719
Chlorophylls and their Degradation in Nature
in River Avon (Warwickshire, UK); <97 μg L −1 in streams and rivers (USA);
<65 μg L −1 in La Trobe River Streams (Victoria, Australia); <44.6 μg L −1 in
Ozark Streams (Missouri, USA); <27 μg L −1 in Rideau River (Ontario, Canada);
<18.0 μg L −1 in sStreams and rivers (Illinois, USA); <17 μg L −1 in Chalk stream
(UK); and 0.0–12.7 μg L −1 in other studied systems (Table 1).
Chl a mostly results from in-channel production rather than from tributary or outside inputs. Chl a concentrations in the Pearl River are high only during summer lowflow periods and are often controlled by temperature and by CDOM concentration
(Duan and Bianchi 2006). Lower phytoplankton biomass (dominated by chlorophytes)
in the Pearl River is likely linked with intense shading by CDOM and lower availability of nutrient inputs (Duan and Bianchi 2006). High concentrations of Chl a (0.4–
170 μg L −1 ) are strongly correlated with high contents of phosphorus (5–1,030 μg
L −1 ) in temperate streams (van Nieuwenhuyse and Jones 1996). Chl a concentrations in the lower Mississippi River are high in summer low-flow periods and also
during interims of winter and spring. They are not coupled with physical variables
or nutrients, likely due to a combination of in situ production and inputs from reservoirs, navigation locks and oxbow lakes in the upper Mississippi River and Missouri
River (Duan and Bianchi 2006). The high, diatom-dominated phytoplankton biomass
in the lower Mississippi River is likely the result of decreasing total suspended solids (because of increased damming in the watershed) and increasing nutrients (due to
enhanced agricultural runoff) over the past few decades (Duan and Bianchi 2006).
Lakes and Reservoirs
Chl a concentrations are significantly variable, from 0.01 to 850 μg L −1 in a variety of lakes (Table 1) (Carrillo et al. 2002; Kasprzak et al. 2008; Fu et al. 2010;
Mostofa KMG et al. unpublished data; Vicente and Miracle 1984; Pedros-Alio et
al. 1987; Guildford and Hecky 2000; Camacho 2006; Satoh et al. 2006; Sawatzky
et al. 2006; Hamilton et al. 2010; Fee 1976; Sommaruga and Augustin
2006; Yuma et al. 2006; Kiefer et al. 1972; Gross et al. 1997; Barbiero
and Tuchman 2004; Fahnenstiel and Scavia 1987; de Moraes Novo
et al. 2006; Aizaki et al. 1981; Rojo and Miracle 1987; Dasí and Miracle
1991; Miracle et al. 1993; Windolf et al. 1996; Camacho 1997; Yoshioka
1997; Biddanda et al. 2001; Kahlert 2002; Laurion et al. 2002; Bachmann
et al. 2003; Camacho et al. 2003; Straškrábová et al. 2005; Blindow et al.
2006; Silsbe et al. 2006; McCallister and del Giorgio 2008; Striebel et al.
2008; Antoniades et al. 2009; James et al. 2009; Pan et al. 2009; Winder
et al. 2009; Lv et al. 2011; Wang et al. 2012; Liu et al. 2011; Zhang et al. 2007;
Rae et al. 2001). These studies demonstrate that the highest detected Chl a concentrations can be ordered as follows: <850 μg L −1 in Lake Cisó (Spain); <327 μg
L −1 in lakes of the Experimental Lakes Area (northwestern Ontario, Canada);
<298 μg L −1 in Lake Arcas (Spain); <276 μg L −1 in several shallow Danish lakes;
<265 μg L −1 in numerous Florida Lakes; <189.8 μg L −1 in Subtropical and urban
shallow Lakes (Wuhan, China); <189 μg L −1 in several lakes in Japan; <175.9 μg
Chlorophylls and their Degradation in Nature
in River Avon (Warwickshire, UK); <97 μg L −1 in streams and rivers (USA);
<65 μg L −1 in La Trobe River Streams (Victoria, Australia); <44.6 μg L −1 in
Ozark Streams (Missouri, USA); <27 μg L −1 in Rideau River (Ontario, Canada);
<18.0 μg L −1 in sStreams and rivers (Illinois, USA); <17 μg L −1 in Chalk stream
(UK); and 0.0–12.7 μg L −1 in other studied systems (Table 1).
Chl a mostly results from in-channel production rather than from tributary or outside inputs. Chl a concentrations in the Pearl River are high only during summer lowflow periods and are often controlled by temperature and by CDOM concentration
(Duan and Bianchi 2006). Lower phytoplankton biomass (dominated by chlorophytes)
in the Pearl River is likely linked with intense shading by CDOM and lower availability of nutrient inputs (Duan and Bianchi 2006). High concentrations of Chl a (0.4–
170 μg L −1 ) are strongly correlated with high contents of phosphorus (5–1,030 μg
L −1 ) in temperate streams (van Nieuwenhuyse and Jones 1996). Chl a concentrations in the lower Mississippi River are high in summer low-flow periods and also
during interims of winter and spring. They are not coupled with physical variables
or nutrients, likely due to a combination of in situ production and inputs from reservoirs, navigation locks and oxbow lakes in the upper Mississippi River and Missouri
River (Duan and Bianchi 2006). The high, diatom-dominated phytoplankton biomass
in the lower Mississippi River is likely the result of decreasing total suspended solids (because of increased damming in the watershed) and increasing nutrients (due to
enhanced agricultural runoff) over the past few decades (Duan and Bianchi 2006).
Lakes and Reservoirs
Chl a concentrations are significantly variable, from 0.01 to 850 μg L −1 in a variety of lakes (Table 1) (Carrillo et al. 2002; Kasprzak et al. 2008; Fu et al. 2010;
Mostofa KMG et al. unpublished data; Vicente and Miracle 1984; Pedros-Alio et
al. 1987; Guildford and Hecky 2000; Camacho 2006; Satoh et al. 2006; Sawatzky
et al. 2006; Hamilton et al. 2010; Fee 1976; Sommaruga and Augustin
2006; Yuma et al. 2006; Kiefer et al. 1972; Gross et al. 1997; Barbiero
and Tuchman 2004; Fahnenstiel and Scavia 1987; de Moraes Novo
et al. 2006; Aizaki et al. 1981; Rojo and Miracle 1987; Dasí and Miracle
1991; Miracle et al. 1993; Windolf et al. 1996; Camacho 1997; Yoshioka
1997; Biddanda et al. 2001; Kahlert 2002; Laurion et al. 2002; Bachmann
et al. 2003; Camacho et al. 2003; Straškrábová et al. 2005; Blindow et al.
2006; Silsbe et al. 2006; McCallister and del Giorgio 2008; Striebel et al.
2008; Antoniades et al. 2009; James et al. 2009; Pan et al. 2009; Winder
et al. 2009; Lv et al. 2011; Wang et al. 2012; Liu et al. 2011; Zhang et al. 2007;
Rae et al. 2001). These studies demonstrate that the highest detected Chl a concentrations can be ordered as follows: <850 μg L −1 in Lake Cisó (Spain); <327 μg
L −1 in lakes of the Experimental Lakes Area (northwestern Ontario, Canada);
<298 μg L −1 in Lake Arcas (Spain); <276 μg L −1 in several shallow Danish lakes;
<265 μg L −1 in numerous Florida Lakes; <189.8 μg L −1 in Subtropical and urban
shallow Lakes (Wuhan, China); <189 μg L −1 in several lakes in Japan; <175.9 μg