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Article

Detection and Characterization of TiO2 Nanomaterials in Sludge from Wastewater Treatment Plants of Chihuahua State, Mexico

by
Juan Reyes-Herrera
1,
Damaris Acosta-Slane
2,
Hiram Castillo-Michel
1,
Ana E. Pradas del Real
3,
Katarina Vogel-Mikus
4,5,
Federico Benetti
6,
Marco Roman
7,
Julie Villanova
1 and
M. Cecilia Valles-Aragón
2,*
1
European Synchrotron Radiation Facility, B.P.220, CEDEX 09, 38043 Grenoble, France
2
Faculty of Agrotechnological Sciences, Autonomous University of Chihuahua, Campus 1, Pascual Orozco, Chihuahua 31350, Mexico
3
Department Agroenvironmental Research, Madrid’s Institute for Rural Research and Development, Agricultural and Food, Leganitos 47, 28013 Madrid, Spain
4
Department of Biology, University of Ljubljana, Večna pot 111, SI-1000 Ljubljana, Slovenia
5
Jozef Stefan Institute, Jamova 39, SI-1000 Ljubljana, Slovenia
6
EcamRicert Srl, European Centre for the Sustainable Impact of Nanotechnology, Corso Stati Uniti 4, 35127 Padua, Italy
7
Department of Environmental Sciences Informatics and Statistics, University Ca’ Foscari, Dorsoduro 2137, 30123 Venezia, Italy
*
Author to whom correspondence should be addressed.
Nanomaterials 2022, 12(5), 744; https://doi.org/10.3390/nano12050744
Submission received: 24 December 2021 / Revised: 9 February 2022 / Accepted: 17 February 2022 / Published: 23 February 2022
(This article belongs to the Special Issue Ecotoxicity of Titanium Dioxide Nanoparticles)
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Abstract

:
TiO2 nanoparticles (TiO2-NPs) have a wide range of industrial applications (paintings, sunscreens, food and cosmetics) and is one of the most intensively used nanomaterials worldwide. Leaching from commercial products TiO2-NPs are predicted to significantly accumulate in wastewater sludges, which are then often used as soil amendment. In this work, sludge samples from four wastewater treatment plants of the Chihuahua State in Mexico were obtained during spring and summer (2017). A comprehensive characterization study was performed by X-ray based (laboratory and synchrotron) techniques and electron microscopy. Ti was detected in all sludge samples (1810–2760 mg/kg) mainly as TiO2 particles ranging from 40 nm up to hundreds of nm. Micro-XANES data was analyzed by principal component analysis and linear combination fitting enabling the identification of three predominant Ti species: anatase, rutile and ilmenite. Micro-XANES from the smaller Ti particles was predominantly anatase (68% + 32% rutile), suggesting these TiO2-NPs originate from paintings and cosmetics. TEM imaging confirmed the presence of nanoscale Ti with smooth surface morphologies resembling engineered TiO2-NPs. The size and crystalline phase of TiO2-NPs in the sludge from this region suggest increased reactivity and potential toxicity to agro-systems. Further studies should be dedicated to evaluating this.

1. Introduction

1.1. NanoTiO2

Due to their novel properties, engineered nanomaterials (ENMs) are extensively used in many commercial products [1], processes and industrial applications [2]. TiO2 nanoparticles (TiO2-NPs) are one of the most produced ENMs worldwide [3], with an estimated production of 88,000 metric tons/year in 2010 [4], and a forecast of 2.5 million tons by 2025 [5]. TiO2-NPs are used in many applications/areas, including food (food-grade TiO2/E171), cosmetics, personal care (sunscreen, toothpaste and deodorants) [6], agriculture, medicine, environmental protection [7], and engineering (solar cells [8] and building materials [9]). These NPs are particularly used in paints and coatings to provide surface self-cleaning and self-disinfecting properties [10]. Despite the benefits of using ENMs, there are also several concerns about their fate and environmental implications [11,12,13].

1.2. TiO2-NPs Release to the Environment

During their manufacturing, transport, usage or disposal, ENMs are unavoidably released into soil, water or air [14]. The latest dynamical models estimating the emissions of ENMs into the environment, agree that TiO2-NPs are amongst those with the highest mass-flow release [15,16], other studies indicate that sewage is the main release pathway of TiO2-NPs [1,17]. TiO2-NPs may release from paints on building facades and reach urban runoff, in addition TiO2-NPs from food are released by human excretion, and TiO2-NPs from cosmetics and personal care products are washed and disposed into sewage systems [18]. Other models also predict a significant release into freshwater, urban and agricultural soil (where biosolids or treated water are the main sources) [19]. On the other hand, the Organization for Economic Cooperation and Development considers sludge treatment for sewage as the most used method in the waste-water treatment plants (WWTPs), worldwide [20]. Studies show that during a treatment process in a WWTP, more than 90% of ENMs are retained in the sludge [21], up to 92% for TiO2-NPs specifically [22]. Therefore, sludge from WWTPs can be considered as the main accumulator of TiO2-NPs coming from anthropogenic activities, as it has been pointed out by many authors [23,24].

1.3. Fate of TiO2-NPs in WWTPs Sludge

A number of studies on characterization of TiO2-NPs in full scale WWTPs detected these nanoparticles in sludge or wastewater. Kiser et al. [18] reported concentrations of 1 to 6 mg Ti/kg in one WWTP located in Arizona (U.S.A.). The same researchers detected TiO2-NPs in wastewater effluents from 10 municipal facilities from southern to central Arizona. Measuring concentrations from <2 to 20 μg/L, they estimated that on average 98.3% of the incoming Ti is removed by the wastewater treatment [25]. Kim et al. [26] reported a total Ti concentration in three sewage sludge products from the US EPA Targeted National Sewage Sludge Survey ranging from 96.9 to 4510 mg/kg, in which they identify TiO2 particles from 40 to 300 nm. Tong et al. [27] found direct evidence of the presence of TiO2 in sludge from a WWTP in Skokie, Illinois (U.S.A.), in particular with coexistence of both anatase and rutile phases with particle size in the range 100–300 nm. Shi et al. [28] investigated the fate of TiO2-NPs in two full scale WWTPs in northern China, they found Ti in the effluent from both plants and their receptor streams, predominantly in the form of TiO2-NPs agglomerates. In sewage sludge samples collected from 26 WWTPs in Shanghai, China, Tou et al. [29] found anatase and rutile aggregates with sizes ranging from 50 to 400 nm. Polesel et al. [30] studied two WWTPs in the city of Trondheim (Norway), and observed agglomerates and aggregates of TiO2 particles from 500 nm to >1 μm in size. Choi et al. [31] conducted a full year study in a WWTP in Maryland (U.S.A.). They found inflow TiO2 concentrations in the range 21.6 ± 5.0 to 391.0 ± 43.0 μg/L and estimated a yearly average capture of TiO2 of 39.8 and 25.1 kg/day by the primary and the secondary sludge particulates, respectively. Wielinski et al. [32] reported concentrations of 1000–1800 mg Ti/kg in sludge samples from a municipal WWTP in Wallisellen, Switzerland, where anatase and rutile were identified as the main mineral bearing species. By spiking these sludge samples with anatase or rutile NPs their transformations due to the incineration process were determined and both phases were susceptible to transform into members of the hematite-ilmenite solid solution. The analytical techniques used in the above-mentioned studies are summarized in Table A1 of Appendix A.
The worldwide sewage sludge production is considerably increasing, and its management represents an important environmental issue. In the EU-27, the production of dry WWTP sludge is estimated to be around 10.13 MT/year, and it was expected to increase to 13 MT/year by 2020 [33]. In 2017, Seiple et al. reported that 13.84 MT/year of dry solids are captured during wastewater treatment in the U.S.A. [34]. The organic matter and nutrients content in sludge may improve the physical, chemical, and biological properties of soils for crop development [35]. According to the report of European Commission published in 2010, 39% of sewage sludge produced in the EU is recycled through agriculture [36]. Meanwhile, in the U.S.A. the application of biosolids reaches 22.4 dry metric Ton/ha [37]. Current regulations define permissible levels for heavy metals, weeds, human and plant pathogens [38] for the reuse of sewage sludge in agriculture. Currently, Ti content (bulk or nano) is not considered by any regulations worldwide [39,40,41].

1.4. Potential Risks of TiO2-NPs

Once the sludge from WWTPs is applied as soil amendment, the potential eco-toxic effects of TiO2-NPs remain unknown because the mechanisms of interaction between such NPs and natural systems are still to be elucidated [42]. However, a relevant toxicity risk arising from the management and transport of sludge material should not be excluded. The National Institute for Occupational Safety and Health (NIOSH) indicated TiO2-NPs as a potential carcinogen and recommended exposure limits of 2.4 for fine and 0.3 mg/m3 for ultrafine TiO2 (including engineered nanoscale), as time-weighted average concentrations for up to 10 h/day during a 40 h-work week [43]. Furthermore, a recent review on the effects of TiO2-NPs exposure based on in vitro and in vivo murine studies, concluded that [7]: intestinal mucosa, brain, heart and other internal organs can be affected by a constant exposure to TiO2-NPs at minor doses, which may lead to increased risks of developing several diseases, tumors or acceleration of existing cancer progression.
As mentioned above, the effects of TiO2-NPs in soils and biological systems such as plants, crops, and rhizosphere microorganisms are still uncertain. For instance, Simonin et al. [44] found that TiO2-NPs trigger cascading negative effects on denitrification enzyme activity and a substantial modification of the bacterial community structure. On the contrary, Moll et al. [45] did not observe negative effects of TiO2-NPs on soil microbial communities, while Timmusk et al. [46] showed that TiO2-NPs can even enhance the activity of growth-promoting rhizobacteria.
Even if many studies investigated the interaction of TiO2-NPs with plants, most of them were performed in hydroponic conditions, whereas just a few considered more realistic environments. Amongst the latter, cucumbers growing in soils spiked with TiO2-NPs were tested by Servin et al. [47], who reported translocation of TiO2-NPs from the soil to the edible part of the plants. Their findings suggest that these NPs could enter the food chain, with unknown consequences on the human health. Giorgetti et al. [48] grew peas in farming soil amended with biosolids containing TiO2-NPs. They found different damages in the plants, including in the root cells. However, Bakshi et al. [49] reported no significant Ti enrichment in tomato fruits due to sewage sludge amendment containing TiO2-NPs, finding no evidence of acute toxicity on plants.
Overall, literature results are inconsistent and there is no consensus on the environmental effects of TiO2-NPs, but it is evident that chemical speciation and particle size plays a crucial role in determining the toxicological properties of TiO2-NPs [50,51,52,53]. Nonetheless, the physicochemical characterization of ENMs in natural media is challenging due to the matrix complexity and the rather low concentrations [42,52].
This study presents a comprehensive physicochemical characterization of TiO2-NPs in sludges collected from the four existent WWTPs in the Chihuahua State, Mexico. Three WWTPs process the waste of the two main cities in the State, serving a population of around 1 million; the fourth locates in a less industrialized small city, therefore a lower concentration of TiO2-NPs is expected. All the sludge from all plants is used to amend nearby fields, representing a potential environmental risk. Therefore, assessing the presence and characteristics of TiO2-NPs in the WWPTs sludge is of primary importance. A variety of complementary analytical techniques were used in this study, starting from bulk techniques: bulk X-ray Fluorescence (XRF) spectrometry, Ti K-edge bulk X-ray Absorption Near-Edge Structure spectrometry (XANES), bulk X-ray Diffraction (XRD); to microscopy techniques: micro-XRD, micro-XANES, micro-XRF and nano-XRF, including transmission electron microscopy coupled to energy dispersive X-ray spectroscopy (TEM-EDX). To the best of the authors’ knowledge there are no other studies performed in WWTPs from Mexico, where the sludge is intensively used as agricultural amendment.

2. Materials and Methods

2.1. Sampling and Sample Preparation

During spring (P) and summer (S) of 2017, sludge samples were collected from four WWTPs of the Chihuahua State in Mexico [54], Figure 1. Two WWTPs were located in the city of Chihuahua, at North (CN) (430 L/s effluent) and South (CS) (1620 L/s effluent), with a sludge generation of 65,700 m3/year [55] in both sites. A third WWTP is located in the city of Juarez (JZ) (1620 south effluent, 1350 L/s effluent). Chihuahua and Juarez are the biggest cities of the State with an overall sludge generation of 85,116 m3/year [56]. The fourth WWTP locates in Casas Grandes (CG) (100 L/s effluent, sludge production data are unavailable), a smaller city with primary activities. The sampling was performed following the official Mexican normative NOM-004-SEMARNAT-2002 [39]. The acronyms of the cities reported above, joined with the initial of the season, were used to name the samples, e.g., Juarez Spring is JZP. The collected sludge was taken in a semisolid form at the dump of the anaerobic digestor, which is fed by the biological reactor. For hygiene reasons and better preservation of the sample, the sludge was dried at ambient temperature and stored in plastic bags with hermetic closure. Then, pressed pellets of approx. 1 g were prepared from the sludge. In addition, water extracts for each site were prepared from 0.2 g of powdered sludge mixed with 1 mL of deionized water, hand-shaken for one minute, left settling for 30 min and decanted. In this case, 10 μL of supernatant were finally deposited onto UltraleneTM film.

2.2. Bulk Analysis

Bulk XRF measurements were performed on all sludge samples pressed in pellets. Each sample was measured twice with a portable XRF spectrometer, Peduzo P01 (Jozef Stefan Institute, Slovenia) equipped with Rh X-ray tube (30 kV) and SDD (Amptek, Inc.; Bedford, MA, USA) detector [57]. The quantitative analysis was performed by the Quantitative X-ray analysis system software package developed in Lab View. The averaged values have an associated uncertainty that includes the statistical uncertainty of measured intensities and the uncertainty of the mathematical fitting procedure [58]. Then, the reported uncertainty corresponds to the combined standard uncertainty. GeoPT standard reference material OU-10 Longmyndian Greywacke was used to validate the quantification procedure.
Samples from both seasons and all WWTPs were used for bulk XRD. Agatha mortar ground sludge was introduced in thin glass capillaries and mounted in the high energy resolution powder diffractometer at ID22 [59] of the European Synchrotron Radiation Facility (ESRF) in Grenoble. Using a 29 keV incident photon beam, the diffracted X-rays were collected by the multianalyzer stage.
Ti K-edge bulk XANES measurements were performed on the sludge pressed pellets, using a scanning x-ray microscope at the ID21 beamline, ESRF [60]. One measurement was acquired per sample using unfocused mode beam (250 μm diameter); with an average flux of 4 × 109 photons/s. X-ray emission was integrated by a silicon drift detector (SDD, SGX sensortech 80 mm2 active area) and the incoming beam flux measured by a photodiode. All energy scans were performed from 4.95 keV to 5.1 keV, with 0.5 eV energy steps with 100 ms dwell time per energy step. Spectra energy was calibrated using a Ti foil reference.

2.3. Microscopy Analyses

Both pressed pellets and water extracts were employed to perform coupled μXRF and μXANES measurements using a scanning X-ray microscope at beamline ID21, ESRF. Kirkpatrick-Baez focused beam of 0.8 × 0.4 μm2 (HxV) and an average flux of 1.2 × 1010 photons/s was used, and energy selection carried out by means of Si (111) double crystal monochromator. XRF emission spectra were obtained with a SDD of 80 mm2 of active area (SGX Sensortech). From Ti distribution in the sample, points of interest were selected for Ti K-edge μXANES scans from 4.95 to 5.1 keV (in fluorescence mode). Depending on the size of the Ti hotspot, XANES spectra were labeled as Large for particles with a diameter larger than 3 μm, or Small for particles with smaller diameter. Full X-ray Absorption Spectroscopy (FXAS) mapping mode [61] was used for the water extracts. In this latter case, μXANES spectra were extracted from a stack of images recorded at each energy step of the spectrum, with a step size of 0.5 μm (horizontal) × 0.5 μm (vertical). Hundreds of XRF images were recorded using a region of interest selective for Ti Kα emission lines, corrected for the detector deadtime and normalized by the incoming photon flux measurement (I0), aligned using Elastix [62] and saved to a.hdf5 file containing the intensity and energy values for each image. μXANES spectra were then extracted from the FXAS maps using PyMCA [63].
Nano-XRF maps were obtained at the beamline ID16B, ESRF [64], at 17.5 keV (ΔE/E = 10−2) with a 60 × 60 nm2 spot size and an average flux of 2 × 1010 photons/s on samples from CNS, JZS and CGS (including water extracts from JZS and CGS). Fluorescence emission spectra were acquired by a VORTEX single element silicon drift detector (SDD) and a three-element SDD array from SGX Sensortech. Particle size distribution was obtained using image segmentation analysis on the Ti-nanoXRF maps. The image processing method is described in supplementary information of Pradas del Real et al. [24].
For the TEM analysis, an aliquot of 5 g of the sludge sample was mechanically ground by mortar and pestle for 5–10 min, depending on the grain size of different samples. Once homogenized, an amount of 3 mg of ground powder was weighed and a volume 1.5 mL ultra-pure water was added. Suspensions were tip-sonicated using a QSONICA sonicator. The suspensions were diluted to acquire a transparent solution, normally 1:100. Three µL of suspension were deposited onto standard electron microscopy grids 400 mesh copper (TED PELLA), previously pre-treated with alcian blue, and let dry.
TEM images were acquired using a 200 KV, JEM-2100 plus electron microscope with lanthanum hexaboride crystal (LaB6) gun equipped with a 12 Mpix NanoSprint1200 camera. Dark field images were taken by JEOL STEM detector (Jeol Ltd., Tokyo, Japan) and EDS analysis were extracted by 30 mm2 JEOL silicon drift detector (JED-2300T, Jeol Ltd., Tokyo, Japan).

2.4. Statistical Analysis

The spectra of all XRF (micro and nano) maps from experiments performed at the ESRF were fitted by PyMCA. Principal component analysis (PCA) was applied on all μXANES data, performed with Orange software [65], including the add-on Spectroscopy [66]. PCA was implemented on the second derivative of the spectra (using the Savitzky-Golay method, second polynomial order and 15 points window) and a vector normalization. From this analysis, three main groups were obtained and the average XANES spectra was then submitted to a linear combination fitting procedure in ATHENA software [67]. Fittings were performed with combinations of three model compounds, anatase and rutile, from Sigma Aldrich (Inc., St. Louis, MO, USA) measured at ID21, ESRF, and ilmenite spectrum obtained from the XAS database of the beamline 10.3.2 at the Advanced Light Source, Berkeley, CA, USA.

3. Results

3.1. Bulk X-ray Analyses

The total concentrations of Ti in sewage sludge are shown in Figure 2. All sites presented Ti content above 2 g/kg, with no significant difference (within the experimental uncertainty) between seasons except for CSS. Additionally obtained from XRF analysis, multi-elemental concentrations in WWTP sludge are presented in Table 1.
The crystalline forms of TiO2 present in the sludge samples were investigated by synchrotron based High Resolution XRD. Results shown in Figure 3 indicate the most intense diffraction peaks, belonging to anatase and rutile forms. The characteristic diffraction peaks of anatase and rutile isoforms of TiO2 are shown in Figure A1.
Another important insight of the presence of TiO2 species in the samples was obtained by bulk Ti K-edge XANES measurements, whose spectra are shown in Figure 4. The spectra from the sites and seasons present spectral features similar to the anatase reference. These results point towards anatase isoform being the predominant species, but, as observed from the XRD data rutile is also present in these samples.

3.2. Microscopy Analysis

As mentioned in Section 2.3, after obtaining a map of total Ti distribution, Ti K-edge μXANES spectra were acquired from rich-dense Ti spots, an example from JZP is shown in Figure 5. Each Ti K-edge μXANES spectrum was labelled as Small (red spots) if originated from a spot smaller or equal to 3 μm in size, or Large (blue spots) otherwise.
FXAS measurements from water extracts were included as well, where all spectra are labelled as Small. An equivalent number of Ti K-edge μXANES spectra were collected from all samples, seasons, and size classes, resulting in 550 spectra (see Figure A2), then pooled for principal component analysis (PCA). Three main groups were identified in the PCA transformed space (Figure 6a), whose average spectra are shown in Figure 6b.
While two thirds (67%) of all analyzed particles are Small and one third are Large, the size distribution differs considerably amongst the PCA-defined spectral groups. Indeed, Group 1 and Group 2 are mainly formed by Large particles. Group 3 represents 83% of the overall population and contains 98% of all Small particles. It is important to mention that no relationship was found between TiO2 isoforms and city, or season. These two categories did not aid the interpretation of the PCA plot (Figure 6).
To investigate the particle size of the Ti phases, present in the sludge, a sub-set of samples was investigated using nanoXRF, CGP, JZP and CNP (Figure 7, left side). Due to the limited access to the nanoXRF beamline ID16B, the sub-set of samples was chosen based on the evidence that the cities and seasons do not present significant differences in Ti content, bulk-XRD and bulk-XANES speciation. From the obtained nanoXRF maps, image segmentation analysis was performed to acquire the particles diameter distribution (Figure 7, right side). Different particle sizes were found where around 50% are below 240 nm for the three samples, CGP stands out with 41% smaller than 120 nm.
A few nanoXRF maps were also obtained from water extracts from JZP and CGP (Figure A3), showing the presence of Ti-NPs, where Zn and Cu nanoparticles where also identified.
Based on TEM analyses, sludge samples contained Ti-NPs with a typical diameter ranging from a minimum of 40 nm to a maximum of a few hundreds of nm (Figure 8). The Energy-dispersive X-ray (EDX) spectra indicate that particles contain Ti and O only (Figure A4).

4. Discussion

As the environmental effects of TiO2-NPs originated from anthropogenic activities are still under research [42], total Ti concentration is currently not regulated in biosolids in Mexico as much as in other countries worldwide [39,40,41]. In the sludge samples analyzed throughout this study, total Ti concentrations were consistent with other field studies (Table 2).
Sewage sludge analysis for the total concentration of trace elements in all WWTPs and both seasons demonstrated low risk of exposure to Pb (<300 mg/kg), Cr (<120 mg/kg), Cu (<1500 mg/kg), Ni (<420 mg/kg) and Zn (<2800 mg/kg) (Table 1), in compliance to Mexican regulation NOM-004-SEMARNAT-2002 [39]. In addition, the elemental concentrations were in compliance to most international regulations [63,64]. The high levels of some essential elements in the sludge of all sampled WWTP, including P (>8450 mg/kg), K (>1065 mg/kg) and Ca (>18,000 mg/kg) (Table 1), their high volume of production and easy availability at affordable cost, justifies its common use as an agricultural amendment in the nearby agricultural fields [33].
High-resolution XRD analyses of the sludge have shown some diffraction peaks typical of anatase and rutile (Figure 3). Unfortunately, some rutile characteristic diffraction peaks were not identified. This is due to overlapping peaks from other components present in the sludge. For instance, in Figure 3c the rutile peak (101) is indistinguishable. Thus, these experiments were followed by XANES, a more selective technique for Ti speciation sensitive enough to distinguish the TiO2 isoforms. Since the energy of the X-ray beam is tuned around the Ti K-edge, interference from other elements is very low [70]. A clear signature of TiO2 was obtained from bulk Ti K-edge XANES (see Figure 4), the spectra from all sites and both seasons’ samples have spectral features similar to the anatase reference compound. However, from these data it was not possible to infer the TiO2 particles size. Actually, this concern was remarked in the study by Tong et al. [27], where bulk Ti K-edge XANES was also used for WWTPs sludge characterization.
Thus, micro-XANES was used for the characterization of TiO2 at the microscale. Once Ti was detected in the samples by micro-XRF mapping, micro-XANES spectra were acquired in the hotspots of the element, labeling each spectrum based on the spot size, looking for a possible chemical speciation dependence on size. After an extended Ti K-edge μXANES measurement campaign, and using PCA analysis, three main groups of hotspots were identified (Figure 6): two main TiO2 species were associated with large particles and one with small particles (<3 μm). These groups resemble the most common TiO2 phases, i.e., rutile, ilmenite and anatase (Group 1, 2 and 3, respectively); see Figure 9.
While the spectra of Group 1 and Group 2 were substantially matching those of rutile and ilmenite references, respectively; Group 3 (which contains 83% of all measurements and consists of all small particles by 98%) resembles anatase, except for some minor differences. The main spectral difference between Group 3 and anatase is observed just after the sharp intense peak due to the rising absorption edge, referred as “white line”, which may indicate a minor contribution of rutile. Linear combination fitting (LCF) was performed on the group spectra and confirmed the predominance of rutile (81% + 19% ilmenite) in Group1, ilmenite (77% + 23% rutile) in Group 2, and anatase (68% + 32% rutile) in Group 2 (see Figure A5). These results are in agreement with those reported by Niltharach et al. [71] that obtained similar Ti K-edge XANES spectra from TiO2 nanostructures having high content of anatase and minor content of rutile. Anatase was the predominant phase for smaller particles in the sludge from all sites in our study. In contrast, Tong et al. [27] determined rutile as the dominant phase in their WWTP sludge samples, with 60 ± 3% rutile, 31 ± 2% anatase, and 11 ± 3% ilmenite. The µXANES results obtained in this study suggest that nano-anatase containing products are the main source of Ti. This isoform is used in pigments, indoor paintings and coatings due to its photocatalytic properties, as well as food additive [72]. Rutile was only a minor phase identified in all samples. This TiO2 isoform is mainly employed in UV light stabilizers and in sunscreens as a nanocomposite with sub-micrometric size [72]. Here it is important to mark that μXANES imaging not only allows to determine the spatial distribution of TiO2 in the sample, but also increased the capability to resolve its isoforms; in comparison to bulk XANES (Figure 4), where the dominating anatase isoform, masks rutile and ilmenite signals.
NanoXRF measurements showed clear evidence of Ti-NPs presence in all the samples, with characteristic particle size distributions (Figure 7). In all cases, more than 50% of the Ti-NPs present were less than 240 nm in diameter. These dimensions were confirmed by TEM where particle sizes varying from 40 nm to hundreds of nm were measured. It is important to emphasize the scope of the nanoXRF technique, which was able to give a wide perspective of distribution and identification of NPs in almost intact sludge samples (only pelletized, avoiding any kind of liquid extraction). However, some of the identified Ti particles could be clusters of smaller particles, as TEM images show (Figure 8). The particle size distributions found in this study are consistent with previous observation by Kim et al. [26], Kiser et al. [18] and Tong et al. [27]. Additionally, nanoXRF mapping in the water extracts revealed the presence of Cu and Zn. Furthermore, Ti detection after basic water extraction for TEM analysis showed that the element is easily mobilized in the sludge matrix. Mobility of TiO2-NPs is crucial for their environmental fate and behaviour; in soils increased mobility increases the risk of transfer into the food chain [73].
TEM images (Figure 8) showed that Ti-NPs in sludge have regular shapes and smooth surfaces. In a characterization research of the natural colloidal Ti background in soil, Philippe et al. [74] found that morphologies and sizes of natural Ti-NPs may vary widely, thus limiting our capability to discern natural and engineered nanoparticles based on morphology. However, natural Ti-NPs present rough surfaces, whereas engineered Ti-NPs present smoother surfaces, as it has been pointed out by Pradas et al. [24] based on TEM images. In this study, Ti-NPs mainly present smooth surfaces, which actually resemble engineered TiO2-NPs, such as P25 used in the study of Nickel et al. [75]. P25 are one of the most efficient commercial photo-catalyst TiO2-NPs, used in the industry of photo catalysis and in cosmetics, constituted by anatase (82–86%) and rutile (18–14%) [60,63]. Furthermore, higher presence of anatase in sludge samples supports the hypothesis of its artificial origin [72] because in nature the most common minerals of Ti are rather ilmenite, rutile, brookite, and more rarely anatase [76].

5. Conclusions and Future Perspectives

This study has provided evidence of the presence of nanoscale TiO2 in sludge samples from four WWTP from Chihuahua, Mexico collected in spring and summer 2017. The TiO2-NPs range in size from 40 to few hundreds nm. TiO2-NPs content did not significantly differ from sampling site or season. Based on a large data set of micro-XANES three main Ti phases were identified (anatase, rutile and ilmenite). The anatase iso-form was predominant in the spectra obtained from smaller particles (68% + 32% rutile), suggesting these TiO2-NPs originate from paints and cosmetics. TEM imaging confirmed the presence of nanoscale Ti with smooth surface morphologies resembling engineered TiO2-NPs.
There could be many implications of the TiO2-NPs accumulation in sludge, starting from the WWTP process itself. Zheng et al. [77] investigated the potential effects of TiO2-NPs on biological nitrogen and phosphorus removal and bacterial community in activated sludge. They found that concentration of 50 mg/L TiO2-NPs reduced the diversity of microbial community in the activated sludge and significantly decreased the removal efficiency of total nitrogen. In addition, Li et al. [78] reported that TiO2-NPs induce bacterial cell death modes which differentially weakened sludge dewatering. They also found that bacterial populations responses are more sensitive to the crystalline phases than dosage.
In a recent review on safety implications on the use of TiO2-NPs, Musial et al. [79] discussed the lack of consensus about the safety of this nanomaterial in the research community. Thus, there could even be a risk during the sludge management, which normally is applied dried as an amendment in agricultural fields. This, for instance, may include exposing farmers to dust inhalation. Incorporation of the sludge in the soil, with consequent accumulation of TiO2-NPs, could influence the microbial communities and the crops. While implications of the TiO2-NPs release in the environment are difficult to evaluate, assessing whether it is hazardous or not is beyond the scope of this study. However, this work has presented clear evidence of nanoscale Ti and its speciation in all WWTP sludge samples. These results provide an important basis for future research on the effects of sludge amendment on agricultural soils, soil microorganisms and plants.

Author Contributions

Conceptualization, H.C.-M. and M.C.V.-A.; methodology, H.C.-M. and J.R.-H.; formal analysis, J.R.-H., H.C.-M., M.C.V.-A., A.E.P.d.R., K.V.-M., F.B. and J.V.; investigation, J.R.-H. and D.A.-S.; data curation, H.C.-M. and J.R.-H.; writing—original draft preparation, J.R.-H.; writing—review and editing, H.C.-M., M.C.V.-A., M.R., A.E.P.d.R., J.V. and F.B.; visualization, J.R.-H. and D.A.-S.; supervision, H.C.-M.; project administration, J.R.-H. All authors have read and agreed to the published version of the manuscript.

Funding

Juan Reyes-Herrera postdoctoral position was funded by the Mexican National Council for Science and Technology (CONACYT) fellow number 17448. Bulk XRF analysis was funded by Slovenian Research Agency, program group P1-0212.

Data Availability Statement

Data from microXANES spectra and its Orange workflow analysis can be found in the following link: https://github.com/jureyherrera/TiO2-NPs_sludge_WWTP_Chihuahua, accessed on 21 February 2022.

Acknowledgments

We thank the ESRF committee for the provision of beamtime and the staff of ID21, particularly to Wout De Nolf. We appreciate the help from Remi Tucoulou (ID16B), Tilman Gruenewald (ID13) and Catherine Dejoie (ID22). We are grateful with Bernhard Hesse for his support and help with the XRD experiments. Finally, we would like to thank Erfan Mafakheri Bashmagh for his technical support in the TEM experiments at ECSIN LAB.

Conflicts of Interest

The authors declare no conflict of interest.

Appendix A

Analytic techniques of the previous WWTP TiO2 characterization studies, Table A1. Glossary of the analytical techniques acronyms can be found just below of the table.
Table
Table A1. Analytic techniques of the previous and present WWTP sludge TiO2 characterization studies.
Table A1. Analytic techniques of the previous and present WWTP sludge TiO2 characterization studies.
Authors [Reference]WWTP SitesSample PreparationsAnalytical Techniques
Choi et al. [31]Maryland, USAcid digestionICP, SEM/EDX
Kim et al. [26]Midwest and West regions of the USVarious extraction
Methods		ICP-AES, SEM, STEM, TEM, nanobeam electron diffraction
Kiser et al. [18]Central Arizona, USAcid digestionICP-OES, SEM/EDX
Polesel et al. [30]Trondheim, NorwayFractionation method (Acid digestion)ICP-MS, STEM
Shi et al. [28]Shijiazhuang, Hebei Province, ChinaAcid digestionICP-MS, TEM/EDS, XPS
Tong et al. [27]Skokie, IL, USDrying and muffle furnace-induced alkaline hydrolysisICP-OES, Bulk Ti K-edge XANES
Tou et al. [29]Shanghai, ChinaAcid digestion, sequential extraction procedureSP-ICP-MS, LD-PSA, SEM, TEM/EDS
Wielinski et al. [32]Wallisellen, SwitzerlandDrying sludgeBulk Ti K-edge XANES, XRD, TEM/EDS
This studyChihuahua State, MexicoDrying and water extraction. Dilution of suspended material for TEMXRF, HR-XRD, microXRD,
Bulk Ti K-edge XANES, microXANES,
nanoXRF, TEM/EDS
Glossary of analytic technics, grouped by similarities and complementarity:
  • ICP: Inductively Coupled Plasma, SP: Single Particle, MS: Mass Spectrometry, OES: Optical Emission Spectroscopy.
  • SEM: Scanning Electron Microscopy, EDX (EDS): Energy-dispersive X-ray Spectrometry, TEM: Transmission Electron Microscopy, STEM: Scanning Transmission Electron Microscopy.
  • XPS: X-ray photoelectron spectroscopy, XRF: X-ray Fluorescence Spectroscopy, XANES: X-ray Absorption Near-Edge Spectroscopy, XRD: X-ray Diffraction.
  • LD-PSA: Laser Diffraction Particle Size Analyzer.
The XRD measurements of pure anatase and rutile crystal phases, which were taken as references are plotted in Figure A1.
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Figure A1. XRD spectra of pure anatase and rutile crystal phases.
Figure A1. XRD spectra of pure anatase and rutile crystal phases.
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Distribution of μXANES obtained from all sites, seasons and sizes.
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Figure A2. Histograms of distribution of μXANES obtained: (a) Divided by season (SP-Spring, SM-summer); (b) Divided by size (L-Large, S-Small), there are Smaller since all μXANES from water extraction samples are included in this category.
Figure A2. Histograms of distribution of μXANES obtained: (a) Divided by season (SP-Spring, SM-summer); (b) Divided by size (L-Large, S-Small), there are Smaller since all μXANES from water extraction samples are included in this category.
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Nano XRF maps from JZP and CGP obtained with the nanobeam at ID16B, ESRF.
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Figure A3. Nanomaps from sludge water extracts: (a) Juarez Spring; and (b) Casas Grandes Spring.
Figure A3. Nanomaps from sludge water extracts: (a) Juarez Spring; and (b) Casas Grandes Spring.
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EDS spectra from the TEM analysis, each spectra corresponds to the TEM images shown in Section 3.2.
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Figure A4. EDS of the TEM analysis showing Ti and O presence in the detected nanoparticles: (a) Chihuahua South Summer; (b) Chihuahua South Spring; (c) Casas Grandes Spring; (d) Chihuahua North Spring; and (e) Juarez Summer.
Figure A4. EDS of the TEM analysis showing Ti and O presence in the detected nanoparticles: (a) Chihuahua South Summer; (b) Chihuahua South Spring; (c) Casas Grandes Spring; (d) Chihuahua North Spring; and (e) Juarez Summer.
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Figure A5. Linear combination fitting (LCF) of groups of spectra obtained by PCA analysis. The LCF was performed in first derivative to maintain consistency with the PCA model. Anatase and rutile references were measured at ID21, ESRF. Ilmenite reference was obtained from XAS database of the beamline 10.3.2 at the Advanced Light Source, Berkeley, CA, USA.
Figure A5. Linear combination fitting (LCF) of groups of spectra obtained by PCA analysis. The LCF was performed in first derivative to maintain consistency with the PCA model. Anatase and rutile references were measured at ID21, ESRF. Ilmenite reference was obtained from XAS database of the beamline 10.3.2 at the Advanced Light Source, Berkeley, CA, USA.
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Appendix B

In order to study the feasibility micro X-ray diffraction experiments, a (random chosen) sample of water extract was scanned at the μXRD station of ID13 of the ESRF [80]. A sample of water extract was considered in place of the sludge to reduce diffraction signals from any other crystalline material present in the original matrix. Debye-Scherrer diffractions ring patterns (detector) and μXRF data maps (by a VortexEM detector) were acquired simultaneously [80]. The experiment was performed in a scanning diffractometer using a 15 keV photon beam of 500 nm square size, on a water extract sample from CNS.
Concerning the simultaneous μXRF and μXRD analysis on a water extract sample from CNS in ID13, the main metals found were Fe, Ti and Cu, μXRF map in Figure A6a. The spatial distribution of Ti element was compared to the spatial distribution of anatase, and rutile obtained thanks to the μXRD analysis, Figure A6, the two maps present overlaps. The XRF signal showed the location of Ti in the sample, but the XRD intensities from rutile and anatase characteristic peaks were not observed in all Ti bearing spots.
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Figure A6. Results from the μXRD analysis; (a) RGB μXRF map of total Ti, Cu and Fe distribution in a CNS water extract sample. (b) RGB μXRF map of total Ti distribution overlapped with the distribution maps of diffraction signals corresponding to anatase and rutile.
Figure A6. Results from the μXRD analysis; (a) RGB μXRF map of total Ti, Cu and Fe distribution in a CNS water extract sample. (b) RGB μXRF map of total Ti distribution overlapped with the distribution maps of diffraction signals corresponding to anatase and rutile.
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As mentioned above, aiming to determine the phase of Ti in smaller scales, a µXRD test was performed in a water extract. An extraction was adopted to reduce the complexity of the matrix and its spectral interfering components observed in the bulk XRD analysis. Still, based on our results (Figure A6), the extraction procedure also reduced the signal of significant diffraction pattern. Further work might be worth to optimize the sample preparation approach in order to improve TiO2 diffraction yields.

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Figure 1. Localization of the WWTPs in the Chihuahua State, northern Mexico; the population size of each city is included in a table at the top-right of the figure.
Figure 1. Localization of the WWTPs in the Chihuahua State, northern Mexico; the population size of each city is included in a table at the top-right of the figure.
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Figure 2. Average Ti concentration in sewage sludge by bulk XRF analysis. Error bars represent the combined standard uncertainty.
Figure 2. Average Ti concentration in sewage sludge by bulk XRF analysis. Error bars represent the combined standard uncertainty.
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Figure 3. XRD diffraction spectra from all sludge samples. Zoomed regions are shown for the most important diffraction peaks of anatase (Ana) and rutile (Rut): (a) anatase 101; (b) rutile 110; (c) rutile 101 and (d) anatase 200. A small vertical shift has been applied for visualization purposes only.
Figure 3. XRD diffraction spectra from all sludge samples. Zoomed regions are shown for the most important diffraction peaks of anatase (Ana) and rutile (Rut): (a) anatase 101; (b) rutile 110; (c) rutile 101 and (d) anatase 200. A small vertical shift has been applied for visualization purposes only.
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Figure 4. Bulk Ti K-edge XANES spectra of sludge samples, including rutile and anatase references. A vertical offset has been applied to help the comparison.
Figure 4. Bulk Ti K-edge XANES spectra of sludge samples, including rutile and anatase references. A vertical offset has been applied to help the comparison.
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Figure 5. Example of Ti K-edge μXANES spectra acquired from hotspots of its total level distribution map from JZP: (a) μXRF map of Ti including some hotspots selected for μXANES analysis; (b) Corresponding XANES spectra. The color code for Small spots is red and for Large spots is blue.
Figure 5. Example of Ti K-edge μXANES spectra acquired from hotspots of its total level distribution map from JZP: (a) μXRF map of Ti including some hotspots selected for μXANES analysis; (b) Corresponding XANES spectra. The color code for Small spots is red and for Large spots is blue.
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Figure 6. Results of PCA of all the Ti K-edge μXANES spectra: (a) PCA scores plot, including a zoom in the region with the highest point density. Between brackets, the percentage of total variance explained by each component is reported; (b) Corresponding average XANES spectra of each of the three identified groups (solid line) with uncertainty bands (standard deviation).
Figure 6. Results of PCA of all the Ti K-edge μXANES spectra: (a) PCA scores plot, including a zoom in the region with the highest point density. Between brackets, the percentage of total variance explained by each component is reported; (b) Corresponding average XANES spectra of each of the three identified groups (solid line) with uncertainty bands (standard deviation).
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Figure 7. Titanium maps obtained from the nanoXRF analysis of sludge and corresponding particle diameter distribution: (a) Casas Grandes Spring (CGP); (b) Juarez Spring (JZP); and (c) Chihuahua North Spring (CNP).
Figure 7. Titanium maps obtained from the nanoXRF analysis of sludge and corresponding particle diameter distribution: (a) Casas Grandes Spring (CGP); (b) Juarez Spring (JZP); and (c) Chihuahua North Spring (CNP).
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Figure 8. TEM images of particles detected in WWTP sludges: (a) Chihuahua South Summer; (b) Chihuahua South Spring; (c) Casas Grandes Spring; (d) Chihuahua North Spring; and (e) Juarez Summer.
Figure 8. TEM images of particles detected in WWTP sludges: (a) Chihuahua South Summer; (b) Chihuahua South Spring; (c) Casas Grandes Spring; (d) Chihuahua North Spring; and (e) Juarez Summer.
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Figure 9. Comparison of the sludge Ti K-edge XANES spectra of three main groups of Ti hotspots identified by PCA, compared to references spectra of TiO2 phases. Anatase and rutile references were measured at ID21, ESRF. Ilmenite was obtained from XAS database of the beamline 10.3.2 at the Advanced Light Source, Berkeley, CA, USA.
Figure 9. Comparison of the sludge Ti K-edge XANES spectra of three main groups of Ti hotspots identified by PCA, compared to references spectra of TiO2 phases. Anatase and rutile references were measured at ID21, ESRF. Ilmenite was obtained from XAS database of the beamline 10.3.2 at the Advanced Light Source, Berkeley, CA, USA.
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Table
Table 1. The total concentration of trace elements [mg/kg] in the sewage sludge samples. The values are the average of two measurements. Combined standard uncertainty is around 10% for each measurement [58].
Table 1. The total concentration of trace elements [mg/kg] in the sewage sludge samples. The values are the average of two measurements. Combined standard uncertainty is around 10% for each measurement [58].
ElementCGPCGSCNPCNSCSPCSSJZPJZS
Ti26152625266023252635191024002090
Si50,10074,20022,65018,95028,75015,05048,05020,100
S437031706190396048503890866525,200
Cl12151130134097013958731215836
P8450192515,35017,60011,250927513,75014,750
K65309840281523102715150034451065
Ca23,85018,00041,70035,70039,15024,30056,40038,950
Mn15821614311514498176150
Fe13,35017,050782060957605509525,30022,250
Br3323413436403036
Ni2015607126252422
Cr1622445140329261
Cu172128270268371228325362
Zn1135741152514051300101722302365
Pb165114141114147126132123
Rb6272242031203219
Sr190144333277214157495503
Zr192206192156179156180188
Table
Table 2. Total Ti concentrations in WWTPs sludge from the literature, including this study.
Table 2. Total Ti concentrations in WWTPs sludge from the literature, including this study.
ReferenceWWTP SitesTi Concentration [mg/kg]
Choi et al. [31]Maryland, US1200 to 4670
Johnson et al. [68]Southern region, England370 to 670
Khosravi et al. [69]Peterborough, Canada320
Kim et al. [26]Midwest and West regions of the USA960 to 4510
Kiser et al. [18]Central Arizona, USA1100
Polesel et al. [30]Trondheim, Norway700
Shi et al. [28]Shijiazhuang, Hebei Province, China1360
Tong et al. [27]Skokie, IL, USA1700
Tou et al. [29]Shanghai, China33 to 2700
Wielinski et al. [32]Wallisellen, Switzerland1000 to 1800
This studyChihuahua State, Mexico1900 to 2600
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Reyes-Herrera, J.; Acosta-Slane, D.; Castillo-Michel, H.; Pradas del Real, A.E.; Vogel-Mikus, K.; Benetti, F.; Roman, M.; Villanova, J.; Valles-Aragón, M.C. Detection and Characterization of TiO2 Nanomaterials in Sludge from Wastewater Treatment Plants of Chihuahua State, Mexico. Nanomaterials 2022, 12, 744. https://doi.org/10.3390/nano12050744

AMA Style

Reyes-Herrera J, Acosta-Slane D, Castillo-Michel H, Pradas del Real AE, Vogel-Mikus K, Benetti F, Roman M, Villanova J, Valles-Aragón MC. Detection and Characterization of TiO2 Nanomaterials in Sludge from Wastewater Treatment Plants of Chihuahua State, Mexico. Nanomaterials. 2022; 12(5):744. https://doi.org/10.3390/nano12050744

Chicago/Turabian Style

Reyes-Herrera, Juan, Damaris Acosta-Slane, Hiram Castillo-Michel, Ana E. Pradas del Real, Katarina Vogel-Mikus, Federico Benetti, Marco Roman, Julie Villanova, and M. Cecilia Valles-Aragón. 2022. "Detection and Characterization of TiO2 Nanomaterials in Sludge from Wastewater Treatment Plants of Chihuahua State, Mexico" Nanomaterials 12, no. 5: 744. https://doi.org/10.3390/nano12050744

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