The Xichú mining district is in the northeast of the state of Guanajuato, Mexico. Mining activity began in the colonial era and ended in the mid-twentieth century. The most important mine in this district is La Aurora, which profited from metals such as silver (Ag) and gold (Au) (Miranda-Gasca 1978). Due to mining activity in the area, four tailings were disposed in the surroundings.

One of the main problems arising from the improper disposal of mine tailings is the introduction of potentially toxic elements into the environment (Ramos-Arroyo et al. 2004, Ramos-Arroyo and Siebe-Grabach 2006). Previous geochemical studies in the zone indicated the presence of copper (Cu), zinc (Zn), silver (Ag), lead (Pb) and arsenic (As) in different environmental matrices (Salas-Megchún 2014, Loredo-Portales et al. 2015, 2017).

The highest levels of Pb and As found in tailings and soils from the zone of La Aurora, could represent a risk for the surrounding populations.

There have been numerous studies regarding exposure to metals in human population from mining zones (García-Vargas et al. 2001, Moreno et al. 2010). An effect reported in populations living in this risk scenery is DNA damage (Yáñez et al. 2003, Jasso-Pineda et al. 2012). The genotoxicity of As and Pb is well demonstrated both in animals (Saleha-Banu et al. 2001, Martínez-Alfaro et al. 2012) and in humans (Méndez-Gómez et al. 2008).

A helpful tool used in the assessment of early biological effects like DNA damage in populations exposed to environmental pollution is the comet assay (Jasso-Pineda et al. 2015). Therefore, the aim of this work was to conduct biomonitoring of As and Pb, as well as to identify the potential genotoxic effects of these elements in a population of children and adults exposed to mine tailings in the vicinity of the Aurora mine in the mining district of Xichú, Mexico.

The Aurora mine is located 6 km from the town of Xichú, Guanjuato, México. It is an abandoned mine site that has four tailing deposits exposed to the environment, so they are prone to incidents of leaching and suspension by wind and water. The waste was generated when there was no environmental regulation and may be considered as an environmental liability; it does not meet the requirements of the Mexican Official Standard NOM-141-SEMARNAT-2003 (SEMARNAT 2005), which establishes the criteria for the construction, operation and post-operation of tailing dams.

To confirm the presence of potentially toxic elements at the site such as Pb and As, a targeted soil sampling was performed (at a depth of 0-5 cm) in the tailing located between the communities Adjuntas and La Fundición (900 and 600 m away from the tailing, respectively).

A total of five samples were selected, one directly in the tailing, one near the tailing and three around the tailing. Samples around the tailing (less than 20 m away from the tailing) were selected in areas able to be in direct contact with the people from surrounding communities.

Figure 1 shows the area of the mining district (UTM 393231 N, 2359598 W), location of the tailings, localities, and sampled soil points.

Fig. 1

Samples of tailing and soils were sieved in particles smaller than 0.85 mm and digested according to the Environmental Protection Agency (EPA) method 3050B.

The Pb analysis in the environmental samples was performed by an atomic absorption spectrophotometer (AAS) (Perkin-Elmer model AAnalyst 400) using the flame technique.

For the analysis of As, special treatment was given to the digested samples, adding potassium iodide (KI) at 2 % for 30 min in the dark. Determination of As was performed by an AAS coupled to a continuous flow injection in a reaction with a 3 % NaBH₄ and 1% NaOH solution, using HCl at 1.5 % as a reaction medium.

The detection limit (DL) was 0.15 mg/kg for Pb and 0.35 mg/kg for As. For quality control, we used the standard reference of the National Institute of Standards and Technology (NIST) using the Montana 2711a soil and the Montana Soil II, getting an accuracy of 91.7 % for Pb and 85 % for As.

For biological monitoring, residents from Adjuntas and La Fundición were invited to participate in the study.

The inclusion criteria for children were age between 6 to 12 years, having lived in the community since birth and the consent of the parent or guardian. For adults, the inclusion criteria were legal age, having lived in the community at least for 5 years and a letter of consent signed by the participant.

The research was approved by an ethical committee. The total population of both communities is 182 inhabitants. Fifty-two were children (younger than 12 years of age) and 96 adults (INEGI 2010).

Only 20 children and 20 adults participated in the study, representing the 38 and 20 %, respectively of the total population.

Malnutrition was evaluated by anthropometric indices. Weight and height for age were used like indicators of acute and chronic malnutrition in children, respectively, and the Body Mass Index (BMI) was used like indicator of malnutrition in adults. All participants were weighed and measured with a scale and stadiometer (Seca).

Hematocrit (Ht) was determined by centrifuging blood in heparinized capillary tubes (50 μL) at 7000 rpm for 10 min in a Ht centrifuge (Sol Bat M-08). Measurement was done with a Ht standard chart (Critops tube reader). The hemoglobin content (Hb) was measured using a diagnostic kit (HemoCueHb 201 Microcuvettes and HemoCueHb 201 Analyzer). The test was performed according to the protocol of the instrument operation manual.

The activity of enzyme delta-aminolevulinic dehydratase (δ-ALAD) was determined according to the standardized European method (Berlin and Schaller 1974). The enzyme activity was expressed as µmol/min per liter erythrocytes.

The blood Pb samples were analyzed with an inductively coupled plasma mass spectrometry (ICP-MS) at the Centro de Innovación Aplicada en Tecnologías Competitivas (Center for Applied Innovation in Competitive Technologies, CIATEC), Mexico, while for the analysis of As, 5 mL of urine acid digestion were used following the Cox method (Cox 1980). The As analysis was carried out with the AAS in the same manner as the soil samples. For quality control, the standard ClinChek Urine Control lyophilized for trace elements from IRIS Technologies was used obtaining an accuracy of 87 % for As. The As concentration in urine was corrected by the urine creatinine value, which was determined by the Jaffe colorimetric method (Singh et al. 1988), using a Randox kit for creatinine.

Assessment of genotoxic damage was carried out in the study population following the comet assay protocol described by Singh et al. (1988). One hundred cells were counted per sample in a Nikon Eclipse E400 epifluorescence microscope using the Komet 4.0 image analysis software (Kinetic Imaging, Liverpool, UK). Measurements of DNA damage were obtained with the Olive Tail Moment (OTM) and the Tail Length (TL).

Descriptive and exploratory data analysis for continuous variables (Pb in soil, As in soil, age, z height by age, z weight by age, BMI, Pb in blood, As in urine, OTM, TL, Ht, Hb and δ-ALAD) and a descriptive analysis with respect to categorical variables (gender) were done. The results were presented for children and adults. OTM did not assume a normal distribution. The variable was log-transformed and reported as geometric mean and standard deviation. Bivariate analysis was made through the Pearson correlation. Correlations were worked in an independent way for children and adults. The statistical analyses were carried out using SPSS statistical software package v. 19.0.

Pb levels in the tailing sample exceeded 9.2 times the reference concentration of 400 mg/kg for residential/agricultural land (NOM-147-SEMARNAT/SSA1-2004) (SEMARNAT 2007), while in the soil samples taken from the surroundings of the mine tailing (1104 mg/kg) and from a nearby river (535 mg/kg), the levels exceeded 2.8 and 1.3 times the reference value, respectively (Table I).

TABLE I

Zone	Pb (mg/kg)	As (mg/kg)
Tailing	3699.1	307 338.4
Soil near tailing	1104.0	1 473.0
Soil 1	262.0	323.0
Soil 2	535.0	204.0
Soil 3	258.0	52.0

*The Official Mexican Standard NOM-147-SEMARNAT/SSA1-2004 (SEMARNAT 2007) establishes limits of 800 mg/kg for Pb and 260 mg/kg for As in industrial lands, and 400 mg/kg for Pb and 22 mg/kg for As in residential/agricultural lands

Regarding As, the mine tailing sample highly exceeded the limits set by Mexican regulations. Soil samples exceeded from 2.4 to 66.9 times the reference value of 22 mg/kg, being the soil near the mine tailing (Table I) the one with the highest level.

Salas-Megchún (2014) made a geochemical characterization of the tailings from La Aurora. The levels of Pb and As in tailing 3 (the same one sampled in our study) were between 699-14945 and 2329-38631 mg/kg for Pb and As, respectively. Regarding the soil samples, levels were less than the DL for Pb and As (3379 and 4708 mg/kg, respectively).

Similarly, in an earlier study, Loredo-Portales et al. (2017) evaluated the same tailing sampled in our study and reported As levels between 3290-12469 and 181-719 mg/kg in the mine tailing and nearby soils, respectively.Our results were similar to these reports. Loredo-Portales (2017) also reported the levels of bio-accessible As (As available to enter the human body). The percentage of bio-accessibility was less than 10 % for mine tailing samples, whereas for soil it was near to 20 %. Although the percentage of bio-accessibility is low, it represents a risk due to the high concentration of As in the sample. These data show the magnitude of contamination in this site.

The possible routes of exposure to these metals in the impacted zone are the suspension of mine tailings by the wind and the resuspension of soil particles generated by activities on roads. The predominant winds in the region are trade winds from the northwest, supporting this exposure route (Martínez-Arredondo et al. 2013). The residents of Adjuntas and La Fundición travel on the main road (which is less than 20 m away from the tailings) for their everyday activities. It is important to mention that there are houses settled over the tailings.

In Mexico, the recommended Pb values in blood for a non-occupational population were 10 μg/dL in children and 25 μg/dL in adults (NOM-199-SSA1-2000) (SSA 2002). However, based on neurotoxicity studies in children (Canfield et al. 2003), the recommended value for children was reduced to 5 μg/dL (SSA 2017).

In the present study, 100 % of the children presented values over 5 μg/dL (Table II). Regarding As in urine, a small percentage of children (12.5 %) and adults (12.5 %) exceeded the limits set by the CDC of 50 µg/g creatinine (Table II).

TABLE II

		Children (min-max)a	Adults (min-max)a
Age (years)		10.8 ± 2.2 (6-12)	42.4 ± 17.9 (18-49)
Gender	male	58.8 %	56.3 %
	female	41.2 %	43.8 %
z height by age	> -2 SDb	0 %	NA
z weight by age	> -2 SDb	6.3 %	NA
Body Mass Index	> 25 kg/cm2	NA	90 %
Haemoglobin (g/dL)		14.3 ± 0.8 (13.2-15.9)	14.7 ± 1.4 (11.7 - 16.6)
	< 11.2c	0 %	NA
	< 13.5 M, < 12.5 Fc	NA	0 %
Hematocrit (% erythrocytes)		57.3 ± 3.9 (53-65)	58.6 ± 5.5 (50 - 69)
	< 35c	0 %	NA
	< 40 M, < 37 Fc	NA	12.5 %
Delta-aminolevulinic acid dehydrataseactivity (µmol/min per liter erythrocytes)		14.1 ± 3.1 (7.2-19.5)	13.2 ± 4.2 (6.4 - 21.5)
	< 20d	100 %	93.8 %
Lead in blood (µg/dL)		7.5 ± 1.2 (5.1-9.3)	7.9 ± 3.3 (4.8 -17.8)
	> 5e	100 %	91.7 %
	> 10e	0 %	8.3 %
Arsenic in urine (µg/g creatinine)		25.2 ± 15.8 (7.5-65.2)	18.3 ± 18.4 (0.8 - 65.1)
	> 50f	12.5 %	12.5 %

NA: does not apply, ^aarithmetic mean ± standard deviation (SD) (minimum and maximum), ^bbenchmark by WHO, ^c minimum reference values (M: male, F: female), ^dreference value to healthy people not exposed to Pb, ^eNOM-199-SSA1-2000, ^fCDC reference values

Trejo-Acevedo et al. (2009) conducted a study in several polluted areas of Mexico. Children from two mining sites were monitored (Comarca Lagunera, Durango, and Zacatecana, Zacatecas), finding Pb blood levels of 3.7 ± 1.49 and 6.0 ± 1.8 µg/dL, respectively, while the levels of As in urine were 33.8 ± 13.7 and 26 ± 9.8 µg/g for creatinine.

Our results were higher in terms of Pb in blood (children, 7.5 µg/dL; adults, 7.9 µg/dL), but similar with respect to As in urine (25.2 and 18.3µg/g creatinine in children and adults, respectively). Yáñez et al. (2003) evaluated children living in Villa de la Paz, San Luis Potosí, Mexico (n = 20), a mine site contaminated with Pb and As (with marginalization status similar to La Aurora), and compared them with a population of lower exposure (Matehuala, San Luis Potosí, Mexico; n = 35). At the exposed site, blood Pb levels (11.6 µg/dL) and As in urine (136 µg/g creatinine) were higher than those found in Matehuala (Pb, 8.3 µg/dL; As, 34 µg/g creatinine).

Four years later, Jasso-Pineda et al. (2007) conducted a risk assessment in the same site. They found a slight reduction in urinary As in children of Villa de la Paz (Pb, 13.8 ± 1.0 µg/dL; As, 52.1 ± 7.5 µg/g creatinine) and Matehuala (Pb, 7.3 ± 1.5 µg/dL; As, 16.8 ± 1.6 µg/g creatinine).

In the present study, the blood Pb levels and As in urine are similar to those found in the population of lower exposure (Matehuala). In all the places studied, including the control site of Matehuala, Pb levels found are inconveniently high for children health and development.

With respect to hematological parameters, Hb levels were found to be within ethe stablished clinical parameters for children (14.3 ± 0.8 g/dL) and adults (14.7 ± 1.4 g/dL). The studied population had very high Ht values (children, 57.3 ± 3.9 % erythrocytes; adults, 58.6 ± 5.5 % erythrocytes), a disorder known as polycythemia (Table II).

This parameter varies significantly in different populations according to several factors, one of them being altitude. Nevertheless, it has also been observed in animals as a response mechanism for secondary anemia caused by Pb. Concerning the activity of the δ-ALAD enzyme, several studies mention that Pb inhibits the activity of δ-ALAD at concentrations between 5 to 50 mg/dL. In the present study, 100 and 91.7 % of the children and adults, respectively, had enzyme activity levels lower than 20 μmol/min per liter of erythrocytes (Table II).

We did not find a relationship between Pb and δ-ALAD. This may be due to the fact that most children and adults presented elevated levels of Pb, more than 5 mg/dL (100 % and 93.8 % respectively). It is necessary to increase the sample size to record different exposure levels.

The nutritional status is also a factor that can influence the biomarkers of exposure level and DNA damage (Peraza et al. 1998). The selected communities had a high degree of marginalization; however, both children and adults did not show malnutrition. Only 6.3 % of the children presented more than two standard deviations (SD) in the z score of weight by age, the benchmark for acute malnutrition marked by WHO (2017). It is worth noting that most adults (90 %) had overweight or were obese (Table II).

Regarding DNA damage (Fig. 2), the average OTM was 5.0 ± 1.6 for children and 4.6 ± 1.0 for adults (Fig. 2a), while the average TL was 40.9 ± 4.9 and 41.8 ± 5.9 µm for children and adults, respectively (Fig. 2b).

Fig. 2

Bajpayee et al. (2002) reported a reference value of 4 for OTM in adults, similar to the OTM of 3.2 and 3.9 observed by Yáñez et al. (2003) and Jasso-Pineda et al. (2007), respectively, in children residing in Matehuala (control group).

In our study, more than half of the population had OTM values greater than 4 (children, 64.3 %; adults, 69.2 %). In the same control group from Matehuala, the average TL was 41.7, while the children and adults from the mine zone of La Aurora showed 40.9 and 41.8 µm, respectively. In the exposed group of Villa de la Paz, studied by Yáñez et al. (2003) and Jasso-Pineda et al. (2007), OTM and TL values were 6.8 and 67.6 µm, respectively. In our population, only one child had a similar OTM value (7.1).

Jasso-Pineda et al. (2015) used OTM as a biomarker for biological effects in child populations living in contaminated areas. Also, they observed that the highest OTM values in children living in those sites were found in subjects with As in urine levels higher than 50 µg/g creatinine, a result that is not observed in children with blood Pb levels higher than 5 µg/dL.

In our study, only 12.5 % of the children and adults presents levels above 50 µg/g creatinine, which could be the reason that OTM values were lower in our population. We did not find a correlation between Pb in blood or As in urine with DNA damage variables. We only observed the tendency, but it was not significative, probably due to our small sample size or the low levels of As.

A major limitation of our study was that we did not evaluate a reference population, since a risk assessment is usually carried out simultaneously in exposed and non-exposed populations under the same nutritional and socioeconomic conditions, in order to correlate the biological effects.

The sample size was very small due to the fact that the population is small and the sampling was voluntary. The main reasons for refusing to participate in the study were the pain produced by the needle during the blood sampling, and the impossibility to participate in the study due to working reasons. In future studies it would be important to increase the sample size, a strategy could be to get involve more people from the region to give more confidence to the participant.

This is the first study to describe the health risk scenario for the population of the mining town La Aurora. The results showed detectable levels of Pb and As in biological matrices from children and adults, indicating an environmental exposure to these elements due to the mine tailing deposits present in the area.

The inactivation of δ-ALAD levels was supported by to Pb levels in blood. Pb exposure was higher than 5 μg/dL where previous studies report biological effects, affecting mainly child population.

In the case of As, a small percentage of the study population presented levels higher than the reference values, probably because this element was determined in urine, which is not the better biomarker for the principal exposure route to As in the site (mine tailing and soil particles). Nevertheless, we found detectable levels indicating As exposure. In this case, other matrices to determine As exposure could be nails or hair, and they should be used in upcoming studies.

The results obtained show the need to continue studying the area and creating risk communication programs in the site, in order to prevent contact with the tailing deposits and diminish the associated exposure.