Skip to main content

Melanin-embedded materials effectively remove hexavalent chromium (CrVI) from aqueous solution



Currently, it is recognized that water polluted with toxic heavy metal ions may cause serious effects on human health. Therefore, the development of new materials for effective removal of heavy metal ions from water is still a widely important area. Melanin is being considered as a potential material for removal of heavy metal from water.


In this study, we synthesized two melanin-embedded beads from two different melanin powder sources and named IMB (Isolated Melanin Bead originated from squid ink sac) and CMB (Commercial Melanin Bead originated from sesame seeds). These beads were of globular shape and 2–3 mm in diameter. We investigated and compared the sorption abilities of these two bead materials toward hexavalent-chromium (CrVI) in water. The isotherm sorption curves were established using Langmuir and Freundlich models in the optimized conditions of pH, sorption time, solid/liquid ratio, and initial concentration of CrVI. The FITR analysis was also carried out to show the differences in surface properties of these two beads.


The optimized conditions for isotherm sorption of CrVI on IMB/CMB were set at pH values of 2/2, sorption times of 90/300 min, and solid-liquid ratios of 10/20 mg/mL. The maximum sorption capacities calculated based on the Langmuir model were 19.60 and 6.24 for IMB and CMB, respectively. However, the adsorption kinetic of CrVI on the beads fitted the Freundlich model with R2 values of 0.992 for IMB and 0.989 for CMB. The deduced Freundlich constant, 1/n, in the range of 0.2–0.8 indicated that these beads are good adsorption materials. In addition, structure analysis data revealed great differences in physical and chemical properties between IMB and CMB. Interestingly, FTIR analysis results showed strong signals of –OH (3295.35 cm− 1) and –C=O (1608.63 cm− 1) groups harboring on the IMB but not CMB. Moreover, loading of CrVI on the IMB caused a shift of broad peaks from 3295.35 cm− 1 and 1608.63 cm− 1 to 3354.21 cm− 1 and 1597.06 cm− 1, respectively, due to –OH and –C=O stretching.


Taken together, our study suggests that IMB has great potential as a bead material for the elimination of CrVI from aqueous solutions and may be highly useful for water treatment applications.


Currently, environmental pollution caused by rapid industrialization and technological advances is a worldwide problem. It is recognized that water polluted with toxic heavy metals can have serious effects on human health [1, 2]. There are many types of materials which have been being used to remove heavy metals from aqueous effluents; these include activated carbon, plant-leaf materials, chitosan gel, and hydrotalcite [3, 4]. However, these materials are not fully effective nor cost efficient.

Chromium is considered to be one of the key contaminants in the wastewaters of many industries, such as plating-electroplating, dying-pigmenting, film-photography, leathering and mining. Although both hexavalent chromium (CrVI) and trivalent chromium (CrIII) are predominant species in industrial effluents, the CrVI is more toxic than CrIII. More seriously, the CrVI is considered as a mutagenic agent, which may cause adverse public health problems [1, 5].

Melanin is synthesized in humans, animals, invertebrate animals, bacteria, and fungi by oxidation of phenol or indole compounds [6,7,8,9]. Besides its role in pigmentation, melanin has many other important biological functions; it serves as an electron transporter, ion balancer, free radical acceptor as well as antioxidant, antibacterial, antivirus, and anticancer agent [6, 9]. Thus, melanin has been widely considered to be a potential material for use in various industries including agriculture, pharmacy, medicine, and cosmetics [6,7,8,9].

Recently, melanin powder (but not melanin bead) has also been examined for its ability to eliminate heavy metal ions (e.g., lead, cadmium, copper, and ferrous) in aqueous solutions [10,11,12]. Generally, for removing of heavy metal ions, a material in powder form should have very high sorption capacity. However, there is no guarantee that a high sorption capacity for the material exists in bead form [3, 4]. For practical conditions, such as in drinking water treatment, the bead form (rather than in powder form) of a material is the most popular and suitable form to avoid the possibility of being stuck when water flow passes through the material column. To date, there has been no study evaluating the use of melanin originated from squid ink sacs for removal of chromium ions, although a previous report showed that melanin secreted from Aureobacidium pullulans could also adsorb CrVI from waste water [13]. However, the different source of melanin may have big different capacity in removing of CrVI ion. In this study, we used two different melanin sources: one was isolated from squid ink sacs, which are considered as waste material of seafood processing companies and named as IMB (Isolated Melanin Bead), and the other was derived from sesame seeds (purchased from Xi’an Green Spring Technology Co., LTD, China) and named as CMB (Commercial Melanin Bead). These two melanin powders were used to make melanin-embedded beads for investigating their abilities to remove hexavalent chromium ions (CrVI). This study also aimed to compare the capacity of CrVI uptake by the two melanin-embedded beads. Comparisons were made by examining differences in their physical and chemical properties due to their different source of origin.


Melanin isolation from squid ink sacs

The method used for isolating melanin has been described previously [14]. Briefly, squid ink sacs collected from the seafood company were broken down to collect ink liquid. This liquid (50 g) was dissolved into 200 mL of 0.5 M HCl. The mixture was then sonicated for 15 min in a sonicator followed by stirring for 30 min. The mixture was then incubated at 4 °C for 48 h before centrifuging at 10,000 rpm at 5 °C for 15 min to collect the pellet. The pellet was washed with acetone for three times then washed with distilled water for three times. The melanin pellet was dried at 60 °C, grinded, sieved through 150 μm, and then stored at room temperature.

Method for making spherical melanin-embedded beads

Melanin beads were made according to a previously published protocol [15]. Briefly, melanin powder was embedded using sodium alginate as a cohesion agent. Sodium alginate was dissolved in 20 mL of distilled water and incubated in a water bath incubator at 70 °C to completely dissolve it before adding 5 g of melanin powder with continuous stirring. The mixture solution was drawn into a syringe and then eluted drop by drop into CaCl2 solution (5%) to create beads with spherical form and with a diameter of 2–3 mm. Next, the melanin beads were dried out and dipped into 5% CaCl2 solution for 24 h before washing with distilled water for three times and drying to unchanged weight.

Fourier-transform infrared analysis

Infrared spectra of the material beads were obtained using a Fourier-transform infrared spectrometer (FTIR Affinity - 1S, SHIMADZU, Kyoto, Japan) [16].

Microscope analysis

Morphology and purification of melanin powder isolated from squid ink sac was investigated by scanning electron microscope, model NANOSEM450 (Netherlands), and surface property of melanin bead was examined under Carlzeiss stereo-microscope, model stemi SV2000 (Germany).

Sorption experiments and CrVI analytical methods

Experiments were conducted at room temperature. Batch equilibrium sorption experiments were carried out in 250 mL Erlenmeyer flasks containing potassium dichromate (K2Cr2O7) solutions (100 mL) of known concentrations (varying from 5 to 200 mg/L). Melanin was added into the K2Cr2O7 solution with various ratios of solid/liquid and placed on a shaker at 200 rpm for various time settings. The solution was then centrifuged at 10,000 rpm for 10 min. In the acidified medium, CrVI reacted with diphenyl carbazide to form a purple-violet colored complex. The concentration of CrVI in the supernatant was determined colorimetrically using a spectrophotometer (Shimadzu). Absorbance was measured at wavelength (λ) of 540 nm [17]. Standard curves were generated and depicted in Fig. 1. Adsorption efficiencies were calculated using following formula:

$$ H=\frac{C_{\mathrm{o}}-{C}_{\mathrm{e}}}{C_{\mathrm{o}}}\times 100\ \left(\%\right) $$
Fig. 1
figure 1

Purple-violet colored complex of (CrVI-diphenyl cacbazide) at different concentrations (a) and standard curve for CrVI analysis measured by spectrophotometer (b) were presented


H: Adsorption efficiency (%)

Co: Initial concentration (mg/L)

Ce: Equilibirium concentration (mg/L)

Method for determining the isotherm adsorption equations

Freundlich adsorption model: The Freundlich model is used to describe the adsorption model from liquids and can be expressed as the following equation [17]:

$$ \ln {q}_{\mathrm{e}}=\ln {K}_{\mathrm{F}}+\frac{1}{n}\times \ln {C}_{\mathrm{e}} $$

Langmuir adsorption model: The Langmuir model, which is mainly used to determine the maximum adsorption capacity, is expressed as the following equation [17]:

$$ \frac{C_e}{q_{\mathrm{e}}}=\frac{1}{q_{\mathrm{max}}}\times {C}_{\mathrm{e}}+\frac{1}{q_{\mathrm{max}}\times {K}_{\mathrm{L}}} $$


Ce: concentration at equilibrium stage (mg)

qe: adsorption capacity at equilibrium stage (mg/g)

qmax: maximum adsorption capacity (mg/g)

KL: adsorption constant for Langmuir (L/mg)

KF, 1/n: adsorption constants for Freundlich (L/mg)

Statistical analysis

In this study, all experiments were repeated three times, and the collected data were analyzed with the appropriate statistical tests. To compare the two groups, the Mann-Whitney U test (for non-parametric comparisons) or Student’s t test (for parametric comparisons) were used. Significance was set at three levels with P < 0.05 [1, 2].


Synthesis of spherical melanin beads

After purification, isolated melanin pellet was lyophilized to obtain the intact natural squid melanin. Then the melanin sample was examined by the scanning electron microscope (SEM), which showed high purity without contamination by any cellular components (Fig. 2). This purified melanin was more than enough for treatment of heavy metal ions in adsorption experiments [18].

Fig. 2
figure 2

Morphology and purification of melanin isolated from squid ink sacs were examined under scanning electron microscope (SEM) at × 10,000 (left image) and × 50,000 (right image)

To produce the spherical melanin-embedded beads, melanin powder was added into the binding agent solution containing alginate at different percentages, which varied from 3 to 15%, to form a mixture before dropping into the CaCl2 solution to form beads (Fig. 3). The results showed that at low percentages of alginate (3 and 4%), the formed melanin beads were not stable and were easily broken since the concentration of the binding agent was insufficient. At the high percentages of alginate (12 and 15%), the formed melanin beads did not have spherical shape because the viscosity of the mixture was too high. Percentages of alginate in the range of 5–10% were optimal to form stable melanin beads with spherical shape (Fig. 3).

Fig. 3
figure 3

Melanin-embedded beads with a 3% alginate, b 4% alginate, c 5% alginate, d 7% alginate, e 10% alginate, and f 15% alginate as binding agent

In addition, neither alginate content (in the range of 3–15%) nor the drying method (un-drying, low-temperature drying, high-temperature drying, or freezing drying) had any significant effect on the sorption capacities of the beads (Fig. 4). However, alginate at 5% was chosen because it yielded the highest productivity and uniformity of the melanin beads.

Fig. 4
figure 4

Effect of drying method (a) and alginate content (b) on sorption efficiency of CrVI on IMB and CMB. (UD: undrying; LTD: low temperature drying; HTD: high temperature drying; FD: freezing drying). Three asterisks indicate significant difference (p < 0.001) between IMB and CMB by the Student’s t test

Effect of pH on CrVI sorption by melanin-embedded beads

The effect of pH on the efficiency of CrVI removal by melanin beads was evaluated for the following set conditions: shaking rate of 200 rpm at 30 °C, solid/liquid ratio of 10 g/L, shaking time of 1 h, and CrVI initial concentration of 200 mg/L. The results are shown in Fig. 5. The removal efficiencies of CrVI by IMB or CMB were better at lower pH values and reached the maximum at pH 1–2 (Fig. 5a). However, IMB had a much higher sorption capacity compared to that of CMB at any pH value. In particular, at the optimized pH (1–2), the sorption capacity of IMB was almost threefold higher than that of CMB.

Fig. 5
figure 5

Effect of pH (a), sorption time (b), solid/liquid (c), and CrVI initial concentration (d) on sorption efficiency of CrVI on CMB and IMB. *, **, and *** Significant difference (p < 0.05, 0.01 and 0.001, respectively) between IMB and CMB by the Student’s t test

Effect of sorption time on CrVI removal efficiency

The effect of sorption time on the efficiency of CrVI removal by melanin beads was also evaluated for the following set conditions: pH of 2, shaking rate of 200 rpm at 30 °C, initial CrVI concentration of 200 mg/L, and the solid/liquid ratios of 20 g/L. The results indicated that the longer the sorption time, the higher the removal efficiency. However, the removal efficiency quickly increased during the first hour then slowly increased and reached the highest values around 96% at 2 h for IMB and 67% at 6 h for CMB (Fig. 5b). In general, at any sorption time, IMB was more effective than CMB at removing CrVI. In particular, at the same sorption time of 2 h, the sorption capacity of IMB was 2.8-fold higher than that of CMB.

Effect of solid/liquid ratios on sorption efficiency

To investigate the effect of solid/liquid ratios on the efficiency of CrVI adsorption, we tested solid/liquid ratios in the range of 1–30 g/L with the following set conditions: pH of 2, shaking rate of 200 rpm at 30 °C, shaking time of 1 h, and CrVI initial concentration of 200 mg/L. The results showed that the removal efficiency increased rapidly as the solid/liquid ratio increased from 1 to 20 g/L and increased only slightly from 20 to 30 g/L. The maximum removal efficiencies reached 95 and 35% for IMB and CMB, respectively, at the solid/liquid ratio of 30 g/L (Fig. 5c). At the same solid/liquid ratio, IMB was much more effective than CMB at eliminating CrVI.

Effect of initial concentration of CrVI on sorption efficiency

The effect of the initial concentration of CrVI on the efficiency of CrVI removal by melanin beads was evaluated for the following set conditions: pH of 2, shaking rate of 200 rpm at 30 °C, solid/liquid ratio of 20 g/L, and sorption time of 2 h for IMB or 4 h for CMB. The initial concentrations of CrVI were in the range of 5–200 mg/L. The CrVI removal efficiencies and the sorption capacities of CMB and IMB are shown in Fig. 5d and presented in Tables 1 and 2. The maximum capacities for IMB and CMB were 19.6 and 6.24, respectively. These results indicate that while CMB is not that efficient at eliminating CrVI, IMB is efficient and serves as a promising material for CrVI removal due to its high sorption capacity, especially as bead form. Previous studies have tested numerous materials (e.g., activated carbon, sludge, plant-leaf materials, and chitosan gel) for CrVI removal from aqueous solution and have shown that these materials as powder form had sorption capacities of wide range from 6 mg/g to 50 mg/g [3, 4]. Our study shows that IMB (in bead form) is a highly effective material for removing CrVI in water.

Table 1 CrVI removal efficiencies and sorption capacities of CMB
Table 2 CrVI removal efficiencies and sorption capacities of IMB

CrVI sorption kinetics

The results of this study indicate that an increase of initial concentration can lead to a decrease of CrVI removal efficiency and increase of the sorption capacity. From the isotherm adsorption results of CrVI at different concentrations on IMB and CMB at optimized conditions, we then examined the suitable isotherm adsorption model for adsorption of CrVI on IMB and CMB using the two common models of Langmuir and Freundlich. The results are shown in Fig. 6. The isotherm equations deduced from Langmuir and Freundlich models were presented as follows:

Fig. 6
figure 6

Langmuir model (a and b) and Freundlich model (c and d) for isotherm sorption mechanisms of CrVI on CMB (a and c) and IMB (b and d)

Equation of the Langmuir model for CMB (Fig. 6a): \( \frac{C_e}{q_e} \) = 0.153 Ce + 1.450; R2 = 0.955

Equation of the Langmuir model for IMB (Fig. 6b): \( \frac{C_{\mathrm{e}}}{q_{\mathrm{e}}} \) = 0.051 Ce + 0.492; R2 = 0.885

Equation of the Freundlich model for CMB (Fig. 6c): ln qe = 0.491lnCe − 0.237; R2 = 0.989.

Equation of the Freundlich model for IMB (Fig. 6d): ln qe = 0.601lnCe + 0.655; R2 = 0.992

Parameters for isotherm adsorption of CMB and IMB are summarized in Table 3. The results suggest that the Freundlich model is more suitable than the Langmuir model to describe the sorption mechanism of CrVI on melanin bead since the R2—coefficient value of the Freundlich model—was higher than that of the Langmuir model. The data also indicate that the surfaces of IMB or CMB are not uniform, and therefore, the distributions of reaction centers on the surface of the materials probably follow an exponential equation rather than a linear one. In the Freundlich model, the mechanism and the rate of adsorption are functions of the constants 1/n and KF. For a good absorbance, the 1/n value should be 0.2 < 1/n < 0.8, and a smaller value of 1/n indicates better adsorption and formation of strong bonds between the adsorbate and adsorbent [19, 20]. In this study, the 1/n values of 0.49 and 0.6 for CMB and IMB, respectively, demonstrate that both IMB and CMB are good materials for adsorption of CrVI; however, IMB has a much better adsorption capacity compared to CMB.

Table 3 Parameters for isotherm sorption of CMB and IMB materials

Fourier transform infrared analysis

In general, on the surface of the melanin material, there are many chemical groups including hydroxyl, carboxyl, and ether, which have been proposed to be responsible for sorption of metal ions by formation of chemical bonding. The chemical-sorption ability of the material depends on factors such as quantity of active centers, its accessibility, and affinity between active centers and metal ions [21]. The surfaces of IMB and CMB were observed under stereo-microscope and presented in Fig. 7. The differences in surface structure of IMB and CMB are clearly distinguishable. It showed that the intensities of peaks of the hydroxyl, carboxyl, and ether groups in IMB were very clear and sharp, while the intensities of these corresponding peaks in CMB were not so clear especially for hydroxyl group. This result indicated that the distribution of chemical groups on the surface of IMB may be denser on the surface of CMB and might lead to difference in numbers of chemical linkages formed between melanin and CrVI ion.

Fig. 7
figure 7

Surface structures of IMB (a and b) and CMB (c and d) at × 10 magnifications

Conversely, FTIR analysis was used to analyze the functional groups on the surfaces of the native and CrVI-bound IMB and CMB; results are shown in Figs. 8 and 9. IMB and CMB showed completely different FTIR spectra. While IMB had the broad absorption peaks at 3296 cm− 1 and 1608 cm− 1 due to the presence of the –OH and –C=O groups, respectively [22, 23], there were almost no peaks at these sites on the surface of CMB (Fig. 8a and Fig. 9a). Although many other sorption peaks were observed, it is difficult to interpret all. After loading CrVI, the FTIR spectra of CrVI-bound IMB and CrVI-bound CMB were presented in Fig. 8b and Fig. 9b. The results indicated that the adsorption of CrVI on the surface of IMB may have caused a shift of the broad peaks at 3296 cm− 1 and 1608 cm− 1 to 3354 cm− 1 and 1597 cm− 1, respectively, due to –OH and –C=O stretching (Fig. 8b).

Fig. 8
figure 8

FTIR spectra of native IMB (a) and CrVI-loaded IMB (b)

Fig. 9
figure 9

FTIR spectra of native CMB (a) and CrVI-loaded CMB (b)


Chromium pollution originated from plating and electroplating industries, iron and steel industries, and inorganic-chemical production represents a huge problem for environmental health [24]. Exposure to chromium ions, especially CrVI, may cause diseases related to the digestive system and lung; such complications can include epigastric pain, nausea, diarrhea, hemorrhage, and cancer [25]. Thus, it is essential to eliminate CrVI from wastewater before disposal. There are many methods which can be applied to remove CrVI from aqueous solutions; these methods include ion exchange [26], chemical precipitation [27], electrochemical precipitation [28], reduction [29], solvent extraction [30], adsorption [31], membrane separation [32], and reverse osmosis and biosorption [33]. However, these different methods have different disadvantages, such as low removal efficiency, expensive equipment, high operating cost, and high energy requirement [34].

In this study, we investigated the ability of melanin (as a material in bead form) to remove CrVI from aqueous solution. Two different natural melanin sources, one originating from plant (commercial one) and the other extracted from ink sacs of squid (isolated one), were used for making melanin-embedded beads; the beads were called CMB and IMB, respectively. In many Asian countries, the seafood industry is one of the most important industries which provide great economic benefit for the country. Squid and octopuses are processed in many seafood processing companies for export. Nevertheless, ink sacs of squid and octopuses are wastes in these seafood companies. More importantly, melanin accounts for about 16–18% in total weight of the sac [14]. Thus, utilization of these wastes for melanin production will have great impact since melanin has not only been considered as a potential material for heavy metal removal but also for many other applications, such as medicine and cosmetics [6,7,8,9].

To examine the effect of IMB and CMB on removing CrVI, the effect of various parameters such as pH, sorption time, and solid-liquid ratio on CrVI sorption were conducted, and isotherm models including Freundlich and Langmuir were applied to fit experimental data. In accordance with previous studies [19, 35,36,37,38,39], the data showed that IMB and CMB both had the highest sorption capacities as pH 1–2 and that the Freundlich model was the best model to represent the sorption model of CrVI on IMB and/or CMB.

There are many materials which have been used to remove chromium ions in effluents from various industries. The removal capacities of these materials vary from 0.2 to 200 mg/g. In general, sorption capacities of materials are different from their origins, for example: plant-originated materials (0.5–10 mg/g), activated carbon materials (2–30 mg/g), coal (6.68 mg/g), hydrous titanium oxide (5 mg/g), maghemite nanoparticles (1.5 mg/g), and tannin gel (200 mg/g) [19, 35,36,37,38,39]. In addition, almost all materials used in previous studies were in powder form, and therefore, their capacities in CrVI removal would be significantly decreased after making the bead form. Previous studies demonstrated that acidic conditions at pH of 1 or 2 were good for the removal of CrVI from water [35,36,37,38,39]. This study also introduced the similar result. In practical conditions, CrVI pollutant mostly comes from the mining and platting industries, which normally have effluents with low pH values. That means IMB should be a suitable material for treatment of CrVI from industrial effluent. Besides that, in some cases, CrVI pollutant may also come from natural water, which has pH of 5–7. However, concentration of CrVI in natural water is below 1 μg/L [40], while this study showed that the adsorption capacity of IMB for CrVI was about 7–8 mg/g at the pH of 6–7 (one third of that at pH of 1–2). It means that IMB is also good enough for removing of CrVI from natural water.


In this study, our results demonstrated that melanin materials are potential for the removal of CrVI from water. However, melanin from different sources have different physical and chemical properties. Particularly, the properties of IMB (melanin extracted from squid ink sacs) were significantly different from those of CMB (melanin extracted from plant). These results led to a difference in the ability of these two melanin materials to eliminate CrVI from aquaous solution. CMB had CrVI sorption capacity of 6.24 mg/g while IMB had CrVI sorption capacity of 19.8 mg/g. In summary, our study suggests that melanin isolated from squid ink sacs (which are considered as waste of seafood processing companies) can be used to synthesis the melanin bead and applied in water treatment to effectively remove CrVI ions.



Commercial Melanin Bead

CrVI :

Hexavalent chromium


Fourier-transform infrared analysis


Isolated Melanin Bead


  1. 1.

    Ohgami N, Yamanoshita O, Thang ND, Yajima I, Nakano C, Wenting W, Ohnuma S, Kato M. Carcinogenic risk of chromium, copper and arsenic in CCA-treated wood. Environ Pollut. 2015;206:456–60.

    CAS  Article  PubMed  Google Scholar 

  2. 2.

    Thang ND, Yajima I, Kumasaka M, Kato M. Bidirectional functions of arsenic as a carcinogen and an anticancer agent in human squamous cell carcinoma. PLoS One. 2014;

  3. 3.

    Singha B, Naiya TK, Bhattacharya AK, Das SK. Cr(VI) ions removal from aqueous solutions using natural adsorbents—FTIR studies. J Environ Protection. 2011;2:729–35.

    CAS  Article  Google Scholar 

  4. 4.

    Mohan D and Pittman CY. Activated carbons and low cost adsorbents for remediation of tri- and hexavalent chromium from water. J Hazard Mater. 2006;137:762–811, 2006.

  5. 5.

    EPA, Environmental Protection Agency, Environmental Pollution Control Alternatives, EPA/625/5–90/025, EPA/625/4–89/023, Cincinnati, US, 1990.

  6. 6.

    Manivasagan P, Venkatesan J, Senthilkumar K, Sivakumar K, Kim SK. Isolation and characterization of biologically active melanin from Actinoalloteichus sp. MA-32. Int J Biol Macromol. 2013;58:263–74.

    CAS  Article  PubMed  Google Scholar 

  7. 7.

    Mbonyiryivuze A, Nuru ZY, Ngom BD, Mwakikunga B, Dhlamini SM, Park E, Maaza M. Morphological and chemical composition characterization of commercial sepia melanin. American Journal of Nanomaterials. 2015;3(1):22–7.

    CAS  Article  Google Scholar 

  8. 8.

    Nosanchuk JD, Casadevall A. Impact of melanin on microbial virulence and clinical resistance to antimicrobial compounds. Antimicrob Agents Chemother. 2006;6:3519–28.

    Article  Google Scholar 

  9. 9.

    Tarangini K, Mishra S. Production, characterization and analysis of melanin from isolated marine pseudomonas sp. using vegetable waste. Res J Engineering Sci. 2013;2(5):40–6.

    Google Scholar 

  10. 10.

    Hong L, Simon JD. Current understanding of the binding sites, capacity, affinity, and biological significance of metals in melanin. J Phys Chem B. 2007;111(28):7938–47.

    CAS  Article  PubMed  PubMed Central  Google Scholar 

  11. 11.

    Hong L, Liu Y, Simon JD. Binding of metal ions to melanin and their effects on the aerobic reactivity. Photochem Photobiol. 2004;80:477–81.

    CAS  Article  PubMed  Google Scholar 

  12. 12.

    Szpoganicz B, Gidanian S, Kong P, Farmer P. Metal binding by melanins: studies of colloidal dihydroxyindole-melanin, and its complexation by Cu(II) and Zn(II) ions. J Inorg Biochem. 2002;89:45–53.

    CAS  Article  PubMed  Google Scholar 

  13. 13.

    Yu XH, Gu GX, Shao R, Chen RX, Wu XJ, Xu W. Study on adsorbing chromium (VI) ions in wastewater by Aureobacidium pullulans secretion of melanin. Adv Mater Res. 2011;156-157:1378–84.

    CAS  Article  Google Scholar 

  14. 14.

    Magarelli M, Passamonti P, Renieri C. Purification, characterization and analysis of sepia melanin from commercial sepia ink (Sepia Officinalis). Rev CES Med Vet Zootec. 2010;5(2):18–28.

    Google Scholar 

  15. 15.

    Kato M, Azimi MD, Fayaz SH, Shah MD, Hoque MZ, Hamajima N, et al. Uranium in well drinking water of Kabul, Afghanistan and its effective, low-cost depuration using Mg-Fe based hydrotalcite-like compounds. Chemosphere. 2016;165:27–32.

    CAS  Article  PubMed  Google Scholar 

  16. 16.

    Bansal M, Singh D, Garg VK. A comparative study for the removal of hexavalent chromium from aqueous solution by agriculture wastes’ carbons. J Hazard Mater. 2009;171(1-3):83–92.

    CAS  Article  PubMed  Google Scholar 

  17. 17.

    Gupta S, Babu BV. Removal of toxic metal Cr(VI) from aqueous solutions using sawdust as adsorbent: equilibrium, kinetics and regeneration studies. Chem Eng J. 2009;150:352–65.

    CAS  Article  Google Scholar 

  18. 18.

    Aoyama M, Sugiyama T, Doi S, Cho NS, Kim HE. Removal of hexavalent chromium from dilute aqueous solution by coniferous leaves. Holzforschung. 1999;53:365–8.

    CAS  Article  Google Scholar 

  19. 19.

    Dakiky M, Khamis M, Manassra A, Mereb M. Selective adsorption of chromium(VI) in industrial wastewater using low-cost abundantly available adsorbents. Adv Environ Res. 2002;6(4):533–40.

    CAS  Article  Google Scholar 

  20. 20.

    Aksu Z, Acikel U, Kabasakal E, Tezer S. Equilibrium modelling of individual and simultaneous biosorption of chromium(VI) and nickel(II) onto dried activated sludge. Water Res. 2002;36:3063–73.

    CAS  Article  PubMed  Google Scholar 

  21. 21.

    Garg UK, Kaur MP, Garg VK, Sud D. Removal of nickel (II) from aqueous solution by adsorption on agricultural waste biomass using a response surface methodological approach. Bioresour Technol. 2008;99(5):1325–31.

    CAS  Article  PubMed  Google Scholar 

  22. 22.

    Liu Y, Simon JD. Metal-ion interactions and the structural organization of Sepia eumelanin. Pigment Cell Res. 2005;18(1):42–8.

    CAS  Article  PubMed  Google Scholar 

  23. 23.

    Ho YS, Chiang CC, Hsu YC. Sorption kinetics for dye removal from aqueous solution using activated clay. Sep Sci Technol. 2001;36(11):2473–88.

    CAS  Article  Google Scholar 

  24. 24.

    Wang YT, Xiao C. Factors affecting hexavalent chromium reduction in pure cultures of bacteria. Water Res. 1995;29:2467–74.

    CAS  Article  Google Scholar 

  25. 25.

    Mohanty K, Jha M, Meikap BC, Biswas MN. Removal of chromium(VI) from dilute aqueous solutions by activated carbon developed from Terminalia Arjuna nuts activated with zinc chloride. Chem Eng Sci. 2005;60:3049–59.

    CAS  Article  Google Scholar 

  26. 26.

    Tiravanti G, Petruzzelli D, Passiono R. Pretreatment of tannery wastewaters by an ion exchange process for Cr(III) removal and recovery. Water Sci Technol. 1997;36:197–207.

    CAS  Google Scholar 

  27. 27.

    Zhou X, Korenaga T, Takahashi T, Moriwake T, Shinoda S. A process monitoring/controlling system for the treatment of wastewater containing chromium(VI). Water Res. 1993;27:1049–54.

    CAS  Article  Google Scholar 

  28. 28.

    Kongsricharoern N, Polprasert C. Chromium removal by a bipolar electrochemical precipitation process. Water Sci Technol. 1996;34:109–16.

    CAS  Google Scholar 

  29. 29.

    Seaman JC, Bertsch BM, Schwallie L. In situ Cr(VI) reduction within coarsetextured, oxide-coated soil and aquifer systems using Fe(II) solutions. Environ Sci Technol. 1999;33:938–44.

    CAS  Article  Google Scholar 

  30. 30.

    Calace N, Muro DA, Nardi E, Petronio BM, Pietroletti M. Adsorption isotherms for describing heavy metal retention in paper mill sludges. Ind Eng Chem Res. 2002;41:5491–7.

    CAS  Article  Google Scholar 

  31. 31.

    Pagilla K, Canter LW. Laboratory studies on remediation of chromium contaminated soils. J Environ Eng. 1999;125:243–8.

    CAS  Article  Google Scholar 

  32. 32.

    Chakravarti AK, Chowdhury SB, Chakrabarty S, Chakrabarty T, Mukherjee DC. Liquid membrane multiple emulsion process of chromium(VI) separation from wastewaters. Colloids Surf A Physicochem Eng Asp. 1995;103:59–71.

    CAS  Article  Google Scholar 

  33. 33.

    Aksu Z, Ozer D, Ekiz H, Kutsal T, Calar A. Investigation of biosorption of chromium(VI) on C. crispate in two staged batch reactor. Environ Technol. 1996;17:215–20.

    CAS  Article  Google Scholar 

  34. 34.

    Aksu Z, Gonen F, Demircan Z. Biosorption of chromium(VI) ions by Mowital B3OH resin immobilized activated sludge in a packed bed: comparison with granular activated carbon. Process Biochem. 2002;38:175–86.

    CAS  Article  Google Scholar 

  35. 35.

    Aoyama M. Removal of Cr(VI) from aqueous solution by London plane leaves. J Chem Technol Biotechnol. 2003;78:601–4.

    CAS  Article  Google Scholar 

  36. 36.

    Aoyama M, Kishino M, Jo TS. Biosorption of Cr(VI) on Japanese ceder bark. Sep Sci Technol. 2004;39(5):1149–62.

    CAS  Article  Google Scholar 

  37. 37.

    Aoyama M, Tsuda M, Seki K, Doi S, Kurimoto Y, Tamura Y. Adsorption of Cr(VI) from dichromate solutions onto black locust leaves. Holzforschung. 2000;54:340–2.

    CAS  Article  Google Scholar 

  38. 38.

    Mohan D, Singh KP, Singh VK. Removal of hexavalent chromium from aqueous solution using low-cost activated carbons derived from agricultural waste materials and activated carbon fabric cloth. Ind Eng Chem Res. 2005;44:1027–42.

    CAS  Article  Google Scholar 

  39. 39.

    Mohan D, Singh KP, Singh VK. Trivalent chromium removal from wastewater using low cost activated carbon derived from agricultural waste material and activated carbon fabric cloth. J Hazard Mater. 2006;135:280–95.

    CAS  Article  PubMed  Google Scholar 

  40. 40.

    WHO. Guidelines for drinking-water quality. 2nd ed. vol. 2. Geneva: World Health Organization; 1996.

    Google Scholar 

Download references


Not applicable


Not applicable

Availability of data and materials

Please contact author for data requests.

Author information




AMC, NTLN, PNT, and TND carried out the melanin bead synthesis, adsorption experiments. NLT carried out the FITR analysis. LBT performed the statistical analysis. NDT conceived and designed the study and drafted the manuscript. All authors read and approved the final manuscript.

Corresponding author

Correspondence to Nguyen Dinh Thang.

Ethics declarations

Ethics approval and consent to participate

Not applicable

Consent for publication

Not applicable

Competing interests

The authors declare that they have no competing interests.

Publisher’s Note

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

Rights and permissions

Open Access This article is distributed under the terms of the Creative Commons Attribution 4.0 International License (, which permits unrestricted use, distribution, and reproduction in any medium, provided you give appropriate credit to the original author(s) and the source, provide a link to the Creative Commons license, and indicate if changes were made. The Creative Commons Public Domain Dedication waiver ( applies to the data made available in this article, unless otherwise stated.

Reprints and Permissions

About this article

Verify currency and authenticity via CrossMark

Cite this article

Cuong, A.M., Le Na, N.T., Thang, P.N. et al. Melanin-embedded materials effectively remove hexavalent chromium (CrVI) from aqueous solution. Environ Health Prev Med 23, 9 (2018).

Download citation

  • Received:

  • Accepted:

  • Published:

  • DOI:


  • CrVI
  • CMB
  • IMB