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Article

Trends of Nitrogen and Phosphorus in Surface Sediments of the Lagoons of the Northern Adriatic Sea

by
Adriano Sfriso
1,*,
Alessandro Buosi
1,
Yari Tomio
1,
Abdul-Salam Juhmani
1,
Michele Mistri
2,
Cristina Munari
2 and
Andrea Augusto Sfriso
2
1
Department of Environmental Sciences, Informatics and Statistics (DAIS), University Ca’ Foscari Venice, Via Torino 155, 30170 Mestre, Italy
2
Department of Chemical and Pharmaceutical Sciences, University of Ferrara, 44121 Ferrara, Italy
*
Author to whom correspondence should be addressed.
Water 2021, 13(20), 2914; https://doi.org/10.3390/w13202914
Submission received: 10 September 2021 / Revised: 8 October 2021 / Accepted: 12 October 2021 / Published: 16 October 2021
(This article belongs to the Section Water Quality and Contamination)
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Abstract

:
The analysis of nutrient concentrations in surface sediments is a reliable tool for assessing the trophic status of a water body. Nitrogen and phosphorus concentrations are strongly related to the sediment characteristics but are mainly driven by anthropogenic impacts. The results of the determination of total nitrogen and total inorganic and organic phosphorus in surface sediments of the lagoons and ponds of the northwestern Adriatic Sea (Marano-Grado, Venice, Po Delta, Comacchio Valleys, Pialassa della Baiona) show the merit of this approach. Indeed, when previous data are available, the ratio between the actual and background values can provide useful information on the trophic changes that have occurred in the most recent times, and the results can also explain the conditions present in less studied environments. In this context, numerous studies performed in the Venice lagoon since the second half of the 20th century during different environmental scenarios provide mean concentration ranges and propose the main causes of changes. The results of single datasets available for the other lagoons fall into scenarios that occurred in the Venice lagoon. At present, the most eutrophic basins are Pialassa della Baiona, the Po Delta lagoons and ponds and the Comacchio valleys due to industrial effluents, fish farming and clam harvesting, respectively, whereas the Venice lagoon is now experiencing environmental recovery.

Graphical Abstract

1. Introduction

In transitional water systems (TWSs; lagoons, ponds, deltas, estuaries, fjords), nutrient concentrations in surface sediments are key parameters strictly related to changes of anthropogenic impacts [1,2,3], mostly eutrophication [3,4,5,6,7,8], river inputs [9,10,11] and clam harvesting [12,13,14,15,16]. Since the Second World War, the rapid increases in industrial activities, agriculture, urban centers and tourism have profoundly altered the trophic conditions of the TWS [4,5], and sediments have proved to be an excellent litmus paper of the changes taking place. Indeed, they accumulate nutrients [17,18] and pollutants [19,20,21], above all, during the death of primary producers and the settlement of suspended particles [22,23].
The lagoon of Venice is the largest TWS in the Mediterranean Sea (549 km2) and presents the ecological conditions recorded in most of these coastal environments [24]. Data on the nitrogen and phosphorus concentrations in the surface sediments of the whole lagoon have been available since the second half of the 20th century [25,26,27] and are strongly correlated with the ecological changes observed over time [2]. Until the 1990s, a progressive increase of nutrients in the superficial sediments was observed, especially with regard to phosphorus, mainly due to (i) the production of nutrients by industrial synthesis (phosphates and ammonia); (ii) the draining waters from an areas of ca. 1800 km2 extensively cultivated with monocultures fertilized with high amounts of nutrients; (iii) the discharge of urban wastewater not yet fully treated from the historic center of Venice, the islands of the lagoon and the city of Mestre and its hinterland [28,29,30]. In addition, the nutrient increase in the water column and surface sediments [18,31] favored the massive production of nuisance macroalgae [21], which during their degradation, further increased the load of nutrients in the surface sediments. The same impacts, especially the increase in trophy with abnormal development of macroalgae nuisance, also affected other TWSs both in Italy and in many other countries worldwide [5,6].
Later, more extensive studies carried out in 2003 and 2011 showed a significant decrease of these eutrophic substances due to industrial activity’s decline, the implementation of water treatment plants equipped with a third stage for nitrogen and phosphorus abatement, the banning of phosphorus from detergent formulations (4–5% of total weight) in 1989 [1] and sediment remobilization during the intense Manila clam harvesting [15]. In 2014 and 2018, two additional extensive nutrient mapping studies were carried out but the data were again unpublished. Since 1987, for the central basin of the Venice lagoon, the TWS most studied due to its greater number of anthropogenic impacts, a greater number of mapping datasets are available for both phosphorus and nitrogen during different environmental scenarios.
On the other hand, there is little information from other TWSs of the Northern Adriatic Sea, data on which are scarce and fragmentary. Indeed, only a few data are available for the lagoons of Grado-Marano (2007) [32], the Po Delta (2008), Pialassa della Baiona (2009) and the Comacchio Valleys (2009) [33]. However, these data, all collected by our research group, are very useful to understand the correlations of nitrogen and phosphorus with the parameters associated with different ecological conditions.
This paper aimed to integrate the knowledge on the nitrogen and phosphorus concentrations in the TWS of the northern Adriatic Sea with particular reference to the Venice lagoon, of which a high number of data is available. The complete dataset allows us to analyze the interactions of nutrients with other sediment characteristics and the ecological conditions of these TWSs as a function of anthropogenic impacts and climate changes. The results allow to understand the roles of these elements as indicators of ecological changes and for forecasting future trends.

2. Materials and Methods

2.1. Description of Study Areas and Sampling Campaigns

The lagoons and ponds investigated in this paper are reported in Figure 1. From the north to the northwestern Adriatic Sea, they are: Marano-Grado lagoon, Venice lagoon, Po Delta lagoons and ponds, Comacchio valleys and Pialassa della Baiona lagoon. The stations sampled in 2003 in the Venice lagoon were selected to study the biomass distribution of macrophytes [34]. All the stations sampled in the Venice lagoon since 2011 and the stations sampled in the other lagoons were selected by the Italian Regional Agencies for Environmental Prevention and Protection. Sampling was carried out to determine the ecological status of TWSs in the framework of the European Water Framework Directive 2000/60/EC by using the biological element “Macrophytes”. On this occasion, our research group also collected surface sediments to study some sediment characteristics and nutrient concentrations.

2.1.1. The Venice Lagoon

The lagoon of Venice (45°11′–45°34′ N, 12°08′–12°38′ E) (Figure 1) is the largest and the most studied TWS of the Mediterranean Sea. It is located in the northwestern Adriatic Sea and extends over an area of ca. 549 km2 accounting for ca. 39% of the total Italian TWSs [24]. The waters have a mean depth of ca. 1.2 m, ranging from a few centimeters in the shallower areas to 15–20 m in the main channels. The water exchange with the sea is mainly driven by tidal action [35]—through the three wide (600–900 m) and deep (12–15 m) inlets of Lido, Malamocco and Chioggia—and accounts for ca. 60% of the total reservoir every 12 h [36], whereas the freshwater inputs (ca. 34.5 m3 s−1) are negligible [37]. This allows a high grain-size difference between the sandy areas close to the inlets where water exchange (ca 19,000 m3 s−1) occurs in a few hours, and the clay chocked areas where water renewal may take 40 days [38]. The lagoon is morphologically separated in three main basins—from the salt marshes of Burano and Torcello in the north and the Malamocco-Marghera canal in the south—showing very different morpho-ecological conditions, the central basin being the most polluted and most affected by anthropogenic impacts.
Since 2003, the research team at the Marine Ecology Lab, Ca’ Foscari University of Venice (Italy) has collected data on the nitrogen and phosphorus concentrations in the superficial sediments of the entire lagoon. Sampling campaigns were carried out in 2003 (165 stations), 2011 (118 stations), 2014 and 2018 (88 stations), in the late spring to early summer period. In this paper, the concentrations recorded at 85 common stations sampled in all the four surveys are analyzed and compared.
In addition, the concentrations of phosphorus compounds (Ptot = total phosphorus, Pinorg = inorganic phosphorus, Porg = organic phosphorus) were recorded at 34 stations of the central lagoon (132 km2) in 1987, 1993, 1998, 2003, 2011, 2014 and 2018, during different ecological scenarios that characterized the lagoon since the late 1980s: the dominance of nuisance macroalgae (1987) [18,34]; the decline of nuisance macroalgae (1993) [39]; the intense Manila clam (Ruditapes philippinarum) harvesting activities (1998–2003) [15]; the collapse of clam stocks (2011) [2]; the decrease of anthropogenic impacts and the beginning of the lagoon’s environmental recovery (2014–2018) [2].

2.1.2. The Lagoon of Marano-Grado

The Marano-Grado lagoon (45°41′–45°46′ N, 13°04′–12°27′ E) (Figure 1) has morphological features similar to those of the Venice lagoon with a surface of ca. 160 km2 and a tidal difference of 65 cm [36]. It is subdivided in two main basins: The Marano basin, a wide shallow water body characterized by a few islands and tidal-marshes, and the Grado basin, which is rich in morphological reliefs and is shallower than the Marano basin [40]. The average freshwater inflow is ca. 98.5 m3s−1 [41], whereas water exchange with the sea occurs through three main inlets (Lignano, Porto Buso, Grado) and other smaller mouths. Fine sediments are on average greater at Grado than at Marano and are prevalently calcareous. Information on the nutrient content is scarce. Falace et al. [42] report data for the total nitrogen (Ntot) only, with the concentration ranging from 0.5 mg g−1 at the sea-inlets, to 1.5 mg g−1 at the internal edges. Samples of surface sediments for the analysis of Ntot, Ptot, Pinorg and Porg were collected at 20 stations evenly distributed throughout the lagoon in summer 2007.

2.1.3. Po Delta Lagoons and Ponds

The Po Delta (44°09′–45°47′ N, 12°16′–12°32′ E) (Figure 1) has a water surface of ca. 204 km2 and is sorted into many lagoons and ponds with depths ranging from 0.5 to 2.5 m, according to the water body. Salinity is the most variable parameter due to the many branches of the Po River. Hard substrata are rare and mainly represented by some stone embankments along the edges of the various basins and oyster beds scattered on their bottoms. Clam-farming and clam-fishing activities are very intense and cause high sediment resuspension with severe environmental consequences. The main primary producers of the Po Delta basins are phytoplankton in the areas affected by clam harvesting or free-floating nuisance macroalgae, especially Ulvaceae, Gracilariaceae and Solieriaceae, in the other areas with lower anthropogenic impact. Populations of the aquatic angiosperm Ruppia cirrhosa (Petagna) Grande that before the 1990s colonized some basins have now completely disappeared [43]. Samples of surface sediments were collected in 2008 at 20 stations (three at Caleri, two at Marinetta, two at Vallona, three at Barbamarco, three at Canarin, four at Scardovari and three at Goro) during late spring-early summer period.

2.1.4. Comacchio Valleys

The Comacchio valleys (44°55′–44°65′ N, 12°10′–12°25′ E) (Figure 1) are a complex of choked shallow ponds with a surface of ca. 110 km2, connected with the sea by two small channels that do not allow for sufficient water renewal. They are affected by anthropogenic impacts like fish farming, especially eel farming, and receive freshwater from the Reno River that has shifted the ecological conditions from a good ecological status dominated by aquatic angiosperms and macroalgae of high ecological value, to a degraded and homogeneous basin dominated by phytoplankton and picocyanobacterial blooms of poor-to-bad status [44,45,46]. Samples for nutrient analyses of surface sediments were collected at two stations, Donna Bona and Dosso Pugnalino, in the main basin during late spring or early summer 2009.

2.1.5. Pialassa Della Baiona

The Pialassa della Baiona lagoon (44°28′–44°31′ N, 12°14′–12°16′ E) (Figure 1) is a shallow basin of ca. 11 km2 characterized by a mean depth of 60 cm. It is furrowed by a network of herringbone canals, 1–4 m deep, which converge towards the Ravenna harbor connected with the Adriatic Sea. The freshwater inputs, coming from a network of small canals draining an intensively cultivated area, are negligible. The basin is colonized by rich populations of macroalgae, especially the non-indigenous species Agarophyton vermiculophyllum [43,47] (Ohmi) Gurgel, J.N. Norris et Fredericq. This species covers mostly the southern part of the lagoon with a biomass of 5–10 kg m−2 on a fresh weight (fwt) basis. It is a little studied basin characterized by poor ecological conditions [48]. Surface sediments were sampled at three stations—Chiaro Magni, Chiaro Risega and Vena del Largo—in 2009 in late spring to early summer. For this basin, no other samples are available.

2.2. Sediment Sampling

At each station, three subsamples of surface sediments (5 cm top layer) were sampled by a Plexiglas corer (i.d. 10 cm) and mixed together. One subsample (ca. 100 mL) was retained for nutrient (total nitrogen, total phosphorus, inorganic phosphorus, organic phosphorus) analyses and another (ca. 50 mL) for the determination of the sediment density and grain size. Both subsamples were stored at −20 °C until the laboratory analyses.

2.3. Nutrient Determination in Surface Sediments

Information on the concentrations of Ptot and Ntot in the sediments of the whole lagoon date back to the mid-20th century. The analyses were carried out in the first 30 cm in 1948–49 and 1968–73 and in the first 20 cm in 1983 and 1987–88. In those periods, sediments were collected with a bucket to study the benthic communities [49,50]. During the following years, sediments were collected with a plexiglass corer (i.d. 10 cm) retaining the first 20 cm [27] or 5 cm top layer (this paper). This latter thickness is the sediment most affected by the growth and degradation cycles of macrophytes.
In the laboratory, sediments were freeze-dried and pulverized using a sediment mill (Fritsch Pulverisette, Germany). The concentration of total nitrogen (Ntot) was measured in duplicate by a CHNS Analyzer (Vario-MICRO, Elementar CHNS by Elementar Italia S.r.l.) after an accurate sample powdering of ca. 0.3 g of sample. The standard used was “low level N- and S-contents” with N = 0.74%, art. no. 05 000 959.
Total phosphorus (Ptot) was determined after sample combustion in the muffle at 550 °C for at least 2 h of 0.3–0.4 g of sample. Subsequently, the residue thus obtained was suspended in 50 mL of 1 N HCl and sonicated for ca. 30 min. After allowing the sample to settle for at least 1 h, 0.5 mL of the supernatant were taken with a graduated gas-chromatographic syringe and brought to exactly 10 mL using volumetric flasks for a final dilution of 1 L, with the result expressed directly in µM. At this point, the phosphorus concentration was determined by spectrophotometry by adding the mixed reagent and reading the absorbance at 885 nm after ca. 10–15 min [51]. Inorganic phosphorus was obtained with the same procedure used for Ptot but without combustion at 550 °C. Organic phosphorus (Porg) was determined by difference. All samples were analyzed in duplicate and the analyses were replicated on two different days to obtain an accuracy > 95. Otherwise, the analyses were repeated until the coefficient of variation (standard deviation/mean) between two replicates was < 5%.

2.4. Map Preparation

Maps of nutrient distribution were prepared in six concentration ranges by using data collected in the surveys carried out in 2003, 2011, 2014 and 2018. Maps were obtained by Kriging methods using the software R, version 4.0.3, and SAGA, version 2.3.2. Models for each analysis were selected to minimize the prediction errors, and model performances were estimated using cross-validation procedures. Maps were then produced using the software QGIS, version 3.6.0 and integrated into one image using Corel Paintshop Pro X5, version 15.0.0.183 (Corel Corporation, 2012).

2.5. Sediment Characteristic Determination

Dry sediment density (g DWT cm−3) was determined in the laboratory by sediment desiccation at 110 °C in tared crucibles of 20–30 mL. The percentage of Fines (fraction <63 µm) was obtained by wet sieving ca. 50 g of dried sediment throughout Endecotts sieves (ENCO Scientific Equipment, Spinea, Italy). All analyses were performed in duplicate.

2.6. Statistical Analyses

The analysis of variance (one-way ANOVA) allowed us to test differences of the sediment parameters in different monitoring periods. The differences were considered significant when p < 0.05. Prior to the analyses, the distribution of each variable was checked for normality and homogeneity of variance by the Kolmogorov-Smirnov test (p < 0.05).
Pearson coefficients (p < 0.05, p < 0.001) highlighted the correlations among environmental parameters and variables using STATISTICA software, version 10 (StatSoft Inc., Tulsa, OH, USA).
Principal component analysis (PCA), determined using the same software, showed the multivariate patterns of the matrix of 162 cases (stations) and five variables (sediment density, fines, inorganic and organic phosphorus, total nitrogen). The significant loading was considered to be at p > 0.7. Moreover, the PCA analysis of the transposed matrix showed the affinity between stations and lagoons.

3. Results

3.1. Nutrient Concentrations and Sediment Characteristics

The mean values of the dry density, the percentages of the fine fraction and the concentrations of nutrients in the surface sediments of the single and total TWSs are reported in Figure 2 and Table S1 (Supplementary Material).
On the whole, the average dry density of all the sampling sites was 0.92 g cm−3 on a dry weight (dwt) basis. The highest density was recorded in the Venice lagoon (0.96 g dwt cm−3), whereas Pialassa della Baiona and the Comacchio valleys showed the lowest values (0.59 g cm−3). The amount of fines on average was 70.2%, with the highest and the lowest concentrations in the Pialassa della Baiona (87.5%) and Comacchio valleys, (57.0%), respectively. Pialassa della Baiona also showed the highest concentrations of Ntot (3.09 mg g−1), Ptot (717 µg g−1), Pinorg (537 µg g−1) and Porg (180 µg g−1). Total phosphorus showed the lowest value at Marano (334 µg g−1), where Ntot was also particularly low (1.23 mg g−1), just higher than that found in the Venice lagoon (1.19 mg g−1).

3.2. Nutrient Variations in the Venice Lagoon

The nutrient concentrations recorded in the whole Venice lagoon by our research team were recorded during four surveys carried out in late spring to early summer 2003, 2011, 2014 and 2018 (Table 1).
Both Ptot and Ntot showed no significant changes. Indeed, the mean values of Ptot recorded in this period were almost the same, ranging from 403 to 412 µg g−1. Similar results were recorded for the minimum and maximum values. On the other hand, Ntot showed more marked changes. The mean concentration recorded in 2003 was 1.42 mg g−1. This value decreased to 1.19 mg g−1 in 2011 and increased again in 2014 (1.38 mg g−1) and 2018 (1.28 mg g−1). The minimum and maximum values were also different, showing more marked extreme values in 2003 and 2011, compared to subsequent periods.
All data for the Ntot, Ptot and Porg concentrations recorded in the surface sediments of the whole Venice lagoon were plotted on maps within six concentration ranges (Figure 3). In 2003, Ntot showed the highest concentrations in the south, southwestern and northern parts of the lagoon. The same was also observed in 2014 and 2018. On the other hand, in 2011, Ntot showed a marked decreased in the whole lagoon, with the lowest values in the central basin.
Total phosphorus did not show significant changes but only a spatial redistribution with the highest concentrations found in the same areas of Ntot. Organic phosphorus showed greater changes. Indeed, the mean concentration recorded in 2003 was 79 ± 56 µg g−1. This value increased to 91 ± 63 µg g−1 in 2011, only to decrease to 81 ± 54 µg g−1 in 2018. The highest changes were recorded in the eastern parts of the central and southern basins.
A better interpretation of the nutrient trends can be obtained from the temporal changes that occurred in the central lagoon, which was monitored several times by our research group between 1987 and 2018, sampling the same 34 stations and considering the same sediment thickness (Table 2).
The total nitrogen displayed the greatest changes. In late spring to early summer 1987, during the period of luxuriant macroalgal growth, the mean Ntot value was 1.25 mg g−1 (Table 2, Figure 4). The mean value in the period of clam harvesting decreased to 0.34 mg g−1 in late spring to early summer 2011, then increased slightly in 2014 and 2018 (0.83 and 0.81 mg g−1, respectively). The decrease in the period 1987–2011 was −72.8%, whereas between 1987 and 2018 it was −35.2% (Figure 4).
The total phosphorus and Pinorg showed no significant changes (Table 2). Instead, Porg had similar variations to Ntot. Indeed, Porg decreased from 109 µg g−1 in 1987 to 53 µg g−1 in 2003, and increased to 66 and 64 µg g−1 in 2014 and 2018, respectively. The difference between 1987 and 2003 was −51.4%, whereas between 1987 and 2018 it was −41.3% (Figure 4).
The one-way ANOVA of the Ntot and Porg concentrations in surface sediments of the central Venice lagoon between the successive sampling periods showed a different behavior for the two nutrients (Table 3). Nitrogen decrease occurred between 1993 and 2011 and was significantly related to clam harvesting activities. In contrast, Porg changes were only significant in the period 1987–1993 when the macroalgal biomass of nuisance macroalgae decreased sharply.

3.3. Statistical Analyses

The statistical analysis (non-parametric Spearman’s coefficients) of nutrient concentrations and sediment characteristics recorded in all the considered TWSs showed a high number of positive or inverse correlations between the sediment dry density and grain-size (fines) and the nutrient concentrations (Table 4). Among them, particularly relevant was the negative correlation of sediment density with Porg (r = −0.84). Conversely, Pinorg showed the fewest number of correlations with the other parameters.
Principal component analyses (PCAs) of the first two components applied to the whole stations sampled in the Marano-Grado lagoons in 2007, Po Delta lagoons and ponds in 2008, Comacchio valleys and Pialassa della Baiona in 2009 and 2011 (the closest dates to those sampled in the Venice lagoon) are shown in Figure 5a. The first two components explained 70.8% of the total variance and dry density. Organic phosphorus and Pinorg showed a loading > 0.7. In addition, PCA highlighted the affinity among parameters, showing a strong association of nutrients with fines as opposed to the sediment density.
The PCA of the transposed matrix applied to the same parameters and stations (Figure 5b) shows the clustering among the stations of the different TWSs. The stations of the Venice lagoon cover the whole biplot, showing high heterogeneity. Among them, some outliers are represented by stations placed inside choked fishing ponds (Doga valley, Cavallino valley) that present peculiar conditions, being separated from the tidal exchange of the open lagoon. The other lagoons and ponds are grouped and placed only in a restricted part of the biplot, showing greater homogeneity.

4. Discussion

The concentrations of nutrients in the surface sediments of the lagoons of the northwestern Adriatic Sea showed a close relationship with sediment characteristics such as the grain size and density. In fact, finer-sized sediments had a greater relative surface and a greater capacity to retain nutrients and pollutants. Vaze and Chew [52] found that almost all the TP and TN were attached to sediments with grain sizes between 11 and 150 µm. Furthermore, their density was lower due to the presence of a greater quantity of interstitial water, which in turn contains, high concentrations of nutrients, especially ammonium [53].
In the case of the Venice lagoon, of which we have numerous data collected in different periods, significant temporal variations due to different anthropogenic impacts were also monitored.
In general, the highest sediment concentrations of Ntot, Ptot, Pinorg and Porg were recorded in Pialassa della Baiona, characterized by the highest percentage of fines (fraction < 63 µm: 87.5%) and the lowest density (0.59 g dwt cm−3). The same low sediment density was also recorded in the Comacchio valleys. However, the Comacchio valleys showed a significantly lower percentage of fines (57.0%), which could explain the lower concentrations of nitrogen and phosphorus in the sediments of this basin. Moreover, the poor water renewal of the Comacchio valleys accounted for the bad ecological conditions of these large ponds recorded since the last two decades of the 20th century. Despite the fact that for this basin, previous data on nutrient concentrations are missing, the list of macrophytes reported by [54] and [55] highlights that before the 1970s, the Comacchio valleys were colonized by aquatic angiosperms such as Ruppia cirrhosa (Petagna) Grande and Zostera noltei Hornemann, and sensitive macroalgae. First of all, these included Lamprothamnium papulosum (Wallroth) J. Grove, a Chlorophycea even more sensitive than aquatic angiosperms and currently present only in some fishing valleys of the Venetian lagoon such as the Cavallino valley, which shows almost pristine ecological conditions [43]. The presence of that vegetation was linked to a low trophy and nutrient concentrations certainly lower than the current ones. Indeed, in the following years, almost all the macrophytes disappeared from the valleys and only cyanobacteria and phytoplankton were recorded [44,45,46]. Discharges from fish farms, especially from eel breeding, the polluted water drainage from extensive agricultural practices and freshwater inputs from the Reno river have irremediably changed the trophic status of these basins and eliminated the macrophytes present, even those of low ecological value. Recently, some small thalli of some tionitrophilic Chlorophyceae, mostly Ulvaceae, have been recorded at only 5–15 cm from the surface because the waters were very turbid and the transparency never exceeded 25–40 cm all year round.
On the whole, the Marano-Grado and Venice lagoons were the less eutrophicated basins, showing the lowest mean concentrations of Ptot (334 and 403 µg g−1, respectively) and Ntot (1.23 and 1.19 mg g−1, respectively). The Comacchio valleys had intermediate concentrations.
However, for the Venice lagoon, many data are available from the mid-20th century (Table 5).
The concentrations of Ptot and Ntot recorded in 1948–49, before the development of the industrial area of Porto Marghera, were very low and can be considered the background values for the lagoon. Indeed, the mean value of the Ptot concentration was only 24 µg g−1, whereas Ntot was 1.00 mg g−1 [49]. Twenty years later, both nutrients were recorded by the same authors at the same stations to have increased markedly. Total phosphorus increased ca. 6.8 times (164 µg g−1) and Ntot almost doubled (1.86 mg g−1 [49]). The highest Ptot concentrations were recorded in 1983, with a mean value of 454 µg g−1 [50], ca. 19 times greater than the value recorded in 1948–49, whereas Ntot reached the highest value in 1968–73, with a mean value of 1.86 mg g−1 [49]. However, single stations close to the industrial area of Porto Marghera reached 1102 µg g−1 for Ptot in 1987–88 and 4.9 mg g−1 for Ntot in 2003. Indeed, after the Second World War, the lagoon received sewage effluents from about 300,000 inhabitants of Venice, Mestre, Marghera and Chioggia, wastes from chemical and steel plants located in the 30-km2 Porto Marghera industrial area and runoff from an intensively-cultivated drainage basin (ca. 2000 km2). Particularly relevant was the massive extraction of phosphorus from phosphorites and the industrial synthesis of ammonia to support the rapidly expanding agricultural production [56,57]. The main consequence was the high pollution of water and sediments. Phosphorus rapidly accumulated in surface sediments until the end of production in the mid-1980s. In the following years, Ptot showed a reverse trend but its concentrations fluctuated between 403 and 412 µg g−1 because this element remained trapped in the sediments due to its sedimentary cycle. In contrast, Ntot changed slightly. It was higher in 2003 (1.42 ± 1.42 mg g−1) and decreased markedly in 2011 (1.19 ± 1.95 mg g−1) during the maximum clam fishing activities [2] that favored nitrogen release in the water column as ammonium and loss into the atmosphere due to the high denitrification processes [58]. In the following years, when clam fishing activities were negligible, Ntot increase again.
The studies carried out in the central part of the Venice lagoon are more recent but they show the variations of nutrients in the sediments (Table 2, Figure 4) during the various scenarios that have characterized the lagoon from the 1980s to today. In addition, for the central lagoon, Pinorg and Porg were also determined, highlighting the significant changes of Porg while Pinorg remained almost unchanged. The concentrations of Porg and Ntot were mainly affected by the presence of a high biomasses of macroalgae and the intensity of clam-fishing activities, which had an inverse impact on nutrient concentrations. Macroalgae produced great quantities of decomposing organic matter, which enriched surface sediments with both Ntot and Porg, whereas biomass reduction and fishing activities occurring between 1995 and 2012, plowing the sediments to a depth of 15–20 cm, which released into the water column the ammonium and reactive phosphorus present in interstitial waters. As a consequence, the Ntot (−73%) in 2011 and Porg (−51%) in 2003 reached their minimum concentrations (Figure 4). In the following years, when clam fishing was negligible or completely absent, both Ntot and Porg increased again but without reaching the concentrations recorded in 1987 due to the negligible macroalgal biomass present in this period. A one-way ANOVA confirmed that the most significant decrease of Ntot was due to clam-harvesting that triggered the release of ammonium from surface sediments into the water column. In contrast, the strong reduction of the macroalgal biomass [36] was the main cause of Porg decreasing. The analysis of the global data (Spearman’s coefficients and PCA) confirms that nutrient concentrations were positively correlated with the sediment grain size (fines) and inversely with sediment density as recorded from many other analyses carried out in these environments [24,59].
Finally, plotting all the stations in the transposed PCA matrix highlights that the concentrations of nutrients in the surface sediments of the Venice lagoon cover all the concentrations recorded in the Po Delta, Marano-Grado, Comacchio and Pialassa della Baiona, which present lower environmental variability, as recorded in [24].
If we consider the concentrations of nutrients in the sediments of other lagoons recorded in the literature, Sørensen et al. [60] reported the concentrations of Ntot and Ptot in the Keta lagoon (Ghana) and compared their results with those of other lagoons around the world. In the Keta lagoon, Ptot and Ntot were in the ranges of 130–240 µg g−1 and 0.1–1.0 mg g−1, respectively. These values were similar to the values recorded in a lagoon of the Balearic islands, Spain [61] and in the Ringkjøbing Fjord, Denmark [62] (Table S2, Supplementary Material), but were significantly lower than the values recorded in this study.
Nutrient concentrations similar to those recorded in the TWS of the northwestern Adriatic Sea were recorded in a system of eutrophic lagoons in northwestern Mexico [63], where Ptot and Ntot were in the ranges of 341–1240 µg g−1 and 0.15–8.89 mg g−1, respectively. High nutrient values were also recorded in the Méjean-Pérols lagoon (France) [64], with Ptot and Ntot concentrations in the ranges of 398–1147 µg g−1 and 1.9–6.0 mg g−1, respectively. Intermediate concentrations were found in some lagoons of the Sabana-Camagüey archipelago at Cuba [65]. In these basins, Ptot and Ntot showed concentrations up to 241 µg g−1 and 11.5 mg g−1, respectively. Therefore, the TWSs of the northwestern Adriatic Sea are placed among the most eutrophic basins and have concentrations strongly linked to the grain-size of the sediment. The Venice lagoon, due to its large surface and the heterogeneity of its micro-environments, presents conditions that cover the concentrations found in most of the other basins.

Supplementary Materials

The following are available online at https://www.mdpi.com/article/10.3390/w13202914/s1, Table S1. Mean, Std, Min, Max values of chemico-physical parameters in the Italian studied la-goons. Table S2. Average concentrations of Ptot and Ntot in the Italian lagoons and in other world transition systems.

Author Contributions

Conceptualization, A.S. and M.M.; formal analysis, A.B., Y.T., A.-S.J. and A.A.S.; funding acquisition, A.S.; investigation, A.S. and A.A.S.; methodology, A.S. and A.A.S.; supervision, A.S., M.M. and C.M.; visualization, A.S. and M.M.; writing—original draft, A.S. and A.A.S.; writing—review & editing, A.S. and A.A.S. All authors have read and agreed to the published version of the manuscript.

Funding

This research was not funded.

Acknowledgments

The authors thank ARPA of the Veneto, Emilia Romagna and Friuli-Venezia Giulia regions for financing the data collection of some measurement campaigns. Thanks also go to the anonymous reviewers who, with their useful suggestions, have made it possible to improve the paper.

Conflicts of Interest

The authors declare no conflict of interest.

References

  1. Solidoro, C.; Bandelj, V.; Bernardi, F.A.; Camatti, E.; Ciavatta, S.; Cossarini, G.; Facca, C.; Franzoi, P.; Libralato, S.; Melaku Canu, D.; et al. Response of the Venice Lagoon Ecosystem to Natural and Anthropogenic Pressures over the last 50 years. In Coastal Lagoons—Critical Habitats of Environmental Change; Kennish, M.J., Paerl, H.W., Eds.; CRC Press: Boca Raton, FL, USA, 2010; Chapter 19; pp. 483–511. [Google Scholar]
  2. Sfriso, A.; Buosi, A.; Mistri, M.; Munari, C.; Franzoi, P.; Sfriso, A.A. Long-Term Changes of the Trophic Status in Transitional Ecosystems of the Northern Adriatic Sea, Key Parameters and Future Expectations: The Lagoon of Venice as a Study Case. Nat. Conserv. 2019, 34, 193–215. [Google Scholar] [CrossRef]
  3. Jessen, C.; Bednarz, V.N.; Rix, L.; Teichberg, M.; Wild, C. Marine Eutrophication. In Environmental Indicators; Armon, R.H., Hänninen, O., Eds.; Springer: Berlin, Germany, 2015; pp. 177–203. [Google Scholar]
  4. Wolfe, D.A. Estuarine Variability; Academic Press, Inc: Orlando, FL, USA, 1986; p. 509. [Google Scholar]
  5. Schramm, W.; Nienhuis, P.H. Marine Benthic Vegetation. Recent Changes and Effects of Eutrophication; Springer: Berlin, Germany, 1990; p. 470. [Google Scholar]
  6. Nedwell, D.B.; Jickells, T.D.; Trimmer, M.; Sanders, R. Nutrients in Estuaries. Estuaries 1999, 29, 43–92. [Google Scholar]
  7. Pastres, R.; Solidoro, C.; Ciavatta, S.; Petrizzo, A.; Cossarini, G. Long-term changes of inorganic nutrients in the Lagoon of Venice (Italy). J. Mar. Syst. 2004, 51, 179–189. [Google Scholar] [CrossRef]
  8. Velasco, J.; Lloret, J.; Millan, A.; Marin, A.; Barahona, J.; Abellan, P.; Sanchez-Fernandez, D. Nutrient and particulate inputs into the mar menor lagoon (Se Spain) from an intensive agricultural watershed. Water Air Soil Pollut. 2006, 176, 37–56. [Google Scholar] [CrossRef]
  9. Moutin, T.; Raimbault, P.; Golterman, H.L.; Coste, B.; Rouzic, B. The input of nutrients by the Rhône river into the Mediterranean Sea: Recent observations and comparison with earlier data. Hydrobiologia 1997, 373, 237–246. [Google Scholar] [CrossRef]
  10. Brown, J.B.; Sprague, L.A.; DuPree, J.A. Nutrient sources and transport in the Missouri River basin, with emphasis on the effects of irrigation and reservoirs1. JAWRA J. Am. Water Resour. Assoc. 2011, 47, 1034–1060. [Google Scholar] [CrossRef] [Green Version]
  11. Collavini, F.; Bettiol, C.; Zaggia, L.; Zonta, R. Pollutant loads from the drainage basin to the Venice Lagoon (Italy). Environ. Int. 2005, 31, 939–947. [Google Scholar] [CrossRef] [PubMed]
  12. Bartoli, M.; Nizzoli, D.; Viaroli, P.; Turolla, E.; Castaldelli, G.; Fano, E.A.; Rossi, R. Impact of Tapes philippinarum farming on nutrient dynamics and benthic respiration in the Sacca di Goro. Hydrobiologia 2001, 455, 203–212. [Google Scholar] [CrossRef]
  13. Castaldelli, G.; Mantovani, S.; Welsh, D.T.; Rossi, R.; Mistri, M.; Fano, E.A. Impact of commercial clam harvesting on water column and sediment physicochemical characteristics and macrobenthic community structure in a lagoon (Sacca di Goro) of the Po River Delta. Chem. Ecol. 2003, 19, 161–171. [Google Scholar] [CrossRef]
  14. Pranovi, F.; Da Ponte, F.; Torricelli, P. Historical changes in the structure and functioning of the benthic community in the lagoon of Venice. Estuar. Coast. Shelf Sci. USA 2008, 76, 753–764. [Google Scholar] [CrossRef] [Green Version]
  15. Sfriso, A.; Facca, C.; Ceoldo, S.; Silvestri, S.; Ghetti, P.F. Role of macroalgal biomass and clam fishing on spatial and temporal changes in N and P sedimentary pools in the central part of the Venice lagoon. Oceanol. Acta 2003, 26, 3–13. [Google Scholar] [CrossRef] [Green Version]
  16. Sfriso, A.; Facca, C.; Marcomini, A. Sedimentation rates and erosion processes in the lagoon of Venice. Environ. Int. 2005, 31, 983–992. [Google Scholar] [CrossRef] [PubMed]
  17. Cunha, D.G.F.; Calijuri, M.D.C.; Dodds, W.K. Trends in nutrient and sediment retention in great plains reservoirs (USA). Environ. Monit. Assess. 2014, 186, 1143–1155. [Google Scholar] [CrossRef] [PubMed]
  18. Sfriso, A.; Pavoni, B.; Marcomini, A.; Orio, A.A. Annual variations of nutrients in the lagoon of Venice. Mar. Pollut. Bull. 1988, 19, 54–60. [Google Scholar] [CrossRef]
  19. Song, Y.; Zhou, Q.; Song, X.; Zhang, W.; Sun, T. Accumulation of pollutants in sediments and their eco-toxicity in the wastewater irrigation channel of western Shenyang. Ying yong sheng tai xue bao = J. Appl. Ecol. 2004, 15, 1926–1930. [Google Scholar]
  20. Sakan, S.M.; Đorđević, D.S.; Manojlović, D.D.; Predrag, P. Assessment of heavy metal pollutants accumulation in the Tisza river sediments. J. Environ. Manag. 2009, 90, 3382–3390. [Google Scholar] [CrossRef] [PubMed]
  21. Marcomini, A.; Sfriso, A.; Zanette, M. Macroalgal Blooms, Nutrient and Trace Metal Cycles in a Coastal Lagoon. In Macroalgae, Eutrophication and Trace Metal Cycling in Estuaries and Lagoons; Rijstenbil, J.W., Haritonidis, S., Eds.; Proceedings of the COST-48 Symposium of Sub Group III Thessaloniki, Commission of the European Communities, Biotechnology Research for Innovation, Development and Growth in Europe (BRIDGE); Thessaloniki, Greece, 24–26 September 1993, pp. 66–90.
  22. Clavier, J.; Chardy, P.; Chevillon, C. Sedimentation of particulate matter in the south-west lagoon of New Caledonia: Spatial and temporal patterns. Estuar. Coast. Shelf Sci. 1995, 40, 281–294. [Google Scholar] [CrossRef]
  23. Sfriso, A.; Pavoni, B.; Marcomini, A.; Raccanelli, S.; Orio, A. Particulate matter deposition and nutrient fluxes onto the sediments of the venice lagoon. Environ. Technol. 1992, 13, 473–483. [Google Scholar] [CrossRef]
  24. Sfriso, A.A.; Buosi, A.; Facca, C.; Sfriso, A.A. Role of environmental factors in affecting macrophyte dominance in transitional environments: The Italian Lagoons as a study case. Mar. Ecol. 2017, 105, 13. [Google Scholar] [CrossRef]
  25. Giordani-Soika, A.; Perin, G. L’inquinamento della laguna di Venezia: Studio delle modificazioni chimiche e del popolamento sottobasale dei sedimenti lagunari negli ultimi vent’anni. Boll. Mus. Civico Storia Nat. Venezia. 1974, 26, 25–68. [Google Scholar]
  26. Cossu, A.; De Fraja-Frangipane, E. Stato delle conoscenze sullo inquinamento della laguna di Venezia; Progetto Venezia, Ministero dei Lavori Pubblici, Magistrato alle Acque, Consorzio Venezia Nuova: Venezia, Italy, 1985; 4 vol. [Google Scholar]
  27. Consorzio Venezia Nuova (CVN); Magistrato alle Acque (MAV). Nuovi Interventi per la Salvaguardia di Venezia; Rapporto sullo Stato Attuale dell’Ecosistema Lagunare. Studio 1.3.9: Final Report: Venice, Italy, 1990; p. 361. [Google Scholar]
  28. Pavoni, B.; Sfriso, A.; Donazzolo, R.; Orio, A.A. Influence of waste waters from the city of Venice and the hinterland on the eutrophication of the lagoon. Sci. Total. Environ. 1990, 96, 235–252. [Google Scholar] [CrossRef]
  29. Marcomini, A.; Sfriso, A.; Pavoni, B.; Orio, A.A. Eutrophication of the Lagoon of Venice: Nutrient Loads and Exchanges. In Eutrophic Shallow Estuaries and Lagoons; Mc Comb, A.J., Ed.; CRC Press: Boca Raton, FL, USA, 1995; pp. 59–80. [Google Scholar]
  30. Sfriso, A.; Marcomini, A. The Lagoon of Venice (Italy). In Marine Benthic Vegetation, Ecological Studies; Schramm, W., Nienhuis, P.N., Eds.; Springer Verlag: Berlin/Heidelberg, Germany, 1996. [Google Scholar]
  31. Sfriso, A.; Facca, C.; Ceoldo, S.; Marcomini, A. Recording the occurrence of trophic level changes in the lagoon of Venice over the ‘90s. Environ. Int. 2005, 31, 993–1001. [Google Scholar] [CrossRef]
  32. Falace, A.; Curiel, D.; Sfriso, A. Study of the macrophyte assemblages and application of phytobenthic indices to assess the Ecological Status of the Marano-Grado Lagoon (Italy). Mar. Ecol. 2009, 30, 480–494. [Google Scholar] [CrossRef]
  33. Sfriso, A.; Facca, C.; Bon, D.; Giovannone, F.; Buosi, A. Using phytoplankton and macrophytes to assess the trophic and eco-logical status of some Italian transitional systems. Cont. Shelf Res. 2014, 81, 88–98. [Google Scholar] [CrossRef]
  34. Sfriso, A.; Facca, C. Distribution and production of macrophytes in the lagoon of Venice. Comparison of actual and past abundance. Hydrobiologia 2007, 577, 71–85. [Google Scholar] [CrossRef]
  35. Gačić, M.; Mosquera, I.M.; Kovačević, V.; Mazzoldi, A.; Cardin, V.; Arena, F.; Gelsi, G. Temporal variations of water flow between the Venetian lagoon and the open sea. J. Mar. Syst. 2004, 51, 33–47. [Google Scholar] [CrossRef]
  36. Masiol, M.; Facca, C.; Visin, F.; Sfriso, A.; Pavoni, B. Interannual heavy element and nutrient concentration trends in the top sediments of Venice Lagoon (Italy). Mar. Pollut. Bull. 2014, 89, 49–58. [Google Scholar] [CrossRef] [PubMed]
  37. Zuliani, A.; Zaggia, L.; Collavini, F.; Zonta, R. Freshwater discharge from the drainage basin to the Venice Lagoon (Italy). Environ. Int. 2005, 31, 929–938. [Google Scholar] [CrossRef]
  38. Cucco, A.; Umgiesser, G. Modeling the Venice Lagoon residence time. Ecol. Model. 2006, 193, 34–51. [Google Scholar] [CrossRef]
  39. Sfriso, A.; Marcomini, A. Decline of Ulva growth in the lagoon of Venice. Bioresour. Technol. 1996, 58, 299–307. [Google Scholar] [CrossRef]
  40. Gatto, F.; Marocco, R. Morfometria e geometria idraulica dei canali della laguna di Grado (Friuli-Venezia Giulia). Geogr. Fis. e Din. 1993, 16, 107–120. [Google Scholar]
  41. Marocco, R. Sediment distribution and dispersal in northern Adriatic lagoons (Marano and Grado paralic system). Geologia, serie 3a 1995, 57, 77–89. [Google Scholar]
  42. Falace, A.; Sfriso, A.; Curiel, D.; Matassi, G.; Aleffi, I.F. The Marano and Grado lagoon (North Adriatic Sea). In Flora and Vegetation of the Italian Transitional Water Systems; Cecere, E., Petrocelli, A., Izzo, G., Sfriso, A., Eds.; CoRiLa, Multigraf: Spinea, Italy, 2009; pp. 1–16. [Google Scholar]
  43. Sfriso, A.; Facca, C.; Bon, D.; Buosi, A. Macrophytes and ecological status assessment in the Po delta transitional systems, Adriatic Sea (Italy). Application of Macrophyte Quality Index (MaQI). Acta Adriat. 2016, 57, 209–226. [Google Scholar]
  44. Sorokin, Y.; Gnes, A. Structure and functioning of the anthropogenically transformed Comacchio lagoonal ecosystem (Ferrara, Italy). Mar. Ecol. Prog. Ser. 1996, 133, 57–71. [Google Scholar] [CrossRef] [Green Version]
  45. Sorokin, Y.I.; Zakuskina, O.Y. Features of the comacchio ecosystem transformed during persistent bloom of picocyano-bacteria. J. Oceanogr. 2010, 66, 373–387. [Google Scholar] [CrossRef]
  46. Munari, C.; Mistri, M. Ecological status assessment and response of benthic communities to environmental variability: The Valli di Comacchio (Italy) as a study case. Mar. Environ. Res. 2012, 81, 53–61. [Google Scholar] [CrossRef]
  47. Sfriso, A.; Buosi, A.; Wolf, M.A.; Sfriso, A.A. Invasion of alien macroalgae in the Venice Lagoon, a pest or a resource? Aquat. Invasions 2020, 15, 245–270. [Google Scholar] [CrossRef]
  48. Covelli, S.; Emili, A.; Acquavita, A.; Koron, N.; Fraganeli, J. Benthic biogeo-chemical cycling of mercury in two contaminated northern Adriatic coastal lagoons. Cont. Shelf Res. 2011, 31, 1777–1789. [Google Scholar] [CrossRef]
  49. Perin, G. L’inquinamento della Laguna di Venezia: Sintesi di sette anni di ricerche. Convegno: Tavola Rotonda “Problemi dell’inquinamento lagunare” 1974, 1, 47–89. [Google Scholar]
  50. Perin, G.; Pastre, B.; Orio, A.A.; Carniel, A.; Gabelli, A.; Pavoni, B.; Donazzolo, R.; Pasquetto, A. Inquinamento chimico del-la laguna di Venezia: Nutrienti e metalli pesanti nei sedimenti. Acqua Aria 1983, 6, 623–632. [Google Scholar]
  51. Aspila, K.I.; Agemian, H.; Chau, A.S.Y. A semi-automated method for the determination of inorganic, organic and total phosphate in sediments. Analyst 1976, 101, 187–197. [Google Scholar] [CrossRef]
  52. Vaze, J.; Chew, F.H.S. Nutrient loads associated with different sediment sizes in urban stormwater and surface pollutants. J. Environ. Eng. 2004, 130, 391–396. [Google Scholar] [CrossRef]
  53. Sfriso, A.; Marcomini, A. Macrophyte production in a shallow coastal lagoon. Part I. Coupling with physico-chemical param-eters and nutrient concentrations in waters. Mar. Environ. Res. 1997, 44, 351–375. [Google Scholar] [CrossRef]
  54. Ferrari, C.; Pirola, A.; Piccoli, F. Carta della vegetazione delle Valli di Comacchio [1:33.000] [Emilia- Romagna]. Ricerche Idro-biologiche nelle Valli di Comacchio. ll. Saggio cartografico della vegetazione delle Valli di Comacchio. Ann. Univ. Ferrara 1972, 1, 35–54. [Google Scholar]
  55. Giaccone, G. Features and changes of the vegetation of the lagoons of the northern Adriatic Sea as a result of pollution. (Lin-eamenti della vegetazione lagunare dell’Alto Adriatico ed evoluzione in conseguenza dell’inquinamento). Boll. Mus. Civico Storia Nat. Venezia 1974, 26, 87–98. [Google Scholar]
  56. Facco, S.; Degobbis, D.; Sfriso, A.; Orio, A.A. Space and Time Variability of Nutrients in the Venice Lagoon. In Estuarine Variability; Wolfe, D.A., Ed.; Academic Press, Inc.: New York, NY, USA, 1996; pp. 307–318. [Google Scholar]
  57. Pavoni, B.; Marcomini, A.; Sfriso, A.; Donazzolo, R.; Orio, A.A. Changes in an Estuarine Ecosystem. The Lagoon of Venice as a Case Study. In The Science of Global Change; Dunnette, D.A., O’Brien, R.J., Eds.; American Chemical Society: Washington, DC, USA, 1992; pp. 287–305. [Google Scholar]
  58. Sfriso, A.; Marcomini, A. Gross primary production and nutrient behaviours in shallow lagoon waters. Bioresour. Technol. 1994, 47, 59–66. [Google Scholar] [CrossRef]
  59. Sfriso, A.; Buosi, A.; Tomio, Y.; Juhmani, A.-S.; Facca, C.; Wolf, M.; Sfriso, A.A.; Franzoi, P.; Scapin, L.; Bonometto, A.; et al. Environmental restoration by aquatic angiosperm trans-plants in transitional water systems: The Venice Lagoon as a case study. Sci. Total Environ. 2021, 795, 148859. [Google Scholar] [CrossRef]
  60. Sørensen, T.H.; Vølund, G.; Armah, A.K.; Christiansen, C.; Jensen, L.B.; Pedersen, S.T. Temporal and spatial variations in concentrations of sediment nutrients and carbon in the Keta Lagoon, Ghana. West Afr. J. Appl. Ecol. 2003, 4, 91–105. [Google Scholar]
  61. Lopez, P.; Lluch, H.; Vidal, M.; Morguí, S.A. Adsorption of phosphorus on sediments of the Balearic islands (Spain) related to their composition. Estuar. Coast. Shelf Sci. 1996, 42, 185–196. [Google Scholar] [CrossRef]
  62. Pedersen, O.B.; Christiansen, C.; Laursen, M.B. Wind induced longterm increase and shortterm fluctuations of shallow water suspended material and nutrient concentration, Ringkøbing fiord, Denmark. Ophelia 1995, 41, 273–287. [Google Scholar] [CrossRef]
  63. de la Lanza-Espino, G.; Flores-Verdugo, F.J.; Hernandez-Pulido, S.; Penié-Rodríguez, I. Concentration of nutrients and C:N:P ratios in surface sediments of a tropical coastal lagoon complex affected by agricultural runoff. Universidad y Ciencia Trópico Húmedo 2011, 27, 145–155. [Google Scholar]
  64. Gomez, E.; Millet, B.; Picot, B. Accumulation des sels nutritifs dans un sediment lagunaire et environnement hydrody-namique. Oceanol. Acta 1998, 21, 805–817. [Google Scholar] [CrossRef] [Green Version]
  65. Zayas, R.G.-D.; Yera, A.B.; Artiles, M.M.; González, J.A.L.; Sandoval, F.S.C.; Merino-Ibarra, M. Trace metals in sediments of seven coastal lagoons of the Sabana-Camagüey Archipelago, Cuba. Soil Sediment Contam. Int. J. 2021, 30, 331–349. [Google Scholar] [CrossRef]
Water 13 02914 g001 550
Figure 1. Main transitional water systems (TWSs) of the northwestern Adriatic Sea.
Figure 1. Main transitional water systems (TWSs) of the northwestern Adriatic Sea.
Water 13 02914 g001
Water 13 02914 g002 550
Figure 2. Average values of sediment dry density (g cm−3), fines (fraction < 63 µm), phosphorus species (Ptot, Pinorg, Porg) and total nitrogen (Ntot) in the studied TWSs.
Figure 2. Average values of sediment dry density (g cm−3), fines (fraction < 63 µm), phosphorus species (Ptot, Pinorg, Porg) and total nitrogen (Ntot) in the studied TWSs.
Water 13 02914 g002
Water 13 02914 g003 550
Figure 3. Distribution maps of Ntot, Porg and Ptot in the surface sediments of the whole Venice lagoon.
Figure 3. Distribution maps of Ntot, Porg and Ptot in the surface sediments of the whole Venice lagoon.
Water 13 02914 g003
Water 13 02914 g004 550
Figure 4. Average values of (a) Ntot and (b) Porg concentrations recorded in the surface sediments (34 stations) and in the central Venice lagoon during different periods. Arrows show the concentrations decreased after 1987, with the lowest values recorded in 2011 for Ntot and 2003 for Porg, before the values increase to those recorded in 2018.
Figure 4. Average values of (a) Ntot and (b) Porg concentrations recorded in the surface sediments (34 stations) and in the central Venice lagoon during different periods. Arrows show the concentrations decreased after 1987, with the lowest values recorded in 2011 for Ntot and 2003 for Porg, before the values increase to those recorded in 2018.
Water 13 02914 g004
Water 13 02914 g005 550
Figure 5. (a) PCA among nutrient species, sediment density and grain size (fines). Red circles represent values of loading > 0.7. (b) PCA of the transposed matrix to highlight the station and lagoon associations. The different colors show different TWSs. Blue circles: Venice lagoon; black squares: Marano-Grado lagoon; ocher triangles: Po Delta lagoons and ponds; in red: Comacchio valleys and Pialassa della Baiona.
Figure 5. (a) PCA among nutrient species, sediment density and grain size (fines). Red circles represent values of loading > 0.7. (b) PCA of the transposed matrix to highlight the station and lagoon associations. The different colors show different TWSs. Blue circles: Venice lagoon; black squares: Marano-Grado lagoon; ocher triangles: Po Delta lagoons and ponds; in red: Comacchio valleys and Pialassa della Baiona.
Water 13 02914 g005
Table
Table 1. Changes of total nutrient concentrations in surface sediments of the Venice lagoon.
Table 1. Changes of total nutrient concentrations in surface sediments of the Venice lagoon.
Phosphorus and Nitrogen Changes in the Whole Venice Lagoon
2003–2018
Sediment Total PhosphorusTotal Nitrogen
YearsThicknessStationsµg g−1mg g−1
cmN°Mean StdminmaxMean STDminmax
20035165409±1132016771.42±1.420.0912.9
20115118403±1131996841.19±1.950.0311.5
2014588412±1112127071.38±1.300.176.98
2018588403±1161807161.28±1.090.196.98
Table
Table 2. Changes of total nutrient concentrations in surface sediments of the central basin of the Venice lagoon.
Table 2. Changes of total nutrient concentrations in surface sediments of the central basin of the Venice lagoon.
Total Nitrogen (Central Lagoon)Inorganic Phosphorus (Central Lagoon)
1987199319982003201120142018 1987199319982003201120142018
mg/g µg/g
Stations N°34343434353434Stations N°34343434353434
Mean1.251.260.890.710.340.830.81Mean287301308305283309293
Std0.590.700.380.360.520.470.45Std53665376626265
Min0.160.250.130.090.030.170.22Min193185202199179179164
Max2.722.851.451.482.072.022.37Max423461430485454424467
Total Phosphorus (Central Lagoon)Organic Phosphorus (Central Lagoon)
1987199319982003201120142018 1987199319982003201120142018
mg/g µg/g
Stations N°34343434343434Stations N°34343434343434
Mean397372370358341375357Mean109716253586664
Std82867999848586Std47344135343335
Min240236221201199212180Min4522122102010
Max577597560635563547548Max240149195150149143166
Table
Table 3. One-way ANOVA values between the different sampling periods of Ntot and Porg in surface sediments of the central Venice lagoon. n.s. = not significant values.
Table 3. One-way ANOVA values between the different sampling periods of Ntot and Porg in surface sediments of the central Venice lagoon. n.s. = not significant values.
Total Nitrogen (One-Way ANOVA 34 Stations)
PeriodSignificanceScenario
1987–1993n.s.Macroalgal biomass decrease
1993–1998p < 8.47 × 10−3Clam harvesting
1998–2003p < 4.27 × 10−2
2003–2011p < 7.81 × 10−4
2011–2014p < 8.68 × 10−5Lagoon resilience
2014–2018n.s.
1987–2018p < 6.97 × 10−4Total
Organic Phosphorus (One-Way ANOVA 34 Stations)
PeriodSignificanceScenario
1987–1993p < 2.86 × 10−4Macroalgal biomass decrease
1993–1998n.s.Clam harvesting
1998–2003n.s.
2003–2011n.s.
2011–2014n.s.Lagoon resilience
2014–2018n.s.
1987–2018p < 2.53 × 10−5Total
Table
Table 4. Spearman’s non-parametric coefficients between phosphorus species, total nitrogen, fines and density of surface sediments of all the lagoons and ponds considered. In blue are significant values: p < 0.05 for r ≥ ± 0.19; in red are highly significant values p < 0.001 for r ≥ ± 0.41.
Table 4. Spearman’s non-parametric coefficients between phosphorus species, total nitrogen, fines and density of surface sediments of all the lagoons and ponds considered. In blue are significant values: p < 0.05 for r ≥ ± 0.19; in red are highly significant values p < 0.001 for r ≥ ± 0.41.
Spearman’s Non Parametric Coefficients
FinesDensityPtotPinorgPorgNtot
Fines1.00
Density−0.551.00
Ptot0.22−0.501.00
Pinorg0.08−0.140.851.00
Porg0.49−0.840.570.131.00
Ntot0.19−0.460.410.200.511.00
Table
Table 5. Global changes of total nutrient concentrations in surface sediments of the Venice lagoon since the mid-20th century.
Table 5. Global changes of total nutrient concentrations in surface sediments of the Venice lagoon since the mid-20th century.
Phosphorus and Nitrogen Changes in the Whole Lagoon
1948–2018
Sediment StationsTotal PhosphorusTotal Nitrogen
AuthorsYearthicknessµg g−1mg g−1
cmN°Mean StdMinMaxMean StdMinMax
Perin, 1974 [49]1948–194930-24±16 -501.00±0.86 -1.96
Perin, 1974 [49]1968–197330-164±79 -2501.86±2.20 -3.56
Perin et al., 1983 [50]198320-454±126 -6821.33±0.59 -2.74
CVN, MAV, 1990 [27]1987–198820-339±215 -11021.33±0.89 -4.80
This paper20035165409±1132016771.42±1.420.0912.9
20115118403±1131996841.19±1.950.0311.5
2014588412±1112127071.38±1.300.176.98
2018588403±1161807161.28±1.090.196.98
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Sfriso, A.; Buosi, A.; Tomio, Y.; Juhmani, A.-S.; Mistri, M.; Munari, C.; Sfriso, A.A. Trends of Nitrogen and Phosphorus in Surface Sediments of the Lagoons of the Northern Adriatic Sea. Water 2021, 13, 2914. https://doi.org/10.3390/w13202914

AMA Style

Sfriso A, Buosi A, Tomio Y, Juhmani A-S, Mistri M, Munari C, Sfriso AA. Trends of Nitrogen and Phosphorus in Surface Sediments of the Lagoons of the Northern Adriatic Sea. Water. 2021; 13(20):2914. https://doi.org/10.3390/w13202914

Chicago/Turabian Style

Sfriso, Adriano, Alessandro Buosi, Yari Tomio, Abdul-Salam Juhmani, Michele Mistri, Cristina Munari, and Andrea Augusto Sfriso. 2021. "Trends of Nitrogen and Phosphorus in Surface Sediments of the Lagoons of the Northern Adriatic Sea" Water 13, no. 20: 2914. https://doi.org/10.3390/w13202914

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