Powdered and beaded sawdust materials modified iron (III) oxide

May 05, 2023

Scientific Reports volume 13, Article number: 531 (2023) Cite this article

756 Accesses

4 Citations

Metrics details

The problems of lead and reactive blue 4 (RB4) dye contamination in wastewater are concerns because of their toxicities to aquatic life and water quality, so lead and RB4 dye removals are recommended to remove from wastewater before discharging. Sawdust powder (SP), sawdust powder doped iron (III) oxide-hydroxide (SPF), sawdust beads (SPB), and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB) were synthesized and characterized with various techniques, and their lead or RB4 dye removal efficiencies were investigated by batch experiments, adsorption isotherms, kinetics, and desorption experiments. SPFB demonstrated higher specific surface area (11.020 m2 g−1) and smaller pore size (3.937 nm) than other materials. SP and SPF were irregular shapes with heterogeneous structures whereas SPB and SPFB had spherical shapes with coarse surfaces. Calcium (Ca) and oxygen (O) were found in all materials whereas iron (Fe) was only found in SPF and SPFB. O–H, C–H, C=C, and C–O were detected in all materials. Their lead removal efficiencies of all materials were higher than 82%, and RB4 dye removal efficiencies of SPB and SPFB were higher than 87%. Therefore, adding iron (III) oxide-hydroxide and changing material form helped to improve material efficiencies for lead or RB4 dye adsorption. SP and SPB corresponded to Langmuir model related to a physical adsorption process whereas SPF and SPFB corresponded to the Freundlich model correlated to a chemisorption process. All materials corresponded to a pseudo-second-order kinetic model relating to the chemical adsorption process. All materials could be reused more than 5 cycles with high lead removal of 63%, and SPB and SPFB also could be reused more than 5 cycles for high RB4 dye removal of 72%. Therefore, SPFB was a potential material to apply for lead or RB4 dye removal in industrial applications.

Water pollutions from heavy metals or dye contaminations create many problems with water quality, toxicity to aquatic life and the environment, a decrease of oxygen in water sources, an obstacle to sunlight for photosynthesis, and persistent, accumulation, and transport through the food chain. In addition, they also create many human health effects of dysfunctions in human systems such as the brain, blood, reproduction, digestive, and respiratory and cause cancers1. Especially, lead (Pb) is a toxic heavy metal with concern its toxicity with persistent and bioaccumulation. A reactive blue 4 (RB4) dye is popularly used in the textile industry because it offers long-lasting color in the fabric. However, if it is released into the environment without treatment, it affects aquatic life and the environment as mentioned above. The sources of releasing lead or RB4 dye are various industries of battery, electronic, paint, dye, plastic, and textile using them in their manufacturing processes2,3, so their wastewater might consist of lead or RB4 dye. As a result, wastewater with lead or dye contamination is required for a treatment to be below water quality standards for safety purposes.

Many methods of chemical precipitation, coagulation-flocculation, electrochemical, ion exchange, and reverse osmosis are used for eliminating heavy metals or dyes in wastewater; however, they have limitations of incompletely heavy metal removals, complicated operations with expensive costs including creating toxic sludges with requiring disposals4. As a result, many studies attempted to find an alternative method with an effective and environmentally friendly instead of them. An adsorption method is a good method to solve the above problems because this method offers high heavy metal and dye removals, suitable cost, simple operation, and creating low sludge volume5. In addition, various available choices of adsorbents of this method are a good option for a user with considering which adsorbent is good for removing a target pollutant by using the considering criteria of available adsorbent in that area, water quality after treatment, and budget. Several adsorbents are used for eliminating specific a target metal or dye ion in wastewater such as activated carbon, chitosan, zeolite, fruit peels, and wastes of agriculture, food, and industrial; however, this study will focus on various wastes as low-cost adsorbents used for improving water quality along with reducing waste volumes in terms of waste management. The elimination of heavy metals or dyes from wastewater from various wastes is demonstrated in Table 1. Among those adsorbents, sawdust is a good offer because it has good chemical properties of cellulose, hemicellulose, lignin, pectin, hydroxyl, and carboxyl groups for good lead or RB4 dye adsorption in wastewater. Furthermore, using sawdust can reduce a huge of sawmill factory waste and help to manage the problem of waste disposal along with improving water quality by using sawdust as an adsorbent material. Although sawdust has good chemical properties for removing lead or RB4 dye, the material improvement method needs to study for increasing lead or RB4 dye removal efficiencies in case of high-strength lead or RB4 dye concentration in industrial applications.

For material modifications, many previous studies have been reported for using a variety of metal oxides of iron (II or III) oxide (Fe4O3 or Fe2O3), zinc oxide (ZnO), titanium dioxide (TiO2), aluminum oxide (Al2O3), tin (IV) oxide (SnO2), and magnesium oxide (MgO) to increase surface area and pore volume of adsorbents offering to increase lead or RB4 dye removal efficiency6,7,8. The modified materials of sugarcane bagasse with Fe2O3, sawdust with ZnO, and lemon peels with iron (III) oxide-hydroxide have been used for lead removal8,9,10, and the modifications of rice bran with SnO2/Fe3O4, bagasse with zinc oxide, and lemon peels beads with iron (III) oxide-hydroxide have been applied for removing RB4 dye11,12,13. Moreover, the stability of the material is another point for applying industrial application, so the changing of material form from a powder form to a bead form in many studies has also been reported with supporting the increase of heavy metal or dye removal efficiencies6,7,8,12,13,14. Therefore, this study attempts to synthesize sawdust materials modified with iron (III) oxide-hydroxide in powder and bead materials, compare their lead or RB4 dye removal efficiencies through batch experiments, and verify whether adding metal oxide or changing form helped to improve a material efficiency for lead or RB4 adsorption.

The study aimed to synthesize four types of adsorbent materials which were sawdust powder (SP), sawdust powder doped iron (III) oxide-hydroxide (SPF), sawdust beads (SPB), and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB). Several characterized techniques of Brunauer–Emmett–Teller (BET), field emission scanning electron microscopy and focus ion beam (FESEM-FIB) with energy dispersive X-ray spectrometer (EDX), and Fourier transform infrared spectroscopy (FT-IR) were used to investigate their specific surface area, pore volume, pore size, surface morphologies, chemical compositions, and chemical functional groups. Lead or RB4 dye removal efficiencies of SP, SPF, SPB, and SPFB were examined by batch experiments with varying doses, contact time, temperature, pH, and concentration. Moreover, linear and nonlinear adsorption isotherms of Langmuir, Freundlich, Temkin, and Dubinin–Radushkevich models and kinetics of pseudo-first-kinetic, pseudo-second-kinetic, Elovich, and intraparticle diffusion models were used for investigating their lead or RB4 dye adsorption patterns and mechanisms. Finally, the desorption experiments were also investigated for confirming the reusability of sawdust materials for lead or RB4 dye adsorption.

The physical characteristics of sawdust powder (SP), sawdust powder doped iron (III) oxide-hydroxide (SPF), sawdust beads (SPB), and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB) are demonstrated in Fig. 1a–d. SP had light brown color powder whereas SPF had brown color powder shown in Fig. 1a,b. SPF had brown color beads while SPFB had dark brown color beads demonstrated in Fig. 1c,d.

The physical characteristics of (a) sawdust powder (SP), (b) sawdust powder doped iron (III) oxide-hydroxide (SPF), (c) sawdust beads (SPB), and (d) sawdust powder doped iron (III) oxide-hydroxide beads (SPFB).

The specific surface area, pore volume, and pore diameter size of sawdust powder (SP), sawdust powder doped iron (III) oxide-hydroxide (SPF), sawdust beads (SPB), and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB) determined by the Brunauer–Emmet and Teller technique (BET) with N2 adsorption–desorption isotherm at 77.3 K and degas temperature of 80 °C for 6 h, and the results of specific surface area and pore volume by Brunauer–Emmett–Teller (BET) and pore size by Barrett–Joyner–Halenda (BJH) method are reported in Table 2.

For the specific surface area of SP, SPF, SPB, and SPFB, they were 0.328, 1.551, 1.960, and 11.020 m2 g−1, respectively which SPFB demonstrated the highest specific surface area than other materials. In addition, their pore volumes were 0.075, 0.356, 0.250, and 2.532 cm3 g−1, respectively, and their pore diameter sizes were 4.256, 3.940, 4.068, and 3.937 nm, respectively. As a result, the addition of iron (III) oxide-hydroxide into sawdust materials (SPF and SPFB) increased the specific surface area and pore volume while the pore diameter size was decreased. In addition, all three parameters increased from changing material form from SP to SPB. Since their pore size was in a range of 2–50 nm, they were classified as mesoporous by the classification of International Union of Pure and Applied Chemistry (IUPAC)35.

For the BET comparison, SP had a lower specific surface area than all studies reported in Table 2 whereas SPF, SPB, and SPFB had higher values than the studies of Chen et al. and Houshangi et al.29,34. The studies of Chen et al. and Houshangi et al. had been reported that the modifications of sawdust materials by sodium hydroxide (NaOH) or triethanolamine (C6H15NO3) or iron dioxide (Fe2O4) helped to increase specific surface area similar to this study29,34.

The surface morphologies of sawdust powder (SP), sawdust powder doped iron (III) oxide-hydroxide (SPF), sawdust beads (SPB), and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB) by FESEM-FIB analysis at 500 × magnification with 400 µm for a surface and at 100 × magnification with 1 mm for a bead illustrated in Fig. 2a–f. SP and SPF were irregular shapes with heterogeneous fiber structures demonstrated in Fig. 2a,b similar reported of sawdust morphologies by other studies36,37. For SPB, it had a spherical shape with a coarse surface at 100 × magnification with 1 mm shown in Fig. 2c, and its surface was a rough surface when zoomed at 500 × magnification with 400 µm demonstrated in Fig. 2d. Finally, SPFB had a spherical shape with a coarse surface at 100 × magnification of 1 mm shown in Fig. 2e, and its surface was an irregular shape with the heterogenous surface when zoomed at 500 × magnification with 400 µm illustrated in Fig. 2f.

The surface morphologies of (a) sawdust powder (SP), (b) sawdust powder doped iron (III) oxide-hydroxide (SPF), (c,d) sawdust beads (SPB), and (e,f) sawdust powder doped iron (III) oxide-hydroxide beads (SPFB).

The chemical compositions of sawdust powder (SP), sawdust powder doped iron (III) oxide-hydroxide (SPF), sawdust beads (SPB), and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB) were analyzed by using EDX analysis represented in Table 3, and the elemental mapping of SP, SPF, SPB, and SPFB demonstrated in Fig. 3a–d which showed the dispersions of chemical elements of each material on the surface. Two main chemical components of carbon (C) and oxygen (O) were found in all materials while copper (Cu) was only found in powder materials of SP and SPF. For calcium (Ca), it was detected in SPB and SPFB. For sodium (Na) and chloride (Cl), they were observed in all materials except SP. In addition, iron (Fe) was found in the materials with the addition of iron (III) oxide-hydroxide which were SPF and SPFB to confirm the successful adding Fe into SP and SPB. For SP and SPF, the mass percentages by weight of C and O were decreased when iron (III) oxide-hydroxide was added to SP whereas Cu was increased. Moreover, Na, Cl, and Fe were detected in SPF which might be from using chemicals in a process of adding iron (III) oxide-hydroxide by ferric chloride hexahydrate (FeCl3.6H2O) and sodium hydroxide (NaOH) for synthesizing SPF. For SP and SPB, the mass percentage by weight of C was deceased while O was increased after changing the material to a bead form. In addition, the mass percentages by weight of Ca, Na, and Cl were also detected in SPB by using sodium alginate (NaC6H7O6) and calcium chloride (CaCl2) in a bead formation. For SPF and SPFB, the mass percentages by weight of C, O, and Na were decreased. While the mass percentages by weight of Ca, Cl, and Fe were increased when SPF was changed to a bead form. The increases of Ca and Cl might be from using chemicals of CaCl2 in a process of a bead formation similar to SPB. Therefore, the addition of iron (III) oxide-hydroxide and the changing material form affected the increases of Ca, Na, Cl, and Fe contents in sawdust materials.

The elemental mapping of (a) sawdust powder (SP), (b) sawdust powder doped iron (III) oxide-hydroxide (SPF), (c) sawdust beads (SPB), and (d) sawdust powder doped iron (III) oxide-hydroxide beads (SPFB) on the surface.

The chemical functional groups of sawdust powder (SP), sawdust powder doped iron (III) oxide-hydroxide (SPF), sawdust beads (SPB), and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB) were examined by FT-IR analysis, and their FT-IR spectra are demonstrated in Fig. 4a–d. Four main function groups of O–H, C–H, C=C, and C–O were detected in all materials. In addition, the carboxyl group of sodium alginate (–COOH) was found in bead materials (SPB and SPFB)38, and Fe–O was observed in materials with adding iron (III) oxide-hydroxide (SPF and SPFB)39. O–H represented the stretching of hydroxyl, alcohol, and phenolic groups of cellulose fiber, lignin, and pectin, and C–H demonstrated the stretching of a methyl group (–CH2) in cellulose and hemicellulose40. C=C referred to the stretching of aromatic rings corresponding to the lignin, and C–O was the stretching of alcohol and carboxylic acid of lignin and hemicellulose41. For SP, it detected the stretching of O–H at 3322.83 cm−1, stretching of C–H at 2918.28 cm−1, stretching of C=C at 1666.59 cm−1, and stretching of C–O at 1245.34 and 1030.31 cm−1 illustrated in Fig. 4a. For SPF, it observed the stretching of O–H at 3325.99 cm−1, stretching of C–H at 2916.52 cm−1, C=C at 1664.48 cm−1, stretching of C–O at 1262.29 and 1028.88 cm−1, and Fe–O at 847.36 cm−1 shown in Fig. 4b. For SPB, it identified the stretching of O–H at 3323.08 cm−1, C–H at 2910.48 cm−1, C=C at 1664.90 cm−1, stretching of C–O at 1249.35 and 1021.42 cm−1, and –COOH at 1419.56 cm−1 shown in Fig. 4c. For SPFB, it found the stretching of O–H at 3323.68 cm−1, stretching of C–H at 2919.56 cm−1, C=C at 1664.33 cm−1, stretching of C–O at 1262.71 and 1024.87 cm−1, –COOH at 1421.49 cm−1, and Fe–O at 813.34 cm−1 shown in Fig. 4d.

FT-IR spectra of (a) sawdust powder (SP), (b) sawdust powder doped iron (III) oxide-hydroxide (SPF), (c) sawdust beads (SPB), and (d) sawdust powder doped iron (III) oxide-hydroxide beads (SPFB).

For lead removal, five different doses from 0.5 to 3 g were used for investigating the dose effect of lead adsorption by sawdust powder (SP), sawdust powder doped iron (III) oxide-hydroxide (SPF), sawdust beads (SPB), and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB), and the results are demonstrated in Fig. 5a. The control condition was the lead concentration of 50 mg L−1, a sample volume of 200 mL, a contact time of 6 h, pH 5, a temperature of 25 °C, and a shaking speed of 200 rpm. Lead removal efficiencies of all materials were increased with the increase of material dose which might be from the increase of active sites of materials7. Their highest lead removal efficiencies were 85.12%, 96.11%, 89.57%, and 100% at 2 g, 1 g, 1.5 g, and 0.5 g for SP, SPF, SPB, and SPFB, respectively. Therefore, they were optimum doses of sawdust materials that were used for studying the contact time effect.

Batch experiments for lead and RB4 dye removals on the effects of (a,b) dose, (c,d) contact time, (f) temperature, (e,h) pH, and (g,i) concentration of sawdust powder (SP), sawdust powder doped iron (III) oxide-hydroxide (SPF), sawdust beads (SPB), and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB).

For RB4 dye removal, six different doses from 0.5 to 3 g were used for investigating the dose effect of RB4 dye adsorption by sawdust beads (SPB) and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB), and the results are demonstrated in Fig. 5b. The control condition was the RB4 dye concentration of 50 mg L−1, a sample volume of 200 mL, a contact time of 12 h, pH 7, a temperature of 60 °C, and a shaking speed of 150 rpm. RB4 dye removal efficiencies of all materials were increased with the increase of material dose which might be from the increase of active sites of materials12. The highest RB4 dye removal efficiency of SPB was found at 3 g with 89.65% while the highest RB4 dye removal efficiency of SPFB was found at 1.5 g with 94.10%. Therefore, they were the optimum dosages of sawdust materials that were used for studying the contact time effect.

For lead removal, the different contact times from 1 to 6 h were used for studying the contact time effect on lead adsorptions by sawdust powder (SP), sawdust powder doped iron (III) oxide-hydroxide (SPF), sawdust beads (SPB), and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB), and the results are demonstrated in Fig. 5c. The control condition was the lead concentration of 50 mg L−1, a sample volume of 200 mL, pH 5, a temperature of 25 °C, a shaking speed of 200 rpm, and the optimum dose of 2 g (SP) or 1 g (SPF) or 1.5 g (SPB) or 0.5 g (SPFB). Lead removal efficiencies of all materials were increased with the increase of contact time similar to the dose effect. Their highest lead removal efficiencies were 86.74%, 97.58%, 90.12%, and 100% at 5 h, 3 h, 4 h, and 2 h for SP, SPF, SPB, and SPFB, respectively. Therefore, they were the optimum contact time of sawdust materials that were used for studying the pH effect.

For RB4 dye removal, the different contact times from 3 to 18 h were used for studying the contact time effect on RB4 dye adsorptions by sawdust beads (SPB) and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB), and the results are demonstrated in Fig. 5d. The control condition was the RB4 dye concentration of 50 mg L−1, a sample volume of 200 mL, pH 7, a temperature of 60 °C, a shaking speed of 150 rpm, and the optimum dose 3 g (SPB) or 1.5 g (SPFB). RB4 dye removal efficiencies of all materials were increased with the increase of contact time similar to the dose effect. Their highest RB4 dye removal efficiencies were found at 12 h with 88.15% for SPB and 9 h with 93.76% for SPFB. Therefore, they were the optimum contact times of sawdust materials that were used for studying the pH effect.

Only dye removal investigated the effect of temperature whether the changing temperature affects RB4 dye removal by sawdust beads (SPB) and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB). The different temperatures from 40 to 80 °C were used for studying the temperature effect on RB4 dye adsorptions by sawdust materials, and the results are demonstrated in Fig. 5f. The control condition was the RB4 dye concentration of 50 mg L−1, a sample volume of 200 mL, pH 7, a shaking speed of 150 rpm, and the optimum dose of 3 g (SPB) or 1.5 g (SPFB) and contact time of 12 h (SPB) or 9 h (SPFB). RB4 dye removal efficiencies of all materials were decreased with the increase of temperature, and the highest RB4 dye removal efficiencies were at a temperature of 40 °C with 87.78% for SPB and 30 °C with 95.12% for SPFB. Therefore, they were the optimum temperatures of sawdust materials that were used for studying the pH effect.

For lead removal, the effect of pH was studied by varying pH values of 1, 3, 5, 7, 9, and 11 represented the acid, neutral, and base conditions on lead adsorptions by sawdust powder (SP), sawdust powder doped iron (III) oxide-hydroxide (SPF), sawdust beads (SPB), and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB), and the results are demonstrated in Fig. 5e. The control condition was the lead concentration of 50 mg L−1, a sample volume of 200 mL, a temperature of 25 °C, a shaking speed of 200 rpm, and the optimum dose of 2 g (SP) or 1 g (SPF) or 1.5 g (SPB) or 0.5 g (SPFB) and contact time of 5 h (SP) or 3 h (SPF) or 4 h (SPB) or 2 h (SPFB). Lead removal efficiencies of all materials were increased with the increase of pH values from 1 to 7, then they were decreased. Their highest lead removal efficiencies of all materials were found at pH 5 with lead removal at 86.21%, 98.15%, 91.45%, and 100% for SP, SPF, SPB, and SPFB, respectively which corresponded to other previous studies reported the highest lead removal efficiency at pH > 47,8,18. Therefore, pH 5 was the optimum pH of sawdust materials that were used for studying the concentration effect.

For RB4 dye removal, the effect of pH was studied by varying pH values of 1, 3, 5, 7, 9, and 11 represented the acid, neutral, and base conditions on RB4 dye adsorptions by sawdust beads (SPB) and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB), and the results are demonstrated in Fig. 5h. The control condition was the RB4 dye concentration of 50 mg L−1, a sample volume of 200 mL, a shaking speed of 150 rpm, and the optimum dose 3 g (SPB) or 1.5 g (SPFB), contact time of 12 h (SPB) or 9 h (SPFB), and temperature of 40 °C (SPB) or 30 °C (SPFB). RB4 dye removal efficiencies of all materials were increased with the increase of pH values from 1 to 3, then they were decreased. Their highest RB4 dye removal efficiencies of all materials were found at pH 3 with RB4 dye removal at 89.12% and 95.96% for SPB and SPFB which corresponded to other previous studies reported the highest RB4 dye removal efficiency found at acidic conditions6,14. Therefore, pH 3 was the optimum pH of sawdust materials that were used for studying the concentration effect.

For lead removal, lead concentrations of 30–70 mg L−1 were used to investigate the concentration effect on lead adsorptions by sawdust powder (SP), sawdust powder doped iron (III) oxide-hydroxide (SPF), sawdust beads (SPB), and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB), and the results are demonstrated in Fig. 5g. The control condition was a sample volume of 200 mL, a temperature of 25 °C, a shaking speed of 200 rpm, and the optimum dose of 2 g (SP) or 1 g (SPF) or 1.5 g (SPB) or 0.5 g (SPFB) and contact time of 5 h (SP) or 3 h (SPF) or 4 h (SPB) or 2 h (SPFB), and pH of 5. Lead removal efficiencies of all materials were decreased with the increase of concentration because of the decreasing available active sites for adsorbing lead ions7. Lead removal efficiencies from 30 to 70 mg L−1 of SP, SPF, SPB, and SPFB were 78.82–84.56%, 92.57–98.12%, 85.41–91.39%, and 97.15–100%, respectively. For the lead concentration of 50 mg L−1, lead removal efficiencies of SP, SPF, SPB, and SPFB were 82.14%, 95.06%, 88.45%, and 100%, respectively, and SPFB demonstrated the highest lead removal efficiency of other materials.

For RB4 dye removal, RB4 dye concentrations of 30–70 mg L−1 were used to investigate the concentration effect on RB4 dye adsorptions by sawdust beads (SPB) and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB), and the results are demonstrated in Fig. 5i. The control condition was a sample volume of 150 mL, and the optimum dose of 3 g (SPB) or 1.5 g (SPFB), contact time of 12 h (SPB) or 9 h (SPFB), temperature of 40 °C (SPB) or 30 °C (SPFB), and pH of 3. RB4 dye removal efficiencies of all materials were decreased with the increase of concentration because RB4 dye ions were more than the available active sites of sawdust materials similar to the report by other studies12,14. RB4 dye removal efficiencies from 30 to 70 mg L−1 of SPB and SPFB were 84.35–89.65% and 88.43–96.12%. For the RB4 dye concentration of 50 mg L−1, RB4 dye removal efficiencies of SPB and SPFB were 87.96% and 92.84%, and SPFB demonstrated the highest RB4 dye removal efficiency of other materials.

In conclusion of lead removal, 2 g, 5 h, pH 5, 50 mg L−1, 1 g, 3 h, pH 5, 50 mg L−1, 1.5 g, 4 h, pH 5, 50 mg L−1, and 0.5 g, 2 h, pH 5, 50 mg L−1 were the optimum conditions in dose, contact time, pH, and concentration of SP, SPF, SPB, and SPFB, respectively, and they could be arranged in order from high to low of SPFB > SPF > SPB > SP. As a result, both changing material form and adding iron (III) oxide-hydroxide helped to improve material efficiency for lead adsorption.

In conclusion of RB4 dye removal, 3 g, 12 h, 40 °C, pH 3, 50 mg L−1 and 1.5 g, 9 h, 30 °C, pH 3, 50 mg L−1 were the optimum conditions in dose, contact time, temperature, pH, and concentration of SPB and SPFB, respectively. As a result, the changing material form and adding iron (III) oxide-hydroxide helped to improve material efficiency for RB4 dye adsorption than only changing material form.

Therefore, sawdust materials could be removed both lead and RB4 dye in aqueous solutions, and SPFB demonstrated the highest removal efficiency on both pollutants. Finally, SPFB was recommended to be applied for lead or RB4 dye removal in the wastewater treatment system in the future.

The adsorption patterns of sawdust powder (SP), sawdust powder doped iron (III) oxide-hydroxide (SPF), sawdust beads (SPB), and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB) for lead adsorption and sawdust beads (SPB) and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB) for RB4 dye adsorption were investigated through various adsorption isotherms of Langmuir, Freundlich, Temkin, and Dubinin–Radushkevich models in both linear and nonlinear models. For linear models, Langmuir, Freundlich, Temkin, and Dubinin–Radushkevich isotherms were plotted by Ce/qe versus Ce, log qe versus log Ce, qe versus ln Ce, and ln qe versus ε2, respectively. For nonlinear models, all isotherms were plotted by Ce versus qe. The plotting graphs of lead and RB4 dye adsorption demonstrated in Figs. 6a–h and 7a–f, respectively, and their isotherm parameters were illustrated in Tables 4 and 5, respectively. Generally, the best-fit isotherm model for explaining the adsorption pattern of material is chosen from the high regression value (R2) which is close to 112.

Graphs of (a) linear Langmuir, (b) linear Freundlich, (c) linear Temkin, (d) linear Dubinin–Radushkevich, and (e–h) nonlinear adsorption isotherms of sawdust powder (SP), sawdust powder doped iron (III) oxide-hydroxide (SPF), sawdust beads (SPB), and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB) for lead adsorptions.

Graphs of (a) linear Langmuir, (b) linear Freundlich, (c) linear Temkin, (d) linear Dubinin–Radushkevich, and (e,f) nonlinear adsorption isotherms of sawdust beads (SPB), and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB) for RB4 dye adsorptions.

For lead adsorption, the adsorption patterns of SP and SPB corresponded to Langmuir isotherm with relating to a physical adsorption because their R2 values in both linear and nonlinear had higher than Freundlich, Temkin, and Dubinin–Radushkevich models. Therefore, Langmuir parameters of qm and KL values were used for explaining the adsorption pattern. Since qm and KL values of SPB were higher than SP, SPB had possibly higher lead removal efficiency with a high adsorption rate than SP correlated to the results of the batch experiment. For SPF and SPFB, their adsorption patterns corresponded to Freundlich isotherm with relating to a physiochemical adsorption because their R2 values in both linear and nonlinear had higher than Langmuir, Temkin, and Dubinin–Radushkevich models. Therefore, Freundlich parameters of KF and 1/n values were used for explaining the adsorption pattern. KF refers Freundlich adsorption constant which SPFB represented the highest KF value, so SPFB had a higher adsorption rate than SPF. For a 1/n value, it is a constant depiction of the adsorption intensity which 0 < 1/n < 1 means the favorable adsorption isotherm, so both materials were favorable adsorption since their 1/n values in this range.

For RB4 dye adsorption, the adsorption pattern of SPB corresponded to Langmuir model relating to a physical adsorption whereas the adsorption pattern of SPFB corresponded to the Freundlich model correlated to a physicochemical adsorption from choosing the highest R2 value isotherm or closely to 1. These results corresponded to lead adsorption patterns that Langmuir and Freundlich isotherms were best-fitted models for explaining lead adsorption patterns of SPB and SPFB. Therefore, both lead and RB4 dye adsorption patterns of SPB and SPFB were physical and physicochemical adsorption processes, respectively.

Moreover, the results of both linear and nonlinear Langmuir, Freundlich, Temkin, and Dubinin–Radushkevich models of all sawdust materials were agreed with each other, so the plotting of both linear and nonlinear isotherm models were also recommended for correct data translations42,43,44.

Finally, the comparison of the maximum adsorption capacity (qm) value for lead and RB4 dye adsorptions by various adsorbents is illustrated in Table 6. For the comparison of lead removal, all sawdust materials in this study had higher qm values than qm values from Picea smithiana sawdust, sawdust-based cellulose nanocrystals, lemon peels, pomelo peels, and onion peels. In addition, SPFB had a higher qm value than all studies in Table 6 except the studies of Hajam et al. (Dibetou sawdust activated by HNO3 and NaOH), Niu et al. (pine sawdust biochar modified with Mn-Zn ferrite), Aigbe and Kavaz (sawdust modified with zinc oxide), Liu et al. (sugarcane bagasse modified with Fe3O4), Zhao et al. (corncob biochar modified with CuFe2O4), Kang et al. (cassava stalks modified with Fe3O4), and Ahmadi et al. (melon peel). For the comparison of RB4 dye removal, both SPB and SPFB had higher qm values than qm values from bagasse, bagasse fly ash, and lemon peels demonstrated in Table 6. Therefore, all sawdust materials in this study were highly efficient materials for lead and RB4 dye adsorptions, and they are potential materials for application in industrial applications in the future, especially SPFB.

The adsorption rates and mechanisms of lead adsorption by sawdust powder (SP), sawdust powder doped iron (III) oxide-hydroxide (SPF), sawdust beads (SPB), and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB) and RB4 dye adsorption by sawdust beads (SPB) and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB) were investigated through various the adsorption kinetics of pseudo-first-order kinetic model, pseudo-second-order kinetic model, Elovich model, and intraparticle diffusion in both linear and nonlinear models. For linear models, they were plotted by ln (qe − qt) versus time (t), t/qt versus time (t), qt versus ln t, and qt versus time (t0.5) for pseudo-first-order kinetic, pseudo-second-order kinetic, Elovich, and intraparticle diffusion models, respectively. For nonlinear models, they were plotted by qt versus time (t). The plotting graphs of lead and RB4 dye adsorptions illustrated in Figs. 8a–h and 9a–f, respectively, and their adsorption kinetic parameters were demonstrated in Tables 7 and 8, respectively. Generally, the best-fit isotherm model for explaining the adsorption rate and mechanism of material is chosen from the high regression value (R2) which is close to 112.

Graphs of (a) linear pseudo-first-order, (b) linear pseudo-second-order, (c) linear Elovich model (d) linear intraparticle diffusion, and (e–h) nonlinear kinetic models of sawdust powder (SP), sawdust powder doped iron (III) oxide-hydroxide (SPF), sawdust beads (SPB), and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB) for lead adsorptions.

Graphs of (a) linear pseudo-first-order, (b) linear pseudo-second-order, (c) linear Elovich model (d) linear intraparticle diffusion, and (e,f) nonlinear kinetic models of sawdust beads (SPB) and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB) for RB4 dye adsorptions.

For lead adsorption, the adsorption rate and mechanism of sawdust materials corresponded to a pseudo-second-order kinetic model with relating to the chemisorption process because their R2 values in both linear and nonlinear pseudo-second-order kinetic models were higher than pseudo-first-order kinetic, Elovich, and intraparticle diffusion models. Therefore, the adsorption kinetic parameters of qe and k2 were used for explaining the adsorption rate and mechanism. Their adsorption capacities (qe) of a pseudo-second-order kinetic model were arranged in order from high to low of SPFB > SPF > SPB > SP correlated to the results of batch experiments and adsorption isotherm. For a k2 value, it is the pseudo-second-order kinetic rate constant in which SPFB demonstrated the highest value than other adsorbents. As a result, SPFB had higher lead adsorption with a fast reaction than other materials.

For RB4 dye adsorption, the adsorption rate and mechanism of SPB and SPFB corresponded to a pseudo-second-order kinetic model similar to lead adsorption. In addition, qe and k2 values of SPFB had also higher than SPB, so SPFB had higher RB4 dye adsorption than SPB corresponding to lead adsorption of SPB and SPFB. Therefore, both lead and RB4 dye adsorption rates and mechanisms of SPB and SPFB were explained by a physicochemical adsorption process.

Finally, the results of both linear and nonlinear pseudo-first-order, pseudo-second-order kinetic, Elovich, and intraparticle diffusion models of all sawdust materials were consistent with each other, so the plotting graphs of both linear and nonlinear kinetic models were also recommended for protecting mistake data translations42,43,44.

The desorption experiments were used to investigate the feasibility of the reuse of sawdust powder (SP), sawdust powder doped iron (III) oxide-hydroxide (SPF), sawdust beads (SPB), and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB) because this is a necessary point to estimate the cost and economic feasibility of industrial applications.

For Lead adsorption, SP, SPF, SPB, and SPFB for 5 cycles of adsorption–desorption were applied to confirm their abilities, and their results are illustrated in Fig. 10a. For SP, it could be reused in 5 cycles with high adsorption and desorption in ranges of 63.33–82.16% and 60.54–81.76%, respectively which adsorption and desorption were decreased by approximately 19% and 21%, respectively. For SPF, it also confirmed to be reusability in 5 cycles with high adsorption and desorption in ranges of 81.83–95.23% and 78.30–94.93%, respectively which adsorption and desorption were decreased by approximately 13% and 17%, respectively. For SPB, it could be reused in 5 cycles with high adsorption and desorption in ranges of 71.58–88.62% and 68.33–88.27%, respectively which adsorption and desorption were decreased by approximately 17% and 20%, respectively. For SPFB, it also confirmed to be reusability in 5 cycles with high adsorption and desorption in ranges of 89.45–100% and 86.33–99.75%, respectively which adsorption and desorption were decreased by approximately 11% and 13%, respectively. Therefore, sawdust materials are potential materials for lead adsorption with the reusability of more than 5 cycles by more than 63%, and they can be further applied to industrial applications.

The desorption experiments of (a) sawdust powder (SP), sawdust powder doped iron (III) oxide-hydroxide (SPF), sawdust beads (SPB), and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB) for lead removal and (b) sawdust beads (SPB) and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB) for RB4 dye removal.

For RB4 dye adsorption, SPB and SPFB for 5 cycles of adsorption–desorption were applied to confirm their abilities, and their results are illustrated in Fig. 10b. For SPB, it could be reused in 5 cycles with high adsorption and desorption in ranges of 72.45–87.84% and 69.36–88.09%, respectively which adsorption and desorption were decreased by approximately 15% and 19%, respectively. For SPFB, it also confirmed to be reusability in 5 cycles with high adsorption and desorption in ranges of 82.85–92.63% and 80.15–92.43%, respectively which adsorption and desorption were decreased by approximately 10% and 12%, respectively. Therefore, SPB and SPFB are potential materials for RB4 dye removal with the reusability of more than 5 cycles by more than 72%, and they can be applied to industrial applications in the future.

The possible mechanisms of lead and RB4 dye adsorptions on sawdust materials are demonstrated in Fig. 11a,b. For lead adsorption, the cellulose, hemicellulose, pectin, lignin, a hydroxyl group (–OH), methyl groups (C–H), aromatic ring represented lignin (C=C), and alcohol and carboxylic acid of lignin and hemicellulose (C–H) were the main structure and chemical functions groups of sawdust materials. The carboxyl group (–COOH) was also demonstrated in sawdust beads (SPB and SPFB) by forming the complex compound between SP or SPF with sodium alginate. In addition, the complex compound between the surface of SPF or SPFB and iron (III) oxide-hydroxide was formed to be SP∙Fe(OH)3 or SPB∙Fe(OH)3 by a process of electron sharing with hydroxyl groups of sawdust. Therefore, the possible mechanism of lead adsorption by sawdust materials might occur from donating a proton (H+) from carboxyl groups (–COOH) or hydroxyl groups (–OH) or SP∙Fe(OH)3 or SPB∙Fe(OH)3 of main chemical compounds or complex compounds to be –COO or –O or FeO(OH)2 for capturing lead (II) ions (Pb2+) by instead of H+ from a process of electrostatic interactions64 shown in Fig. 11a.

Possible mechanisms of (a) sawdust powder (SP), sawdust powder doped iron (III) oxide-hydroxide (SPF), sawdust beads (SPB), and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB) for lead adsorption and (b) sawdust beads (SPB) and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB) for RB4 dye adsorption.

For RB4 dye adsorption, the main structure and chemical groups of SPB and SPFB were the same as mentioned above, but the possible mechanism of RB4 dye adsorption used a different explanation based on Ngamsurach et al.12 shown in Fig. 11b. Three possible mechanisms of electrostatic attractions, hydrogen bonding interactions, and n–π bonding interactions were used for explaining RB4 dye adsorptions by SPB and SPFB. For electrostatic interactions, the surface of SPB or SPFB adsorbed RB4 dye molecule from the interaction between the positively charged hydroxy group (–OH) of their surface and the negatively charged sulfonate groups (–SO3−) of RB4 dye molecules. For hydrogen bonding interactions, the nitrogen (N) in the RB4 dye structure was caught by hydrogen ions (H+) in the hydroxyl group (–OH) of SPB or SPFB14. Finally, the n–π bonding interactions occurred by the interaction of oxygen bond (–O) in the hydroxyl group (–OH) in SPB or SPFB and the aromatic rings in RB4 dye molecules6.

Four sawdust materials of sawdust powder (SP), sawdust powder doped iron (III) oxide-hydroxide (SPF), sawdust beads (SPB), and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB) were successfully synthesized for lead or RB4 dye removals in an aqueous solution. SPFB demonstrated higher specific surface area (11.020 m2 g−1) and smaller pore size (3.937 nm) than other materials, and the results illustrated that the addition of iron (III) oxide-hydroxide into sawdust materials increased the specific surface area and pore volume while the pore diameter size was decreased. The surface morphologies of SP and SPF were irregular shapes with heterogeneous fiber structures whereas SPB and SPFB had spherical shapes with coarse surfaces. Carbon (C) and oxygen (O) were found in all materials whereas iron (Fe) was only found in the materials with the addition of iron (III) oxide-hydroxide (SPF and SPFB). Four main function groups of O–H, C–H, C=C, and C–O were detected in all materials. For batch experiments, the optimum conditions of SP, SPF, SPB, and SPFB for lead adsorptions were 2 g, 5 h, pH 5, 50 mg L−1, 1 g, 3 h, pH 5, 50 mg L−1, 1.5 g, 4 h, pH 5, 50 mg L−1, and 0.5 g, 2 h, pH 5, 50 mg L−1, respectively, and the optimum conditions of SPB and SPFB for RB4 dye adsorptions were 3 g, 12 h, 40 °C, pH 3, 50 mg L−1 and 1.5 g, 9 h, 30 °C, pH 3, 50 mg L−1, respectively. Since SPFB demonstrated the highest lead or RB4 dye removal than other materials, adding iron (III) oxide-hydroxide and changing material form helped to improve material efficiencies for lead or RB4 dye adsorptions. For adsorption isotherms, SP and SPB corresponded to Langmuir model correlated to physical adsorption whereas SPF and SPFB corresponded to the Freundlich model relating to a physicochemical adsorption process. For the kinetic study, all materials corresponded to a pseudo-second-order kinetic model related to a chemisorption process with heterogenous adsorption. For desorption experiments, all materials could be reused more than 5 cycles with high lead removal of 63%, and SPB and SPFB also could be reused more than 5 cycles with high RB4 dye removal of 72%. Therefore, all sawdust materials were high potential materials for lead or dye adsorption in an aqueous solution, and SPFB demonstrated the highest lead and RB4 dye removals. Therefore, SPFB was suitable for wastewater treatment in industrial applications.

For future works, the real wastewater with contaminated lead or RB4 dye should be investigated to confirm the ability of sawdust materials, and the continuous flow study also needs to study for further industrial applications.

Sawdust (Pterocarpus indicus) was obtained from a local sawmill in Khon Kaen province, Thailand.

All chemicals were analytical grades (AR) without purification before use. For material synthesis, ferric chloride hexahydrate (FeCl3·6H2O) (LOBA, India), sodium hydroxide (NaOH) (RCI Labscan, Thailand), sodium alginate (NaC6H7O6) (Merck, Germany), and calcium chloride dehydrate (CaCl2·2H2O) (RCI Labscan, Thailand) were used. For preparing wastewater samples, lead nitrate (Pb(NO3)2) (QRëC, New Zealand), and reactive blue 4 (RB4) dye (Sigma-Aldrich, Germany) were used. The chemical characteristic and structure of RB4 dye demonstrated in Table 9. For pH adjustment, 1% NaOH and 1% HNO3 (Merck, Germany) were used.

The flow diagrams of synthesis methods of four sawdust materials which were sawdust powder (SP), sawdust powder doped iron (III) oxide-hydroxide (SPF), sawdust beads (SPB), and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB) based on Threepanich and Praipipat8 are demonstrated in Fig. 12a–c and the details were clearly explained below.

Flow diagrams of synthesis methods of (a) sawdust powder (SP), (b) sawdust powder doped iron (III) oxide-hydroxide (SPF), and (c) sawdust beads (SPB) and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB).

Firstly, sawdust was washed with tap water to remove contaminants, and then it was dried overnight in a hot air oven (Binder, FED 53, Germany) at 105 °C. Then, it was ground and sieved to a size of 125 µm. Finally, it was kept in a desiccator before use called sawdust powder (SP).

Firstly, 5 g of SP were added to 500 mL of Erlenmeyer flask containing 160 mL of 5% FeCl3·6H2O, and they were mixed by an orbital shaker (GFL, 3020, Germany) of 200 rpm for 3 h. Secondly, they were filtrated and air-dried at room temperature for 12 h. Then, they were added to 500 mL of Erlenmeyer flask containing 160 mL of 5% NaOH, and they were mixed by an orbital shaker of 200 rpm for 1 h. After that, they were filtered and air-dried at room temperature for 12 h. Finally, they were kept in a desiccator before use called sawdust powder doped iron (III) oxide-hydroxide (SPF).

Firstly, 5 g of SP or SPF were added to 500 mL of a beaker containing 200 mL of 2% sodium alginate, and then they were homogeneously mixed and heated by a hot plate (Ingenieurbüro CAT, M. Zipperer GmbH, M 6, Germany) at 60 °C with a constant stirring of 200 rpm. Secondly, they were dropped by drop by using a 10 mL syringe with a needle size of 1.2 × 40 mm into 250 mL of 0.1 M CaCl2·2H2O. The beaded samples were soaked in 0.1 M CaCl2·2H2O for 24 h, and then they were filtered and rinsed with DI water. After that, they were air-dried at room temperature for 12 h and kept in a desiccator before use called sawdust beads (SPB) or sawdust powder doped iron (III) oxide-hydroxide beads (SPFB).

Various characterized techniques of Brunauer–Emmett–Teller (BET) (Bel, Bel Sorp mini X, Japan) by isothermal nitrogen gas (N2) adsorption–desorption at 77.3 K and degas temperature of 80 °C for 6 h, field emission scanning electron microscopy and focus ion beam (FESEM-FIB) with energy dispersive X-ray spectrometer (EDX) (FEI, Helios NanoLab G3 CX, USA), and Fourier transform infrared spectroscopy (FT-IR) (Bruker, TENSOR27, Hong Kong) were used for investigating the specific surface area, pore volume, pore size, surface morphology, chemical compositions, and chemical functional groups of sawdust powder (SP), sawdust powder doped iron (III) oxide-hydroxide (SPF), sawdust beads (SPB), and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB).

A series of batch adsorption experiments were designed to investigate the effect of dose, contact time, pH, and concentration on lead removal efficiency by sawdust powder (SP), sawdust powder doped iron (III) oxide-hydroxide (SPF), sawdust beads (SPB), and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB). The differences in dose from 0.5 to 3 g, contact time from 1 to 6 h, pH values of 1, 3, 5, 7, 9, 11, and lead concentration from 30 to 70 mg L−1 with the control condition of initial lead concentration of 50 mg L−1, a sample volume of 200 mL, a shaking speed of 200 rpm, a temperature of 25 °C were applied. The lowest value of each affecting factor with the highest lead removal efficiency was selected as the optimum value, and that value was applied to the next affecting factor study. Lead concentrations were analyzed by an atomic adsorption spectrophotometer (PerkinElmer, PinAAcle 900 F, USA), and triplicate experiments were conducted to confirm the results. Lead removal in the percentage (%) to calculate the following Eq. (1).

where C0 is the initial lead concentration (mg L−1), and Ce is the final lead concentration (mg L−1).

A series of batch adsorption experiments were designed to investigate the effect of dose, contact time, temperature, pH, and concentration on RB4 dye removal efficiency by sawdust beads (SPB) and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB). The differences in dose from 0.5 to 3 g, contact time of 3, 6, 9, 12, 15, 18 h, temperature from 30 to 80 °C, pH values of 1, 3, 5, 7, 9, 11, and RB4 dye concentration from 30 to 70 mg L−1 with the control condition of initial RB4 dye concentration of 50 mg L−1, a sample volume of 200 mL, a shaking speed of 150 rpm, and a contact time of 12 h were applied. The lowest value of each affecting factor with the highest RB4 dye removal efficiency was selected as the optimum value, and that value was applied to the next affecting factor study. Dye concentrations were analyzed by UV–Vis spectrophotometer (Hitachi, UH5300, Japan) at a maximum wavelength of 595 nm, and triplicate experiments were conducted to confirm the results. Dye removal in the percentage (%) to calculate the following Eq. (2).

where C0 is the initial dye concentration (mg L−1), and Ce is the final dye concentration (mg L−1).

The adsorption patterns of sawdust powder (SP), sawdust powder doped iron (III) oxide-hydroxide (SPF), sawdust beads (SPB), and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB) are investigated by adsorption isotherms for explaining that are the adsorption process of monolayer or multi-layer or heat or thermodynamic. Linear and nonlinear Langmuir, Freundlich, Temkin, and Dubinin–Radushkevich models are used to analyze followed Eqs. (3)–(10)65,66,67,68.

Langmuir isotherm:

Freundlich isotherm:

Temkin isotherm:

Dubinin–Radushkevich isotherm:

where Ce is the equilibrium of lead or dye concentration (mg L−1), qe is the amount of adsorbed lead or dye on sawdust materials (mg g−1), qm is indicated as the maximum amount of lead or dye adsorption on adsorbent materials (mg g−1), KL is the adsorption constant (L mg−1). KF is the constant of adsorption capacity (mg g−1) (L mg−1)1/n, and 1/n is the constant depicting the adsorption intensity. R is the universal gas constant (8.314 J mol−1 K−1), T is the absolute temperature (K), bT is the constant related to the heat of adsorption (J mol−1), and AT is the equilibrium binding constant corresponding to the maximum binding energy (L g−1). qm is the theoretical saturation adsorption capacity (mg g−1), KDR is the activity coefficient related to mean adsorption energy (mol2 J−2), and ε is the Polanyi potential (J mol−1). Graphs of linear Langmuir, Freundlich, Temkin, and Dubinin–Radushkevich isotherms were plotted by Ce/qe versus Ce, log qe versus log Ce, qe versus ln Ce, and ln qe versus ε2, respectively whereas graphs of their nonlinear were plotted by qe versus Ce.

For adsorption isotherm experiments, 2 g of SP or 1 g of SPF, or 1.5 g of SPB or 0.5 g of SPFB was added to 200 mL Erlenmeyer flasks with variable lead concentrations from 30 to 70 mg L−1 with the control condition of sample volume of 200 mL, a shaking speed of 200 rpm, pH 6, a temperature of 25 °C, and a contact time of 5 h for SP, 3 h for SPF, 4 h for SPB, and 2 h for SPFB for studying lead adsorption. For studying RB4 dye adsorption, 3 g of SPB or 1.5 g of SPFB was added to 200 mL Erlenmeyer flasks with variable RB4 dye concentrations from 30 to 70 mg L−1 with the control condition of a sample volume of 200 mL, a shaking speed of 150 rpm, pH 7, a temperature of 40 °C for SPB and 30 °C SPFB, and a contact time of 12 h.

The adsorption mechanisms of sawdust powder (SP), sawdust powder doped iron (III) oxide-hydroxide (SPF), sawdust beads (SPB), and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB) are determined by various adsorption kinetics which were linear and nonlinear pseudo-first-order kinetic, pseudo-second-order kinetic, Elovich, and intraparticle diffusion models calculated by Eqs. (11)–(17)69,70,71,72.

Pseudo-first-order kinetic model:

Pseudo-second-order kinetic model:

Elovich model:

Intraparticle diffusion model:

where qe is the amount of adsorbed lead or dye on adsorbent materials (mg g−1), qt is the amount of adsorbed lead or dye at the time (t) (mg g−1), k1 is a pseudo-first-order rate constant (min−1), and k2 is a pseudo-second-order rate constant (g mg−1 min−1)73. α is the initial adsorption rate (mg g−1 min−1) and β is the extent of surface coverage (g mg−1). ki is the intraparticle diffusion rate constant (mg g−1 min−0.5) and Ci is the constant that gives an idea about the thickness of the boundary layer (mg g−1). Graphs of linear pseudo-first-order, pseudo-second-order, Elovich, and intraparticle diffusion models were plotted by ln (qe − qt) versus time (t), t/qt versus time (t), qt versus ln t, and qt versus time (t0.5), respectively whereas their nonlinear graphs were plotted by the capacity of lead or dye adsorbed by sawdust materials at the time (qt) versus time (t).

For adsorption kinetic experiments, 10 g of SP or 5 g of SPF, or 7.5 g of SPB or 2.5 g of SPFB was added to 1000 mL of breaker with the control condition of the initial lead concentration of 50 mg L−1, a sample volume of 1000 mL, a shaking speed of 200 rpm, pH 5, a temperature of 25 °C, and a contact time of 8 h for studying lead adsorption. For studying RB4 dye adsorption, 15 g of SPB or 7.5 g of SPFB was added to 1000 mL of breaker with the control condition of initial RB4 dye concentration of 50 mg L−1, a shaking speed of 150 rpm, pH 3, a temperature of 40 °C for SPB and 30 °C SPFB, and a contact time of 18 h.

The possible material reusability is an important factor for considering adsorbents of industrial applications, so the desorption experiments are designed to examine by studying five adsorption–desorption cycles to confirm the abilities of sawdust powder (SP), sawdust powder doped iron (III) oxide-hydroxide (SPF), sawdust beads (SPB), and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB) for lead adsorption or sawdust beads (SPB) and sawdust powder doped iron (III) oxide-hydroxide beads (SPFB) for RB4 dye adsorption. For lead adsorption, the saturated sawdust materials were added to 500 mL of Erlenmeyer flask containing 200 mL of 0.5 M HNO3 solution, then it was shaken by an incubator shaker (New Brunswick, Innova 42, USA) at 200 rpm for 6 h. Then, they were washed with deionization water and dried at room temperature, and sawdust materials are ready for the next adsorption cycle. For RB4 dye adsorption, the saturated sawdust materials were added to 500 mL of Erlenmeyer flask containing 200 mL of 0.01 M NaOH solution, then it was shaken by an incubator shaker at 150 rpm for 15 h with a temperature of 30 °C. Then, they were washed with deionization water and dried at room temperature, and sawdust materials are ready for the next adsorption cycle. The desorption efficiency in percentage is calculated following Eq. (18).

where qd is the amount of lead or dye desorbed (mg mL−1) and qa is the amount of lead or dye adsorbed (mg mL−1).

The datasets used and/or analyzed during the current study are available from the corresponding author upon reasonable request.

Tounsadi, H., Metarfi, Y., Taleb, M., El Rhazi, K. & Rais, Z. Impact of chemical substances used in textile industry on the employee's health: Epidemiological study. Ecotoxicol. Environ. Saf. 197, 110594 (2020).

Article CAS Google Scholar

Li, M. et al. Review on clean recovery of discarded/spent lead-acid battery and trends of recycled products. J. Power Sources 436, 226853 (2019).

Article CAS Google Scholar

Benkhaya, S., M’rabet, S. & El Harfi, A. A review on classifications, recent synthesis and applications of textile dyes. Inorg. Chem. Commun. 115, 107891 (2020).

Article CAS Google Scholar

Al-Tohamy, R. et al. A critical review on the treatment of dye-containing wastewater: Ecotoxicological and health concerns of textile dyes and possible remediation approaches for environmental safety. Ecotoxicol. Environ. Saf. 231, 113160 (2022).

Article CAS Google Scholar

Soliman, N. K. & Moustafa, A. F. Industrial solid waste for heavy metals adsorption features and challenges; A review. J. Mater. Res. Technol. 9, 10235–10253 (2020).

Article CAS Google Scholar

Praipipat, P., Ngamsurach, P., Thanyahan, A. & Sakda, A. Reactive blue 4 adsorption efficiencies on bagasse and bagasse fly ash beads modified with titanium dioxide (TiO2), magnesium oxide (MgO), and aluminum oxide (Al2O3). Ind. Crops Prod. 191, 115928 (2023).

Article CAS Google Scholar

Ngamsurach, P., Namwongsa, N. & Praipipat, P. Synthesis of powdered and beaded chitosan materials modified with ZnO for removing lead (II) ions. Sci. Rep. 12, 17184 (2022).

Article ADS CAS Google Scholar

Threepanich, A. & Praipipat, P. Powdered and beaded lemon peels-doped iron (III) oxide-hydroxide materials for lead removal applications: Synthesis, characterizations, and lead adsorption studies. J. Environ. Chem. Eng. 9, 106007 (2021).

Article CAS Google Scholar

Aigbe, R. & Kavaz, D. Unravel the potential of zinc oxide nanoparticle-carbonized sawdust matrix for removal of lead (II) ions from aqueous solution. Chin. J. Chem. Eng. 29, 92–102 (2021).

Article CAS Google Scholar

Liu, G. et al. Organic adsorbents modified with citric acid and Fe3O4 enhance the removal of Cd and Pb in contaminated solutions. Chem. Eng. J. 395, 125108 (2020).

Article CAS Google Scholar

Ma, C. M., Hong, G. B. & Wang, Y. K. Performance evaluation and optimization of dyes removal using rice bran-based magnetic composite adsorbent. Materials (Basel) 13, 2764 (2020).

Article ADS CAS Google Scholar

Ngamsurach, P., Nemkhuntod, S., Chanaphan, P. & Praipipat, P. Modified beaded materials from recycled wastes of bagasse and bagasse fly ash with iron (III) oxide-hydroxide and zinc oxide for the removal of reactive blue 4 dye in aqueous solution. ACS Omega 7, 34839–34857 (2022).

Article CAS Google Scholar

Praipipat, P., Ngamsurach, P. & Prasongdee, V. Comparative reactive blue 4 dye removal by lemon peel bead doping with iron (III) oxide-hydroxide and zinc oxide. ACS Omega 7, 41744–41758 (2022).

Article CAS Google Scholar

Praipipat, P., Ngamsurach, P., Saekrathok, C. & Phomtai, S. Chicken and duck eggshell beads modified with iron (III) oxide-hydroxide and zinc oxide for reactive blue 4 dye removal. Arab. J. Chem. 15, 104291 (2022).

Article CAS Google Scholar

Wijeyawardana, P. et al. Removal of Cu, Pb and Zn from stormwater using an industrially manufactured sawdust and paddy husk derived biochar. Environ. Technol. Innov. 28, 102640 (2022).

Article CAS Google Scholar

Hashem, A. et al. Non-linear adsorption characteristics of modified pine wood sawdust optimised for adsorption of Cd(II) from aqueous systems. J. Environ. Chem. Eng. 8, 103966 (2020).

Article CAS Google Scholar

Harripersadth, C., Musonge, P., Makarfi Isa, Y., Morales, M. G. & Sayago, A. The application of eggshells and sugarcane bagasse as potential biomaterials in the removal of heavy metals from aqueous solutions. South Afr. J. Chem. Eng. 34, 142–150 (2020).

Article Google Scholar

Threepanich, A. & Praipipat, P. Efficacy study of recycling materials by lemon peels as novel lead adsorbents with comparing of material form effects and possibility of continuous flow experiment. Environ. Sci. Pollut. Res. 29, 46077–46090 (2022).

Article CAS Google Scholar

Ahmadi, H. et al. Low cost biosorbent (melon peel) for effective removal of Cu (II), Cd (II), and Pb (II) ions from aqueous solution. Case Stud. Chem. Environ. Eng. 6, 100242 (2022).

Article CAS Google Scholar

Grassi, P. et al. Application of Cordia trichotoma sawdust as an effective biosorbent for removal of crystal violet from aqueous solution in batch system and fixed-bed column. Environ. Sci. Pollut. Res. 28, 6771–6783 (2021).

Article CAS Google Scholar

Bouhadjra, K., Lemlikchi, W., Ferhati, A. & Mignard, S. Enhancing removal efficiency of anionic dye (Cibacron blue) using waste potato peels powder. Sci. Rep. 11, 2090 (2021).

Article ADS CAS Google Scholar

Munagapati, V. S., Yarramuthi, V., Kim, Y., Lee, K. M. & Kim, D. S. Removal of anionic dyes (Reactive Black 5 and Congo Red) from aqueous solutions using Banana Peel Powder as an adsorbent. Ecotoxicol. Environ. Saf. 148, 601–607 (2018).

Article CAS Google Scholar

Bayomie, O. S. et al. Novel approach for effective removal of methylene blue dye from water using fava bean peel waste. Sci. Rep. 10, 7824 (2020).

Article ADS CAS Google Scholar

Peyghami, A. et al. Evaluation of the efficiency of magnetized clinoptilolite zeolite with Fe3O4 nanoparticles on the removal of basic violet 16 (BV16) dye from aqueous solutions. J. Dispers. Sci. Technol. 1, 1–10. https://doi.org/10.1080/01932691.2021.1947847 (2021).

Article CAS Google Scholar

Abdollahzadeh, H. et al. Efficiency of activated carbon prepared from scrap tires magnetized by Fe3O4 nanoparticles: Characterisation and its application for removal of reactive blue19 from aquatic solutions. Int. J. Environ. Anal. Chem. 102, 1911–1925 (2022).

Article CAS Google Scholar

Rashtbari, Y. et al. Application of powdered activated carbon coated with zinc oxide nanoparticles prepared using a green synthesis in removal of reactive blue 19 and reactive black-5: Adsorption isotherm and kinetic models. Desalin. Water Treat. 179, 354–367 (2020).

Article CAS Google Scholar

Pourali, P. et al. Removal of acid blue 113 from aqueous solutions using low-cost adsorbent: Adsorption isotherms, thermodynamics, kinetics and regeneration studies. Sep. Sci. Technol. 56, 3079–3091 (2021).

Article CAS Google Scholar

Rashtbari, Y. et al. Green synthesis of zinc oxide nanoparticles loaded on activated carbon prepared from walnut peel extract for the removal of Eosin Y and Erythrosine B dyes from aqueous solution: Experimental approaches, kinetics models, and thermodynamic studies. Environ. Sci. Pollut. Res. 29, 5194–5206 (2022).

Article CAS Google Scholar

Chen, X. et al. Natural adsorbent based on sawdust for removing impurities in waste lubricants. J. Hazard. Mater. 350, 38–45 (2018).

Article CAS Google Scholar

Ibrahim, J. E. F. M., Tihtih, M. & Gömze, L. A. Environmentally-friendly ceramic bricks made from zeolite-poor rock and sawdust. Constr. Build. Mater. 297, 123715 (2021).

Article CAS Google Scholar

Benyoucef, S. et al. Preparation and characterization of novel microstructure cellulosic sawdust material: Application as potential adsorbent for wastewater treatment. Cellulose 27, 8169–8180 (2020).

Article CAS Google Scholar

Liang, J. et al. Magnetic nanoferromanganese oxides modified biochar derived from pine sawdust for adsorption of tetracycline hydrochloride. Environ. Sci. Pollut. Res. 26, 5892–5903 (2019).

Article CAS Google Scholar

Pooladi, H., Foroutan, R. & Esmaeili, H. Synthesis of wheat bran sawdust/Fe3O4 composite for the removal of methylene blue and methyl violet. Environ. Monit. Assess. 193, 276 (2021).

Article CAS Google Scholar

Houshangi, A., Jamehbozorgi, S., Yousefi, M. & Ghiasi, R. Preparation of CoFe2O4/sawdust and NiFe2O4/sawdust magnetic nanocomposites for removal of oil from the water surface. J. Chin. Chem. Soc. 67, 288–297 (2020).

Article CAS Google Scholar

Rouquerol, J. et al. Recommendations for the characterization of porous solids (Technical report). Pure Appl. Chem. 66, 1739–1758 (1994).

Article CAS Google Scholar

Orelma, H., Tanaka, A., Vuoriluoto, M., Khakalo, A. & Korpela, A. Manufacture of all-wood sawdust-based particle board using ionic liquid-facilitated fusion process. Wood Sci. Technol. 55, 331–349 (2021).

Article CAS Google Scholar

El Hajam, M. et al. Pb2+ ions adsorption onto raw and chemically activated Dibetou sawdust: Application of experimental designs. J. King Saud Univ. Sci. 32, 2176–2189 (2020).

Article Google Scholar

Zhong, C. et al. The role of sodium alginate in the flotation separation of apatite and dolomite. Powder Technol. 373, 620–626 (2020).

Article CAS Google Scholar

Saeed, S. et al. La3+-substituted β-ferrite: Investigation of structural, dielectric, FTIR and electrical polarization properties. J. Alloys Compd. 831, 154854 (2020).

Article CAS Google Scholar

Rahman, N. U. et al. Activated Ailanthus altissima sawdust as adsorbent for removal of acid yellow 29 from wastewater: Kinetics approach. Water 13, 2136 (2021).

Article ADS CAS Google Scholar

Tejada-Tovar, C., Villabona-Ortíz, A., Ortega-Toro, R., Mancilla-Bonilla, H. & Espinoza-León, F. Potential use of residual sawdust of Eucalyptus Globulus Labill in Pb (II) adsorption: Modelling of the kinetics and equilibrium. Appl. Sci. 11, 3125 (2021).

Article CAS Google Scholar

Ngamsurach, P. & Praipipat, P. Modified alginate beads with ethanol extraction of Cratoxylum formosum and Polygonum odoratum for antibacterial activities. ACS Omega 6, 32215–32230 (2021).

Article CAS Google Scholar

Ngamsurach, P. & Praipipat, P. Antibacterial activities against Staphylococcus aureus and Escherichia coli of extracted Piper betle leaf materials by disc diffusion assay and batch experiments. RSC Adv. 12, 26435–26454 (2022).

Article ADS CAS Google Scholar

Ngamsurach, P. & Praipipat, P. Comparative antibacterial activities of Garcinia cowa and Piper sarmentosum extracts against Staphylococcus aureus and Escherichia coli with studying on disc diffusion assay, material characterizations, and batch experiments. Heliyon 8, e11704 (2022).

Article CAS Google Scholar

Mahmood-Ul-Hassan, M., Yasin, M., Yousra, M., Ahmad, R. & Sarwar, S. Kinetics, isotherms, and thermodynamic studies of lead, chromium, and cadmium bio-adsorption from aqueous solution onto Picea smithiana sawdust. Environ. Sci. Pollut. Res. 25, 12570–12578 (2018).

Article CAS Google Scholar

Semerjian, L. Removal of heavy metals (Cu, Pb) from aqueous solutions using pine (Pinus halepensis) sawdust: Equilibrium, kinetic, and thermodynamic studies. Environ. Technol. Innov. 12, 91–103 (2018).

Article Google Scholar

Oyewo, O. A., Ramaila, S., Mavuru, L., Leswifi, T. & Onyango, M. S. Adsorptive and coagulative removal of trace metals from water using surface modified sawdust-based cellulose nanocrystals. J. 4, 193–205 (2021).

CAS Google Scholar

Niu, Z. et al. Green synthesis of a novel Mn–Zn ferrite/biochar composite from waste batteries and pine sawdust for Pb2+ removal. Chemosphere 252, 126529 (2020).

Article ADS CAS Google Scholar

Shi, J. et al. Removal of lead by rice husk biochars produced at different temperatures and implications for their environmental utilizations. Chemosphere 235, 825–831 (2019).

Article ADS CAS Google Scholar

Jaber, L. et al. Adsorptive removal of lead and chromate ions from water by using iron-doped granular activated carbon obtained from coconut shells. Sustainability 14, 10877 (2022).

Article CAS Google Scholar

Morifi, E. L., Ofomaja, A. E. & Pillay, K. Microwave assisted modified macadamia nutshells/Cu–Mn oxide composite for the removal of Pb(II) from aqueous solution. J. Environ. Chem. Eng. 8, 103822 (2020).

Article CAS Google Scholar

Vivian Loh, Z. T., Ping, T. Y. & Abdullah, A. H. Removal of Pb(II) from aqueous solution by pineapple plant stem. Malays. J. Anal. Sci. 23, 219–228 (2019).

Google Scholar

Pap, S. et al. Synthesis of highly-efficient functionalized biochars from fruit industry waste biomass for the removal of chromium and lead. J. Mol. Liq. 268, 315–325 (2018).

Article CAS Google Scholar

Zhao, T., Ma, X., Cai, H., Ma, Z. & Liang, H. Study on the adsorption of CuFe2O4-loaded corncob biochar for Pb(II). Molecules 25, 3456 (2020).

Article CAS Google Scholar

Kang, C. et al. EDTAD-modified cassava stalks loaded with Fe3O4: Highly efficient removal of Pb2+ and Zn2+ from aqueous solution. Environ. Sci. Pollut. Res. 28, 6733–6745 (2021).

Article CAS Google Scholar

Adeoye, B. et al. Evaluation of biosorptive capacity of waste watermelon seed for lead (II) removal from aqueous solution. Am. J. Environ. Eng. 2020, 1–8 (2020).

Google Scholar

Afolabi, F. O., Musonge, P. & Bakare, B. F. Adsorption of copper and lead ions in a binary system onto orange peels: Optimization, equilibrium, and kinetic study. Sustainability 14, 10860 (2022).

Article CAS Google Scholar

Yu, X. L. & He, Y. Optimal ranges of variables for an effective adsorption of lead(II) by the agricultural waste pomelo (Citrus grandis) peels using Doehlert designs. Sci. Rep. 8, 729 (2018).

Article ADS Google Scholar

Afolabi, F. O., Musonge, P. & Bakare, B. F. Bio-sorption of a bi-solute system of copper and lead ions onto banana peels: Characterization and optimization. J. Environ. Health Sci. Eng. 19, 613–624 (2021).

Article CAS Google Scholar

Olasehinde, E. F., Adegunloye, A. V., Adebayo, M. A. & Oshodi, A. A. Sequestration of aqueous lead(II) using modified and unmodified red onion skin. Anal. Lett. 51, 2710–2732 (2018).

Article Google Scholar

Teixeira, R. A. et al. Preparation of hybrids of wood sawdust with 3-aminopropyl-triethoxysilane. Application as an adsorbent to remove Reactive Blue 4 dye from wastewater effluents. J. Taiwan Inst. Chem. Eng. 125, 141–152 (2021).

Article CAS Google Scholar

Ma, C. M., Yang, B. Y. & Hong, G. B. Husk of agarwood fruit-based hydrogel beads for adsorption of cationic and anionic dyes in aqueous solutions. Molecules 26, 137 (2021).

Article Google Scholar

Dos Reis, G. S. et al. Preparation and application of efficient biobased carbon adsorbents prepared from spruce bark residues for efficient removal of reactive dyes and colors from synthetic effluents. Coatings 11, 772 (2021).

Article Google Scholar

Malool, M. E., Keshavarz Moraveji, M. & Shayegan, J. Optimized production, Pb(II) adsorption and characterization of alkali modified hydrochar from sugarcane bagasse. Sci. Rep. 11, 22328 (2021).

Article ADS CAS Google Scholar

Langmuir, I. The adsorption of gases on plane surfaces of glass, mica and platinum. J. Am. Chem. Soc. 40, 1361–1403 (1918).

Article CAS Google Scholar

Freundlich, H. Over the adsorption in solution. J. Phys. Chem. 57, 385–470 (1906).

CAS Google Scholar

Temkin, M. I. & Pyzhev, V. Kinetics of ammonia synthesis on promoted iron catalysts. Acta Physiochim. URSS 12, 327–356 (1940).

CAS Google Scholar

Dubinin, M. M. & Radushkevich, L. V. The equation of the characteristic curve of activated charcoal. Proc. USSR Acad. Sci. 55, 327–329 (1947).

CAS Google Scholar

Lagergren, S. About the theory of so-called adsorption of soluble substances. K. Sven. Vetenskapsakademiens Handl. 24, 1–39 (1898).

Google Scholar

Ho, Y. S. & Mckay, G. Pseudo-second order model for sorption processes. Process Biochem. 34, 451–465 (1999).

Article CAS Google Scholar

Elovich, S. Y. & Larinov, O. G. Theory of adsorption from solutions of non electrolytes on solid (I) equation adsorption from solutions and the analysis of its simplest form, (II) verification of the equation of adsorption isotherm from solutions. Izv. Akad. Nauk. SSSR Otd. Khim. Nauk. 2, 209–216 (1962).

Google Scholar

Weber, W. J. & Morris, J. C. Kinetics of adsorption carbon from solution. J. Sanit. Eng. Div. 89, 31–60 (1963).

Article Google Scholar

Jangkorn, S., Youngme, S. & Praipipat, P. Comparative lead adsorptions in synthetic wastewater by synthesized zeolite A of recycled industrial wastes from sugar factory and power plant. Heliyon 8, e09323 (2022).

Article CAS Google Scholar

Download references

The authors are grateful for the financial support received from The Office of the Higher Education Commission and The Thailand Research Fund grant (MRG6080114), Coordinating Center for Thai Government Science and Technology Scholarship Students (CSTS) and National Science and Technology Development Agency (NSTDA) Fund grant (SCHNR2016-122), and Research and Technology Transfer Affairs of Khon Kaen University.

Department of Environmental Science, Khon Kaen University, Khon Kaen, 40002, Thailand

Pornsawai Praipipat, Pimploy Ngamsurach, Sichon Kosumphan & Jirasak Mokkarat

Environmental Applications of Recycled and Natural Materials (EARN) Laboratory, Khon Kaen University, Khon Kaen, 40002, Thailand

Pornsawai Praipipat & Pimploy Ngamsurach

You can also search for this author in PubMed Google Scholar

You can also search for this author in PubMed Google Scholar

You can also search for this author in PubMed Google Scholar

You can also search for this author in PubMed Google Scholar

P.P.: Supervision, Conceptualization, Funding acquisition, Investigation, Methodology, Validation, Visualization, Writing—Original Draft, Writing—Review and Editing. P.N.: Visualization, Writing—Original Draft. S.K.: Investigation. J.M.: Investigation.

Correspondence to Pornsawai Praipipat.

The authors declare no competing interests.

Springer Nature remains neutral with regard to jurisdictional claims in published maps and institutional affiliations.

Open Access This article is licensed under a Creative Commons Attribution 4.0 International License, which permits use, sharing, adaptation, distribution and reproduction in any medium or format, as long as you give appropriate credit to the original author(s) and the source, provide a link to the Creative Commons licence, and indicate if changes were made. The images or other third party material in this article are included in the article's Creative Commons licence, unless indicated otherwise in a credit line to the material. If material is not included in the article's Creative Commons licence and your intended use is not permitted by statutory regulation or exceeds the permitted use, you will need to obtain permission directly from the copyright holder. To view a copy of this licence, visit http://creativecommons.org/licenses/by/4.0/.

Reprints and Permissions

Praipipat, P., Ngamsurach, P., Kosumphan, S. et al. Powdered and beaded sawdust materials modified iron (III) oxide-hydroxide for adsorption of lead (II) ion and reactive blue 4 dye. Sci Rep 13, 531 (2023). https://doi.org/10.1038/s41598-023-27789-9

Download citation

Received: 24 November 2022

Accepted: 09 January 2023

Published: 11 January 2023

DOI: https://doi.org/10.1038/s41598-023-27789-9

Anyone you share the following link with will be able to read this content:

Sorry, a shareable link is not currently available for this article.

Provided by the Springer Nature SharedIt content-sharing initiative

Scientific Reports (2023)

Scientific Reports (2023)

By submitting a comment you agree to abide by our Terms and Community Guidelines. If you find something abusive or that does not comply with our terms or guidelines please flag it as inappropriate.