Evaluation of Restoration and Flow Interactions on River Structure and Function: Channel Widening of the Thur River, Switzerland

: Removal of lateral constraints to restore rivers has become increasingly common in river resource management, but little is known how the interaction of de-channelization with ﬂow inﬂuences ecosystem structure and function. We evaluated the ecosystem effects of river widening to improve sediment relations in the Thur River, Switzerland, 12 years after implementation. We tested if restored and non-restored reaches differed in water physico-chemistry, hyporheic function, primary production, and macroinvertebrate density and composition in relation to the ﬂow regime. Our results showed that (i) spatio-temporal variation in sediment respiration and macroinvertebrate taxonomic richness were driven by interactions between restoration and ﬂow; (ii) riverbed conditions including substrate size, organic matter content, and groundwater–surface water exchange changed due to restoration, but (iii) physico-chemistry, hydraulic conditions, and primary production were not altered by restoration. Importantly, our study revealed that abiotic conditions, except channel morphology, changed only marginally, whereas other ecosystem attributes responded markedly to changes in ﬂow-restoration interactions. These results highlight integrating a more holistic ecosystem perspective in the design and monitoring of restoration projects such as river widening in resource management, preferably in relation to ﬂow-sediment regimes and interactions with the biotic components of the ecosystem.


Introduction
Flow regime is a principal driver of riverine ecosystems [1][2][3], maintaining habitat conditions and connectivity, and influencing flora and fauna [4][5][6][7]. Sediment regime also sustains riverine ecosystems [8], driving channel morphology and riverbed heterogeneity, and structuring aquatic and riparian communities [9][10][11][12]. Flow and sediment regimes mutually interact, as streamflow transports sediment, and river morphology formed by sediment transport determines hydrodynamics. Therefore, both regimes and their interaction play a decisive role in maintaining habitat structure and ecosystem heterogeneity. Until recently, and rather surprisingly, flow and sediment regimes have been studied separately [13,14], especially in the context of river management [8].
Many ecological attributes of rivers worldwide have been compromised for human needs, mostly through the alteration of flow and sediment regimes. Longitudinal and latitudinal connectivity of water and sediment is dramatically reduced by dams, weirs, and levees, decreasing the physical complexity (ecosystem homogenization) of river channels [15,16]. For example, more than 14,000 km (22%) of rivers in Switzerland have been channelized [17]. Such artificial constraints increase flow velocity and river incision, inducing river-floodplain disconnection [18,19]. In addition, river morphology is simplified by eliminating important hydro-geomorphic processes, reducing sinuosity and homogenising instream habitats among others [20]. Collectively, human interventions have severely modified flow and sediment regimes in rivers with concomitant impacts on resident biota.
Responding to a recent mandate to achieve good ecological status of water bodies, restoration of laterally protected rivers and/or channel reconfiguration has been established as a priority action in various restoration programs in Europe [21], and also globally. A primary goal of these actions is to restore river hydromorphology, resulting in increased habitat heterogeneity for flora and fauna. Through specific restoration actions, river areas with wider channels that foster local sediment deposition and gravel bar development, or areas with greater sediment inputs that increase sediment heterogeneity of streambeds, can create and sustain ecological hotspots with enhanced habitat diversity along rivers [22].
In this study, we assessed the effects of artificial river widening and its interactions with the natural flow on ecosystem structure and function at a reach scale in the Thur River, Switzerland, 12 years after de-channelization. We tested if restored and non-restored reaches differed in water physico-chemistry, hyporheic function, primary production, and macroinvertebrate density and composition, in response to intra-annual flow conditions. The spatial scale of study, i.e., reach scale (10 2 -10 3 m), is quite relevant in such medium-size rivers with dynamic gravel bars where erosion and deposition processes dominate ecosystem structure and function, properties inherent in the response of river ecosystems to restoration measures [23].

Study Site
We examined the Thur River, the largest river in Switzerland free of retention structures such us reservoir complexes. The Thur is a seventh order (Strahler order) perialpine river draining a catchment of 1730 km 2 ( Figure 1A), originating in the north-east alpine region of Switzerland from Mount Säntis (2502 m a.s.l.). Lacking large retention structures, the flow regime of the Thur is natural and dynamic, fluctuating from 3 to 900 m 3 /s with an average discharge of 47 m 3 /s (1995-2016 records). As with many rivers in Switzerland, the Thur was channelized with stone rip-rap in the 1890s for flood protection. In the 1990s, lateral rip-rap from different channel sections of 1-3 km in length was removed to allow the formation of new gravel bars and increase the hydrological connectivity between the river and riparian areas. In the 2002, a 1-km channel of protection (lateral levees, etc.) was removed along both banks of the river, allowing the river to widen using natural processes. This particular stretch was selected for the present study ( Figure 1B). For more information on the restoration see [24,25].
The study reach was located in the lower part of the river (370 m a.s.l.), 12 km upstream of the confluence to the Rhine River. The 2-km long study area comprised the restored reach, which was subject to river widening, and channelized areas upstream and downstream of the restored section ( Figure 1B). Channel width in the channelized reaches was about 50 m, while the maximum width in the restored area was 160 m. The slope of the reach was 0.16%. We selected five sampling sites in the study area ( Figure 1B,C). Two sampling sites were located in the channelized reaches: one upstream (Site 1) and one downstream of the restored reach (Site 5). Three sampling sites were located along the main gravel bar in the restored reach: an erosional site (Site 2), a point bar site (Site 3), and a depositional site (Site 4).

Flow Regime Classification
Field surveys were conducted six times each in 2014 and 2015, monthly from early March to late November. Surveys were conducted when water levels were safe for access into the main channel (wadeable), but after flow pulses of different magnitude to account for hydrological variability ( Figure 2). We used a daily discharge record from a gauging station located 7 km downstream of the sampling sites, at the municipality of Andelfingen, for flow and temperature data. To study the effects of flow variation affecting each sample collection, each period was defined as the time elapsed between two sampling dates. As no defined period can be given for the first sampling date in both years, we used the average flow value from the previous 41 days (average duration of all periods). For categorization, nine hydrological descriptors were calculated for each period using the daily discharge data: mean, median, skewness, maximum, minimum, coefficient of variation, number of days flow was below the first quartile (low-flow events), number of days flow was above the third quartile (high-flow events), and number of days flow was above the sediment motion threshold (150 m 3 /s). The first and third quartiles (20 and 60 m 3 /s, respectively) were calculated from the 20-year record [4], while the sediment motion threshold value was taken from a previous study at the same site [26]. Each sampling period was categorized then into four flow classes according to similarity in the hydrological descriptors using Ward's clustering: high, moderately high (Mod. High), intermediate, and low. We determined the number of classes from an inspection of the cluster dendrogram in a preliminary analysis to reasonably represent the flow regime in the study area (see Results).

Physico-Chemistry and Abiotic Hyporheic Measures
We measured local abiotic conditions including physical, chemical, and hyporheic attributes at each site on each sampling date. Physical attributes were represented by three variables: water depth (cm), velocity (cm/s), and median grain size of streambed sediments (stream d50; mm). An area of around 2 × 6 m near the left bank of the river was defined for each study reach. Due to erosion of the right bank, depths of over 2-m were impossible to sample using both banks. All measurements were randomly sampled within each plot, minimizing sampling disturbance between sites. Water depth was measured using a ruler (n = 5), water velocity at 0.6 depth (cm, n = 5) was measured using a portable velocity meter (MiniAir2, Schiltknecht AG, Gossau, Switzerland), and sediment size distribution was estimated by measuring the b-axis of 50 randomly-collected stones per site [27]. Further, a 0.5-litre water sample was collected at each site, returned to the laboratory, filtered (cellulose nitrate 0.45 µm, Sartorius Stedim Biotech) and analyzed for dissolved organic carbon (DOC; mg C/L), total nitrogen (TN; mg N/L), nitrate-N (NO 3 -N; mg N/L), and total phosphorus (TP; µg P/L) using methods in [28]. Electrical conductivity (µS/cm at 20 • C) was measured in the field using a portable meter (WTW model 340, Weilheim, Germany).
Hyporheic measures included particulate organic matter and median grain size of sediments used in sediment respiration experiments (see below), and vertical hydraulic gradient (VHG). Sediment used in respiration experiments was stored in plastic bags and kept frozen (−20 • C) until analysis. In the laboratory, coarse (CPOM) and fine organic matter (FPOM) was sieved (2 mm) from the sediments, dried at 60 • C, weighed, burned at 450 • C for 4 h, and reweighed to determine ash-free dry mass (AFDM). These sediments then were separated using a sieve column for quantifying grain size fractions >8 mm, 8-4 mm, 4-2 mm, 2-1 mm, 1-63 µm, and <63 µm. Median grain size (Hypo-d50, mm) was calculated using Gradistat v8 [29]. Vertical hydraulic gradient was measured in situ to characterize groundwater-streamwater exchange direction and magnitude. Minipiezometers were driven to a depth of ca. 50 cm into the streambed [30]. Positive values above stream-water surface levels indicated upwelling conditions, while negative values indicated downwelling conditions.

Sediment Respiration and Primary Production
Hyporheic sediment respiration (SR; mg O 2 kg −1 sed h −1 ), a proxy for hyporheic organic matter processing, was measured in-situ following methods in [31]. Change in O 2 concentration (mg/L) was measured overtime in sealed Plexiglas tubes (n = 3) half-filled with hyporheic sediments (5 to 20 cm depth, sieved <8 mm as standard protocol) and then filled with stream water. Surface sediments (first 5 cm of sediments) were excluded to avoid effects on respiration by autotrophs (after [32]). Sediment sampling locations were selected randomly within the study plot. A portable oxygen meter (Hach HQ40d connected to a LD0101 oxygen probe) was used to measure oxygen concentration and temperature in each tube before and after incubation. Hyporheic sediment respiration was calculated based on the consumption of O 2 in the tube and the weight of sediment (R, mg O 2 kg −1 sed h −1 ) and then normalized by a reference temperature (20 • C) to account for seasonal variation [33].
Periphyton biomass (AFDM, g/m 2 ) and chlorophyll concentration (Chl-a, mg/m 2 ) were measured as a proxy for primary production from five random cobbles collected from the streambed, stored in plastic bags, and kept frozen at −20 • C until processed. Periphyton was scrubbed from the surface of each stone using a metal brush, the slurry collected, volume measured, and divided into two sub-samples. Both sub-samples were filtered using Whatman GF/F filters. One filter was dried at 60 • C, weighed, combusted at 450 • C and reweighed for periphyton biomass estimation as AFDM. Surface area of each stone was calculated by wrapping the stone with aluminum foil and using a weight-to-area relationship [34]. The second filter was extracted for 7 min in 90% ethanol at 70 • C, and chlorophyll concentration measured by high performance liquid chromatography [35].

Macroinvertebrate Density and Taxa Richness
Benthic macroinvertebrates were randomly collected (n = 3, at each site and date) using a Hess sampler (250-um mesh, 0.04 m 2 area) and preserved with 70% ethanol. Due to the characteristics of the river and the size of our study plots at a site, local habitats within each plot were relatively homogeneous. In the laboratory, collected individuals were hand-picked and identified to family level (Ephemeroptera, Plecoptera, Trichoptera, Diptera, Coleoptera, Gastropoda, Crustacea, Isopoda, and Odonata) or subclass level (Oligochaeta) and their abundances counted using a stereomicroscope (10× magnification). Macroinvertebrate density (individuals/m 2 ) and taxa richness were calculated from the dataset.

Statistical Analysis
Two-way analysis of variance (ANOVA) was used to test if measured variables differed and interacted among sites (1-5) and flow classes (high, moderately high, intermediate, low) [36]. For better interpretation of the results, sites were re-grouped as restored (Sites 2-4) and non-restored sites (Sites 1 and 5), and the coefficient of variation (CV, defined as the standard deviation/mean) was used to examine the temporal variation of each variable within an area. Variation partitioning was used to determine the relative importance of sites and flow classes on the variation in ecosystem structure and function (various measures), except for macroinvertebrate community composition. The main ecosystem variables were explained individually by linear regression using the 'varpart' function [37] in the 'vegan' package of R software [38]. An ANOVA-like permutation test using the function 'anova.rda' then was used to evaluate the different partitions of each variable. A non-metric multidimensional scaling (NMDS) based on Bray-Curtis distance and calculated on log 10 (x + 1) transformed macroinvertebrate densities was used to examine changes in macroinvertebrate community composition followed by an analysis of similarity (ANOSIM), to test for among-group differences. All analyses were carried out using the R statistical computing software [38].

Flow Classes
Ward's cluster classification resulted in 4 flow classes. The high (n = 4) class showed the highest values of almost every flow indicator except for minimum discharge and low-flow events, followed by moderately high (n = 4), intermediate (n = 2), and low (n = 2) ( Table 1). Periods were classified mainly by seasonality, but differences between 2014 (wet) and 2015 (dry) also contributed to classify intermediate and low classes (Figure 2). Maximum water temperature was 26.6 • C in July 2015 and minimum was 0.8 • C in December 2014.

Abiotic Factors
All collected data are summarized in Table 2. Statistical differences among sites were found in stream-d50, FPOM, CPOM, Hypo-d50, and VHG (Table 3). Their variability also was explained by flow class either directly or interactively with site, indicating that substrate size and hyporheic measures were influenced by de-channelization together with flow. Chemical variables (DOC, TN, and TP) were not explained by site but by flow class, indicating spatial homogeneity at the reach scale and intra-annual variation associated with flow.

Ecosystem Function
Sediment respiration (SR) ranged from 0.10 to 1.39 (mg O 2 kg −1 sed h −1 ) and differed among sites, flow classes and their interactions (all p < 0.01, Table 3), indicating that the spatial patterns of SR differed according to flow class. For instance, SR was lowest and spatially homogeneous for flow class high, while SR became higher and spatially heterogeneous in the other flow classes (Figure 3). SR at non-restored sites showed less variation among flow classes than restored sites (CV = 40% and 71%, respectively). Among restored sites, the temporal variability of SR was highest at the point bar (Site 3). Variation partitioning revealed a stronger influence of flow class (34%) than of site (11%) (Figure 4). Variation in periphyton AFDM and Chl-a was explained only by flow class (p < 0.01; >60% according to variance partitioning) (Figure 4, Table 3). Primary production was highest in flow class low (up to 22 g/m 2 AFDM, >500 mg/m 2 Chl-a) and extremely low (near 0) in the other flow classes.

Ecosystem Structure
Macroinvertebrate density and taxa richness were significantly different among sites and flow classes (p < 0.01) (Figure 3). Taxa richness also was explained by their interaction (p = 0.02). Densities ranged from <100 to over 25,000 ind m −2 . Erosional and point bar areas (Sites 2 and 3) had lower density and taxa richness than the other sites, while non-restored sites (Sites 1 and 5) had slightly higher densities and richness than restored sites (Figure 3). Density CV was higher in restored sites (176%) than in non-restored sites (124%), whereas richness CVs were the same for both (38%). The variation in macroinvertebrate density and richness was explained best by flow class (55 and 15%, respectively) and site (8% and 5%, respectively) ( Figure 4).  Note: Stream-d50 = streambed median sediment size; DOC = dissolved organic carbon; TN = total nitrogen; NO 3 -N = nitrate-N; TP = total phosphorus; Cond = electrical conductivity; FPOM = fine particle organic matter; CPOM = coarse particle organic matter; Hypo-d50 = hyporheic median sediment size; VHG = vertical hydraulic gradient; SR = sediment respiration; Chl-a = periphyton chlorophyll; Density = macroinvertebrate density; and Richness = macroinvertebrate taxonomic richness. * represents the interaction between site and flow class.  NMDS analysis (stress = 0.21; Figure 5) showed a difference in macroinvertebrate composition among flow classes (ANOSIM by groups, R = 0.37, p = 0.001). Assemblages shifted in composition from class high to mod to intermediate along both NMDS axes, and a clearly different grouping was evident for class low ( Figure 5). Restored and non-restored site assemblages were not statistically different in each flow class (ANOSIM, R = 0, p = 0.5), although the difference between restored and non-restored sites were distinctive owing to their position along axis-1 ( Figure 5). The differences between restored and non-restored site communities were constant despite flow type.

Discussion
We investigated the effect of channel protection removal (river widening) on ecosystem structure and function after 12 years in the Thur River, Switzerland. Our results showed that (i) spatial and temporal variation in sediment respiration and macroinvertebrate taxonomic richness were driven by interactions between flow and restoration; (ii) riverbed measures including substrate size, organic matter content, and groundwater-surface water interchange were changed due to restoration, but (iii) water chemistry, hydraulic conditions, and primary production were not affected by restoration.
These findings are important because river restoration often focuses on abiotic conditions with little attention on biotic assemblages or ecosystem function [39][40][41]. Our study revealed that abiotic measures, except channel morphology, changed only marginally but ecosystem structure and function showed complex responses in relation to flow-restoration interactions that are usually absent in channelized rivers due to more stable conditions in sediment and flow regimes. These results highlight designing restoration projects using a more holistic perspective including biotic and functional measures [42] at multiple temporal (intra-and inter-annual) and spatial (habitat, reach) scales, which will help assess results of a project beyond the before/after design.
We found a more abundant and richer macroinvertebrate assemblage, on average, in non-restored than restored sites. These results are in line with previous studies showing marginal changes in macroinvertebrate assemblages in restored reaches despite enhanced habitat heterogeneity [43,44]. The greater disturbance in restored sites, in terms or sediment movement and deposition, may be one explanation for the differences in our study. Other potential explanations for this response by macroinvertebrates include irrelevant spatial scales of management actions, time limitations for assemblages to show a response, or ignoring other stressors in the same river [45]. Further, spatial differences in community composition should be considered. For instance, the community was dominated by snails (Hydrobiidae, Valvatidae, and Planorbidae), Odonata (Gomphidae, Corduliidae), and isopods (Ashellidae) in flow class low, while these groups were absent in the other flow classes (results not shown). Nevertheless, the reduction in abundance and richness does not necessarily lead us to conclude that the restoration had an overall negative impact because the aim of the project was successfully achieved by re-generating flow-sediment interactions.
Measures of ecosystem function revealed various responses to restoration. Here, restoration resulted in the enhancement of spatio-temporal dynamics in sediment respiration due to the interaction between flow and sediment dynamics. Sediment movement in the restored sites was affected differently by the different classes of flow events, whereas this effect on sediment movement was not evident in the non-restored sites, likely because the non-restored sites were more stable and lack the interaction between flow and sediment movement of the streambed. Importantly, this interaction may indicate re-establishment of organic matter processing at the reach scale [46]. Periphyton biomass (AFDM and Chl-a) showed no difference due to restoration but differed among flow classes, likely reflecting greater susceptibility to physical disturbance by scouring and sheer stress [26,47]. The fact that this response occurred in restored and non-restored sites suggests a remarkably low resistance of surface biofilms to spates [26], despite spatial differences in river morphology and bed heterogeneity.
Hyporheic sediment respiration (SR) also showed different responses to flow classes among sites. SR was less variable over time in non-restored relative to restored sites. The lack of natural disturbance in rivers may have general consequences that could lead to a regime shift in habitats [48], such as an increase in (in)organic matter and less organic carbon transported downstream [49]. Restoration clearly increased the heterogeneity in ecosystem function of hyporheic sediments in the Thur River.
Exchange between the water column and channel bed and river banks (vertical and lateral linkages) can affect water quality because these are biogeochemically active areas where organic matter decomposition and nitrogen removal occurs [50,51]. Our results showed that water chemistry was not influenced by the restoration, and is in agreement with previous studies [52,53]. Water chemistry was best explained by intra-annual flow variability, indicating that river water chemistry responds mainly to large-scale processes such as snowmelt water intrusion or major precipitation events [54] as well as large-scale patterns in river morphology such as meandering [55]. Here, the length of the restored stretch (ca. 500 m) may have been too short to detect or cause changes in water chemistry. Overall, the results demonstrate a positive response of rivers to channel widening actions by facilitating sediment flow relations in restored sections.