The studied area is the Yaagda region in the North of Burkina Faso surrounding the mining site of Seguenega, approximately 190 km from Ouagadougou, the Capital City of Burkina Faso.

Soils

Soils in this region can be classified into four (04) groups:

Rough mineral soils, more or less hard and unsuitable for crops (10% of the area). The soils are not very evolved, having a humiferous horizon of 20 to 80 cm. More common in the region (57.6% of the area);

Soils of the type “ferruginous leached deep” (10% of the surface), they are located on medium glazes, and therefore fairly susceptible to erosion;

Brown and ferruginous soils, these soils are of satisfactory depth from 80 to120 cm and represent only 2.1% of the area;

Plains, lowland and depression soils; their silty-clay texture and their depth (over 120 cm) give them a good water retention capacity (20% of the area) [6].

Geology

The crystalline rocks constitute almost the entire subsoil of the Yaadga Region except in the northwest where the base disappears under the sedimentary formations of the infra cambrian [6].

Soil samples were collected randomly within selected areas around 1.7 km² surrounding the mining site of Seguenega in Burkina Faso. A plastic dust pan and brush are used to collect the soil and transferred into some clean polythene bags. The samples were properly labeled catalogued and brought to the radiation laboratory. The samples were analyzed using gamma spectrometry to determine the activity concentration of radionuclides. In the laboratory, the soil samples collected were air-dried in trays for 7 days and then oven dried at a temperature of 105˚C to remove all the moisture contents. The samples were then grinded into fine powder using a ball mill to increase the total emission area [7] and packed into 1 litre Marinelli beakers. The Marinelli beakers filled with the samples were then sealed and stored for four weeks in order to allow secular equilibrium between ²²⁶Ra and ²³²Th and their decay products before counting by gamma-ray

Figure 1.Sampling locations points.

spectrometry. Each sample was counted using a high purity germanium detector (HPGe).

Figure 1 shows the sampling locations obtained by using the GPS coordinates of sampling points.

The gamma spectrometry system used for this study consists of a High Purity Germanium (HPGe) detector with the following characteristics (Canberra detector model GX4020, cryostat model 7500SL and preamplifier model 2002CSL). It has a diameter of 60.5 mm, length of 61.5 mm. The resolution of the detector is 2.0 keV and relative efficiency of 40% for 1.33 MeV gamma energy of ⁶⁰Co. The output from the detector is connected to a desk top computer provided with “Genie 2000” configuration software for spectrum acquisition and evaluation. In order to do the measurement, energy and efficiency calibration were done previously.

A relationship between the channel numbers corresponding to specific gamma-ray energies was determined before sample counting. The establishment of this relationship is known as energy calibration and the idea is to identify the radionuclides in a sample. The linearity of energy response is an essential feature for any γ-ray detector and the direct proportionality between the quality of energy deposited in the detector by the incident radiation event and the height of the output pulse ensures that the system is working properly [8]. Accurate calibration involves a standard source with gamma ray energies that are not widely different from those to be measured in the unknown spectrum. The energy calibration was done by means of multi peaked and multi nuclides radioactive standard sources emitting gamma rays of precisely known energy and the peak position in channels with this energy is identified. In this study this was carried out by counting

Figure 2. Energy calibration curve.

standard radionuclides (a mixture of ²⁴¹Am, ¹⁰⁹Cd, ¹³⁹Ce, ⁵⁷Co, ⁶⁰Co, ¹³⁷Cs, ¹¹³Sn, ⁸⁵Sr and ⁸⁸Y) of known activities with well-defined energies in the energy range of 60 to ~2000 keV. The standard was counted on a detector for 10 hours or 36,000 s. The energy calibration curve is given in Figure 2.

From the spectrum analysis, count rates for each detected photo peak and activity per unit mass, the specific activity for each of the detected nuclides are calculated. The specific activity (in Bq.kg⁻¹), A_Sk, of a nuclide k, and for a peak at energy E, is given by Equation 1

Where,

A S k is the activity concentration (Bq/kg) of the radionuclide of interest.

ϵ E k is the detection efficiency at energy Ε_k.

T is the counting live time.

Pγ is the number of gamma-rays per disintegration of this radionuclide for a transition at energy E of the measured sample of water [9]. If there is more than one peak in the energy analysis range for a nuclide, then an attempt is made to average the activities for the peak. The result is then the weighted radionuclide’s average activity concentration. The activity concentrations of ²³⁸U and ²³²Th in samples collected were determined using the measured γ-ray photo peaks, emitted by specific radionuclides in their decay series whereas the activity concentrations of ⁴⁰K is calculated from the measured γ-ray photo peaks directly. In other words, the activity concentration of ²³⁸U was calculated from the average of 609.31 keV of ²¹⁴Bi and 1764.5 keV of ²¹⁴Bi, in the decay series of ²³²Th gamma photons are emitted at energies of 239 keV (²¹²Pb), 583 keV (²⁰⁸Tl) and 911 keV (²²⁸Ac) which are used to determine the activity concentrations of ²³²Th by gamma spectrometry, and ⁴⁰K was determined from 1460.0 keV.

A direct relationship between radioactivity concentrations of natural radionuclides and their exposure is referring to as absorbed dose rate in air at 1 m above the ground. This factor is important quantity to assess when considering radiation risk to a bio system. This is calculated from the activity concentrations by using Equation (2) [2][9][10].

Where DCF_K = 0.0417, DCF_U = 0.462 and DCF_Th = 0.604 are the absorbed dose rate conversion factors for K-40, U-238 and Th-232 in nGy/h/Bq/kg and A_K, A_U and A_Th are the activity concentrations for K-40, U-238 and Th-232, respectively.

For the safe use of soil, D must be lower than the recommended value 55 nGy/h [11][12]. The Radium equivalent and hazard indices will be calculated for the studied soil.

In order to provide the radiological risk to which an individual is exposed, the absorbed dose is considered in terms of annual effective dose equivalent from terrestrial gamma radiation considering the conversion coefficients from absorbed dose in air to effective dose which is estimated to be 0.7 Sv/Gy and the outdoor occupation factor of 0.2 [3]. The outdoor annual effective dose equivalent was estimated by using the following Equation (3) [2][13][14].

Where Eᵧ is the average annual effective dose and Dr is the absorbed dose rate in air.

The radiological hazard of the natural radioactivity was evaluated also by calculating the radium equivalent concentration (Ra_eq), the external and internal hazard indices. The radium equivalent concentration (Ra_eq) is used to compare the uniformity in radiation of material containing different amounts of ²²⁶Ra, ²³²Th and ⁴⁰K. It is based on the estimation that 350 Bq/kg of ²²⁶Ra, 259 Bq/kg of ²³²Th and 4810 Bq/kg of ⁴⁰K produce the same γ-ray dose rate [15]. (Ra_eq) was calculated by using Equation (4) [16].

Where C_Ra, C_Th and C_K are the activity concentration of 226 Ra, 232 Th and 40 K respectively. The external and internal hazard indices values must be less than one for the radiation hazard to be considered negligible i.e. the radiation exposure due to the radioactivity from the construction material is limited to 1.5 mSv/y [16]. In addition, Radon and its short-lived products are hazardous to the respiratory organs and as a result, the internal exposure to radon and its short-lived daughter products is quantified using the internal hazard index. Radiation exposure due to 226 Ra, 232 Th and 40 K may be external and defined in terms of external hazard index. To evaluate the external gamma (γ) radiation dose from soil, the following model was used as criterion. This model uses the external hazard index Hex defined Equation (5) [17].

Where C_Ra, C_Th and C_K are the activity concentrations of 226 Ra, 232 Th and 40 K, respectively. This index must be less than unity so that the annual effective dose due to radioactivity in the soil will be less than or equal to 1.5 mSv yr⁻¹. Radon and its short-lived products are also hazardous to the respiratory organs. The internal exposure to radon and its daughter products is quantified by the internal hazard index (Hin) which is given by the following Equation (6) [17].

Where C_Ra, C_Th and C_K are the activity concentrations of 226 Ra, 232 Th and 40 K, respectively, in Bq kg⁻¹ for the soil. For the safe use of a soil Hin should be less than unity.

The activity concentrations of ²³⁸U, ²³²Th and ⁴⁰K in soil samples from Seguenega site in Yaadga Region of Burkina Faso around the mining site of Seguenega are shown in Table 1.

Table 1. Activity concentration in soil samples from Seguenega site.

The highest value of radioactivity of ²³⁸U, ²³²Th and ⁴⁰K are 18.97, 29.00 and 412.89 Bq.kg⁻¹ respectively while the lowest values are 10.82, 12.52 and 136.25 Bq.kg⁻¹.

The mean values for ²³⁸U, ²³²Th and ⁴⁰K are 18.97 ± 1.43 Bq.kg⁻¹, 22.98 ± 0.96 Bq.kg⁻¹ and 212.72 ± 29.75 Bq.kg⁻¹ respectively.

The average activity concentrations of ²³⁸U, ²³²Th and ⁴⁰K in this study are lower than the worldwide average values of 32, 45 and 420 Bq.kg⁻¹ respectively [3]. The activity concentration varies from one location to another location. These differences could be explained by the mineral content difference of soil or the non-uniformity of sampling depth. We can also notice that the ²³⁸U, ²³²Th and ⁴⁰K activity concentration in all the samples are lower than the world average.

Figure 3. compares the average concentrations of radionuclides ²³⁸U, ²³²Th, and ⁴⁰K of this present work with our previous work concerning Kalsaka site [18].

Figure 3.Comparison of activity concentration of ²³⁸U, ²³²Th and ⁴⁰K between Seguenega and Kalsaka sites.

Figure 4.Comparison of activity concentrations of ²³⁸U, ²³²Th and ⁴⁰K of the present work and other works and UNSCEAR standards.

The average concentrations of ²³⁸U and ²³²Th at Kalsaka are higher than those at Seguenega wile, the average concentration of ⁴⁰K at Seguenega is almost twice more than Kalsaka site. This difference could be attributed to differences in geology and geochemical conditions.

Figure 4 shows a Comparison of the activity concentrations of ²³⁸U, ²³²Th and ⁴⁰K of the present work with our previous work concerning Kalsaka site, and other works [19]-[25] and UNSCEAR reference limits in soil sample. The results of the activity concentrations in this study are lower than the worldwide average values compared quite well with similar works which have been done in other countries as show in Figure 4.

The absorbed dose in air is the received dose in the open air from the radiation emitted from radionuclides activity concentrations in the environmental materials. This factor is important quantity to assess when considering radiation risk to a bio system. The absorbed dose rate obtained in this work varied in a range of 18.31 - 47.07 nGy/h with an average value of 31.97 nGy/h. The average value in this study is lower than the worldwide average value of 60 nGy/h estimated from soil concentrations.

The natural radioactivity in soil samples is usually determined from the activity concentrations of ²²⁶Ra, ²³²Th and ⁴⁰K. The corresponding average annual effective dose for the present studies was 0.040 mSv/year

The radium equivalent activity (Raeq) is related to the external gamma dose from the terrestrial radionuclides and the internal dose due to radon and its decay products of ²¹⁰Pb and ²⁰¹Po. In this study, the average radium equivalent activity (Raeq) obtained in the samples was 69.11 Bq/kg in a range of 39.36 - 99.97 Bq/kg. The acceptable limit value of Raeq for building purposes is 370 Bq/kg for the material to be considered safe for use.

Radiation exposure due to ²²⁶Ra, ²³²Th and ⁴⁰K may be external and defined in terms of external hazard index. The average external is 0.19 which are less than the unity. Radon and its short-lived products are also hazardous to the respiratory organs. The internal exposure to radon and its daughter products is quantified by the internal hazard index (Hin). The average internal is 0.24 which is less than the unity. Figure 5 shows a comparison between the external (Hex) and internal (Hin) risk indices of Kalsaka and Seguenega with the UNSCEAR reference limits

Table 2 shows the absorbed dose rate, the annual effective dose, the radium equivalent activity (Ra_eq), and the external (H_ex) and internal (H_in) hazard indices)

Figure 5.Comparison between external (Hex) and internal (Hin) risk indices of Kalsaka and Seguenega with the UNSCEAR reference limits.

in the soil samples activity from Yaadga Region of Burkina Faso surrounding the mining site of Seguenega.

The radium equivalent activity (Ra_eq), the external (H_ex) and internal (H_in) hazard are used in order to assess if the soil could be a source of public radiation exposure.

The values of Ra_eq, H_ex and H_in are below the acceptable values. This indicates that soil in the studied area that might be used for building purposes may not pose any significant radiological radiation hazard and, thus, regarded safe.

All the average values are below the references’ limits.

Table 2.Doses and radium equivalent activity, and external (H_ex) and internal (H_in) hazard index.