Turning an environmental problem into an opportunity

Environ Sci Pollut Res DOI 10.1007/s11356-017-0181-1

RESEARCH ARTICLE

Turning an environmental problem into an opportunity: potential use of biochar derived from a harmful marine biomass named Cladophora glomerata as anode electrode for Li-ion batteries Pejman Salimi 1 & Soheila Javadian 1 & Omid Norouzi 2 & Hussein Gharibi 1

Received: 9 April 2017 / Accepted: 11 September 2017 # Springer-Verlag GmbH Germany 2017

Abstract The electrochemical performance of lithium ion battery was enhanced by using biochar derived from Cladophora glomerata (C. glomerata) as widespread green macroalgae in most areas of the Iran’s Caspian sea coast. By the utilization of the structure of the biochar, micro-/macroordered porous carbon with olive-shaped structure was successfully achieved through pyrolysis at 500 °C, which is the optimal temperature for biofuel production, and was activated with HCl. The biochar and HCl treatment biochar (HTB) were applied as anode electrode in lithium ion batteries. Then, electrochemical measurements were conducted on the electrodes via galvanostatic charge–discharge, cyclic voltammetry (CV), and electrochemical impedance spectroscopy (EIS) analyses. The electrochemical results indicated a higher specific discharge capacity (700 mAh g−1) and good cycling stability for HTB at the current density of 0.1 A g−1 as compared to the biochar. The reason that HTB electrode works better than the biochar could be due to the higher surface area, formation functional groups, removal impurities, and formation some micropores after HCl treatment. The biochar derived from marine biomass and treatment process developed here could provide a promising path for the low-cost, renewable, and environmentally friendly electrode materials.

Responsible editor: Bingcai Pan * Soheila Javadian [email protected]; [email protected]

1

Department of Physical Chemistry, Faculty of Science, Tarbiat Modares University, PO Box 14115-175, Tehran, Iran

2

School of Chemistry, College of Science, University of Tehran, Tehran, Iran

Keywords Biochar . Carbon . HCl treatment . Lithium-ion batteries . Anode . Environmentally friendly

Introduction Among all energy storage devices, Li-ion batteries (LIBs) have attracted increasing attention for portable electronic devices and transportation applications because of their obvious advantages including high energy density, good rate performance, reliable stability, and long lifespan (Javadian et al. 2016; Gul et al. 2014; Wang et al. 2016). To date, a few carbon-based materials, such as carbon nanotubes, and graphene have been investigated as battery electrodes (Jin et al. 2014). Unfortunately, due to their low-energy density, high cost of processing the materials, and negative environmental impacts, the application of these materials has been limited to comparatively small markets (Yu et al. 2016; Zheng et al. 2014; Hong et al. 2016). Considering the demand for renewable sources of energy, more and more attention has been focused on thermochemical processes (e.g., pyrolysis and hydrothermal gasification) to convert biomass to biofuel and valuable chemicals such as phenol, acetic acid, and furfural (Qu et al. 2015). Biochar is one of the by-products of the pyrolysis process which is often considered as a soil amendment, water treatment, activated carbon production, and catalyst support (Ren et al. 2014). Recently, extensive research has been carried out on the biochar derived from biomass to find a promising alternative source of carbonbased material which is low cost and environmentally friendly (Kalyani and Anitha 2013). Various types of biochars, particularly those derived from terrestrial biomass,

Environ Sci Pollut Res

have been applied in the systems of production and saving energy as fuel cells, batteries and supercapacitors (Huggins et al. 2015; Wang et al. 2015; Zequine et al. 2016; Zhang et al. 2016a). The capacity of 181 mAh g−1 at the current density of 200 mA g−1 after 220 cycles was observed for pomelo peels treated with phosphoric acid as an anode for sodium-ion battery (Hong et al. 2014). However, studies of using algal biochar, especially those derived from macroalgae, are relatively rare in the field of energy storage. Using a kind of macroalgae biomass named Polysiphonia fucoides, saturated with glucose solution, was showed the maximum capacity of 578 mAh g −1 (Nowak and Lisowska-oleksiak 2014). Also, the maximum specific capacitance of 230 mAh g−1 was obtained at the current density of 20 mA g−1 for carbon material derived from blue-green algae (Meng et al. 2015). Furthermore, N, O-codoped hierarchical porous carbons derived from algae was indicated a high specific capacity of 1347–1709 mAh g−1 for LiBs (Yu et al. 2016). In another study, in order to enhance the performance of the silicon anode, Si nanopowder was mixed with alginate and demonstrated a reversible capacity which is eight times higher than the theoretical capacity of graphite (Kovalenko et al. 2011). So, there is still significant room for the investigation of algal biochar potential in the LiBs and supercapacitors. Utilization of marine biomass, especially algae, is considered as the most suitable option for preparing biochar among other competitors because of reducing land use and water consumption in the manufacturing process cycle of Li-ion battery (Vassilev and Vassileva 2016). Nowadays, the severe eutrophication of coastal areas of, among others, Iran, the USA, Indonesia, the Philippines, Australia, Japan, and the Baltic region has raised public concern about the excessive blooming of macroalgae, triggered by various environmental pollutants of industrial or agricultural origin (Guo et al. 2013). Macroalgae also are a waste problem, because these plants spontaneously are decomposed by bacteria on the shore. This process consumes a considerable amount of oxygen and weakens the function of marine ecosystems. In addition, the excessive blooming of coastal macroalgae results in some hygienic problems such as spreading a pungent septic odor around which in turn leads to the excessive increase in number of insects (Plis et al. 2015). To address these problems and turn these global socio-environmental problems into opportunities, the potential of Caspian sea green macroalgae for producing bio-fuels was investigated (Safari et al. 2016). The results of this study showed that the char obtained from the pyrolysis of Cladophora glomerata has exclusive features, such as the existence of regular matrix of pores spread on the surface and the presence of considerable amounts of alkali and alkaline earth metals in its structure, which makes it distinct from

its terrestrial counterparts and a convenient option for upgrading biofuels (Norouzi et al. 2016). Apart from biofuel production technology, recently, a study was conducted regarding the sustainable utilization of Cladophora in energy storage sector as separators for lithium-ion batteries (Pan et al. 2016). The main novel investigations of the present study were as follows: &

& &

Utilization of the C. glomerata biochar obtained by pyrolysis at the temperature of 500 °C, which is considered as the optimal temperature in biofuel production (Norouzi et al. 2016) Characterization of the pyrolysis derived biochar of C. glomerata as an anode to investigate its potential in LiBs The holistic electrochemical measurements of the solid residue derived from C. glomerata as a widespread Caspian sea coast green macroalga

Materials and methods Preparation and treatment of biochar C. glomerata macroalgae were collected from the Southern coast of Caspian Sea, Iran, where a stable coverage was found. First, the collected C. glomerata was washed with distilled water, dried at the atmospheric condition for 48 h, and sieved to the particle size of smaller than 150 μm in diameter. Then, the collected C. glomerata was used as a feedstock in the pyrolysis process at the temperature of 500 °C for 1 h under Ar atmosphere. The schematic diagram of the pyrolysis experimental setup and the details of the method used in this study can be found elsewhere (Norouzi et al. 2016). Afterwards, in order to surface modification and removal impurities of biochar, 0.5 g of biochar was added to 10 ml of 1 M HCl and sonicated for 1 h. Then, the prepared solution was rotated at 8000 rpm for 10 min by means of centrifuge. After that, for obtaining HTB, the separated solid washed with deionized water and dried in vacuum oven at 80 °C for 10 h (Ryu et al. 2015). Preparation of cell The electrodes were prepared by mixing biochar or HTB with carbon black and poly(vinylidene fluoride) (PVDF) binder at the weight percentage of 75, 15, and 10 wt%, respectively, in N-methyl-2-pyrrolidone (NMP) solvent to form a slurry. The slurry was ground with mortar for 15 min to become homogeneous. Then, the viscose homogeneous slurry was coated on copper foil and dried in


vacuum oven at 100 °C for 24 h. The 2032 coin-type cells (20 mm in diameter and 32 mm in thickness) were assembled in a glove box under a high purity argon atmosphere (> 1 mg/L of O2 and H2O). The cell consisted of a prepared electrode as a working, lithium metal as a reference electrode as well as the counter, and a microporous membrane (Celgard 3501) as a separator and nonaqueous conventional electrolyte (1 mol dm−3 LiPF6 in EC/DMC = 1/1 (v/v)). Prior to battery testing, all cells were aged for 24 h.

Electrochemical impedance spectroscopy (EIS) analyses were done using the potentiostat/galvanostat 273 A (EG&G). Analyses of the obtained data were conducted with Z-view software. The electrolyte used in the aforementioned analyses consists of 1.0 mol dm−3 of LiPF6 in EC/DMC (1:1, v/v). The half-cells were assembled with a high purity of Ar gas at room temperature in the glove box.

Results and discussion Characterization and electrochemical measurements

Biochar and HTB characterization

Characterization of HTB

XRD

XRD measurements of the biochar and HTB were conducted from 10° to 90° with Xpert MPD diffractometer. The Raman spectrum was recorded using Takram P50C0R10 spectrometer. To characterize the structure and confirm the formation of functional groups, the FT-IR absorption technique was conducted on a Bruker ISS-88. A smooth transparent pellet of 0.55% biochar and 0.55% of HTB mixed with 95–99.5% potassium bromide (KBr) was made, and the infrared beam passed through this pellet. The thermal stability of HTB was determined using thermogravimetric analysis (TGA). The experiments were carried out by feeding HTB to a thermogravimetric analyzer (TGA Q50 V6.3 Build 189 Instrument). Test conditions were controlled under Ar atmosphere at the temperatures 30–600 °C with the heating rate of 20 °C min−1. Morphology was observed through field emission scanning electron microscope (FESEM, MIRA3 LM, Tuscan) and scanning electron microscope-energy dispersive X-ray spectroscopy (SEM-EDS, VEGA3 TESCAN at 20 kV). The biochar and HTB surface analysis was carried out by TriStar II 3020 version 3.02 Micromeritics. The samples were degassed at 200 °C for 4 h under 50 mTorr vacuum, and their BET surface area was determined.

The structures of both biochar and HTB derived from C. glomerata were studied by XRD diffractogram. The measurements revealed broad Bragg peaks at 2θ values of 10° and 90°. The XRD patterns are shown in Fig. 1a. Broad reflections were detected between 20° and 30° attribute to the amorphous carbon and confirm the existence of micropores in the structure of biochars. Furthermore, other intensive peaks were identified as impurities of inorganic materials which are in the structure of biochar mainly in the form of metal salts. Sharp peaks in the diffractogram of HTB indicate CaCO3 and SiO2. The presence of these materials can be ascertained by the results of EDS analysis and also are in agreement with the previous results in the literature (Zhang et al. 2016b; Yu et al. 2016). In addition, as shown in the XRD pattern of HTB, HCl treatment removed some of trace impurities and resulted in a carbon-rich material which is better to the stability of the electrochemical performance (Jiang et al. 2013).

Electrochemical measurements Cyclic voltammetry (CV) tests were carried out through the electroanalyzer system (Sama 500) which includes biochar or HTB as a working electrode and lithium metal as reference and counter electrodes. CV measurements were conducted under the potential range of 0–2.5 V with the scan rate of 0.1 mV s−1. The charge/discharge tests were performed at the range of 0–2.5 V by means of the battery analyzer Kimiastat model 127 A.

Raman spectroscopy analysis Figure 1b presents Raman spectra of both biochar and HTB samples. The peak around 1360 cm−1 (D band) assigns to disordered or turbostratic structure of carbon materials and another intensity peak at 1592 cm−1 (G band) representative the graphite-like structure (Hu et al. 2012). ID/IG is defined as a measure of disordered degree of carbon-based materials (Wang et al. 2013). The I D /I G ratio for biochar and HTB was 0.93 and 0.89, respectively, showing both biochar and HTB almost has a same disordered degree of carbon structure. We guess that the excellent electrochemical performance of HTB is very likely associated with higher surface area and formation of micropores which results from removing some impurities (Zequine et al. 2016).


Fig. 1 a XRD patterns of the biochar and HTB. b Raman spectra of the biochar and HTB. c FT-IR spectrum of the biochar and HTB. d Thermogravimetric analysis of the HTB

FT-IR spectroscopy analysis Considering the FT-IR results in Fig.1c, biochar and HTB have almost the same functional groups. The peak at around 3400 cm−1 is due to the vibrations of O–H functional groups. The signals at 2850 and 2900 cm−1 can be assigned to the C–H alkenes. The peak at 1600 cm−1 is due to the stretching mode of double bonds (C=C). The slender and distinct vibration peak at 1380 cm−1 stemmed from nitrogen group component (N–O). In addition, carboxylic acid’s functional groups were observed near 1090 cm−1. The IR bands ranging from approximately 400 to 800 cm−1 can be assigned to aromatic C–C ring structures in the biochar and HTB, which is in agreement with the results of Nanda et al. regarding the FT-IR analysis of biochar derived from horse manure (Nanda et al. 2016). Although the IR signals in both biochars are similar, the

HTB electrode led to some changes in the intensity of a number of peaks. The most significant change in peak intensity is related to carboxylic groups at 1090 cm−1 indicating that acid treatment increased carboxylic C–O bonds, such as phenol and aromatic C–H bonds, on the biochar surface (Tong et al. 2016). TGA In order to examine the thermal stability of HTB electrode, the TGA was performed. As shown in Fig. 1d, the decomposition of HTB occurred in three steps. The first weight loss at the temperature of below 150 °C was about 3 wt%, corresponding to drying. The second weight loss in at 150–450 °C was 2 wt%, which is in association with slight volatile release. The last decomposition ranging from 450 to 600 °C with the


major weight loss (5%) is associated with major decomposition in which the remaining volatile matters are released (Ren et al. 2014). The total weight loss in these samples was 10 wt% which confirmed the high thermal stability of HTB as compared to the other biochars (Wu et al. 2016).

FESEM Figure 2 demonstrates the FFSEM images of C. glomerata biochar treated with HCl. As shown, numerous micro- and macropores are spread all over the surfaces of biochar in a regular way with lengths of 200–300 nm and widths of 70–100 nm. The macroporous structures in HTB are primarily a reflection of the cellular organization of the raw material and also the cracking process happened during the thermochemical process (Safari et al. 2016; Deng et al. 2016). Also, microstructures suggest the effects of volatilization of carbon compounds and crystallization processes that can cause rearrangements within HTB. Macro-microporous structures improved the electrochemical performance of carbon-based Li-ion anodes through surface area enhancement and providing electrochemically active sites, as compared to their raw forms (Jiang et al. 2014).

Fig. 2 FESEM images of HTB

SEM–EDS analysis The SEM analysis was employed to investigate the effect of HCl treatment on the structure of biochar. As depicted in Fig. 3, after HCl treatment, great amounts of collapsed structures on the biochar surface (Fig. 3a) turned into a carbon-rich structure with a higher surface area in HTB (Fig. 3d) (Jin et al. 2013). This can be due to the eroding effect of HCl during acid treatment (Tong et al. 2016). In addition, in order to reveal mineral diversity, the EDS spectrum was performed on the surface of both biochar and HTB (Fig. 3c–f). The EDS spectra reveal great mineral diversity, which includes Si, Ca, K, Al, Fe, Cl, Mg, Na, Ti, S, and N, which are in association with the ash fraction of biochar. Moreover, the high intensity of C and O is peculiar to biochars (de la Rosa et al. 2014; Han et al. 2016). As shown in Fig. 3, the total weight percentage of carbon and oxygen increased from 56.5 to 85.6 wt%. This can be related to the formation of carboxylic acids and removal of impurities on the outer surface of biochar during HCl treatment. In order to reveal the distribution of elements on the surface of both biochar and HTB, elemental mapping was performed. As shown in Fig. 4, the carbon-rich area of HTB is more observable than that of biochar. Furthermore, in Fig. 4a, Ca and Si elements were observed on the border of biochar, but


Fig. 3 SEM images and corresponding EDS spectra of a the biochar and b HTB samples

they are almost vanished in the HTB, because of removal of impurities during HCl treatment. Other elements are negligible in HTB and, therefore, not clearly visible in the EDS mapping image. Surface area analysis BET According to the BET surface analysis, the surface areas of biochar and HTB were equal to 42.4 and 190.7 m2 g−1, respectively. The increment in surface area can be explained by the removal of some trace impurities and eroding effect of HCl during acid treatment (Tong et al. 2016). Although the surface area of HTB is lower than that of the previous results for biochar derived from agricultural wastes, its capacity is comparable with their, which may be related to the convenient pore volume for ion exchange and presence of considerable amounts of alkali and alkaline earth metals in the structure of biochar (Deng et al. 2016).

small reduction peaks at around 1.15 and 0.75 Vare associated with the irreversible reaction of the electrolyte with surface functional groups and the formation of passivation film, respectively (Hong et al. 2014; Ru et al. 2016a; Chang et al. 2007). Presumably due to the formation of the solid electrolyte interface (SEI) film, the discharge capacity in the first cycle is larger than that of other cycles (Wu et al. 2010). Furthermore, the peak at around 0.2 V corresponds to the Li+ intercalation and deintercalation (Reiter et al. 2012). The smooth current response during the potential scan of anodes in the half cell is matched with typical cycling voltammetry curves of carbon for Li-ion insertion/extraction. In addition, there is considerable overlap between the third and tenth cycles, indicating the highly reversible and electrochemically stable performance of the HTB and biochar electrodes. Because the area of CV curves is larger in HTB electrode than in biochar electrode, we can conclude that the capacity of biochar was increased by surface modification treatment with HCl (Ryu et al. 2015). Charge and discharge measurements

Electrochemical measurements CV The CV of biochar and HTB electrodes was performed in the potential range of 0–2.5 V at the scan rate of 0.1 mV s−1. As shown in Fig. 5a, b, for both electrodes, in the first cycle, the

The charge–discharge profile was recorded between 0 and 2.5 V vs. Li+/Li at the current density of 0.1 A g−1 (Fig. 6a, b). The HTB electrode was indicated the specific charge capacity of 491, 444, and 370 mAh g−1 in the first, third, and tenth cycles, respectively. While, these values for biochar electrode is much lower than HTB electrode. In terms of the


Fig. 4 SEM elemental mapping for both a biochar and b HTB

Fig. 5 CV of a the biochar and, b HTB electrodes for first, third, and tenth cycles at scanning rate of 0.1 mV s−1 in the voltage range of 0–2.5 V


Fig. 6 Galvanostatic charge–discharge curves of a biochar and b HTB electrodes at 0.1 A g−1. c The rate capability of the biochar and HTB electrodes at different current densities and d cycle life at the current density of 0.1 A g−1

specific discharge capacity, in the first cycle, capacity of biochar and HTB electrodes reached 480 and 700 mAh g−1, respectively, which is higher than the theoretical specific capacity of graphite (372 mAh g−1). This high discharge capacity could be due to the higher theoretical capacity of alkali and alkaline earth metals such as Mg, Ca, Na, and K, which was ascertained by Norouzi et al. through ICP-OES analysis (Norouzi et al. 2016). The rate performance of biochar and HTB electrodes is shown in Fig. 6c. The cell was discharged and charged at different current densities from 0.1 to 1 A g−1. The discharge capacity of biochar was 479, 158, 111, and 66 mAh g−1 at various current densities of 0.1, 0.2, 0.5, and 1 A g−1, respectively. For comparison, HTB electrode with higher surface area than biochar, demonstrated the capacity of 698, 322, 226, and 150 mAh g−1 at the current density of 0.1, 0.2, 0.5, and 1 A g−1, respectively. Furthermore, when the current density decreased back to 0.1 A g−1, the specific capacity showed

96 and 89% of discharge capacity retention compared to the tenth cycle at 0.1 A g−1 for HTB and biochar electrodes, respectively. The discharge capacity as a function of cycle number of biochar and HTB electrodes at the current density of 0.1 A g−1 is illustrated in Fig. 6d. After 100 cycles, HTB electrode had the remarkably high reversible discharge capacity of 350 mAh g−1. By contrast, biochar exhibited the relatively low reversible discharge capacity of 152 mAh g−1 after 100 cycles. The better electrochemical performance of the HTB electrode compared to the biochar electrode is related to the change of porous structure after HCl treatment (Ryu et al. 2015; Yin et al. 2007). In addition, after the initials cycles, both cells indicated significant capacity fades resulting from the continuous trapped Li ions and the formation of SEI film (Yu et al. 2016). The very good cycling performance after initial cycles for both electrodes (specially, HTB) is caused by the high porosity and moderate surface area of the


Fig. 7 a, b EIS of the biochar and HTB electrodes before discharge and after 100 cycles

electrodes that shows proper electrochemical stability. After the initial forth cycle, the coulombic efficiencies in both products increased dramatically to the range of about 99%, demonstrating the outstanding reversibility of both electrodes. A comparison of electrochemical performance especially the discharge capacity at first and last cycle of different biochars derived from agricultural waste is summarized at Table 1. According to Table 1, the biochar used in this work showed better discharge capacity compared to the biochar derived from rice straw which treated with HCL and H2O2. EIS analysis To demonstrate the kinetics of Li ions in the electrode and its general electrochemical performance, the EIS of biochar and Table 1

HTB electrodes was measured in the half cell before discharge and after 100 cycles, from 100 kHz to 10 MHz. Before discharge, the Nyquist plot of the coin cell showed that impedance spectra are composed of a semicircle and a long inclined line (Warburg impedance) in medium to high and low frequencies for both electrodes, respectively. The semicircle shows the charge transfer resistance in the electrolyte/ electrode interface. The Warburg part shows the diffusion of Li + ions from the solution into the electrode interface. Meanwhile, after 100 cycles, impedance spectra indicated two semicircles. The higher frequency region is ascribed to the interfacial charge transfer process, and the medium frequency range is related to the SEI film (Gu et al. 2014). All data are analyzed using equivalent circuits and shown in Fig. 7a, b, where Rs, Rct, CPE, Rsei, and W are the resistance

Electrochemical performance of LIBs basing on different biochars derived from agricultural waste

Samples (anode)

Treatment

Rate

Initial capacity (mAh g−1)

Cycle capacity (mAh g−1)

Ref.

Waste tea leaves

HCl

0.2 C

869

479 (200th)

Zequine et al. (2016)

Rice straw

HCl

0.2 C

680

About 200 (5th)

Ryu et al. (2015)

Rice straw

H2O2

0.2 C

650

About 170 (5th)

Ryu et al. (2015)

Peanut shell

KOH

1 A g−1

1077

474 (400th)

Lv et al. (2015)

Bean-dreg

KOH

0.1 C

801

748 (100th)

Ru et al. (2016b)

Bean-dreg

ZnCl2

0.1 C

664

605 (100th)

Ru et al. (2016b)

Cladophora glomerata

HCl

0.1 A g−1

700

350 (100th)

This work

Environ Sci Pollut Res Table 2 EIS model fit data for the biochar and HTB electrodes before and after cycling Cycle number

Resistance (Ω)

Biochar electrode

HTB electrode

The fresh cell

Rs Rct Rs Rct

7.1 478 9.8 1011

2.3 55.2 5.2 317.5

Rsei

801.6

101

After 100 cycles

contribution from the electrolyte, charge transfer at the conductive, a constant phase element, resistance of surface film, and the Warburg impedance caused by the lithium-ion diffusion process in the electrode, respectively. Before the first semicircle, the electrolyte resistance is observed. Since, electrolyte conditions are the same for two samples, we can reach the conclusion that this difference in electrolyte resistance can be attributed to the type of electrode used for measuring conductivity. Also, the fitting data demonstrate that the values of Rs and Rct for both electrodes increased after 100 cycles, which suggests SEI layer generation after a few cycles and the resistance increment of the surface film (Table 2) (Li et al. 2013). Generally, HTB electrode has a much lower resistance than biochar electrode as revealed in the impedance spectra. This can be interpreted to the finer porous carbon structure and high surface area of HTB electrode caused by the HCl treatment (Guo et al. 2015; Lv et al. 2015).

Conclusion We have studied a new generation of carbonaceous material from marine biomass precursors for utilization in battery industry as a result of its abundant, cheap, widely available, and sustainable resource. The biochar obtained from the pyrolysis of C. glomerata as green macroalgae of the Caspian sea coast has been found to be a good source of the carbon-based electrode in Li-ion batteries. The characterization of HTB demonstrated a high thermal stability and macro-/microporous structure which make it a suitable candidate for utilization in energy storage devices. Electrochemical measurements suggested the promising capacity of the HTB electrode for application in commercial Li-ion batteries. Moreover, the higher specific capacity (700 mAh g−1) of this kind of material as compared to the theoretical specific capacity of graphite (372 mAh g−1) results from the significant amount of alkali and alkaline earth metals in the structure of HTB electrode. Acknowledgements The authors would like to thank Dr. Ahmad Tavasoli, from University of Tehran, for providing the facilities to conduct the thermochemical tests. Also, the authors thank Arash Tahmasbi

from the University of Science and Technology Liaoning and Amir Pourhosseini (Arbab) for their kind support and guidance for the better production of this paper.

References Chang C, Liu S, Wu J, Yang C (2007) Nano-tin oxide/tin particles on a graphite surface as an anode material for lithium-ion batteries. Society 111(44):16423–16427 Deng J, Li M, Wang Y (2016) Biomass-derived carbon: synthesis and applications in energy storage and conversion. Green Chem 18: 4824–4854 Gu X, Wang Y, Lai C et al (2014) Microporous bamboo biochar for lithium-sulfur batteries. Nano Res 8:129–139 Gul H, Uysal M, Çetinkaya T et al (2014) Preparation of Sn-Co alloy electrode for lithium ion batteries by pulse electrodeposition. Int J Hydrog Energy 39:21414–21419 Guo C, Zhou L, Lv J (2013) Effects of expandable graphite and modified ammonium polyphosphate on the flame-retardant and mechanical properties of wood flour-polypropylene composites. Polym Polym Compos 21:449–456 Guo J, Zhang J, Jiang F et al (2015) Microporous carbon nanosheets derived from corncobs for lithium–sulfur batteries. Electrochim Acta 176:853–860 Han Y-J, Chung D, Nakabayashi K et al (2016) Effect of heat pretreatment conditions on the electrochemical properties of mangrove wood-derived hard carbon as an effective anode material for lithiumion batteries. Electrochim Acta 213:432–438 Hong K, Qie L, Zeng R et al (2014) Biomass derived hard carbon used as a high performance anode material for sodium ion batteries. J Mater Chem A 2:12733 Hong JE, Oh RG, Ryu KS (2016) Electrochemical possibility of iron compounds in used disposable heating pads and their use in lithium ion batteries. Environ Sci Pollut Res 23:14656–14662 Hu ZJ, Cui Y, Liu S et al (2012) Optimization of ethylenediamine-grafted multiwalled carbon nanotubes for solid-phase extraction of lead cations. Environ Sci Pollut Res 19:1237–1244 Huggins TM, Pietron JJ, Wang H et al (2015) Graphitic biochar as a cathode electrocatalyst support for microbial fuel cells. Bioresour Technol 195:147–153 Javadian S, Kakemam J, Sadeghi A, Gharibi H (2016) Pulsed current electrodeposition parameters to control the Sn particle size to enhance electrochemical performance as anode material in lithium ion batteries. Surf Coat Technol 305:41–48 Jiang J, Zhang L, Wang X et al (2013) Highly ordered macroporous woody biochar with ultra-high carbon content as supercapacitor electrodes. Electrochim Acta 113:481–489 Jiang J, Zhu JH, Ai W et al (2014) Evolution of disposable bamboo chopsticks into uniform carbon fibers: a smart strategy to fabricate sustainable anodes for Li-ion batteries. Energy Environ Sci 7:2670– 2679 Jin H, Wang X, Gu Z, Polin J (2013) Carbon materials from high ash biochar for supercapacitor and improvement of capacitance with HNO3 surface oxidation. J Power Sources 236:285–292 Jin H, Wang X, Shen Y, Gu Z (2014) A high-performance carbon derived from corn stover via microwave and slow pyrolysis for supercapacitors. J Anal Appl Pyrolysis 110:18–23 Kalyani P, Anitha A (2013) Biomass carbon & its prospects in electrochemical energy systems. Int J Hydrog Energy 38:4034–4045 Kovalenko I, Zdyrko B, Magasinski A et al (2011) A major constituent of brown algae for use in high-capacity Li-ion batteries. Science 334(80):75–79

Environ Sci Pollut Res Li H, Pang J, Yin Y et al (2013) Application of a nonflammable electrolyte containing Pp13TFSI ionic liquid for lithium-ion batteries using the high capacity cathode material Li[Li0.2Mn0.54Ni0.13Co0.13]O2. RSC Adv 3:13907–13914 Lv W, Wen F, Xiang J et al (2015) Peanut shell derived hard carbon as ultralong cycling anodes for lithium and sodium batteries. Electrochim Acta 176:533–541 Meng X, Savage PE, Deng D (2015) Trash to treasure: from harmful algal blooms to high-performance electrodes for sodium-ion batteries. Environ Sci Technol 49:12543–12550 Nanda S, Dalai AK, Gökalp I, Kozinski JA (2016) Valorization of horse manure through catalytic supercritical water gasification. Waste Manag 52:147–158 Norouzi O, Jafarian S, Safari F et al (2016) Promotion of hydrogen-rich gas and phenolic-rich bio-oil production from green macroalgae Cladophora glomerata via pyrolysis over its bio-char. Bioresour Technol 219:643–651 Nowak AP, Lisowska-oleksiak A (2014) Red algae—an alternative source of carbon material for energy storage application. Int J Electrochem Sci 9:3715–3724 Pan R, Cheung O, Wang Z et al (2016) Mesoporous Cladophora cellulose separators for lithium-ion batteries. J Power Sources 321:185–192 Plis A, Lasek J, Skawińska A, Zuwała J (2015) Thermochemical and kinetic analysis of the pyrolysis process in Cladophora glomerata algae. J Anal Appl Pyrolysis 115:166–174 Qu WH, Xu YY, Lu AH et al (2015) Converting biowaste corncob residue into high value added porous carbon for supercapacitor electrodes. Bioresour Technol 189:285–291 Reiter J, Nádherná M, Dominko R (2012) Graphite and LiCo1/3Mn1/ 3Ni1/3O2 electrodes with piperidinium ionic liquid and lithium bis(fluorosulfonyl)imide for Li-ion batteries. J Power Sources 205: 402–407 Ren S, Lei H, Wang L et al (2014) Hydrocarbon and hydrogen-rich syngas production by biomass catalytic pyrolysis and bio-oil upgrading over biochar catalysts. RSC Adv 4:10731 de la Rosa JM, Paneque M, Miller AZ, Knicker H (2014) Relating physical and chemical properties of four different biochars and their application rate to biomass production of Lolium perenne on a Calcic Cambisol during a pot experiment of 79 days. Sci Total Environ 499:175–184 Ru H, Bai N, Xiang K et al (2016a) Porous carbons derived from microalgae with enhanced electrochemical performance for lithium-ion batteries. Electrochim Acta 194:10–16 Ru H, Xiang K, Zhou W et al (2016b) Bean-dreg-derived carbon materials used as superior anode material for lithium-ion batteries. Electrochim Acta 222:551–560

Ryu D-J, Oh R-G, Seo Y-D et al (2015) Recovery and electrochemical performance in lithium secondary batteries of biochar derived from rice straw. Environ Sci Pollut Res 22:10405–10412 Safari F, Norouzi O, Tavasoli A (2016) Hydrothermal gasification of Cladophora glomerata macroalgae over its hydrochar as a catalyst for hydrogen-rich gas production. Bioresour Technol 222:232–241 Tong Y, Mayer BK, McNamara P (2016) Triclosan adsorption using wastewater biosolids-derived biochar. Environ Sci Water Res Technol 2:761–768 Vassilev SV, Vassileva CG (2016) Composition, properties and challenges of algae biomass for biofuel application: an overview. Fuel 181:1–33 Wang L, Mu G, Tian C et al (2013) Porous graphitic carbon nanosheets derived from cornstalk biomass for advanced supercapacitors. ChemSusChem 6:880–889 Wang M, Lai Y, Fang J et al (2015) N-doped porous carbon derived from biomass as an advanced electrocatalyst for aqueous aluminium/air battery. Int J Hydrog Energy 40:16230–16237 Wang Y, Yu Y, Huang K et al (2016) Quantifying the environmental impact of a Li-rich high-capacity cathode material in electric vehicles via life cycle assessment. Environ Sci Pollut Res 24(2):1–10. https://doi.org/10.1007/s11356-016-7849-9 Wu XL, Chen LL, Xin S et al (2010) Preparation and Li storage properties of hierarchical porous carbon fibers derived from alginic acid. ChemSusChem 3:703–707 Wu H, Che X, Ding Z et al (2016) Release of soluble elements from biochars derived from various biomass feedstocks. Environ Sci Pollut Res 23:1905–1915 Yin CY, Aroua MK, Daud WMAW (2007) Review of modifications of activated carbon for enhancing contaminant uptakes from aqueous solutions. Sep Purif Technol 52:403–415 Yu W, Wang H, Liu S et al (2016) N, O-codoped hierarchical porous carbons derived from algae for high-capacity supercapacitors and battery anodes. J Mater Chem A 4:5973–5983 Zequine C, Ranaweera CK, Wang Z et al (2016) High performance and flexible supercapacitors based on carbonized bamboo fibers for wide temperature applications. Sci Rep 6:31704 Zhang X, Yan P, Zhang R et al (2016a) Fabrication of graphene and coreshell activated porous carbon-coated carbon nanotube hybrids with excellent electrochemical performance for supercapacitors. Int J Hydrog Energy 41:6394–6402 Zhang Y, Guo X, Yao Y et al (2016b) Mg-enriched engineered carbon from lithium-ion battery anode for phosphate removal. ACS Appl Mater Interfaces 8:2905–2909 Zheng C, Zhou X, Cao H et al (2014) Synthesis of porous graphene/ activated carbon composite with high packing density and large specific surface area for supercapacitor electrode material. J Power Sources 258:290–296