Skip to main content
PMC home page
Scientific Reports logoLink to Scientific Reports
. 2018 Dec 3;8:17560. doi: 10.1038/s41598-018-35656-1

Efficacy of engineered GO Amberlite XAD-16 picolylamine sorbent for the trace determination of Pb (II) and Cu (II) in fishes by solid phase extraction column coupled with inductively coupled plasma optical emission spectrometry

Hina Javed 1, Aminul Islam 1,✉, Anjali Chauhan 1, Suneel Kumar 1, Sushil Kumar 2
PMCID: PMC6277385  PMID: 30510289

Abstract

Graphene oxide (GO) was immobilized innovatively through azo spacer arm onto the surface of polymeric Amberlite XAD-16 resin in order to expose all oxygen functionalities freely available for metal ions coordination and further modification with picolylamine which governs selectivity. The GO Amberlite XAD-16 picolylamine enables the development of SPE column coupled with ICP-OES for preconcentration and determination of Pb (II) and Cu (II) in water and fish samples. Elution was performed by mild acid (2M HCl) no other carcinogenic organic solvent was used, prevents ligand leaching. Under optimized conditions, the preconcentration factors of 150 and detection limits 1.434 and 0.048 µg L−1 for Pb (II) and Cu (II)  were obtained respectively.

Introduction

Graphene Oxide (GO), one of the derivatives of graphene1–3, but now has written its own history in the field of material chemistry such as environmental applications of water treatment4,5. GO readily disperses in water to form stable colloidal dispersions, facilitating mainly its carboxyl, hydroxyl groups to readily dissociate into their anionic forms in aqueous systems6–9. It maintains its negative surface charge down to very low values of pH. Combining with this huge surface area to mass ratio provided by the sheets, attributed to the fact that, why investigations into the use of GO as an adsorbent material has a plethora of the removal of toxic metals from aquatic environments6,8. In spite of many standard analytical methods for the determination of metal ions in real samples, development of another new selective method is at the forefront due to variation of sample matrices and concentration level of analyte which influences interferences and detection limit parameters respectively. Analytical techniques with superior detection limits frequently require separation methods to eliminate interferences and less sensitive one need preconcentration10. Solid phase extraction (SPE) addresses both these issues along with advantages such as low cost, high efficiency, rapid phase separation, ease of operation, excellent recovery of the sorbed analyte with small volumes of mineral acids rather than toxic organic solvents and reusability11. Moreover, this method can be easily incorporated with other spectroscopic techniques like FAAS, ICP-OES etc. in offline and online modes. ICP-OES exhibits higher sensitivity, large dynamic linear range, low detection limits, and simultaneous analysis12. Despite the aforementioned facts, determination of the trace metals in environmental samples by ICP-OES constitutes one of the major problems of interferences in direct determination. Therefore, their determination is coupled with SPE in order to exclude all interfering matrices. GO serve as a potential candidate over graphene or any other currently reported sorbents like CNT13–16, sulfur nanoparticle17, activated carbon18 etc. due to its ultra-high sorption capacities for various metal ions19. This is attributed to the fact that GO has an exceptional morphology and properties, all carbon atoms are characterized by oxygen functionalities on its either side in a planar geometry, renders its hydrophilicity, chemical reactivity and huge surface area20,21. These groups coordinate with metal ions through sharing of a lone pair of electrons, exposing it’s both sides for coordination to the available surrounding and enabling fast metal ion sorption and elution22. Although, huge success has been achieved by employing GO as an ideal sorbent, yet possesses some limitations. For instance, separation and recycling of GO for its direct and multiple uses, becomes challenging. GO tends to aggregate in a batch method, due to the strong van der Waals and π-π stacking which can significantly affect the efficiency and reusability of GO as it requires sonication and ultracentrifugation before its use in the next sorption cycle and also the complete collection of GO sheets from aqueous solution is insurmountable even with the 0.22 µm cellulose membrane23. Henceforth, fabrication with magnetic nanoparticles Fe3O424 and further modification through covalent bonding with TETA25, Polyimide26 has somehow been able to resolve these issues of using direct GO in batch technique. Magnetic nanoparticles occupy some surface sites on GO and reduces binding sites available for metal ions resulting in a decrease in sorption capacity27 and number of regeneration cycles28,29. Moreover, the restriction of using large sample volume for metal ion preconcentration remains a challenge in batch method. These problems can be resolved by choosing a column method owing to its significant number of theoretical plates needed for good extraction, higher preconcentration factor, large number of regeneration cycles and possible on-line automation with different determination techniques30. However, SPE column loaded with GO sheets generates high back pressure and may escape to the environment and has been found to report Parkinson’s disease like symptoms in zebra fish larvae31. Efforts were made to deal with these limitations by immobilizing GO through covalent coupling onto a solid support such as silica22 while glycidylmethacrylate32 and polystyrene divinylbenzene via spacer arm by utilising its carboxylic functionalities23. One of the drawbacks of utilizing carboxylic group through solid support is that its oxygen group will not be available for coordination to metal ions as well as for further functionalization through a ligand in order to get selectivity. Therefore, a novel and innovative approach is developed by immobilizing GO onto the surface of Amberlite XAD-16 resin through azo coupling with the objective of exposing all freely available oxygen functionalities for metal ion coordination and further modification with picolylamine in order to improve selectivity. The synthesized sorbent was employed for the development of SPE column coupled with ICP-OES for preconcentration and determination of Pb (II) and Cu (II) in both water sample as well as different animal tissues (muscle, liver, brain, kidney etc.) of fishes. Fishes are preferred because of their longer survival in polluted water bodies and have more chances of metal contamination.

Results and Discussion

Characterization

To study the surface modification of GO, the FT-IR spectra of (GO AXAD-16 picolylamine) GOXPA was inspected (Fig. 1). The most prominent sharp peak at 3331 cm−1 is attributed to NH stretching vibration of amide bond indicating the coupling of GO and picolylamine33,34. The band at 1580 cm−1 assigned to the azo (-N=N) stretching which confirmed the immobilization of GO onto AXAD-16 resin through azo spacer arm33,34. The peak at 1627 cm−1 corresponds to (-C=O). Additionally, peaks structured at 1314, 1241 and 759 cm−1, are associated with stretching of (-C-N, -C-O and pyridine ring) vibration of picolylamine respectively35. Moreover, the peak appearing at 639 cm−1 is assigned to (-N-H) wagging. The immobilization of GO onto the AXAD −16 resin was also confirmed by SEM micrograph. As it can be seen, the surface of AXAD-16 was disorderly covered by GO nano sheets (Fig. 2A–C). The EDS results (Fig. 2D–G) procured from SEM images of GOXPA and their elemental mapping showing spots of homogenous distribution of C (66.15%), N (16.12%), O (12.08%) revealing the presence of azo spacer arm and picolylamine. Furthermore, appearance of GO onto AXAD-16 was also confirmed by TEM image (Fig. 2H). In the selected area electron diffraction (SAED) pattern of GOXPA (Fig. 2I) the diffraction dots are not present, indicating the amorphous nature of GOXPA, which may describe the presence of oxygen functionalities on GO surface. The surface area of GOXPA investigated after adsorption and desorption of nitrogen using BET method, was found to be 134 m2 g−1 which was higher than reported earlier for the immobilized GO on to the solid support23,32,36. 13C NMR of GOXPA was also analyzed and observed a chemical shift in the spectrum showing the presence of amide bond (155 ppm), -CH2-NHR (45 ppm), benzylic −C−NHR (38 ppm), styrenic −CH and −CH2 (23,33 ppm), carboxylic carbon (165 ppm), -C-N=N-C- (126 ppm)23,32 (Supplementary Fig. S1). The TGA/DTA curve of GOXPA depicts a significant weight loss due to the desorption of adsorbed interstitial water molecules around 170 °C. Then GOXPA exhibit gradual decrease in weight up to 210 °C which may be attributed to the loss of CO and CO2 from decomposition of its oxygen functionalities which was supported by DTA endothermic curve suggesting its stability up to 210 °C. Then, a sharp weight loss observed around 420 °C illustrates lowering in its thermal stability (Supplementary Fig. S2).

Figure 1.

Figure 1

Open in a new tab

FT-IR spectrum of GOXPA.

Figure 2.

Figure 2

Open in a new tab

SEM images of (A) cluster of GOXPA resin beads (B) single GOXPA resin bead (C) GO sheets (D–G) Elemental mapping images of C, O and N respectively (H) TEM image of GOXPA (I) SAED pattern.

Optimization

pH Effect

It is experimentally found that the metal ion sorption is governed by protonation and deprotonation of available binding sites of functional groups of a sorbent and metal species present in the aqueous solution. Moreover, the suitable pH not only raises the adsorption capacity of metal ion but also reduces the interferences of coexisting ions. Therefore, pH plays a key role in the adsorption and desorption of metal ion. The efficacy of adsorption of Pb (II) and Cu (II) on to the GOXPA was revealed by plotting sorption capacity as a function of pH (Supplementary Fig. S3). The surface charge of GOXPA was further explained by point zero charge studied by the procedure as reported in the previous literature32. The point zero charge obtained from the plot of ∆pH vs pHi was found to be 4.3. If pH < pHpzc then surface of a sorbent is positively charged and if pH > pHpzc then surface is negatively charged32. Thus, the surface of GOXPA is negatively charged and it shows electrostatic interactions with metal ions. At higher acidic condition the adsorption capacity decreases because the binding sites on GOXPA were protonated and undergo electrostatic repulsion when a metal species approached to it, resulting in poor adsorption of Pb (II) and Cu (II). However, the adsorption capacity increases from 3.6 to 4.6 and shows maximum adsorption at pH 5.6. This is attributed to the fact that the positively charged density generated on binding sites now starts decreasing and left partially unprotonated resulting in the decrease in repulsion between binding sites of GOXPA and the metal cation. Pb (II) and Cu (II) found in different forms at different pH values. Here the predominated species are (Pb2+ and PbOH+, and Cu2+, CuOH+). Following higher pH (>8) it was investigated that Pb shows higher sorption capacity which is due to the contribution of co precipitation (Pb (OH)2 of Pb (II) apart from electrostatic and chelate effect. Hence, pH 5.6 was used for further experimental studies of both Pb (II) and Cu (II)37. Although, the adsorption capacity of GO was reported to be very high for transition metals19. However, when GO is incorporated on to support, capacity was shown to be decreased22,32,38 since incorporation of a support material on to GO is requested in order to resolve some limitations attached with the direct use of GO in column.

Sample flow rate

The optimization of a sample flow rate is an important parameter for the sorption and elution of Pb (II) and Cu (II) onto the GOXPA. Therefore, effect of flow rate of sample solution was investigated by passing 5 µg of Pb (II) and Cu (II) in 50 mL of an aqueous solution buffered at pH 5.6 through the column in the range of 3–7 mL min−1 (Fig. 3). In all flow rates Pb (II) observed to be kinetically faster than Cu (II). It was observed that both metal ions could be recovered quantitatively (>98%) in the range of flow rate 3–5 mL min−1. At the flow rate of 5 mL min−1 recoveries were found to be 103 and 99% for Pb (II) and Cu (II), respectively. However, at a higher flow rate of 7 mL min−1 efficiency was reduced to 87% and 77.3% this may be due to the less interaction time of Pb (II) and Cu (II) with the sorbent. To enhance the analytical speed, an eluent flow rate of 5.0 mL min−1 was optimized in this work.

Figure 3.

Figure 3

Open in a new tab

Sample (GOXPA) flow rate.

Elution studies and Reusability

To evaluate the effect of eluent type, concentration and volume on the recovery studies of Pb (II) and Cu (II), various eluting agents such as HCl, HNO3 and H2SO4 of different concentrations(1,1.5 and 2 M) were employed while keeping the elution volume constant i.e. 5 mL. Elution studies revealed that Pb (II) and Cu (II) can be quantitatively eluted by 5 mL of 2 M HCl with recovery of 103 and 99% respectively which is highest among the eluting agents tested. The interaction between an analyte and a chelating group can be easily destroyed by protonation of available binding sites leading to the elution of the analyte. Since HCl and HNO3 can easily dissociate their H+ ion in aqueous solution and can form an ionic bond with metal ion than H2SO4 acid. Such a low volume and concentration (5 mL of 2M HCl) gave efficient recoveries. Quantitative elution was not achieved by smaller volume (<5 mL) and lower concentration (<2 M). However, it was attained by 7 to 10 mL of 2M HCl but at the expense of preconcentration factor. In order to get a good preconcentration factor volume of an eluent is kept as small as possible. Therefore, 5 mL of 2M HCl was used for elution studies. As shown in graph (Fig. 4). Reusability test was performed on the GOXPA for the successive sorption and elution of analytes having concentration 100 µg L−1, volume 50 mL at a 5 mL min−1. The results indicated that the resin can be used for quantitative sorption and elution up to 50 cycles as no significant loss in sorption capacity was found and >96% recoveries were obtained. This may be attributed to the structural rigidity of the sorbent which is due to the presence of azo spacer arm. Additionally, the elution was performed by using mild acid (2M HCl) so it does not cause any leaching of ligand. However, slight loss in capacity was assessed for both Pb (II) and Cu (II) (94 and 91% recoveries) respectively for over 55 cycles. It was concluded that the resin GOXPA, could be re-used up to 50 cycles.

Figure 4.

Figure 4

Open in a new tab

Elution studies (a,b).

Interference studies

The real sample usually contains more than one metallic species. Therefore, it is necessary to evaluate the sorption behavior under competitive conditions, which may be either through a redox reaction or by competition for complex formation. In general, cationic matrices compete for the active binding sites of the sorbent with the analyte ion whereas anionic part will compete for analyte with sorbent resulting in a decrease of sorption capacity of target metal ion. The interference to analyte ratio for various alkali, alkaline earth and transition metal ions was investigated by preconcentrating a trace quantity of Pb (II) and Cu (II) (5 µg), 0.1 g resin, pH 5.6, flow rate 5 mL min−1 in the presence of a large amount of interfering ions. It was found that no significant effect was there on preconcentration of Pb (II) and Cu (II) up to (3–6 folds) of the added ions as the recovery was >96% for both ions (Table 1).

Table 1.

Effect of Foreign species under optimized conditions.

Interfering ions Added as Interferent to analyte ratio Mean % Recovery Cu (II) RSDa N = 3 Mean % Recovery Pb (II) RSD N = 3
Cd CdCl2 3 99.7 0.56 99.5 0.71
6 96.0 1.47 98.0 1.44
Ni Ni(NO3)2 3 99.0 1.42 100.2 0.28
6 95.8 1.18 99.5 0.42
Co Co(NO3)2 3 99.2 0.21 99.9 0.14
6 96.1 3.09 98.6 0.57
Zn ZnCl2 3 99.3 0.42 99.8 0.14
6 98.5 0.71 99.3 0.14
Cu Cu(NO3)2 3 — — 98.7 0.14
6 — — 97.4 0.36
Pb Pb(NO3)2 3 97.1 0.43 — —
6 97.0 1.45 — —
NaCl Na+ 5 × 104 102.4 0.82 103.7 0.13
Cl− 2 × 104 99.9 0.14 100.2 0.56
Na2SO4 SO42− 1 × 104 99.8 1.13 99.9 1.55
KCl k+ 1 × 104 103.2 0.82 100.5 0.14
MgCl2 Mg2+ 2 × 104 103.3 0.13 101.2 1.39
Open in a new tab

aRelative standard deviation.

Preconcentration

Direct determination of metal ions in a real sample is insurmountable due to their low concentration therefore needs preconcentration prior to their determination. In order to study the quantitative recovery of Pb (II) and Cu (II) by keeping the metal ions loading constant at 5 µg, we continuously increase the sample volume and found the quantitative recoveries of Pb (II) and Cu (II) up to a sample volume of 750 mL (101.1 and 99.2%). When the volume was further increased to 1000 mL, the recoveries were reduced to (92.2 and 89.7%) for Pb (II) and Cu (II) respectively. Hence, the preconcentration factor was calculated as 150 with a preconcentration limit of 6.7 µg L−1 for both Pb (II) and Cu (II).

Comparative studies of GOXPA with other SPE method

Although, the adsorption capacity of GO was reported very high for transition metals19. However, when GO is incorporated on to solid support, capacity was shown to decreased22,32,38 since, incorporation of a support material on to GO is requested in order to resolve some limitations attached with direct use of GO in column or batch. This is quiet paramount that only a small quantity of GO is immobilized onto a long polymeric styrene support material through azo spacer arm without utilizing any oxygen functionality, used in column operation. The results of the current study based on some separation/preconcentration of Pb (II) and Cu (II) are compared with other proposed method (Table 2). The comparative data indicating the superiority of our work over others regarding sorption capacity, detection limit, preconcentration factor, elution studies of the system apart from inherent advantages of column operation and reusability.

Table 2.

Comparison of figure of merits with previously reported GO based column SPE method.

Sorbents Analytes SCa (mg g−1) LODb (µg L−1) Eluents PFc Techniques Applications Reference
GOXPA Pb, Cu 51.8,17.4 1.43, 0.048 5 mL (2M HCl) 150 ICP-OES Battery effluent, Fish samples This work
Dithizone immobilized silica gel Cu 0.76 0.2 10% HNO3 43 FAAS Water samples 42
Sulfur nanopartice Cu, Pb 3.55, 4.69 0.24, 0.63 3 mL(3.0M HNO3) in methanol 158.0, 175.0 FAAS Marine samples 43
GO-TBCPA Cu 6.0 0.63 3M HNO3 250 FAAS Water, blood, tomato, spinach and soil samples 44
GO@SiO2 Pb, Cu 13.6,6.0 0.27,0.084 2 mL (2M HNO3) 200, 250 FAAS water sample 22
Graphene with dithizone Pb 16.6 0.61 2 mL (2M HNO3) 125 FAAS water and vegetable samples 45
GO-TiO2 Cu, Pb, 0.8, 13.5, 0.48, 2.64 1.5 mL (0.5M HNO3) 10 ICP-OES Environmental sample 46
GO-MCNTs-DETA Pb 6.6 0.24 2 mL (2M HCl) 75 ICP-OES Wastewater samples 38
Polycarboxylic microsphere polymer gel Cu, Pb — 0.01,0.02 2M HNO3 50–150 FAAS, ETAAS Sea water, Mineral water 47
Nanometer-sized ZrO2 Cu 1.3 0.058 3M HCl 25 ICP-OES Dried fish and water 12
Dithizone modified TiO2 nanoparticle Pb 22.5 1.72 1.5 mL (0.25M HCl) — ICP-AES Food stuff & Plant sample 48
Acrylic acid grafted polytetrafluorethane fibers Pb 213 0.26 1.0M HNO3 49 FAAS environmental and biological samples 49
Cu(II)-imprinted styrene–divinylbenzene Cu 9.55 1.03 0.5% HNO3 12 FAAS Water sample 50
Silica gel Pb 27.1 0.60 20.0 mL of 0.10 mol/L HNO3 — FAAS Water sample 51
Multi-walled carbon nanotubes Pb — 0.0028 0.3M HNO3 26 HG-AFS water sample 52
GO–silica Cu, Pb — 0.023, 0.028 0.1M (0.5 M HNO3) 120 ICP-MS Environmental water sample 53
PS GO Pb 227.92 2.3 5 mL (2M HCl) 400 FAAS Water and food 23
Open in a new tab

asorption capacity, blimit detection, cpreconcentration factor.

Method Validation

The validity of a new method is checked by assessing parameters such as calibration, precision, limit of detection (LOD), limit of quantification (LOQ), accuracy and robustness under optimized column conditions. The linearity of calibration curve plotted by least square method after preconcentrating the series of standards for Pb (II) and Cu (II), was reported linear having correlation coefficient (R2), regression equation; and concentration range (µgL−1) as 0.9953, A = 13.9212*xpb + −0.0567, 6.7–20000 and 0.9952, A = 1091.4904*xcu + 2.0125 and 6.7–5000 respectively. The relative standard deviation characterizing for precision of the proposed method, analyzing for five replicate synthetic samples of 5 µg Pb (II) and Cu (II) in 50 mL, were found to be <5%. IUPAC defined (LOD) and (LOQ) as 3 S/m and 10 S/m39 of mean blank signal for 20 replicates, were found to be 1.434, 4.782 µg L−1 and 0.048, 0.160 µg L−1 for Pb (II) and Cu (II) respectively. Accuracy, assessed by analyzing an SRM following Student’s t test values calculated for Pb (II) and Cu (II) were less than the critical Student’s t value of 4.303 at 95% confidence level for N = 3 (Table 3). The observed mean concentration was not significant statistically when compared with the certified values, describing the absence of systematic errors. Reliability is strongly requested for the developed method which was studied by spiking with a known amount of 5 µg of analyte into the different fish samples and battery waste water. The percentage recoveries were checked for the spiked analytes and found to be (95–103.82%) having a relative standard deviation (RSD) < 5% in maximum results (Table 4).

Table 3.

SRM analysis under optimized column conditions.

SRM Certified value (µg g−1) Found value (µg g−1)a (RSD) Calculated Student’s t test valueb
Rompin hematite JSS (800–3) Pb: 210 Pb: 203.8(1.63) Pb: 3.21
Cu: 640 Cu: 621.8(1.37) Cu: 3.69
Open in a new tab

aMean value, b95% confidence limit, N = 3.

Table 4.

ICP-OES determination of Pb (II) and Cu (II) in fish tissues samples and battery effluent after Column Preconcentration under optimized conditions.

Samples Amount spiked Pb(II), Cu (II) (µg) Amount found Pb (II) (µg g−1) Mean %recovery Pb (II) (µg g−1) RSDa N = 3 Amount found Cu (II) (µg g−1) Mean %recovery Cu (II) (µg g−1) RSDa N = 3
Labeo rohita
Kidney 0 0.85 — 4.55 0.21 — 4.02
5 5.47 95.6 2.4 5.3 98.6 2.73
10 10.54 104.4 2.59 9.88 96.8 1.81
Liver 0 0.18 — 4.5 0.27 — 3.46
5 5.22 102 1.31 5.14 95 4.4
10 10.68 98.3 4.53 10.47 101.6 3.31
Muscle 0 0.14 — 4.44 0.12 — 4.09
5 5.1 95.6 3.99 5.07 97.7 1.07
10 9.64 100.2 2.69 9.49 98.4 3.98
Brain 0 0.65 — 4.95 0.22 — 4.14
5 5.58 98 2.45 5.27 100.1 2.45
10 10.96 100 3.43 10.7 103.5 4.91
Gills 0 0.21 — 3.31 0.12 — 3.28
5 5.11 95.9 3.64 5.18 97.3 3.62
10 9.93 104.8 3.5 10.01 100.9 2.06
Channa punctatus
Kidney 0 8.66 — 5.21 0.47 — 5.3
5 13.61 102 3.88 5.4 98.8 1.29
10 17.93 98 2.84 10.42 104.1 2.74
Liver 0 6.34 — 4.21 1.35 — 4.94
5 11.16 97.8 1.87 6.34 96.9 3.88
10 16.67 96.7 4.61 11.67 95.1 4.85
Muscle 0 1.09 — 5.5 2.35 — 5.4
5 6.06 98.74 2.05 7.32 103.8 4.26
10 11.25 102.9 1.56 13.22 104.6 3.73
Brain 0 9.8 — 3.9 0.69 — 4.91
5 15.01 102.4 4.44 5.73 98.8 3.45
10 20.24 101.2 3.35 10.13 95.6 2.28
Gills 0 13.47 — 4.3 0.56 — 1.32
5 18.37 99.54 2.14 5.14 96.7 4.19
10 22.81 96.4 2.99 10.58 98.1 2.94
Battery waste
Effluent 0 1.76 — 4.13 1.1 — 4.54
5 6.85 95.8 2.86 6.25 101.8 1.97
10 12.23 103.3 3.71 11.45 99.7 3.5
Open in a new tab

Robustness of the method was checked by tuning the pH 5.6 to pH 5.6 ± 0.5 and flow rate 5 to 5 ± 0.5 mL min−1 of the solution no significant change in the recovery was found (>96%) for Pb (II) and Cu (II) respectively.

Materials and Methods

Reagents and solutions

All chemicals were procured from the analytical reagent. Graphite powder (50 µm) was obtained from Otto Chemie Pvt. Ltd. (Mumbai, India). Amberlite XAD-16 (AXAD-16) (particle size 20–60, pore size 100 Å, pore volume 1.82 mL g−1, and surface area 800 m2 g−1) and (2-picolylamine) were purchased from Sigma-Aldrich (Steinem, Germany). All aqueous solutions were prepared in deionized water. Rompin hematite JSS (800-3) obtained from the Iron and Steel Institute of Japan (Tokyo, Japan) was used as a standard reference material (SRM). Buffer solutions were prepared by suitable amounts of HCl-glycine for pH 2.6, acetic acid-sodium acetate for pH 3.6–5.6 and ammonia-ammonium chloride for pH 8.0–10.0. Metal stock solutions of Pb (II) and Cu (II) (1000 mg L−1) were purchased from Merck (Darmstadt, Germany). HNO3, HCl, HClO4 and H2O2 were obtained from Merck (Mumbai, India).

Instrumentation

Optimized column procedure for preconcentration/determination of metal ions

A column was packed with 0.1 g of GOXPA resin. The column was preatreated by passing 5 mL of buffer solution at pH 5.6 before subjected to experimental studies. Sample solution containing 5 µg Pb (II) and Cu (II) having pH 5.6 was allowed to pass through the column at a flow rate of 5 mL min−1. Elution of sorbed metal ions were done by 5.0 mL of 2M HCl followed by determination with ICP-OES. For the determination of Pb (II) and Cu (II) an inductively coupled plasma optical emission spectrometer (ICP–OES), Thermo Scientific (iCAP 7000 series, Waltham, USA) was used at the wavelengths 220, 353 and 324.754 nm respectively. Glass column 15 mm (8 mm × 100 mm) used for experimental studies obtained from J-SIL Scientific Industries (Agra, UP, India). The pH meter from Thermo Scientific (Orion 2 star, Waltham, MA, USA) was used for pH measurement. FT-IR spectral studies were analysed on a PerkinElmer Spectrum (Waltham, MA, USA), using a KBr disk method lies in the range between 500 and 4000 cm−1 with the resolution of 2.0 cm−1. Quantachrome Instrument (Boynton Beach, FL, USA) for Brunauer-Emmett-Teller (BET) surface area analysis. Shimadzu TGA/DTA simultaneous measuring instrument, (DTG-60/60 H, Kyoto, Japan) was run for thermo gravimetric analysis (TGA) and differential thermal analysis (DTA) at temperatures of 50−600 °C at a 10 °C min−1 heating rate and kept at an inert atmosphere (N2 flow rate of 50 mL min−1). Scanning electron microscopy (SEM) and energy dispersive X-ray analysis (EDS) (Jeol JSM-6510LV, Tokyo, Japan) was used after Coating with gold over layer to perform microstructural observations of the surface morphology and compositional analysis of the resin. Transmission electron microscope (TEM) images were obtained by using a Jeol JEM-2100 microscope (Peabody, MA). 13C NMR was recorded by Bruker BioSpin GmbH (Rheinstetten, Germany).

Analysis of real samples and SRM

Ethical statement

Experiments on fishes for research purpose identifying the licensing committee approving the experiments, registration no. 714/02/a/CPCSEA issued and approved by the Institutional Animal Ethic Committee (IAEC) with Order no: D. No. 4165, by the Department of Biochemistry, Faculty of Life Sciences, Aligarh Muslim University, Aligarh, India. It has also been confirmed that all experiments were performed in accordance with relevant guidelines and regulations.

Battery waste water (Aligarh, India) was collected and filtered through cellulose membrane (Millipore) having a pore size of 0.45μm, acidified to pH 2.0 with HNO3 acid and kept in a precleaned polyethylene bottles. Samples of fishes Labeo rohita (n = 10, length 14.8 ± 2 cm, total weight 2 kg) and Channa punctatus (n = 5, length 13.4 ± 2 cm, total weight 1 kg) were collected from Panethi reservoir (Aligarh, India). Fishes were dissected and different organ tissues (muscle, kidney, liver, brain, gills) were separated and digested as reported in the literature40. The digestion of an SRM (JSS 800-3), rompin hematite was also reported in the literature38.

Immobilization of GO onto solid support AXAD-16

Graphene Oxide (GO) was synthesized from natural graphite powder by modified Hummers method41. The diazotization of AXAD-16 resin was reported in the previous literature40.

Synthesis of GO AXAD-16

Subsequently, GO was chemically immobilized onto surface of AXAD-16 resin through azo coupling. Briefly, 5 mL of prepared GO (2 mg mL−1) and 4 g of diazotized resin were added into the beaker containing methanol and NaOH (2:1) and then the mixture was kept at 0–2 °C for 48 h during this time GO was reacting with diazotized resin. Afterwards, the products were filtered and washed with deionized water several times. Finally, the (GO AXAD-16) were dried under vacuum at 50 °C for 24 h.

Functionalization of (GO AXAD-16) with picolylamine

In a 250 mL round bottomed flask, the synthesized GO AXAD-16 resin was dispersed into 50 mL DMF solution. Then DCC (1 g) and 2 picolylamine (2.5 mL in 30 mL aqueous solution) were added into the above mixture under heating at 70 °C for 8 h. Finally, the mixture was filtered and washed with deionized water with several times until pH become neutral. Lastly, the product was dried. The final product was abbreviated as GOXPA. As represented in the scheme (Fig. 5).

Figure 5.

Figure 5

Open in a new tab

Representing immobilization of GO onto AXAD-16 resin through azo spacer arm and coupling via carboxyl group of GO and –NH2 group of ligand picolylamine.

Conclusion

The objective of the work was to engineer a novel and innovative solid phase extractant GOXPA in order to develop an environmentally safe column method for preconcentration and determination of Pb (II) and Cu (II) coupled with ICP-OES. As this involved immobilization of GO onto the surface of AXAD-16 resin through azo spacer arm without utilizing any oxygen functionality, which was revealed by sharp azo peak in FT-IR spectrum and through SEM images of disordered covering of GO onto AXAD-16 resin and further scrolling of GO was supported by TEM image. 13C NMR of GOXPA was also analyzed and observed a chemical shift in the spectrum, confirming successful immobilization and modification. The higher surface area was achieved by utilizing AXAD-16 resin as a solid support which was investigated by BET analysis. Hence, this engineered sorbent has efficacy for preconcentration and determination of Pb (II) and Cu (II). Moreover, it was successfully applied to both different tissues of animals like fishes as well as water sample which confirmed that the method was reliable with good accuracy and precision.

Electronic supplementary material

Supplementary information (125.5KB, docx)

Acknowledgements

Authors are thankful to University Sophisticated Instrument Facility (USIF) for SEM and TEM analysis of GOXPA. The authors acknowledge the support provided by the UGC-SAP program and DST (FIST & PURSE), New Delhi and Dr. S. Yadav (SES, JNU, New Delhi) for allowing us to use ICP-OES in his lab.

Author Contributions

H.J. carried out the main experimental work, interpretation of results and wrote the main manuscript text. A.I. provided supervision and intellectual input in experimental and interpretation of results and edited the manuscript. A.C. assisted in experimental work and interpretation of results of GOXPA. S.K1. contributed to the synthesis of GOXPA during his studentship in AMU. S.K.2 performed only the sample analysis by ICP-OES in his institution with the permission of his guide.

Data Availability Statement

All the described data is available in the manuscript.

Competing Interests

The authors declare no competing interests.

Footnotes

Publisher’s note: Springer Nature remains neutral with regard to jurisdictional claims in published maps and institutional affiliations.

Electronic supplementary material

Supplementary information accompanies this paper at 10.1038/s41598-018-35656-1.

References

  • 1.Scida K, Stege PW, Haby G, Messina GA, Garcia CD. Recent applications of carbon-based nanomaterials in analytical chemistry. Critical review. Anal. Chim. Acta. 2011;691:6–17. doi: 10.1016/j.aca.2011.02.025. [DOI] [PMC free article] [PubMed] [Google Scholar]
  • 2.Jiang X, et al. Nanomaterials in analytical atomic Spectrometry. Trends Anal. Chem. 2012;39:38–59. doi: 10.1016/j.trac.2012.06.002. [DOI] [Google Scholar]
  • 3.Bhatnagar A. Role of nanomaterials in water treatment applications: A review. Chem. Eng. J. 2016;306:1116–1137. doi: 10.1016/j.cej.2016.08.053. [DOI] [Google Scholar]
  • 4.Sofer Z, et al. Graphene oxide sorption capacity toward elements over the whole periodic table: a comparative study. J. Phys. Chem. C. 2016;120:24203–24212. doi: 10.1021/acs.jpcc.6b08088. [DOI] [Google Scholar]
  • 5.Tang S, Zhang H, Lee HK. Advances in sample extraction. Anal. Chem. 2016;88:228–224. doi: 10.1021/acs.analchem.5b04040. [DOI] [PubMed] [Google Scholar]
  • 6.McCoy TM, Brown P, Eastoe J, Tabor RF. Noncovalent magnetic control and reversible recovery of graphene oxide using iron oxide and magnetic surfactants. ACS Appl. Mater. Interfaces. 2014;7:2124–2133. doi: 10.1021/am508565d. [DOI] [PubMed] [Google Scholar]
  • 7.Gao Wei, Alemany Lawrence B., Ci Lijie, Ajayan Pulickel M. New insights into the structure and reduction of graphite oxide. Nature Chemistry. 2009;1(5):403–408. doi: 10.1038/nchem.281. [DOI] [PubMed] [Google Scholar]
  • 8.Li Dan, Müller Marc B., Gilje Scott, Kaner Richard B., Wallace Gordon G. Processable aqueous dispersions of graphene nanosheets. Nature Nanotechnology. 2008;3(2):101–105. doi: 10.1038/nnano.2007.451. [DOI] [PubMed] [Google Scholar]
  • 9.Kotov NA, Dekany I, Fendler JH. Ultrathin graphite oxide–polyelectrolyte composites prepared by self-assembly: transition between conductive and non-conductive states. Adv. Mater. 1996;8:637–641. doi: 10.1002/adma.19960080806. [DOI] [Google Scholar]
  • 10.Turhanen PA, Vepsalainen JJ, Peraniemi S. Advanced material and approach for metal ions removal from aqueous solutions. Sci. reports. 2015;5:8992. doi: 10.1038/srep08992. [DOI] [PMC free article] [PubMed] [Google Scholar]
  • 11.Ahmad, H. Preconcentration and speciation of arsenic by using a graphene oxide nanoconstruct functionalized with a hyperbranched polyethyleneimine. Microchim. Acta., 10.1007/s00604-018-2829-z (2018). [DOI] [PubMed]
  • 12.Jibrin SS, et al. Nanometer-sized zirconium dioxide microcolumn separation/preconcentration of trace metals and their determination by ICP-OES in environmental and biological samples. Microchim. Acta. 2007;159:379–385. doi: 10.1007/s00604-007-0742-y. [DOI] [Google Scholar]
  • 13.Madadrang CJ, et al. Adsorption behavior of EDTA-graphene oxide for Pb (II) removal. ACS. Appl. Mater. Interfaces. 2012;4:1186–1193. doi: 10.1021/am201645g. [DOI] [PubMed] [Google Scholar]
  • 14.Liu Q, et al. Evaluation of graphene as an advantageous adsorbent for solid-phase extraction with chlorophenols as model analytes. J. Chromatogr. A. 2011;1218:197–204. doi: 10.1016/j.chroma.2010.11.022. [DOI] [PubMed] [Google Scholar]
  • 15.Sun N, Han Y, Yan H, Song Y. A self-assembly pipette tip graphene solid phase extraction coupled with liquid chromatography for the determination of three sulfonamides in environmental water. Anal. Chim. Acta. 2014;810:25–31. doi: 10.1016/j.aca.2013.12.013. [DOI] [PubMed] [Google Scholar]
  • 16.Ye Q, Liu L, Chen Z. Analysis of phthalate acid esters in environmental water by magnetic graphene solid phase extraction coupled with gas chromatographye mass spectrometry. J. Chromatogr. A. 2014;1329:24–29. doi: 10.1016/j.chroma.2013.12.086. [DOI] [PubMed] [Google Scholar]
  • 17.Ghanemi K, Nikpour Y, Omidvar O, Maryamabadi A. Sulfur-nanoparticle-based method for separation and preconcentration of some heavy metals in marine samples prior to flame atomic absorption spectrometry determination. Talanta. 2011;85:763–769. doi: 10.1016/j.talanta.2011.04.066. [DOI] [PubMed] [Google Scholar]
  • 18.He Q, et al. Preconcentration of Cu (II), Fe (III), and Pb (II) with 2-((2-Aminoethylamino) methyl) phenol-Functionalized activated carbon followed by ICP-OES determination. J. Hazard. Mater. 2010;175:710–714. doi: 10.1016/j.jhazmat.2009.10.067. [DOI] [PubMed] [Google Scholar]
  • 19.Sitko R, et al. Adsorption of divalent metal ions from aqueous solutions using graphene oxide. Dalton Trans. 2013;42:5682. doi: 10.1039/c3dt33097d. [DOI] [PubMed] [Google Scholar]
  • 20.Gong X, Liu G, Li Y, Denis YWY, Teoh WY. Functionalized-graphene composites: fabrication and applications in sustainable energy and environment. Chem. Mater. 2016;28:8082–8118. doi: 10.1021/acs.chemmater.6b01447. [DOI] [Google Scholar]
  • 21.Perreault F, Fonseca de Faria A, Elimelech M. Environmental applications of graphene-based nanomaterials. Chem. Soc. Rev. 2015;44:5861–5896. doi: 10.1039/C5CS00021A. [DOI] [PubMed] [Google Scholar]
  • 22.Sitko R, et al. Spherical silica particles decorated with graphene oxide nanosheets as a new sorbent in inorganic trace analysis. Anal. Chim. Acta. 2014;834:22–29. doi: 10.1016/j.aca.2014.05.014. [DOI] [PubMed] [Google Scholar]
  • 23.Islam A, Ahmad H, Zaidi N, Kumar S. Graphene oxide sheets immobilized polystyrene for column preconcentration and sensitive determination of lead by flame atomic absorption spectrometry. ACS. Appl. Mater. Interfaces. 2014;6:13257–13265. doi: 10.1021/am5031215. [DOI] [PubMed] [Google Scholar]
  • 24.Yin Lili, Lin Yuexin, Jia Li. Graphene oxide functionalized magnetic nanoparticles as adsorbents for removal of phthalate esters. Microchimica Acta. 2014;181(9-10):957–965. doi: 10.1007/s00604-014-1187-8. [DOI] [Google Scholar]
  • 25.Islam A, Ahmad H, Zaidi N, Kumar S. Graphene oxide decorated with triethylenetetramine-modified magnetite for separation of chromium species prior to their sequential speciation and determination via FAAS. Microchim. Acta. 2016;183:289–296. doi: 10.1007/s00604-015-1641-2. [DOI] [Google Scholar]
  • 26.Mehdinia A, Ramezani M, Jabbari A. Preconcentration and determination of lead ions in fish and mollusk tissues by nanocomposite of Fe3O4@graphene oxide@polyimide as a solid phase extraction sorbent. Food Chem. 2017;237:1112–1117. doi: 10.1016/j.foodchem.2017.06.051. [DOI] [PubMed] [Google Scholar]
  • 27.Sitko R, Zawisza B, Malicka E. Graphene as a new sorbent in analytical chemistry. Trends Anal. Chem. 2013;51:33–43. doi: 10.1016/j.trac.2013.05.011. [DOI] [Google Scholar]
  • 28.Gu W, Zhu X. Nanoparticles of type Fe3O4-SiO2-graphene oxide and coated with an amino acid-derived ionic liquid for extraction of Al(III), Cr(III), Cu(II), Pb(II) prior to their determination by ICP-OES. Microchim. Acta. 2017;184:4279–4286. doi: 10.1007/s00604-017-2469-8. [DOI] [Google Scholar]
  • 29.Neyestani MR, Shemirani F, Mozaffari S, Alvand M. A magnetized graphene oxide modified with 2-mercaptobenzothiazole as a selective nanosorbent for magnetic solid phase extraction of gold(III), palladium(II) and silver(I) Microchim. Acta. 2017;184:2871–2879. doi: 10.1007/s00604-017-2299-8. [DOI] [Google Scholar]
  • 30.Luis AE, Luis DM, José AS, José AG. Determination of Zn(II) in natural waters by ICP-OES with on-line preconcentration using a simple solid phase extraction system. Microchemi. Journal. 2010;95:164–168. doi: 10.1016/j.microc.2009.11.003. [DOI] [Google Scholar]
  • 31.Ren C, Hu X, Li Xb, Zhou Q. Ultra-trace graphene oxide in a water environment triggers Parkinson’s disease-like symptoms and metabolic disturbance in zebrafish larvae. Biomaterials. 2016;93:83–94. doi: 10.1016/j.biomaterials.2016.03.036. [DOI] [PubMed] [Google Scholar]
  • 32.Islam A, Kumar S. Glycidylmethacrylate based resin functionalized with graphene oxide for column preconcentration and trace determination of Cd (II) and Ni (II) in environmental and food samples. RSC. Adv. 2016;6:77629. doi: 10.1039/C6RA15612F. [DOI] [Google Scholar]
  • 33.Drago, R. S. Physical Methods in Inorganic Chemistry, Litton Educational Publishing, USA, (1965).
  • 34.Socrates, G. Infrared Characteristics GroupFrequencies, John Wiley & Sons, New York, (1980).
  • 35.Keramat A, Dorabei RZ. Ultrasound-assisted dispersive magnetic solid phase extraction for preconcentration and determination of trace amount of Hg (II) ions from food samples and aqueous solution by magnetic graphene oxide (Fe3O4@ GO/2-PTSC): Central composite design optimization. Ultrason. Sonochem. 2017;38:421–429. doi: 10.1016/j.ultsonch.2017.03.039. [DOI] [PubMed] [Google Scholar]
  • 36.Bao C, et al. Preparation and characterization of chitosan/graphene oxide composites for the adsorption of Au(III) and Pd(II) Talanta. 2012;93:350–357. doi: 10.1016/j.talanta.2012.02.051. [DOI] [PubMed] [Google Scholar]
  • 37.Sitko R, et al. Green Approach for Ultratrace Determination of Divalent Metal Ions and Arsenic Species Using Total-Reflection X-ray Fluorescence Spectrometry and Mercapto-Modified Graphene Oxide Nanosheets as a Novel Adsorbent. Anal. Chem. 2015;5:b00283. doi: 10.1021/acs.analchemb00283. [DOI] [PubMed] [Google Scholar]
  • 38.Zhu XB, Cui Y, Chang X, Wang H. Selective solid-phase extraction and analysis of trace-level Cr(III), Fe (III), b(II), and Mn (II) ions in waste water using diethylenetriamine-functionalized carbon nanotubes dispersed in graphene oxide colloids. Talanta. 2016;146:358–363. doi: 10.1016/j.talanta.2015.08.073. [DOI] [PubMed] [Google Scholar]
  • 39.Long GL, Winefordner JD. Limit of detection a closer look at the IUPAC definition. Anal. Chem. 1983;55:712A–724A. doi: 10.1021/ac00259a060. [DOI] [Google Scholar]
  • 40.Islam A, Laskar MA, Ahmad A. Characterization of a novel chelating resin of enhanced hydrophilicity and its analytical utility for preconcentration of trace metal ions. Talanta. 2010;81:1772–1780. doi: 10.1016/j.talanta.2010.03.035. [DOI] [PubMed] [Google Scholar]
  • 41.Hummers WS, Offeman RE. Preparation of graphitic oxide. J. Am. Chem. Soc. 1958;80:1339–1339. doi: 10.1021/ja01539a017. [DOI] [Google Scholar]
  • 42.Yua H, Song H, Chena M. Dithizone immobilized silica gel on-line preconcentration of trace copper with detection by flame atomic absorption spectrometry. Talanta. 2011;85:625–630. doi: 10.1016/j.talanta.2011.04.039. [DOI] [PubMed] [Google Scholar]
  • 43.Ghanemi K, Nikpour Y, Omidvar O, Maryamabadi A. Sulfur-nanoparticle-based method for separation and preconcentration of some heavy metals inmarine samples prior to flame atomic absorption spectrometry determination. Talanta. 2011;85:763–769. doi: 10.1016/j.talanta.2011.04.066. [DOI] [PubMed] [Google Scholar]
  • 44.Pourjavid MR, et al. Use of 2-(tert-butoxy)-N-(3-carbamothioylphenyl)acetamide and graphene oxide for separation and preconcentration of Fe(III), Ni(II), Cu(II) and Zn(II) ions in different samples. Chinese Chem. Let. 2014;25:791–793. doi: 10.1016/j.cclet.2014.01.045. [DOI] [Google Scholar]
  • 45.Wang Y, Gao S, Zang X, Li J, Ma J. Graphene-based solid-phase extraction combined with flame atomic absorption spectrometry for a sensitive determination of trace amounts of lead in environmental water and vegetable samples. Anal. Chim. Acta. 2012;716:112–118. doi: 10.1016/j.aca.2011.12.007. [DOI] [PubMed] [Google Scholar]
  • 46.Zhang Y, et al. Graphene oxide-TiO2 composite as a novel adsorbent for the preconcentration of heavy metals and rare earth elements in environmental samples followed by on-line inductively coupled plasma optical emission spectrometry detection. RSC Adv. 2015;5:5996–6005. doi: 10.1039/C4RA13333A. [DOI] [Google Scholar]
  • 47.Ivanka GD, Irina BK, Ventsislava TG, George SG. Polycarboxylic microsphere polymer gel for solid phase extraction of trace elements. Microchim. Acta. 2009;164:55–61. doi: 10.1007/s00604-008-0031-4. [DOI] [Google Scholar]
  • 48.Ning Lian., et al. Application of Dithizone-Modified TiO2 Nanoparticles in the Preconcentration of Trace Chromium and Lead from Sample Solution and Determination by Inductively Coupled Plasma Atomic Emission Spectrometry. Microchim. Acta. 2005;151:81–88. doi: 10.1007/s00604-005-0381-0. [DOI] [Google Scholar]
  • 49.Zhao-Hui Wang., et al. Acrylic acid grafted polytetrafluoroethylene fiber as new packing for flow injection on-line microcolumn preconcentration coupled with flame atomic absorption spectrometry for determination of lead and cadmium in environmental and biological samples. Anal. Chim. Acta. 2004;514:151–157. doi: 10.1016/j.aca.2004.03.049. [DOI] [Google Scholar]
  • 50.Anna T, et al. Cu(II)-imprinted styrene–divinylbenzene beads as a new sorbent for flow injection-flame atomic absorption determination of copper. Microchemi. Journal. 2009;93:87–92. doi: 10.1016/j.microc.2009.05.002. [DOI] [Google Scholar]
  • 51.Hongbo X, et al. Simultaneous preconcentration of cadmium and lead in water samples with silica gel and determination by flame atomic absorption spectrometry. J.Environ.Sci. 2013;25:45–49. doi: 10.1016/S1001-0742(14)60624-0. [DOI] [PubMed] [Google Scholar]
  • 52.Hong W, et al. Simple micro-column with multi-walled carbon nanotubes for on-line preconcentration and determination of lead in natural water by hydride generation atomic fluorescence spectrometry. Microchim. Acta. 2009;166:41–46. doi: 10.1007/s00604-009-0161-3. [DOI] [Google Scholar]
  • 53.Su S, Chen B, He M, Hu B. Graphene oxide–silica composite coating hollow fiber solid phase microextraction online coupled with inductively coupled plasma mass spectrometry for the determination of trace heavy metals in environmental water samples. Talanta. 2014;123:1–9. doi: 10.1016/j.talanta.2014.01.061. [DOI] [PubMed] [Google Scholar]

Associated Data

This section collects any data citations, data availability statements, or supplementary materials included in this article.

Supplementary Materials

Supplementary information (125.5KB, docx)

Data Availability Statement

All the described data is available in the manuscript.

Articles from Scientific Reports are provided here courtesy of Nature Publishing Group

RESOURCES