Thank you for visiting nature.com. You are using a browser version with limited support for CSS. To obtain the best experience, we recommend you use a more up to date browser (or turn off compatibility mode in Internet Explorer). In the meantime, to ensure continued support, we are displaying the site without styles and JavaScript.
Scientific Reports volume 6, Article number: 20003 (2016 ) Cite this article 2-Iodo-1-P-Tolylpropan-1-One
Water contamination becomes one of the most pervasive environmental issues all over the world in recent years. In this paper, the functionalization of graphene oxide (GO) with copolymers containing methacrylic acid (MAA) and butyl methacrylate (BMA) was investigated to prepare a new microcomposite material (PGO) via free radical solution polymerization. PGO was used for the adsorption of N,N-dimethylformamide (DMF) from aqueous solution by utilizing the characteristics of ultralarge surface and the Van der Waals force between DMF molecules and polymers on the surface of PGO. Besides, PGO was used not only a high-capable adsorbent but also a carrier for the immobilization of Paracoccus denitrificans cells in the treatment of high-concentrated DMF. Bacterial cells could immobilized on the PGO (PGO@P. denitrificans) stably by covalent coupling process after acclimatization and high-concentrated DMF (2000 mg/L) could be removed completely and relatively rapidly from aqueous solutions by the simultaneous adsorption-biodegradation (SAB) process of PGO@P. denitrificans. Furthermore, the excellent recycle performance of PGO@P. denitrificans made the whole process more economical and practical.
Lobna Nassar, Vijay S. Wadi, …Shadi W. Hasan
H. Idress, S. Z. J. Zaidi, … F. C. Walsh
KO Sodeinde, SO Olusanya, … AA Adediran
As a versatile organic solvent, N,N-dimethylformamide (DMF) is widely used in pharmaceutical, chemical and textile industries due to its excellent miscibility with both water and most organic solvents1. Hence, high concentrations and considerable amounts of DMF are commonly found in many industrial effluents even after its recovery, which cause adverse toxic effects on both environment and human health2,3,4. Therefore, many methods have been studied in the past few years to deal with DMF in wastewater, such as distillation, adsorption, biodegradation, chemical oxidation and solvent extraction5. Biodegradation has considered to be the most practical, economical, environmentally friendly and promising approach6,7,8,9,10,11. Moreover, numerous researches based on the biodegradation of different organic pollutants by using immobilization technique have been reported12,13,14. The biodegradation process combining with immobilization technique owns more advantages than free cells, including enhancing the stability of microbial cells, avoiding the biomass-liquid separation and discontinuous process operation. However, the high-concentrated DMF wastewater may have toxic to bacterial cells and the removal efficiency of the DMF was improved hardly.
Recently, simultaneous adsorption and biodegradation (SAB, immobilize on adsorbents) was common used in the treatment process of wastewater containing high-concentrated DMF. Therefore, adsorbents play an important role in the performance of adsorption process. Some traditional adsorbents are popular in removal of organic contaminants in water treatment15. However, these adsorbents have many disadvantages, such as high cost and low reusability. Therefore, a considerable amount of researches have focused on various commercially available and regenerated adsorbents instead of traditional adsorbents16. In addition to inorganic absorption materials, some nanomaterials are also popular in environmental remediation, which provided a lower cost, greater sensitivity, smaller sizes, higher efficiency than traditional adsorbents17.
As a fascinating new nanomaterial, graphene oxide (GO) which is an amazing derivative of graphene, has attracted great attention all over the world recently18,19,20,21,22,23,24. In addition, GO has been used as an effective adsorbent on the treatment of different kinds of organic wastewater owing to its extraordinary mechanical strength and relatively large specific area25,26,27,28,29. And because GO is heavily decorated by oxygen-containing groups (carboxyl, hydroxyl, epoxy) on their basal planes and edges, various of polymers can be modified on the surface of GO easily, which cause a higher efficiency to the adsorption of organic contaminants than GO30,31,32,33,34,35. However, as a normal adsorbent, GO can reach a maximal equilibrium adsorption amount of DMF but cannot remove DMF completely.
Here, in order to resolve the problems mentioned above, the fabrication of the new adsorbent microcomposite material (PGO) for the efficient removal of DMF from water is reported. The key strategy is to use copolymers containing methacrylic acid (MAA) and butyl methacrylate (BMA) to modify the surface of GO, leading to the formation of GO@poly(MAA-co-BMA) (PGO) consisting abundant oxygen-containing groups (Fig. 1). In addition, the unique PGO also showed a favorable adsorption property for its ultra large surface and Van der Waals force between DMF molecules and polymers on its surface, which was employed to be the superior carrier of P. denitrificans (ATCC 19367) (had already been reported on the biodegradation of DMF9) for its large loading amount of bacterial cells. The immobilization process was achieved by covalent coupling process36, which made the bacterial cells immobilized on matrix stably than other immobilization method37,38. Moreover, when the cells were immobilized on the PGO (PGO@P. denitrificans), the concentration of DMF was dropped off continuously until 0 mg/L by SAB process. In consideration of the advantages mentioned above, PGO@P. denitrificans was used in the treatment of relatively high concentration DMF from aqueous solution (2000 mg/L) without any pre-treatment, which made the adsorption-biodegradation process more simple and economical. On the other hand, PGO@P. denitrificans also showed an excellent recycle performance, which made the whole process more practical and promising.
Illustration of PGO synthetic procedure and adsorption-biodegradation process of cells-immobilized PGO for DMF.
The microstructure and morphology of GO and PGO were analyzed by SEM (Fig. 2). The morphology of GO was shown in Fig. 2a, which presented a laminated structure with smooth surface and wrinkled edge. However, the PGO showed a significantly rougher surface than GO (Fig. 2b), which suggested that the polymers were successfully grafted to the surface of GO.
The SEM images of GO (a) and PGO (b), TGA curves of GO and PGO obtained in nitrogen atmosphere (c), FT-IR spectra of GO and PGO (d).
The amount of polymers that modified on the surface of GO was studied by TGA. Fig. 2c showed the weight loss of the samples. GO was thermally more unstable than PGO and it suffered about 30% weight loss at around 200 °C, which might be owed to the thermal decomposition of the unstable oxygen-containing groups. However, PGO showed a slighter weight loss at around 200 °C compared with GO. In the range between 100 and 600 °C, GO was found to have about 50 wt % weight loss. At the same time, the weight loss of PGO was 75% at 100–600 °C, which resulted from the thermal degradation of polymers and the loss of oxygen-containing functional groups on the GO sheets. So the polymers in PGO were calculated to be approximately 25 wt %.
The FT-IR spectra of GO and PGO were shown in Fig. 2d. Different oxygen-containing functional groups were found in the FT-IR spectrum of GO, the characteristics bands appeared at 3400 cm−1 (-OH stretching band), 1730 cm−1 (C=O bending of COOH), 1620 cm−1 (C-OH vibration frequency), 1380 cm−1 (C=C bending) and 1100 cm−1 (C-O-O bending). Compared with GO, the obvious increase in the peak at 1730 cm−1 could be attributed to the C=O bending of PGO, which also indicated the polymers were grafted to GO successfully. In addition, new bands appeared in the range between 1300–1050 cm−1 were the C-O stretching vibration of the polymers in PGO. These changes in FT-IR spectra confirmed the presence of poly(MAA-co-BMA) on the surface of GO.
To investigate the adsorption performance of GO and PGO, equilibrium adsorption experiments were carried out in the 250 mL flasks containing 100 mg of diverse adsorbents (GO and PGO) and 50 mL aqueous solution with an initial DMF concentration of 1000 mg/L. And the flasks were shaken in the constant temperature oscillator at 30 °C and 150 r/min. As shown in Fig. 3, for GO and PGO, the adsorption rate were fast at the initial stage and gradually slowed until equilibrium after shaking for about 8 h and 5 h, respectively. For the same initial DMF concentration of 1000 mg/L, the maximal equilibrium adsorption amount of PGO was significantly increased by 40% compared with GO. PGO had more abundant oxygen-containing groups than GO due to polymers on its surface, which formed the Van der Waals force between DMF molecules and polymers, therefore, PGO showed an obviously higher adsorption capacity than GO.
Adsorption capacity of GO and PGO (dry weight of GO = 100 mg, dry weight of PGO = 100 mg, initial DMF concentration = 1000 mg/L, volume of DMF solution = 50 mL and T = 30 °C).
Acclimatization process of P. denitrificans cells is shown in Fig. 4. During this process, the DMF concentration was increased 100 mg/L every time when the DMF concentration decreased to 0 mg/L. After acclimatization for 33 days, the P. denitrificans could biodegrade DMF with the initial concentration of 1000 mg/L completely without glucose, which indicated that the P. denitrificans was capable of utilizing DMF as a sole source of carbon and nitrogen. With the increasing of DMF concentration continually, the P. denitrificans could attain a higher biodegradability (2000 mg/L). DMF could be biodegraded under a certain concentration ranged from 0 to 2000 mg/L.
Before the biodegradation experiments, the optimal conditions of the biodegradation of DMF by P. denitrificans cells need to be determined first and batch experiments were carried out at different pH (3–10) and temperatures (25–40 °C) respectively with the same initial DMF concentration of 1000 mg/L. The results of the optimal conditions for the biodegradation of DMF by P. denitrificans cells were shown in Fig. 5, which indicated that it had a best biodegradation rate at the optimized temperature of 30 °C and the optimum pH value near neutrality. Then all the following experiments were carried out under this optimal condition (T = 30 °C, pH = 7).
Effect of pH (a) and temperature (b) on biodegradation efficiency of DMF (initial DMF concentration = 1000 mg/L, volume of DMF solution = 50 mL, wet weight of P. denitrificans = 2.0 g).
The biodegradation efficiency of free cells was detected under the optimal conditions. The changes of DMF concentration and OD600 were represented in Fig. 6a. It could be seen that P. denitrificans alone was able to degrade DMF completely within 12 h when the initial concentration was 1000 mg/L. And the increase amount of P. denitrificans cells was calculated according to the relation curve between OD600 and dry cell weight (DCW) (Fig. 6b) as 6.85 mg.
(a) Biodegradation curve and OD600 of free P. denitrificans (initial DMF concentration = 1000 mg/L, volume of DMF solution = 50 mL, wet weight of P. denitrificans = 2.0 g, pH = 7 and T = 30 °C) and (b) the relative conversion curve of OD600 and DCW.
The immobilization process was achieved by covalent coupling. P. denitrificans cells had many innate amine groups on the surface, so the bacterial cells could be immobilized onto PGO stably which contained many carboxyl groups (-COOH) on the surface by direct covalent chemical conjugation. N-hydroxy succinimide (NHS) as a robust and highly reactive chemical for introducing functional surface of component to cell membrane was used to accomplish the immobilization process, which could avoid loss of bacterial cells viability. The acclimatized P. denitrificans cells were immobilized onto PGO (PGO@P. denitrificans) at 30 °C in the constant temperature oscillator (150 r/min). The microstructure and morphology of PGO@P. denitrificans were studied by SEM and TEM after freeze-dried at −40 °C for 6 h. As shown in Fig. 7, the acclimatized P. denitrificans cells were immobilized onto sheet-shaped PGO firmly by covalent coupling process and also form a large amount of biomass. In addition, it could be clearly seen that the morphology of bacterium cells were well-shaped rodlike structures, which also indicated the PGO had no antimicrobial effect to P. denitrificans cells39.
The SEM images (a,b) and TEM images (c,d) of PGO@P. denitrificans.
Subsequently, the amount of P. denitrificans cells immobilized onto PGO was discussed and batch experiments were carried out in the 250 mL flasks at 30 °C. Each flask contained 50 mL PBS solution and the same weight of P. denitrificans cells and the amount of bacterium cells was calculated according to the relation curve between OD600 and DCW (Fig. 6b). Then, PGO was added (10 mg, 15 mg and 20 mg) to the flasks to accomplish the immobilization process. As shown in Table 1, for 50 mg (dry cell weight) of P. denitrificans cells, the maximum amount of PGO that coupled to the surface of bacterium cells was approximately 15 mg. Then the amount of P. denitrificans cells and PGO used for the next adsorption-biodegradation process were followed by this ratio.
The PGO@P. denitrificans and poly(MAA-co-BMA)@P. denitrificans were directly used in the removal of high-concentrated DMF from water.The SAB efficiency and recycle performance of PGO@P. denitrificans were detected under the optimal conditions and the results were shown in Fig. 8. DMF was removed completely within 10 h from the initial concentration of 1000 mg/L by PGO@P. denitrificans (Fig. 8a), which showed a significantly higher efficiency than free cells (Fig. 6a) with the same wet weight of materials even after recycled for 3 times. In addition, the initial DMF concentration of 2000 mg/L could be removed completely just need 14 h by PGO@P. denitrificans (Fig. 8b). As can be seen in Fig. 8, the whole process could be divided into two stages. During the first stage within about 4 h, the concentration of DMF decreased quickly, which indicated that PGO played a main role in this adsorption process and most of DMF molecules were adsorbed. Then in the second stage, the adsorption of PGO attained equilibration and the decrease of DMF concentration attributed to the biodegradation of P. denitrificans. Besides, the concentration of DMF was dropped off continuously by biodegradation process, which was clearly different from ordinary adsorption process of PGO that maintained at an equilibrium adsorption amount and could not remove DMF from water completely.As can be seen in Fig. 9, DMF was removed completely within 12 h and 24 h for the initial concentration of 1000 mg/L and 2000 mg/L by poly(MAA-co-BMA)@P. denitrificans, respectively. Thus, PGO@P. denitrificans showed a significantly higher SAB efficiency than poly(MAA-co-BMA)@P. denitrificans, which could be attributed to the relatively large specific area of PGO.
The SAB process of PGO@P. denitrificans at different initial DMF concentrations (wet weight of PGO@P. denitrificans = 2.0 g, volume of DMF solution = 50 mL, pH = 7 and T = 30 °C).
The SAB process of poly(MAA-co-BMA)@P. denitrificans at different initial DMF concentrations (wet weight of poly(MAA-co-BMA)@P. denitrificans = 2.0 g, volume of DMF solution = 50 mL, pH = 7 and T = 30 °C).
The results of recycle performances of PGO@P. denitrificans to the different initial concentrations of DMF were also presented in Fig. 8. After recycling for 3 times, DMF could be removed completely from aqueous solutions within 12 h and 24 h for the initial DMF concentrations of 1000 mg/L and 2000 mg/L, respectively. Although, the processing efficiency of cells-immobilized PGO showed a bit lower than the first process, it still displayed an excellent recycle performance for removal of DMF from aqueous solution. From above we can conclude that PGO@P. denitrificans showed not only remarkable removal efficiency but also an excellent recycle performance in the treatment of DMF wastewater compared with free cells and simple material. As can be seen in Fig. 9, after recycled for 3 times, DMF could be removed completely within 14 h and 30 h for the initial DMF concentrations of 1000 mg/L and 2000 mg/L by poly(MAA-co-BMA)@P. denitrificans, respectively. It is worth noting that poly(MAA-co-BMA)@P. denitrificans still showed a poorer recycle performance than PGO@P. denitrificans obviously.
In order to analyze the SAB kinetic mechanisms, the kinetic data obtained from the batch experiments were investigated with pseudo-first-order and pseudo-second-order kinetic models, respectively.
The pseudo-first-order kinetic model can be expressed by the following equation:
which can be rearranged as:
where qt is the amount of DMF processed at time t (mg/g); qe is the amount of DMF processed at equilibrium (mg/g); and k1 is the rate constant of pseudo-first-order kinetic model (min−1). The qe and k1 values were obtained by plotting qt versus t.
The pseudo-second-order kinetic model of Ho and McKay can be written as follows:
which can be rearranged as:
where k2 is the rate constant of pseudo-second-order kinetic model (g/mg min). The qe and k2 values were calculated by plotting qt versus t.
The adsorption kinetic parameters were presented in Table 2. For the initial DMF concentration of 1000 mg/L, the correlation coefficient (R2) in pseudo-second-order model (0.998) was closer to 1.0 than that in pseudo-first-order model (0.959). Similarly, the correlation coefficient (R2) in pseudo-second-order model (0.996) was also higher than that in pseudo-first-order model (0.944) for the initial DMF concentration of 2000 mg/L. According to the values of R2, it can be concluded that adsorption kinetics fit better to the pseudo-second-order model than to the pseudo-first-order model.
The adsorption property of PGO@P. denitrificans after freeze-dried was studied subsequently and the result was shown in Fig. 10. As can be seen, for the same initial DMF concentration of 1000 mg/L, the maximal equilibrium adsorption amount of PGO@P. denitrificans was increased slightly than PGO (Fig. 3), which could be attributed to a small amount of DMF adsorbed onto the surface of bacterial cells.
Adsorption capacity of PGO@P. denitrificans (dry weight of PGO = 100 mg, initial DMF concentration = 1000 mg/L, volume of DMF solution = 50 mL and T = 30 oC).
Synthesis of GO with copolymers containing MAA and BMA was achieved to prepare a novel PGO via free radical solution polymerization. The PGO was used as an adsorbent as well as a carrier in the treatment of high-concentrated DMF. The PGO@P. denitrificans system could cleanse high-concentrated DMF (2000 mg/L) wastewater completely, which showed not only remarkable removal efficiency but also an excellent recycle performance compared with free cells and simple material. Moreover, PGO@P. denitrificans needed no pretreatment or regeneration procedure during the recycle process, which made the whole process more simple and practical. In summary, the two-step method based on SAB has a great prospect in the treatment process of wastewater containing high-concentrated DMF.
Tryptone and yeast extract were purchased from Suzhou Biogene Biotechnology Co.,Ltd. Graphite powder, sulfuric acid (H2SO4), hydrochloric acid (HCl), hydrogen peroxide (H2O2), dimethylacetamide (DMAC), triethylamine (TEA), methacryloyl chloride (MAC), azobisisobutyronitrile (AIBN), methacrylic acid (MAA), butyl methacrylate (BMA), N-hydroxy succinimide (NHS), N,N’-Dicyclohexylcarbodiimide (DCC), 4-dimethylaminopyridine (DMAP), cyclohexanone, petroleum ether, ether and inorganic salts were all in analytical reagent grade were commercially obtained from Sinopharm Chemical Reagent Co.,Ltd. and used as received without further treatment. HPLC grade methanol was purchased from Shanghai Qiangshun Chemical Reagent Co.,Ltd. HPLC grade DMF was obtained from Tedia Company Inc.
Before experiments, Luria Bertani (LB) liquid medium (Tryptone, 10 g/L; Yeast extract, 5 g/L; NaCl, 10 g/L), mineral salt medium (MM1) solution (K2HPO4, 6.3 g/L; KH2PO4, 1.8 g/L; MgSO4·7H2O, 0.1 g/L; MnSO4·4H2O, 0.1 g/L; CaCl2·2H2O, 0.1 g/L; FeSO4·7H2O, 0.1 g/L; NaMoO7·7H2O, 0.006 g/L), Phosphate Buffered Saline (PBS) solution and all instruments were autoclaved at 120 °C for 20 min and the DMF and glucose solution were separately sterilized by 0.22 μm membrane filter before use.
A pure strain of P. denitrificans (ATCC 19367) was purchased from Shanghai Fuxiang Biotechnology Co.,Ltd. Firstly, the bacterium was inoculated in the LB liquid medium and incubated at 30 °C and 150 r/min on the constant temperature oscillator (SHA-CA) until it grew into the logarithmic phase. The P. denitrificans was harvested by centrifuging at 6000 rpm for 10 min and then transferred in a 50 mL MM1 solution with 1000 mg/L of glucose (usually used as the source of carbon) and incubated at 30 °C, 150 r/min.
The acclimatization process was accomplished by increasing the DMF concentration (100 mg/L every time) gradually and in the meanwhile decreasing the glucose concentration (100 mg/L every time) gradually in MM1 solution until 0 mg/L. During this time, the strain was capable of utilizing DMF as a sole source of carbon and nitrogen. Constantly increased the DMF concentration up to 2000 mg/L and completed the acclimatization process. The acclimatized bacteria were used for next DMF biodegradation and immobilization experiments.
GO was prepared from graphite powder by a modified Hummers method reported in the previous study40,41. Briefly, graphite (3.0 g) and NaNO3 (1.5 g) were mixed in concentrated H2SO4 (69 mL) and the mixture was cooled using an ice bath to 0 °C. Then, KMnO4 (9.0 g) was added to the suspension slowly to keep the reaction temperature lower than 20 °C. The reaction system was warmed to 35 °C and vigorously stirred for 7 h. Next, additional KMnO4 (9.0 g) was added in one portion and the reaction was still stirred at 35 °C for 12 h. After that, the reaction mixture was cooled to room temperature and poured into ice water (400 mL), then 30% H2O2 (3 mL) was added dropwise to reduce the residual KMnO4 until no bubbles appeared and the color of solution from brown turned to yellow. Then the mixture was centrifuged and washed with HCl (5%) to remove metal ions and rinsed with deionized water repeatedly to remove acid. The product was dispersed in deionized water to make a GO aqueous dispersion and then purified by dialysis for two weeks to remove the salt impurities and remaining acid. Subsequently, the solution was centrifuged at 11000 rpm for 20 min to remove redundant impurities. Finally, the supernatant liquor was obtained as GO solution and then was dried in vacuum desiccator. The dried GO was used for the next experiments.
Poly(MAA-co-BMA) was prepared via free radical solution polymerization with MAA and BMA as monomers and AIBN as the initiator. The monomers mixture (MAA, 70 μL; BMA, 385 μL) and initiator (AIBN, 8 mg) were added into a 50 mL round-bottomed flask containing 10 mL cyclohexanone. Then, the reaction system was heated to 70 °C and stirred for 8 h under N2 atmospheric. Subsequently, the mixture was cooled to room temperature and precipitated in petroleum ether and then was filtered, washed completely with petroleum ether to remove the residual monomer and dried in vacuum desiccator to obtain poly(MAA-co-BMA).
PGO was prepared via free radical solution polymerization with MAA and BMA as monomers and AIBN as the initiator. Firstly, dried GO (100 mg) and TEA (268 μL) were dispersed in DMAC (40 mL) in a 100 mL round-bottomed flask equipped with a mechanical stirrer and constant pressure funnel (50 mL) that contained MAC (188 μL) and DMAC (20 mL). The TEA (TEA : MAC = 1: 1 in stoichiometric molar ratio) was used for neutralizing the HCl produced from the reaction. The mixture in the constant pressure funnel was added dropwise into the flask under N2 atmospheric conditions at 0 °C for 0.5 h. Then the reaction system was warm to room temperature and stirred for 24 h. Subsequently, the product was centrifuged, washed with acetone and dried to give 140 mg solid. Next, the resulting solid was dispersed in 20 mL DMF in a 50 mL round-bottomed flask equipped with a mechanical stirrer. After adding the monomers mixture (MAA, 70 μL; BMA, 385 μL) and the initiator (AIBN, 8 mg) into the flask, the reaction system was heated to 70 °C for 8 h under N2 atmospheric conditions. After the system was cooled to room temperature, the mixture was precipitated in ether and then was filtered, washed completely with ether to remove the residual monomer and dried in vacuum desiccator to obtain PGO.
Firstly, 50 mL of acclimatized bacterial cells were incubated at 30 °C in the LB liquid medium, then the free cells were centrifuged and washed with PBS solution for 3 times. Subsequently, dried PGO (100 mg) and NHS (100 mg) were disperse in DMF (40 mL) in a 100 mL round-bottomed flask. Then DCC (300 mg) and DMAP (DCC : DMAP = 1 : 1 in stoichiometric molar ratio) which were used as catalyst were added to the flask and stirred for 24 h at room temperature. Then the mixture was centrifuged and washed with PBS solution for 3 times and added to the bacteria suspension containing 50 mL PBS solution in 250 mL Erlenmeyer flasks. The immobilization process was carried out in the constant temperature oscillator at 30 °C and 150 r/min for about 24 h. The immobilization process of P. denitrificans cells onto poly(MAA-co-BMA) was consistent with that onto PGO. The PGO@P. denitrificans and poly(MAA-co-BMA)@P. denitrificans were used for next DMF adsorption-biodegradation studies.The amount of PGO coupled to the surface of P. denitrificans was estimated by determining the difference of dried PGO weight before and after immobilization.
All batch experiments were carried out to investigate the DMF adsorption performance in 250 mL Erlenmeyer flasks shaking in the constant temperature oscillator (SHA-CA).
The adsorption amount of DMF was calculated using the following equation:
where Q (mg/g) represents the adsorption amount of adsorbents, C0 (mg/L) is the initial DMF concentration, Ct (mg/L) is the residual DMF concentration at time t, V (L) denotes the volume of the solution and M (dry weight, g) is the dosage of adsorbents.
The concentration of DMF was determined against a calibration curve of standard DMF solutions of known concentration by high performance liquid chromatograph (HPLC, Agilent 1260 Infinity) using a Accurasil C18 column (4.6 mm × 150 mm inner diameter, 5 mm particle size) at 25 °C, G1311C pumps and Ultraviolet detector (1260 MWD) at 205 nm. The mobile phase consisted of 15 : 85 (v/v) methanol : water at a flow rate of 1 mL/min. And the samples were centrifuged and filtered through 0.22 μm membrane filters before injection. Cell growth was monitored by measuring the optical density (OD) in a UV-Vis spectrophotometer (TU-1901) at the wavelength of 600 nm. And dry cell mass could be known from the OD600 value by using a relation curve which was described by the known quantities. The pH value of solution was determined by a HANNA pH meter. Scanning electron microscopy (SEM) images were obtained on a Hitachi S-4800 electron microscope. Transmission electron microscopy (TEM) images were taken on a Hitachi H600 electron microscope. Fourier transform infrared spectroscopy (FT-IR) was performed on a Nicolet 4700 spectrometer (Thermo Fisher Scientific) in the range of 4000–500 cm−1 in KBr pellet at room temperature. Thermogravimetric analysis (TGA) was carried out using a TG209 F1 Libra thermal analyzer from room temperature to 600 °C with heating rate of 10 °C/min and a N2 flow rate of 200 mL/min.
How to cite this article: Zheng, Y. et al. Efficient simultaneous adsorption-biodegradation of high-concentrated N,N-dimethylformamide from water by Paracoccus denitrificans-graphene oxide microcomposites. Sci. Rep. 6, 20003; doi: 10.1038/srep20003 (2016).
Bromley-Challenor, K. C. A., Caggiano, N. & Knapp, J. S. Bacterial growth on N,N-dimethylformamide: implications for the biotreatment of industrial wastewater. J. Ind. Microbiol. Biotechnol. 25, 8–16 (2000).
Käfferlein, H. U. & Angerer, J. N-Methylcarbamoylated valine of hemoglobin in humans after exposure to N,N-dimethylformamide:evidence for the formation of methyl isocyanate? Chem. Res. Toxicol. 14, 833–840 (2001).
Article PubMed CAS Google Scholar
Shieh, D. B. et al. Mitochondrial DNA alterations in blood of the humans exposed to N,N-dimethylformamide. Chem. Biol. Interact. 165, 211–219 (2007).
Article CAS PubMed Google Scholar
Kim, T. H. et al. Synergistic hepatotoxicity of N,N-dimethylformamide with carbon tetrachloride in association with endoplasmic reticulum stress. Chem. Biol. Interact. 184, 492–501 (2010).
Article CAS PubMed Google Scholar
Ye, C. S., Wang, H. X., Huang, G. Q. & Qiu, T. Adsorption and desorption of DMF on macroporous resin NKA-II in the fixed bed. Chem. Eng. Res. Des. 91, 2713–2720 (2013).
Sanjeev Kumar, S., Santosh Kumar, M., Siddavattam, D. & Karegoudar, T. B. Generation of continuous packed bed reactor with PVA-alginate blend immobilized Ochrobactrum sp. DGVK1 cells for effective removal of N,N-dimethylformamide from industrial effluents. J. Hazard. Mater. 199/200, 58–63 (2012).
Vidhya, R. & Thatheyus, A. J. Biodegradation of dimethylformamide using bacillus subtilis. Microbiol. Res. 1, 10–15 (2013).
Swaroop, S., Sughosh, P. & Ramanathan, G. Biomineralization of N,N-dimethylformamide by Paracoccus sp. strain DMF. J. Hazard. Mater. 171, 268–272 (2009).
Article CAS PubMed Google Scholar
Sanjeevkumar, S., Nayak, A. S., Santoshkumar, M., Siddavattam, D. & Karegoudar, T. B. Paracoccus denitrificans SD1 mediated augmentation with indigenous mixed cultures for enhanced removal of N,N-dimethylformamide from industrial effluents. Biochem. Eng. J. 79, 1–6 (2013).
Veeranagouda, Y., Emmanuel Paul, P. V., Gorla, P., Siddavattam, D. & Karegoudar, T. B. Complete mineralisation of dimethylformamide by Ochrobactrum sp. DGVK1 isolated from the soil samples collected from the coalmine leftovers. Appl. Microbiol. Biotechnol. 71, 369–375 (2006).
Article CAS PubMed Google Scholar
Yang, N. et al. Toxicity formation and distribution in activated sludge during treatment of N,N-dimethylformamide (DMF) wastewater. J. Hazard. Mater. 264, 278–285 (2014).
Article CAS PubMed Google Scholar
El-Naas, M. H., Al-Muhtaseb, S. A. & Makhlouf, S. Biodegradation of phenol by Pseudomonas putida immobilized in polyvinyl alcohol (PVA) gel. J. Hazard. Mater. 164, 720–725 (2009).
Article CAS PubMed Google Scholar
Qiao, L., Wen, D. H. & Wang, J. L. Biodegradation of pyridine by Paracoccus sp. KT-5 immobilized on bamboo-based activated carbon. Bioresour. Technol. 101, 5229–5234 (2010).
Chen, H. Y., Guan, Y. X. & Yao, S. J. A novel two-species whole-cell immobilization system composed of marine-derived fungi and its application in wastewater treatment. J. Chem. Technol. Biotechnol. 89, 1733–1740 (2014).
Article ADS CAS Google Scholar
Matsui, Y. et al. Adsorption capacities of activated carbons for geosmin and 2-methylisoborneol vary with activated carbon particle size: Effects of adsorbent and adsorbate characteristics. Water Res. 85, 95–102 (2015).
Article CAS PubMed Google Scholar
Travlou , NA , Kyzas , GZ , Lazaridis , NK & Deliyanni , EA Functionalization of graphite oxide with magnetic chitosan for the preparation of a nanocomposite dye adsorbent .Language 29, 1657–1668 (2013).
Article CAS PubMed Google Scholar
Khin, M. M., Nair, A. S., Babu, V. J., Murugan, R. & Ramarkrishna, S. A review on nanomaterials for environmental remediation. Energy Environ. Sci. 5, 8075–8109 (2012).
Yang, K. J., Chen, B. L. & Zhu, L. Z. Graphene-coated materials using silica particles as a framework for highly efficient removal of aromatic pollutants in water. Sci. Rep. 5, 11641 (2015).
Article ADS CAS PubMed PubMed Central Google Scholar
Qi, X. Y., Tan, C. L., Wei, J. & Zhang, H. Synthesis of graphene–conjugated polymer nanocomposites for electronic device applications. Nanoscale 5, 1440–1451 (2013).
Article ADS CAS PubMed Google Scholar
Liu, J. Q. et al. Fabrication of flexible, all-reduced graphene oxide non-volatile memory devices. Adv. Mater. 25, 233–238 (2013).
Article PubMed CAS Google Scholar
Tan, C. L., Huang, X. & Zhang, H. Synthesis and applications of graphene-based noble metal nanostructures. Mater. Today 16, 29–36 (2013).
Liu, J. Q. et al. Multilayer stacked low-temperature-reduced graphene oxide films: preparation, characterization and application in polymer memory devices. Small 6, 1536–1542 (2010).
Article CAS PubMed Google Scholar
Yin, Z. Y. et al. Real-time DNA detection using Pt nanoparticle-decorated reduced graphene oxide field-effect transistors. Nanoscale 4, 293–297 (2012).
Article ADS CAS PubMed Google Scholar
Sun, G. Z. et al. Hybrid fibers made of molybdenum disulfide, reduced graphene oxide and multi-walled carbon nanotubes for solid-state, flexible, asymmetric supercapacitors. Angew. Chem. Int. Ed. 54, 4734–4739 (2015).
Jiao. T. F. et al. Facile and scalable preparation of graphene oxide-based magnetic hybrids for fast and highly efficient removal of organic dyes. Sci. Rep. 5, 12415 (2015).
Apul, O. G., Wang, Q., Zhou, Y. & Karanfil, T. Adsorption of aromatic organic contaminants by graphene nanosheets: comparison with carbon naontubes and activated carbon. Water Res. 47, 1648–1654 (2013).
Article CAS PubMed Google Scholar
Wang, F., Haftka, J. J. H., Sinnige, T. L., Hermens, J. L. M. & Chen, W. Adsorption of polar, nonpolar and substituted aromatics to colloidal graphene oxide nanoparticles. Environ. Pollut. 186, 223−233 (2014).
Wang, J., Chen, Z. M. & Chen, B. L. Adsorption of polycyclic aromatic hydrocarbons by graphene and graphene oxide nanosheets. Environ. Sci. Technol. 48, 4817–4825 (2014).
Article ADS CAS PubMed Google Scholar
Chen, X. X. & Chen, B. L. Macroscopic and Spectroscopic Investigations of the adsorption of nitroaromatic compounds on graphene oxide,reduced graphene oxide,and graphene nanosheets. Environ. Sci. Technol. 49, 6181−6189 (2015).
Article ADS CAS PubMed Google Scholar
Chen, Y. Q., Chen, L. B., Bai, H. & Li, L. Graphene oxide-chitosan composite hydrogels as broad-spectrum adsorbents for water purification. J. Mater. Chem. A 1, 1992–2001 (2013).
Sui, Z. Y., Cui, Y., Zhu, J. H. & Han, B. H. Preparation of three-dimensional graphene oxide-polyethylenimine porous materials as dye and gas adsorbents. ACS Appl. Mater. Interfaces 5, 9172–9179 (2013).
Article CAS PubMed Google Scholar
Shi, H. C., Li, W. S., Zhong, L. & Xu, C. J. Methylene blue adsorption from aqueous solution by magnetic cellulose/graphene oxide composite:equilibrium,kinetics,and thermodynamics. Ind. Eng. Chem. Res. 53, 1108–1118 (2014).
Wu, Z. B. et al. Adsorptive removal of methylene blue by rhamnolipid-functionalized graphene oxide from wastewater. Water Res. 67, 330–344 (2014).
Article CAS PubMed Google Scholar
Shen, Y. & Chen, B. L. Sulfonated graphene nanosheets as a superb adsorbent for various environmental pollutants in water. Environ. Sci. Technol. 49, 7364–7372 (2015).
Article ADS CAS PubMed Google Scholar
Pastrana-Martínez, L. M., Morales-Torres, S., Figueiredo, J. L., Faria, J. L. & Silva, A. M .T. Graphene oxide based ultrafiltration membranes for photocatalytic degradation of organic pollutants in salty water. Water Res. 77, 179–190 (2015).
Article PubMed CAS Google Scholar
Taherkhani, S., Mohammadi, M., Daoud, J., Martel, S. & Tabrizian, M. Covalent binding of nanoliposomes to the surface of magnetotactic bacteria for the synthesis of self-propelled therapeutic agents. ACS Nano 8, 5049–5060 (2014).
Article CAS PubMed Google Scholar
Li, N. J. et al. A reusable immobilization matrix for the biodegradation of phenol at 5000 mg/L. Sci. Rep. 5, 8628 (2015).
Article CAS PubMed PubMed Central Google Scholar
Kalia, J. & Raines, R. T. Advances in bioconjugation. Curr. Org. Chem. 14, 138–147 (2010).
Article CAS PubMed PubMed Central Google Scholar
Perreault, F., de Faria, A. F., Nejati, S. & Elimelech, M. Antimicrobial properties of graphene oxide nanosheets: why size matters. ACS Nano 9, 7225–7236 (2015).
Marcano, D. C. et al. Improved synthesis of graphene oxide. ACS Nano 4, 4806–4814 (2010).
Article CAS PubMed Google Scholar
Zhu, Y. W. et al. Graphene and graphene oxide:synthesis,properties,and applications. Adv. Mater. 22, 3906–3924 (2010).
Article CAS PubMed Google Scholar
This work was supported by Collaborative Innovation Center of Suzhou Nano Science and Technology. The authors gratefully acknowledge the financial support provided by National Natural Science Foundation of China (21336005, 21301125), Natural Science Foundation of Jiangsu Province (BK2012625), Suzhou Nano-project (ZXG2013001, ZXG2014020) and Natural Science Foundation of the Education Committee of Jiangsu Province (15KJB150026).
College of Chemistry, Chemical Engineering and Materials Science, Collaborative Innovation Center of Suzhou Nano Science and Technology, Soochow University, Suzhou, 215123, China
Yuan Zheng, Dongyun Chen, Najun Li, Qingfeng Xu, Hua Li, Jinghui He & Jianmei Lu
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
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
J.L. and D.C. conceived the project; Y.Z. designed and performed the experiments; N.L., Q.X., H.L. and J.H. contributed to data analysis; Y.Z. prepared the manuscript. All the authors reviewed the manuscript.
The authors declare no competing financial interests.
This work is licensed under a Creative Commons Attribution 4.0 International License. The images or other third party material in this article are included in the article’s Creative Commons license, unless indicated otherwise in the credit line; if the material is not included under the Creative Commons license, users will need to obtain permission from the license holder to reproduce the material. To view a copy of this license, visit http://creativecommons.org/licenses/by/4.0/
Zheng, Y., Chen, D., Li, N. et al. Efficient simultaneous adsorption-biodegradation of high-concentrated N,N-dimethylformamide from water by Paracoccus denitrificans-graphene oxide microcomposites. Sci Rep 6, 20003 (2016). https://doi.org/10.1038/srep20003
DOI: https://doi.org/10.1038/srep20003
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
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.
Scientific Reports (Sci Rep) ISSN 2045-2322 (online)
Chloroauric Acid Sign up for the Nature Briefing newsletter — what matters in science, free to your inbox daily.