44
lithogenic element (Loring and Rantala 1992). The distributions of concentration
data and Li normalized data of As are shown in Fig. 2.2. The distribution of 2010
concentration data of As is shown in the same Fig. 2.2.
The spatial analysis of As (linear model) shows local enrichment of As mainly
positioned in the southern and northern parts of the country. The As anomalies are
probably linked with the combination of the long-range transport and strong effects
of local emission sources such as geogenic factor and windblown dust from industrial and mining waste deposits in the north and the use of pesticides in the south
particularly in the past decades. As normalized data show high As content in fewer
stations than was found by spatial distribution of concentration data. It was mostly
evident in agriculture areas (St. 2 and St. 3 in the south) that were probably derived
from the use of pesticides in agriculture activity. The next high As contents were
found in St. 39, St. 51 and St. 52 (Lozhan, Puke, Fushë-Arrëz) that are probably
derived from geogenic factors, mining activity and the windblown mineral fine particles from the mineral waste deposits. The median concentration of As 2015 is higher
than the median concentration of As 2010 . The differences founded in long-term pollution level of metals depend on a number of factors including changes of anthropogenic and secondary emission data, long-term climatic trends, changes of land use,
etc. (Colette et al. 2016).
Moderate and significant correlations were found between As and the normalized As (As(N)) data (r > 0.6, p < 0.001), indicating the stronger anthropogenic
effect to As concentration in 2015 moss samples. It shows weak and significant
correlation with Cd (r = 0.372, p = 0.005). Arsenic did not correlate with Hg, a
3.0
2.5
2.0
1.5
1.0
0.5
0.0
3
2
1
0
-1
S
0 .414620
R-Sq
47.1%
R-Sq(adj)
4 6.1%
As(N)
As
Regression
95% CI
95% PI
Fitted Line Plot
As = 0.2823 + 0.7027 As(N)
Fig. 2.3 Linear regression analysis of As vs. As(N)
S. Allajbeu et al.
lithogenic element (Loring and Rantala 1992). The distributions of concentration
data and Li normalized data of As are shown in Fig. 2.2. The distribution of 2010
concentration data of As is shown in the same Fig. 2.2.
The spatial analysis of As (linear model) shows local enrichment of As mainly
positioned in the southern and northern parts of the country. The As anomalies are
probably linked with the combination of the long-range transport and strong effects
of local emission sources such as geogenic factor and windblown dust from industrial and mining waste deposits in the north and the use of pesticides in the south
particularly in the past decades. As normalized data show high As content in fewer
stations than was found by spatial distribution of concentration data. It was mostly
evident in agriculture areas (St. 2 and St. 3 in the south) that were probably derived
from the use of pesticides in agriculture activity. The next high As contents were
found in St. 39, St. 51 and St. 52 (Lozhan, Puke, Fushë-Arrëz) that are probably
derived from geogenic factors, mining activity and the windblown mineral fine particles from the mineral waste deposits. The median concentration of As 2015 is higher
than the median concentration of As 2010 . The differences founded in long-term pollution level of metals depend on a number of factors including changes of anthropogenic and secondary emission data, long-term climatic trends, changes of land use,
etc. (Colette et al. 2016).
Moderate and significant correlations were found between As and the normalized As (As(N)) data (r > 0.6, p < 0.001), indicating the stronger anthropogenic
effect to As concentration in 2015 moss samples. It shows weak and significant
correlation with Cd (r = 0.372, p = 0.005). Arsenic did not correlate with Hg, a
3.0
2.5
2.0
1.5
1.0
0.5
0.0
3
2
1
0
-1
S
0 .414620
R-Sq
47.1%
R-Sq(adj)
4 6.1%
As(N)
As
Regression
95% CI
95% PI
Fitted Line Plot
As = 0.2823 + 0.7027 As(N)
Fig. 2.3 Linear regression analysis of As vs. As(N)
S. Allajbeu et al.