCA, N2 adsorption/desorption isotherms and pore size distributions were similar to those of OBDCA. For M2-OBDCA, the N2 adsorption/desorption isotherms of OBDCA were irreversible approximate type II with an obvious hysteresis loop; despite the relatively high pore volume, the data of pore size distribution still indicated the non-porous structure of M3-OBDCA due to the small total pore volume. According to the result of the BET parameter (Table 1), the order of the surface area and total pore volume was as follows: OBDCA < M3-OBDCA < M1-OBDCA < M2-OBDCA. The highest surface area was obtained for M2-OBDCA due to the reduction of barite, vaterite, and other impurities after HCl modification.

Figure 4.

Figure 4

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BET analysis of MOBDCA and OBDCA: (a) N2 isotherm and (b) pore size distribution.

Table 1. Brunauer–Emmett–Teller (BET) Parameters of MOBDCA and OBDCA.

  BET surface area (m2/g) total volume (cm3/g) average pore diameter (nm)
OBDCA 1.0993 0.0037 13.4
M1-OBDCA 3.8590 0.0093 9.7
M2-OBDCA 14.5641 0.0197 5.2.
M3-OBDCA 1.9371 0.0080 12.6
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The colloidal dispersion stability and potential value under different pH values were analyzed using ζ-potential analysis (Figure 5). The obtained pHpzc values for OBDCA and MOBDCA were all less than 3.0, which indicated the negative charge on the surface of OBDCA and MOBDCA when pH > 3.0.

Figure 5.

Figure 5

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ζ-Potential measurement of OBDCA and MOBDCA under different pH values.

Results and Discussion

Figure 6a shows the effect of the modification method of OBDCA on RhB adsorption. Three modified OBDCA samples had higher adsorption capacity for RhB than OBDCA. The order of the removal rate for RhB was as follows: OBDCA (60.1%) < M2-OBDCA (75.0%) < M1-OBDCA (76.3%) < M3-OBDCA (81.3%). The conclusion was not consistent with the BET surface area of the adsorbent. Especially, M2-OBDCA with the highest BET surface area had little enhanced adsorption capacity compared with OBDCA. This was possible due to the discussion mentioned in XRD patterns. HCl modification could corrode the surface of OBDCA to generate more adsorption sites for RhB adsorption. However, barite, vaterite, and other impurities in OBDCA, which could also adsorb the dye at a certain degree, were also reduced after HCl modification.40−42 The H3PO4 and H2O2 modification could oxidize and corrode the surface of OBDCA with relatively intact retention of barite and vaterite. In addition, among the three MOBDCA, M3-OBDCA had the lowest BET surface area and the optimal adsorption efficiency for RhB, which could indicate that the H2O2 modification could enhance the hydrophilicity and affinity of OBDCA for RhB.43

Figure 6.

Figure 6

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(a) Effect of the modification method of OBDCA on the removal rate of RhB. Experimental conditions: dosage of the adsorbent: 1 g/L, pH: 7, reaction time: 180 min, and initial RhB concentration: 10 mg/L. (b) Effect of the pH value on the removal rate of RhB. Experimental conditions: dosage of the adsorbent: 1 g/L, pH: 3–11, reaction time: 180 min, and initial RhB concentration: 10 mg/L.

Figure 6b shows the effect of pH on RhB adsorption. For the four adsorbents, the pH value had an obvious effect on the removal rate of RhB, and the removal rate increased with increasing pH value. This was because (i) RhB is a weakly basic dye, which has a positive surface charge.44 (ii) According to the result of the ζ-potential analysis of the adsorbent, the surface charge of the adsorbent was negative when pH > 3, while there was a strong electrostatic attraction between the adsorbent and the RhB solution when pH > 3. Therefore, a higher pH value was conducive for RhB adsorption due to the more obvious electrostatic attraction.

Adsorption Kinetics and Adsorption Isotherm

The pseudo-first-order model, pseudo-second-order model, and intraparticle diffusivity model were employed to determine the kinetic mechanism of the adsorption process.45,46 The kinetic plots and the corresponding parameters are shown in Figure 7 and Table 2, respectively. According to the calculated coefficients (R2), the pseudo-second-order kinetic model was more suitable to explain the adsorption process of RhB on the adsorbent, which indicated that the main adsorption process was controlled by chemisorption. The intraparticle diffusivity model was also suitable to fit the adsorption process. As shown in Figure 7c, the intraparticle diffusivity plot was divided into two steps ((I) and (II)). For the first (I) step, the experiment data had a high coefficient and the fitted curve was close to the origin, which indicated that this step was mainly controlled by intraparticle diffusivity.47 For the second (II) step, the experiment data had a low coefficient and the fitted curve was far from the origin, which indicated that this step was mainly controlled by extraparticle diffusivity.

Figure 7.

Figure 7

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(a) Pseudo-first-order, (b) pseudo-second-order, and (c) intraparticle diffusivity model plots. Experimental conditions: dosage of the adsorbent: 1 g/L, pH: 7, reaction time: 10–720 min, and initial RhB concentration: 10 mg/L.

Table 2. Adsorption Kinetic Model Parameters.

pseudo-first-order
  k1 (min–1) qm (mg/g) R2
OBDCA 0.09 ± 0.01 5.7 ± 0.1 0.6434
M1-OBDCA 0.10 ± 0.01 7.1 ± 0.3 0.5446
M2-OBDCA 0.10 ± 0.01 6.9 ± 0.4 0.5391
M3-OBDCA 0.11 ± 0.01 7.5 ± 0.6 0.4644
pseudo-second-order
  qe (mg/g) k2 (g/mg/min) R2
OBDCA 6.0 ± 0.2 0.017 ± 0.001 0.9998
M1-OBDCA 7.8 ± 0.3 0.013 ± 0.001 0.9997
M2-OBDCA 7.6 ± 0.2 0.013 ± 0.001 0.9970
M3-OBDCA 8.3 ± 0.2 0.012 ± 0.001 0.9967
intraparticle diffusivity
  kw (min–1) b R2
OBDCA 0.21 ± 0.01 (I)/0.0082 ± 0.0004(II) 3.3 ± 0.3 (I)/5.9 ± 0.3 (II) 0.9473 (I)/0.4541 (II)
M1-OBDCA 0.26 ± 0.03(I)/0.0043 ± 0.0006(II) 4.3 ± 0.2 (I)/7.6 + 0.5 (II) 0.9805 (I)/0.3683 (II)
M2-OBDCA 0.23 ± 0.03 (I)/0.0027 ± 0.0003(II) 4.2 + 0.3 (I)/7.4 + 0.6 (II) 0.9861 (I)/0.8207 (II)
M3-OBDCA 0.25 ± 0.02(I)/0.0052 ± 0.0004(II) 4.8 + 0.3 (I)/8.1 + 0.7(II) 0.9931 (I)/0.4531 (II)
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The Langmuir and Freundlich models were employed to fit the adsorption isotherm of RhB on the adsorbent.48,49 The isotherm plots and the corresponding parameters are shown in Figure 8 and Table 3, respectively. According to the calculated coefficients (R2), the Langmuir and Freundlich isotherm models were both suitable to explain the adsorption process of RhB on the adsorbent. The parameters kl (<1) and n (<1) indicated the homogeneous, monolayer, and favorable adsorption process. The theoretic adsorption capacity, Qm, was calculated from the Langmuir equation in the following order: OBDCA (18 mg/g) < M2-OBDCA (21 mg/g) < M1-OBDCA (30 mg/g) < M3-OBDCA (50 mg/g).

Figure 8.

Figure 8

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(a) Langmuir and (b) Freundlich model plots. Experimental conditions: dosage of the adsorbent: 1 g/L, pH: 7, reaction time: 180 min, and initial RhB concentration: 10–200 mg/L.

Table 3. Adsorption Isotherm Parameters.

Freundlich
  kf n R2
OBDCA 4.3 ± 0.3 0.27 ± 0.01 0.9880
M1-OBDCA 5.8 ± 0.4 0.29 ± 0.02 0.9869
M2-OBDCA 5.6 ± 0.3 0.25 ± 0.01 0.9858
M3-OBDCA 6.3 ± 0.5 0.39 ± 0.03 0.9902
Langmuir
  kl (L/mg) Qm (mg/g) R2
OBDCA 0.055 ± 0.003 18 ± 1 0.9757
M1-OBDCA 0.061 ± 0.004 30 ± 2 0.9872
M2-OBDCA 0.066 ± 0.002 21 ± 1 0.9822
M3-OBDCA 0.043 ± 0.002 50 ± 3 0.9744
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Comparison with Other Adsorbents for RhB

The adsorption capacity of M3-OBDCA for RhB was compared with other adsorbents (Table 4). The adsorption capacity of M3-OBDCA was not at a high level compared with some adsorbents. Different from other adsorbents, OBDCA is a solid waste and the modification of OBDCA was very low cost. Meanwhile, the use of M3-OBDCA for RhB adsorption achieved waste utilization, which had a certain environmental significance. However, the regeneration of used M3-OBDCA may result in secondary environmental pollution and disproportionate cost consumption. The used M3-OBDCA was considered to be utilized and developed to prepare other materials, such as bricks, cement-based materials, and proppants.25,26,50

Table 4. Comparison with Other Adsorbents for RhB Adsorption.

adsorbent adsorption capacity (mg/g) refs
M3-OBDCA 50.32 this study
TMPTA-G-M 45.64 (51)
ZIF-67/AC 46.2 (52)
E-spun GO/MIL-101(Fe)/PANCMA NFs 10.46 (53)
MgO-FCM-NPs 1106 (54)
NiO/SiO2 nanocomposites 68.0 (55)
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Experimental Section

Materials and Instruments

Materials: OBDC was provided by Agriculture and Forestry Department of Fuling Shale Gas Company. OBDCA was obtained by pyrolysis of OBDC. The pyrolysis conditions were as follows: pyrolysis temperature was 750 °C, pyrolysis time was 45 min, and heating rate was 6 °C/min. OBDCA was ground and sieved through a 200-mesh screen. Phosphoric acid (H3PO4), hydrochloric acid (HCl), rhodamine B (RhB), hydrogen peroxide (H2O2), and (NaOH) were bought from Aladdin Company.

Instruments: An automatic surface area and porosity analyzer (ASAP 2020M) was used to analyze the N2 adsorption isotherms and pore size distribution of the samples. A ζ-potential analyzer (NanoPlus) was used to analyze the ζ-potential of the samples. An X-ray diffractometer (D8 Advance) was used to analyze the X-ray diffraction (XRD) pattern of the samples. A field emission scanning electron microscope (FE-SEM; JSM-IT300) was used to measure the surface morphologies of the samples. A Fourier transform infrared spectrometer (Nexus) was used to analyze the Fourier transform infrared spectroscopy (FTIR) spectrum of the samples.

Modification of OBDCA

H3PO4, HCl, and H2O2 were used for OBDCA modification. In the modification process, 20 g of OBDCA was added into each 1000 mL conical flask with 800 mL of a H3PO4 (30%) solution, 800 mL of a HCl (10%) solution, and 800 mL of a H2O2 (30%) solution, separately. Then, the conical flasks were sealed and shaken in a shaker for 24 h at 25 °C. Modified OBDCA was collected and rinsed using ultrapure water until the pH was neutral. The modified OBDCA was dried using a dryer for 24 h at 120 °C. H3PO4-, HCl-, and H2O2-modified OBDCA were denoted as M1-OBDCA, M2-OBDCA, and M3-OBDCA, respectively.

Adsorption Experiment

Adsorption tests were carried out using batch experiments. OBDCA (0.1 g) was added into 150 mL conical flasks with 100 mL of the RhB solution. H2SO4 (0.1 mol/L) and NaOH (0.1 mol/L) were used to adjust the pH value. Then, the conical flasks were sealed and shaken in a shaker for 3 h at 25 °C. After adsorption, the RhB aqueous solution was filtered using a syringe filter to remove the OBDCA residue. The concentration of RhB in the filtrate was measured using an ultraviolet spectrometer at λmax wavelength of HA (wavelength: 554 nm). The removal rate (%) and unit adsorption quantity (mg/g) of RhB were calculated according to eqs 1 and 2, respectively. All experiments were carried out three times at least.

graphic file with name ao1c02214_m001.jpg 1
graphic file with name ao1c02214_m002.jpg 2

where C0 and Ct are the initial concentration (mg/L) and residue concentration (mg/L) after the adsorption of RhB, respectively; V is the volume of the solution (L); and W is the weight of the dosage of the adsorbent (g).

The adsorption kinetics of RhB on OBDCA was fitted with the pseudo-first-order, pseudo-second-order, and intraparticle diffusivity models (eqs 3–5, respectively).

graphic file with name ao1c02214_m003.jpg 3
graphic file with name ao1c02214_m004.jpg 4
graphic file with name ao1c02214_m005.jpg 5

where Qe and Qt are the adsorption capacities (mg/g) at equilibrium and at time t, respectively. k1 and k2 are the pseudo-first-order and pseudo-second-order constants, respectively.

The adsorption isotherm of RhB on OBDCA was fitted with the Langmuir and Freundlich models (eqs 6 and 7, respectively).

graphic file with name ao1c02214_m006.jpg 6
graphic file with name ao1c02214_m007.jpg 7

where Qm is the theoretic adsorption capacity (mg/g). kl and kf are the Langmuir and Freundlich constants, respectively. kw and b both are intraparticle diffusivity constants.

Conclusions

OBDCA was modified using HCl, H2O2, and H3PO4 to enhance the adsorption capacity for organic pollutants. H2O2-modified OBDCA showed good adsorption performance for RhB adsorption due to enhanced adsorption sites and the presence of barite and vaterite. The result of adsorption isotherms indicated that the adsorption process belonged to heterogeneous adsorption. The result of adsorption kinetics indicated that the adsorption process was dominated by chemisorption and the adsorption rate was controlled by both the intraparticle diffusion stage and the extraparticle diffusivity stage. Although the adsorption capacity of M3-OBDCA for RhB (50 mg/g) was not at a high level compared with other adsorbents, this study achieved the resource utilization of OBDCA for the treatment of organic pollutants at first.

Acknowledgments

The authors sincerely thank the grant funded by the Study on Comprehensive Control of Rocky Desertification and Ecological Service Function Improvement in Karst Peaks (No. 2016YFC0502402) and Fuling Shale Gas Environmental Exploration Technology of National Science and Technology Special Project (Grant No. 2016ZX05060). This work was also financially supported by the National Natural Science Foundation of China (No. 51709254) and Youth Innovation Promotion Association, Chinese Academy of Sciences (No. 2020335)

The authors declare no competing financial interest.

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