# New Developments in Liquid Chromatography Mass Spectrometry for the Determination of Micropollutants

Authors: Zoraida Sosa-Ferrera; Cristina Mahugo-Santana; José Juan Santana-Rodríguez
Journal: Chromatography Research International
 (2012)

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## Abstract

The combination of liquid chromatography (LC) with mass spectrometry (MS) in the environmental field has appeared as a valuable tool for the determination of micropollutants. Several groups of compounds have been considered as particularly relevant (e.g., pharmaceuticals, hormones and other endocrine-disrupting, personal care products and their metabolites, flame retardants, surfactants, and plasticizers, among others) since the same ones are continuously being released in the environment mainly as a result of the manufacturing processes, the disposal of unused or expired products, and the excreta. Because these micropollutants are not completely removed in the environment, very specific and sensitive analytical procedures are needed for their identification and quantification. High performance liquid chromatography coupled to tandem mass spectrometry (LC-MS/MS) (or LC-MS2) and especially time-of-flight mass spectrometry (TOF/MS), has allowed that many environmental contaminants that are highly polar or nonvolatile or have a high molecular weight to be analyzed or identified. In this work we present an overview focused on the developments of liquid chromatography mass spectrometry applied to the analysis of the main classes of micropollutants in aqueous and solid environmental samples. Various aspects of methodologies based on these techniques, including sample preparation (extraction/preconcentration) and matrix effects, are discussed.


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## Body

## 1. Introduction

Over the last two decades the use of LC techniques coupling with a high resolution MS to identify unknown contaminants has advanced spectacularly. This progress is mostly due to the development of new instrumentation. LC techniques have replaced gas chromatography (GC) as they present obvious advantages such as reduced sample pretreatment and their capacity to determine polar or thermally stabile compounds.The combination of LC and MS offers the possibility to take advantages of both LC as a powerful and versatile separation technique and MS as a powerful and sensitive detection and identification technique. The intrinsic properties of these two techniques result in an extremely analytical tool useful with many application areas. There are many different LC-MS systems on the market, that present advantages and limitations according to the type of samples that must be analyzed.Interface designs have changed considerably and have become much more sophisticated and efficient. Since the introduction of atmospheric pressure ionization techniques (API), LC-MS has played an increasingly important role in environmental analysis allowing to analyze a broad range of compounds, including nonvolatile, thermally labile, and polar species. Today, the interfaces most widely used for the LC-MS analysis are electrospray (ESI) and atmospheric pressure chemical ionisation (APCI), both using atmospheric pressure ionization (API). They produce protonated [M+H]+ or deprotonated [M−H]− molecules. ESI is particularly well suited for the analysis of polar compounds whereas APCI is highly effective in the analysis of medium- and low-polarity substances. When ESI is operating in the negative ion mode of ionisation (NI) the sensitivity achieved in the analysis of some relevant pollutant compounds is considerably better than that of the ESI interface operating in the positive ion mode of ionisation (PI) and the APCI interface operating in the NI mode [1, 2]. However, some recent studies [3–5] indicate that the APCI interface operating in the PI mode can furnish sensitivities comparable in many cases to that of the negative ion ESI.Combined ion sources can be considered as an option merging the advantages and application ranges of atmospheric pressure ionization techniques, but on the other hand their sensitivity may be a compromise between both modes. The advantage of combined ESI/APCI [6] ion sources is the possible detection of both polar and nonpolar analytes in one run, which can increase the number of the identified components for highly complex matrices.These API technologies have been interfaced with a variety of mass analysers, including single-(Q) and triple-quadrupole (QqQ), orthogonal-acceleration time-of-flight (oaTOF), linear ion trap (LIT), and sector-field MS instruments.For complex samples, containing many compounds, LC-MS is not enough for the unequivocal confirmation of analytes for the final identification. LC-MS2 takes out this problem and results in a much higher degree of certainty in the identification of the unknowns. Triple-quadrupole (QqQ) mass analyzers have become the most widely used analytical tool in the environmental analysis. Their application has allowed the determination of a great number of compounds, especially polar ones that were previously difficult or even impossible to analyze. More recent approaches in LC-MS2 are linear ion traps (LITs), new-generation QqQs, and hybrid instruments, such as quadrupole time-of-flight (Qq-TOF) and Q-linear ion traps (Qq-LITs). When the first quadrupole of a QqQ is replaced by a double-focusing mass spectrometer, the instrument is termed a hybrid. Hybrid Qq-TOF-MS technique is the most common application in the structural characterization in the environmental analysis and allows an unequivocal confirmation of the contaminants detected. Moreover, TOF-based mass analyzers allow to find additional nontarget organic contaminants. The elimination of false positives is possible by generating full-scan production spectra with an exact mass. Qq-LIT is considered as a very powerful tool for a rapid identification and confirmation of metabolites in different matrices because of its capability of producing additional spectral information useful for structure clarification [7–9].Some papers compared a real performance of different types of modern tandem mass analyzers for particular applications, which provides valuable complementary information. LC-MS with QqQ and LIT has been compared for the determination of 6 pesticides in fruits [10]. QqQ provides better linear dynamic range, higher precision, less matrix interferences, and better robustness, while LIT provides an excellent sensitivity for product ion measurements. Four LC-MS systems equipped with Q, QqQ, IT (ion trap) and Q-TOF have been compared in the quantitative analysis (sensitivity, precision, and accuracy) of carbosulfan and its main transformation products [11]. QqQ provides at least 20-fold higher sensitivity compared to other mass analyzers and better linear dynamic range. The repeatability (within a day) is slightly better for Q (5–10%) and QqQ (5–9%) compared to LIT (12–16%) and Q-TOF (9–16%). Although the QqQ is more sensitive and precise, mean values obtained by all instruments are comparable.The miniaturization is an important issue considered in all fields of analytical instrumentation including both parts of LC-MS coupling. The most widespread and well-established approach is UHPLC [12], which is based on the use of small particle size (sub-2 μm particles) in the stationary phase and short columns, at ultrahigh pressures (up to 1300 bars) yielding fast analyses and narrow chromatographic peaks. Moreover, UHPLC dramatically shortens analysis times, often to 10 min or less [13, 14]. On the other hand, it requires a higher acquisition speed of mass spectrometer to obtain enough sampling points for the reliable peak integration. Typical peak widths in routine LC-MS are 3–10 s [14–16], while peak widths in the fast/ultrafast UHPLC-MS are generally in the range 1–3 s, but they can be narrower than 1 s under well-optimized conditions [17, 18]. Modern TOF-based mass analyzers and also some ion traps are capable of reaching higher acquisition speed points for peak, what is useful to generate more sampling points per peak for a better quantification. Examples of potential applications of these methods have been published. Ibáñez et al. published an overview of the applications of UHPLC with TOF-MS for the rapid screening of multiclass organic pollutants in water [19].The composition of the mobile phase is an important factor for improving separation in LC. An acidic condition with acetonitrile-water and methanol-water mixtures with a gradient elution is among the most common approach for improved peak shape in chromatography. Modification of the mobile phase, when performed in an attempt to improve the sensitivity of MS detection, has been accomplished with acetic acid, formic acid, or ammonium acetate. Nonvolatile additives, such as oxalic acid, should be avoided when ESI is used and trifluoroacetic (TFA) acid can suppress the ionization in the electrospray source.The ion suppression/enhancement effects play an important role in LC–MS quantification and extend of these effects needs to be quantitatively assessed. The ion suppression and matrix effects can cause severe problems with the quantification in the trace analysis.In MS quantification, to eliminate any possible variations during the ionization process and the mass analysis, such as the ion suppression/enhancement, the contamination of the ion source or the mobile phase, extraction losses, or any other unpredictable reasons, an internal standard must be used.Another important issue is the sample preparation prior to LC-MS analysis [20]. Obviously, the internal standard must be added before any sample preconcentration step. Another alternative approach for the relative quantification is the use of response factors determined from the calibration curves of pure standards and then applied for real samples [21, 22]. The internal standard addition and response factors approach can be combined in one platform together with the well-optimized chromatographic separation.An overview of the applications of LC techniques coupled to mass spectrometry in the determination of the main classes of micropollutants in aqueous and solid environmental samples is presented. These compounds are present to very low concentrations and due to the high complexity of some environmental samples; very specific and sensitive analytical procedures are needed for their determination. Although these compounds are not currently covered by the existing regulations, the possibility of adverse effects on humans and animals and their extensive environmental distribution has recently attracted an increasing interest. In particular, these compounds include pharmaceuticals, personal care products, flame retardants, surfactants, and plasticizers, among others. Figure1 shows a scheme summary of the micropollutants considered in this work.Figure 1
Scheme summary of the micropollutants considered in this paper.Micropollutants contaminants are released into environment mainly as a result of the manufacturing processes, the disposal of unused or expired products, and the excreta, mostly through urban wastewater and many of them can further spread through the water cycle, even reaching drinking water, due to their hydrophilic character and low removal at wastewater treatment plants (WWTPs) and drinking water treatment plants (DWTPs) [23–25]. They can also enter into the environment due to surface-water runoffs and soil leaching after the agricultural applications of manure. Once released into the environment, micropollutants are subject to different processes, such as biodegradation and chemical and photochemical degradation, which contribute to their elimination. When these transformations take place, degradation products can differ in the environmental behaviour and toxicity. However, they are often more persistent than their corresponding parent compounds [26].To obtain high recoveries and minimise interference, the determination of these pollutants requires extraction and clean-up steps prior to detection. Solid phase extraction (SPE) is frequently used to extract these compounds from aqueous samples [27]. However, the demand to reduce the solvent volumes and avoid the use of toxic organic solvents has led to substantial efforts to adapt existing sample preparation methods to the development of new approaches. Miniaturisation has been a key factor in the search of these objectives. Microextraction techniques allow high enrichment factors and minimise solvent consumption which avoid environmental pollution. Among these techniques are solid phase microextraction (SPME), stir-bar sorptive extraction (SBSE), and liquid-phase microextraction (LPME) approaches. Although SPME has been the technique most widely used, in recent years LPME approaches, such as single-drop microextraction (SDME), hollow-fiber liquid-phase microextraction (HF-LPME), and dispersive liquid-liquid microextraction (DLLME), have been growing more interest. The extraction of emerging pollutants from solid matrices is carried out by accelerated solvent extraction (ASE) pressurised liquid extraction (PLE), ultrasound assisted extraction (UAE), and microwave-assisted extraction (MAE). These methods have been replaced to Soxhlet extraction, the classical procedure for solid matrices [28–30].The US Environmental Protection Agency (USEPA) published the final Contaminant Candidate List (CCL-3) in September 2009, which is a drinking water priority contaminant list for regulatory decision making and information collection. The listed contaminants are either known or anticipated to exist in drinking water systems and will be considered for a potential regulation. This final CCL-3 contains 104 chemicals and 12 microbial contaminants, and it includes three pharmaceuticals, eight hormones, and several disinfectant by-products and industrial additives [31]. In the European Union (EU), the Water Framework Directive (WFD) sets the strategy against the pollution of water by dangerous substances. The WFD provisions will be required from Member States and Associated States to establish programs to monitor the quality of water, which implies a review of human activity on the pollutants and an economic analysis of water use. In this context, there is an urgent need for a list of emerging contaminants as possible candidates for introduction into the WFD list of priority substances. This can be amended every four years with revisions and additions of new contaminants [32].


## 2. Application to the Determination of Micropollutants in Environmental Samples

### 2.1. Pharmaceuticals Compounds

Among new contaminants, pharmaceuticals belong to a group of an increasing interest due to their pharmacological activity and rising consumption deriving from their use in human and veterinary medicine [33, 34]. Moreover, due to their ubiquitous presence in the environment arising from continual input into the aquatic compartment, they are considered as “pseudo” persistent pollutants [35]. The discharge of therapeutic agents in effluents from production facilities, hospitals and private households, improper disposal of unused drugs, and the direct discharge of veterinary medicines leads to the contamination of environmental waters, and wastewater-treatment plants are considered to be a major source [33, 34, 36–38]. Biological treatment in WWTPs affects only the partial removal of a wide range of microcontaminants, especially polar ones, which are discharged into the final effluent. Thus, it has become evident that the application of more enhanced technologies may be crucial to full the requirements to recycle municipal and industrial wastewaters as drinking water. However, the removal of polar contaminants during drinking water treatment is incomplete. This fact was demonstrated by Ternes et al. when they investigated the elimination of selected pharmaceuticals, such as clofibric acid, bezafibrate, or carbamazepine, during drinking water treatment at the pilot-plant scale and in real waterworks in Germany [39]. The concentration of pharmaceuticals in water can vary between a few nanograms per liter to the micrograms per liter levels. These levels have to be removed in order to achieve the drinking water quality and to protect the water resources. Therefore, the concentrations and identities of these contaminants in water have to be monitored during the entire water purification and transportation process.Antibiotics, followed by steroid compounds, analgesics, and nonsteroidal anti-inflammatory drugs (NSAIDs), are the most widely studied pharmaceuticals. Table1 shows the diverse determinations of these compounds in environmental samples.Table 1
Determination of pharmaceutical compounds in environmental samples by LC coupled to mass spectrometry.
Compounds
Samples
Extraction
Determination
Analytical parameters
Reference
SMMX,  SDMX, SMXZ, STZL, SCPD, SMRZ,  SMTZ, OXTC, MCLN, DOXN, MECN, CTCL, DEMN, and TCLN
River water, sewage and agricultural wastewater
Online SPE
LC-MSESI (PI)
Recoveries: 74.3–116.5%LOQs: 0.09–0.11 μg·L−1
[40]
ENR, LOM, LVFX, FLX, SPFX, AMX, OTC, and SQX
Lake water, river water and sewage effluent
MIP
LC-Qq-ITESI (PI)MRM
Recoveries: 76.3–94.2%RSD < 9.1%LODs: 3.2–6.2 ng·L−1
[41]
4-Acetamidophenol, carbamazepine, (+)-cis-diltiazem hydrochloride, norfluoxetine hydrochloride, ranitidine hydrochloride, sulfamethoxazole, caffeine, trimethoprim, atorvastatin, lovastatin, levofloxacin, and sertraline
River water
SPE
UHPLC-QqQESI (PI)MRM
Mean recovery: 77.9%Mean RSD: 7.3%LODs < 4.1 ng·L−1
[47]
28 basic/neutral pharmaceuticals
River water
SPE
UHPLC-QqQESI (PI)MRM
LOQs: 0.3–50 ng·L−1
[48]
18 androgens and progestogens
River water and wastewater
SPE
UHPLC-QqQESI (PI)MRM
Recoveries: 77–100%RSD: 1.7–12%LODs: 0.01–50 ng·L−1
[51]
49 pharmaceuticals and 6 metabolites
Wastewater
SPE
UHPLC-QqLITESI (PI and NI)MRM and IDA
Recoveries: 55–111%RDS < 5%LODs: 0.02–50 ng·L−1
[52]
Ketoprofen, naproxen, diclofenac, and ibuprofen
Sewage sludge
HF-LPME
LC-MSESI (NI)SIM
Recoveries: 52–63%RSDs:  0.5–7%LODs < 10 μg·L-1
[58]
Levofloxacin, norfloxacin, ciprofloxacin, and enrofloxacin
Marine sediments and sewage sludge
MAME
LC-QqQESI (PI)MRM
Recoveries > 73%RSD < 8%LODs: 0.15–0.55 μg·kg−1
[60]
Ibuprofen, diclofenac, and salicylic acid
Wastewater
HF-LPME
LC-MS/MS
Recoveries: 52–100%RSDs:  1.1–1.6%.LODs: 20–300 ng·L−1
[114]
Ibuprofen, naproxen, clofibric acid, piroxicam, ketorolac, bezafibrate, fenoprofen, diclofenac, and indomethacin
Wastewater
HF-LPME
LC-MS/MS
Recoveries: 80–111%RSDs: 3.4–32%LOQs:  0.5–42 ng·L−1
[115]
Estrone, 17β-estradiol, estriol, ethynyl estradiol, and diethylstilbestrol
Surface water and wastewater
In-tube SPME
LC/MS/MS
Recoveries: 86.1–106.8LODs: 2.7–11.7 ng·L−1
[116]
36 endocrine-disrupting chemicals, including estrogens and progestogens
Potable and river water
SPE
UHPLC-QqTOF
Recoveries: 46%–134%LODs < 0.72 ng·L−1
[117]
17β-estradiol, estriol, and 17α-ethinylestradiol
Sewage sludge
MAE
LC-QqQESI (PI)MRM
Recoveries: 71.7–103.1%RSD < 12%LODs: 0.6–3.5 μg·kg−1
[63]
28 estrogenic compounds
Sewage sludge
UAE
LC-QqQESI (PI and NI)MRM
Recoveries:  44–200%RSD: 0.6–11.6%LODs: 0.08–2.06 μg·kg−1
[64]
Oestrone, testosterone, androstenedione, norethindrone, levonorgestrel, and progesterone
Soil
PLE
LC-QqQESI (PI)MRM
Recoveries: 45–100%RSD: 2.2–10.3%LODs: 0.08–2.84 μg·kg−1
[65]
Estrone, 17α-estradiol, 17β-estradiol, estriol, 17α-ethinylestradiol and diethylstilbestrol, and five conjugates
Sewage sludge
PLE
LC-QqQESI (PI)MRM
Recoveries > 81%RSD < 6%LODs < 26 μg·kg−1
[66]
α-estradiol, β-estradiol, estriol,estrone, ethynylestradiol and their sulfate, glucuronide, and acetate conjugates
River sediments
MAE
LC-Qq-ITESI (NI)MRM
Recoveries: 83–107%RSD: 4.9–9.6%LODs < 1 μg·kg−1
[67]
Abbreviations: LC: liquid chromatography; UHPLC: ultrahigh pressure liquid chromatography; MS: mass spectrometry; QqQ: triple quadrupole; IT: ion trap; LIT: lineal ion trap; ESI: electrospray ionization; APCI: atmospheric pressure chemical ionization; APPI: atmospheric pressure photoionization; NI: negative ion mode of ionisation; PI: positive ion mode of ionisation; SIM: selected ion monitoring; MRM: multiple reaction monitoring; SRM: selected reaction monitoring.
SPE: solid phase extraction; HF-LPME: hollow-fiber liquid-phase microextraction; MIP: molecularly imprinted polymer; UAE: ultrasound assisted extraction; PLE: pressurised liquid extraction; MAE: microwave-assisted extraction; MAME: microwave-assisted micellar extraction.
RSD: relative standard deviation; LOQ: limit of quantification; LOD: limit of detection.
SMMX: sulfamonomethoxine; SDMX: sulfadimethoxine; SMXZ: sulfamethoxazole; STZL: sulfathiazole; SCPD: sulfachloropyridazine; SMRZ: sulfamerazine; SMTZ: sulfamethazine; OXTC: oxytetracycline HCl; MCLN: minocycline HCl; DOXN: doxycycline hyclate; MECN: meclocycline sulfosalicylate; CTCL: chlortetracycline HCl; DEMN: democlocycline HCl; TCLN: tetracycline.
ENR: enrofloxacin; LOM: lomefloxacin; LVFX: levofloxacin; FLX: fleroxacin; SPFX: sparfloxacin; AMX: amoxicillin; OTC: oxytetracycline; SQX: sulfaquinoxaline.


#### 2.1.1. Liquid Samples

Methods of sample preparation and extraction for pharmaceuticals have evolved significantly for aqueous phases since they were first described as early as the late 1980s. The traditional sample preparation method, liquid-liquid extraction (LLE), has largely been replaced by solid-phase extraction (SPE) for the aqueous matrices.Regarding separation and detection techniques, LC, combined with MS or MS2, is the most suitable technique to separate and detect pharmaceutical residues or metabolites in environmental samples. Most of the pharmaceutical compounds are not very volatile and some are highly polar, containing ionizable functional groups. It requires additional derivatization steps that may involve more labor and time, and cause unwanted contamination in the sample. Many antibiotics are nonvolatile with a high molecular weight, which respond well to ESI interface operating in the positive ion mode of ionization; therefore LC-MS or LC-MS2 is often selected for their separation and analysis. When using a single MS step, selected-ion monitoring, SIM, is preferred for increased analytical sensitivity and selectivity in complex matrices such as wastewaters. Choi et al. [40] applied this methodology for the simultaneous analysis of seven tetracycline antibiotics and sulfonamide antibiotics from agricultural wastewater samples and sewage effluent samples. They combined the pretreatment technique, SPE, with LC-MS through online connection. This type of connection suppressed the target loss by keeping the cartridge from drying, which resulted in improvement on the recovery and saving of the analytical time. The average LOQ achieved was between 0.09 and 0.11 μg·L−1 for tetracycline antibiotics and sulfonamide antibiotics, respectively. Chen et al. [41], using IT-MS, reached LODs in the range of 3.2–6.2 ng·L−1 when they determined fluoroquinolones in water samples. The target compounds were extracted from samples by molecularly imprinted polymer (MIP) as sorbent. ESI was performed in positive mode and the data acquisition was performed in multiple reaction monitoring (MRM).Some works can be found in the bibliography which use hybrid quadrupole instruments coupled to conventional liquid chromatography systems for the analysis of pharmaceuticals in waters. For instance, Martínez Bueno et al. [42] developed a method for the determination of 38 pharmaceuticals and 10 metabolites by LC-MS2 using hybrid triple-quadrupole linear ion trap mass spectrometer in combination with time-of-flight mass spectrometry operating under SRM mode in both positive and negative ESI. This methodology was successfully applied to a monitoring study intended to characterize wastewater effluents of six sewage treatment plants in Spain. A different MS combination, QqLIT, was proposed by Gros et al. [43] for the determination of 73 pharmaceuticals by using both SRM and information-dependent analysis (IDA) acquisition modes with a total analysis time of 87 min. The method developed was applied to the analysis of various influent and effluent wastewaters.The combination of UHPLC with an MS detector appears to be a suitable approach that fulfills key requirements in terms of sensitivity, selectivity, and peak-assignment certainty for the rapid determination of analytes at low concentrations in complex matrices. Modern QqQ instruments operating in the SRM mode are preferred for targeted analysis, while TOF-MS analyzers are particularly useful for nontargeted analysis. Batt et al. [44] developed a UHPLC method coupled to a QqQ mass spectrometer for the determination of 48 drugs and 6 metabolites in wastewater and surface waters. However, total analysis time was 48 min since four chromatographic conditions were used to determine all the compounds. Langford and Thomas [45] used UHPLC-QqQ with an ESI source; however, chromatographic separation of the 40 pharmaceuticals from hospital effluents took more than 50 min. A different MS analyzer was selected by Petrovic et al. [46] who developed an UHPLC method coupled to a Q-TOF mass spectrometer for the determination of 29 pharmaceuticals in wastewater in 14 min.Conley et al. [47] described the determination of 13 pharmaceuticals and 1 metabolite in less than 4 min using UHPLC interfaced to a QqQ mass spectrometer with an ESI source. The mass analyzer operated in positive ionization mode for all analytes. The method was applied to samples of surface water collected from the Upper Tennessee River Basin. The same technique was applied by Kasprzyk-Hordern et al. [48] for the determination of 28 basic/neutral pharmaceuticals in river water samples from UK and Poland and fifteen compounds were determined at levels ranging from nanograms to micrograms per liter. In this case they achieved the separation of the target compounds in 16 min.Considerable attention had been focused on the occurrence of steroid hormones in the environment since recent studies have documented that the exposure of fish to municipal wastewater effluents affects the reproductive physiology and behavior in many fish species at ng·L−1 or even pg·L−1 levels [49, 50]. Chang et al. [51] developed a method for the simultaneous determination of eighteen androgens and progestogens in environmental waters by using UHPLC-MS2. Mass spectrometry was performed using a triple-quadrupole detector which was operated with ESI in the positive ion mode. After SPE procedure, a silica cartridge was used to purify the extract and reduce the signal suppression due to coeluting interferences. The developed method was applied to the analysis of these compounds in wastewater and surface-water samples and LODs for the eighteen analytes in the influent, effluent, and surface-water samples were in the ranges 0.20–50, 0.04–20, and 0.01–12 ng·L−1, respectively.Hybrid mass spectrometers have also been used in combination with UHPLC to determine pharmaceutical compounds. Recently, Huerta-Fontela et al. [52] developed a method for the determination of 49 pharmaceuticals and 6 metabolites in six wastewater treatment plants using the dual acquisition modes of a hybrid triple-quadrupole linear ion trap system. The proposed method enabled all the 55 compounds to be separated chromatographically in less than 9 min (6.3 min positive mode and 2.7 min negative mode) with a total analysis time of 18 min.


#### 2.1.2. Solid Samples

Despite the rather low lipophilicity of pharmaceuticals, interaction of the polar functional groups of them with organic matter and/or minerals may result in adsorption to solids. Furthermore, the application of sewage sludge as a fertilizer to the agricultural land and the reuse of manure containing veterinary medicines may also introduce pharmaceuticals into the soil. Animal origin pharmaceuticals, including aquaculture-derived compounds, contribute significantly to the occurrence of pharmaceuticals in solid matrices due to their patterns of application. Sewage sludge is the main solid produced in sewage treatment plants and the European Union (EU) promotes the use of sewage sludge as a fertilizer on agricultural land. Therefore it is important to know the occurrence of contaminants in sewage-sludge samples as those could reach surface or ground waters.The presence of pharmaceuticals in sediment, soil, and sewage sludge has been studied extensively. Analytical methods for the determination of specific groups of pharmaceuticals, including NSAIDs, antidepressants, antibiotics, andβ-blockers [53, 54], and multiclass methods have been reported in recent years. Soxhlet extraction method for soil or sediment has been replaced by PLE, MAE, and UAE because of the time-consuming nature and high usage of hazardous organic solvents. Sample extracts obtained from solid matrices are most of the time with interfering co-extracts, which dictate an additional cleanup before LC analysis. Soil or sediment sample preparation needs to combine additional cleanup or purification steps, mainly SPE after the extraction step in the solvent due to the complexity of environmental samples [55, 56].Haller et al. [57] used LC-MS and ESI with SIM mode to measure seven veterinary antibiotics in manure and reported 100 μg·kg−1 as LOQ. This technique was also applied by Sagristà et al. [58] for the direct determination of four NSAIDs in dried sludge from a sewage treatment plant (Figure 2). Extraction experiments were carried out using a magnetic stirrer at 660 rpm for several hours and then a three-phase hollow-fiber liquid-phase microextraction (HF-LPME) was applied. This microextraction procedure allowed for the enrichment factors about 3000 times for all analytes. Data acquisition was performed in negative ion mode with SIM. LODs and LOQs were about 10 and 33 μg·L−1, respectively.Single ion monitoring chromatograms obtained by LC-MS from reagent water spiked at 0.4 mg·L−1. (a) m/z = 294 (diclofenac), (b) m/z = 253 (ketoprofen), (c) m/z = 229 (naproxen), and (d) m/z = 205 (ibuprofen). From reference [58].
(a)
(b)
(c)
(d)Determination by Qq-IT, with an ESI source operated in positive mode, has been used to characterize the persistence of tetracyclines in soil fertilized with liquid manure. The analytes were extracted from soil samples by vortex with citrate buffer and ethyl acetate and the LOQ was 5μg·kg−1 for all compounds [59]. More recently, microwave-assisted micellar extraction combined with a QqQ mass spectrometer and ESI source, in a positive mode, was applied for the analysis of fluoroquinolone antibiotics in coastal marine sediments and in sewage-sludge samples. This extraction technique, which uses a micellar solution as extractant and LC-MS2, allowed LODs and LOQs between 0.15–0.55 μg·kg−1 and 0.49–1.85 μg·kg−1, respectively [60]. In addition, Jacobsen et al. [61] applied two different LC-MS2 methods to quantify eight antibiotics from different classes in soil and reported LOQs in the range 1.1–12.8 μg·kg−1. Löffler and Ternes [62] used two different APCI-MS2 methods for ten acidic pharmaceuticals in negative mode and ESI-MS2 for seven antibiotics in positive mode to determine residues in river sediment. This study illustrated that different ionization methods can be adapted to the characteristics of the compounds being examined.Estrogenic compounds are medium polar to relatively nonpolar substances, with log Kow values in the range 2.5–5.3. Consequently, we can expect sorption of estrogens to the suspended matter and a tendency of them to accumulate in soil and sediments. Several estradiol-mimicking compounds, including 17β-estradiol, estriol, and 17α-ethinylestradiol, were determined from sewage-sludge samples by using MAE followed by LC-MS2 with ESI in a positive mode. The method provided LODs ranging from 0.6 to 3.5 μg·kg−1 [63]. A greater group of steroids, including natural and synthetic estrogens, androgens, progestogens, and glucocorticoids, were determined in the same type of sample by using UAE followed, with analysis; by rapid resolution LC-MS2. In this case, a triple quadrupole detector was used, which was operated with ESI in both negative and positive modes. LODs for the 28 analytes were 0.08–2.06 μg·kg−1 [64]. LC-ESI(PI)-MS2 and PLE as an extraction technique madeit possible to determine the traces of steroid hormones (including oestrogen, androgens, and progestogens) in soil with LODs in the range 0.08–0.89 μg·kg−1. The results obtained showed ionization suppression for all the analytes in proportions ranging up to nearly 50% [65]. Using the same technique, with ESI (NI), Nieto et al. [66] achieved the determination of a greater number of natural and synthetic estrogens in sewage sludge. The MRM mode enabled LODs lower than 26 μg·kg−1 of the dry weight of sewage sludge for most of target analytes. Using an IT-MS equipped with ESI (NI) source, after extraction by MAE, Matjıcek et al. [67] carried out the simultaneous separation and determination of five hormones and their sulfate, glucuronide, and acetate conjugates in river sediments reaching LODs lower than 1 μg·kg−1.


### 2.2. Personal Care Products

Personal care products (PCPs) constitute a group of emerging contaminants which have received a considerable attention in recent years. PCPs are regarded as being potentially hazardous compounds as many of them are ubiquitous and persistent and due to their continuous introduction might cause unwanted effects in the environment.The principal pathway by which PCPs enter the environment is disposal in urban receiving waters from individual households, after showering and bathing. A variety of PCPs have been detected everywhere at the ng·L−1 concentration level in the effluents of WWTPs, since conventional water-treatment processes do not seem to be sufficient to remove PCPs from sewage water (30–90% efficiency) [68–74]. The occurrence of PCPs in municipal sewage effluent and other environmental samples could negatively impact the health of the ecosystem and the health of humans, due to the persistent and long-term chronic exposure of aquatic organisms to the concentrations of PCPs [68]. Moreover, there is some evidence of potential interactive effects of PCPs, so that low doses may lead to cumulative stress and synergic toxicity effects in exposed organisms [68, 75]. PCPs, such as UV screens, insect repellents, and some synthetic musk fragrances, have also been suspected endocrine-disrupting compounds (EDCs) (i.e., compounds that can mimic the natural hormones of animals) [71, 73, 74].Nowadays, in order to achieve greater protection to solar radiation, UV filters are added not only to cosmetics to be used for sunbathing but also to daily cosmetic products, such as face day creams, after-shave products, makeup formulations, lipsticks, and shampoos, thus resulting in an increase in the use of UV filters. Moreover, they can be found as additives in textiles, plastics, paints, car polishes, and so forth [76]. This excessive use of UV filters has led to their presence in the aquatic environment and increased their potential for endocrine and developmental toxicity [77, 78]. The increasing usage of these compounds, combined with their moderate-to-high water solubility, has led to the appearance of some of them in the aquatic environment. As regards toxicological effects, in vivo and in vitro studies have demonstrated that some hydroxylated benzophenones exert estrogenic and antiandrogenic actions [79].Triclosan, triclocarban and methyl-triclosan are bactericides widely used in household and personal-care products, for example, shampoos, soaps, creams, mouthwash, and toothpaste [80]. Triclosan is found to be acutely toxic to some aquatic organisms and it has been also shown to photo transform into members of the dioxin family, which is known as the most carcinogenic chemicals in the world [81]. Although a relatively few data exist about the toxicity of triclocarban, it has been found to impair reproduction in laboratory rats and that some of its degradation products are carcinogenic. Methyl-triclosan, a metabolite of triclosan, is more lipophilic and environmentally persistent, suggesting its relatively high bioaccumulation potential in aquatic organisms [82].Table2 illustrates some applications of LC-MS to the determination of PCPs in environmental samples.Table 2
Determination of personal care products in environmental samples by LC coupled to mass spectrometry.
Compounds
Samples
Extraction
Determination
Analytical parameters
Reference
UV filters: BP-1, BP-2, BP-3, BP-4, BP-6, and BP-8
River water and wastewater
SPE
LC-QqQ ESI (NI and PI)MRM
Recoveries: 83–105%LOQs 1–32 ng·L−1
[83]
Triclosan and triclocarban
Wastewater and tap water
IL-DLLME
LC-QqQESI (NI)MRM
Recoveries: 70.0–103.5%RSD 7.0–8.8% LODs: 0.040–0.58 μg·L−1
[84]
Triclocarban
Wastewater effluents
SBSE
LC-QqQ ESI (NI)MRM
Recoveries: 92–96%RSD: 2%LOQ: 10 ng·L−1
[85]
BP-1, BP-3, BP-8, OC, OD-PABAtriclocarban, triclosan,methylparaben, ethylparaben, benzylparaben, propylparaben
Surface water and wastewaters
SPE
UHPLC-QqQESI  (NI and PI)MRM
Recoveries: 20–101%RSD: 1–14%LODs:  20–200 ng·L−1
[86]
53 multiclass emerging pollutants (UV filters and insect repellents, among others)
Tap water, surface water, and wastewater
SPE
LC-qqQESI  (NI and PI)MRM
Recoveries > 60%RSD < 15%LODs: 0.3–30 ng·L−1
[90]
Benzotriazoles (UVP,  UV 329,  UV 326,  UV 328, UV 327, UV 571, and UV 360)
Coastal marine water and wastewater
SPE online
UHPLC-QqQESI (PI)MRM
Recoveries: 65–94%RSD: 6.2–10 %LODs: 0.6–4.1 ng·L−1
[118]
4-HydroxybenzophenoneBP-1, BP-2, BP-3, and BP-8
Sediments and sludge
LLE
LC-QqQESI (NI)MRM
Recoveries: 70–116%RSD: 3.3–13.8% LOQs: 0.06–1.65 ng·g−1
[92]
Biocides, UV filters, and benzothiazoles
Sludge sample
PLE
LC-QqQESI, APCI (NI and PI)MRM
Recoveries: 74–119%RSD < 25%
[93]
Triclosan, triclocarban,methyl paraben, ethyl paraben, propyl paraben, benzyl paraben,OD-PABA, OC, PMDSA, BP-1, BP-3, and  BP-8
Sewage sludge
PLE
UHPLC-QqQESI (NI and PI)MRM
Recoveries: 15–100%RSD ≤ 9%LODs < 8 ng·g−1
[94]
Abbreviations: LC: liquid chromatography; UHPLC: ultrahigh pressure liquid chromatography;  QqQ: triple quadrupole; IT: ion trap; LIT: lineal ion trap; ESI: electrospray ionization; APCI: atmospheric pressure chemical ionization; NI: negative ion mode of ionisation; PI: positive ion mode of ionisation; MRM: multiple reaction monitoring; SRM: selected reaction monitoring.
IL: ionic liquid; LLE: liquid-liquid extraction; SDME: single-drop microextraction; DLLME: dispersive liquid-liquid microextraction; SBSE: stir-bar sorptive extraction; PLE: pressurised liquid extraction.
RSD: Relative standard deviation; LOQ: limit of quantification; LOD: limit of detection.
OC: octocrylene; PMDSA: 2-phenylbenzimidazole-5-sulfonic acid; OD-PABA: octyldimethyl-p-aminobenzoic acid; BP-1: 2,4-dihydroxybenzophenone; BP-2:  2,2′,4,4′-tetrahydroxybenzophenone; BP-3:  2-hydroxy-4-methoxybenzophenone; BP-4: 2-hydroxy-4-methoxybenzophenone-5-sulphonic acid; BP-6:  2,2′-dihydroxy-4,4′-methoxybenzophenone; BP-8: 2,2′-dihydroxy-4-methoxybenzophenone.


#### 2.2.1. Liquid Samples

Negreira et al. [83] determined six derivatives of 2-hydroxybenzophenone, which are extensively employed as UV absorbers, in water samples by LC-QqQ using ESI in positive and negative modes, except for one compound (2-hydroxy-4-methoxybenzophenone-5-sulphonic acid) which could be ionized only in a negative mode. Benzophenones were recorded in MRM mode using two transitions per compound. Recoveries from the SPE step remained unaffected by the nature of the matrix; however, the efficiency of ESI was compound and sample dependant. Under optimized conditions, the proposed method provided LOQs from less than 1 to 32 ng·L−1, depending on the compound and the type of water sample.Triple quadrupole is the most common and most useful tool for determining PCPs in high-sensitivity target analysis. This mass spectrometer fitted with an ESI source operating in a negative mode has been used by Zhao et al. to determine triclosan and triclocarban in wastewater and tap water samples (Figure3). Enrichment of target analytes before analysis was carried out by using ionic liquid dispersive liquid-phase microextraction. The sensitivity of the proposed method allowed for LODs in the range 0.04–0.58 μg·L−1 [84]. Klein et al. determined triclocarban in wastewater effluents by LC-QqQ after stir-bar sorptive extraction (SBSE) obtaining an LOQ of 10 ng·L−1 for the target analyte [85]. ESI source was also operated in a negative mode and MRM mode was applied.LC-ESI-MS2 chromatogram obtained from wastewater. (a) Wastewater (b) Wastewater spiked with 0.40 μg·L−1 triclocarban (1) and 2.0 μg·L−1 triclosan (2). From reference [84].
(a)
(b)Pedrouzo et al. [86] determined eleven PCPs, including hydroxylated benzophenones, triclocarban and triclosan, and parabens, (another type of preservatives used in personal care products) by SPE and UHPLC-MS2 in surface and wastewaters in 9 minutes of chromatographic separation. A triple-quadrupole mass spectrometer and ESI in both PI and NI modes were applied. LOQ was 5 ng·L−1 for all the compounds, except for methylparaben (3 ng·L−1). Most of PCPs determined were found in influent waters being methylparaben and propylparaben found at the highest concentration. Both are the most widely used parabens and they are normally used together due to their synergistic preservative effects [87, 88].By using MRM to monitor two transitions between precursor and product ions, it is possible to confirm and quantify the presence of PCPs in waters at very low levels [89]. For example, Rodil et al. [90] developed a method to determine a group of 53 multiclass emerging organic pollutants (included the types mentioned above) by LC-MS2, using ESI in both PI and NI modes, after SPE. The proposed method allowed LODs between 0.3 and 30 ng·L−1. The method was used for the simultaneous determination of target analytes in water samples, including tap, surface, and wastewater. LC-QqIT was the technique chosen for determining the presence of 84 pollutants of different classes in wastewaters, including some PCPs such as sunscreen agents and synthetic musks. Previous to LC-QqIT analysis (ESI in PI and NI modes), wastewater samples were preconcentrated by SPE [91].


#### 2.2.2. Solid Samples

Several PCPs (e.g., triclosan, triclocarban, and most UV-filtering compounds) show affinity to solid matrices. As a consequence, to allow the correct evaluation of the ecological impact of these substances, evaluation of their prevalence in solid matrices is important. Several analytical approaches were therefore reported recently.LC-MS2, with ESI operated in negative mode and MRM, was applied by Zhang et al. [92] to analyse benzophenone UV filters in sediment and sludge. The method developed allowed LOQs in the ranges of 0.06–0.33 ng·g−1 dry weight (dw) and 0.1–1.65 ng·g−1 dw for sediment and sludge samples, respectively. ESI and APCI sources, operated in the positive and in the negative ion mode using MRM, were applied by Wick et al. [93] to determine different classes of compounds such as, biocides, UV filters, and benzothiazoles in sludge samples. ESI exhibited a strong ion suppression for most target analytes, while APCI was generally less susceptible to ion suppression which led to higher signal intensities in the samples and consequently to lower LOQs as long as the background noise was not increasing.UHPLC-MS2 was applied by Nieto et al. [94] for the determination of a group of parabens and two UV filters in sewage sludge. In the chromatographic step, after pressurized liquid extraction, the compounds were detected by using tandem mass spectrometry with a triple-quadrupole analyzer with ESI in positive and negative modes. The use of small diameter particles in the chromatographic column allowed the compounds to be eluted in 9 min. LODs and LOQs were lower than 8 μg·kg−1 and 12.5 μg·kg−1 of dw, respectively.


### 2.3. Flame Retardants

Flame retardant (FR) compounds are a structurally diverse group of chemicals that are added to or reacted with polymers, and they are used in plastics, textiles, electronic circuitry, and other materials to reduce the risk of fire. One of these groups of compounds comprises brominated FRs (BFRs), some of which are ubiquitous, and many of which have been detected in biota, sediments, air, water, marine mammals, and even human milk [95, 96]. BFRs are mainly represented by tetrabromobisphenol A (TBBPA), polybrominated diphenyl ethers (PBDEs), which are aromatic compounds, and the cycloaliphatic compound hexabromocyclododecane (HBCD). Regarding TBBPA, one of the most important and commonly used flame retardants, although the use of TBBPA as an additive is estimated to account for about 10% of the total amount used,excessive non-polymerized TBBPA can be emitted, contaminating the environment [97]. Mainly due to its low bioaccumulation potential, it presents concentration levels lower than those of PBDEs or HBCD in the environment [98]. However, TBBPA, being a phenolic compound, may have a greater adverse effect on humans and wildlife. Likewise, TBBPA can be considered a potential EDC due to the similarities in its structure with 17β-estradiol and thyroxine.LC, coupled to tandem MS, and ESI, APCI or atmospheric pressure photoionization (APPI), represents a valid tool to the determinations of these compounds, since that the determination of some congeners is known to be difficult due to thermal degradation problems and also because a derivatisation step is needed [99–102].Some applications of the use of LC-MS to the determination of these micropollutants in environmental samples are shown in Table3.Table 3
Determination of flame retardants in environmental samples by LC coupled to mass spectrometry.
Compounds
Samples
Extraction
Determination
Analytical parameters
Reference
38 HFRs
Wastewater
SPE
LC-QqQAPCI (NI)MRM
Recoveries 25–132%LOQs 0.1–5.6 μg·L−1
[105]
TBBPA and five PBDEs
Wastewater, river, and drinking water
LLE
LC-LITAPPI (NI)MRM
Recoveries 43–99%RSD < 17%LOQs: 0.2–3.3 ng·L−1
[106]
TBBPA and brominated BPA analogues
Sediment and sludge
Soxhlet
LC-QqQESI (NI) MRM
Recoveries: 70–105%RSD: 4.9–13.1% LOQs 0.02–0.15 ng·g−1
[107]
HBCD isomers
Suspended sediments from Detroit River
ASE
LC-QqQ,ESI (NI) MRM
—
[109]
HBCD diastereoisomers
Marine sediment
MAE
LC-ITESI (NI)
Recoveries: 68–91%RSD: 2–11%LOQs: 25–40 pg·g−1
[110]
TBBPA, BPA, Mono-BBPA, Di-BBPA, and Tri-BBPA
Sewage sludge and sediment
Sonication-SPE
LC-QqLITESI (NI)SRM
Recoveries: 39–120%RSD < 13%LODs: 0.6–2.7 ng·g−1
[111]
HBCDs and TBBPA
Sewage sludge
PLE
UHPLC-MS2 ESI, APPI, APCIMRM
Recoveries: 65–112%LOQs: 0.005–0.14 ng·g−1
[112]
Abbreviations: LC: liquid chromatography; UHPLC: ultrahigh pressure liquid chromatography; MS: mass spectrometry; QqQ: triple quadrupole; IT: ion trap; LIT: lineal ion trap; ESI: electrospray ionization; APCI: atmospheric pressure chemical ionization; APPI: atmospheric pressure photoionization; NI: negative ion mode of ionisation; PI: positive ion mode of ionisation; MRM: multiple reaction monitoring; SRM: selected reaction monitoring.
SPE: solid phase extraction; ASE: assisted solvent extraction; LLE: liquid-liquid extraction; PLE: pressurised liquid extraction; MAE: microwave-assisted extraction.
RSD: relative standard deviation; LOQ: limit of quantification; LOD: limit of detection.
TBBPA: tetrabromobisphenol A; PBDEs: polybrominated diphenyl ethers; BDE: decabrominated diphenyl ether; HBCD: hexabromocyclododecane; HFRs: halogenated flame retardants.


#### 2.3.1. Liquid Samples

The use of LC-MS in the determination of TBBPA provides several different detection modes and eliminates the need for the derivatization of the phenolic group. Moreover, it facilitates the use of13C-labelled TBBPA. Tollbäck et al. [103] reported that the most suitable LC-MS interface for TBBPA analysis is ESI operating in a negative ionization mode. ESI gave 30–40 times lower LODs compared to APCI. In addition, it permits the monitoring of the intact TBBPA molecule through the soft ionization of ESI, resulting in improved method selectivity and accuracy. Frederiksen et al. [104] compared LC-MS2 to GC-MS for the determination of TBBPA and concluded that LC-MS2 is the method of choice, not only because derivatisation is not needed, but also because of its higher sensitivity and better detection. LC-MS2 using QqQ and APCI source was performed for the analysis of 38 BFRs in wastewater, finding decabromodiphenylethane (DBDPE), bis(2-ethyl-1-hexyl)tetrabromophthalate (BEHTBP), and TBBPA at ng·L−1 levels [105]. Bacaloni et al. [106] proposed an LC-MS2 method for the simultaneous determination of TBBPA and five PBDEs in water samples. LIT mass spectrometer, coupled with an APPI source, was operated in the negative ion mode and each compound was quantified operating in MRM obtaining LOQs of 0.2–3.3 ng·L−1, except for one compound. PBDEs were poorly retained by SPE from river water and sewage treatment plant effluent samples; thus LLE by n-hexane was used for these samples.


#### 2.3.2. Solid Samples

Due to its low solubility in water (0.72 mg·L−1) and high log Kow (4.5), TBBPA is likely to be associated with suspended particulate matter once released in the water column and ultimately buried in sediments [107, 108]. However, due to the lower bioaccumulation potential, TBBPA presents lower concentrations than PBDEs and HBCD in the environment. IT-MS was reported for the determination of TBBPA in sediment and sewage sludge after LC separation [108]. Although the ion suppression of the TBBPA signal due to matrix components in the ESI process was not high, sewage-sludge extracts suffered greatly from ion suppression and an extensive cleanup was required to minimize this effect.The distribution of HBCD isomers in suspended sediments from Detroit River was analyzed by QqQ, with an ESI source operated in negative mode and detection by MRM but using ASE as extraction technique [109]. LOD of 10 pg on column was estimated for individual HBCD diastereoisomers. An LC-IT-MS method, employing ESI operated in a negative ionization mode, was developed to determine HBCD diastereoisomers in marine sediment samples, obtaining LOQs ranged from 25 to 40 pg·g−1 (dw). Target analytes were extracted from sediment samples by MAE. Efficiency of this technique was compared with Soxhlet extraction and PLE and the results obtained showed that MAE provides better extraction efficiencies than either PLE or Soxhlet extraction [110].LC-ESI-MS2-based method was developed by Chu et al. [107] for the simultaneous determination of TBBPA, as well as lower brominated BPA analogues, in sediment and sludge samples. LOQs for both kind of samples were in the range 0.02–0.15 ng·g−1 (dw).Hybrid mass spectrometer (LC-QqLIT) with an ESI interface was proposed by Guerra et al. to analyze TBBPA and related compounds (bisphenol A (BPA), monobromobisphenol A (MonoBBPA), dibromobisphenol A (DiBBPA), and tribromobisphenol A (TriBBPA)) in sewage-sludge and sediment samples. Sample extraction was based on the use of ultrasonication SPE, allowing for LODs in the range of 0.6–2.7 ng·g−1 and 1.4–66 ng·g−1 for sediment and sludge samples, respectively [111].ESI, APPI, and APCI sources were tested in the determination of HBCDs and TBBPA in sewage-sludge samples [112]. In this study, involving the use of UHPLC-MS2 and PLE, APCI gave a higher sensitivity than APPI while for TBBPA-bis, APCI and APPI showed a similar performance. ESI was the best option for TCBPA, TBBPA, and HBCDs. Figure 4 shows the total ion current transition of target analytes using APCI as an ionization source.TIC of transitions of tetra-BDE (a), penta-BDE (b), esa-BDE (c), epta-BDE (d), and octa-BDE (e) obtained from PLE extraction and UHPLC-APCI/MS/MS analysis of NIST Standard Reference Material New York/New Jersey Waterway Sediment 1944. From reference [112].
(a)
(b)
(c)
(d)
(e)


## 2.1. Pharmaceuticals Compounds

Among new contaminants, pharmaceuticals belong to a group of an increasing interest due to their pharmacological activity and rising consumption deriving from their use in human and veterinary medicine [33, 34]. Moreover, due to their ubiquitous presence in the environment arising from continual input into the aquatic compartment, they are considered as “pseudo” persistent pollutants [35]. The discharge of therapeutic agents in effluents from production facilities, hospitals and private households, improper disposal of unused drugs, and the direct discharge of veterinary medicines leads to the contamination of environmental waters, and wastewater-treatment plants are considered to be a major source [33, 34, 36–38]. Biological treatment in WWTPs affects only the partial removal of a wide range of microcontaminants, especially polar ones, which are discharged into the final effluent. Thus, it has become evident that the application of more enhanced technologies may be crucial to full the requirements to recycle municipal and industrial wastewaters as drinking water. However, the removal of polar contaminants during drinking water treatment is incomplete. This fact was demonstrated by Ternes et al. when they investigated the elimination of selected pharmaceuticals, such as clofibric acid, bezafibrate, or carbamazepine, during drinking water treatment at the pilot-plant scale and in real waterworks in Germany [39]. The concentration of pharmaceuticals in water can vary between a few nanograms per liter to the micrograms per liter levels. These levels have to be removed in order to achieve the drinking water quality and to protect the water resources. Therefore, the concentrations and identities of these contaminants in water have to be monitored during the entire water purification and transportation process.Antibiotics, followed by steroid compounds, analgesics, and nonsteroidal anti-inflammatory drugs (NSAIDs), are the most widely studied pharmaceuticals. Table1 shows the diverse determinations of these compounds in environmental samples.Table 1
Determination of pharmaceutical compounds in environmental samples by LC coupled to mass spectrometry.
Compounds
Samples
Extraction
Determination
Analytical parameters
Reference
SMMX,  SDMX, SMXZ, STZL, SCPD, SMRZ,  SMTZ, OXTC, MCLN, DOXN, MECN, CTCL, DEMN, and TCLN
River water, sewage and agricultural wastewater
Online SPE
LC-MSESI (PI)
Recoveries: 74.3–116.5%LOQs: 0.09–0.11 μg·L−1
[40]
ENR, LOM, LVFX, FLX, SPFX, AMX, OTC, and SQX
Lake water, river water and sewage effluent
MIP
LC-Qq-ITESI (PI)MRM
Recoveries: 76.3–94.2%RSD < 9.1%LODs: 3.2–6.2 ng·L−1
[41]
4-Acetamidophenol, carbamazepine, (+)-cis-diltiazem hydrochloride, norfluoxetine hydrochloride, ranitidine hydrochloride, sulfamethoxazole, caffeine, trimethoprim, atorvastatin, lovastatin, levofloxacin, and sertraline
River water
SPE
UHPLC-QqQESI (PI)MRM
Mean recovery: 77.9%Mean RSD: 7.3%LODs < 4.1 ng·L−1
[47]
28 basic/neutral pharmaceuticals
River water
SPE
UHPLC-QqQESI (PI)MRM
LOQs: 0.3–50 ng·L−1
[48]
18 androgens and progestogens
River water and wastewater
SPE
UHPLC-QqQESI (PI)MRM
Recoveries: 77–100%RSD: 1.7–12%LODs: 0.01–50 ng·L−1
[51]
49 pharmaceuticals and 6 metabolites
Wastewater
SPE
UHPLC-QqLITESI (PI and NI)MRM and IDA
Recoveries: 55–111%RDS < 5%LODs: 0.02–50 ng·L−1
[52]
Ketoprofen, naproxen, diclofenac, and ibuprofen
Sewage sludge
HF-LPME
LC-MSESI (NI)SIM
Recoveries: 52–63%RSDs:  0.5–7%LODs < 10 μg·L-1
[58]
Levofloxacin, norfloxacin, ciprofloxacin, and enrofloxacin
Marine sediments and sewage sludge
MAME
LC-QqQESI (PI)MRM
Recoveries > 73%RSD < 8%LODs: 0.15–0.55 μg·kg−1
[60]
Ibuprofen, diclofenac, and salicylic acid
Wastewater
HF-LPME
LC-MS/MS
Recoveries: 52–100%RSDs:  1.1–1.6%.LODs: 20–300 ng·L−1
[114]
Ibuprofen, naproxen, clofibric acid, piroxicam, ketorolac, bezafibrate, fenoprofen, diclofenac, and indomethacin
Wastewater
HF-LPME
LC-MS/MS
Recoveries: 80–111%RSDs: 3.4–32%LOQs:  0.5–42 ng·L−1
[115]
Estrone, 17β-estradiol, estriol, ethynyl estradiol, and diethylstilbestrol
Surface water and wastewater
In-tube SPME
LC/MS/MS
Recoveries: 86.1–106.8LODs: 2.7–11.7 ng·L−1
[116]
36 endocrine-disrupting chemicals, including estrogens and progestogens
Potable and river water
SPE
UHPLC-QqTOF
Recoveries: 46%–134%LODs < 0.72 ng·L−1
[117]
17β-estradiol, estriol, and 17α-ethinylestradiol
Sewage sludge
MAE
LC-QqQESI (PI)MRM
Recoveries: 71.7–103.1%RSD < 12%LODs: 0.6–3.5 μg·kg−1
[63]
28 estrogenic compounds
Sewage sludge
UAE
LC-QqQESI (PI and NI)MRM
Recoveries:  44–200%RSD: 0.6–11.6%LODs: 0.08–2.06 μg·kg−1
[64]
Oestrone, testosterone, androstenedione, norethindrone, levonorgestrel, and progesterone
Soil
PLE
LC-QqQESI (PI)MRM
Recoveries: 45–100%RSD: 2.2–10.3%LODs: 0.08–2.84 μg·kg−1
[65]
Estrone, 17α-estradiol, 17β-estradiol, estriol, 17α-ethinylestradiol and diethylstilbestrol, and five conjugates
Sewage sludge
PLE
LC-QqQESI (PI)MRM
Recoveries > 81%RSD < 6%LODs < 26 μg·kg−1
[66]
α-estradiol, β-estradiol, estriol,estrone, ethynylestradiol and their sulfate, glucuronide, and acetate conjugates
River sediments
MAE
LC-Qq-ITESI (NI)MRM
Recoveries: 83–107%RSD: 4.9–9.6%LODs < 1 μg·kg−1
[67]
Abbreviations: LC: liquid chromatography; UHPLC: ultrahigh pressure liquid chromatography; MS: mass spectrometry; QqQ: triple quadrupole; IT: ion trap; LIT: lineal ion trap; ESI: electrospray ionization; APCI: atmospheric pressure chemical ionization; APPI: atmospheric pressure photoionization; NI: negative ion mode of ionisation; PI: positive ion mode of ionisation; SIM: selected ion monitoring; MRM: multiple reaction monitoring; SRM: selected reaction monitoring.
SPE: solid phase extraction; HF-LPME: hollow-fiber liquid-phase microextraction; MIP: molecularly imprinted polymer; UAE: ultrasound assisted extraction; PLE: pressurised liquid extraction; MAE: microwave-assisted extraction; MAME: microwave-assisted micellar extraction.
RSD: relative standard deviation; LOQ: limit of quantification; LOD: limit of detection.
SMMX: sulfamonomethoxine; SDMX: sulfadimethoxine; SMXZ: sulfamethoxazole; STZL: sulfathiazole; SCPD: sulfachloropyridazine; SMRZ: sulfamerazine; SMTZ: sulfamethazine; OXTC: oxytetracycline HCl; MCLN: minocycline HCl; DOXN: doxycycline hyclate; MECN: meclocycline sulfosalicylate; CTCL: chlortetracycline HCl; DEMN: democlocycline HCl; TCLN: tetracycline.
ENR: enrofloxacin; LOM: lomefloxacin; LVFX: levofloxacin; FLX: fleroxacin; SPFX: sparfloxacin; AMX: amoxicillin; OTC: oxytetracycline; SQX: sulfaquinoxaline.


### 2.1.1. Liquid Samples

Methods of sample preparation and extraction for pharmaceuticals have evolved significantly for aqueous phases since they were first described as early as the late 1980s. The traditional sample preparation method, liquid-liquid extraction (LLE), has largely been replaced by solid-phase extraction (SPE) for the aqueous matrices.Regarding separation and detection techniques, LC, combined with MS or MS2, is the most suitable technique to separate and detect pharmaceutical residues or metabolites in environmental samples. Most of the pharmaceutical compounds are not very volatile and some are highly polar, containing ionizable functional groups. It requires additional derivatization steps that may involve more labor and time, and cause unwanted contamination in the sample. Many antibiotics are nonvolatile with a high molecular weight, which respond well to ESI interface operating in the positive ion mode of ionization; therefore LC-MS or LC-MS2 is often selected for their separation and analysis. When using a single MS step, selected-ion monitoring, SIM, is preferred for increased analytical sensitivity and selectivity in complex matrices such as wastewaters. Choi et al. [40] applied this methodology for the simultaneous analysis of seven tetracycline antibiotics and sulfonamide antibiotics from agricultural wastewater samples and sewage effluent samples. They combined the pretreatment technique, SPE, with LC-MS through online connection. This type of connection suppressed the target loss by keeping the cartridge from drying, which resulted in improvement on the recovery and saving of the analytical time. The average LOQ achieved was between 0.09 and 0.11 μg·L−1 for tetracycline antibiotics and sulfonamide antibiotics, respectively. Chen et al. [41], using IT-MS, reached LODs in the range of 3.2–6.2 ng·L−1 when they determined fluoroquinolones in water samples. The target compounds were extracted from samples by molecularly imprinted polymer (MIP) as sorbent. ESI was performed in positive mode and the data acquisition was performed in multiple reaction monitoring (MRM).Some works can be found in the bibliography which use hybrid quadrupole instruments coupled to conventional liquid chromatography systems for the analysis of pharmaceuticals in waters. For instance, Martínez Bueno et al. [42] developed a method for the determination of 38 pharmaceuticals and 10 metabolites by LC-MS2 using hybrid triple-quadrupole linear ion trap mass spectrometer in combination with time-of-flight mass spectrometry operating under SRM mode in both positive and negative ESI. This methodology was successfully applied to a monitoring study intended to characterize wastewater effluents of six sewage treatment plants in Spain. A different MS combination, QqLIT, was proposed by Gros et al. [43] for the determination of 73 pharmaceuticals by using both SRM and information-dependent analysis (IDA) acquisition modes with a total analysis time of 87 min. The method developed was applied to the analysis of various influent and effluent wastewaters.The combination of UHPLC with an MS detector appears to be a suitable approach that fulfills key requirements in terms of sensitivity, selectivity, and peak-assignment certainty for the rapid determination of analytes at low concentrations in complex matrices. Modern QqQ instruments operating in the SRM mode are preferred for targeted analysis, while TOF-MS analyzers are particularly useful for nontargeted analysis. Batt et al. [44] developed a UHPLC method coupled to a QqQ mass spectrometer for the determination of 48 drugs and 6 metabolites in wastewater and surface waters. However, total analysis time was 48 min since four chromatographic conditions were used to determine all the compounds. Langford and Thomas [45] used UHPLC-QqQ with an ESI source; however, chromatographic separation of the 40 pharmaceuticals from hospital effluents took more than 50 min. A different MS analyzer was selected by Petrovic et al. [46] who developed an UHPLC method coupled to a Q-TOF mass spectrometer for the determination of 29 pharmaceuticals in wastewater in 14 min.Conley et al. [47] described the determination of 13 pharmaceuticals and 1 metabolite in less than 4 min using UHPLC interfaced to a QqQ mass spectrometer with an ESI source. The mass analyzer operated in positive ionization mode for all analytes. The method was applied to samples of surface water collected from the Upper Tennessee River Basin. The same technique was applied by Kasprzyk-Hordern et al. [48] for the determination of 28 basic/neutral pharmaceuticals in river water samples from UK and Poland and fifteen compounds were determined at levels ranging from nanograms to micrograms per liter. In this case they achieved the separation of the target compounds in 16 min.Considerable attention had been focused on the occurrence of steroid hormones in the environment since recent studies have documented that the exposure of fish to municipal wastewater effluents affects the reproductive physiology and behavior in many fish species at ng·L−1 or even pg·L−1 levels [49, 50]. Chang et al. [51] developed a method for the simultaneous determination of eighteen androgens and progestogens in environmental waters by using UHPLC-MS2. Mass spectrometry was performed using a triple-quadrupole detector which was operated with ESI in the positive ion mode. After SPE procedure, a silica cartridge was used to purify the extract and reduce the signal suppression due to coeluting interferences. The developed method was applied to the analysis of these compounds in wastewater and surface-water samples and LODs for the eighteen analytes in the influent, effluent, and surface-water samples were in the ranges 0.20–50, 0.04–20, and 0.01–12 ng·L−1, respectively.Hybrid mass spectrometers have also been used in combination with UHPLC to determine pharmaceutical compounds. Recently, Huerta-Fontela et al. [52] developed a method for the determination of 49 pharmaceuticals and 6 metabolites in six wastewater treatment plants using the dual acquisition modes of a hybrid triple-quadrupole linear ion trap system. The proposed method enabled all the 55 compounds to be separated chromatographically in less than 9 min (6.3 min positive mode and 2.7 min negative mode) with a total analysis time of 18 min.


### 2.1.2. Solid Samples

Despite the rather low lipophilicity of pharmaceuticals, interaction of the polar functional groups of them with organic matter and/or minerals may result in adsorption to solids. Furthermore, the application of sewage sludge as a fertilizer to the agricultural land and the reuse of manure containing veterinary medicines may also introduce pharmaceuticals into the soil. Animal origin pharmaceuticals, including aquaculture-derived compounds, contribute significantly to the occurrence of pharmaceuticals in solid matrices due to their patterns of application. Sewage sludge is the main solid produced in sewage treatment plants and the European Union (EU) promotes the use of sewage sludge as a fertilizer on agricultural land. Therefore it is important to know the occurrence of contaminants in sewage-sludge samples as those could reach surface or ground waters.The presence of pharmaceuticals in sediment, soil, and sewage sludge has been studied extensively. Analytical methods for the determination of specific groups of pharmaceuticals, including NSAIDs, antidepressants, antibiotics, andβ-blockers [53, 54], and multiclass methods have been reported in recent years. Soxhlet extraction method for soil or sediment has been replaced by PLE, MAE, and UAE because of the time-consuming nature and high usage of hazardous organic solvents. Sample extracts obtained from solid matrices are most of the time with interfering co-extracts, which dictate an additional cleanup before LC analysis. Soil or sediment sample preparation needs to combine additional cleanup or purification steps, mainly SPE after the extraction step in the solvent due to the complexity of environmental samples [55, 56].Haller et al. [57] used LC-MS and ESI with SIM mode to measure seven veterinary antibiotics in manure and reported 100 μg·kg−1 as LOQ. This technique was also applied by Sagristà et al. [58] for the direct determination of four NSAIDs in dried sludge from a sewage treatment plant (Figure 2). Extraction experiments were carried out using a magnetic stirrer at 660 rpm for several hours and then a three-phase hollow-fiber liquid-phase microextraction (HF-LPME) was applied. This microextraction procedure allowed for the enrichment factors about 3000 times for all analytes. Data acquisition was performed in negative ion mode with SIM. LODs and LOQs were about 10 and 33 μg·L−1, respectively.Single ion monitoring chromatograms obtained by LC-MS from reagent water spiked at 0.4 mg·L−1. (a) m/z = 294 (diclofenac), (b) m/z = 253 (ketoprofen), (c) m/z = 229 (naproxen), and (d) m/z = 205 (ibuprofen). From reference [58].
(a)
(b)
(c)
(d)Determination by Qq-IT, with an ESI source operated in positive mode, has been used to characterize the persistence of tetracyclines in soil fertilized with liquid manure. The analytes were extracted from soil samples by vortex with citrate buffer and ethyl acetate and the LOQ was 5μg·kg−1 for all compounds [59]. More recently, microwave-assisted micellar extraction combined with a QqQ mass spectrometer and ESI source, in a positive mode, was applied for the analysis of fluoroquinolone antibiotics in coastal marine sediments and in sewage-sludge samples. This extraction technique, which uses a micellar solution as extractant and LC-MS2, allowed LODs and LOQs between 0.15–0.55 μg·kg−1 and 0.49–1.85 μg·kg−1, respectively [60]. In addition, Jacobsen et al. [61] applied two different LC-MS2 methods to quantify eight antibiotics from different classes in soil and reported LOQs in the range 1.1–12.8 μg·kg−1. Löffler and Ternes [62] used two different APCI-MS2 methods for ten acidic pharmaceuticals in negative mode and ESI-MS2 for seven antibiotics in positive mode to determine residues in river sediment. This study illustrated that different ionization methods can be adapted to the characteristics of the compounds being examined.Estrogenic compounds are medium polar to relatively nonpolar substances, with log Kow values in the range 2.5–5.3. Consequently, we can expect sorption of estrogens to the suspended matter and a tendency of them to accumulate in soil and sediments. Several estradiol-mimicking compounds, including 17β-estradiol, estriol, and 17α-ethinylestradiol, were determined from sewage-sludge samples by using MAE followed by LC-MS2 with ESI in a positive mode. The method provided LODs ranging from 0.6 to 3.5 μg·kg−1 [63]. A greater group of steroids, including natural and synthetic estrogens, androgens, progestogens, and glucocorticoids, were determined in the same type of sample by using UAE followed, with analysis; by rapid resolution LC-MS2. In this case, a triple quadrupole detector was used, which was operated with ESI in both negative and positive modes. LODs for the 28 analytes were 0.08–2.06 μg·kg−1 [64]. LC-ESI(PI)-MS2 and PLE as an extraction technique madeit possible to determine the traces of steroid hormones (including oestrogen, androgens, and progestogens) in soil with LODs in the range 0.08–0.89 μg·kg−1. The results obtained showed ionization suppression for all the analytes in proportions ranging up to nearly 50% [65]. Using the same technique, with ESI (NI), Nieto et al. [66] achieved the determination of a greater number of natural and synthetic estrogens in sewage sludge. The MRM mode enabled LODs lower than 26 μg·kg−1 of the dry weight of sewage sludge for most of target analytes. Using an IT-MS equipped with ESI (NI) source, after extraction by MAE, Matjıcek et al. [67] carried out the simultaneous separation and determination of five hormones and their sulfate, glucuronide, and acetate conjugates in river sediments reaching LODs lower than 1 μg·kg−1.


## 2.1.1. Liquid Samples

Methods of sample preparation and extraction for pharmaceuticals have evolved significantly for aqueous phases since they were first described as early as the late 1980s. The traditional sample preparation method, liquid-liquid extraction (LLE), has largely been replaced by solid-phase extraction (SPE) for the aqueous matrices.Regarding separation and detection techniques, LC, combined with MS or MS2, is the most suitable technique to separate and detect pharmaceutical residues or metabolites in environmental samples. Most of the pharmaceutical compounds are not very volatile and some are highly polar, containing ionizable functional groups. It requires additional derivatization steps that may involve more labor and time, and cause unwanted contamination in the sample. Many antibiotics are nonvolatile with a high molecular weight, which respond well to ESI interface operating in the positive ion mode of ionization; therefore LC-MS or LC-MS2 is often selected for their separation and analysis. When using a single MS step, selected-ion monitoring, SIM, is preferred for increased analytical sensitivity and selectivity in complex matrices such as wastewaters. Choi et al. [40] applied this methodology for the simultaneous analysis of seven tetracycline antibiotics and sulfonamide antibiotics from agricultural wastewater samples and sewage effluent samples. They combined the pretreatment technique, SPE, with LC-MS through online connection. This type of connection suppressed the target loss by keeping the cartridge from drying, which resulted in improvement on the recovery and saving of the analytical time. The average LOQ achieved was between 0.09 and 0.11 μg·L−1 for tetracycline antibiotics and sulfonamide antibiotics, respectively. Chen et al. [41], using IT-MS, reached LODs in the range of 3.2–6.2 ng·L−1 when they determined fluoroquinolones in water samples. The target compounds were extracted from samples by molecularly imprinted polymer (MIP) as sorbent. ESI was performed in positive mode and the data acquisition was performed in multiple reaction monitoring (MRM).Some works can be found in the bibliography which use hybrid quadrupole instruments coupled to conventional liquid chromatography systems for the analysis of pharmaceuticals in waters. For instance, Martínez Bueno et al. [42] developed a method for the determination of 38 pharmaceuticals and 10 metabolites by LC-MS2 using hybrid triple-quadrupole linear ion trap mass spectrometer in combination with time-of-flight mass spectrometry operating under SRM mode in both positive and negative ESI. This methodology was successfully applied to a monitoring study intended to characterize wastewater effluents of six sewage treatment plants in Spain. A different MS combination, QqLIT, was proposed by Gros et al. [43] for the determination of 73 pharmaceuticals by using both SRM and information-dependent analysis (IDA) acquisition modes with a total analysis time of 87 min. The method developed was applied to the analysis of various influent and effluent wastewaters.The combination of UHPLC with an MS detector appears to be a suitable approach that fulfills key requirements in terms of sensitivity, selectivity, and peak-assignment certainty for the rapid determination of analytes at low concentrations in complex matrices. Modern QqQ instruments operating in the SRM mode are preferred for targeted analysis, while TOF-MS analyzers are particularly useful for nontargeted analysis. Batt et al. [44] developed a UHPLC method coupled to a QqQ mass spectrometer for the determination of 48 drugs and 6 metabolites in wastewater and surface waters. However, total analysis time was 48 min since four chromatographic conditions were used to determine all the compounds. Langford and Thomas [45] used UHPLC-QqQ with an ESI source; however, chromatographic separation of the 40 pharmaceuticals from hospital effluents took more than 50 min. A different MS analyzer was selected by Petrovic et al. [46] who developed an UHPLC method coupled to a Q-TOF mass spectrometer for the determination of 29 pharmaceuticals in wastewater in 14 min.Conley et al. [47] described the determination of 13 pharmaceuticals and 1 metabolite in less than 4 min using UHPLC interfaced to a QqQ mass spectrometer with an ESI source. The mass analyzer operated in positive ionization mode for all analytes. The method was applied to samples of surface water collected from the Upper Tennessee River Basin. The same technique was applied by Kasprzyk-Hordern et al. [48] for the determination of 28 basic/neutral pharmaceuticals in river water samples from UK and Poland and fifteen compounds were determined at levels ranging from nanograms to micrograms per liter. In this case they achieved the separation of the target compounds in 16 min.Considerable attention had been focused on the occurrence of steroid hormones in the environment since recent studies have documented that the exposure of fish to municipal wastewater effluents affects the reproductive physiology and behavior in many fish species at ng·L−1 or even pg·L−1 levels [49, 50]. Chang et al. [51] developed a method for the simultaneous determination of eighteen androgens and progestogens in environmental waters by using UHPLC-MS2. Mass spectrometry was performed using a triple-quadrupole detector which was operated with ESI in the positive ion mode. After SPE procedure, a silica cartridge was used to purify the extract and reduce the signal suppression due to coeluting interferences. The developed method was applied to the analysis of these compounds in wastewater and surface-water samples and LODs for the eighteen analytes in the influent, effluent, and surface-water samples were in the ranges 0.20–50, 0.04–20, and 0.01–12 ng·L−1, respectively.Hybrid mass spectrometers have also been used in combination with UHPLC to determine pharmaceutical compounds. Recently, Huerta-Fontela et al. [52] developed a method for the determination of 49 pharmaceuticals and 6 metabolites in six wastewater treatment plants using the dual acquisition modes of a hybrid triple-quadrupole linear ion trap system. The proposed method enabled all the 55 compounds to be separated chromatographically in less than 9 min (6.3 min positive mode and 2.7 min negative mode) with a total analysis time of 18 min.


## 2.1.2. Solid Samples

Despite the rather low lipophilicity of pharmaceuticals, interaction of the polar functional groups of them with organic matter and/or minerals may result in adsorption to solids. Furthermore, the application of sewage sludge as a fertilizer to the agricultural land and the reuse of manure containing veterinary medicines may also introduce pharmaceuticals into the soil. Animal origin pharmaceuticals, including aquaculture-derived compounds, contribute significantly to the occurrence of pharmaceuticals in solid matrices due to their patterns of application. Sewage sludge is the main solid produced in sewage treatment plants and the European Union (EU) promotes the use of sewage sludge as a fertilizer on agricultural land. Therefore it is important to know the occurrence of contaminants in sewage-sludge samples as those could reach surface or ground waters.The presence of pharmaceuticals in sediment, soil, and sewage sludge has been studied extensively. Analytical methods for the determination of specific groups of pharmaceuticals, including NSAIDs, antidepressants, antibiotics, andβ-blockers [53, 54], and multiclass methods have been reported in recent years. Soxhlet extraction method for soil or sediment has been replaced by PLE, MAE, and UAE because of the time-consuming nature and high usage of hazardous organic solvents. Sample extracts obtained from solid matrices are most of the time with interfering co-extracts, which dictate an additional cleanup before LC analysis. Soil or sediment sample preparation needs to combine additional cleanup or purification steps, mainly SPE after the extraction step in the solvent due to the complexity of environmental samples [55, 56].Haller et al. [57] used LC-MS and ESI with SIM mode to measure seven veterinary antibiotics in manure and reported 100 μg·kg−1 as LOQ. This technique was also applied by Sagristà et al. [58] for the direct determination of four NSAIDs in dried sludge from a sewage treatment plant (Figure 2). Extraction experiments were carried out using a magnetic stirrer at 660 rpm for several hours and then a three-phase hollow-fiber liquid-phase microextraction (HF-LPME) was applied. This microextraction procedure allowed for the enrichment factors about 3000 times for all analytes. Data acquisition was performed in negative ion mode with SIM. LODs and LOQs were about 10 and 33 μg·L−1, respectively.Single ion monitoring chromatograms obtained by LC-MS from reagent water spiked at 0.4 mg·L−1. (a) m/z = 294 (diclofenac), (b) m/z = 253 (ketoprofen), (c) m/z = 229 (naproxen), and (d) m/z = 205 (ibuprofen). From reference [58].
(a)
(b)
(c)
(d)Determination by Qq-IT, with an ESI source operated in positive mode, has been used to characterize the persistence of tetracyclines in soil fertilized with liquid manure. The analytes were extracted from soil samples by vortex with citrate buffer and ethyl acetate and the LOQ was 5μg·kg−1 for all compounds [59]. More recently, microwave-assisted micellar extraction combined with a QqQ mass spectrometer and ESI source, in a positive mode, was applied for the analysis of fluoroquinolone antibiotics in coastal marine sediments and in sewage-sludge samples. This extraction technique, which uses a micellar solution as extractant and LC-MS2, allowed LODs and LOQs between 0.15–0.55 μg·kg−1 and 0.49–1.85 μg·kg−1, respectively [60]. In addition, Jacobsen et al. [61] applied two different LC-MS2 methods to quantify eight antibiotics from different classes in soil and reported LOQs in the range 1.1–12.8 μg·kg−1. Löffler and Ternes [62] used two different APCI-MS2 methods for ten acidic pharmaceuticals in negative mode and ESI-MS2 for seven antibiotics in positive mode to determine residues in river sediment. This study illustrated that different ionization methods can be adapted to the characteristics of the compounds being examined.Estrogenic compounds are medium polar to relatively nonpolar substances, with log Kow values in the range 2.5–5.3. Consequently, we can expect sorption of estrogens to the suspended matter and a tendency of them to accumulate in soil and sediments. Several estradiol-mimicking compounds, including 17β-estradiol, estriol, and 17α-ethinylestradiol, were determined from sewage-sludge samples by using MAE followed by LC-MS2 with ESI in a positive mode. The method provided LODs ranging from 0.6 to 3.5 μg·kg−1 [63]. A greater group of steroids, including natural and synthetic estrogens, androgens, progestogens, and glucocorticoids, were determined in the same type of sample by using UAE followed, with analysis; by rapid resolution LC-MS2. In this case, a triple quadrupole detector was used, which was operated with ESI in both negative and positive modes. LODs for the 28 analytes were 0.08–2.06 μg·kg−1 [64]. LC-ESI(PI)-MS2 and PLE as an extraction technique madeit possible to determine the traces of steroid hormones (including oestrogen, androgens, and progestogens) in soil with LODs in the range 0.08–0.89 μg·kg−1. The results obtained showed ionization suppression for all the analytes in proportions ranging up to nearly 50% [65]. Using the same technique, with ESI (NI), Nieto et al. [66] achieved the determination of a greater number of natural and synthetic estrogens in sewage sludge. The MRM mode enabled LODs lower than 26 μg·kg−1 of the dry weight of sewage sludge for most of target analytes. Using an IT-MS equipped with ESI (NI) source, after extraction by MAE, Matjıcek et al. [67] carried out the simultaneous separation and determination of five hormones and their sulfate, glucuronide, and acetate conjugates in river sediments reaching LODs lower than 1 μg·kg−1.


## 2.2. Personal Care Products

Personal care products (PCPs) constitute a group of emerging contaminants which have received a considerable attention in recent years. PCPs are regarded as being potentially hazardous compounds as many of them are ubiquitous and persistent and due to their continuous introduction might cause unwanted effects in the environment.The principal pathway by which PCPs enter the environment is disposal in urban receiving waters from individual households, after showering and bathing. A variety of PCPs have been detected everywhere at the ng·L−1 concentration level in the effluents of WWTPs, since conventional water-treatment processes do not seem to be sufficient to remove PCPs from sewage water (30–90% efficiency) [68–74]. The occurrence of PCPs in municipal sewage effluent and other environmental samples could negatively impact the health of the ecosystem and the health of humans, due to the persistent and long-term chronic exposure of aquatic organisms to the concentrations of PCPs [68]. Moreover, there is some evidence of potential interactive effects of PCPs, so that low doses may lead to cumulative stress and synergic toxicity effects in exposed organisms [68, 75]. PCPs, such as UV screens, insect repellents, and some synthetic musk fragrances, have also been suspected endocrine-disrupting compounds (EDCs) (i.e., compounds that can mimic the natural hormones of animals) [71, 73, 74].Nowadays, in order to achieve greater protection to solar radiation, UV filters are added not only to cosmetics to be used for sunbathing but also to daily cosmetic products, such as face day creams, after-shave products, makeup formulations, lipsticks, and shampoos, thus resulting in an increase in the use of UV filters. Moreover, they can be found as additives in textiles, plastics, paints, car polishes, and so forth [76]. This excessive use of UV filters has led to their presence in the aquatic environment and increased their potential for endocrine and developmental toxicity [77, 78]. The increasing usage of these compounds, combined with their moderate-to-high water solubility, has led to the appearance of some of them in the aquatic environment. As regards toxicological effects, in vivo and in vitro studies have demonstrated that some hydroxylated benzophenones exert estrogenic and antiandrogenic actions [79].Triclosan, triclocarban and methyl-triclosan are bactericides widely used in household and personal-care products, for example, shampoos, soaps, creams, mouthwash, and toothpaste [80]. Triclosan is found to be acutely toxic to some aquatic organisms and it has been also shown to photo transform into members of the dioxin family, which is known as the most carcinogenic chemicals in the world [81]. Although a relatively few data exist about the toxicity of triclocarban, it has been found to impair reproduction in laboratory rats and that some of its degradation products are carcinogenic. Methyl-triclosan, a metabolite of triclosan, is more lipophilic and environmentally persistent, suggesting its relatively high bioaccumulation potential in aquatic organisms [82].Table2 illustrates some applications of LC-MS to the determination of PCPs in environmental samples.Table 2
Determination of personal care products in environmental samples by LC coupled to mass spectrometry.
Compounds
Samples
Extraction
Determination
Analytical parameters
Reference
UV filters: BP-1, BP-2, BP-3, BP-4, BP-6, and BP-8
River water and wastewater
SPE
LC-QqQ ESI (NI and PI)MRM
Recoveries: 83–105%LOQs 1–32 ng·L−1
[83]
Triclosan and triclocarban
Wastewater and tap water
IL-DLLME
LC-QqQESI (NI)MRM
Recoveries: 70.0–103.5%RSD 7.0–8.8% LODs: 0.040–0.58 μg·L−1
[84]
Triclocarban
Wastewater effluents
SBSE
LC-QqQ ESI (NI)MRM
Recoveries: 92–96%RSD: 2%LOQ: 10 ng·L−1
[85]
BP-1, BP-3, BP-8, OC, OD-PABAtriclocarban, triclosan,methylparaben, ethylparaben, benzylparaben, propylparaben
Surface water and wastewaters
SPE
UHPLC-QqQESI  (NI and PI)MRM
Recoveries: 20–101%RSD: 1–14%LODs:  20–200 ng·L−1
[86]
53 multiclass emerging pollutants (UV filters and insect repellents, among others)
Tap water, surface water, and wastewater
SPE
LC-qqQESI  (NI and PI)MRM
Recoveries > 60%RSD < 15%LODs: 0.3–30 ng·L−1
[90]
Benzotriazoles (UVP,  UV 329,  UV 326,  UV 328, UV 327, UV 571, and UV 360)
Coastal marine water and wastewater
SPE online
UHPLC-QqQESI (PI)MRM
Recoveries: 65–94%RSD: 6.2–10 %LODs: 0.6–4.1 ng·L−1
[118]
4-HydroxybenzophenoneBP-1, BP-2, BP-3, and BP-8
Sediments and sludge
LLE
LC-QqQESI (NI)MRM
Recoveries: 70–116%RSD: 3.3–13.8% LOQs: 0.06–1.65 ng·g−1
[92]
Biocides, UV filters, and benzothiazoles
Sludge sample
PLE
LC-QqQESI, APCI (NI and PI)MRM
Recoveries: 74–119%RSD < 25%
[93]
Triclosan, triclocarban,methyl paraben, ethyl paraben, propyl paraben, benzyl paraben,OD-PABA, OC, PMDSA, BP-1, BP-3, and  BP-8
Sewage sludge
PLE
UHPLC-QqQESI (NI and PI)MRM
Recoveries: 15–100%RSD ≤ 9%LODs < 8 ng·g−1
[94]
Abbreviations: LC: liquid chromatography; UHPLC: ultrahigh pressure liquid chromatography;  QqQ: triple quadrupole; IT: ion trap; LIT: lineal ion trap; ESI: electrospray ionization; APCI: atmospheric pressure chemical ionization; NI: negative ion mode of ionisation; PI: positive ion mode of ionisation; MRM: multiple reaction monitoring; SRM: selected reaction monitoring.
IL: ionic liquid; LLE: liquid-liquid extraction; SDME: single-drop microextraction; DLLME: dispersive liquid-liquid microextraction; SBSE: stir-bar sorptive extraction; PLE: pressurised liquid extraction.
RSD: Relative standard deviation; LOQ: limit of quantification; LOD: limit of detection.
OC: octocrylene; PMDSA: 2-phenylbenzimidazole-5-sulfonic acid; OD-PABA: octyldimethyl-p-aminobenzoic acid; BP-1: 2,4-dihydroxybenzophenone; BP-2:  2,2′,4,4′-tetrahydroxybenzophenone; BP-3:  2-hydroxy-4-methoxybenzophenone; BP-4: 2-hydroxy-4-methoxybenzophenone-5-sulphonic acid; BP-6:  2,2′-dihydroxy-4,4′-methoxybenzophenone; BP-8: 2,2′-dihydroxy-4-methoxybenzophenone.


### 2.2.1. Liquid Samples

Negreira et al. [83] determined six derivatives of 2-hydroxybenzophenone, which are extensively employed as UV absorbers, in water samples by LC-QqQ using ESI in positive and negative modes, except for one compound (2-hydroxy-4-methoxybenzophenone-5-sulphonic acid) which could be ionized only in a negative mode. Benzophenones were recorded in MRM mode using two transitions per compound. Recoveries from the SPE step remained unaffected by the nature of the matrix; however, the efficiency of ESI was compound and sample dependant. Under optimized conditions, the proposed method provided LOQs from less than 1 to 32 ng·L−1, depending on the compound and the type of water sample.Triple quadrupole is the most common and most useful tool for determining PCPs in high-sensitivity target analysis. This mass spectrometer fitted with an ESI source operating in a negative mode has been used by Zhao et al. to determine triclosan and triclocarban in wastewater and tap water samples (Figure3). Enrichment of target analytes before analysis was carried out by using ionic liquid dispersive liquid-phase microextraction. The sensitivity of the proposed method allowed for LODs in the range 0.04–0.58 μg·L−1 [84]. Klein et al. determined triclocarban in wastewater effluents by LC-QqQ after stir-bar sorptive extraction (SBSE) obtaining an LOQ of 10 ng·L−1 for the target analyte [85]. ESI source was also operated in a negative mode and MRM mode was applied.LC-ESI-MS2 chromatogram obtained from wastewater. (a) Wastewater (b) Wastewater spiked with 0.40 μg·L−1 triclocarban (1) and 2.0 μg·L−1 triclosan (2). From reference [84].
(a)
(b)Pedrouzo et al. [86] determined eleven PCPs, including hydroxylated benzophenones, triclocarban and triclosan, and parabens, (another type of preservatives used in personal care products) by SPE and UHPLC-MS2 in surface and wastewaters in 9 minutes of chromatographic separation. A triple-quadrupole mass spectrometer and ESI in both PI and NI modes were applied. LOQ was 5 ng·L−1 for all the compounds, except for methylparaben (3 ng·L−1). Most of PCPs determined were found in influent waters being methylparaben and propylparaben found at the highest concentration. Both are the most widely used parabens and they are normally used together due to their synergistic preservative effects [87, 88].By using MRM to monitor two transitions between precursor and product ions, it is possible to confirm and quantify the presence of PCPs in waters at very low levels [89]. For example, Rodil et al. [90] developed a method to determine a group of 53 multiclass emerging organic pollutants (included the types mentioned above) by LC-MS2, using ESI in both PI and NI modes, after SPE. The proposed method allowed LODs between 0.3 and 30 ng·L−1. The method was used for the simultaneous determination of target analytes in water samples, including tap, surface, and wastewater. LC-QqIT was the technique chosen for determining the presence of 84 pollutants of different classes in wastewaters, including some PCPs such as sunscreen agents and synthetic musks. Previous to LC-QqIT analysis (ESI in PI and NI modes), wastewater samples were preconcentrated by SPE [91].


### 2.2.2. Solid Samples

Several PCPs (e.g., triclosan, triclocarban, and most UV-filtering compounds) show affinity to solid matrices. As a consequence, to allow the correct evaluation of the ecological impact of these substances, evaluation of their prevalence in solid matrices is important. Several analytical approaches were therefore reported recently.LC-MS2, with ESI operated in negative mode and MRM, was applied by Zhang et al. [92] to analyse benzophenone UV filters in sediment and sludge. The method developed allowed LOQs in the ranges of 0.06–0.33 ng·g−1 dry weight (dw) and 0.1–1.65 ng·g−1 dw for sediment and sludge samples, respectively. ESI and APCI sources, operated in the positive and in the negative ion mode using MRM, were applied by Wick et al. [93] to determine different classes of compounds such as, biocides, UV filters, and benzothiazoles in sludge samples. ESI exhibited a strong ion suppression for most target analytes, while APCI was generally less susceptible to ion suppression which led to higher signal intensities in the samples and consequently to lower LOQs as long as the background noise was not increasing.UHPLC-MS2 was applied by Nieto et al. [94] for the determination of a group of parabens and two UV filters in sewage sludge. In the chromatographic step, after pressurized liquid extraction, the compounds were detected by using tandem mass spectrometry with a triple-quadrupole analyzer with ESI in positive and negative modes. The use of small diameter particles in the chromatographic column allowed the compounds to be eluted in 9 min. LODs and LOQs were lower than 8 μg·kg−1 and 12.5 μg·kg−1 of dw, respectively.


## 2.2.1. Liquid Samples

Negreira et al. [83] determined six derivatives of 2-hydroxybenzophenone, which are extensively employed as UV absorbers, in water samples by LC-QqQ using ESI in positive and negative modes, except for one compound (2-hydroxy-4-methoxybenzophenone-5-sulphonic acid) which could be ionized only in a negative mode. Benzophenones were recorded in MRM mode using two transitions per compound. Recoveries from the SPE step remained unaffected by the nature of the matrix; however, the efficiency of ESI was compound and sample dependant. Under optimized conditions, the proposed method provided LOQs from less than 1 to 32 ng·L−1, depending on the compound and the type of water sample.Triple quadrupole is the most common and most useful tool for determining PCPs in high-sensitivity target analysis. This mass spectrometer fitted with an ESI source operating in a negative mode has been used by Zhao et al. to determine triclosan and triclocarban in wastewater and tap water samples (Figure3). Enrichment of target analytes before analysis was carried out by using ionic liquid dispersive liquid-phase microextraction. The sensitivity of the proposed method allowed for LODs in the range 0.04–0.58 μg·L−1 [84]. Klein et al. determined triclocarban in wastewater effluents by LC-QqQ after stir-bar sorptive extraction (SBSE) obtaining an LOQ of 10 ng·L−1 for the target analyte [85]. ESI source was also operated in a negative mode and MRM mode was applied.LC-ESI-MS2 chromatogram obtained from wastewater. (a) Wastewater (b) Wastewater spiked with 0.40 μg·L−1 triclocarban (1) and 2.0 μg·L−1 triclosan (2). From reference [84].
(a)
(b)Pedrouzo et al. [86] determined eleven PCPs, including hydroxylated benzophenones, triclocarban and triclosan, and parabens, (another type of preservatives used in personal care products) by SPE and UHPLC-MS2 in surface and wastewaters in 9 minutes of chromatographic separation. A triple-quadrupole mass spectrometer and ESI in both PI and NI modes were applied. LOQ was 5 ng·L−1 for all the compounds, except for methylparaben (3 ng·L−1). Most of PCPs determined were found in influent waters being methylparaben and propylparaben found at the highest concentration. Both are the most widely used parabens and they are normally used together due to their synergistic preservative effects [87, 88].By using MRM to monitor two transitions between precursor and product ions, it is possible to confirm and quantify the presence of PCPs in waters at very low levels [89]. For example, Rodil et al. [90] developed a method to determine a group of 53 multiclass emerging organic pollutants (included the types mentioned above) by LC-MS2, using ESI in both PI and NI modes, after SPE. The proposed method allowed LODs between 0.3 and 30 ng·L−1. The method was used for the simultaneous determination of target analytes in water samples, including tap, surface, and wastewater. LC-QqIT was the technique chosen for determining the presence of 84 pollutants of different classes in wastewaters, including some PCPs such as sunscreen agents and synthetic musks. Previous to LC-QqIT analysis (ESI in PI and NI modes), wastewater samples were preconcentrated by SPE [91].


## 2.2.2. Solid Samples

Several PCPs (e.g., triclosan, triclocarban, and most UV-filtering compounds) show affinity to solid matrices. As a consequence, to allow the correct evaluation of the ecological impact of these substances, evaluation of their prevalence in solid matrices is important. Several analytical approaches were therefore reported recently.LC-MS2, with ESI operated in negative mode and MRM, was applied by Zhang et al. [92] to analyse benzophenone UV filters in sediment and sludge. The method developed allowed LOQs in the ranges of 0.06–0.33 ng·g−1 dry weight (dw) and 0.1–1.65 ng·g−1 dw for sediment and sludge samples, respectively. ESI and APCI sources, operated in the positive and in the negative ion mode using MRM, were applied by Wick et al. [93] to determine different classes of compounds such as, biocides, UV filters, and benzothiazoles in sludge samples. ESI exhibited a strong ion suppression for most target analytes, while APCI was generally less susceptible to ion suppression which led to higher signal intensities in the samples and consequently to lower LOQs as long as the background noise was not increasing.UHPLC-MS2 was applied by Nieto et al. [94] for the determination of a group of parabens and two UV filters in sewage sludge. In the chromatographic step, after pressurized liquid extraction, the compounds were detected by using tandem mass spectrometry with a triple-quadrupole analyzer with ESI in positive and negative modes. The use of small diameter particles in the chromatographic column allowed the compounds to be eluted in 9 min. LODs and LOQs were lower than 8 μg·kg−1 and 12.5 μg·kg−1 of dw, respectively.


## 2.3. Flame Retardants

Flame retardant (FR) compounds are a structurally diverse group of chemicals that are added to or reacted with polymers, and they are used in plastics, textiles, electronic circuitry, and other materials to reduce the risk of fire. One of these groups of compounds comprises brominated FRs (BFRs), some of which are ubiquitous, and many of which have been detected in biota, sediments, air, water, marine mammals, and even human milk [95, 96]. BFRs are mainly represented by tetrabromobisphenol A (TBBPA), polybrominated diphenyl ethers (PBDEs), which are aromatic compounds, and the cycloaliphatic compound hexabromocyclododecane (HBCD). Regarding TBBPA, one of the most important and commonly used flame retardants, although the use of TBBPA as an additive is estimated to account for about 10% of the total amount used,excessive non-polymerized TBBPA can be emitted, contaminating the environment [97]. Mainly due to its low bioaccumulation potential, it presents concentration levels lower than those of PBDEs or HBCD in the environment [98]. However, TBBPA, being a phenolic compound, may have a greater adverse effect on humans and wildlife. Likewise, TBBPA can be considered a potential EDC due to the similarities in its structure with 17β-estradiol and thyroxine.LC, coupled to tandem MS, and ESI, APCI or atmospheric pressure photoionization (APPI), represents a valid tool to the determinations of these compounds, since that the determination of some congeners is known to be difficult due to thermal degradation problems and also because a derivatisation step is needed [99–102].Some applications of the use of LC-MS to the determination of these micropollutants in environmental samples are shown in Table3.Table 3
Determination of flame retardants in environmental samples by LC coupled to mass spectrometry.
Compounds
Samples
Extraction
Determination
Analytical parameters
Reference
38 HFRs
Wastewater
SPE
LC-QqQAPCI (NI)MRM
Recoveries 25–132%LOQs 0.1–5.6 μg·L−1
[105]
TBBPA and five PBDEs
Wastewater, river, and drinking water
LLE
LC-LITAPPI (NI)MRM
Recoveries 43–99%RSD < 17%LOQs: 0.2–3.3 ng·L−1
[106]
TBBPA and brominated BPA analogues
Sediment and sludge
Soxhlet
LC-QqQESI (NI) MRM
Recoveries: 70–105%RSD: 4.9–13.1% LOQs 0.02–0.15 ng·g−1
[107]
HBCD isomers
Suspended sediments from Detroit River
ASE
LC-QqQ,ESI (NI) MRM
—
[109]
HBCD diastereoisomers
Marine sediment
MAE
LC-ITESI (NI)
Recoveries: 68–91%RSD: 2–11%LOQs: 25–40 pg·g−1
[110]
TBBPA, BPA, Mono-BBPA, Di-BBPA, and Tri-BBPA
Sewage sludge and sediment
Sonication-SPE
LC-QqLITESI (NI)SRM
Recoveries: 39–120%RSD < 13%LODs: 0.6–2.7 ng·g−1
[111]
HBCDs and TBBPA
Sewage sludge
PLE
UHPLC-MS2 ESI, APPI, APCIMRM
Recoveries: 65–112%LOQs: 0.005–0.14 ng·g−1
[112]
Abbreviations: LC: liquid chromatography; UHPLC: ultrahigh pressure liquid chromatography; MS: mass spectrometry; QqQ: triple quadrupole; IT: ion trap; LIT: lineal ion trap; ESI: electrospray ionization; APCI: atmospheric pressure chemical ionization; APPI: atmospheric pressure photoionization; NI: negative ion mode of ionisation; PI: positive ion mode of ionisation; MRM: multiple reaction monitoring; SRM: selected reaction monitoring.
SPE: solid phase extraction; ASE: assisted solvent extraction; LLE: liquid-liquid extraction; PLE: pressurised liquid extraction; MAE: microwave-assisted extraction.
RSD: relative standard deviation; LOQ: limit of quantification; LOD: limit of detection.
TBBPA: tetrabromobisphenol A; PBDEs: polybrominated diphenyl ethers; BDE: decabrominated diphenyl ether; HBCD: hexabromocyclododecane; HFRs: halogenated flame retardants.


### 2.3.1. Liquid Samples

The use of LC-MS in the determination of TBBPA provides several different detection modes and eliminates the need for the derivatization of the phenolic group. Moreover, it facilitates the use of13C-labelled TBBPA. Tollbäck et al. [103] reported that the most suitable LC-MS interface for TBBPA analysis is ESI operating in a negative ionization mode. ESI gave 30–40 times lower LODs compared to APCI. In addition, it permits the monitoring of the intact TBBPA molecule through the soft ionization of ESI, resulting in improved method selectivity and accuracy. Frederiksen et al. [104] compared LC-MS2 to GC-MS for the determination of TBBPA and concluded that LC-MS2 is the method of choice, not only because derivatisation is not needed, but also because of its higher sensitivity and better detection. LC-MS2 using QqQ and APCI source was performed for the analysis of 38 BFRs in wastewater, finding decabromodiphenylethane (DBDPE), bis(2-ethyl-1-hexyl)tetrabromophthalate (BEHTBP), and TBBPA at ng·L−1 levels [105]. Bacaloni et al. [106] proposed an LC-MS2 method for the simultaneous determination of TBBPA and five PBDEs in water samples. LIT mass spectrometer, coupled with an APPI source, was operated in the negative ion mode and each compound was quantified operating in MRM obtaining LOQs of 0.2–3.3 ng·L−1, except for one compound. PBDEs were poorly retained by SPE from river water and sewage treatment plant effluent samples; thus LLE by n-hexane was used for these samples.


### 2.3.2. Solid Samples

Due to its low solubility in water (0.72 mg·L−1) and high log Kow (4.5), TBBPA is likely to be associated with suspended particulate matter once released in the water column and ultimately buried in sediments [107, 108]. However, due to the lower bioaccumulation potential, TBBPA presents lower concentrations than PBDEs and HBCD in the environment. IT-MS was reported for the determination of TBBPA in sediment and sewage sludge after LC separation [108]. Although the ion suppression of the TBBPA signal due to matrix components in the ESI process was not high, sewage-sludge extracts suffered greatly from ion suppression and an extensive cleanup was required to minimize this effect.The distribution of HBCD isomers in suspended sediments from Detroit River was analyzed by QqQ, with an ESI source operated in negative mode and detection by MRM but using ASE as extraction technique [109]. LOD of 10 pg on column was estimated for individual HBCD diastereoisomers. An LC-IT-MS method, employing ESI operated in a negative ionization mode, was developed to determine HBCD diastereoisomers in marine sediment samples, obtaining LOQs ranged from 25 to 40 pg·g−1 (dw). Target analytes were extracted from sediment samples by MAE. Efficiency of this technique was compared with Soxhlet extraction and PLE and the results obtained showed that MAE provides better extraction efficiencies than either PLE or Soxhlet extraction [110].LC-ESI-MS2-based method was developed by Chu et al. [107] for the simultaneous determination of TBBPA, as well as lower brominated BPA analogues, in sediment and sludge samples. LOQs for both kind of samples were in the range 0.02–0.15 ng·g−1 (dw).Hybrid mass spectrometer (LC-QqLIT) with an ESI interface was proposed by Guerra et al. to analyze TBBPA and related compounds (bisphenol A (BPA), monobromobisphenol A (MonoBBPA), dibromobisphenol A (DiBBPA), and tribromobisphenol A (TriBBPA)) in sewage-sludge and sediment samples. Sample extraction was based on the use of ultrasonication SPE, allowing for LODs in the range of 0.6–2.7 ng·g−1 and 1.4–66 ng·g−1 for sediment and sludge samples, respectively [111].ESI, APPI, and APCI sources were tested in the determination of HBCDs and TBBPA in sewage-sludge samples [112]. In this study, involving the use of UHPLC-MS2 and PLE, APCI gave a higher sensitivity than APPI while for TBBPA-bis, APCI and APPI showed a similar performance. ESI was the best option for TCBPA, TBBPA, and HBCDs. Figure 4 shows the total ion current transition of target analytes using APCI as an ionization source.TIC of transitions of tetra-BDE (a), penta-BDE (b), esa-BDE (c), epta-BDE (d), and octa-BDE (e) obtained from PLE extraction and UHPLC-APCI/MS/MS analysis of NIST Standard Reference Material New York/New Jersey Waterway Sediment 1944. From reference [112].
(a)
(b)
(c)
(d)
(e)


## 2.3.1. Liquid Samples

The use of LC-MS in the determination of TBBPA provides several different detection modes and eliminates the need for the derivatization of the phenolic group. Moreover, it facilitates the use of13C-labelled TBBPA. Tollbäck et al. [103] reported that the most suitable LC-MS interface for TBBPA analysis is ESI operating in a negative ionization mode. ESI gave 30–40 times lower LODs compared to APCI. In addition, it permits the monitoring of the intact TBBPA molecule through the soft ionization of ESI, resulting in improved method selectivity and accuracy. Frederiksen et al. [104] compared LC-MS2 to GC-MS for the determination of TBBPA and concluded that LC-MS2 is the method of choice, not only because derivatisation is not needed, but also because of its higher sensitivity and better detection. LC-MS2 using QqQ and APCI source was performed for the analysis of 38 BFRs in wastewater, finding decabromodiphenylethane (DBDPE), bis(2-ethyl-1-hexyl)tetrabromophthalate (BEHTBP), and TBBPA at ng·L−1 levels [105]. Bacaloni et al. [106] proposed an LC-MS2 method for the simultaneous determination of TBBPA and five PBDEs in water samples. LIT mass spectrometer, coupled with an APPI source, was operated in the negative ion mode and each compound was quantified operating in MRM obtaining LOQs of 0.2–3.3 ng·L−1, except for one compound. PBDEs were poorly retained by SPE from river water and sewage treatment plant effluent samples; thus LLE by n-hexane was used for these samples.


## 2.3.2. Solid Samples

Due to its low solubility in water (0.72 mg·L−1) and high log Kow (4.5), TBBPA is likely to be associated with suspended particulate matter once released in the water column and ultimately buried in sediments [107, 108]. However, due to the lower bioaccumulation potential, TBBPA presents lower concentrations than PBDEs and HBCD in the environment. IT-MS was reported for the determination of TBBPA in sediment and sewage sludge after LC separation [108]. Although the ion suppression of the TBBPA signal due to matrix components in the ESI process was not high, sewage-sludge extracts suffered greatly from ion suppression and an extensive cleanup was required to minimize this effect.The distribution of HBCD isomers in suspended sediments from Detroit River was analyzed by QqQ, with an ESI source operated in negative mode and detection by MRM but using ASE as extraction technique [109]. LOD of 10 pg on column was estimated for individual HBCD diastereoisomers. An LC-IT-MS method, employing ESI operated in a negative ionization mode, was developed to determine HBCD diastereoisomers in marine sediment samples, obtaining LOQs ranged from 25 to 40 pg·g−1 (dw). Target analytes were extracted from sediment samples by MAE. Efficiency of this technique was compared with Soxhlet extraction and PLE and the results obtained showed that MAE provides better extraction efficiencies than either PLE or Soxhlet extraction [110].LC-ESI-MS2-based method was developed by Chu et al. [107] for the simultaneous determination of TBBPA, as well as lower brominated BPA analogues, in sediment and sludge samples. LOQs for both kind of samples were in the range 0.02–0.15 ng·g−1 (dw).Hybrid mass spectrometer (LC-QqLIT) with an ESI interface was proposed by Guerra et al. to analyze TBBPA and related compounds (bisphenol A (BPA), monobromobisphenol A (MonoBBPA), dibromobisphenol A (DiBBPA), and tribromobisphenol A (TriBBPA)) in sewage-sludge and sediment samples. Sample extraction was based on the use of ultrasonication SPE, allowing for LODs in the range of 0.6–2.7 ng·g−1 and 1.4–66 ng·g−1 for sediment and sludge samples, respectively [111].ESI, APPI, and APCI sources were tested in the determination of HBCDs and TBBPA in sewage-sludge samples [112]. In this study, involving the use of UHPLC-MS2 and PLE, APCI gave a higher sensitivity than APPI while for TBBPA-bis, APCI and APPI showed a similar performance. ESI was the best option for TCBPA, TBBPA, and HBCDs. Figure 4 shows the total ion current transition of target analytes using APCI as an ionization source.TIC of transitions of tetra-BDE (a), penta-BDE (b), esa-BDE (c), epta-BDE (d), and octa-BDE (e) obtained from PLE extraction and UHPLC-APCI/MS/MS analysis of NIST Standard Reference Material New York/New Jersey Waterway Sediment 1944. From reference [112].
(a)
(b)
(c)
(d)
(e)


## 3. Conclusions and Trends

The applications of advanced LC-MS technologies to an environmental analysis have allowed the determination of a great number of compounds, especially polar compounds, that were previously difficult or even impossible to analyze. In particular, the introduction of API interfaces and triple-quadrupole analyzers has greatly improved the sensitivity and selectivity of detection and today, the analysis of many micropollutants in the environment samples is possible at the ng·L−1 and ng·g−1 levels, and even at the pg·L−1 and pg·g−1 levels in the routine bases. Because of the improved sensitivity and selectivity of the detection systems, a sample preparation is becoming easier, and the probe of it is the current trend towards a more extensive application of automated online methodologies with simple sample pretreatment and high sample throughput. However, despite the high selectivity of LC-MS systems, false negative findings can still occur due to the often high complexity of environmental matrices. Therefore, the application of stringent confirmation and identification criteria [113], in terms of retention time, base peak and diagnostic ions, relative abundances, and so forth, is essential.The recent introduction of tandem mass spectrometry can help eliminate the false identification and quantification of coeluting compounds that can occur with single ion monitoring while it also reduces the amount of background noise present. More recent, the possibility to couple liquid chromatography to ion trap or the new generation of triple-quadrupole and hybrid instruments such as quadrupole time-of-flight and linear traps, more and more applications for the determination of micropollutants have been described for liquid chromatography.These new approaches are a powerful analytical technique with excellent capabilities due to their high sensitivity in a full-spectrum acquisition mode together with their resolving power and accurate-mass measurements. These features make these techniques very attractive in qualitative analysis, especially for the wide-scope screening of a large number of organic contaminants and residues at trace levels in different fields.The fastest growing chromatography trend continues to be the use of the ultrahigh performance liquid chromatography. In addition to providing narrow peaks and improved chromatographic separations, it dramatically shortens analysis times.In the area of sample pretreatment, an important progress has been made also with regards to the preparation techniques. The efforts have gone directed towards to obtain high recoveries and minimise interference, as well as to reduce solvent volumes and avoid the use of toxic organic solvents. Microextraction techniques allow high enrichment factors and minimise solvent consumption which avoid the environmental pollution.



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*Source: 748989-2012-12-17.xml*