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13 December 2012 Midges, Cladophora, and epiphytes: shifting interactions through succession
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Midge larvae (Pseudochironomus richardsoni Malloch) in the South Fork Eel River, California, weave retreats in mats of Cladophora glomerata (L.) Kütz. and graze on its algal epiphytes. Densities of these midges and their effects on Cladophora vary over time (seasonally, over the course of succession, and interannually) and space (down the drainage network). New Cladophora growth is green, turns yellow with early colonization by a monolayer of Cocconeis, and rusty-red as it becomes heavily epiphytized by a multistory layer of Epithemia spp. (Rhopalodiaceae), diatoms that contain N-fixing endosymbiotic cyanobacteria. To determine how midges influence epiphyte assemblage structure, we incubated Cladophora in early (green [G]), mid (yellow [Y]), and late (rusty-red [R]) stages of succession with and without midges and assessed changes in epiphyte density and composition. Midge effects on epiphyte composition and density (as measured by % cover on Cladophora filaments) varied with stage of succession and proximity to the ends of midge retreats. Local increases in retreat-associated cyanobacteria occurred in Y and R stages. Percent cover of Cocconeis increased on Y filaments >2 cm from midge retreats (ambient) indicating indirect midge effects (e.g., fertilization). Midges were less effective grazers on adnate Cocconeis cells than on loosely attached Epithemia and often ingested Cladophora in the process of grazing or retreat building, especially in G and Y stages. In contrast, midges that grazed on R Cladophora primarily consumed diatoms in the Rhopalodiaceae. Midge survival and retreat quality were lower in G than in Y or R stages, where retreats were longer and denser. Shifts in epiphyte composition and % cover caused by midge–algae interactions at small scales (µm–m) could affect ecologically significant processes, such as N-fixation and foodweb interactions at larger reach and watershed scales.

Small-scale variation in the quality and quantity of periphyton can influence the structure and function of river ecosystems at larger scales by affecting biogeochemical cycling and interactions with higher trophic levels (Power 1992b, Wetzel 1993, Kim and Richardson 2000, Romaní et al. 2004). The composition and density of algal assemblages can vary over small spatial scales (µm–mm) with microenvironmental variation in light, flow, substrate topography, nutrients, or moisture (Krejci and Lowe 1986, Furey et al. 2007, Lowe et al. 2007, Villeneuve et al. 2010). The patchy distributions of periphyton in riverine benthic environments (Henry and Fisher 2003, Soininen 2003, Veselá 2009) also result in part from complex and varied interactions with grazers (Feminella and Hawkins 1995, Liess and Hillebrand 2004). Grazers can alter algal composition and density directly by grazing (Steinman et al. 1987, Hillebrand 2002, 2008) or indirectly via excretion (Hillebrand et al. 2002). Reciprocally, variation in periphyton composition and density can affect grazer fitness and survival, i.e., via differences in the quality and quantity of food (Gresens 1997, Hessen et al. 2002) or by providing refuge. Thus, grazer–periphyton interactions in rivers may have strong ecological consequences for foodweb dynamics and biogeochemical processes at reach and watershed scales. Understanding ecological linkages that cross scales (both temporally and spatially) will strengthen our ability to predict ecosystem response to environmental changes.

In the South Fork of the Eel River, California, spatial (down the drainage network) and temporal (seasonal and interannual) variation in grazer–algae interactions can significantly influence the amount and distribution of algal biomass (Finlay et al. 2002, Power et al. 2008). The Eel River is an N-limited river in a Mediterranean climate. Most rain falls between October and April, and interannual variation in the magnitude and frequency of floods significantly influences algae–grazer dynamics in summer (Power et al. 2008). After winters with scouring floods, densities of a large voracious caddisfly, Dicosmoecus gilvipes (Hagen), are reduced, releasing the filamentous green alga, Cladophora glomerata (L.) Kütz., from grazing pressure (Power 1990b, 1992a). Subsequent proliferations of Cladophora filaments, often several meters in length, can increase the surface area available to algal epiphytes up to 200,000× over plan-view (water surface) area (Power et al. 2009).

Epiphyte assemblages on Cladophora vary seasonally and spatially down the drainage network, e.g., as light, flow, and substrate change (Power 1990a, b, Bergey et al. 1995, Power et al. 2009). In early summer, new Cladophora growth is green with a light load of algal epiphytes, which generally include stalked diatoms, such as Gomphonema Ehrenb. and Rhoicosphenia Grunow. By mid-summer, Cladophora turns yellow because of colonization by a dense monolayer dominated by the adnate diatom Cocconeis pediculus Ehrenberg. This mid-successional epiphyte assemblage changes to a rusty-red multistory epiphyte assemblage dominated by diatoms in the Rhopalodiaceae, especially Epithemia sorex Kütz. and Epithemia turgida (Ehrenb.) Kütz, but also Epithemia adnata (Kütz.) Bréb. and Rhopalodia gibba (Ehrenb.) O. Müller. This unique group of diatoms contains N-fixing endosymbiotic cyanobacteria (Floener and Bothe 1980, DeYoe et al. 1992). Epithemia-covered Cladophora can elevate rates of N-fixation, increasing the biologically available N in the river (J. Welter, St. Catherine University, unpublished data), especially in reaches draining >100 km2, where Cladophora and its epiphytes dominate the summer biomass of primary producers (Power et al. 2009). Spatial and temporal variation in densities and distribution of loosely vs tightly attached algal epiphytes and N-fixing taxa probably influence the quality and quantity of algal food available to grazers (McCormick and Stevenson 1989, Dudley 1992).

Larvae of the herbivorous midge, Pseudochironomus richardsoni, weave retreats from Cladophora and graze on its algal epiphytes, primarily diatoms (Power 1991, Gresens 1997, Power et al. 2009). Initially, retreat weaving by midges reduces Cladophora biomass through clipping and fragmentation (Power 1990a), but midge grazing grooms epiphytes from underlying Cladophora (fig. 6 in Power et al. 2009), enhancing its exposure to light and nutrient fluxes. These observations suggest a complex interaction between midges, Cladophora, and its associated epiphytes. However, little is known about how grazing by midges changes local algal assemblage composition and densities, especially of N-fixing Rhopalodiaceae. Cladophora proliferations and retreat-weaving midges are widespread and abundant in the Eel and similar rivers, so they could have large ecological and biogeochemical effects at basin scales, if midge–Cladophora interactions significantly alter epiphyte composition.

We examined effects of P. richardsoni on the composition and % cover of epiphytic assemblages on Cladophora in early (green [G]), mid (yellow [Y]), and late (rusty-red [R]) stages of succession, with special focus on N-fixing diatoms in the Rhopalodiaceae. We also examined midge retreats (length, density of retreat walls, construction rates) built with Cladophora filaments in these 3 stages. We hypothesized that retreat-weaving midges would change the composition and % cover of epiphytic assemblages on Cladophora in areas near or associated with their retreats by decreasing the densities of N-fixing diatoms like Epithemia and upright diatoms like Rhoicosphenia. We expected these taxa to be more common in midge guts relative to adnate diatoms like Cocconeis. Second, we hypothesized that Cladophora health, as measured by chloroplast vigor, would increase in the presence of midges if midges reduced epiphyte loads and exposed underlying Cladophora to increased light and water-column nutrients. We expected this facilitation would be stronger in R Cladophora with more loosely attached epiphytes than in G Cladophora with light epiphyte loads or in Y Cladophora with dense loads of the Cocconeis, predicted to be more difficult to graze.


We collected midges (P. richardsoni) and algae (C. glomerata and associated epiphytes) on 13 July 2009 from the South Fork of the Eel River in the Angelo Coast Range Reserve, Mendocino County, California, USA (lat 39°43′45″N, long 123°38′45″W; Midges were collected from R Cladophora from the same reach with similar habitat conditions (light, substrate, flow). We incubated Cladophora with epiphyte assemblages indicative of the 3 different successional stages (G, Y, R stages) at room temperature (20–23°C) in the laboratory in Petri plates (8.9 cm diameter) in the presence and absence of midges (2 × 3 factorial design, 6 replicates). River temperatures during this time ranged from 19.5 to 21.0°C. Temperature in the laboratory, which lacked heat or air conditioning and was within the riparian corridor <100 m from the river, was similar to temperature at the river–air interface during July and August, when midge abundance was highest. Lack of flow in the Petri plates was of potential concern as a laboratory artifact. However, the short (∼2-d) duration of the incubation, the low biomass density of Cladophora in the Petri plates, refreshment of water in the Petri plates, and the partial similarity of laboratory to field conditions somewhat reduced these concerns. During the low-flow summer period, floating Cladophora, its epiphytes, and heavy midge infestations commonly occur in stagnant backwaters and along pool margins where flow is minimal. Petri plates were incubated next to a corner of windows (facing north and west), where they received ambient sunlight filtered through forest. We added river water daily as needed.

We removed insects and debris from freshly gathered Cladophora with gentle rinsing and by picking with forceps. We held cleaned Cladophora samples in a 0.3-mm-mesh net to allow excess water to drain for 30 s before weighing to obtain damp mass. We added 0.76 ± 0.08 g (mean ± SE) damp mass to each Petri plate and filled each Petri plate with river water. We laid plates out in a randomized blocked design with different treatments cross-grouped by the 3 successional stages (and corresponding epiphyte loads) of Cladophora and the presence or absence of midges. Before we added midges, we determined epiphyte densities from samples of algae from each Petri plate (see below). We gently teased midges from their retreats and added 3 midges (8.0–11.2 mm body length) to each with-midge Petri plate. We ran the experiment until midges were preparing to pupate (indicated by an enlarged thorax) (52 h). At hour 22 we replaced any midges that had died.

We assessed retreat robustness at hours 9, 19, 23, 31, and 52. We measured retreat length and scored retreat-wall density on a relative scale: 1  =  little to no weaving of Cladophora filaments, 2  =  light weaving, bottom of the Petri plate easily visible through much of the retreat, 3  =  <50% of the bottom of the Petri plate visible, 4  =  <80% of the bottom of the Petri plate visible, 5  =  could not see through retreat.

At the end of the experiment, we scored the overall percentages of healthy vs unhealthy Cladophora (as determined by changes in color and texture and the presence of any surface films that developed on the water). We compared chloroplast health between the beginning and the end of the experiment by assessing the fullness of unpreserved Cladophora cells along filaments. We scored cell fullness/chloroplast health on a relative scale (5  =  very healthy, bright green chloroplast that filled 95 to 100% of the cell, 4  =  healthy chloroplast that filled 70 to 94% of the cell, 3  =  chloroplast filled 40 to 69% of the cell, 2  =  chloroplast not healthy and filled 20 to 39% of the cell, 1  =  chloroplast filled <20% of the cell or only remnants of the chloroplast present, 0  =  cell appeared to be dead). We preserved (2% formaldehyde) algae collected from the middle of the Petri plate in control treatments, and algae collected >2 cm from both ends of midge retreats (not associated with retreats; ambient algae) and <0.2 cm from retreat ends (retreat-associated) from each with-midge treatment (retreats made by midges that had been replaced were not selected). We collected and preserved material from midge fore- and hindguts. We preserved 2 retreats from each of the G, Y, and R treatments in 2% formaldehyde for scanning electron microscope (SEM) analysis. Retreats from G treatments did not maintain sufficient structure and were not analyzed under the SEM.

Algal analysis

We counted 10 Whipple-grid views (10 × 10 squares; square width  =  12 µm) for each algal sample at 500× (400× with a 1.25 optivar) using a Nikon Optiphot photomicroscope with Nomarski differential interference contrast optics (Nikon Co., Tokyo, Japan). The Whipple-grid method of counting allowed us to take into account differences in biovolume among algal species. We determined epiphyte loads (% cover) by lining up Cladophora filaments horizontally under a Whipple-grid and counting only the epiphytes on the upper surface and half way down the curve on each side of a filament (½ of the cylindrical filament). When the width of the Cladophora filament was less than the width of the Whipple grid, we normalized filament width to 100% of the Whipple-grid area by applying a correction factor. The cyanobacterium Chamaesiphon Braun et Grunow was too small to estimate accurately by this method, so we counted each Chamaesiphon cell and divided the total count by 10 to establish a Chamaesiphon areal-equivalency unit for data analyses (i.e., 10 Chamaesiphon cells  =  1 Chamaesiphon unit). In addition, we used the cell counts to calculate Chamaesiphon density/Cladophora surface area (cells/cm2). Relative biovolume of epiphytes was also calculated. For midge gut analyses, we used the Whipple grid to count live and dead cells, including broken parts of diatoms when >25% of the frustule was present.

We processed midge retreats for SEM analysis through an alcohol series to remove water prior to critical-point drying (Samdri-780A Critical Point Dryer; Tousimis Research Corp., Rockville, Maryland). We sectioned samples with a sharp razor blade and mounted the sections on aluminum SEM stubs with the aid of a dissecting microscope to establish retreat orientation. We sputter-coated midge retreats with 10 nm of AuPd and examined and photographed them under a high-resolution Hitachi S2700 SEM (Hitachi Co., Tokyo, Japan).

Data analysis

For epiphyte assemblage analysis, we normalized % cover with an arcsine√(x) transformation (appropriate for proportional data) and examined clustering based on a reduced taxon list with nonmetric multidimensional scaling (NMDS) of Bray–Curtis similarities (Primer 5, version 5.2.9; Primer-E Ltd., Ambleside, UK; Clarke 1993). We excluded taxa that were present in only 1 or 2 Petri plates to ensure sufficient data for ordination. We examined NMDS clustering patterns of ambient algae based on Cladophora stage (G, Y, R), time (beginning and end of the experiment), presence/absence of midges, and combinations of these variables. We examined the effect of midges on epiphyte assemblage structures closer to the midge retreats (a more local effect) by including epiphyte assemblages on retreat-associated Cladophora and using position (ambient and retreat-associated) as an additional factor. We derived Analysis of Similarity (ANOSIM) routines from the Bray–Curtis similarity matrix to determine whether % cover of taxa in epiphyte assemblages differed in the presence and absence of midges at the beginning and end of the experiment or between epiphyte assemblages from retreat-associated and ambient algae. When significant differences were detected, we conducted post hoc pairwise comparisons and explored the R values of the pairwise comparisons (larger values indicate greater segregation of samples). We applied Bonferroni corrections to account for multiple comparisons.

To examine the grazing preferences of midges for a particular algal type i out of m possible algal food types in the environment, we used Chesson's (1978, 1983) food preference index:


where αi is the estimated preference for algal food type i, ri is the abundance of the ith food type in the diet, ni is the abundance of the ith food type in the environment, scaled so that αi for all available food types in the environment sum to 1. We used Chesson's (1983) model, which assumed no food depletion. We assumed that consumed epiphytic algae were replaced by reproduction or that the difference over 2 d was insignificant relative to total epiphytic algal biomass. Midges may have reduced algal cell densities on a local microscale, but algae did not look visibly depleted of epiphytes.

We used a 2-way analysis of variance (ANOVA) to determine if change in chloroplast health of Cladophora between the beginning and end of the experiment was affected by the presence/absence of midges, Cladophora stage, or the interaction of these 2 factors. We ran Tukey's post hoc multiple comparisons with a Bonferroni-corrected p-value when we found significant differences among means. We used repeated measures analysis of variance (RM ANOVA) with 1 within-subjects factor (time) and 1 between-subjects factor (Cladophora stage) to test whether retreat length or density score differed with time or Cladophora stage. We used retreat measurements made on all 4 dates. We used an ANOVA with Tukey's post hoc comparisons to test for differences over time and between retreat ends and ambient algae in mean Chamaesiphon cell densities on Y Cladophora. We did all ANOVA and RM ANOVA statistical procedures with SPSS (version 16.0; SPSS, Chicago, Illinois).


Algal assemblages

The composition of ambient epiphyte assemblages differed significantly among G, Y, and R Cladophora stages (ANOSIM1, global R  =  0.803, p  =  0.001; Table 1). Within each Cladophora stage, epiphyte assemblages in control and midge plates were similar at the start of the experiment (though they were variable) but changed over time (duration of the experiment) or in the presence of midges (ANOSIM1; Tables 1, 2, Fig. 1A–C). G Cladophora had diverse but low % cover of epiphytes, of which Cocconeis and Rhoicosphenia were most common (Table 2). Y Cladophora had a denser load of epiphytes dominated by a monolayer of Cocconeis (>95% relative biovolume), primarily Cocconeis pediculus (Table 2, Fig. 2A–D). R Cladophora had a multilayered (2–3 layers) load of epiphytes, rich in N-fixing taxa, and predominantly diatoms in the Rhopalodiaceae (>50% relative biovolume), especially E. sorex and E. turgida (Table 2, Fig. 2E, F, H). Chlorophytes on R Cladophora were dominated by Gongrosira, a taxon that was absent from G or Y successional stages. Over time, % cover of C. pediculus increased on G Cladophora in the control and on Y Cladophora in the presence of midges and at retreats ends (Table 2). Over time, % cover of Rhopalodiaceae and N-fixing cyanobacteria increased on R Cladophora in the control and midge treatments and on retreat ends (Table 2). The insides of Y and R retreats were lined with silk and absent of epiphytes (Fig. 2 C, G).

Fig. 1.

Two-dimensional nonmetric multidimensional scaling ordination of Bray–Curtis similarities from arcsine√(x)-transformed % cover of epiphytic algae on green (A), yellow (B), and rusty-red (C) Cladophora from the beginning (before) and end (after) of the experiment in the absence (C) and presence (M) of midges. In the key to symbols, assemblages from treatment combinations circled in gray are statistically different (ANOSIM1, post hoc pairwise comparisons p < 0.0042; Table 1).


Fig. 2.

Scanning electron micrographs of midge retreats constructed from yellow (A–D) and rusty-red (E–H) Cladophora filaments. A.—Opening (O) of retreat with Cocconeis-dominated Cladophora filaments. B.—Outer mid-retreat areas with Cocconeis-dominated Cladophora filaments. C.—Mid-retreat cross section. Note the paucity of algae on the inner silk lining (S). D.—Close up of a retreat-associated Cladophora filament with bacteria and cyanobacteria (including Chamaesiphon) at the margins and between Cocconeis cells. E.—Opening (O) of retreat with Cladophora filaments with heavy and light epiphyte loads. F.—Outer mid-retreat areas with Cladophora filaments with heavy and light epiphyte loads. G.—Mid-retreat cross section. Note the paucity of algae on the inner silk lining (S). H.—Close up of an Epithemia-rich, retreat-associated Cladophora filament. Ch  =  Chamaesiphon, Cl  =  Cladophora, Cpd  =  Cocconeis pediculus, Cpl  =  Cocconeis placentula, Et  =  Epithemia turgida; Es  =  Epithemia sorex, M  =  Melosira, Rc  =  Rhoicosphenia, Rh  =  Rhopalodia.


Table 1.

Post hoc comparisons from Analysis of Similarity (ANOSIM) derived from the Bray–Curtis similarity matrix of arcsine√(x)-transformed % cover of epiphytic algal taxa. The 1st ANOSIM (ANOSIM1) examines broader midge effects on epiphytes by comparing epiphyte assemblages from the ambient Cladophora in the presence of midges (Midge) with epiphyte assemblages in the absence of midges (Control) from the beginning (Before) and end (After) of the experiment for green, yellow, and rusty-red Cladophora stages (see Fig. 1A–C). The 2nd ANOSIM (ANOSIM2) examines more local midge effects by comparing epiphyte assemblages from ambient Cladophora in midge treatments with retreat-associated epiphyte assemblages for Cladophora stages (see Fig. 3A–C). The p value for the post hoc comparisons was adjusted to p < 0.0042 (ANOSIM1) and p < 0.0167 (ANOSIM2) to account for multiple comparisons. Significant p values are underlined.


Table 2.

Mean % cover and relative biovolume of epiphytic algae on green, yellow, and rusty-red Cladophora from the beginning (Before) and end (After) of the experiment from treatments with midges (Midge) and without midges (Ctrl) and from the ends of midge retreats (Rtrt  =  retreat-associated). Cyano  =  cyanobacteria, Chl  =  Chlorophyta, F  =  N fixer, X  =  non-N-fixer.


Midges affected % cover of the epiphyte assemblages on ambient Y but not G or R Cladophora (broader midge effect, ANOSIM1, after-control vs after-midge pairwise comparisons, p < 0.0042; Fig. 1, Table 1). Percent cover of C. pediculus on ambient Y Cladophora increased more with midges than in their absence (Table 2). No significant difference in overall epiphyte assemblage structure on G Cladophora was detected in the presence and absence of midges (ANOSIM1; Table 1).

Midges significantly altered the composition and % cover of epiphytes on retreat-associated Cladophora compared to on ambient Cladophora in the Y and R stages, but not in the G stage (ANOSIM2, global R  =  0.807, p  =  0.001, pairwise comparisons, p < 0.0167; Fig. 3A–C, Table 1). On Y Cladophora, % cover of Cocconeis (Table 2) was lower and % cover and density of Chamaesiphon were greater on retreat-associated filaments than on ambient filaments (Tables 2, 3). Chamaesiphon densities were 9× higher on retreat-associated than on ambient Cladophora (Table 3). On R Cladophora, % cover of cyanobacteria (especially N-fixing cyanobacteria such as Calothrix) was greater on retreat-associated than on ambient filaments (Table 2). Except for Chamaesiphon, cyanobacteria generally were absent or present in lower numbers on Y and G than on R Cladophora (Table 2). On R Cladophora, Chamaesiphon was found only on retreats (Tables 2, 3). Percent cover of Cocconeis was slightly higher on retreat-associated than on ambient R Cladophora, but overall densities of Rhopalodiaceae were similar between control, ambient midge, and retreat-associated filaments (Table 2). SEM micrographs of retreats constructed of Y Cladophora did not show any filaments at the retreat opening or mid retreat that were notably cleared of epiphytes (Fig. 2A–B), whereas micrographs of retreats constructed of R Cladophora showed that some filaments were largely epiphyte-free (Fig. 2E).

Fig. 3.

Two-dimensional nonmetric multidimensional scaling ordination of Bray–Curtis similarities from arcsine√(x)-transformed % cover of epiphytes on ambient and retreat-associated green (A), yellow (B), and rusty-red (C) Cladophora filaments. Asterisks indicate significant differences (p < 0.001). See Table 1 for pairwise comparisons.


Table 3.

Densities of Chamaesiphon (cells/cm2) on filaments of yellow and rusty-red Cladophora stages. Densities of Chamaesiphon were higher on yellow retreat-associated Cladophora than on after-midge ambient Cladophora filaments (ANOVA, F3,34  =  3.389, p < 0.05; Tukey post hoc: p  =  0.018). No statistics were run on Chamaesiphon on rusty-red Cladophora.


Midge gut contents

Live cells (i.e., cells with intact chloroplasts) were predominant in midge foreguts and empty frustules were predominant in hindguts (Table 4). Rhopalodiaceae frustules in the hindgut often contained cyanobacterial endosymbionts, but other cellular contents (i.e., diatom chloroplasts) were absent. Overall, midges showed a dietary preference for diatoms (αi > 0.89) relative to green algae and cyanobacteria (Chesson 1983). Midge intake of Cocconeis relative to other diatoms was greater in plates with G Cladophora, whereas midges preferentially consumed non-Cocconeis diatoms in plates with Y and R Cladophora (Table 5). Guts from midges in plates with G Cladophora contained a variety of diatoms, including Cocconeis, Rhoicosphenia, and Rhopalodiaceae taxa (Table 4). Guts from midges in plates with Y Cladophora primarily contained Cocconeis frustules and some Rhopalodiaceae cells (Table 4). Guts from midges with R Cladophora contained >93% Rhopalodiaceae taxa (Table 4). Midges in plates with Y and G Cladophora consumed more filamentous green algae, especially Cladophora (but α was not high), than midges from plates with R Cladophora (Tables 4, 5; PCF, personal observation).

Table 4.

Mean relative biovolume units (%) of all algae (live and dead) and relative biovolume units of live vs dead cells from the foreguts and hindguts of midges from green, yellow, and rusty-red Cladophora stages. Cells were considered dead if they were completely void of cell contents. Cyano  =  cyanobacteria, Chl  =  Chlorophyta, F  =  N fixer, X  =  non-N-fixer. See Table 1 for taxon groupings.


Table 5.

Average αi values from the food preference model (Chesson1983; Case 1) based on algae found in midge foreguts and hindguts after grazing on green, yellow, and rusty-red Cladophora filaments and associated epiphytes. The model assumes food densities did not change (i.e., algal reproduction or consumption was insignificant compared to total amount of algal biomass available). αi indicates a preference of the midge for particular algal taxon relative to the algal taxa available to graze. If αi  =  1, then the midge diet consisted entirely of that food type. If αi  =  0, then that food type was not present in the midge diet. Chl  =  Chlorophyta (Cladophora and other green filaments), Cyano  =  cyanobacteria, E.  =  Epithemia; Rhoic  =  Rhoicosphenia; Cocc  =  Cocconeis; other diatoms I  =  all other diatoms (Nitzschia, Navicula, Gomphonema, Melosira, etc.); other diatoms II  =  all diatoms excluding Cocconeis. For green and yellow Cladophora stages, diatoms were grouped into other diatoms II because of patchiness on the filaments and to provide sufficient data to run the model.


Midge retreats and Cladophora health

Midges in plates with G, Y, and R Cladophora lined their retreats with woven silk (Fig. 2C, G; no SEM data are available for G Cladophora: PCF and AMC-C, personal observation). The density and length of retreats in G, Y, and R stages of Cladophora increased significantly with time as midges constructed their retreats (RM ANOVAl, F3,84 length  =  7.775, F3,84 density  =  17.960, p < 0.000; Fig. 4A, B). Overall, midges built denser retreats faster in Y and R Cladophora than in G Cladophora, where density scores were never >3 (Fig. 4B). More midges died in the first 24 h in G (44%) than Y and R Cladophora (11%).

Fig. 4.

Mean (±1 SE) retreat length (A) and density (B) for retreats built with green, yellow, and rusty-red Cladophora filaments. Time on the x-axis is presented sequentially and represents measurements taken every 8 to 12 h.


Chloroplasts from G Cladophora were significantly healthier (vibrant color and higher chloroplast health score) at the beginning than at the end of the experiment and were healthier than chloroplasts in Y and R Cladophora regardless of time (ANOVA, F8,62  =  19.82, p < 0.05; Tukey post hoc, p < 0.004). Overall, midges exerted a positive effect on the health of Cladophora. Less filament discoloration and water film was observed in the presence than in the absence of midges, and the chloroplast health score decreased less between the beginning and end of the experiment in the presence than in the absence of midges (2-way ANOVA with midge presence/absence and Cladophora stage as fixed factors, F1,29  =  13.69, p < 0.05). Decreases in Cladophora health scores were affected by a significant interaction between presence/absence of midges and Cladophora stage (2-way ANOVA, F2,29  =  6.25, p < 0.05). The effect of midges on Cladophora health scores was strongest in G Cladophora, which in the absence of midges, had notably discolored filaments (80% discolored in the absence of midges vs 20% discolored in the presence of midges; Fig. 5), a film on the water surface, and a significantly greater decrease in Cladophora chloroplast health score compared to Y and R Cladophora (Tukey post hoc, p < 0.05; Fig. 5). This midge effect was present in Y and R Cladophora (color change and presence of a surface film on the water) but was less noticeable than in G Cladophora, and the change in chloroplast health score was not significant (2-way ANOVA: Tukey post hoc, p > 0.05; Fig. 5).

Fig. 5.

Photographs taken of green (G), yellow (Y), and rusty-red (R) Cladophora grown with (midge) and without (control) midges at the end of the experiment. Note the degree of discoloration (decrease in health) in G Cladophora in the absence vs presence of midges.



The effects of midges on Cladophora epiphyte composition and % cover on Cladophora differed among successional stages (G, Y, R), as did the spatial scale of midge effects, both local (on retreat-associated algae) and general (on ambient algae >2 cm from retreats). Midges affected epiphyte composition via grazing or incidental consumption during retreat building. Indirect effects of midges could have been mediated through nutrient regeneration and removal of certain epiphytes, which helped maintain Cladophora health and released nonselected epiphytes from competition with those that were preferentially grazed.

Direct midge–algae interactions

Midges influenced the composition and % cover of epiphytes by reducing or increasing specific epiphytes on ambient (a broader effect) and on retreat-associated Cladophora (a localized effect). Midge effects changed with Cladophora stage. On G Cladophora, midges affected epiphytes only on ambient filaments, whereas they affected both ambient and retreat-associated Y Cladophora, and only retreat-associated R Cladophora. Midges preferentially consumed diatoms, as has previously been observed in the Eel River and in other studies (Power 1991, Álvarez and Peckarsky 2005, Power et al. 2009). Midges generally preferentially grazed or consumed upright or nonadnate diatoms relative to tightly attached, adnate cells like Cocconeis (Steinman et al. 1987, McCormick and Stevenson 1989, Dudley 1992). In our study, the strength of the midge–algae interactions varied with Cladophora stage, evidenced by differences in % cover of upright, loosely attached, and tightly adhered epiphytes among stages.

G Cladophora.—

Low densities and patchy distributions of epiphytes on G Cladophora made changes in epiphyte % cover and composition difficult to detect. Midges grazed upright or nonadnate taxa, such as Rhoicosphenia and Gomphonema. Frustules of these genera were found readily in midge guts, and these genera occurred in lower densities on Cladophora filaments in the presence than in the absence of midges. The diversity of algal taxa in the midge guts was high, and the density of epiphytic algae available to grazers was low during this early successional stage, and midges appeared to consume all available diatom taxa, including tightly adhered Cocconeis cells. Hungry grazers will graze adnate algae more intensively than satiated grazers will (Steinman 1991). Midges attempting to graze Cocconeis may have consumed Cladophora filaments incidentally because many Cocconeis cells present in the midge guts remained attached to Cladophora (PCF, personal observation). Midges struggled noticeably to build retreats in G Cladophora, and both Cladophora and associated Cocconeis epiphytes may have been ingested incidentally during construction. Mechanical disturbance during attempts to build cases may have further reduced availability of epiphytes (Cattaneo and Mousseau 1995), although Scrimgeour et al. (1991) found that at low algal densities, algal losses occurred primarily because of consumption rather than mechanical foraging-related causes.

Y Cladophora.—

Epiphyte assemblages were composed of >95% Cocconeis on Y Cladophora, and midge guts were full of Cocconeis. Thus, midges grazed Cocconeis. However, the high α values for non-Cocconeis diatoms in midges indicate that midges preferentially grazed, or more easily consumed, these nonadnate diatoms (Steinman 1991, Dudley 1992), a possible indication of selective grazing (Hart 1985). Guts of midges from plates with Y Cladophora had even higher Cladophora content than guts of midges from plates with G Cladophora, a result suggesting that midges ingested Cladophora while attempting to graze adnate, tightly adhering Cocconeis cells. Lower Cocconeis densities on retreat-associated than on ambient filaments in Y Cladophora indicate a strong local effect of grazing.

R Cladophora.—

Like in other studies (Steinman 1991, Dudley 1992), midges preferentially grazed on non-Cocconeis taxa, especially N-rich Rhopalodiaceae taxa. The higher densities of Cocconeis cells on retreat-associated filaments probably occurred because removal of the overstory of Epithemia during grazing exposed underlying epiphytes. Removal of overstory epiphytes can promote growth of understory algae (Dudley 1992), so the exposure of underlying Cocconeis cells may have increased their viability and promoted growth of associated Chamaesiphon (Stevenson and Stoermer 1982). Over longer time intervals in the river, midges remove epiphytes from R Cladophora and expose underlying filaments to yield macroscopically visible greening of Cladophora near midge retreats (see fig. 6 in Power et al. 2009). In our laboratory experiment, we did not observe macroscopic change in Cladophora color, but SEM micrographs of retreat-associated Cladophora filaments (Fig. 2E) and microscopic observations support field observations of epiphyte removal by midges. Ultimately, the color of the assemblage will depend on grazing rates relative to the growth rates of Rhopalodiaceae and of the Cladophora host.

Algal effects on midges.—

Midge survival and the quality of midge retreats (length and density) were poor in plates with G Cladophora but better in plates with Y and R Cladophora. In the field, retreat-weaving midges are more common in Y and R stages of Cladophora and are rare in G Cladophora (Power et al. 2009). In our study, the low % cover of epiphytes and low density of branching in G Cladophora (Bergey et al. 1995) may not have provided sufficient roughness or structure for midges to grasp filaments, making it more difficult to build high-quality retreats. Poorer-quality retreats in G Cladophora would increase midge vulnerability to predators, such as the hydrophilid beetle larvae, Enochrus sp., which is common in Cladophora mats (Power 1990b). In contrast, the denser retreats built in Y and R Cladophora may protect midges from predation (Peckarsky 1982) and desiccation (Zamora-Munoz and Svensson 1996) in floating mats or as flow recedes and midge retreats are exposed to air. In Y and R Cladophora, midges appeared to tighten the weave of the filaments along the length of their retreats before pupation by weaving more Cladophora into the retreat or tightening the weave of filaments already present. Older midge retreats also are wider than new retreats (Power 1991). Caddisflies with stronger or wider cases are better protected from predators than caddisflies with weaker or narrower cases (Nislow and Molles 1993, Otto and Johansson 1995).

Food quality (i.e., polyunsaturated fatty acid and lipid content, C∶N ratio) strongly affects growth rates and other fitness correlates of freshwater invertebrate primary consumers (Gresens 1997, Ravet and Brett 2006, Brett et al. 2009). Pseudochironomus larvae have higher specific growth and developmental rates and larger pupae when reared on a diet of diatoms than when reared on a diet of detritus (Gresens 1997). Food quality may increase over the course of epiphyte succession on Cladophora for 2 reasons. First, late-successional Rhopalodiaceae fix N, a limiting nutrient in the Eel River ecosystem (Hill and Knight 1988, Power 1991), so these unique diatoms are rich in proteins relative to other algae (Kupferberg 1994). Second, midges may spend less time and energy acquiring food as loosely attached epiphytes become relatively more abundant than adnate diatoms like Cocconeis. Therefore, we predict that as midges increase their consumption of diatoms and decrease their ingestion of low-quality Cladophora filaments during algal succession, midge growth rates should increase and their time to maturation should decrease. This prediction is supported by areal rates of emergence of adult midges, which are up to 25× greater from R than from G Cladophora mats (Power et al. 2009).

Indirect midge–algae interactions

Indirect midge-driven changes to epiphyte composition and % cover and to Cladophora health and growth (e.g., from nutrient inputs from excretion) could affect Cladophora microenvironments. For example, midges had a positive indirect effect on Cocconeis densities and reproduction in Y Cladophora, probably via nutrients from midge excretion. Midges may be increasing their food base by increasing densities of diatoms with fertilization (gardening sensu Ings et al. 2010) or by clearing epiphytes from Cladophora and increasing surface area for colonization by new food epiphytes (gardening sensu Hart 1985).

Midges had a positive indirect (nutrient-mediated) local effect on densities of cyanobacteria on retreat-associated filaments in both Y and R Cladophora stages. Algae, especially cyanobacteria and other small taxa with their high surface area to volume ratio (i.e., Chamaesiphon and Calothrix), may take advantage of local nutrient increases caused by midge excretion or feces (Liess and Hagland 2007), especially at the ends of midge retreats, or from nutrients released by cell breakage during grazing (Saba et al. 2011) and filament fragmentation during retreat construction. In Y Cladophora, Chamaesiphon at retreat ends and along ambient filaments may take advantage of leakage of nutrients, such as P, caused by Cocconeis-induced injury to Cladophora cell walls (Stevenson and Stoermer 1982). Chamaesiphon, like Cocconeis, exhibits luxury uptake of P (Stevenson and Stoermer 1982). Midge feces that accumulated in larval retreats were removed and deposited at retreat ends by midges, especially before pupation (PCF and AMC-C, personal observation). Fecal deposits can concentrate nutrients for uptake by algae. Pringle (1985) observed increases of diatoms on chironomid cases that probably were caused by nutrients excreted by larvae. In contrast, Bergey and Resh (1994) did not find an algal (chlorophyll a) response to fecal material from Gumaga (caddisfly) larvae.

When midges build retreats, they fragment Cladophora and cause turfs to detach (Power 1990a), thereby reducing local biomass. However, on smaller scales and during later phases of succession, midges may prolong viability (and possibly stimulate growth) of filaments in or near retreats, particularly detached Cladophora, by removing epiphytes (Dudley 1992) and regenerating nutrients. Midges often infest Cladophora proliferations in the Eel River at high densities (peaking seasonally at 40,000–60,000 individuals/m2 plan-view area projected to the water surface; Power et al. 2008). Following scouring floods, proliferations of Cladophora in the Eel River during the early summer can be massive (Power et al. 2008). During many such years, 80 to 90% of Cladophora biomass is woven into retreats by midges (Power 1991). Thus, interactions of Cladophora, its epiphytes, and resident midges are likely to have basin-wide ecological consequences for the riverine ecosystem. These consequences also may ramify to watershed and nearshore marine ecosystems linked to the river by aerial exchange (N fixation; insect emergence) and downstream discharge of solutes, biomass, and detritus. Understanding ecology at markedly different scales (both temporally and spatially) should help us detect key watershed–river–ocean linkages, and predict ecosystem changes relevant to watershed and coastal management.


This research was conducted at the Angelo Coast Range Reserve, California, a protected site in the University of California Natural Reserve System. We give special thanks to the reserve manager, Pete Steel. We thank Bowling Green State University, Department of Biological Sciences, for use of their microscopy facilities, including use of the SEM. Funding support was received, in part, from National Science Foundation grants to Jill Welter (DEB 0950016) and John Schade (DEB 0543363) and the National Science Foundation National Center for Earth-surface Dynamics. We thank members of Jacques Finlay's laboratory, University of Minnesota, and 2 anonymous referees for providing valuable critical comments on earlier drafts of our manuscript.

Literature Cited

  1. M Álvarezand B. L Peckarsky 2005. How do grazers affect periphyton heterogeneity in streams? Oecologia (Berlin) 142:576–587. Google Scholar

  2. E. A Bergey C. A Boettigerand V. H Resh 1995. Effects of water velocity on the architecture and epiphytes of Cladophora glomerata (Chlorophyta). Journal of Phycology 31:264–271. Google Scholar

  3. E. A Bergeyand V. R Resh 1994. Interactions between a stream caddisfly and the algae on its case: factors affecting algal quantity. Freshwater Biology 31:153–163. Google Scholar

  4. M. T Brett M Kainz S. J Taipaleand H Seshan 2009. Phytoplankton, not allochthonous carbon, sustains herbivorous zooplankton production. Proceedings of the National Academy of Science of the United States of America 106:21197–21201. Google Scholar

  5. A Cattaneoand B Mousseau 1995. Empirical analysis of the removal rate of periphyton by grazers. Oecologia (Berlin) 103:249–254. Google Scholar

  6. J Chesson 1978. Measuring preference in selective predation. Ecology 59:211–215. Google Scholar

  7. J Chesson 1983. The estimation and analysis of preference and its relationship to foraging models. Ecology 64:1297–1304. Google Scholar

  8. K. R Clarke 1993. Non-parametric multivariate analyses of changes in community structure. Australian Journal of Ecology 18:117–143. Google Scholar

  9. H. R DeYoe R. L Loweand J. C Marks 1992. Effects of nitrogen and phosphorus on the endosymbiont load of Rhopalodia gibba and Epithemia turgida (Bacillariophyceae). Journal of Phycology 28:773–777. Google Scholar

  10. T. L Dudley 1992. Beneficial effects of herbivores on stream macroalgae via epiphyte removal. Oikos 65:121–127. Google Scholar

  11. J. W Feminellaand C. P Hawkins 1995. Interactions between stream herbivores and periphyton: a quantitative analysis of past experiments. Journal of the North American Benthological Society 14:465–509. Google Scholar

  12. J. C Finlay S Khandwalaand M. E Power 2002. Spatial scales of carbon flow in a river foodweb. Ecology 83:1845–1859. Google Scholar

  13. L Floenerand H Bothe 1980. Nitrogen fixation in Rhopalodia gibba, a diatom containing blue-greenish inclusions symbiotically. Pages 541–552 in W Schwemmlerand H. E. A Schenk (editors). Endocytobiology, endosymbiosis, and cell biology. Walter de Gruyter and Co., Berlin, Germany. Google Scholar

  14. P. C Furey R. L Loweand J. R Johansen 2007. Wet wall algal community response to in-field nutrient manipulation in the Great Smoky Mountains National Park, U.S.A. Algological Studies 125:17–43. Google Scholar

  15. S Gresens 1997. Interactive effects of diet and thermal regime on growth of the midge Pseudochironomus richardsoni Malloch. Freshwater Biology 38:365–373. Google Scholar

  16. D. H Hart 1985. Grazing insects mediate algal interactions in a stream benthic community. Oikos 44:40–46. Google Scholar

  17. J. C Henryand S. G Fisher 2003. Spatial segregation of periphyton communities in a desert stream: causes and consequences for N cycling. Journal of the North American Benthological Society 22:511–527. Google Scholar

  18. D. O Hessen P. J FærØvigand T Andersen 2002. Light, nutrients, and P: C ratios in algae: grazer performance related to food quality and quantity. Ecology 83:1886–1898. Google Scholar

  19. W. R Hilland A. W Knight 1988. Nutrient and light limitation of algae in two northern California streams. Journal of Phycology 24:125–132. Google Scholar

  20. H Hillebrand 2002. Top-down versus bottom-up control of autotrophic biomass: a meta-analysis on experiments with periphyton. Journal of the North American Benthological Society 21:349–369. Google Scholar

  21. H Hillebrand 2008. Grazing regulates the spatial variability of periphyton biomass. Ecology 89:165–173. Google Scholar

  22. H Hillebrand M Kahlert A-L Haglund U-G Berninger S Nageland S Wickham 2002. Control of microbenthic communities by grazing and nutrient supply. Ecology 83:2205–2219. Google Scholar

  23. N. L Ings A. G Hildrewand J Grey 2010. Gardening by the psychomyiid caddisfly Tinodes waeneri: evidence from stable isotopes. Oecologia (Berlin) 163:127–139. Google Scholar

  24. M. A Kimand J. S Richardson 2000. Effects of light and nutrients on grazer periphyton interactions. Pages 497–501 in L. M Darling (editor). Proceedings of a Conference on the Biology and Management of Species and Habitats at Risk, Kamloops, B.C., 15–19 February 1999. Volume 2. British Columbia Ministry of Environment, Lands and Parks, Victoria, British Columbia. Google Scholar

  25. S. J Kupferberg J. C Marksand M. E Power 1994. Effects of variation in natural algal and detrital diets on larval anuran (Hyla regilla) life-history traits. Copeia 1994:446–457. Google Scholar

  26. M. E Krejciand R. L Lowe 1986. Importance of sand grain mineralogy and topography in determining micro-spatial distribution of epipsammic diatoms. Journal of the North American Benthological Society 5:211–220. Google Scholar

  27. A Liessand A Haglund 2007. Periphyton responds differentially to nutrients recycled in dissolved or faecal pellet form by the snail grazer Theodoxus fluviatilis. Freshwater Biology 52:1997–2008. Google Scholar

  28. A Liessand H Hillebrand 2004. Invited review: Direct and indirect effects in herbivore – periphyton interactions. Archiv für Hydrobiologie 159:433–453. Google Scholar

  29. R. L Lowe P. C Furey J. R Ressand J. R Johansen 2007. Diatom distribution on wet walls in the Great Smoky Mountains National Park. Southeastern Naturalist 6(Special Issue 1):135–152. Google Scholar

  30. P. V McCormickand R. J Stevenson 1989. Effects of snail grazing on benthic algal community structure in different nutrient environments. Journal of the North American Benthological Society 8:162–172. Google Scholar

  31. K. H Nislowand M. C Molles 1993. The influence of larval case design on vulnerability of Limnephilus frijole (Trichoptera) to predation. Freshwater Biology 29:411–417. Google Scholar

  32. C Ottoand A Johansson 1995. Why do some caddis larvae in running waters construct heavy, bulky cases? Animal Behavior 49:473–478. Google Scholar

  33. B. L Peckarsky 1982. Aquatic insect predator–prey relations. BioScience 32:261–266. Google Scholar

  34. M. E Power 1990a. Benthic turfs vs floating mats of algae in river food webs. Oikos 58:67–79. Google Scholar

  35. M. E Power 1990b. Effects of fish in river food webs. Science 250:811–814. Google Scholar

  36. M. E Power 1991. Shifts in the effects of tuft-weaving midges on filamentous algae. American Midland Naturalist 125:275–285. Google Scholar

  37. M. E Power 1992a. Hydrologic and trophic controls of seasonal algal blooms in northern California rivers. Archiv für Hydrobiologie 125:385–410. Google Scholar

  38. M. E Power 1992b. Top-down and bottom-up forces in food webs: do plants have primacy? Ecology 73:733–746. Google Scholar

  39. M Power R Lowe P. C Furey M Limm J Finlay C Bode S Chang M Goodrichand J Sculley 2009. Algal mats and insect emergence in rivers under Mediterranean climates: towards photogrammetric surveillance. Freshwater Biology 54:2101–2115. Google Scholar

  40. M. E Power M. S Parkerand W. E Dietrich 2008. Seasonal reassembly of a river food web: floods, droughts, and impacts of fish. Ecological Monographs 78:263–282. Google Scholar

  41. C Pringle 1985. Effects of chironomid (Insecta: Diptera) tube-building activities on stream diatom communities. Journal of Phycology 21:185–194. Google Scholar

  42. J. L Ravetand M. T Brett 2006. Phytoplankton essential fatty acid and phosphorus content constraints on Daphnia somatic growth and reproduction. Limnology and Oceanography 51:2438–2452. Google Scholar

  43. A. M Romaní H Guasch I Muñoz J Ruana E Vilalta T Schwartz F Emtiaziand S Sabater 2004. Biofilm structure and function and possible implications for riverine DOC dynamics. Microbial Ecology 47:316–328. Google Scholar

  44. G. K Saba D. K Steinbergand D. A Bronk 2011. The relative importance of sloppy feeding, excretion, and fecal pellet leaching in the release of dissolved carbon and nitrogen by Acartia tonsa copepods. Journal of Experimental Marine Biology and Ecology 404:47–56. Google Scholar

  45. G. J Scrimgeour J. M Culp M. L Bothwell F. J Wronaand M. H McKee 1991. Mechanisms of algal patch depletion: importance of consumptive and non-consumptive losses in mayfly-diatom systems. Oecologia (Berlin) 85:343–348. Google Scholar

  46. J Soininen 2003. Heterogeneity of benthic diatom communities in different spatial scales and current velocities in a turbid river. Archiv für Hydrobiologie 156:551–564. Google Scholar

  47. A. D Steinman 1991. Effects of herbivore size and hunger level on periphyton communities. Journal of Phycology 27:54–59. Google Scholar

  48. A. D Steinman C. D McIntire S. V Gregory G. A Lambertiand L. R Ashkenas 1987. Effects of herbivore type and density on taxonomic structure and physiognomy of algal assemblages in laboratory streams. Journal of the North American Benthological Society 6:175–188. Google Scholar

  49. R. J Stevensonand E. F Stoermer 1982. Luxury consumption of phosphorus by five Cladophora epiphytes in Lake Huron. Transactions of the American Microscopical Society 101:151–161. Google Scholar

  50. J Veselá 2009. Spatial heterogeneity and ecology of algal communities in an ephemeral sandstone stream in the Bohemian Switzerland National Park, Czech Republic. Nova Hedwigia 88:531–547. Google Scholar

  51. A Villeneuve B Montuelleand A Bouchez 2010. Influence of slight differences in environmental conditions (light, hydrodynamics) on the structure and function of periphyton. Aquatic Sciences 72:33–44. Google Scholar

  52. R. G Wetzel 1993. Microcommunities and microgradients: linking nutrient regeneration, microbial mutualism, and high sustained aquatic primary production. Netherlands Journal of Aquatic Ecology 27:3–9. Google Scholar

  53. C Zamora-Munozand B. W Svensson 1996. Survival of caddis larvae in relation to their case material in a group of temporary and permanent pools. Freshwater Biology 36:23–31. Google Scholar

Society for Freshwater Science
Paula C Furey, Rex L Lowe, Mary E Power, and Alexis M Campbell-Craven "Midges, Cladophora, and epiphytes: shifting interactions through succession," Freshwater Science 31(1), 93-107, (13 December 2012).
Received: 8 March 2011; Accepted: 1 October 2011; Published: 13 December 2012

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