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= Preparation and Characterization of Chitosan Nanocomposite Based on Nanoscale Silver an= d Nanomontmorillonite

=  

= Fatemeh-Sadat Ebnerasool = and Negar Motakef-Kazemi,

=  

ABSTRACT

<= span style=3D'mso-bookmark:OLE_LINK8'>The chitosan nanocomposites were rapidly prepared by simple solution method. This biopolymer matrix was modified by prepared nanoscale silver (Ag) using in situ <= span style=3D'mso-bookmark:OLE_LINK8'>= synthesis<= span style=3D'mso-bookmark:OLE_LINK8'> from precursor and <= /span><= span style=3D'mso-bookmark:OLE_LINK8'>= nanomontmorillonite<= span style=3D'mso-bookmark:OLE_LINK8'> (NMMT). Moreover, the samples were characterized by fourier transform infrared (FTIR) spectroscopy, thermogravimetric analysis (TGA), field emission scanning electron microsco= py (FESEM), and energy dispersive x-ray spectroscopy (EDX). Moreover, the water vapor properties (WVP) of nanocomposites were investigated using gravimetric standard. In addition, the antibacterial activity of nanocomposite was meas= ured by the well diffusion method on Muller–Hinton Agar against Esc= herichia coli (E. coli) <= span style=3D'mso-bookmark:OLE_LINK8'>by zone inhibition. Finally, based on the obtained results, the nanocomposite can have a good candidate for different applications and food packaging industry.

 

= Keywords:= Nanocomposite, Chitosan, Nanoscale silver, Nanomontmorillonite, Packaging.

=  

= 1. Introduction

Today, nanotechnology has expanded in vari= ous fields duo to the potential of application benefits in the world [1]. Nanomaterials have size of 1-100 nm that showed unique properties because of small size and high surface area [2]. In recent years, population growth wa= s resulted in the extension of packaging for food source protection [3]. Since, nanote= chnology can be affected because of the wide application in production, processing, storage, packaging, and transport of food products with environment protect= ion and earth resources [4]. The main factor is included a lot of effort to produce functional materials, food processing, product development, methods, and tools design<= /span> [5]. The application of nanocomposite is expanded because of its unique properties in food packaging [6,7]. The nanocomposites can control the permeability of polymer and increa= se shelf life to improve the efficiency of packaging materials [8]. In packaging industry, the use of biodegradable material can reduce the= waste and results to consume the less material precursor [9].=

= The nanomaterials have been developed the research work in food product= s [10]. Recently, biodegradable nanocomposite has been used to investigat= e barrier materials and antimicrobials in packaging [11]. = Moreover, nanocomposite based on = = biopolymer = = can be named such as starch [12,13], cellulose <= /a>[14], and chito= san (CS) [15,16] for food packaging. Moreover, chitosan is derived from chitin, and its use has expanded as biomaterials [= = 17]. The chitosan has several excellent properties such as biodegradability, non-toxicity, and antimicrobial properties which investigated in food packa= ging widely [18-20]. The polymer nanocomposite included the polymer as matrix phase and nanomaterial as filler phase to improvement of physical and mechanical properties = [21]. In addition, the use of nanocomposites can enhance the applications of differe= nt properties for nanomaterials in food packaging technology [22]. Moreover, silver nanoparticles are well known as antimicrobial agents in curative and preventive health care with low toxicity for humans<= /span>= [23,24]. Clay filler has received significant att= ention because of suitable dispersion, thermal stability, and barrier properties in polymer nanocomposites [25]. <= /span>In the present study, chitosan nanocomposite based on nanoscale silver and = nanomontmorillonite has been prepared by a simple method= using in situ synthesis <= span style=3D'mso-bookmark:OLE_LINK101'>of nanoscale silver for food packaging. The aim of this work is to study antibacterial activity against Escherichia coli and barrier for water vapor permeability= of this nanocomposite= .

=  

= 2. Experimental procedure

= 2.1. Materials

= All chemicals used were analytical grade. Chitosan was obtained from Sigma–Aldr= ich with medium molecular weight. Glacial acetic acid, <= /a>trisodium citra= te and silver nitrate (AgNO3) were obtained from Merck. Ultra-pure water was used for the preparation of all reagents solutions. Moreover, the modif= ied montmorillonite clay was obtained from Nano Pasargad Novin Company. The test strains, Escherichia coli ATCC 1399, were procured f= rom Islamic Azad University.

=  

2.2. Methods

= 2.2.1. Preparation of nanoscale Ag

= The nanoscale silver was prepared by reducing silver nitrate using trisodium citrate. AgNO3 solution (2 M) was added to the 1% acetic acid solution. Then trisodium cit= rate solution (4 M) was added to the resulting solution and stirred for 2 h. The= nanoscale silver was = centrifuged at 10,000 rpm for 10 min and dried at room temperature for 48 h [26]. =

=  

= 2.2.2. Preparation of chitosan–nanoscale Ag nanocomposite

= Chitosan aqueous solution of 2 wt.% was prepared by dissolving  chitosan powder (2 g) in 100 mL of 1% (v/v) acetic acid. Then AgNO3 solution (2 M) and trisodium citrate (4 M) were added to the chitosan solution and stirred for 2 h at room temperature. The preparation of chitosan–nanoscale Ag nanocomposite was don= e by in situ synthesis of nanoscale silver. The mixture solution was cast on= to glass plates and dried at room temperature for 48 h [26-27].

=  

= 2.2.3. Preparation of chitosan–NMMT nanocomposite

= Chitosan aqueous solution of 2 wt.%  was pre= pared in acetic acid solution (1% v/v). The nanomontmorillonite was prepared by dispersing of montmorillonite clay int= o 10 mL of 1% acetic acid solution and vigorously stirring for 24 h. The nanomontmorillonite solution (1% and 3 = wt.%) was added slowly to chitosan solution and stirred continuously for 2 h. The= n the mixture was cast onto glass plates and dried at = room temperature for 72 h [26-27].

=  

= 2.2.4. Preparation of chitosan–nanoscale Ag–NMMT nanocomposite=

= Chitosan aqueous solution of 2 wt.% was prepared by 1% (v/v) acetic acid. Then AgNO3<= /sub> solution (2 M), trisodium citrate<= span style=3D'font-size:12.0pt;font-family:"Times New Roman","serif";mso-ascii-t= heme-font: major-bidi;mso-hansi-theme-font:major-bidi;mso-bidi-theme-font:major-bidi'>= (4 M), and nanomontmor= illonite solution (1% and 3% wt) were added into the chitosan solution and stirred f= or 2 h at room temperature. Then the mixture was cast onto glass plates and drie= d at room temperature for 72 h [26].

=  

= 2.3. Characterization of samples

The samples were characterized by = Fourier transform infrared spectroscopy, thermogravimetric analysis, field emission scanning electron microscop= y, and energy-dispersive x-ray spectroscopy. FTIR <= /a>spectra were obtained using a FTIR spectrophotometer (SHIMADZU Co) in the range of 400–4000 cm−1 at a resolution of 4 cm−1 i= n a KBr matrix. The thermogravimetric analysis was measured by a TGA-SF1 (Mettl= er Co) that carried out to 800 C at the heating rate of 20 C/min under nitrogen atmosphere. The morphologies of the samples were analyzed on= a MIRA3 TeScan LMU (TeScan Co) FESEM at 5 kV. Afterwards, th= e specimens were coated with a thin conductive gold layer before observation. The EDX analysis was measured by usingASK SEM-CL View VIS (OXFORD INSTRUMENTS Co. T= he antimicrobial activity was investigated for pure chitosan, montmorillonite,= and chitosan-based nanocomposites by measurement of the minimum inhibition concentration (MIC) against E. coli as gram-negative bacteria. The c= ells of E. coli were cultivated on Mueller-Hinton Agar and incubated at 3= 7ºC for 1 day. The samples were systematically diluted from 0.02% (w/v) to 0.000625% (w/v) to determine of the MIC values.

= The WVP of films was determined using gravimetric standard ASTM E96-= 05 [28]. Glass bottles were used to perform the test with a diameter of 20 mm and de= pth of 45 mm. The bottles were filled with 3 g of CaCl2 for maintaining a relative humidity (0% RH) and covered with the film specimen. = The result bottles were placed in a container containing K= 2SO4 super saturated solution (97% RH) at 25 C. Then the bottl= es were weighed ten times at 3 h intervals. Afterwards, water vapor transmissi= on rate (WVTR) was determined from slope of mass change of bottle versus time curve divided by area of glass bottle mouth (m2). Then the WVP of film was calculated using Eq. 1:

= WVP =3D WVTR × L / ΔP    (1)<= /o:p>

= where WVTR is water vapor transmission rate (g/m2s) through film, L is= the mean thickness of film (m), and ∆P is partial water vapor pressure difference (Pa) across film [21].

=  

= 3. Results and Discussion

= 3.1. FTIR

= The FTIR spectra are shown for CS, nanoscale Ag, NMMT, CS-nan= oscale Ag nanocomposite, CS-NMMT nanocomposite and CS-nanoscale Ag-NMMT nanocompos= ite in Fig. 1. The spectrum of chitosan (Fig. 1 a) shows the band at 1647 cm−1 that corresponds to the amide function due to acetylated amine, where= as the band at 1600 cm−1 is corresponded to the free amine I function due to deacetylated amine. The broad band at 3400-3500 cmW= 22;1 is assigned with the overlapping O-H stretching bands. The N-H bending, C-H bendin= g, and C-O stretching are shown at 1600cm−1, 1382 cm−1= and 1087 cm−1 respectively. The results corresponded to the results [27, 29]. The FTIR spectrum of NMMT (Fig.1 b) is shown the vibration bands at 3624 cm−1 for = O-H, at 3425 cm−1 due to interlayered O-H, at 1641 cmͨ= 2;1 for H-O-H bending, at 1035 and 914 cm−1 for Si-O stretching, and at 528 and 468 cm−1 for Si-O bend= ing. These characteristic peaks have shifted to lower frequencies in nanocomposi= tes which recommend some interaction between functional groups of chitosan and = NMMT. The results are corresponded to the reported results [30, 31]. The FTIR spe= ctra of CS-NMMT nanocomposite and CS-nanoscale Ag-NMMT nanocomposite (Fig.1 c,d)= are shown the combination of the characteristic absorption bands due to nanosca= le Ag, NMMT and amine groups of chitosan. The overlapping peak of O-H and N-H show= s more broadening at 3103-3392 cm−1 in pure chitosan. = The bands of−NH2 groups are shifted to 1616 and 1668 cm&#= 8722;1 in the CS-NMMT and CS-NMMT -nanoscale Ag nanocomposites. This shift corresponds to deformation and vibration of chito= san amine groups. The characteristic bands of clay are all shifted to lower absorption wavenumber from 500 to 1035 cm−1 as shown on the figure. These observations are confirmed the electrostatic interaction = of chitosan’s NH2+ groups with the negatively charged silicate laye= r of clay in both composites. The spectrum of CS-nanoscale Ag nanocomposites is investigated (Fig.1 e). The omission of existing should= erin 1548 cm−1 is related to NH bending vibration bond that shows interaction between chitosan and nanosca= le Ag that corresponds to the results [27]. The FTIR spectra of nanoscale Ag (Fig.1 f)= are shown the peaks at 1643 cm−1, 1578 cm−1, = 1392 cm−1 and 1278 cm−1 that corresponded to t= he results [31]. Based on FTIR= results, the qualitative change is confirmed for nanocomposite formation.

= Fig 1. Transmission FTIR spectra of (a) pure CS, (b) NMMT, (c) CS-NMMT nanocomposite, (d) CS-nanoscale Ag-NMMT nanocomposite, (e) CS-nanoscale Ag nanocomposite and (f) nanoscale Ag.

=  

=  

= 3.2. TGA

= The weight-loss curve was obtained by heating of samples and determined thermal stability analysis as the function of temperature. The TGA analysis is shown for CS-NMMT nanocomposite that two weight = loss regions were observed (Fig. 2. a), = about 100°C (related to loss of water), and about 300°C (related to degradation o= f chitosan), at the result the remained weight = perent was related to NMMT.<= /span> The TGA analysis is shown for CS-nanoscale Ag nanocomposite that two weight loss regions were observed (Fig. 2. b), about 100°C (related to loss = of water), and about 300 °C (related to degradation of chitosan), at the result the remained weight perent was rela= ted to silver. The TGA analysis is shown for CS-nanoscale = Ag-NMMT nanocomposite that two weight loss regions we= re observed (Fig. 2. c), about 100°C (related to loss of water), and about 300°C (related to degradation of chitosan), at the result the remained weight perent was related to NMMT and silver. Based on TGA results, thermal stability of nanocomposite which are as follows: CS-NMMT > CS-nanoscale Ag- NMMT >= CS-nanoscale Ag that the presence of NMMT and nanoscale Ag have been caused= an increase and decrease in this property respectively. CS-nanoscale Ag- NMMT was avera= ge thermal stability because of the opposite effects of two fillers. The TGA results are comparable to those of previous research= ers [32].

= Fig 2. The TGA of (a) CS-NMMT nanocomposite, (b) CS-nanoscale Ag nanocomposite, and (c) CS-nanoscale Ag-NMMT nanocomposite.

=  

= 3.3. FESEM

= The size and morphology structures of samples were studied using FESEM that sho= wn nanoscale Ag, NMMT, CS-nanoscale Ag nanocomposite, CS-NMMT nanocomposite, = CS-nanoscale Ag-NMMT nanocomposite in Fig. 3. Moreover, the NMMT has shaped sheet-like layer silicates and that includ= ed a two-dimensional layer with thickness of about 1 nm and length and width of about 300 nm to several microns (Fig.3 a). The morphol= ogy of nanoscale Ag has been nanorod arrays with the mean diameter of about 40 nm<= span lang=3DEN style=3D'font-size:12.0pt;font-family:"Times New Roman","serif"; mso-ascii-theme-font:major-bidi;mso-hansi-theme-font:major-bidi;mso-bidi-th= eme-font: major-bidi;mso-ansi-language:EN'> and the length of about 200 nm (Fig.3 b).= The morphology= of CS-nanoscale Ag has been nanorod arrays with the mean diameter of about 70 nm and the lengt= h of about 250 nm (Fig.3 c) that slightly increased in size due to the presence = of chitosan. Moreover, the CS-NMMT nanocomposite is shown the palte-like structure with thickness of 30 nm and = length and width of about 500 nm (Fig.3 d). The CS-nanoscale Ag-NMMT nanocomposite is shown nanoparticle morphology for nanoscale A= g with size of about 40 nm and palte-l= ike structure for NMMT with diameter of 40 nm and length and widt= h of 200 nm (Fig.3 e). = These images are represented the = uniform structure and complete distributio= n in the matrix of chitosan polymer. Also, the nanoscale silver morphology = is observed nanoparticle instead of nanorod for chitosan nanocomposite in the presence of NMMT. In fact, NMMT is acted as capping agent and controlled crystal growth.

= Fig 3. The SEM of (a) NMMT, (b) nanoscale Ag, (c) CS-nanoscale Ag nanocomposite, (d) CS-NMMT nanocomposite and (e) CS-nanoscale Ag-NMMT nanocomposite.

 

<= /span>= 3.4. EDX =

= The EDX analysis is shown for nanoscale Ag, Cs-nanoscale Ag nanocomposit= e, (c) CS-NMMT nanocomposite and CS-nanoscale Ag-NMMT nanocomposite in figure = 4. The intense signal has been at 3 keV that confirmed the presence of nanoscale silver (Fig.4 a). The EDX analysis of CS-nanoscale Ag nanocomposite has been the signal of nanoscale silver at 3 keV and appeared the other signa= l of C, O, and N due to chitosan (Fig.4 b). Based on the result is confirme= d the presence of CS a= nd nanoscale silver. The EDX analysis of CS-NMMT has = been the signal of clay for Al and Si and appeared the other signal of C, O, and= N due to chitosan (Fig.4 c). The EDX analysis of CS-nanoscale Ag-NMMT nanocom= posite has indicated the presence of silver, = chitosan and clay in the nanocomposite (Fig.4 d).

= Fig 4.= EDX analysis of (a) nanoscale Ag, (b) CS-nanoscale Ag nanocomposite, (c) CS-NMMT nanocomposite and (d) CS-nanoscale Ag-NMMT nanocomposite.=

 

3.5. WVP tests=

WVP test is used to study water vapor b= arrier properties of packaging films and investigated the inhibition of= the humidity exchange between food and environment. The WVP of samples was determined by the gravimetric method using WVP (Table 1). The chitosan film was showed the reduction in = WVP permeability. The = increase and decrease in = WVP permeability were observed because of the addition of nanoscale Ag and NMMT respectively into chitosan nanocomposite films. The nanoscale Ag can form the hydrogen bond and resulted to the incr= ease passage while NMMT with high aspect ratio can disperse uniformly in polymer matrix and lead to prevent permeability.

 

= Table 1. WVP of samples.

Sample=

Sample

WVP (g/(m s Pa))

1

CS solution 2% wt

1.92 × 10-10

2

3

CS-MMT nancomposite 3%

1.63 × 10-10

4

5

CS- Silver -MMT nancomposite 3%

4.78 × 10-10

6

=                                     <= /o:p>

= 3.6. Antibacterial activity =

= The antibacterial activity of samples was tested against E. coli bacteria using= the well diffusion method on Muller–Hinton Agar. All tests were done in triplicate. The antibacterial tests were summarized in Table 2 that observed the effect of chitosan and nano= scale Ag while NMMT has not exhibited any effect. The inhibition zone was the same for nanoscale Ag and chitosan–nanoscale Ag and the effect of nanoscale Ag has been evident apparent in comparison with chitosan. The minimum inhibitory concentration = was 0.005 mol/L for chitosan–nanoscale Ag composite. Antibacterial activity results are comparable to those of previous researchers [33].

=  

= Table 2. Inhibition zone of samples.

Sample

Sample

Inhibition zone (mm)

1

2

3

4

5

=  

= 4. Conclusions

= The chitosan nanocomposites were successfully prepared from NMMT and = in situ synthesis of nanoscale silver using the reducti= on of AgNO3 by trisodium citrate. Based on FESEM results, in situ synthesis of <= span style=3D'font-size:12.0pt;font-family:"Times New Roman","serif";mso-ascii-t= heme-font: major-bidi;mso-hansi-theme-font:major-bidi;mso-bidi-theme-font:major-bidi'>= nanoscale Ag was formed silver nanoparticle in chitosan nanocomposite duo to the pres= ence of NMMT although the silver nanorod was observed by reduc= tion of silver precursor. Moreover, the TGA analysis was shown the increase in t= hermal stability duo to the presence of NMMT. The FTIR and EDS of nanocomposites w= ere confirmed the presence of chitosan and silver. Finally, the effective role = of NMMT and nanoscale Ag were obser= ved= in the decrease of WVP<= span lang=3DEN style=3D'font-size:12.0pt;font-family:"Times New Roman","serif"; mso-ascii-theme-font:major-bidi;mso-hansi-theme-font:major-bidi;mso-bidi-th= eme-font: major-bidi;mso-ansi-language:EN'> permeability and increase in antibacterial activity against E. coli respectively. Furthermore, based on these results chitosan–nanoscale Ag–NMMT nanocomposite can have a = good potential for packaging.

=  

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= Microplastics, an Emerging Concern: A Review of Analytical Techniques for Detecting and Quantifying Microplatics

Verla Andrew Wirnkor1, Enyoh Christian Ebere1* and Verla Evelyn Ngozi2

1. Group Research in Analytical Chemistry, Environment and Clim= ate change (GRACE&CC), Department of Chemistry, Faculty of Science, Imo State University, Owerri, Imo State Nigeria

2. Department of Environmental Technology, School of Environmental Technology Federal Univer= sity of Technology, Owerri, Imo State Nigeria.

*Email: Cenyoh@gmail.com, +2347063715081

= Abstract

Microplastics are ubiquitous tiny plastic particles (< 5 mm) nonbiodegradable and have large surface area in the environment or the body= of living things due to anthropogenic activities or fragmentation of plastic debris. Though they have been found in sea food and human body, their health implications are still speculative. Moreover, a major reason for dearth of information on this topical issue is the lack of standard operating protocol for detecting and quantifying microplastics as a result of their presence in more complex environmental matrices. In the present review some methodologi= es for analyzing microplastics reported in the period 2000 to 2018 have been documented with the aim of assessing which methods is most suitable and in = what matrix. The following methods have been studied: CHN analyzers, pyrolysis-g= as chromatography/mass spectroscopy (PyrGC/MS), optical microscopy, fourier transform infrared microspectroscopy (Micro-FTIR), raman microspectroscopy (RMS) and scanning electron microscopy with energy dispersive x-ray spectroscopy (SEM-EDS), effective for particles <500 μm. However, t= he quality of result obtained strongly relies on good sampling and sample purification= . Specifically, Micro-Raman spectroscopy is best for particles of <1 μm while degradation process of plastics is best monitored with SEM-EDS. Generally, = studies have been conducted with often a combination of two methods; one separating= and the other quantifying which can be problematic moreso in living tissue where there is no harm reported as at the time of this study. Ultimately based on this study, microplastics have become a cause for concern and advance studi= es are required to unravel the potential risk of their presence in our food and environment.

= Keywords: Anthropogenic, Fragmentation, Health implications, Hyphenated methods, Matrices, Seafood. 

= 1. Introduction

Plastics are organic polymers, synthesized from the polymerisation of monomers extracted from oil or gas. Since it first modern development in 1907 called “Bakelite= ”, it global production rose from = = 0.3 billion tons in 2010 [1] to 348 million metric tons in 2017 [= 2]. Approximately 10 % end up in the marine environment [3] and only a fraction= of about 3 % was recycled in 2016. The plastics while in the environment breaks down to form debris. Many studies have reported that majority (60-80 %) of debris in marine environment are made up of plastics [4-6], which are further broken down to tiny particles through weathering processes. The tiny particles are defined as ‘‘microplastics’’ together with primary plastic particles manufactured at microsize dimensions [5,7].<= /o:p>

 =

Microplasti= cs can simply be defined as small plastic particles in the environment. Term “micoplastics” was recently coined, although the occurrence of small plastic particles on beaches and in coastal waters was first reported in the 1970s = [8]. The U.S. National Oceanic and Atmosph= eric Administration (NOAA) classified microplastics as less than 5 mm in diameter [5]. However, different authors have given different classifications of microplastics with numerous size-ranges. Graham and Thompson [9] classified= with diameters of <10 mm, diameter of <5 mm was given by Barnes et al. [5]= and Betts [10], 2–6 mm by Derraik [3], <2 mm and <1 mm [11-13]. Their sou= rces vary including cosmetics, clothing, and industrial processes via urban wastewater treatment etc. Microplastics are classified as primary microplas= tics and secondary microlastics. The primary microplastics are produced from anthropogenic means while secondary microplastics are derived from breakdow= n of larger plastic debris into microscopic plastic fragments [14]. <= /span>

 

Microplastics can be ubiquitous and remain in = the environment at high levels for many years because of their difficulty in breaking down. In the last decade, many researchers have developed interest= and conducted studies on microplastics due to their massive buildup in the environment [12,13,15-17].

Currently, their mobility and entire cycle in = the environment is not yet known. They are more particularly in aquatic and marine ecosystems. Due to their persistence in the environment, th= ey find their way and accumulate in the bodies and tissues of many organisms. When in the host organism they could easily undergo chemical exchange due to their large surface area. This may possibly pose some health issues to the host organisms. In addition, they serve as vector to pollutan= ts whose health implications are already established; which include heavy meta= ls (HMs) and persistent organic pollutants (POPs) (i.e polyaromatic hydrocarbo= ns, PAHs, organochlorine pesticides, OCPs and polychlorinated biphenyls, PCBs).= Many research reports have shown that PCBs are capable of attaching to the surfa= ce of plastics [18-21] and become bioavailable when injected by animals [22,23= ]. For heavy metals, studies by Holmes [24] and Rochman [25] reported their adsorption to plastics surface when suspended in the marine environment. As= hton and coworkers [26], also reported adsorption of heavy metals such as iron (= Fe), manganese (Mn), aluminium (Al), lead (Pb), copper (Cu), silver (Ag), zinc (= Zn) in seawater on virgin (new) polyethylene pellets. In the sa= me study, heavy metals, such as Cu, Zn, Fe, w= ere found in higher concentration on plastic production pellets than local sediments in coastline of South West, England [26]. According to Holmes et = al. [24, 27], the extent of adsorption of metals on plastics in marine environm= ent is probably due to the weathering, adhesion to foreign material (viz organic matter) over time, surface area and availability of anionic active sites.

Many scientist worldwide have reported on the uptake of microplastics by various marine organisms such as fish, sandhoppe= rs, sea turtle, crustacean and mussel [7,11,28-30]. Due to this, their digestive system may be blocked, thereby leading to potentially serious injuries [31]. Furthermore, microplastics have been fou= nd in table salts used for cooking, potable water and human excreta [32]. However, the health implications of microplastics are still scantly studied with no evidence of impacts on human. This is an emerging area of concern. The very scarce available evidence is currently under review by World Health Organization (WHO). Their objectives are to indentify gaps in evidence and create an agenda for research, in order to provide detailed information concerning risk pose to human by microplastics [33].

Researchers argued that the scantly research on microplastics have majorly centered on lack of standard operation protocols (SOP) or methodology for sampling, detecting and quantifying them in the en= vironment [34-38]. Although, different methods have been developed and used by differ= ent researchers due to their presence in more complex environmental matrices [3= 5,36,39,40]. A review by Klein et al. [41] summarized possible procedure provided by different researchers for analyzing microplastics in environmental matrix. The review describes the entire study process from sample collection to reporting of results (presented in Figure= 1). One key aspect of some of the analytical methods is the extraction of microplastics from dissolving biomass using one or more fairly aggressive chemicals such as potassium hydroxide (KOH), hydrogen peroxide (H2O2), perchloric acid (HClO4) and nitric acid (HNO3) which = can be destructive to the plastic particles and thus not accurately identifying= and quantifying their presence in a sample. These aggressive chemicals are best suited for extracting heavy metals from samples of soil [42-44], water [45,= 46] and sediment [47].

Microplastics quantification is simply based o= n differentiating or separating these particles from other matter whether inorganic (e.g. sediment) or organic (e.g. plant material). Density based methods have been applied by many researchers in order to separate lighter compartments of the sample from sediment in a marine environment [35,36,39,48]. Using the densi= ty based method, Song et al. [49], explained that interference from other organic particles poses a major prob= lem when identifying microplastics as synthetic polymers. Other methods involve= the use of enzymatic digestion and li= pophilic dye Nile Red (9-diethylamino-5H-benzo[α]phenoxazine-5-one) quantitative differential staining for = small microplastics (1 mm to 20 μm) in a samples [40, 50-52].

Here, we review comm= on analytical techniques by which plastic types are identified, which can also= be used in microplastic detection in the environment. These techniques are commonly used in analytical and environmental studies.  They have been reported to be sensitive= and accurate for indentifying and detecting microplastics in the environment.

 

Fig. 1: Strategies provided by researchers for microplastics analysis from sampling to reporti= ng results [41].=

= 2. Sources of data

Materials such as statistical bulletins, journals articles and conference/workshop/seminar papers were used for sourcing information. Web = of Science and Google Scholar were two major scientific databases used to sear= ch for related articles and at least one of the following the keywords needed = to appear in article’s title or abstract: “Microplastics”, “Plastics”, “Marine= ”, “Spectrophotometer”, “Microscopy” and “Spectroscopy” (conducted in May, Aug= ust and December 2018). One or more of the aforementioned keywords must be pres= ent in an article for the article to be included in the present review. All searches were restricted to peer-reviewed articles written in English that = were published after 2000 to ensure review focus on recent literature on microplastics. Additionally, selected article prior to 2000 were included (= e.g [53] and [54]) due to importance in the initial set of empirical studies.

3. Experimental procedure and methods for identifying and quantifying microplastics in the environment

= 3.1. CHN analyzers

CHN Analyzer&n= bsp;is a scientific instrument which can determine the concentrations of elem= ents in a given sample using combustion technique. The analyzer is useful in the development and production of plastics. It identifies plastic materials and= quantifies nitrogen, carbon, hydrogen, sulfur and oxygen contents in plastics. No samp= le digestion or toxic chemicals is required for it use,thus making it a reliab= le system [55].

Liliana and Guido [56] characterized plasti= cs (pellets, powders and films) by the Thermo Scientific FLASH 2000 Elemental Analyzer. This instrument operates with dynamic flash combustion of the sam= ple. A graphical flow diagram of the instrument is presented in Figure 2. The fi= rst thing was to introduce samples into the combustion reactor with oxygen using tin containers. The gases produced after combustion was transported by a he= lium flow to a layer containing copper, and then passed through a GC column, whi= ch separate these gases. The gases will be finally measured by a thermal condu= ctivity detector (TCD). The measured gases revealed acrilonitrile (monomer), a main component of many types of compounds (polyacrylonitriles) such as plastics.= The configuration can be achieved using either sulphur (CHNS) or oxygen (CHNO) respectively [56].

 

 

 

 

 

 

Fig. 2. CHNS/O configuration [56]

In an environment sample, the CHN analyzer = will detects microplastics by the ability to identify materials with higher percentage of carbon, hydrogen and nitrogen content. The sizes of the sampl= es are very small (a few milligrams), but may differ depending on system. Some samples matrix being heterogenous in nature and thus larger mass is preferr= ed for their analysis using CHN analyzer.

This method was modified by Morét-Ferguson = and coworkers [57], using density separation with subsequent C:H:N analysis to identify the polymer origin of visually sorted microplastics. They concluded that the approach narrows the search for the potential polymer, thus enabli= ng identification of microplastic particles by type, which requires no rigorous chemical analysis. However, the major drawbacks of this technique are (1) t= he relatively high time effort, which impede a high sample throughput and (2) = not applicable to smaller particles [38].<= /span>

= 3.2. Pyrolysis-gas chromatography/mass spectrometry (PyrGC/MS)

Pyrolysis–gas chromatography–mass spectrometry (PyrGC/MS) is a chemical analytical technique in which the sam= ple are decomposed into smaller molecule through heating which are separated by= gas chromatography and detected using mass spectrometry [48,58]. It is classified under mass spectrometry. The analytes for PyrGC/MS includes poly= mer, biomolecules and paint. A simple schematic representation of PyrGC/MS proce= ss is presented in Figure 3.

 

 

 

 

 

 

 

 

 

 

 

 

Fig. 3. A simple schematic representation of PyrGC/MS process

The sample is placed in pyrolyzers and rapidly heated to 600–1000 °C (or > 1000 °C, depending on the application). The heati= ng techniques that can be employed include; Isothermal furnace, inductive heat= ing and resistive heating. Large molecules are decomposed into volatile fragmen= ts through the combustion [59,60]. The fragments will be separated by gas chromatography (GC), which will provide characteristic combustion products. These products will then be identified by mass spectroscopy (MS) and struct= ural information elucidated by comparing with reference of known pyrograms sampl= es [37,61].This method has been used by researchers to identify unknown plastic samples of different polymer type= s and organic plastic additives (OPAs) [61,62]. A typical Pyrolysis–GC/MS chromatogram of a plastic sample is presented in Figure 4.

Fig. 4. A typical Pyrolysis–GC/MS chromatogram of a plastic sam= ple pyrolyzed at 600 °C, identified as flexible poly vinyl chloride (PVC) [62].=

The major drawback is the manual placing of sample particle into the pyrolyzer. This limit the size of particle that can be analyzed because only particles of a certain minimum size can be manipulated manually [38]. = For this reason, samples are analyzed in sequence (one particle per run) and th= us not suitable for routine monitoring programs where samples are analyzed in continuous manner. However, as at 2015 promising pyrolysis-GC/MS approaches= for the qualitative/quantitative analysis of microplastics on whole environment= al sample filters was being developed. This will address the drawbacks of analyzing a particle per run.

= 3.3. Optical Microscopy

Optical microscopy is the use of optical microscope (= light microscope) to magnify images of small subjects using visible light and a system of lenses. The image from an optical microscope can be captured by normal, photosensitive cameras to generate a micrograph. This method is based on visual identification under a microscope. Visual sorting works well in separating large microplastics as = well as separating potential microplastics from other organic or inorganic mater= ial in the sample residues [34,57] whereas dissection microscope is used in sor= ting smaller microplastic particles [63].

The use of this method has been reported in literature [40,52,6= 4]. Wagner et al. [40] used two reflected-light stereozoom microscopes (Leica S8APO and S6D) with digital C= CD cameras (Leica DFC 420 and 320) for initial documentation, gut dissection, = and pre-screening of any observed particles that visually resembled microplasti= cs in fish samples. The optical microscopy was conducted at 6.3x – 80x with a minimum resolution of approximately 10 µm [52]. Wang et al. [67] also used = optical microscope for analyses of microplastics in ocean trawl and fish guts.

This method can be aided by staining using dyes such as Nile Re= d [52,64]. Samples will be treated first = with the dye solution (often 1 mL) for 48 hours under a fume cupboard until all moisture evaporated to form a dyed membrane. Subsequently, the dyed membrane filters were photographed using a camera under Ultra-violet (UV) light. Exa= mple of a useful camera is the Pentax K-30 with resolution 2420x2343 used by Matthias and coworkers [64] in their study.

The dye solution can be prepared using different extraction solvent such as acetone, chloroform and n-hexane. Chloroform with recovery rates of 83.3 % was reported to be most suitable solvent for the group of high-density and low-density polyethylene (HDPE, L= DPE), polypropylene (PP) and PVC [64,65]. However, the findings of Shim et al. [6= 6] implicated n-hexane to be most effective for PE and PP, whereas PET and PA = were not detectable. The variation in solvent efficiency in detecting the differ= ent microplastic type could be due to different surface and density properties = of the microplastic materials. Also, a typical visually identified stained microplastics under an optical microscope is sh= own in Figure 5.

 

 

 

 

 

 

 

 

 

 

 

Fig. 5. A typical visually identified stained microplastics und= er an optical microscope [64].

It is asserted by Wang et. al. [67] that optical microscopy enables morphological classification of particles or fibers types, quantification of particle size ranges and fiber lengths presents in a sample. However, it is suggested by Hidalgo-Ruz et al. [34] that for particles < 500 mm ordinary visual sorting with the naked = eye or hand lens should not be applied. This may cause misidentification of particles with high probability. To sort visually, there are factors that should be considered generally, which include source, type, shape, degradat= ion stage, and color of the particles [34,57], which is extremely time-consumin= g. Martin and Gunner [38] explained that, “even an experienced person cannot discriminate all potential microplastic particles unambiguously from sand grains, chitin fragments, diatom frustule fragments, etc.” Thus the error r= ate of this method reported ranges from 20 % [68] to 70 % [34], which increases= as particle size decreases. Therefore, a size limit of 1 mm was recommended for visual sorting [34,57].

 

 

= 3.4. Fourier Transform InfraRed Microspectroscopy (Micro-FTIR)=

Fourier transform infrared (FTIR) microspectroscopy is a technique which produces molecular microscopic images from samples. The instrument allows observation of spectra measured from regions as small as 5 microns across because it uses an infrared microscope. The spectra correspond to specific chemical bonds between atoms which makes= it possible to identify the exact composition of the particle [69]. In Micro-FTIR, two feasible measuring mode= s are used viz reflectance and transmittance [70]. The former (i.e reflectance mo= de) handles difficult spectra obtained from measurements of irregularly-shaped microplastics that may not be interpretable due to refractive error [71].The later mode (i.e transmittance mode) handles the total absorption patterns a= nd uses IR transparent filters (e.g. aluminium oxide). Furthermore, it can onl= y be limited by a certain thickness of the microplastics sample [38]. In additio= n, the use of micro-ATR (Attenuated Total Reflectance) in combination with microscopy enable= s the direct measurement on the sample filter without the need for manual handlin= g of particles, when IR spectra are collected at the surface of a particle [40,7= 0-72].

The micro-FTIR meth= od has been used on biological samples such as articular cartilage [73] and to track microplastics in the environment with Attenuated Total Reflectance (A= TR) [40,73,72] and Focal Plane Array= -Based Reflectance [38,70,74].Wagner [40] and Bradley et al. [72] both used the Th= ermo Scientific Nicolet Continuum FTIR Microscope with 10x optical objective, 15= x IR objective, and a Nexus 470 spectrometer with attenuated total reflectance (= ATR) (diamond and Ge-ATR). In the study, majority of the particles were analyzed either on glass slides or directly on filter. All acquired FTIR spectra were compared to quantitative matches from commercial FTIR libraries. . In addit= ion, in Figure 6, FTIR spectra of a microplastic fiber on filter from a river wa= ter sample are shown.

 

 

Fig. 6: FTIR spectra of a microplastic fibe= r on filter from a river water sample. The top spectrum is from Nicolet iN5 microscope fitted with Ge-ATR; the lower spectrum is a library search resul= t [72].

 

Kerstin and Federik [69] screened microplas= tic particles in and down-stream a wastewater treatment plant with a Bruker FTIR Tensor in Attenuated Total Reflectance (ATR) mode equipped with a diamond crystal. Different plastic fragments (≥300 μm) were reportedly f= ound in wastewater treatment plant. Alexander et al. [74] used the FPA-Based Reflectance Micro-FT-IR Imagi= ng to identify and quantify microplastics in wastewater. The authors concluded th= at the tool is good for identifying and quantifying microplastics in wastewater and also to determine the abundance of microplastics in other organic-rich = environments, such as peat soils [74]. This FPA based micro-FTIR spectroscopy is a very promising technique for verifying polymer origin of microplastic particles. Martin and Gunner [38] recommended for use in monitoring programs on microp= lastics.

 

Micro-FTIR enables identification of repetitive fingerprint-like molecular composition of plastic polymers for a clear assignment of a sample to a certain polymer origin. It offers the possibility of accurate identification of plastic polymer particles accordi= ng to their characteristic IR spectra [15-17,48,71,75], simultaneously record several thousand spectra within an area with a single measurement and thus the generation of chemical images (Figure 7) [38]. In figure 7,= the analysis was done by FPA based micro-FTIR spectroscopy. The intensity of the chosen spectral bands is reflected by the color scale according to peak are= a (bluish color scale intensity of the peak 1,931–1,832 cm−1; reddish color scale intensity of the peak 2981–2780 cm−1). This enabled clear identification of a quartz particles in light blue (a) at band of 1931–1832 cm−1 and a polyethylene particle in <= i>orange (b) at band of 2981–2780 cm&#= 8722;1 in a sample.

 

 

 

 

 

 

 

 

 

 

 

Fig. 7. Chemical imaging of an integr= ation of typical spectral bands [38].

The simplicity of this method is in b= oth sampling and analysis. Samples are simply filtered and analyzed directly on= the dried filter without further sample preparation.  This enables the rapid assessment of mi= croplastic encroachment and can assist in the development of remediation techniques [7= 2]. However, it is extremely time-consuming when targeting the whole sample fil= ter surface at a high spatial resolution because it uses only a single detector element, which happens to be limitation of this technique [15,71].

= 3.5. Raman micro-spectroscopy (RMS)

Raman spectroscopy is a “surface technique”, thus large, visual= ly sorted microplastic particles can be analyzed and the technique can also be coupled with microscopy. Raman micro-spectroscopy is straightforward and us= es a scattering technique. The simple principle of this technique is measuring t= he wavelength and intensity of inelastically scattered light from molecules ca= used by a monochromatic light. The Raman scattered light occurs at wavelengths t= hat are shifted from incident light by the energies of molecular vibrations giv= ing out spectra (Figure 8). A very small volume (< 1 µm in diameter) of= the sample can generate the Raman spectra which allow the identification of spe= cies present in that volume [76].<= /span>

 

 

 

 

 

 

 

 

 

 

 

Fig. 8. Schematic for process involved in collecting Raman spectra. A Raman spectrum for tetra(4-aminophe= nyl) porphyrin (TAPP) powder is shown [77].

The instrument consists of a standard optical microscope, an excitation laser, a notch filter, a monochromator, and a sensitive detector (such as a charge-coupled device (CCD), or photomultiplier tube (PMT)). The notch filter is used to block elastically scattered l= ight which would otherwise overwhelm the weak signal from the Raman or inelastic= ally scattered photons (~ 1/106 scattered photons). The Raman scatter= ed light may be dispersed according to wavelength and detected by a CCD as sho= wn in Figure 8. Angel et al.[53] sta= ted that when a UV laser source is used for Raman microspectroscopy (RMS), then Ultraviolet microscopes and UV aided optics must be used. Earlier stud= ies by Taylor et al.[78] and Adrian et al.[79] have expressed the suitability of RMS for the microscopic examination of minerals, materials such as polymers= and ceramics, cells, proteins and forensic trace evidence.

RMS have been used by a lot of researchers for detecting microplastics with high reliability in marine environment [7,16,28,36,80] a= nd for testing simulated microplastics polluted water [81]. Wagner et al. [40] performed the analyses on ocean trawl and fish using both Renishaw inVia and Bruker Senterra dispersive Raman microscopes with 785 nm and 532 nm lasers.= In the study, analytical laser optimization was achieved using several differe= nt objectives (5x, 20x, 50x and 100x). The author marched the Raman spectra obtained with spectral matching performed using GRAMS software, which was equipped with commercially available Raman spectral libraries. Rocchia et a= l. [81] simulated microplastics polluted water. A few milligrams of three different reference materials (irregularly shaped polyethylene particles si= eved at 74 microns, polystyrene-divinylbenzene PS-DVB microspheres sieved betwee= n 37 -74 microns and polyethylene-titanium dioxide PE-TiO2 microspheres with a s= ize range of 27-45 micron) were used to simulate microplastic debris with diffe= rent particle sizes in 0.5 L of water. The Raman spectra data were collected usi= ng the DXR2xi Raman imaging microscope and the accompanying ThermoScientific OMNICxi Raman imaging software. The obtained spectra are presented in Figur= e 9. The author concluded that Raman microscopy allows the analysis of particles below 1-micron size and the correct identification of plastic materials as = well as inorganic materials such as titanium dioxide or other additives.

 

 

 

 

 

Fig. 9. Raman spectra of PE - polyethylene; PE-TiO2 polyethylene-titanium dioxide and PS-DVB – polystyrene-divinylbenzene microplastic standards [81].

The Raman techniques have one major advantage over FTIR, which = is its ability to identify particles up to 500 nm in size [80]. By comparison with reference spectra or standard library spectra (e.g from GRAMS software), specific plastic polymers can be identified within minutes. Accordingly, RMS allows broad range of detection and quantification of very small plastic particles of sizes < 1 µm [7,35] and when combined with Raman spectral imaging, spatial chemical images can be produced based on the Raman spectra= of a sample. This was recently demonstrated by [81]. Cole et al. [7] demonstra= ted that polymer particles within biological tissues with subcellular precision= can be located with Raman technique when coupled with confocal laser-scanning microscopy. One limitation of this technique is drawn from its inability to measure laser excited fluorescent samples (e.g. residues of biological orig= in from samples) as they block the generation of interpretable Raman spectra [38].Generally, lower laser wave lengths transmit high energy result and si= gnal intensity but also in a high fluorescence. Therefore, higher laser waveleng= ths greater than 1000 nm will minimize fluorescence but the lower energy of the laser results in a lower signal of the polymer sample. More study is requir= ed to find the optimum wave length of the laser light which will address this problem of fluorescence and low intensity for assessments of microplastics = in environmental samples. In line, [38] recommended that fluorescence should be prevented through a sample pre-purification step prior to measurements for = a clear identification of the polymer type of microplastic particles

Raman spectroscopy and FTIR are complementary techniques. Molec= ular vibrations, which are Raman inactive are IR active and vice versa and can t= hus provide complementary information on microplastic samples [38].<= /span>

= 3.6. Scanning electron microscopy with energy-dispersive x-ray spectroscopy (SEM/EDS)

Scanning Electron Microscopy (SEM) magnifies a specific sample region using a high energy focused beam of electrons. The analyzed region evaluated with SEM can also be assayed for specific elements using Energy Dispersion Spectroscopy (EDS). SEM generates micrographs while EDS provides concentration of chemical composition of the sample. Thus the combined technique is referred to as SEM/EDS or SEM/EDX Analysis. The SEM/EDS method enables the detection of microplastics and its degradation process in a sam= ple due to its micro-scale and nano-scale features with magnification up to 500,000x [15,36]. The method determines particle sizes and elemental compos= ition of microplastics in your test sample. It can only be performed only on solid samples [82]. 

A key factor in SEM is the interaction volume, which depends on= the accelerating voltage of the electron beam and other factors including speci= men nature, composition and sample preparation. The higher the accelerating vol= tage applied, the larger the interaction volume. This is turn determines the emission depth of the different signals used. The emission of secondary electrons (topography) and backscattered electrons (atomic number) are used= to generate micrographs in SEM. Thereby providing information on topography, morphology, composition and crystallographic nature of microplastics in an environmental sample [83]. This method has been used to detect microplastics particles in sample [15,36]. Vianello [15] analysed sediments collected from Lagoon of Venice in Italy using SEM to characterize the surface morphology = of the microplastic particles. Result showed irregular shapes and similar surf= ace textures for several microplastics in contrast with comparable amorphous and regular surfaces of other plastic microfibers. Furthermore, the method reve= aled possible occurrence of degradation processes by showing images of weakened surfaces caused by adhering particles [15]. Imhof et al. [36] identified degraded microplastics in sediments of subalpine lake beach using SEM imagi= ng. Many of the PP microplastics showed cracks, pits, grooves, disintegration, = and adherent and attached diatoms. A typical SEM image of microplastic particle= s is presented in Figure 10.

 

 

 

 

 

Fig. 10. Scanning electron microscopy images showing the surfac= e of several thermoplastics: polyethylene (PE), polypropylene (PP), polystyrene = (PS) and polyvinyl chloride (PVC) [83].

Whilst SEM is effective for identification, EDS helps in quantification. In addition, SEM/EDS analyses have been conducted on ocean trawl and fish gut for microplastics by [40] and [67]. Potential microplastics using particle morphology and elemental chemistry profiles have been tested by Wagner et al [40]. The analytical instrument used has been FEI XL30 Environmental SEM an= d a Thermo Fisher Scientific Noran System 7 EDS System. Moreover, samples has b= een imaged at 50x – 10,000x using an atomic number sensitive, backscattered electron (= BSE) detector with a resolution of approximately 0.1 µm. [67] reported that SEM/= EDS is effective in identifying chlorinated plastics such as polyvinyl chloride (PVC) due to their unique elemental signatures. Typical SEM-EDS results for microplastics in an environmental sample are shown in Figure 11.=

Fig. 11. Typical SEM-EDS results for microplastics in an environmental sample [67].

The technique (SEM/EDS) has been used in identification of plas= tic additives of inorganic origin contained in= microplastic particles, characterization and toxic chemicals extracted from microplastic= s in samples from the North Pacific Gyre by Mendoza and Jones [84]. SEM-EDS have become an indispensable tool for analysis microplastic particles present in a sample. This method enables scientists to monitor how plastics degrade to form microplastic particles, emergent pollutants expressively threatening biota life [61,83].=

The limitation of quantitative SEM-EDS is that, this technique should only be carried out in flat polished samples or very thin films with irrelevant topography. Prior to spectra acquisition for quantification purp= ose, it is imperative that several well-assigned spectra with sufficient X-ray counts have been previously collected (serving as a reference). Then, the spectra need to be processed with matrix corrections with oxygen calculated= by stoichiometry and the appropriate ZAF (the atomic number-Z, absorption-A and fluorescence-F correction) procedure. Again, EDS software applies the ZAF correction and carries out subsequent integration of the peaks to give the final semiquantification of the elements present in the specimen. Neverthel= ess, the user should be as critical as possible when accepting each step of the quantification process provided by the software [85].

= 4. Conclusions

This study reviewed spectroscopic techniques for quantifying an= d identification of microplastics in an environmental sample. Generally, for microplastics p= articles <500 μm, spectroscopic techniques is important for their identifica= tion while the quality of result obtained strongly rely on good sampling and effective sample purification. During purification aggressive agents (e.g. strong acidic or alkaline solutions) should be avoided to conserve the whole plastic spectrum and because aggressive solutions negatively affect certain plastic polymer. Also, ordinary visual inspection of samples alone is insufficient but when in tandem with optical microscope it becomes effective, especially, in the case of particles <5= 00 μm. In addition, CHN analyzer, pyrolysis-GC/MS and SEM-EDS have been used effectively for sample identification and quantification. The former which is based on combustion techniques works better for larger particle while SEM-EDS techniques is a better update to optical microscopy  by providing information on the degradation process of plastic particles. A spectroscopic verification of microplastic particles by micro-FTIR or micro-Raman spectroscopy is essential and has also been used successfully f= or analyzing the particles of microplastics. Micro-Raman spectroscopy is very effective for microplastic particles of <1 μm. Furthermore, spectroscopic techniques create an added value = as they also provide information on the polymer composition. However, some of = the discussed methods have its drawbacks in their use which include cost effectiveness, time consuming and difficulty to use (especially if you are inexperienced) like pyrolysis-GC/MS where samples have to be placed manuall= y.

Finally, microplastics have been studied with non destructive methods often a combination of two methods: one separating and the other quantifying. It could be observed that since microplastics undergo very few reactions, their identification and quantification can be problematic more = so in living tissue where there is no harm reported as at the time of this stu= dy. However, microplastics have become a cause for concern and advance studies = are required to unravel the potential risk of their presence in our food and environment.

= Conflicts of interest

The authors declare no conflicts of interest =

= Acknowledgement

This research did not receive any specific funding

Nomenclatures (Abbreviations)

NOAA: National Oceanic and Atmospheric Administration;

POPs: Persistent organic pollutants;

PAHs: Polyaromatic hydrocarbons;

OCPs: Organochlorine pesticides;

PCBs: polychlorinated biphenyls;

WHO: World Health Organization;

SOP: standard operation protocols;

FTIR: Fourier Transform infrared spectroscopy; <= o:p>

SEM-EDS: scanning electron microscopy energy-dispersive X-ray spectroscopy (SEM-EDS); PyrGC/MS: pyrolysis- chromatography/mass spectrometry;

TD-GC/MS: thermal desorption-gas chromatography/= mass spectrometry;

GC: gas chromatography;

MS: mass spectroscopy;

TCD: thermal conductivity detector;

OPAs: organic plastic additives;

HDPE, LDPE: high-density and low-density polyethylene;

ATR: Attenu= ated Total Reflectance (ATR);

FPA: Focal Plane Array-Based Reflectance;

RMS: Raman micro-spectroscopy;

CCD: charge-coupled device;

PMT: photomultiplier tube;

UV: Ultraviolet;

PE: polyethylene;

PE-TiO= 2: polyethylen-titanium dioxide;

PS-DVB: pol= ystyrene-divinylbenzene;

SEM: Scanni= ng Electron Microscopy;

EDS: Energy Dispersion Spectroscopy;

PP: polypropylene;

PS: polystyrene;

PVC: polyvi= nyl chloride;

ZAF: atomic number-Z, absorption-A and fluorescence-F.=

 

= References


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Investigation of graphene/CNT hybrid structural effect on 

absorption of Mn2+ by activated Carbon =

 = ;

à= Corresponding Author.

= E-mail addresses: ghozatlooa@ripi.ir

 = ;

 = ;

Ahmad Ghozatloo1,* and Mojtaba Shariaty-Niassar2

1 Research Institute of Petro= leum Industry (RIPI), West Blvd. Azadi Sport Complex, Tehran, Iran

2 Transp= ort phenomena and Nanotechnology Laboratory (TPNT), Department of Chemical Engineering, School of Eng., University of Tehran, Tehran, Iran<= /span>

&n= bsp;

&n= bsp;

Abstract

In this paper, an effort is made to improve the adsorption amount by adding graphene/CNT hybrid in the structure of Activated Carbon (AC) for removing manganese ions from aqueous solutions. The bonding G/CNT hybrid wi= th activated carbon creates a structure which is an excellent absorbent for removing some heavy metal ions. Therefore, a comparison between the perform= ance increasing ion adsorption and AC results as the blank adsorbent was made. M= oreover, the influence of time, pH solution, initial concentration of Mn2+, and temperature investigated as experimental conditions. Finally, the maxim= um adsorption was 89.38% and 96.18% for  AC and AC/G/CNT composite respectively at 30 min, initial concentration of 30 mg/L, pH=3D4.5 in 15 °C for both adsorbents. Finally, the results showed th= at under the same conditions, the presence of G/CNT hybrid in the structure of= AC increased the amount of adsorption by 7.5%=

Keywords: Adsorption, Manganese, Activated Carbon, graphene, CNT, hybrid=

 =

1.    Introduction

Heavy metal ions and organics are two major classes of water pollutants. Heavy metal (a range of toxic metals) ions as poisonous compoun= ds are one of the main problems that pollute the waters and plants. Dischargin= g of pollutant water in plants will be absorbed in soil and will not degrade and accumulate in living organisms, causing various poisoning problems in anima= ls and indirection for humans. Therefore, elimination of these heavy metal ions from waste water is necessary and interest [1]. Moreover, the major techniq= ues have been used to reduce or decrease the heavy metal ions from wastewaters = such as flotation, solvent extraction, silica, adsorption processes, ion exchang= e, reverse osmosis, lime chemical precipitation and coagulation [2]. Among the= se, adsorption is an industrial and good method for removing heavy metals from aqueous solutions [3]. Copper (Cu), mercury, cadmium, manganese (Mn2+<= /sup>), nickel, chromium and lead are known to be greatly toxic effect on waters [4= ]. The ion of Mn2+ can be found in the effluents of petrochemical plants is one of dangers source of pollution. In addition, pore structure of some substances which have active surface such as chitosan, anthracite, lig= nite, and specially activated carbon (AC) are common and suitable for adoption Mn= 2+ and widely used for high adsorption capacity [5]. The objective of this pap= er was to improve performance of AC by G/CNT structures. Because the multi-lay= er configuration of graphene/CNT (G/CNT) hybrid structure is to have good adsorption performance, so recently, graphene hybrid structure has been app= lied as the adsorbent for absorption= of some pollutants from waste water, because of its excellent capacitance. To improve interface and chemistry surface behavior, wide researches have been conducted on the structure of G/CNT hybrid structures [6]. In this paper, t= he effects of temperature, time, pH, and initial Mn2+ concentration were investigated to remove the cations  of Mn2+ from water by AC/G/CNT composite as adsorbent and comparison with AC.

 

2.    Material and Methods

 

The chemicals used for this paper were all Merck grade and used without further purification. Analytical grade of AC Powder was obtained fr= om activat­ed charcoal with the purity of > 99.9%. The solutions were prepa= red in deionized water. The Synthetic aqueous solutions of Mn2+ were prepared by dissolving enough amount of Mn(NO3)2 in p= ure water. In order to prepare the aqueous solutions with various concentration= s, first a stock solution was prepared with a concentration of 1000 mg/L of Mn= 2+. For this purpose, 0.65 g of Mn(NO3)2 was introduced in 1000 mL volumetric flask, added adequate water, and stirrer the solution.  Then the purposed solutions were prepar= ed with lower concentrations by dilution.

2.1.= Preparation of activated carbon

First, 200 g of powdered glucose are placed in a tubular quartz reactor into the furnace under nitrogen atmosphere for 30 min. It is then gently warmed up to a temperature of 350 °C and remains for 2 hr. The gluco= se is carbonized under these conditions and is colored as a black powder. The powder placed in a furnace and heated at 400 °C for 1 hr under neutral atmosphere. Next the powder was extracted from the reactor and poured into 1 molar HCl at 90 °C for 30 min. The remaining mixture is filtered and washed with distilled water several times. Afterwards, the filter cake was dried in oven 65 °C for 11 hr. Dried powder is a activated carbon that is susceptibl= e to participation in the carbon nanostructures.

2.2.=         Synt= hesis of AC/G/CNT composite

To synthesis of Graphene/CNT hybrid (G/CNT hybrid) a two-step method of chemical vapor deposition (CVD) was used. Its mechanism includes copper sheets by FeMo nanoparticles (as a catalyst) in the space of interla= yer of copper sheets to formation of CNT/Graphene nanostructure as illustrated = in Fig. 1.

= Figure 1:  Schematic illustration synthesis of G/CNT hybrid= .

 =

According to Fig. 1 in the section (a), metal NPs nucleated on = the surface of copper sheets as activated catalyst for growth of CNT. Section (= b) is as first step of G/CNT hybrid synthesis which CNT fully grown on copper sheets by FeMo in 600 °C as low temperature process CVD catalyst and section (c) is as second step of G/CNT hybrid synthesis which uniform Graphene nanosheets deposited on copper for G/CNT hybrid formation as higher tempera= ture process. Finally, in section (d), acid washing was done to remove FeMo, cop= per sheets and other pollutants from G/CNT hybrid structure to obtain the high carbon purity [7]. 0.3 g of G/CNT powder prepared in 200 ml of distilled wa= ter and exposed to ultrasounds at 100 W for 2 hr. Then the amount of 20 g of AC powder is slowly added to the ultrasonic mixture for 3 hr. The mixture is t= hen placed in the 50 °C for a day and then the water evaporates. The remaining solid layer was entering in tube quartz, under nitrogen atmosphere and slow= ly heated to 350 °C and remains for 2 hr. The residual product in reactor us AC/G/CNT composite. TEM image of the AC/G/CNT composite structure was shown= in Fig. (2).

= Figure 2:  TEM image of AC/G/CNT composite (a) AC/ CNT (b) G/CNT (c) AC/G. 

2.3.=         Inde= pendent variables & experiment design

For economic removal of Mn2+ from the wastewater, it= is necessary to find the optimum conditions of adsorption. Moreover, adsorptio= n experimental parameters such as Mn2+ ions concentration (30-130 mg/L), temperature (15-35°C), time (1= 5-45 min), and pH (3.5-5.5) were studied in a batch mode. All experiments were conducted in 500 mL Erlenmeyer flasks. The levels of variables are shown in Table 1.

Table 1: The levels of Independent Variables process.=

Independe= nt Variables

-1 level

0 level

+1 level

Mn+2= conc. (mg/L)

80

130<= /o:p>

Temperatu= re (o

25

35

Time (min= )

30

45

pH

4.5

5.5

 

According to Table 1, for design of experiments because of vari= ous variables (each at 3 varied levels), Taguchi method was used. The software = of Design Expert 8.3 was used to decrease the number of experiments to 9 based= on Taguchi, and the results were shown in Table 2 include of detail of conditi= ons.

Table 2: Condition of designed experiments by Taguchi method.

NO

Independe= nt Variables

AC/G/CNT<= /span>

AC=

Mn+2

(mg/L)<= span lang=3DFA dir=3DRTL>

Temp.

(oC)

Time

(min)

pH

 

C0 (mg/l)

Ce (mg/l)

Reduction (%)

Reduction

 (%)

1

0

-1

-1

0

80

4.26

94.68

88.02

2

0

0

+1

80

5.29=

93.38

86.45

3

0

+1

+1

-1

80

7.07

91.16

84.81

4

-1

-1

+1

+1

30

1.15

89.38

5

-1

0

-1

-1

30

2.05

93.17

86.64

6

-1

+1

0

0

30

2.17

7

+1

-1

0

-1

130

13.20

89.85

84.49

8

0

+1

0

130<= /o:p>

13.85

89.35

83.15

9

+1

+1

-1

+1

130

17.90

86.23

80.31

2.4.=         Batch Adsorption process

The surfaces of adsorbents are cleaned from pollutants, fats, a= nd activates by alkali washing [8]. For this purpose, treatment of AC and AC/G= /CNT hybrid as adsorbents were done before using by alkali washing. Therefore, adsorbents separately were poured into 5 wt.% of HCl, stirred for 25 min, a= nd washed with hot distilled water. Then the adsorbents washed with 1 wt.% of = NaOH solution to eliminate the residual HCl [9]. The samples were filtered and washed with pure water until the pH of the filtrating solution was neutral. Next adsorbents were dried in oven (OVEN, XU 112, France) at 90 = °C for 6 hr. Ground and sifted to obtain fine powder. Finally, the adsorbents = kept in desiccators for subsequent uses.

The required amount of adsorbents was introduced in a stirred t= ank reactor containing 250 mL of the prepared solution of Mn2+ ions.= The flasks were mechanically agitating for the desired time, wished temperature= in fixed 650 rpm. Solution of hydrochloric acid/sodium hydroxide 0.1 M was also prepared for pH adjustments. According to Table 2, after each condition, the adsorbent was separated from the solution and filtered (0.45µm cellulose acetate paper). All experiments were performed in duplicate. After filtrati= on, Mn2+ ions remaining in the solution were determined with a Perkin-Elmer 3100 ato= mic absorption spectrophotometer. The amount of adsorbed Mn2+ ions w= as calculated using the qe =3D (C0 – Ce) × v/m equation. where qe is the quantity of adsorbed Mn2+ ions = at equilibrium (mg/g), C0 and Ce respectively are the initial and equilibrium concentrations of Mn2+ ions (mg/L), V is= the volume of metal solution (L), and m is the weight of adsorbent used (g). Mo= reover, the removal percentage of Mn2+ ions was calculated using the R(%= ) =3D (C0 – Ce)/C0 × 100 equations.

3.    Results and Discussion

3.1.=             Effe= ct of pH

According to surface chemistry, the amount of Adsorption depend= s on the surface behavior of adsorbent, such as porosity and situation and distribution of active sites for bonding with metal ions. These indexes generally depend on the pH of the solution [10]. At this study the pH solut= ion was varied at 3.5, 4.5 and 5.5. During adsorption process, pH of solution adjustment at fix purposed value and measure with a pH meter using a combination glass electrode. Fig. 3 indicates the effect of pH solution on = the removal of Mn2+ ions onto AC and AC/G/CNT composite from aqueous solutions at 30 min.

Figure 3:  <= /span>Effect of PH on adsor= ption.

The Mn2+ removal was 86.45% and 93.38% at pH 3.5 by = AC and AC/G/CNT respectively, it was 86.26% and 92.76% for adsorbent at pH whi= ch is equal to 4.5 and decreased 84.49% and 89.85% for pH=3D5.5. It is seen th= at removal of Mn2+ was strongly dependent on pH conditions at AC/G/= CNT than AC as an adsorbent. In addition, the percentage removal of Mn2+ first sharply increased by increasing of the pH until 4.5 and half flat in higher pH of solution more than 4.5. Good adsorption at middle range of pH (4.5) indicates that low pH leads to an increase in H+ ions on t= he Adsorbents surface, resulting in significantly strong electrostatic attract= ion between positively charged surface of Adsorbents and Mn2+ ions. = At higher pH values, from 4.5, the precipitation of Mn2+ ions is occurred and both ion exchange and aqueous metal hydroxide formation are th= en occured. So the best value of solution pH is equal to 4.5.

3.2.=             Effe= ct of Time

Contact time is a significant factor affecting removal of initi= al Mn2+ ions in the solution. Effect of time on the adsorption was shown in Table 2. The Results reveal that increasing contact time caused increasing the adsorption of Mn2+ ions or different initial concentrations. So,= if the time increases from 15 to 30 min, the amount of absorption increases wi= th more slopes, while with increasing time from 30 to 45 min, the absorption r= ate increases with less intensity. The Mn2+ removal is higher at the first 30 min. This is due to larger surface area of the Adsorbents at the beginning for the adsorption of Manganese. It has been matched with other results [11]. For example, at fix Mn2+ concentration 80 mg/l, wi= th the increasing time from 15 to 30 min, the absorption rate was 3.6% while w= ith the increasing time from 30 to 45 min, this value was changed by only 2%. Therefore, based on economic considerations and the rate of absorption chan= ges, the best time for the absorption process is 30 min.

3.3.=             Effe= ct of temperature  and Mn2+ Concentration

Thermodynamically behavior of large amount adsorption process is exothermic and so temperature has a negative effect on removing metal ions = and other pollutants [12]. According to this, the mechanism of Mn2+ = ions adsorption by AC and AC\G\CNT was a function of temperature and has been considered this research. Fig. 4 shows the effect of temperature on Mn= 2+ removing for both adsorbents of AC and AC\G\CNT.

= Figure 4:  temperature effect on Mn2+ removing for both adsorbents.=

The results of Fig. 4 were shown at initial concentration of 30= mg Mn2+ removing decreased from 89.3% to 84.1% by AC and 96.18% to 91.16% by AC\G\C= NT with increasing of temperature from 15 to 35 °C. This cha= nge for high concentration of Mn2+ is more evident at higher temperatures. But the best initial concentration of Mn2+ is 80 m= g/L. At higher concentrations of this, between the adsorption of metal ions and = the surface of adsorbent, a competition phenomenon was occurred based on steric hindrance and as a result, the amount of absorption decreases. The simultan= eous effect of three variables include initial Mn2+ concentration in = the range of 30, 80, and 130 mg/L for temperatures of 15, 25, and 35 = °= C and contact time of 15, 30, and 45 min were done at  fixed pH of 4.5, and the results are shown in Fig 5.

= Figure 5:  simultaneous effect of three variables on = Mn2+ removing.

Based on Fig. 5, it is observed that the effect of Temperature = on amount of absorption is more than time because by increasing temperature, t= his decreases with a constant trend. However, when time increases, the amount of adsorption decreases, and then it is flat that due to the saturation of the adsorbent surface. It is also observed that the best absorption conditions occur at lower temperatures for medium concentrations of Mn2+ at= 30 min. At lower Manganese concentration, the percentage removal of Mn2+<= /sup> ions is high and by increasing temperature the slop of adsorption decreases, this means is the ratio of Mn2+ ions removing more decrease in h= igh temperature. Therefore, the technique of diluting wastewater and cooling du= ring the removing process can be used to absorb more metal Mn2+ ions.=

4.&n= bsp;       Conc= lusions

Generally, at fix conditions, the presence of G/CNT hybrid in t= he structure of AC 7.5% increases the amount of adsorption. Moreover, the most important reason being to improve surface properties and create more porosi= ty in the AC structure. In addition, the inherent property of CNT in absorptio= n of Mn2+ ions based on ionic bonding under a wide range of graphene sheets has enhanced the absorption performance of AC. The best absorption conditions occurred at a 15°C and a concentration of  30 mg Mn2+ at pH of about 4.5. Increasing pH of the solution caused to the partial hydrolysis of Mn2+= , bringing the arrangement of complexes. The result of this present shown adsorption of Mn2+ was exothermic mechanism and the rate of remo= ving was decrease by increasing temperature. This difference is a result of the enhanced escaping tendency of metal ions moving and species in higher temperatures. In addition, a solubility increase in Mn2+ ions in water at higher temperatures caused decreasing sorption on surface of adsor= bents. Ultimately, because AC is a basic, available and inexpensive sorbent, the results of this study will be useful for the removal of Mn2+ from industrial effluents.

 

Refrences

[1] H. Bessbousse, T. Rhlalou, J.F. Verche = re, L. Lebrun, Removal of heavy metal ions from aqueous solutions by filtration with a novel complexing membrane containing poly(ethyleneimine) in a poly(v= inyl alcohol) matrix, J. Membr. Sci., 307 (2008)  249-259.

[2] C. Namasivaysm, K. Kadirvelu, Uptake of mercury (II) from wastewater by activated carbon from an unwanted agricultu= ral solid waste by-product: coirpith. Carbon, 37 (1999) 79-84.

[3] C. Brasquet, P. Le Cloirec, Effects of activated carbon cloths surface on organics adsorption in aqueous solutions-utilization of statistical methods for mechanisms approaches. Langmuir, 15 (1999) 5906-12.

[4] I. Mobasherpour, E. Salahi, M. Pazouki, Removal of divalent cadmium cations by means of synthetic nano crystallite hydroxyapatite. Desalination, 266 (2011) 142-148.

[5] P.A. Brown, S.A. Gill, S.J. Allen, Metal removal from wastewater using peat. Water Res., 34 (2000) 3907-16.

[6] V. Varshney, S.S. Patnaik, A.K. Roy, Modeling of thermal transport in pillared-graphene architectures. ACS nano.= , 4 (2010) 1153-1161.

[7] K. Xia, H. Zhan, G. Yuantong, Graphene = and Carbon Nanotube Hybrid Structure: A Review, Procedia IUTAM, 21 (2017) 94-10= 1.

[8] W. Feng-Chin, T. Ru-Ling, J. Ruey-Shin, Preparation of highly microporous carbons from fir wood by KOH activation f= or adsorption of dyes and phenols from water, Sep. Purif. Technol., 47 (2005) 10–19.

[9] Z. Hu, M.P. Srinivasan, Preparation of high-surface-area activated carbons from coconut shell, Micropor. Mesopor. Mater., 27 (1999) 11-18.

[10] K.K. Wong, C.K. Lee, K. Low, M.J. Haro= n, Removal of Cu and Pb by tartaric acid modified rice husk from aqueous solutions. Chemospher., 50 (2003) 23-28.

[11] M. Ajmal, R.A. Rao, S. Anwar, J. Ahmad= , R. Alunad, Adsorption studies on rice husk: removal and recovery of Cd (II) fr= om wastewater. Bioresour. Technol., 86 (2003) 147-149.

[12] S. Netpradit, P. Thiravetyan, S. Towprayoon, Application of waste metal hydroxide sludge for adsorption of a= zo reactive dyes, Water Res., 37 (2003) 763–772.

 

 

 

 

 

 

 

 

 

Determination of H2S in Crude Oil via a Rapid, Relia= ble and Sensitive Method

Amir Vahid

 

= aResearch Institute of Petroleum Industry (RIPI), West Entrance Blvd., Olympic Village, P.O. Box: 14857-33111, Tehran, Iran

 

Email: avahid753@gmail.com; vahida@ripi.ir

Abstract

Determination of hydrogen sulfide (H2S) in crude oil= is very important due to the environmental impacts, industrial problems, and l= egal international limitation of transportation. In the present work, H2S of crude oil is determined by liquid-liquid extraction followed by potentiometric titration. Moreover, three factors including dilution ratio = of crude oil with toluene, extraction time of H2S into the caustic phase and API of crude oil were investigated via factorial design. The ANOVA results have revealed that the dilution ratio, crude type, and extraction t= ime have the highest effect of the recovery of H2S from crude oil. In addition, the linear dynamic range of the method was from 1 up to 2000 ppm which can be manipulated for lower or higher concentration by further optimization of the above-mentioned parameters. Finally, this method is rap= id, reliable, operator-independent, which these characteristics make it a useful technique for the field test of crude oil and overcome extreme uncertainty = of H2S measurement.

Keywords: Crude Oil; Determination; Experimental Design; Field test; Hydrogen Sulfide.

1. Introduction

H2S is one of the most hazardous compounds which is colorless gas and can dissolved in aqueous and organic solvents. In additio= n, it is a poisonous and corrosive compound. In addition, it causes environmen= tal damages = (1-3). H2S can be present in petroleum and petroleum products including asphalt, resid= ual fuel oil, mid-distillates and their blend, natural gas and LPG = (4-6). H2S is evolved and produced in production of fossil fuels in oil and gas indust= ry. There is very tight international regulations in the transportation of crude oil and hydrocarbons = (7). Due to th= is regulations, determination of H2S at low level and also high lev= el is very critical from industrial and environmental point of view = ADDIN CSL_CITAT= ION {"citationItems":[{"id":"ITEM-1","itemDa= ta":{"DOI":"10.1002/jssc.201400727","ISBN&quo= t;:"1615-9314","ISSN":"16159314","abstra= ct":"Two-dimensional heart-cutting gas chromatography is used to analyze dissolved hydrogen sulf= ide in crude samples. Liquid samples are separated first on an HP-PONA column, = and the light sulfur gases are heart-cut to a GasPro column, where hydrogen sul= fide is separated from other light sulfur gases and detected with a sulfur chemiluminescence detector. Heart-cutting is accomplished with the use of a Deans switch. Backflushing the columns after hydrogen sulfide detection eliminates any problems caused by high-boiling hydrocarbons in the samples. Dissolved hydrogen sulfide is quantified in 14 crude oil samples, and the results are shown in this work. The method is also applicable to the analys= is of headspace hydrogen sulfide over crude oil samples. Gas hydrogen sulfide measurements are compared to liquid hydrogen sulfide measurements for the s= ame sample set. The chromatographic system design is discussed, and chromatogra= ms of representative gas and liquid measurements are shown.","author":[{"dropping-particle":""= ;,"family":"Heshka","given":"Nicole E.","non-dropping-particle":"","parse-names&q= uot;:false,"suffix":""},{"dropping-particle":= "","family":"Hager","given":"D= arcy B.","non-dropping-particle":"","parse-names&q= uot;:false,"suffix":""}],"container-title":&q= uot;Journal of Separation Science","id":"ITEM-1","issued":{"d= ate-parts":[["2014"]]},"title":"A multidimensional gas chromatography method for the analysis of hydrogen sul= fide in crude oil and crude oil headspace","type":"article-journal"},"uris&qu= ot;:["http://www.mendeley.com/documents/?uuid=3D12020bd6-df8a-4660-9f2= 9-577beef1ffb3","http://www.mendeley.com/documents/?uuid=3D23a000= ff-21fa-45c7-bf73-1aeaee51421b"]},{"id":"ITEM-2",&= quot;itemData":{"DOI":"10.1016/S0021-9673(02)00995-0&qu= ot;,"ISBN":"0021-9673","ISSN":"00219673&= quot;,"PMID":"12416874","abstract":"In the past 50 years, gas chromatography (GC) has played a most important role= in the analysis of oil. In this review, the early history is briefly reviewed; next developments in this highly relevant application area since about 1985= are highlighted. The main topic of interest are the introduction and decisive r= ole of capillary GC, the use of selective detection techniques, the versatility= of coupled-column techniques and, specifically, the additional power of comprehensive two-dimensional GC.","author":[{"dropping-particle":"",&= quot;family":"Blomberg","given":"J",&quo= t;non-dropping-particle":"","parse-names":false,&q= uot;suffix":""},{"dropping-particle":"",= "family":"Schoenmakers","given":"P.J&quo= t;,"non-dropping-particle":"","parse-names":f= alse,"suffix":""},{"dropping-particle":"= ","family":"Brinkman","given":"U.A.= Th","non-dropping-particle":"","parse-names&q= uot;:false,"suffix":""}],"container-title":&q= uot;Journal of Chromatography A","id":"ITEM-2","issued":{"date-pa= rts":[["2002"]]},"title":"Gas chromatographic methods for oil analysis","type":"article-journal"},"uris&quo= t;:["http://www.mendeley.com/documents/?uuid=3D6318071d-2c8f-456f-9107= -aa175bcbfe31","http://www.mendeley.com/documents/?uuid=3Dd75c3dd= b-d6c4-4cf4-ab6e-0fddcb4e7049"]}],"mendeley":{"formatte= dCitation":"(Blomberg et al. 2002; Heshka and Hager 2014)","plainTextFormattedCitation&= quot;:"(Blomberg et al. 2002; Heshka and Hager 2014)","previouslyFormattedCitation":"(Blomberg et al. 2002; Heshka and Hager 2014)"},"properties":{"noteIndex":0},"schema&= quot;:"https://github.com/citation-style-language/schema/raw/master/cs= l-citation.json"}= (8, 9)= (10-17). Furthermo= re, there is demand for a method which comprises requirements of a good method. These requirements including easy operation in field or laboratory, low hea= lth and safety problem, operator independent, low cost, repeatable, reproducible and providing very low detection limit as well as wide linear dynamic range. Among the methods of H2S determination, each of them has its own limitation (18-20). The health and safety hazards related to H2S= are summarized in Table 2 = (21). Furthermo= re, among the properties of the crude oil reported for the sale and refinery designing, H2S may be the most unstable parameter, even in comparison with Reid vapor pressure and specific gravity. So far, to the be= st of our knowledge, there is not an appropriate analytical method for determi= nation of H2S in crude oil for use in both oil field and laboratory tes= t. In the present work, a rapid method was developed and investigated using factorial experimental design for the determination of H2S of cr= ude oil which can be used in laboratory or field test and led to the repeatable= and accurate results.

 

Table1.

 

The health and safety hazards related to H2S are summarized in Table 2 = (Wedmann et al. 2014).

 

Table 2.

 

Furthermore, among the properties of the crude oil reported for= the sale and refinery designing, H2S may be the most unstable parame= ter, even in comparison with Reid vapor pressure and specific gravity. So far, to the best of our knowledge, there is not an appropriate analytical method for determination of H2S in crude oil for use in both oil field and laboratory test. In the present work, a rapid method was developed and investigated using factorial experimental design for the determination of H= 2S of crude oil which can be used in laboratory or field test and led to the repeatable and accurate results.

 

2. Materials and Methods  =

All chemicals were purchased from Merck and used as received. I= n a typical determination, 50 mL of crude oil and predetermined amount of tolue= ne as Diluting ratio were poured into a decanting funnel and shaken for a abou= t 5 minutes. Then 25 mL of 5 w/w% aqueous caustic solution was used as extracti= ng agent and was shaken for a predetermined time. The mixture was aged for 10 minutes to separate oil and aqueous solution. Afterwards, 10 mL of aqueous solution was decanted on a paper filter, and the filtrate was collected in a titration beaker. After addition of 2 mL on concentrated solution of ammoni= a, the filtrate was titrated with 0.05 N of silver nitrate solution. The first equ= ivalent point at about -600 mV is related to the H2S. Titration was carr= ied out using a Metrohm titrando 880 according to the UOP 209.

 

For the optimization of the condition of determination, a facto= rial design was applied for the investigation of three main effects, including t= ime required for extraction, diluting ratio ration and crude type according to its API. = 12 experimental runs were designed and carried out. Calculation and modeling of results were done using Design Expert 7.

Recovery is defined as the ratio of the concentration of the H<= sub>2S obtained in the designed test to H2S obtained at 2 hours and 60 C with diluting ratio of 5.

 

3. Results and Discussion

The condition of statistically designed runs and their corresponding results are given in Table 3.

 

Table 3.

 

Analysis of variance of obtained results is calculated and give= in Table 4. The obtained Equation for model is given as Eq. 1 in terms of coded factors.

 

Table 4.

 


    Recovery =3D +91.75 - (1.25 * A[1]) + (0= .50 * A[2]) +(4.75  * B) + (1.75 * C) + (= 0.42 * BC) (Eqn. 1)

 

As seen in Figure 1, and according to the Equation 1 and ANOVA (Table 4), it can be said that Time has very little effect on the recovery = of H2S. It is a very good property for an analytical method to carry out in short t= ime.

 

 

Figure 1.

 

 

 

 

Figure 2.

Fig. 2 displays the effect of Diluting ratio which is the most effective factor among all. Moreover, it is generally known that crude oil = has very broad range of properties in term of density and viscosity. H2S is trapped in the complex matrix of crude oil. Thus, the presence of toluen= e is essential for the dilution of the crude oil and breaks its complex matrix a= nd semi ordered array of large molecules (wax, resin, and asphaltene) to easily evolve the trapped H2S.

As the crude oil becomes heavier as well as viscose, the evolve= of H2S becomes more difficult and led to the reduction of recovery.= So higher Diluting ratio is necessary in case of heavy crude oil. This means t= hat Diluting ratio is the most important factor, as could be deduced from its F value in Table 4.

 

 

Figure 3.

 

Fig. 3 shows the effect of crude type on the recovery of H= 2S. As the API of crude oil increases, the crude oil become lighter and recover= y is higher due to the better contact of oil phase and caustic phase an so need = to low Diluting ratio and vice versa.

 

Figure 4.

 

Fig. 4 illustrates the interaction of the crude type and diluti= ng ratio in a 3D curve. In case of heavier crude oil, i.e. at lower API, the effect = of diluting ratio is very large while at higher API, this effect is lower. <= /span>

It can overall said that higher diluting ratio and lower extrac= tion time are in favor of recovery despite the fact that higher time, 10 minutes= , is steel low for a typical analytical method. For the determination of other merits of this analytical method, additional test was done. In addition, on= e of the most important properties of a robust analytical methods is Linear Dyna= mic Range. Four crude oils containing H2S concentration ranged from = 0.2 to 1902 ppmw were examined. Moreover, obtained results showed that any concentration of H2S can be determined by manipulation of amount= of aliquot of crude oil used for test. For the Crude oil contains 1902 ppmw, o= nly 2 grams of crude oil is adequate while for sample containing 0.2 ppmw of H<= sub>2S, 100 grams of crude oil is needed. RSD for the 148 ppmw H2S, in f= our determinations, was obtained 98%.

Another advantage of this methods is its compatibility for field determination because H2S is very volatile and unstable. It is generally known that long delay between sampling and determination led to t= he loss of H2S and cusses lower result.  

Furthermore, for field test, operator can pour the fresh crude sample into the decanter containing toluene and caustic solution. After tha= t, vigorous stirring of this mixture led to the absorption of H2S i= nto the caustic phase and prevent loss of the analyte before titration or trans= port to laboratory.

It is noteworthy to say that for further improvement of quantification limit and RSD of method, once can increase the absolute amou= nt of crude oil and extraction time. Furthermore, decreasing the amount of cau= stic solution, which results in higher concentration factor, and using centrifuge instead of decanter for separation of caustic phase prior to titration can improve quantification limit and RSD.

It is well known for those who work in petroleum laboratories t= hat H2S is very unstable and as the time between sampling and analys= is increases, the error of the obtained results drastically increases. In this method, once can pour known quantity of caustic solution in to the pre-weig= hed sample container and then rinse the crude oil from sampling point in to the container to absorb H2S into the caustic solution during transfe= r to the laboratory.

 

Conclusions

In this work, a method comprising the merits of very good analytical method is reported. The method is rapid because the time needed = for extraction is lower than 10 minutes and a traditional potentiometric titrat= ion. Quantification limit of the method is low enough. Linear Dynamic Range of t= he method is very broad and this range can be 

tuned by changing the amount of crude oil. In addition, RSD of = the method is up to 98% which is very good for a volatile and unstable compound, i.e. H2S in a complex matrix of crude oil. The equipment needed = for this method is very simple, accessible and cheap. Finally, the procedure of determination, including extraction and titration, is very traditional and don't need high level of expertise and skill. Furthermore, the method is ca= pable of performing for field test which is very important from industrial point = of view. Also, main factors of the method can be tuned easily according to the properties of the crude oil to manipulate lower and upper limit of quantifi= cation.

 

Acknowledgment

This work was financially supported by Research Institute of Petroleum Industry under the grant number of 1647601.

 

References

1.      R.J. Dieffenstein, W.C. Hulbert, S.H. Roth, Toxicology of Hydrogen Sulfide, Annu. Rev. Pharmacol. Toxicol., 32 (1992) 109-134.

2.      H. Kimura, Metabolic turnover of hydrogen sulfide, Front Physiol., 3 (2012) 1-3

3.      H.S. Kalal, A.A.M. Beigi, M. Farazmand, Determination of trace element= al sulfur and hydrogen sulfide in petroleum and its distillates by preliminary extraction with voltammetric detection, Analyst, 125 (2000) 903-908.

4.      L. Zhang, P. De Schryver, B. De Gusseme, Chemical and biological technologies for hydrogen sulfide emission control in sewer systems: A revi= ew, Water Res., 42 (2008) 1-12.

5.      M. = Abdouss, N. Hazrati, A.A. Miran Beigi, Effect of= the structure of the support and the aminosilane type o the adsorption of H2S from model gas, RSC Adv., 4 (2014) 6337-6345.<= /o:p>

6.      N. Hazrati, M. Abdouss, A. Vahid, Removal of H2S from crude oil via stripping followed by adsorption using ZnO/MCM-41 and optimization of parameters, Int. J. Environ. Sci.Technol., 11 (2014) 997-1006.

7.      X. Zhao, J.B. Gao, W.D. Zhang, B. Wang, Study on the risk of a crude o= il shipping channel in China, ICCTP, 6 (2011) 3877- 3886.

8.      J. Blomberg, P. Schoenmakers, U.A.T. Brinkman, Gas chromatographic met= hods for oil analysis, J. Chromatogr. A, 972 (2002) 137-173.

9.      N.E. Heshka, D.B. Hager, A multidimensional gas chromatography method = for the analysis of hydrogen sulfide in crude oil and crude oil headspace, J. S= ep. Sci, 37 (2014) 3649-3655.

10.  H. Sid Kalal, A.A. Miran Beigi, M. Farazmand, S.A. Tash, Determination= of trace elemental sulfur and hydrogen sulfide in petroleum and its distillate= s by preliminary extraction with voltammetric detection, Analyst, 125 (2000) 903-908.

11.  N.S. Lawrence, R.P. Deo, J. Wang, Electrochemical determination of hydrogen sulfide at carbon nanotube modified electrodes, Anal. Chim. Acta, = 517 (2004) 131–137.

12.  S.K. Pandey, K.H. Kim, K.T. Tang , A review of sensor-based methods for monitoring hydrogen sulfide, TrAC - Trends Anal. Chem, 32 (2012) 87–99.

13.  Y. Zhao, T.D. Biggs, M. Xian, Hydrogen sulfide (H2S) releas= ing agents: chemistry and biological applications, Chem. Commun., 50 (2014) 11788-11805.

14.    J.F.S. Petruci, A. Wilk, A.A. Cardoso, B. Mizaikoff, Online analysis of H2S and SO2= via advanced mid-infrared gas sensors, Anal. Chem., 87 (2015) 9605–9611. <= /o:p>

15.  O. Yassine, O. Shekhah, A.H. Assen,  H2S sensors: fumarate-based fcu-MOF thin film grown on a capacitive interdigitated electrode, Angew Chem., 55 (2016) 15879-15883.

16.  N.E. Heshka, J.M. Choy, J. Chen, Gas chromatographic sulphur speciatio= n in heavy crude oil using a modified standard D5623 method and microfluidic dea= ns switching, J. Chromatogr. A,1530 (2017) 241-146.

17.  F. Huber, S. Riegert, M. Madel, K. Thonke, H2S sensing in t= he ppb regime with zinc oxide nanowires, Sensor. Act. B. Chem., 239 (2017) 358-363.

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20.  O.A. Habeeb, R. Kanthasamy, G.A.M. Ali, Hydrogen sulfide emission sour= ces, regulations, and removal techniques: a review, Rev. Chem. Eng., 34 (2017) 9= -19.

21.  R. Wedmann, S. Bertlein, I. Macinkovic, et al. Working with “H2S”: Fac= ts and apparent artifacts: nitric oxide, Biol. Chem, 41 (2014) 85-96.

 =

 

 =

 =


 

 =

= Figures

Figure 1. <= o:p>

 

Figure 2.

 

 

 

 

 

Figure 3.

 

Figure 4.

 


 

= Figure captions

Figure 1. Effect of factor A: Time on recovery.

Figure 2. Effect of factor B: Diluting ratio on recovery.<= /o:p>

Figure 3. Effect of factor C:Crude type on recovery.=

Figure 4. 2D representation of  interaction of Crude type and Diluting ratio.


 

= Tables

Table 1.

Method

Disadvantage

Scope of work

Dynamic range

ASTM D5623

Narrow dynamic range, High cost, Limited sample boiling range=

GC of Liquid distillates with FBP < 230 °C

0.1 - 100 ppm

UOP 212

Limited sample boiling range, High cost

Potentiometric titration, etha= ne to such gasoline

1 to several thousand ppmw of H2=

ASTM D5705

Only applicable to vapor phase, Poor repeatability=

 H2S in the va= por phase (equilibrium) of a residual fuel oil for field test using gas detection tubes and Can test

5 ppm v/v to 4000 ppm v/v =

UOP 163

Not applicable to crude oil, Complex data interpretation=

H2S in

1 up to 100 ppmw.

ASTM D7621

IP 570

ISO 8217

Not applicable to crude oil, mercaptan interference

H2S in Fuel Oils by Rapid Liquid Phase Extraction<= /span>

1 up to 50 ppmw<= /span>

 

UOP 41

ASTM D4952

Doctor Test

Only for qualitative analysis, Using of poisonous metal<= /o:p>

qualitative test of H2S in gasoline, jet fuel, kerosine and similar petroleum products and solvents

 

ASTM 6021

 

skilled operator and complex calculations, High cost

H2S in Residual Fuels by Multiple Headspace Extraction and Su= lfur Specific Detection

0.01  to 100 ppmw 

IP 399

Complex procedure and pure materials needed. Oxidation and absorption may occur.

H2S in Residual Fuels by sprctrophotometric determination.

0.50  to 32 ppmw&n= bsp;

 =

 =

Table 2.

Concentration mg/kg

Health & Hazard Effect

Considered Immediately Hazardous

 =

Table 3.

Std. run order

A:

Time (min)

B:

Diluting ratio

C:

Crude type (API)

Recovery %

1

2

1

22

84

2

6

1

22

86

3

10

1

22

87

4

2

2

22

93

5

6

2

22

95

6

10

2

22

95

7

2

1

36

87

8

6

1

36

89

9

10

1

36

89

10

2

2

36

98

11

6

2

36

99

12

10

2

36

99

 

Table 4.

Source

Sum of Squares

df

Mean Square

F Value

P-value Prob > F

Remark

Model

319.1

5

63.8

328.2

< 0.0001

significant

A-Time

9.5

2

4.8

24.4

0.0013

B-Diluting ratio

270.8

1

270.8

1392.4

< 0.0001

C-Crude type

36.8

1

36.8

189.0

< 0.0001

BC

2.1

1

2.1

10.7

0.0170

Residual

1.2

6

0.2

Corr. Total

320.3

11

 

Table Legends

Table1. Standard methods of H2S determination and th= eir properties = (Nadkarni 2000).

Table 2. Exposure limit and its related hazards.

Table 3. Designed test runs for = H2S determination.  <= /p>

Table 4. ANOVA of obtained results of H2S analysis.<= o:p>

 

 

 

 

 

 

 

 

 

 

 

 

 

 

 

Functionalized graphene-trimethoxyphenyl silane for toluene rem= oval from workplace air by sorbent gas extraction method <= /p>

Majid Bagheri Hosseinabadi1, Shahnaz Timoori2 and Ali Faghihi Zarandi3,*

1- School of Public Health, Shahroud University of Medical Sciences, Shahroud, Iran.

2- Department of Environment and Natural Resources, Islamic Azad University, Science and Research Branch, Tehran, Iran.

3- Occupational Health Engineering Department, School of Public Health, Kerman University of Medical Sciences, Kerman, Iran.

 

Abstract

Inhalation exposure to toluene in the environment and workplace causes that some concerns about its adverse health effects on public and workers raise. So the implementation of high-performance methods to control toluene emission in industrial and environment settings is very important. = Moreover, a new synthesized sorbent based on functionalizing graphene with N-Phenyl-3-aminopropyl trimethoxy silane (G-PhAPTMS, C12H21= NO3Si) was developed as a novel sorbent for removal of toluene from a= ir by sorbent gas extraction procedure (SGEP). By proposed method, the removal efficiency of G-PhAPTMS was compared with other sorbents such as activated carbon (AC), graphene (G), and graphene oxide (GO). In addition, the standa= rd gas of toluene generated in pure air with different concentrations, and the effects of parameters such as temperature (10-90 °C), flow rate (50-500 mL = min-1) and the amount of sorbent (2-30 mg) were investigated. According to the results, increasing the flow rate and temperature had negative effects on t= he removal efficiency of all sorbents. The highest removal efficiency of G-PhA= PTMS was obtained up to 35 °C and less than 250 mL min-1 (>95%). <= span style=3D'mso-spacerun:yes'> In optimized conditions, the amount of s= orbent for toluene removal from air was achieved more than 10 mg of G-PhAPTMS. Fin= ally, the results indicate that the G-PhAPTMS has high removal efficiency and sur= face area as compared to the AC, G, and GO. Furthermore, functionalizing graphene with N-Phenyl-3-aminopropyl trimethoxy silane improved the absorption of to= luene due to chemical bonding (π–π electron donor–acceptor) and introduced an environmentally friendly sorbent.

Key words: Toluene, Chemical adsorption, Graphene, N-Phenyl-3-aminopropyl trimethoxy silane, Sorbent gas extraction procedure,

 

= = 1.&n= bsp;       = Introduction

Toluene is one of the well-known air contaminants and widely us= ed as an organic solvent in various industries such as petroleum refining, shipping, rubber manufacturing, automobile repairing, and shoe manufacturin= g = (1). It is est= imated that toluene is consumed about 2.3 million tons in worldwide annually= (2). Moreover, public and occupational exposure to toluene can occur through the inhalatio= n of toluene fumes from cigarette smoking and vehicle emission = (3). In additi= on, it is likely to release from indoor sources such as paints, paint thinners,= and adhesives = (4).The studies have been shown that chronic exposure to toluene can cause a wide variety of health problems including neurotoxic effects (from headache and fatigue to narcosis with increasing exposure level) and mucosal irritation = (5, 6). Because o= f the harmful effects of toluene, the implementation of high-performance methods = to control toluene emission in industrial and environment settings is inevitab= le = (7). There are some different methods such as including adsorption, condensation, thermal oxidation, catalytic oxidation, photo catalytic oxidation and bio filtratio= n that can be applied to reduce the concentration of toluene in air = (8-11). It seems = that adsorption as a low operating cost and effective method can be used to remo= ve toluene from air at low concentration= (12, 13). Adsorptio= n is a process in which the molecules of pollutants are trapped at the surface of porous materials such as zeolites, silica gel and activated carbons by phys= ical adsorption = (14-16).

Among the different adsorbents, carbon adsorbing materials such= as graphene oxide, activated carbons, carbon nanotubes, and porous carbon have demonstrated more advantage due to their low density, chemical stability an= d variety of structural forms = (17-20). The found= ing of new<= /span> carbon materials= is always one of the favorite subjects= in the process of adsorption and seque= stration (21). Graphene, = new two-dimensional carbon nanomaterial, as a new member of the carbon family w= ith desirable properties such as low weight, small size, high surface area, and superior electrical, thermal and mechanical properties has attracted much attention = (22-24). The more advantage of graphene is the adsorption ability of chemicals with benzene r= ings like toluene through strong π-π interaction= (25, 26). In additi= on,  some functional groups has turned graphene = into an excellent adsorbent [27].

On the other hand, graphene has high theoretic surface area up to 2620 m2 g= -1 that it become an ideal adsorption = (28, 29). Furthermo= re, graphene can be easily obtained from the cheap natural graphite in large scale = (29, 30). = In this regard, the high adsorption capacity of graphene and its derivatives was confirm= ed for dyes = (31), pharmaceutical antibiotics = (32), heavy met= als, and VOCs in water = (33, 34). However, = the studies on toluene adsorption characteristics and behaviors onto graphene from air are limited = (35).

      In this stu= dy, toluene removed from air based on G-PhAPTMS by SGEP. The different experimental conditions such as mass, flow rate, and temperature were investigated and optimized. By proposed procedure, the chemically adsorption mechanism of toluene was achieved based on π-π interaction between toluene and= the surface of the G-PhAPTMS.

 

2. Experimental procedure

2.1. Material and Instruments

        Toluene was pur= chased from Fluka (Germany) with purity above 99.5%. In addition, standard gas was obtained by injecting a certain amount of toluene into a 10 ml glass vial w= ith PTFE cap to determine absorption capacity. In this study, helium and pure air we= re used as the dilution gas. Standard gas was prepared with a relative humidity of 32±5% for simulating the humidity in the workplace air. Thus, before fillin= g the vial, the dilution gas was passed through deionized water. The concentratio= ns of toluene in the standard gas were prepared from 9 to 75 mg L-1 (in batch system, high concentration up to 400 mg L-1). <= /span>

In addition, a dynamic standard gas generation was designed to measure removal efficiency. This system consisted of impinger, adsorption t= ube, micro compressor, and sampling Tedlar bag (SKC Inc., USA). A certain amount= of toluene was injected to the impinger, and then the dilution gas with a cert= ain flow was passed through the adsorption tube. At the end of the system, unab= sorbed toluene was collected into the Tedlar bag.  The concentration of toluene in the Tedl= ar bag was measured by gas chromatography equipped with flame ionization detector (GC-FID) and air sample loop injection (Agilent GC, 7890A, FID, Netherland). Also, GC-MS was used for validation toluene concentration in air.

The crystal structure studies of the solids were carried out by X-ray diffractions (PW 1840, Phillips X-ray diffractmeter, Netherland) with Cu-Kα radiation source. Raman spectroscopy was performed us= ing an Almega Thermo Nicolet and 532 nm Ar-ion laser excitation source. The Fou= rier transform infrared (FT-IR) spectrum was recorded on Bruker IFS 88 spectrome= ter (Bruker Optik GmbH, Ettlingen, Germany) with KBr pelleting method in the 4000–400 cm−1. The morphology of the sorbent was examined = using scanning electron microscopy (SEM, Phillips, PW3710, Netherland) and transmission electron microscopy (TEM, CM30, Philips, Netherland).

 

2.2. Synthesis of functionalized graphene with N-Phenyl-3-amino= propyl trimethoxy silane

Graphene (G) was prepared by our special CVD (chemical vapor deposition) method by an electrical furnace consisting of a quartz tu= be. The furnace heating tuned up to 1000 ºC for 25 min. The reaction between methane and hydrogen (4:1) was obtained. In order to pure grapheme without = any metals, the product was stirred in HCl solution (ultra-trace) for about 20 = h. The sample was then washed repeatedly with ultra-pure water until the solut= ion became neutral. The treated product was finally dried in oven at 120 ºC. Fo= r carboxylation process, 1 g of the as-prepared G was first mixed with a 200 mL mixture of concentrated H2SO4 and HNO3 (3:1 v/v) and stirred for 20 min at room temperature followed by sonication at 55 ºC for 4 hours in an ultrasonic bath (50 kHz and 100 W). After cooling to room temperature, the reaction mixture was diluted with 500 ml of deionized water and then vacuum-filtered through a filter paper (0.2 μm). Finall= y, G-COOH was dried in oven at 70 °C. In order to the formation of the free hydroxyl group, 0.5= g of filtered G-= COOH was added to a methanolic solution of sodium borohydride. Then, the G bearing –OH group were all= owed to disperse in xylene followed by addition of N-Phenyl-3-aminopropyl trimethoxy silane (Ph= APTMS) to synthesize functional= ized G in refluxing. After washing with xylene to remove the unreacted excess Ph= APTMS, the product was dried fo= r 10 h at 90 °C under reduced pressure. Morphology of the G-PhAPTMS was studied using scanning electron microscopy (SEM) and transmission electron microscopy (TEM).  Grap= hite powder (5 g) and NaNO3 (2.5 g) were mixed with 120 mL of concentrated H2SO4 and stirred for 30 min in an ice b= ath (0-5 °C). KMnO4 (15 g) was gradually added to the vigorously stirred suspension and the temperature of the mixture was kept to be below = 15 °C. The ice bath was then removed, and the mixture was stirred at 35 °C until it gradually became brownish slurry, and then it was diluted slowly with 250 m= L of water. The reaction temperature was rapidly increased to 98 °C with effervescence, and the color changed to brown color. Later, H2O<= sub>2 solution (30%) was added to stop the oxidation process, and the color of the mixture changed to bright yellow, indicating fully oxidized graphite. The graphite oxide formed was washed by rinsing and centrifugation with diluted= HCl solution and then repeatedly with deionized water until the filtrated solut= ion became neutral. Graphene oxide nanosheets were obtained by ultra-sonication= of the filtered graphite oxide suspension followed by centrifugation for 15 mi= n at 3000 rpm to remove any un-exfoliated graphite oxide. Finally, it was air-dr= ied at 60 °C for 12 h. In this study, graphene oxide and activated carbon commercially were purchased from RIPI, Iran.

 

 

 

General procedure

= Because the removal efficiency is highly affected by the amount of sorbent, the eff= ects of amount of sorbents were studied in 1, 2, 4, 5, 10, 15, 20, 25, and 30 mg= of different sorbents including G-PhAPTMS, G, GO and AC. The flow rate of the dilution gas was set from 50 to 500 ml min-1. The effects of temperature on the absorption of toluene were investigated in different temperature from 10 to 90 °C. The same concentration of standard gas of tol= uene was passed through the adsorption tube containing different amount of each sorbents in various thermal and flow rate conditions. The concentration of unabsorbed toluene collected in the Tedlar bag was analyzed by gas chromatography equipped with flame ionization detector. Removal efficiency = was calculated as seen in Equation 1. The removal of toluene was evaluated in present of pure air in different flow rate by G= -PhAPTMS, G, GO and AC as nanosorbents. In optimized conditions, the static and dynam= ic system was used by SGEP. The air was purified with electro air cleaner (EAC) and mixed with toluene in pilot. By proposed pilot, the pure air with and without toluene gas based on SGEP met= hod was measured (5 times) by GC-FID and validated by GC-MS.  The novel G-PhAPTMS sorbent had chemical and physical adsorption between G and N-Phenyl with toluene, respectively.  The mechanism of che= mical adsorption was occurred based on π–π interaction of N-Phenyl with toluene. Moreover, the G-PhAPTMS was more interaction than G for toluene removal from air.=   By new synthesis, G was function= ed by PhAPTMS and improved the compatibility between toluene and surface of sorbent in optimized conditions as compared to G, Go, and AC. 

Removal Efficiency =3D Cin-Cout/Cin<= /sub> × 100              Eq 1

 

Cin (mg L-1) and Cout (mg L-1) were the concentration of toluene before and after adsorption respectively.

Results and discussion

Morphology of the G-PhAPTMS has been studied by SEM and TEM (Fi= g. 1 and 2). After functionalizing of graphene with N-Phenyl-3-aminopropyl trime= thoxy silane, it seems that the graphene has much more active surface to absorb toluene.

 

 

Figure 1: SEM images of the G-PhAPTMS.

 

 

Figure 2: TEM image of the G-PhAPTMS.

 

 

Effect of Temperature:

The removal efficiency of G-PhAPTMS, G, GO and AC in temperature from 10 to 90 °C are shown in Fig. 3. Functionalizing graphene could improve the properties of graphene in absorption of toluene from the air by increas= ing temperature. In addition, activated carbon had more removal efficiency rath= er than graphene oxide in the same conditions. The removal efficiency of G-PhA= PTMS decreased more than 50 °C, while, the removal efficiency of AC and GO decre= ased sharply from 68% and 40% in 45 °C to 5% and 2% in 90 °C respectively. Based= on the results, the temperature can play a main role in removal efficiency of sorbents for toluene removal from air. By paying attention to previous stud= ies, the removal efficiency with increasing temperature was reported in other studies = [36]. For insta= nce, Sone et al. (2008) reported that absorption of VOCs can be highly influence= d by increasing temperature. They found that when temperature was increased from= 50 °C to 80 °C, the percentage of recovery of toluene decreased from 105.04 to 96.86 for charcoal = [37]. Furthermo= re, it has been found out by Shih an Li in 2008 that lower temperature is a favori= te condition for absorbing VOCs into the surface of carbon nanotube= [38]. Overall, = it can be argued the negative relation between increasing temperature and decreasing removal efficiency indicates that the sorption is an exothermic process, and decreasing temperature can improve the absorption properties of all investigated sorbents.

 

Figure 3: the effects of temperature on removal efficiency of G-PhAPTMS= , AC, and GO.

 

Effect of flow rate

The effect of flow rate on removal efficiency in 25 °C was investigated to optimize the flow rate conditions. The flow rate was set on= 50 to 500 ml min-1 for all sorbents. The results are presented in F= ig. 4.

Figure 4: the effects of flow rate on removal efficiency of G-PhAPTMS, A= C, and GO.

 

The removal efficiency of G-PhAPTMS, G, GO, and AC decreased by increasing the flow rate, like temperature. The results showed, the more removal efficiency of G-PhAPTMS as compared to other sorbents, and the remo= val efficiency of G-PhAPTMS was decreased up to 62% in 500 ml min-1.= However, the removal efficiency of AC and GO in this flow rate was 32% and 5% respectively. Increasing the flow rate affected on the removal efficiency of all sorbents, but this effect was lower for G-PhAPTMS. Similarly, the impac= t of flow rate (45, 92 and 184 ml min-1) on the removal efficiencies = of toluene, limonene and methyl ethyl ketone was investigated by Yao et al in 2009. The= ir results showed that removal efficiency was decreased from 79% to 21% by increasing the flow rate = [39]. Moreover,= declining removal efficiency of fluoride by increasing the flow rate from 20 to 30 ml= min-1 in activated alumina was reported by Ghorai and Pant = [40]. The influ= ence of flow rate on removal efficiency may be explained by reaction time. When = the flow is high, the molecules of toluene have a little time to interact with = the surface of absorbent, so they begin to escape from the end of the sorption = tube = [41].

 =

Effect of mass sorbent

The amount of sorbent is another important parameter which was investigated in this study. The absorption tubes were loaded by different amounts of each absorbent from 1 to 30 mg by proposed method. The temperatu= re and flow rate were set on 25 °C and 200 ml min-1. The results are shown in Fig. 5.

Figure 5: the effects of amount of sorbent on removal efficiency of G-Ph= APTMS, AC, and GO.

 

The removal efficiency of toluene with G-PhAPTMS increased by i= ncreasing the amount of sorbent and reached the highest pint in 5 mg of sorbent. In addition, the removal efficiencies of AC and GO followed the same pattern as the G-PhAPTMS, while reached the highest pint in 15 and 30 mg of sorbents respectively. The GO had the lowest removal efficiency rather than the G-Ph= APTMS, G, and AC for all amount of sorbent. The positive impact of amount of sorbe= nt on removal efficiency was reported by Samarghandi et al (2017) in the remov= al of reactive red from distillated water. They found that the removal efficie= ncy increased when the amount of active carbon and graphene increase from 0.2 t= o 4 g L-1 and 0.02 to 0.4 g L-1 respectively = [42]. Higher am= ount of sorbent provides much more chance for the molecule of toluene to react w= ith the available surface of sorbent. So, the removal efficiencies of sorbents increase effectively. Based on the results, the more active absorption site= s of g L-1 allow the molecules of toluene to absorb rapidly and functionalizing graphene creates this opportunity that in the lower amount = of sorbent, So we have maximum removal efficiency by G-PhAPTMS as compared with other sorbents. Repeatability of the sorbents was investigated in 25 °C, 20= 0 ml min-1 and from 2 to 30 mg of each sorbent (Figure 6). Each type = of sorbent was used for twenty times and the mean of removal efficiencies were calculated.  

 

Figure 6: The removal efficiency of different sorbents after using repeatedly.

The G-PhAPTMS had the highest removal efficiency for all invest= igated amount of sorbent compared with G, GO and AC sorbents after twenty times ab= sorption and desorption. The mean of removal efficiency of AC experienced a downward pattern from 5 to 30 mg. Decreasing the removal efficiency for the GO happe= ned from 20 mg to 30 mg where the removal efficiency fell from 64 to 42%. According = to the results, functionalizing graphene with N-Phenyl-3-aminopropyl trimethoxy silane (G-PhAPTMS) can improve the absorption characteristics of graphene to absorb toluene from air.

 

Validation

The G-PhAPTMS was used as a novel and low-cost sorbent for remo= val of toluene vapor from air. By proposed method, a mixture of 5-100 ppm of to= luene vapor in artificial air with argon gas as a carrier gas passed through sorb= ent (G-PhAPTMS) by a pump. The concentration of toluene in standard gas was validated by highly sensitive and accurate GC-MS instrument in different concentration before using by proposed method. Since standard reference material for toluene in air is not currently available, the spiked of valid= ated toluene concentration in a bag (GC-MS, 50 ppm, bag 5 Li, 0.2 L min-1) were prepared to demonstrate the reliability of the method by G-PhAPTMS. At= optimum condition in one minute, 2.0 ppm of toluene vapor in air was almost removed= by G-PhAPTMS. The efficient recovery of spiked samples was reasonable and was confirmed u= sing addition method, which it indicates the capability of proposed method for removal of toluene from air (Table 1).

= Table 1: The recovery of G-PhAPTMS for removing toluene from air.

Samples

Toluene in air (ppm)*

Toluene in sorbent (ppm

Sorbent Recovery (%)

Sample A<= o:p>

2.63 ± 0.= 07

2.57 ± 0.= 11

97.7=

Sample B<= o:p>

6.89 ± 0.14<= /p>

6.48 ± 0.21<= /p>

94

Sample C<= o:p>

10.72 ± 0= .19

10.51 ± 0= .32

98

Sample D<= o:p>

14.08 ± 0.34=

13.52 ± 0.84=

96

Sample E<= o:p>

18.73 ± 0= .17

17.35 ± 0= .28

92.6=

* Initial concentration in standard gas

= ** Measured concentration in sorbent

 

Conclusions

In this study, different absorbents such as G-PhAPTMS, G, GO, a= nd AC were used to remove toluene from air. The results showed that functional= izing graphene with N-Phenyl-3-aminopropyl trimethoxy silane (G-PhAPTMS) promotes= the removal efficiency of graphene by chemical bonding as π–π electron donor–acceptor. Furthermore, increasing temperature and flow rate have negative effects of = the removal efficiency of all sorbents, but the results of G-PhAPTMS showed hig= h removal efficiency of toluene compared to the AC, G, and GO. The amount of sorbent = was another parameter which was investigated. In optimized conditions, the amount of sorbent for the G-PhAPTMS, AC, and the GO were obtained 5, 5, and 30 mg respectively. This result shows that the G-PhAPTMS has many more available = active sites for absorption of toluene. By lower amount of G-PhAPTMS, high removal efficiency was achieved more than 95% by interaction between toluene and N-= Ph. The results of repeatability of sorbents also indicate that functionalizing graphene with N-Phenyl-3-aminopropyl trimethoxy silane allows graphene to b= e used repeatedly, and it can be introduced as an environmentally friendly sorbent= .

 

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Food Analysis: Task specific ionic liquids for separation of nickel and cadmium from olive oil samples by thermal ultrasound-assisted dispersi= ve multiphasic microextraction

 

=  

Hamid Shirkhanloo1,à= and Aisan Khaligh 2,3

 

=            

1= Research Institute of Petroleum Industry (RIPI), West Entrance Blvd., Olympic Villag= e, P.O. Box: 14857-33111, Tehran, Iran

2 Department of Chemistry, Semnan University, Semnan, 35131-1911, Iran.<= /o:p>

 

Email: hamidshirkhanloo@gmail.com

 

 

 

 

 

 

 

 

 

 

 

Abstract

In this stu= dy, a novel task-specific ionic liquid (TSILs) was used for highly sensitive extraction and separation of nickel and cadmium in olive oil by thermal ultrasound-assisted dispersive multiphasic microextraction (TUSA-DMPμE). By proposed method, a mixture containing of hydrophilic TSILs (α- Cyano-4-hydroxycinnamic acid diethylamine; [CHCA] [DEA] and 1-(2-Hydroxyethyl)-3-methylimidazolium tetrafluoroborate; [HEMIM][BF4]) as a complexing and extracting solvent, acetone as a dispersant of TSILs was add= ed to diluted olive oil with n-hexane containing Cd (II) and Ni (II) that was already complexed by TSILs in 60OC at pH 6.0-7.5. After optimized conditions, the enrichment factor (EF), Linear range (LR) and limit of detection (LOD) were obtained (19.3; 19.6), (5.0- 415 μg L-1; 2.7- 92 μg L-1) and (1.3 μg L-1;  0= .6 μg L-1) with [CHCA] [DEA] and (13.7; 14.2), (7.5- 600 μ= ;g L-1; 3.6- 128 μg L-1) and (2.2 ng L-1; 0.9 μg L<= sup>-1) with [HEMIM][BF4] for Ni and Cd ions in olive oil samples respectively. In addition, the ions extraction with [CHCA] [DEA] is more efficient than [HEMIM][BF4] by TUSA-DMPμE method (less than 60%). Moreover, the validation of methodology was achieved by standard oil by microwave digestion/ETAAS = technique= atom trap flame atomic absorption spectrometry (AT-FAAS)

=  =

= Keywords: Olive oil; Cadmium and nickel; Thermal ultrasound-assisted dispersive multiphasic microextraction; Task specific ionic liquid; Atom tr= ap flame atomic absorption spectrometry

=  

=  

= 1. Introduction

= The edible oil toxicity by cadmium (Cd) and nickel (Ni) ions is very important problem in food industry because of bioaccumulation in human body and cause damage to organs such as kidney dysfunction, hypertension, liver damage, lu= ng damage, cancer and adverse DNA modifications = [1-3]. The prese= nce of high concentration of Cd (II) and Ni (II) in edible oils may also have deleterious effects on the quality of the product, causing changes to their taste and smell = [4]. Cd (II) a= nd Ni (II) ions are easily transferred from arable land to oil plants, which a= re increasingly contaminated by cadmium and nickel from phosphate-based fertilizers. These toxic elements can also be present in edible oils, as a result of contamination from the environment, the refining process, the sto= rage tank, and the packing with different materials = [5-7]. The U.S. = Food and Drug Administration (USFDA) reported that the permissible limits of nic= kel and cadmium in the vegetables oils are less than 1.0 mg/kg and 0.1 mg/kg, respectively. For healthy people, the mean of cadmium and nickel concentrat= ion in human serum samples is less than 0.2 μg L-1. Therefore, = the accurate determination of trace cadmium and nickel ions in edible oils is an important concern because of their toxic role in human body and possibiliti= es for adulteration detection and oil characterization = [8-10]. The prese= nce of trace metal ions in edible oils were quantitatively determined by differ= ent techniques such as flame atomic absorption spectrometry (F AAS) = [1, 3, 11], electro-thermal atomic absorption spectrometry (ET AAS) = [12], inductive= ly coupled plasma atomic emission spectrometry (ICP AES) = [12, 13], inductive= ly coupled plasma mass spectrometry (ICP MS) = [4, 14], and adsorptive stripping square wave voltammetry (Ad SSWV) = [15]. Sample preparation is a critical step in the whole analytical procedure due to low concentration levels of metal ions and high organic matrix of oils <= !--[if supportFields]>=  ADDIN EN.CITE <EndNote><Cite><Author>Tokay</Author><Year>20= 15</Year><RecNum>156</RecNum><DisplayText><style font=3D"Times New Roman" size=3D"12">[3, 16]</style></DisplayText><record><rec-number>156<= ;/rec-number><foreign-keys><key app=3D"EN" db-id=3D"frsr5sd0eewzr7etr5rxtpa9pze9xfa2a0ve&quo= t;>156</key></foreign-keys><ref-type name=3D"Journal Article">17</ref-type><contributors><authors><= author>Tokay, Feyzullah</author><author>Bağdat, Sema</author></authors></contributors><titles><t= itle>Spectrometric determination of iron and copper in vegetable oils after separation with Sc= hiff base impregnated silica gel column: A simple approach for eliminating the h= igh organic matrix</title><secondary-title>International journal of food science &amp; technology</secondary-title></titles><periodical><full= -title>International journal of food science &amp; technology</full-title></periodical><pages>2694-2699</= pages><volume>50</volume><number>12</number><= dates><year>2015</year></dates><isbn>1365-2621&l= t;/isbn><urls></urls></record></Cite><Cite>= ;<Author>Baran</Author><Year>2012</Year><RecNum&= gt;157</RecNum><record><rec-number>157</rec-number>= <foreign-keys><key app=3D"EN" db-id=3D"frsr5sd0eewzr7etr5rxtpa9pze9xfa2a0ve">157</key>= </foreign-keys><ref-type name=3D"Journal Article">17</ref-type><contributors><authors><= author>Baran, Eda Köse</author><author>Yaşar, Sema Bağdat</author></authors></contributors><titles&g= t;<title>Zinc and nickel determination in liquid edible oils by FAAS after the extraction</title><secondary-title>European journal of lipid science and technology</secondary-title></titles><periodical><full= -title>European journal of lipid science and technology</full-title></periodical&g= t;<pages>1320-1326</pages><volume>114</volume><n= umber>11</number><dates><year>2012</year></da= tes><isbn>1438-9312</isbn><urls></urls></reco= rd></Cite></EndNote>= [3, 16]. Moreover,= many of conventional methods employed for the sample pretreatment such as acid digestion, wet or dry ashing of oil matrix, closed-vessel, and focused open-vessel microwave dissolution, dilution as well as basic alcoholic solubilization are not recommended because of associated safety hazards, a potential risk of sample contamination, analyte losses and being time-consu= ming = [17]. In this regard, preconcentration and separation steps are required prior to analyte determination. Recently, dispersive liquid–liquid microextraction (DLLME) h= as introduced by Rezaee et al = [18] has gained increasing popularity for the trace metal ions preconcentration-separation = in food and biological samples because of its simplicity, rapidity, low cost, = low consumption of toxic organic solvents as well as the high preconcentration factor and extraction efficiency that are achieved = [19, 20]. DLLME use= s an extraction solvent, immiscible in the aqueous phase, and a disperser solven= t, miscible in both the extraction solvent and in the aqueous sample solution.= In this method, the contact area between the extraction solvent and the sample solution is extremely large, so the extraction equilibrium is reached rapid= ly. In the DLLME, the choice of the appropriate mixture of the extraction and dispersive solvents is critical for achieving high enrichment factor = [21]. Ionic liq= uids (ILs), as an alternative to traditional organic solvents in sample preparat= ion, are one of the mostly considered extraction solvents in DLLME due to their = low volatility, high viscosity, dual natural polarity, good thermal stability, = and miscibility with water and organic solvents (TSIL1,chempaper) without requi= ring a dispersive solvent = [20, 22, 23]. It has be= en demonstrated that organic analytes can be partitioned to ILs based on the hydrophobicity of the analytes and ILs, but metal ions cannot be extracted = in liquid/liquid systems owing to negligible partitioning and the tendency of metal cations to remain hydrated in the aqueous phase = [21]. Therefore= , it is necessary to use chelating agents which firstly form hydrophobic complex with metal ions, and then the formed complex extract into extraction solven= t. In recent years, task specific ionic liquid (TSIL), a new group of ionic liqui= ds, has been introduced in which thiol or urea groups are covalently attached to the cationic or ionic impart of the IL. TSIL can be used as a dispersive and extraction solvent for metal ions in DLLME method without any chelating age= nts = [23]. In the TSIL-DLLME, extraction and complexation of metal ions were done simultaneou= sly and this newly developed procedure is a very fast and easy single-step meth= od without needing chelating agents compared to the traditional DLLME method <= /span>= [24]. To date, different DLLME modes based on the ILs have been developed such as temperat= ure controlled, ultrasonic-assisted, microwave-assisted and vortex-assisted = [25]. Zhou et a= l. made the most preferred modifications in IL-DLLME which are ultrasound-assi= sted (US) and temperature-controlled (TC) techniques = [26, 27]. In TC, IL-dispersive liquid–liquid microextraction, the extraction solvent is heat= ed until it is completely solubilized in the water matrix. The heating improves the mass transfer of the analyte to the IL = [28]. In US, IL-dispersive, liquid–liquid microextraction, ultrasound and dispersive solvents are used to increase the extraction ability of ILs = [28]. The motivation behind the present work is that a great number of the TSIL-DLLME analytical procedures reported to date have dealt with water analysis or relatively simple matrices. For example, Werner developed TSIL-USA-DLLME combined with liquid chromatography for preconcentration and determination = of Cd (II), Co(II) and Pb (II) ions in tea samples = [22]. However, application of this method in edible oil samples has not been studied yet. Therefore, the main aim of the current study is to develop a simple, rapid, reliable and economic method for the determination of trace Cd2+= and Ni2+ ions in olive oil samples without chelating agents. Th= is method is based on the combination of the thermal ultrasound-assisted-task specific ionic liquid-dispersive multiphasic microextraction technique (TUS-TSIL-DMPμE) and AT-FAAS. In the present approach, two hydrophilic=  TSILs, ([CHCA] [DEA]) and [HEMIM][BF4]), were used and compared not only as an extraction solvent but also as a selective chelating agent. Experimental parameters including sample pH, amount of sorbent, sample volume, eluent ty= pe and volume, and time of ultrasound, etc., have been studied and optimized. =

=  

= 2. Experimental procedure

2.1 Apparatus

The measure= ments of Cd (II) and Ni(II) ions were performed with a spectra GBC 906 double beam atomic absorption spectrophotometer equipped with atom trap, air-acetylene flame and ultra-pulse deuterium as a background correction (AT-FAAS, GBC, Model; Plus 906, Australia). The atom trap was installed on an air-acetylene burner. A data station (AT-compatible computer) with 906 AAS operating soft= ware was utilized for collecting and storing data. For the matter of interest, t= he operating parameters were set as recommended by the manufacturer. A Cd and = Ni hollow cathode lamps as the radiation sources were used at a current of 10 = mA and 3 mA, and a wavelength of 279.5 nm and 228.8 nm, respectively, with a spectral bandwidth of 0.5 nm. The pH values of the solutions were measured = by a Metrohm pH-meter (model 744, Herisau, Switzerland) supplied with a glass-combined electrode. Phase separation was carried out by a Demerd centrifuge (model LC8-12). A Kunshan ultrasonic bath with temperature contr= ol (model KQ-100DE, Kunshan, China) was used throughout this study.

 =

 =

= 2.2 Chemical Reagents and Material

standard st= ock solutions (1000 mg L-1) of Ni (II) and= Cd (II), α- Cyano-4-hydroxycinnamic acid diethylamine ([CHCA] [DEA]) ionic liquid, acetone, sodium tetrafluoroborate (NaBF4), ethyl acetate, chloroethanol, 1-methylimidazole and all of the other chemical compounds and reagents were of analytical grade and purchased from Merck (Darmstadt, Germany). Ultra-pure deionized w= ater (DW, 18 MΩ cm-1) from Milli-Q plus water purification system (Millipore, Bedford, MA, USA) was used for preparing all aqueous solutions.= The standard and experimental solutions of Ni2+  and Cd2+  were prepar= ed daily by appropriate dilution of the stock solutions with DW. The pH adjustments of samples were made using appropriate buffer solutions includi= ng sodium acetate (CH3COONa/CH3COOH, 1-2 = mol L-1) for pH 3.8–5.8, sodium phosphate (Na2HPO4/NaH2PO4, 0.2 mol L−1) for pH of 5.8–8.0, and ammonium chloride (NH<= sub>3/NH4Cl, 0.2 mol L−1) for pH 8–10.  All the laboratory glassware and plastic tubes were cleaned by soaki= ng in 10% (v/v) nitric acid for at least 24 h and then rinsed several times wi= th deionized water and dried in a clean oven prior to use. In this study, five= olive oils (Cooking and skin)= was selected and used for investigation.

2.3. Synthe= sis of TSIL

The hydroph= ilic TSILs, (α- Cyano-4-hydroxycinnamic acid diethylamine; [CHCA] [DEA] purchased from Merck and [HEMIM][BF4] was prepared according to the synthes= is method [27]. The general procedure for synthesis of [HEMIM][BF4]  TSIL is described as follows: Fi= rst, 13.9 g (0.169 mol) of 1-methylimidazole (99 %), distilled over KOH, was slo= wly added to 15.0 g (0.186 mol) of freshly distilled 2-chloroethanol in a round-bottomed flask equipped with a magnetic stirrer and a condenser, under nitrogen atmosphere. The mixture was refluxed at 100 ºC for 4 h. After cool= ing to 70 ºC, the reaction mixture was washed four times with ethyl acetate, and then dried in vacuo at 70 ºC for 8 h. The product, 1-(2- hydroxyethyl)-3-methylimidazolium chloride ([HEMIM][Cl]), was obtained in f= orm of white crystalline solid (65% yield, 17.9 g). This compound was character= ized by 1H NMR (500 MHz, D2O, 25 °C, δ; ppm). The obtained data are here: 3.87 (3H, S, NCH3), 3.89 (2H, t, NCH2CH2OH), 4.28 (2H, t, NCH2CH2OH), 7.42 (1H, d, H-4), 7.47 (1H,= d, H-5), and 8.71 (1H, S, H-2).

Then 30.0 g (0.185 mol) of [HEMIM][Cl] was reacted with 26.4 g (0.24 mol) of NaBF4= in acetonitrile solvent at room temperature for 48 h, under nitrogen atmosphere. The reaction mixture was then cooled to 18 ºC overnight and filtered through a short column of Celite to remove NaCl. The solvent was removed using a rotary evaporator, and the residual chloride test (a concentrated AgNO3 solution test) performed on product was negative. The product, 1-(2-hydroxyethyl)-3-methylimidazolium tetrafluorobo= rate ([HEMIM][BF4]), was obtained as a viscous material (62% yield). Karl Fischer test showed < 100 ppm of water and the absence of chloride ion confirmed= the product purity (> 99.5 %). This compound was also characterized by 1H NMR (500 MHz, D2O, 25 °C, δ; ppm): 3.83 (3H, S, NCH3), 3= .87 (2H, t, NCH2CH2OH),4.24 (2H, t, NCH2CH2OH), 7.38 (1H, d, H-4), 7.43 (1H, d, H-5), and 8.66 (1H, S, H-2).

 

 

2.4.General procedure

In this procedure, [CHCA] [DEA] and [HEMIM][BF4] were used as hydrophilic task-spec= ific ionic liquids (TSILs) to complex the ultra-trace amounts of = in Olive oil samples and extract them. The TUSA-DMPμE of metal ions was performed as follows: In a 100 mL glass centrifuge tube with a conical bottom, 26.0 g (20 mL) of olive oil sample containing Cd and Ni ions was diluted with n-hexane= up to 40 mL. Then, the mixture of 0.25 g of the mentioned above TSILs and 0.5 = mL of acetone (as a dispersive solvent) which was diluted with DW up to 5.0 mL= was prepared and then, the pH adjusted between 2 to 10 by buffer solution. Afte= rwards, the mixture was injected rapidly into 40 mL of edible oil samples with HPLC autosampler syringe (5 mL, gastight, CTC-PAL, Trajan, AUS) and stirred for 5 min at 85 ºC. The cloudy phases were then separated by centrifuging of the turbid solution for 4 min at 4000 rpm (25oC). The Cd/Ni complexes were settled down at the bottom of the conical tube into droplets of TSILs.= The upper phase of the sample (edible oil) was removed with a pipette, the metal complexes was  back extracted from = TSIL with HNO3 ( 0.2 mL, 0.5 M) and finally the concentration of = in the resulting solution was determined by AT-FAAS after dilution with deioni= zed water up to 1 mL. For validation, I mL of sample oils was digested with microwave accessory for 1 hour (UV, 5:1 mL; HNO3/H2O<= sub>2, 220oC) and concentration of Ni and Cd ions determined by F-AAS/ET-AAS/ICP-MS(Fig. 1).

 Fig. 1. General procedure for extraction of Ni/Cd from olive oil by TUSA-DMPμE

 =

3. Results and Discussion

3.1. Effect= of sample pH

Complexation was strongly conditioned by the pH of the solutions. In the present work, t= he solution pH affected the extraction process through the functional group moieties of the TSIL. The influence of sample pH on the complex formation a= nd the extraction of Ni (II) = and Cd (II) ions with [CHCA] [DEA] and [HEMIM][BF4] TSILs was separately investigatedat different pH values from 2 to 10 for 40 mL buffered diluted = olive oil samples, according to the general procedure.  The results were depicted in figures 2a = and 2b. Obviously, the maximum extraction efficiencies for Ni (II) and Cd (II) ions = were obtained with [CHCA] [DEA] TSIL in pH range of 6-8, and then the recoveries were decreased by increasing of pH (Fig. 2a). Whereas, by using [HEMIM][BF4= ] = quantitative recoveries were less than 40-70% at pH 7.5-10.

=  

=  

=  

= .

 

F<= /p>

 

= Fig. 2a. Effect of pH on extraction of Ni (II) and Cd (II) ions in olive oil with = = [CHCA] [DEA] by TUSA-DMPμE.

= Fig. 2b. Effect of pH on extraction of Ni (II) and Cd (II) ions in olive oil with = = [CHCA] [DEA] by TUSA-DMPμE.

=  

3.2. Effect= of sample volume

The sample volume is one of the = most important parameters to be studied by TUSA-DMPμE method, since it determines the sensitivity and enhancement of the technique. The effect of sample volume was studied in the range of 5–40 mL for 5 - 100 μg L−1= of standard solution of Ni and Cd (Fig. 3).

Fig. 3. Effect of sample volume on extraction of Ni (II) and Cd (II) ions in olive oil = by TUSA-DMPμE.

3.3.Effect of TSIL amount on Ni and Cd extraction

The amounts= of ILs on the extraction efficiencies of Ni/Cd in Olive oil by TUSA-DMPμE method was studied and optimized. For this purposed, the range of 0.01-0.1 = g of [CHCA] [DEA] and [HEMIM][BF4] as a TSIL was used in human biological samples and standard solution containing; 5-100 μg L−1 = of Ni (II) and Cd(II) (Fig. 3)= = . = quantitative recoveries were obtained with 20-40 mg of [CHCA] [DEA] as a 98% recovery. Therefore, in order to achieve a suitable preconcentration, 50 mg of [CHCA] [DEA] was chosen as optimum leading to a final IL for blood/urine and stand= ard solution analysis. Also, the effect of IL used on the recovery efficiencies= of Ni/Cd ions with TSIL of [HEMIM][BF4] was investigated by TUSA-DMPμE method. The results showed us, the maximum recoveries of Ni/Cd in ol= ive oils were less than 64% by using = [HEMIM][BF4], therefore the [HEMIM][BF4] had lower recovery as compared to [CHCA] [DEA]. = Moreover, by increasing the ultra-sonication time = up to 60 min and 150 mg of [HEMIM][BF4], the almost 73% of Ni/Cd ions from olive oils can be extracted b= y [HEMIM][BF4] in standard solution (Fig. 4). So, the recovery extraction of ions with [HEMIM][BF4] cannot be increased by long time or amount of IL.  

 

Fig. 4. Effect of amount of TSILs on extraction of Ni (II) and Cd (II) ions in olive oil = by TUSA-DMPμE

 

3.4.Effect of ultra-sonication time for Ni and Cd extraction

The ultra-s= onication time during the extraction process can improve the extraction recovery sinc= e it enhances the complexation of Ni/Cd ions to TSIL. Based on procedure, kind of TSILs are the most important factors for sonication time by TUSA-DMPμE method. Therefore, the effect of sonication type, shaker tube or ultrasound bath, on the recovery efficiencies of Ni/Cd ions in olive oils was examined= by [CHCA] [DEA] and [HEMIM][BF4]. The results showed, the maximum recovery was obtained using sonication at 5 min. The optimization of sonication time inc= reased the extraction recovery and decreased the time and IL mass. This fact can be related to the large contact area between dispersion of TSILs with olive oil samples. In this study, ultrasound assisted extraction times ranging from 1= to 25 min were evaluated. Therefore, the ultrasonic time of 5 min was selected as optimum time (Fig. 5).

Fig. 5. Effect of shaking time on extraction of Ni (II) and Cd (II) ions in olive oil = by TUSA-DMPμE

3.5.Interference study

=  The determination of Ni/Cd ions in different olive= oil samples in the presence of interfering matrix ions was examined. In order to get the acceptable analytical technique by TUSA-DMPμE= ̶ 100 µgL-1 of Ni2+ and Cd2+ in optimized conditions. Interfering ions concentration cau= sing less than ± 5% deviation in the recovery of Ni(II) and Cd(II) was considere= d as the tolerance limit. Based on the results, the presence of interfering ions= has no considerable effect on the recovery efficiencies of Ni(II) and Cd(II) in=  olive oil samples. 

3.6.Effect of Temperature on Ni and Cd extraction

The temperature has a critical r= ole in extraction recovery of Ni(II) and Cd(II) in  olive = oil samples  by = TSILs. As evaluation of TSILs, the effect of temperature was studied and optimized between 20─90 OC. The results showed us, the extraction efficiency of Ni(II) and Cd(II) =  by [CHCA] [DEA] and [HEMIM][BF4]was depe= nded to temperature. The results showed us, the optimized temperature was obtain= ed between 40- 60 oC. In optimized temperature, the extraction ions= in olive oils with [CHCA] [DEA] was more than [HEMIM][BF4]. =

 

 Be= cause of high viscosity of TSILs, the direct injection of ILs into = AT-FAASNi(II) ions into the aqueous phase. Different mineral acids such as HCl, HNO<= sub>3,CH3COOH and H2SO4 (0.1‒0.5 M) were studied for Ni/CdNi/Cd ions from the olive oil samples before diluted with DW up to  1 mL = .

 

3.8.Validat= ion of Method

= The analytical characteristics of the developed= = TUSA-DMPμE method at the optimum conditions were show= n in table 1. After sample preparation, Ni/Cd in olive oils and standard samp= les was determined by proposed method. The olive oils samples as a real sample was used for determination of Ni/Cd as the ave= rage of three separate determinations. The accuracy of the results was verified by analyzing the spiked samples with known concentration of Ni/Cd (II) in olive oils<= /span> samples (Tables 2). =  Based on the obtained results, a good agreement was obtained between the added and measured Ni/Cd amount, which confirms the accuracy of the procedu= re and its independence from the matrix effects.= The recoveries of spiked samples = demonstrated that the developed method was satisfactory for Ni/Cd analysis. In order to validate the method described, certified reference materials in olive oils = (CRM, A-D) which was determined with ET-AAS after microwave digestion with pure a= cid and H2O2, were analyzed by proposed method (Table 3).= = Analytical results of the CRM samples were satisfactorily in agreement with the certif= ied values. Moreover, a good agreement was obtained between added and found values of the Ni/Cd ions in spiked samples by = CRM samples.

 

 

=  

Table 1. Analytical characteristics of the developed= = TUSA-DMPμE method at the optimum conditions by = = [CHCA] [DEA].=

Metal ions

Sample volume (mL= )

Linear range=

(𝜇g L−1)

Regression coefficient (R2)

LOD a = (n =3D 10) (𝜇g L−1<= /sup>)

RSD b = (n =3D 10)      (%)

PF c

 

Cd2+ <= o:p>

<= /o:p>

0.9996=

0.6

4.4%

19.6

 

Ni2+

20

5.0- 415<= /span>

0.9998

1.3

5.1%

19.3

 

a Limit of detection , b Relative stand= ard deviation, c  Preconce= ntration factor

&nb= sp;

&nb= sp;

&nb= sp;

&nb= sp;

&nb= sp;

&nb= sp;

&nb= sp;

&nb= sp;

Table 2<= /span>. Analytical results for determination of analytes in spiked olive oil samples.

  Recovery (%)

(_= 6;g L-1)

20.0

a = Mean of three determinations ± confidence interval (P =3D 0.95, n =3D5), b Relative standard deviation.

 =

 =

Table 3. Validation of developed TUSA-DMPμE = method with Standard Reference Material (CRM).

 

sample

Certified a

(μg L-1= )

Added

(μg L-1= )

Found b<= /span>

(μg L-1= )

Recovery

(%)

 

Cd(II)

Ni(II)

Cd(II)

Ni(II)

Cd(II)

Ni(II)

Cd(II)

Ni(II)

A

4.5

10.5

5

10

9.3

19.9

97.9

97.1

B

12.8

45.6

10

50

22.1

94.4

96.9

98.7

C

55.2

117.9

50

100

99.9

209.7

94.9

96.2

D

88.6

267.9

100

200

191.1

460.2

101.0

98.3

a Certified by ETAAS after digestion with micro wave of oils

b Mean of three determinations ± confidence interval (P =3D 0.9= 5, n =3D5),

 

4. Conclusions=

A novel, reliable and efficient method was used for preconcentration, separat= ion and determination of trace Ni/Cd in olive oil samples by TUSA-DMPμE procedure. The proposed method was developed based on hydrophil= ic TSILs (α- Cyano-4-hydroxycinnamic acid diethylamine; [CHCA] [DEA] and 1-(2-Hydroxyethyl)-3-methylimidazolium Tetrafluoroborate; [HEMIM][BF4]) as a complexing and extracting solvent which was coupled by AT-FAAS technique. Finally, the newly developed method was low interference, easy usage for sample preparat= ion in olive oil samples and also provides low LOD, and RSD values as well as g= ood PF values and quantitative recoveries for Ni/Cd extraction in difficulty ol= ive oil matrix (>95%).= = = Therefore, the proposed method can be considered as simple and applied sample preparat= ion techniques with TSILs for Ni/Cd separation / determination in olive oil sam= ples by AT-FAAS.

= 5. Acknowledgements

=             The authors wish to thank the Iranian Research Institute of Petroleum Industry (RIPI) for this work (No grant or fund by RIPI).<= /p>

=  

= 6. References

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[16] F. Tokay, S. Bağdat, Spectrometric determinatio= n of iron and copper in vegetable oils after separation with Schiff base impregn= ated silica gel column: A simple approach for eliminating the high organic matri= x, Int. j. food sci. technol., 50 (2015) 2694-2699.

[17] F. Tokay, S. Bağdat, Determination of iron and copper in edible oils by flame atomic absorption spectrometry after liquid–liquid extraction, J. Am. Oil Chem. Soc., 92 (2015) 317-322.<= /a>

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[19] I. López-García, Y. Vicente-Martínez, M. Hernández-Córdoba, Determination of cadmium and lead in edible oils by elec= trothermal atomic absorption spectrometry after reverse dispersive liquid–liquid microextraction, Talanta, 124 (2014) 106-110.

[20] H. Shirkhanloo, A. Khaligh, H.Z. Mousavi, M.M. Eskandari, A.A. Miran-Beigi, Ultra-trace arsenic and mercury speciation and determination in blood samples by ionic liquid-based dispersive liquid-liqu= id microextraction combined with flow injection-hydride generation/cold vapor atomic absorption spectroscopy, Chem. Papers, 69 (2015) 779-790.=

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[27] Q. Zhou, X. Zhang, J. Xiao, Ultrasound-assisted ionic liquid dispersive liquid-phase micro-extraction: A novel approach for the sensitive determination of aromatic amines in water samples, J. Chromatogr.= A, 1216 (2009) 4361-4365.

[28] J. Zhang, H. Gao, B. Peng, S. Li, Z. Zhou, Compariso= n of the performance of conventional, temperature-controlled, and ultrasound-assisted ionic liquid dispersive liquid–liquid microextraction combined with high-performance liquid chromatography in analyzing pyrethroi= d pesticides in honey samples, J. Chromatogr. A, 1218 (2011) 6621-6629.

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The use of = zinc metalloporphyrin grafted<= span style=3D'font-size:12.0pt;font-family:"Times New Roman","serif";mso-ascii-t= heme-font: major-bidi;mso-hansi-theme-font:major-bidi;mso-bidi-theme-font:major-bidi'> magnetic nanoparticles for the removal of sulfate ions from wastewaters

Tahereh Poursaberia and Ali Akbar Miran Beigib,*

Analytical Research Group, Research Institute of Petroleum Industry, Tehran, Iran=

b= Oil Refining Research Division, Research Institute of Petroleum Industry, Tehra= n, Iran

Correspondi= ng autho;: Tel: +98-21-48255042, Fax: +98-21-44739738, E-mail: = amiranbeigi@yahoo.com

miranbeigiaa@ripi.ir

=  

Abstract

This study investigates an application of zinc metalloporphyrin grafted Fe3O4 nanoparticles as a new adsorbent for re= moval of sulfate ions from wastewaters. The modification of magnetite nanoparticl= es was conducted by 3-aminopropyltriethoxysilane followed by zinc (II) porphyrin in order to enhance the removal of sulfate ions. Moreover, Fourier Transform Infrared Spectrosc= opy (FT-IR)= , X-ray diffraction (XRD), Transmiss= ion Electron Microscopy (TEM) and Scanning Electron Microscopy (SEM) were used = to characterize the synthesized nanosorbent. The effect of important experimen= tal factors such as pH, contact time, sorbent dosage and some co-existing anions present in aqueous solutions were investigated. Under optimal conditions (i.e. contact time: 30 min, pH:= 6.5 and nanosor= bents dosage: 100 mg) for a sulfate sample (50 mL, 50 mgL-1 ), = the percentage of the extracted sulfate ions was 94.5%. Regeneration of sulfate adsorbed material could be possible by NaOH solution and the modified magnetic nanosorbent exhibited good reusability. The proposed system can provide a = fast and efficient removal of the sulfate ion by using just an external magnetic field. In a= ddition, the competitive adsorption tests verified that this system has good adsorption selectivity for sulfate ion. Finally, the synthesized sorbent was successfully applied for treati= ng a wastewater sample from glass industry.

 

Keywords: Magnetic nanoparticles; water samples;= = Sulfate removal, Zinc (II) porphyrin;= = Nanosorbent.

 

1. Introduction

Sulfate = is a common constituent of many natural waters and wastewaters [1], which it is prese= nt as a dissolved compound in seas and oceans or as insoluble salt (e.g., gypsumlayers). Industrial wastewaters are respons= ible for most anthropogenic emissions of sulfate into the environment. Domestic sewage typically contains between 20 and 500 mg L<= sup>-1 sulfate [2] while certain industrial effluents may contain several thousands of milligrams per liter. The main source of sulfate in the labora= tory wastewaters is the use of sulfuric acid in many routine chemical analyses. Sulfur compounds are also present in wastewaters used in the research activities such as those from the pulp and paper industry, the food process= ing industry, and the photographic sector, among others [3].<= /p>

The dama= ge which is caused by sulfate emissions is not direct, since sulfate is a chemically inert, non-volatile, and non-toxic compound. However, high sulfate concentrations can unbalance the natural sulfur cycle [1, 2]= , and also endanger human health when excessive ingestion. The accumulatio= n of sulfate-rich sediments in lakes, rivers and sea may cause the release of to= xic sulfides that can provoke damages to the environment [4].= The World Health Organization (WHO) has established the maximum tolerable level of sulfate in water as 500 mg L-1[5]= . The current U.S. EPA national Secondary Maximum Contaminant Level for sulfate, based on organoleptic effects, is 250 mg L-1 [6].=

A number= of methods are currently used to promote the removal of dissolved sulfate. They include reversed osmosis, electrodialysis, or nanofiltration, which are expensive, can b= e poisoned by impurities, and require a post-treatment of the brine [2]. In addition, established methods for removal of sulfate from industrial effluents include chemical precipitation, biological treatment and adsorption technologies. Chemical precipitation, for example, to add barium= or calcium salts, is rapid and effective, but it may produce another kind of pollution and secondary treatment for solid phase is necessary [1]. Removal= of sulfate by sulfate-reducing bacteria is another alternative; however, the e= fficiency of biological treatment is susceptible to environmental conditions because = the growth requirements of this microbial are relatively rigid [7]. Adsorption method may be preferred for their rapid and high selectivity, and sulfur ca= n be recovered.

More recently, the u= se of NPs for sample extraction is gaining researchers interest [8-16]. Compar= ed with micrometer-sized particles used in the SPE, the NPs offer a multitude = of benefits that make it a better choice. They have a significantly higher surface area-to-volume ratio and a short diffusion route, resulting = in a higher extraction capacity; rapid dynamics of extraction and its higher extraction efficiencies [17, 18]. Also, the main advantage of magnetic nanoparticle= s is their separation by application of external magnetic field. In addition, c<= /span>ombination of the molecular scale recognition and nano scale surface modification creates a powerful tool for the development of selecti= ve separation systems. Depending on the usage, surface modification can be performed by physical / chemical sorption or surface coating of specific ligands [19-23].

Supramolecular chemistry of anio= ns has been widely studied and created a lot of artificial anionophores [24, 25] among them; in addition, metalloporph= yrins (MP) are well known for their ability as anion carriers. The coordinating s= ite of MPs is an acidic metal and the anion recognition is the result of specif= ic anion coordination with this central metal ion = [26]. Previously, it has been reported by us that the application of magnetic nanoparticles modified by Zr(IV) porphyrin and oxovanadium(IV) porphyrin for removal of  fluoride and nitr= ate respectively [27, 28].

Herein, we have combined the sul= fate selectivity of zinc (II) porphyrin with the advantages of magnetic nanoparticles has been combined by us to fabricate a new kind of magnetic nanosized sorbent with high affinity toward sulfate ion and good magnetic separability. The effect of pH, contact time, nanosorbent dosage and some co-existing anions present in aqueous solutions on sulfate removal efficien= cy were investigated.

 

2. Experimental procedure

2.1. Materials=

Ferric chloride hexahydrate, ferrous chloride tetrahydrate, APTES, dichloromethane (DCM), N,N-dimethylformamide (DMF), dicyclohexylcarbodiimide (DCHC), methanol, ammonia, sodium salts of indicated anions were all analyt= ical grade from Merck Chemical Co. Meso<= /i>-Tetrakis (4-carboxyphenyl) porphyrinato zinc (II) (ZnTCPP) was obtained by metallati= on of the free ligand porphyrin tetrakis (4-carboxyphenyl) porphine H2 (TCPP) (Aldrich) according to the methods described in the literature [29]. Schematic of the Zinc (II) porphyrin is shown i= n Fig. 1.

Fig. 1. Schematic representation of the Zinc (II) porphyrin used in this work.

 

 

 

2.2. Equipments

The morphology and dimension of = Fe3O4/APTES/ZnTCPP were examined by transmission electron microscope (TEM) using Zeiss 900 TEM= at a voltage of 80 kV. Size and morphology of the nanosorbent were investigate= d by Tescan Mira LMU SEM. The phase purity was characterized by X-ray powder diffraction (XRD) (PW-1840 diffractometer from Philips Co) using Cu-Kα radiation (l=3D1.54178 = Å). Ion chromatography (IC) determinations were carried out in a S 1122 Sykam i= on chromatograph. In addition, pH measurements were performed with a Metrohm 691 pH meter. FTIR spectra were recorded on a Vertex 70 FT-IR spectrophotometer from Bruker Co. using standard KBr pellet technique.=

 

2.3. Sorbent preparation

3O= 4 nanoparticles

The chemical co-precipitation method was used in the preparation of the Fe3O<= sub>4 NPs [30]. First, for preparing a stock solution, 10.4 g of FeCl3= ·6H2O, with 4.0 g of FeCl2·4H2O and 1.7 mL of HCl (12 mol L<= sup>-1) were mixed and dissolved in 50 mL of deionized water in a beaker which was = then degassed using nitrogen gas for 20 min before use. Simultaneously, 500 mL of 1.5 mol L -1 NaOH solution was degassed (for 15 min) and heated = to 80 °C in a reactor. The stock solution was then added dropwise using a drop= ping funnel for 30 min under nitrogen gas protection and vigorously stirring (10= 00 rpm) using a glassware stirrer. During the whole process, the solution temperature was maintained at 80 °C, and nitrogen gas was used to prevent t= he intrusion of oxygen. After the reaction, the obtained Fe3O4= NPs precipitate was separated from the reaction medium by using a magnetic field, and then washed four times with 500 mL of deionized water. Fin= ally, Fe3O4 nanoparticles were dried.

 

2.3.2. Modification of Fe<= span class=3DJPP08titleC>3O4 nanoparticles with APTES groups<= /span>

Fe3O4/APTES nanoparticles were synthesized via the reaction of APTES and hydroxyl group= s on the surface of magnetite. 2.3 g of Fe3O4 nanoparticles were dispersed in 100 mL of ethanol by sonication for about 1 h. Then under continuous mechanical stirring, 20.34 mL of APTES was added dropwise to the suspension. The reaction mixtu= re was kept at 40 °C for 20 h under nitrogen atmosphere with vigorous mechanical stirring. The prepared APTES nanopartic= les were collected with a magnet, and washed with ethanol and deionized water. Finally, Fe3O4/APTES nanoparticles were dried under vacuum at 50 ◦C.

 

2.3.3. Grafting of Zn (TCPP) groups at t= he surface of Fe3O4/APTES

Functionalization of the modified nanoparticles was carried out= by suspension of Fe3O4/APTES= and DCHC in DMF under nitrogen [31]. Then Zn (TCPP) was dissolved in DMF and ad= ded to the suspension. The mixture was refluxed at 140 = C for 8 h. In order to prevent the presence of vola= tile dimethylamine, a product of DMF decomposition, a high flux of nitrogen is recommended. After reaction, the solid Fe3O4/APTES/Zn (TCPP) nanoparticles were separated magnetically and washed with DMF, CH2Cl2, and methanol to remove non-covalently bonded porphyrins from Fe3= O4/APTES. A scheme of the magnetite synthesis and surface modification process is sho= wn in Fig. 2.

Fig. 2. A scheme of the magnetite synthesis and surface modification process using APTES followed by metalloporphyr= in insertion.

 

2.4. Removal of sulfate ions by = Fe3O4/APTES/Zn (TCPP)

Adsorption of sulfate by Fe3O4/APTES/ZnTCPP h= as been studied in batch experiments. A known amount of nanosorbent (100 mg) w= as mixed with 50 ml of 50 mgL-1 aqueous sulfate solution and was sh= aken at room temperature with 200 rpm for a 3= 0 min= . The sor= bent was separated before measurement. The residual sulfate concentration of aqu= eous solution was determined by ion chromatography. The sulfate removal efficien= cy was calculated according to Eq. (1):

                                                     <= /span>      (1)

where Co and Cr<= /sub> are the initial and final concentrations of the sulfate ion before and after the sorption, respectively.

 <= /span>

3. Results and discussion

3.1. Characterization of the synthesized nanosorbent

3.1.1. X-ray powder Diffraction (XRD)

XRD analysis was used to investigate the crystalline structure= of synthesized nanoparticles (Fig. 3). The Joint Committee on Powder Diffraction Standards (JCPDS) reference pattern of magnetite (No. 19-629) was used for comparison. As seen, the XRD pattern of magnetite nanoparticles was in good agreeme= nt with that of the standard Fe3O4 structure. The same set of characteristic = peaks were also observed for Fe3O4/APTE= S and = Fe3O4/APTES/ZnTCPP, indicating the stability of the crystalline phase of Fe3O4 nanoparticles during functionalization and revealed that the APTES coating and metalloporphyrin graft= ing did not result in the phase change of Fe3O4.

<= span style=3D'font-size:12.0pt;font-family:"Times New Roman","serif";mso-ascii-t= heme-font: major-bidi;mso-hansi-theme-font:major-bidi;mso-bidi-theme-font:major-bidi; mso-bidi-language:AR-SA'>Fig. 3. XRD patterns of Fe3O4 (a), Fe3O4/APTES (b), and Fe3O4/APTES/Zn(TCPP) (c).

The Single formula given by Debye Scherre (Eq. 2) can be used to calculate the crystal= line size from the available XRD data. The average size of the Fe3O4 nanoparticles using Debye Scherre was about 27 nm.

 D =3D Kλ= ; / βcos(θ)   (2)<= /span>

 

3.1.2. Scanning Electron Microscopy (SEM= ) 

The particle size and morphological characteristics of the magnetite nanoparticles, before and after surface modification, were investigated by using SEM (Fig. 4). As can be seen from Fig. 4a, the bare magnetic nanoparticles show spherical shape with some aggregates due to the lack of any repulsive force between the magnetite nanoparticles. This is ma= inly due to the nano-size of the Fe3O4, which is about 27 = nm. After APTES introduction (Fig. 4b), particles with an approximate spherical shape and an average diameter of 30 nm were observed. This may be considere= d as indirect evidence that the magnetite core of the APTES magnetite particles consisted of a single magnetite crystallite with a typical diameter of 27 n= m; and that the difference of 3 nm corresponds the APTES-coating. After metalloporphyrin immobilization(Fig. 4c), the dispersion of particles were improved greatly. It can easily be explained by the electrostatic repulsion force and steric hindrance between the metaloporphyrin on the surface of Fe= 3O4 nanoparticles. Fig. 4c shows that the morphology of the functionalized magn= etic nanoparticles almost maintains the original state.

3.1.3. Transmission Electron Microscopy (TEM)The introduction of = = Zn (TCPP) into the magnetite nanoparticles was evi= dent from TEM results. The dark nano-Fe3O4 cores surrounde= d by a grey shell could be observed in Fig.5. Moreover, the particles hav= e special characteristics such as an approximate spherical shape and an average size of 45 nm, whi= ch their characteristics complement the SEM data.

 

 

Fig. 4. SEM images of Fe3O4 (a), Fe3O4/APTES (b) and Fe3O4/= APTES/Zn(TCPP) (c).

<= span style=3D'font-size:12.0pt;font-family:"Times New Roman","serif";mso-ascii-t= heme-font: major-bidi;mso-hansi-theme-font:major-bidi;mso-bidi-theme-font:major-bidi'>= Fig. 5. TEM micrograph of Fe3O4/APTES/Zn (TCPP) nanosorbents.

 

3.1.4. FT-IR spectrum

FT-IR is a reliable technique for the monitoring of the variations in the functio= nal groups. Thereofre, the structures of the synthesized nanosorbent (Fe3<= /sub>O4/APTES/Zn (TCPP)) were characterized by FTIR spectroscopy (Fig. 6). Fe–O stretching band at 580 cm1 is the characteristic peak of magnetite. <= span style=3D'font-size:12.0pt;font-family:"Times New Roman","serif";mso-ascii-t= heme-font: major-bidi;mso-hansi-theme-font:major-bidi;mso-bidi-theme-font:major-bidi'>= Moreover, absorption bands at 2925 and 2860 cm1 assigned to stretching vibration of C–H bond of the propyl amine group. The silica netw= ork adheres to the particle surface via Fe–O–Si bond. The introduction of APTES to the surface of = Fe3O4 nanopartic= les was confirmed by the bands around 1012 and 1115 cm-1 from the SiO–H and Si–O–Si groups. A band at 3430 cm-1 = N–H stretching vibration. A peak at 1647 cm= 1 relating to the amide group stretching ban= d= , which proves that the metalloporphyrin can be covalently attached to the amine groups of APTES through the formation of a stable amide bond. The spectrum also showed the C=3DC stretching vibrations of carbon-carbon bonds of the aromatic ring about 150= 0 cm1.

 

<= span style=3D'font-size:12.0pt;font-family:"Times New Roman","serif";mso-ascii-t= heme-font: major-bidi;mso-hansi-theme-font:major-bidi;mso-bidi-theme-font:major-bidi; color:black;mso-bidi-language:AR-SA'>Fig. 6. FTIR spectra of Fe3O4/APTES= /Zn (TCPP) nanoadsorbents.

3.2. Adsorption experiments=

3.2.1. Optimization of the parameters

3.2.1.1. Effect of the solution pH

It is well known that pH is one = of the most important factors which affect the sorption process. Experiments w= ere performed to find the optimum pH on the sorption of sulfate ions onto propo= sed nanosorbents using different pH values changing from 4.0 to 9.0. =

As presented in Figure 7, while = the sulfate removal depends on the pH of the sample, there is only a slight variation of the sulfate removal percentage with the pH values in the 6.0 – 7.0 pH range= . In the acidic region the sulfate removal is decreased as a result of partial demetallation of the metalloporphyrin complex during the contact with the l= ow pH test solution [32, 33]. At high pH values, sulfate and OH- io= ns are in competition to coordinate to the central metal ion (Zinc) of the porphyrin and therefore the sorption of nitrite ions is decreased [34]. The= refore, pH=3D6.5 was selected for all subsequent experiments.

 

Fig= . 7. The pH influence on the removal efficiency of sulfate (amount of adsorbent:100 mg; sulfate concentration: 50 mg L−1).<= /span>

3.2.1.2. Effect of the contact time

Contact time studies were performed to obtain the optimum time with the maximum amo= unt of sulfate removed. The adsorption of sulfate onto nanoadsorbents was monit= ored for 120 min. Sulfate was adsorbed onto nanosorbents quickly, and equilibrium was achieved within 30 min and thereafter remains constant (Fig. 8).= = Therefore, the time of 30 min was chosen as optimum value for all subsequent experimen= ts.

 

Fig. 8. Effect of contact time on the adsorption of sulfate by modified nanosorbent= (pH of the solution: 6.5, amount of adsorbent: 100 mg; sulfate concentration: 5= 0 mg L−1).

 

3.2= .1.3. Effect of the adsorbent dosage

= To find the optimum amount of nanosorbents nanosorbent= s. = The sulfate removal efficiency as a function of nanosorbents dosage is presented in Fig. 9. Moreover, it is evident that the percent of sulfate removal increased with the increase of the sorbent dosage which is due to t= he fact that a greater amount of sorbent implies a greater amount of available binding sites. As seen in Fig.9, the percent removal reached steady state v= alue after 100 mg of Fe3O4/APTES/ Zn (TCPP) nanosorbents for 50 mL of aqueous solution containing 50 mg L-1 sulfate ion. Therefore, in all the experiments, 0.1= g of the nanoadsorbents was fixed as the optimum dose.=

Fig. 9. Effect of nanosorbents dosage on the sulfate removal<= span style=3D'font-size:12.0pt;font-family:"Times New Roman","serif";mso-ascii-t= heme-font: major-bidi;mso-hansi-theme-font:major-bidi;mso-bidi-theme-font:major-bidi'>= by modified nanosorbent (pH of the solution: 6.5, contact time: 30 min, sulfate concentration: 50 mg L−1).

 

3.2= .2. Removal studies<= /span>

3.2= .2.1. Removal of sulfate from spiked sample

 In order = to evaluate the performance of the synthesized nanosorbent for sulfate removal, solid-phase extraction was used under optimal conditions. The deionized wat= er was spiked with sulfate ion to make a 50.0 mg L1 solution. The batch adsorption experiment was carried out on 50 mL = of this spiked sample under optimal conditions; i.e. contact time: 30 minutes,= pH=3D6.5 and sorbent dosage: 100 mg. It was found that the sulfate content decreased from 50.0 mg L−<= /span>1 to 2.75 mg L−<= /span>1 (94.5 ±= 2.7% removal efficiency, (n=3D5)).

3.2.= 2.2. Effect of co-existing anions

 Depending on the water source, more than one anion might be present. By considering the competition for the binding sites betw= een sulfate ions and such anions, they may affect the extraction efficiency of the prop= osed nanosorbent and might interfere with the removal efficiency of sulfate. In = due course, prior to the application of proposed method on real samples, it is = essential to investigate the effect of some of the interfering ions on the recovery percentage of sulfate; therefore, the adsorption of sulfate ion is tested in the presence of spiked known amounts of interfering ions. The tolerance lim= it was defined as the amount of the foreign ion causing a change of ±5% in the removal efficiency. As seen from Fig. 10, the removal percentage of sulfate= was remained within the tolerance limit in the presence of fifty-fold of nitrite and nitrate and one hundred-fold of fluoride, chloride and bromide concentr= ations. These experimental results indicated that the method has a good tolerance toward matrix interferences.

 

 

            Fig. 10. Effect of co-existing anions on removal efficiency of a 50 mg L1 sulfate ion.

 

3.2.2.3. Regeneration of the us= ed sorbent<= /span>

 In the evaluation of the performance of = the sorbents, regeneration is an important factor to make an economic process. = Moreover, in this work, NaOH was chosen as the stripping reagent for the recovery of = sulfate ions from the adsorbents. The concentration of the NaOH solution was optimi= zed, and the results indicated that the highest recovery was obtained by using N= aOH 0.1 M solution (Fig. 11).

= Fig. 11. The effect of NaOH concentration= as desorbing eluent on the recovery percentage of sulfate ion.

 

Regeneration performance of Fe3O4/APTES/ZnTCPP was tested for repeatedly use in practice applications. The spent Fe3O4/APTES/ZnTCPP was immersed in 10 ml 0.1 M NaOH solution and shaken for 30 min to desorb t= he loaded sulphate ions. Then the exchanger was separated from the NaOH soluti= on with aid of magnet and washed with deionized water until the eluent was up = to a neutral pH.

 

3.2.= 2.4. Reusability of the recycled sorbent=

After the first regeneration, nanosorbent was used in the followed adsorption test to record its sulphate adsorption efficiency again. This adsorption and desorption cycle was repeated five times. As seen in Fig.12, after four sorption–desorption cycles, the efficiency of nanosorbent for the sulfate removal was not significantly reduced (not more than 5%), but at fifth run,= an 8% decrease in its performance was observed; therefore, the desorption limit for sulfate was four cycles. It could be concluded that the chemical bonding between Zn porphyrin group and magnetite plays the major role in retaining = the capacity of the Fe3O4/APTES/Zn (TCPP) nanosorbents. <= o:p>

Fig. 12. The removal efficiency after fi= ve repetition usage on proposed nanosorbents.

 

3.2.2.5. Removal of sulfate fr= om real sample

Considering the practical applicabilit= y of proposed nanosorbent for removal of sulfate from real samples, it was also tested with wastewater obtained from glass industry (Kaveh glass industry group, Saveh, Iran). The detailed characteristics of the wastewater are presented in Table 1. As can be seen, the untreated wastewater had sulfate concentration of 108±15 mg L−1. Therefore, = removal experiments were performed by using 200 mg of nanosorbent at pH=3D6.5 and 3= 0 min for contact time. It was found that the sulfate content decreased to 10±2 mg L1 (90.7 ±= 2.4% removal efficiency, (n=3D3)).

<= span style=3D'font-size:12.0pt;font-family:"Times New Roman","serif";mso-ascii-t= heme-font: major-bidi;mso-hansi-theme-font:major-bidi;mso-bidi-theme-font:major-bidi; color:black;mso-bidi-language:AR-SA'>Table 1: The characteristics of glass industrial wastewat= er used in this study.

Anions

Value (mg L-1)<= /p>

Chloride

228±19

Fluoride

35.5±1.2

Nitrate

8.52±0.6

Sulphate

108±15

Bromide

0.06±0.004

Nitrite

0.12±0.006

 

4. Conclusions=

In this paper, Zinc (II) metalloporphyrin grafted Fe3O<= sub>4 nanoparticle as a new and powerful sorbent for the removal of sulfate ions from aqueous media is introduced. Moreover, the sorbent showed a good efficiency in sulfate extraction and a high selectivity toward the target anion. In addition, the advantage of this pro= duct is its ease of separation by an external magnetic field and possibility of simple recovery after washing with basic aqueous solution. Finally, the rec= overy of sulfate ion could be achieved, and the reuse of the sorbents is possible= .

 

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